Cyprus - Sovereign Base Areas Administration

Transcription

Consulting CYPRUS
FINAL REPORT
June 2012
Hydrological Study & Further Studies
to be incorporated in the
Akrotiri Peninsula Management Plan
(Work Order: 1044844)
This Study was prepared by
AP Marine Environmental Consultancy Ltd
&
ATLANTIS Consulting Cyprus Ltd
AP MARINE ENVIRONMENTAL CONSULTANCY LTD
P.O.Box 26728 1647 Nicosia
Tel. 22331660, Fax: 22339959
Email: apmarine@valicom.com.cy
www.apmarine.com.cy
Consulting CYPRUS
TABLE OF CONTENTS
1
2
Introduction ......................................................................................................10
1.1
Structure of this Report.............................................................................11
1.2
Project Team – Key Experts .....................................................................11
Methodology.....................................................................................................12
2.1
Site visits ..................................................................................................12
2.2
Desktop work............................................................................................13
2.3
Field Surveys............................................................................................14
2.3.1
Objectives of field surveys ..................................................................... 14
2.3.2
Survey Area ........................................................................................... 15
2.3.3
Overview of field surveys ....................................................................... 15
2.3.4
Hydrological Conditions ......................................................................... 15
2.3.5
Status of Phallocryptus (Branchinella) spinosa population at the Akrotiri
Salt Lake 16
2.3.6
Flora Conditions..................................................................................... 16
3
Legal requirements for monitoring ....................................................................17
4
Description of the project area..........................................................................20
4.1
General Area Description .........................................................................20
4.2
Hydrology / Geology .................................................................................20
4.2.1
Hydrology............................................................................................... 20
4.2.2
Physical parameters .............................................................................. 25
4.2.3
Land use, water users and pollutant sources ......................................... 27
4.2.4
Geology ................................................................................................. 39
4.3
Birds .........................................................................................................44
4.3.1
Ramsar designation ............................................................................... 44
4.3.2
Important Bird Area designation............................................................. 45
4.3.3
Special Protection Areas (SPA) designation. ......................................... 46
4.4
Phallocryptus (Branchinella) spinosa ........................................................48
4.4.1
Status of the taxonomy of Phallocryptus (Branchinella) spinosa ............ 48
4.4.2
Status of Phallocryptus (Branchinella) spinosa in the IUCN Red List ..... 48
4.4.3
Status of Phallocryptus (Branchinella) spinosa in Cyprus and elsewhere
48
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4.4.4
Salt Lake 49
4.4.5
Other observations (flamingos, Aphanius fasciatus, dragonflies and diving
beetles) 51
4.4.6
Aphanius fasciatus................................................................................. 56
4.4.7
Revised Food Web - Phallocryptus’ perspective .................................... 57
4.4.8
Aquatic biotic components ..................................................................... 59
4.4.9
Aquatic Macrophytes ............................................................................. 59
4.4.10
Benthic Macroinvertebrates ................................................................... 61
4.5
5
Flora .........................................................................................................62
4.5.1
Reference Conditions and Bioindicators ................................................ 62
4.5.2
Vegetation - Habitats ............................................................................. 62
4.5.3
Halophytic Vegetation ............................................................................ 66
4.5.4
Fresh Water Wetlands ........................................................................... 68
4.5.5
Sand Dune Vegetation........................................................................... 70
4.5.6
Thermo-Mediterranea Shrub Vegetation ................................................ 73
Model Conceptualization and Definition of Monitoring objectives......................89
5.1
Geographic scope ....................................................................................89
5.2
Hydrological network / water sources .......................................................89
5.3
Land use, water uses and pollutant sources to be considered ..................90
5.4
Management Goals and Objectives ..........................................................91
5.5
Proposed management objectives in relation to Branchinella and Aphanius
94
5.6
6
Proposed management objectives in relation to birds ...............................94
Reference Conditions.......................................................................................95
6.1
Defining the Akrotiri wetland character......................................................95
6.2
Setting of Reference conditions – Typological issues ...............................97
6.2.1
Hydrology............................................................................................... 99
6.2.2
Macrophytes Reference conditions ........................................................ 99
6.2.3
Macroinvertebrate Reference conditions.............................................. 101
6.2.4
Characterization of the Salt Lake water properties and Phallocryptus
(Branchinella) spinosa population........................................................................ 102
6.2.5
Reference conditions for Phallocryptus (Branchinella) spinosa population
105
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7
Proposed Monitoring Programme...................................................................109
7.1
Hydrology ...............................................................................................110
7.1.1
Water balance...................................................................................... 110
7.1.2
Water levels ......................................................................................... 114
7.1.3
Water Quality ....................................................................................... 115
7.2
Flora and habidats monitoring ................................................................119
7.2.1
Aims and objectives of Monitoring – General Methodology .................. 121
7.2.2
Flora .................................................................................................... 124
7.2.3
Monitoring plan - Habitat mapping ....................................................... 126
7.2.4
Monitoring plan - Vegetation Transects................................................ 128
7.2.5
Monitoring of abiotic parameters .......................................................... 135
7.2.6
Distribution mapping of threatened species.......................................... 136
7.2.7
Population size of species having a population lower than the MVP .... 136
7.3
Fauna .....................................................................................................138
7.3.1
Proposed monitoring objectives and indicators in relation to Phallocryptus
138
7.3.2
Proposed bird monitoring programme .................................................. 140
7.4
Distribution studies .................................................................................141
7.5
Population monitoring .............................................................................142
7.6
Monitoring migrating and over-wintering birds.........................................143
7.7
Monitoring breeding bird populations ......................................................157
7.7.1
Proposed Monitoring Programme for Aquatic biotic components ......... 177
7.7.2
Proposed biotic monitoring indicators................................................... 177
7.7.3
Aquatic Macrophytes ........................................................................... 178
7.7.4
Aquatic Macroinvertebrates ................................................................. 179
7.8
Proposed additional studies....................................................................182
7.8.1
Additional studies in relation to Phallocryptus, Aphanius, and aquatic
insects
183
8
References.....................................................................................................185
9
APPENDICES ................................................................................................192
HABITAT IDENTIFICATION FORM ......................................................................224
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List of Figures
Figure 1 – Water from Zakaki area and the port flowing towards Zakaki marsh ................................... 21
Figure 2- Fasouri Marsh.................................................................................................................... 22
Figure 3 – Zakaki drainage canal....................................................................................................... 22
Figure 4 – Bridge near Pluto project .................................................................................................. 23
Figure 5 – Eucalyptus forest.............................................................................................................. 24
Figure 6 – Stormwater drain pipes ..................................................................................................... 24
Figure 7 – Main hydrological features of the Akrotiri Penynsula .......................................................... 25
Figure 8: Locations of observations and monitoring stations ............................................................... 26
Figure 9: Points 39 and 40 showing flooded areas of the Fasouri Marsh ............................................. 27
Figure 10: Sample locations .............................................................................................................. 28
Figure 11: Water Quality ................................................................................................................... 30
Figure 12: Flow measurement on point 46 (measurements in metters - m).......................................... 30
Figure 13: Flow measurement at point 46. ......................................................................................... 31
Figure 14: Flow measurement at Zakaki Marsh (Bridge) .................................................................... 31
Figure 15: Flow measurement on Zakaki Marsh (bridge). ................................................................... 32
Figure 16: Flow measurement on Zakaki Marsh (bridge). ................................................................... 32
Figure 17: Flow measurements on Urban and Port flows. Combined outflow through Zakaki trench to
Akrotiri Salt Lake. ............................................................................................................ 34
Figure 18: Regression between the salinity values measured with the optical refractometer and the
digital conductometer. Even though there is an apparent strong correlation, it is not
significant. ....................................................................................................................... 37
Figure 19: Conditions of the water at the Salt Lake during the sampling: almost transparent, small pond,
site #6 (A), stained red probably by tannins, small pond near the airstrip, site #9 (B), milky or
cloudy due to resuspended sediments and disturbance of the bottom by feeding flamingos,
site #19 (C). Extensive areas around the lake with thick biofilm layers, site #18 (D). Number
of the sites according to Table 2....................................................................................... 38
Figure 20: View of the cross section .................................................................................................. 41
Figure 21: Cross section ................................................................................................................... 41
Figure 22: Top and middle soil layer ................................................................................................. 42
Figure 23: Middle and lower soil layer................................................................................................ 43
Figure 24: Lower Soil layer................................................................................................................ 43
Figure 25: Underwater observations of the Phallocryptus (Branchinella) spinosa populations at the Salt
Lake: underwater high definition video camera, GoPro, site #18 (A), snapshot of a female P.
Spinosa with a full egg pouch visible in the upper part of the abdomen, site #17 (B), snapshot
of an aggregation of numerous individuals (male and female) of P. spinosa near the
submerged vegetation, site #18 (C), snapshot of a male P. spinosa feeding between the
shoots of Ruppia maritima, site #18 (D). Number of the sites according to Table 2............. 51
Figure 26: General observations at the site #12, where flamingos tend to aggregate more often (A),
bottom modification by the feeding activities of the flamingos (B), input of nutrients (e.g.
feathers, droppings, carcasses) to the Salt Labe by the birds (C). At the same site, we
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confirmed the presence of two juveniles of the toothcarp (killifish) Aphanius fasciatus in the
ponds formed by wheel tracks (D). The site (see Table 2 for coordinates) is near the
drainage canal from the Zakaki Marsh. ............................................................................. 54
Figure 27: Reported and firsthand sightings of the Mediterranean toothcarp (killifish) Aphanius fasciatus
in the Salt Lake in relation to rainfall monthly anomalies (Akrotiri Meteorological Station) and
water salinity (data from the Fisheries Department). Arrows denote the conditions
before/during the observations of the fish: algae bloom (green), rainy days (white), rainy days
and firsthand report (orange). Rainfall monthly anomalies were produced by subtracting the
long-term average (1966-2011) of a given month from the total rainfall for that month, and
smoothed with an 11-point filter. Horizontal grey area denotes the salinity range of A.
fasciatus in the Mediterranean area (Triantafyllidis et al. 2007).......................................... 55
Figure 28: Original food web proposed for the Akrotiri Salt Lake. Flamingos are the top consumers
feeding exclusively on Phallocryptus. ............................................................................... 57
Figure 29: Revised food web proposed for the Akrotiri Salt Lake. White arrows indicate possible
interactions if the waterfowl consumes fry, eggs or small juveniles and adult aquatic insects
and fish. .......................................................................................................................... 58
Figure 30: GLM model of species response graph for the environmental variable Fire. Acacia saligna
trees (Acasalt) and seedlings (Acasall) have a positive response and the other species have
a negative response ........................................................................................................ 65
Figure 31: GAM model of species response graph for the environmental variable Organic Matter.
Juniperus phoenicea has a strong positive almost linear response, Zygophyllum album and
Cakile maritima have negative response.
Plantago maritima and Arthrocnemum
macrostachyum present a unimodal response .................................................................. 65
Figure 32: Vegetation of the habitat type 3170 with Juncus ambiguus and Isolepis cernua in Akrotiri
(14/05/2011).................................................................................................................... 70
Figure 33: Distribution range of 5 threatend plants in Akrotiri Peninsula. ............................................. 88
Figure 34: Conceptual model of the hydrology of the project area ....................................................... 90
Figure 35: Characterization of waterbodies according to WFD 2000/60/EC......................................... 95
Figure 33: Generalized model of aquatic communities in reference and impacted ponds (Coleman, 2009)
......................................................................................................................................... 1
Figure 37: Monthly average and standard deviation of precipitation (Akrotiri Meteorological Station) and
water salinity (data from the Fisheries Department) of the Salt Lake. Averages derived from
the time period 1966-2011 (precipitation) and 1988-2011 (salinity) .................................. 104
Figure 38: Monthly average and standard deviation of water temperature and pH of the Salt Lake.
Averages derived from the time period 1988-2011 (data from the Fisheries Department). 104
Figure 39: Abundance (individuals) of Phallocryptus (Branchinella) spinosa in one sampling station
(“Lake-Recorder”, November 1991 to May 1992) at the Akrotiri Salt Lake (data from Ortal
1992) in relation to water parameters (temperature, salinity, and pH)............................... 105
Figure 40: Abundance (mean and standard deviation) of Phallocryptus spinosa in six sampling stations
(PLUTO II, March 2002) at the Akrotiri Salt Lake (data from Kerrison 2002). There are
differences statistically significant between stations, Kruskal-Wallis P=0.0001698, MannWhitney pairwise comparisons (P<0.005): A ≠ B, E, F; B ≠ C, F; C ≠ E; F ≠ E. ................. 106
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Figure 41: Periods (arrows) when the abundance of Phallocryptus spinosa was studied (Ortal 1992,
Kerrison 2002) and monthly averages of water temperature, salinity, and pH of the Salt Lake
(data from the Fisheries Department) and monthly precipitation (Akrotiri Meteorological
Station). Averages derived from three to four monitoring stations during the time period
1988-2011..................................................................................................................... 107
Figure 42: Periods (arrows) when the abundance of Phallocryptus spinosa was studied (Ortal 1992,
Kerrison 2002) and monthly averages of water salinity of the Salt Lake (data from the
Fisheries Department) and rainfall monthly anomalies (Akrotiri Meteorological Station).
Salinity averages derived from three to four monitoring stations during the time period 19882011. Rainfall monthly anomalies were produced by subtracting the long-term average
(1966-2011) of a given month from the total rainfall for that month................................... 107
Figure 43:Flow measurement locations............................................................................................ 111
Figure 44:Zakaki and Port flow meters............................................................................................. 111
Figure 45: Flow measurement locations near Zakaki Marsh ............................................................. 112
Figure 46: Flow measurement location near Fasouri Marsh.............................................................. 112
Figure 47: Location of 35 transects (yellow lines). Black triangles: species with threat category EN, VU,
DD, and NT. Blue stars: species with threat category CR. ............................................... 128
Figure 48: Diagram of transect and quadrats. .................................................................................. 132
Figure 49: Orchis palustris, plant and habitat in Akrotiri (14/5/2011).................................................. 137
Figure 50: Standard deviation of monthly averages (three to four stations) of water salinity, pH and
temperature of the Akrotiri Salt Lake (data from the Fisheries Department). Arrows indicate
the sampling periods when the abundance of Phallocryptus was studied (Ortal 1992,
Kerrison 2002)............................................................................................................... 138
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List of tables
Table 1: Synopsis of Monitoring Activities .......................................................................................... 12
Table 2: Values of water salinity, conductivity, oxygen, pH at the sites visited during the fieldtrips of
December 2011 and January 2012 in relation to the Phallocryptus (Branchinella) spinosa
component of the study. Numbers represent sampling locations as per Table 2 .................... 35
Table 3: Information of the sites visited during the fieldtrips of December 2011 and January 2012 in
relation to the Phallocryptus (Branchinella) spinosa component of the study.......................... 36
Table 4: Description of the composition of the sediments in the three visible layers. ............................ 40
Table 5: Qualifying species for the identification of Akrotiri Peninsula – Episkopi Cliffs as an Important
Bird Area (taken from Iezekiel et al. 2004)............................................................................ 45
Table 6: Qualifying species, listed in Schedule 1 of the Game and Wild Birds Ordinance, for the SPA
designation of Akrotiri Wetlands and Akrotiri Cliffs. ............................................................... 46
Table 7: Submerged aquatic macrophyte species recorded in the Akrotiri peninsula (VU: Vulnerable, EN:
Endangered, UN: Unknown) ................................................................................................ 60
Table 8: General Principles for the Reference Conditions of habitats .................................................. 66
Table 9: Biological quality index values for the Halophytic habitats of the area of Akrotiri. The working
reference conditions are illustrated by the values of the indices in the undisturbed communities
(Impact=0). ......................................................................................................................... 77
Table 10: Biological quality index values for the Sand Dune habitats of the area of Akrotiri. The working
(Impact=0). Part I. ............................................................................................................... 78
Table 11: Biological quality index values for the Sand Dune habitats of the area of Akrotiri. The working
(Impact=0). Part II. .............................................................................................................. 80
Table 12: Minimum viable population assessment scheme (Primack 1996)......................................... 83
Table 13: List and current data for 30 rare and threatened plants in Akrotiri Peninsula (Data Tsintides et
al. 2007). ............................................................................................................................ 85
Table 14: Habitats identified in Akrotiri peninsula. Map 2000: Hadjikyriakou et al. 2000; Map 2009: Cox
et al. 2009......................................................................................................................... 120
Table 15: Attributes of the proposed transects. ................................................................................ 130
Table 16: Bird Survey Schemes ...................................................................................................... 140
Table 17: Guidance on mandatory attributes for migrating raptors .................................................... 144
Table 18: Guidance on mandatory attributes for the Red-footed Falcon ............................................ 147
Table 19: Guidance on mandatory attributes for the Demoiselle Crane ............................................. 150
Table 20: Guidance on mandatory attributes for the Greater Flamingo.............................................. 152
Table 21: Guidance on mandatory attributes for the Greater Sandplover .......................................... 154
Table 22: Guidance on mandatory attributes for the Kentish Plover .................................................. 155
Table 23: Guidance on mandatory attributes for the Ferruginous Duck ............................................. 157
Table 24: Guidance on mandatory attributes for the Black-winged Stilt ............................................. 160
Table 25: Guidance on mandatory attributes for the Spur-winged Lapwing ....................................... 163
Table 26: Guidance on mandatory attributes for the Kentish Plover .................................................. 165
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Table 27: The information that should be recorded to describe each colony or sub-division of a colony.
......................................................................................................................................... 170
Table 28: Guidance on mandatory attributes for the Eleonora’s Falcon............................................. 171
Table 29: Guidance on mandatory attributes for the Peregrine Falcon .............................................. 172
Table 30: Guidance on mandatory attributes for the Griffon Vulture .................................................. 174
Table 31: Guidance on mandatory attributes for the Mediterranean Shag ......................................... 175
Table 32: Proposed sampling locations for the monitoring of biotic components in Akrotiri waterbodies
......................................................................................................................................... 180
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1
Introduction
In October 2011, A P Marine was commissioned by Interserve Defence Ltd to
undertake the project “Hydrological Study & Further Studies to be incorporated
in the Akrotiri Peninsula Management Plan, Work Order: 1044844”. For the
implementation of the project, A.P Marine cooperated with Atlantis Consulting Cyprus
ltd.
The monitoring plan was developed in response to the mandate for monitoring
activioties that would be able toi inform, enrich and evaluate the effectiveness the
Akrotiri Salt lake Management Plan.
As per the Terms of Reference, the Method Statement covers the following Tasks:
·
Baseline studies to identify the significant biotic parameters of the wetland
ecosystems of Akrotiri Salt Lake, Fasouri Marsh and Zakaki Marsh and associate
them with the abiotic parameters of the wetlands.
·
The definition of abiotic and biotic indicators for a healthy wetland ecosystem at
each of the three sites in line with EU Water Framework Directive.
·
The establishment of a long-term monitoring system for these indicators to inform
decision making under the management plan for the wetlands.
During the course of the project, the consultants have studied the available
bibliography and have implemented several site visits to the project area. In
accordance with project objectives the following have been achieved:
·
Available bibliography and data were collected and studied in order to identify
management objectives for the project area. Results were utilized in determining
monitoting objectives.
·
The area’s key hydrological and ecological characteristics have been determined.
·
The issue of defining reference conditions was examined and a proposal for the
selection of reference conditions has been prepared.
·
A monitoring plan has been prepared.
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1.1
Structure of this Report
This report presents the draft proposed monitoring plan for the Akrotiri Peninsula. It is
a working document intended to provide information regarding the final foreseen
report structure and content as well as current progress. The report is divided into the
following chapters:
·
Chapter 1
–
Introduction
·
Chapter 2
–
Methodology, Bibliographical and past report consulted,
the information collected as well as data requested but
not acquired
·
Chapter 3
–
Legal framework for monitoring
·
Chapter 4
–
Description of the project area
·
Chapter 5
–
Environmental Setting and Conceptual Model
·
Chapter 6
–
Reference Conditions
·
Chapter 7
–
Monitoring Programme
·
Chapter 8
–
References
·
Chapter 9
–
Appendices
1.2
Project Team – Key Experts
·
Antonis Petrou,
Aquatic resource management: Project
coordinator.
·
Charalambos Panayiotou,
Environmental Science: Scientific coordinator,
hydrology
analysis,
integration
and
interpretation of studies, editing of the report.
·
Iacovos Tziortzis,
Aquatic Macroinvertebrates specialist: Studies
of aquatic biotic parameters
·
Pinelopi Delipetrou,
Biology: Flora and habitat studies
·
Iris Charalambidou,
Ornithologist, Aquatic bird study
·
Carlos Jimenez,
Aquatic Biologist
Supporting Staff
·
Elias Eliades,
Geotecnician MSc (Management of the
Environment, Natural Resources and Forestry)
MSc in Civil Engineering
·
Ourania Tzoraki,
Hydrologist
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2
Methodology
2.1
Site visits
Table 1 summarizes the site visits that were undertaken during the project.
Table 1: Synopsis of Monitoring Activities
Date
Objective
Clarify the objectives
of the study
11-Nov-2011
Elaborate key issues
of concern
Where
Akrotiri Environmental
Education and
Information Centre,
Project site
Site tour
22-Nov.-2011
18-Dec-2011
Obtain GPS points of
key features
Map the hydrological
network of the
project area
Limited water
samping
Record presence,
distribution,
abundance
Phallocryptus
spinosa
27-Dec-2011
Ditto. Collect live
Phallocryptus
spinosa specimens
04-Jan-2012
Ditto. Measure
salinity and collect
water samples
Participants
Present:
Interserve Defences Ltd:
P. Nicolaou, A. Perdiou
Akrotiri Environmental
Education and Information
Centre:
T. Hadjikyriakou
Contractors:
A. Petrou (A.P. Marine), C.
Panayiotou, T. Toumazi &
E.Eliades (Atlantis
Consulting Cyprus Ltd),
I.Charalambidou, C.
Jimenez, I.Tziortzis,
O.Tzoraki
Akrotiri Penynsoula
T.Toumazis
O.Tzoraki
Akrotiri Salt Lake: Small
pond between the road
and the Lake. Pond
Agios Georgios Church
C. Jimenez, M. Sour, I.
Tziortzis, C. Thoma
pond between the road
and the Lake. Lake
shore near Zakaki
Marsh.
Akrotiri Salt Lake: Pond
Agios Georgios Church,
Small ponds near
airstrip. Lake shore
across the
environmental Centre.
Charalambidou, S. Glucel,
C. Thoma
C. Jimenez, M. Sour
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Date
Objective
05-Jan-2012
Ditto, except water
samples
08-Jan-2012
Ditto, except water
samples. UW videos
of Phallocryptus
spinosa
Where
Vernal Ponds at
Potamos to Liopetriou,
Larnaka Salt Lake
ponds near airstrip,
Pond Agios Georgios
Church, Lake shore
near end of airstrip.
Phassouri Marsh
19-Jan-2012
6-Apr-2012
7-Apr-2012
C. Jimenez, M. Sour, R.
Abu-Alhaija
Tziortzis, G. Fyttis
Elias Eliades & T.Toumazis
Sampling and
monitoring
10-Apr-2012
All water bodies of the
project site and
souurounding areas
11-Apr-2012
2.2
Participants
Penelope Delipetrou
Elias Eliades
Desktop work
The project team examined the bibliography provided by the client as well as
additional bibliography and studies collected from Competent Authorities and through
internet searches. These studies contributed further to the formulation of the project
report. New information included:
·
Groundwater level data Salt lake water monitoring results (depth, pH,
temperature and salinity)
The description of the study area and the drafting of the monitoring plan have been
based on bibliographical studies and field visits. In particular the project team took
the following steps:
·
Study of current bibliography acquired from Interserve Defence Ltd.
·
Study of additional bibilography
·
Data collection from Competent Authorities
·
Field visits and monitoring
·
Contact and discussion with authorities in Salt Lake ecology and Taxonomy
Interserve Defence Ltd. provided the contractor with all the available major studies
undertaken in Akrotiri Peninsula, as well as with various other relevant reports.
Additional reports and publications were collected from Competent Authorities,
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internet searches and other sources. A list of collected reports is provided in
Bibliography of the monitoring plan.
Relevant data were also requested from the Cyprus National Competent Authorities
as follows:
·
Meteorological/
climate data,
Meteorological Department,
Ministry
of
Agriculture, Natural Resources and Environment.
·
Boreholes and water abstraction, Water Development Department, Ministry of
Agriculture, Natural Resources and Environment. We haven’t received this
data set of the bore holes, I requested it in December and I am still waiting.
·
Water levels and water quality data, Water Development Department, Ministry
of Agriculture, Natural Resources and Environment
·
Geological and Geochemical data, Geological Survey Department, Ministry of
Agriculture, Natural Resources and Environment.
·
Monthly waterbird bird counts from the Cyprus Game Fund, Ministry of
Interior.
·
SBAA Environment Department.
·
Land use maps, Department of Environment
·
Temperature, salinity, depth and pH of the Salt Lake from the Fisheries
Department
2.3
Field Surveys
2.3.1
Objectives of field surveys
The surveys aim to produce baseline information regarding the key hydrological and
ecological characteristics of the project are, and the ecological status of conservation.
Through the collected information, key parameters pertaining to the physical and
ecological characteristics of the area will be identified and will be considered in the
drafting of the monitoring plan. In addition, suitable locations for monitoring activities
will be selected.
More precisely the objectives of the surveys are:
§
Identify the key hydrological features and charateristics of the project area
§
Describe the key ecological features and the habitat types of the area.
§
Determine key hydrological indicators and suggest suitable baseline/
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reference values
§
Determine key ecological parameters and suggest suitable baseline /
reference values
§
Identify indicator species
§
Support the preparation of the monitoring plan for the key hydrological and
ecological parameters and indicator species
2.3.2
Survey Area
The surveys extended to the three key wetlands of the Akrotiri salt lake, the Zakaki
Marsh and the Fasouri Marsh. It also included surrounding areas which constitute a
direct water source to the wetlands as well as the canals that link the two marshes
with the salt lake. Upstream water sources are implicitly considered as boundary
conditions through the monitoring of water inflows at the Zakaki Marsh.
2.3.3
Overview of field surveys
An initial field visit took place on November 11th, 2011 which invlolved all partners as
well as representatives from Interserve. During the meeting, the project team
requested clarifications regarding the project objectives as well as information
regarding the project area. The project team was subsequently toured around the
project area, including the Salt Lake, Zakaki Marsh, Fasouri Marsh and the
surrounding area.
2.3.4
Hydrological Conditions
The hydrological network of the project area has been initialy determined from
existing data and maps. Additional field visits took place in order to complete the
network and to gather data concerning the storm water runoff conditions. During the
visits the team members took GPS points of the main areas where the water enters
the salt lake and verified the linkage between the marshes and the salt lake. In
particular the drainage system crossing the the Akrotiri road, which consists of a
series of drainage pipes, and the channel between Zakaki Marsh and the salt lake
were marked with the use of a GPS (Geographical Positioning System). The results
are available in Chapters 3.2 and 4.2. Preliminary water flow rates were alsso taken
with use of a mobile flow meter where possible. In addition, water samples were
taken for chemical analysis in order to determined water quality parameters.
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Soil samples were taken from a cross section in a ditch in the salt lake that was
recently open to a depth of approximately 1.5 meters and a width of about 4 meters.
Sipping water was also collected from the ditch. The sediment profile analysis is
available in Chapter 3.6.
2.3.5
Salt Lake
During December 2011 and January 2012, a total of four field trips were made to the
Salt Lakes of Akrotiri, Larnaka and the vernal ponds of Potamos tou Liopetriou
aiming to survey the emergence/hatching and abundance of Phallocryptus at
particular sites. Additionally, water samples for nutrient analysis and measurements
of several parameters were made as well as observations on the presence/absence
of the toothcarp Aphanius fasciatus in the Agios Georgios Pond and at the Salt Lake.
Results are shown in Chapter 4.
2.3.6
Flora Conditions
During November 2011 to May 2012, field surveys were made to the salt lakes area,
covering all possible areas for flora species expansions, studying also Acacia saligna,
Eucaliptus and Arundo donax intrusions. The entire study area is shown in figure,
Physical Parameters, of chapter 4. Reference conditions or high ecological status is
a state of a water body or other natural element where no or only minor changes can
be found due to anthropogenic disturbance. The determination of the reference
conditions of biological quality element, such as the vegetation, requires the
determination of certain biological values of the element in undisturbed status.
The determination of the reference conditions for the sclerophyllous shrub vegetation,
phrygana (habitat type 5420), juniper matorral (habitat type 5210), and maquis (9320)
as well as for the Mediterranean tall humid grasslands (habitat type 6420) was based
not only to the pre mentioned field surveys but also on the published literature and
expert knowledge of the attributes of these habitats in Cyprus.
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3
Legal requirements for monitoring
Below is a brief account of monitoring requirements as the arise form National and
EU legislation. These requirements we considered during the preparation of the
monitoring plan in combination with the monitoring requirements that arise from the
management objectives of the area.
Water Framework Directive 2000/60/EC:
European Water Framework Directive (WFD) 2000/60/EC establishes a common
strategy for Community action in the field of water policy. The purpose of this
Directive is to establish a framework for the protection of inland surface waters,
transitional waters, coastal waters and groundwater. All member states are obliged to
establish monitoring networks for all waterbodies in their vicinity and apply
appropriate management measures in order to achieve at least ‘’Good Ecological
Quality’’ by 2015. The most important innovation of WFD is the inclusion of Biological
Quality Elements (BQE’s) in the monitoring plans. The directive prescribes four
biological groups to be monitored im transitional waters: Aquatic Macrophytes,
Phytoplankton, Benthic macro-invertebrates and Fish; depending each time by the
communities flourishing. Monitoring of specific biological communities must be
supported
by
monitoring
of
relevant
hydromorphological,
chemical
and
physicochemical elements, all prescribed by the directive (Annex V).
Protection of groundwater against pollution and deterioration Directive
2006/118/EC
Water Framework Directive states that measures should be adopted to prevent and
control groundwater pollution. These measures are set out in this Directive, which is
why it is known as the "daughter Directive" to the Framework Directive. Furthermore,
in 2013 the Water Framework Directive will repeal Directive 80/68/EEC on the
protection of groundwater against pollution by certain dangerous substances.
Groundwater’s Directive is designed to protect groundwater and fill the legislative gap
following the repeal of Directive 80/68/EEC.
The provisions of Directive 2006/118/EC include: criteria for assessing the chemical
status of groundwater; criteria for identifying significant and sustained upward trends
in groundwater pollution levels and for defining starting points for reversing these
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trends; preventing and limiting indirect discharges (after percolation through soil or
subsoil) of pollutants into groundwater.
The direct relationship of the aquifer with surface waters by feeding Fasouri marsh,
intensifies the need for protection of groundwater quality. The construction of Kouris
Dam, in combination with reduced precipitation and the ongoing intensive abstraction
of water from Akrotiri aquifer have already resulted in significant degradation of the
ecosystem in the past decades. All of the above in combination with the proximity to
the sea have resulted in the sea intrusion and increase of salinity levels of
groundwater. In addition, various activities taking place in the Akrotiri peninsula such
as intense agriculture, various forms of development such as urbanisation, industry,
infrastructure, quarrying etc, as well as military activities and installations, oppose
additional threats for the underground waters and highlight the need for protection of
the aquifer.
Habitats Directive 92/43/EEC:
The European Community Habitats Directive (together with the Birds Directive) forms
the cornerstone of Europe's nature conservation policy. It is built around two pillars:
the Natura 2000 network of protected sites and the strict system of species protection.
The directive protects over 1.000 animals and plant species and over 200 so called
"habitat types" (e.g. special types of forests, meadows, wetlands, etc.), which are of
European importance. Among others, three habitat types associated with freshwater
or brackish aquatic communities are found in Akrotiri wetlands: Lagoons (1150*),
Mediterranean salt meadows (1410) and Hard oligo-mesotrophic waters with benthic
vegetation of Chara formations (3140). These types are included in Annex I of the
Habitats Directive (92/43/EC) and their conservation requires the designation of
special areas of conservation (SAC’s), which is still pending for the area. Especially
habitat type Lagoons-1150 which covers a major part of the study area is considered
as priority habitat of European interest requiring strict protection through SAC
designation. The characterisation of SAC’s and their restoration and protection
through management plans is considered a priority.
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Urban Waste Water Treatment Directive 91/271/EEC:
Directive 91/271/EEC concerns the collection, treatment and discharge of urban
waste water (including run-off rain water) and the treatment and discharge of waste
water from certain industrial sectors. Its aim is to protect the environment from any
adverse effects caused by the discharge of such waters. Industrial waste water
entering collecting systems and the disposal of waste water and sludge from urban
waste water treatment plants are subject to regulations and/or specific authorization
by the competent authorities. Sensitive areas, within the meaning of the directive,
include:
·
freshwater bodies, estuaries and coastal waters which are eutrophic or which
may become eutrophic if protective action is not taken
·
surface freshwaters intended for the abstraction of drinking water which
contain or are likely to contain more than 50 mg/l of nitrates
·
areas where further treatment is necessary to comply with other directives,
such as the directives on fish waters, on bathing waters, on shellfish waters,
on the conservation of wild birds and natural habitats.
The directive also provides derogations for areas designated as "less sensitive" and
such derogations were approved for several countries.
The unregulated inflow of untreated wastewaters in Zakaki marsh and concomitantly
to the salt lake, as well as in other areas of the wetland, can cause severe
degradation to the ecosystem, especially in cases were run-off becomes severely
polluted.
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4
Description of the project area
4.1
General Area Description
Akrotiri Peninsula is the southernmost part of Cyprus, located 5km south-west of the
city of Limassol (population 150,000). It also borders Akrotiri village to its southwest
west (population 800), RAF Station Akrotiri to the south, and Asomatos village
(population 350) to the north.
The Akrotiri Ramsar site is composed of two distinct areas that are hydrologically
connected. The first and largest area is the large salt lake and sand flats that are
situated in the centre of the Akrotiri peninsula. Over the last three centuries, this
former lagoon has been isolated from the sea and a number of saltmarsh vegetation
communities have developed and now surround the lake. The lake and surrounding
saltmarsh is important for a range of wetland birds, and in particular greater flamingo
Phoenicopterus ruber. A eucalyptus forest borders the northern side of the lake and
this is an important raptor roosting area. The second distinct area is the Fassouri
marsh that lies to the northeast of the salt lake. This area is made up of a matrix of
freshwater habitat types including grazing marsh and reed beds. Rain water is the
key hydrological input for both areas, although the lake receives occasional input
from the sea during storms. The two areas are hydraulically connected and the
Fassouri marsh provides important water inputs to the seasonal salt lake. A small
permanent lake is found to the west of the Akrotiri salt lake, which is hydraulically
connected to the sea.
4.2
Hydrology / Geology
4.2.1
Hydrology
Hydrologically the Akrotiri wetlands area can be distinguished into three main water
bodies.
·
The Zakaki Marsh to the north east
The Zakaki marsh is a freshwater marsh located to the east of the Akrotiri salt lake. It
receives storm water from the western urban areas of Limassol via two canals
(Figure 1). The main canal flows from the Zakaki area and collects water from the
western urban areas of Limassol. The second canal flows from the Limassol port. A
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new canal is under construction which will collect water from the areas north of the
Zakaki Marsh.
Figure 1 – Water from Zakaki area and the port flowing towards Zakaki marsh
·
The Fasouri Marsh.
The marsh (Figure 2) is located to the northwest of the Akrotiri salt lake (See Fig.
7). The overall area of the Marsh is about 60 hectares. The core section of the
Marsh spreads over an area of 20 hectares and hosts reeds and marshy
vegetation. The remaining area is covered by grassland.
The Marsh is fed by rain water from a limited catchment of agricultural land to its
north and west. It is also considered to be hydraulically connected to the Akritiri
aquifer and can therefore receive water in periods when the aquifer water level is
sufficiently high. In periods of high flooding, the Marsh drains southward towards
the Akrotiri salt lake. After the Pluto project has been constructed, drainage has
been preserved via a dirt road that channels the water along the western boarder
of the Pluto project.
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Figure 2- Fasouri Marsh
·
The Akrotiri Salt lake
o The salt lake is fed mainly by storm water collected by a) the surface area of
the salt lake itself, inflows from the Zakaki Marsh via a connecting canal
(Figure 3), from Akrotiri village via storm pipes, from the Phasouri Marsh
and from the Eucalyptus forest located north of the salt lake.
Figure 3 – Zakaki drainage canal
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o Water flows from the Fasouri Marsh. During rainy days the water coming from
Fasouri Marsh flows through a canal with 4 meters width. The canal passes
under the road (Figure 4) and flows directly onto Pluto project. Around the
Pluto project, there is a dirt road with lower elevation thus serving as a
drainage canal. The water firstly creates a small pond/marsh near the Pluto
project and then slowly travels towards the salt lake.
Figure 4 – Bridge near Pluto project
o Water flows from the Eucalyptus forest area: Based on site visits undertaken
in January it is considered that considerable amounts of water flows into the
salt lake from the north. The Eucalytus forest area is at a slightly higher
elevation than the salt lake and has a steady small downward gradient
towards the lake. Although there is no obvious hydrological network from
the northern area, during rainy days water flows from the citrus plantations
through the eucalyptus forest into the lake via a series of dispersed
drainage routes including dirt roads (Figure 5).
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Figure 5 – Eucalyptus forest
o Another important source of water is the Akrotiri village stormwater. There are
18 drain pipes connecting the areas on both sides of the road leading the
water towards the salt lake. (figure 6)
Figure 6 – Stormwater drain pipes
o Sea overflows: Occasionally flows from the sea have been witnessed. This is
only observed high storm winds, when surge in combination with high waves
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overtake the sand dunes. Overflowing seawater then drains towards the salt
lake.
Figure 7, shows the three water bodies of the area. The three areas can be
distinguished as the Akrotiri salt lake, the Zakaki and the Fasouri marshes. The
maximum extent of each of the marshes is indicated by grey shading. Light blue
shading indicates the area that is frequently flooded. Eighteen storm water drains
have been located across the Akrotiri road.
The blue-coloured lines represent the routes connecting the marshes with the salt
lake, whereas to the northwest the orange line represents the occasional flow
towards the salt lake.
In addition, a small lake that is permanently flooded is found west of the Akrotiri salt
lake (indicated by yellow arrow on Fig. 7). Given the fact that it is permanently
flooded despite having a minimal catchment area and that its salinity is slightly higher
than that of seawater, it is concluded that this lake is hydraulically connected with the
sea and is directly fed by seawater.
Figure 7 – Main hydrological features of the Akrotiri Penynsula
4.2.2
Physical parameters
Three field visits for the monitoring of hydrological and water quality parameters took
place during the first four months of the project. Below is a brief description of
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observations made during the visits. The locations of various observations and of
monitoting sites are shown on Fig. 8.
Figure 8: Locations of observations and monitoring stations
INDEX
Point 33
Point 34
Point 35
Point 36
Point 37
Point 38
Point 39
Point 40
Point 41
Point 42
Point 43
Point 44
Point 45
Point 46
Point 47
Upper limits of acacia, reeds, crops (vines, cereals, olives) and Cypress
Western limits of acacia, reeds, Crops and Cypress
Acacia, reeds and shrubs
Fasouri marsh - sample 06
Acacias on the left of the road and eucalyptus on the right
Flooded on the right and left of the road and all over the region are installed
antennas
Marsh Lakes – No water drainage (Fig. 9)
Area enclosed between points 37 – 39 – 40 – 41 – 42 – 45 and 38 was
flooded (Fig. 9)
Fenced area - Acacias
Pond – Akrotiri Merra – Sample 05
Small salt lake – sample 04
Acacias, eucalyptus and crops
Acacia expansion inside salt lake area, in aproximately 5 meters.
Extensive expansions from Acacias
Salt lake sample 01
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Point 39
Point 40
Marsh Lakes – No water drainage
Area enclosed between points 37 – 39 –
40 – 41 – 42 – 45 and 38 was flooded
Figure 9: Points 39 and 40 showing flooded areas of the Fasouri Marsh
Key results of the monitoring are described below.
4.2.3
Land use, water users and pollutant sources
The surroundings of the project area are mainly used for agricultural purposes as
also support a small number of farming units. It also has military uses and several
military installations are preset with various projects (e.g. Pluto) being built inside the
study area. During the third visit samples were collected and analysed. Sampling
locations are shown on Figure 10. Results are shown on Figure 11.
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Figure 10: Sample locations
·
Sampling code on GPS and Figure 10: 01
Location: Akrotiri salt lake
Comments: The water collected was from inside the lake. Two samples were
collected, one to analyze E-coli and one to analyze pH, conductivity, Chloride,
Nitrates, Nitrite, Ammonium, Phosphates, Total P, Total N, BOD5, TOC, Cd, Ni,
Pb and Hg. The water collected was analyzed for salinity also.
·
Location: Zakaki Marsh (Bridge).
Comments: Flow measurements conducted. The water collected was from inside
the salt. Two samples were collected for each point, one to analyze E-coli and
one to analyze pH, conductivity, Chloride, Nitrates, Nitrite, Ammonium,
Phosphates, Total P, Total N, BOD5, TOC, Cd, Ni, Pb and Hg. The water
collected was analyzed for salinity also.
·
Location: Zakaki Marsh (Bridge).
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Comments: The water collected was from the urban inflows outlet. Two samples
were collected for each point, one to analyze E-coli and one to analyze pH,
conductivity, Chloride, Nitrates, Nitrite, Ammonium, Phosphates, Total P, Total N,
BOD5, TOC, Cd, Ni, Pb and Hg. The water collected was analyzed for salinity
also.
·
Location: Small salt lake.
Comments: The water collected was from inside the salt lake. Two samples were
collected for each point, one to analyze E-coli and one to analyze pH,
conductivity, Chloride, Nitrates, Nitrite, Ammonium, Phosphates, Total P, Total N,
BOD5, TOC, Cd, Ni, Pb and Hg. The water collected was analyzed for salinity
also.
·
Location: Pond (Akrotiri Merra)
Comments: The water collected was from inside the salt lake. The water
collected was analyzed for salinity. Two samples were collected for each point,
one to analyze E-coli and one to analyze pH, conductivity, Chloride, Nitrates,
Nitrite, Ammonium, Phosphates, Total P, Total N, BOD5, TOC, Cd, Ni, Pb and
Hg.
·
Location: Fasouri Marsh
Comments: The water collected was from inside the salt lake. The water
collected was analyzed for salinity. Two samples were collected for each point,
one to analyze E-coli and one to analyze pH, conductivity, Chloride, Nitrates,
Nitrite, Ammonium, Phosphates, Total P, Total N, BOD5, TOC, Cd, Ni, Pb and
Hg.
The results of the water analysis are shown below. It is noted that laboratory testing
of the samples collected on the 19th of January had not been made available in time
to be considered in this report.
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Parameter
Unit
pH
Conduct.
Nitrates NO3
10/4/2012
10/4/2012
Port - Urban
Pond
10/4/2012
10/4/2012
10/4/2012
10/4/2012
Fasouri Marsh Salt Lake - south Salt Lake - North Zakaki Bidge
pH
7.90
8.11
7.36
8.17
8.20
7.99
mS/cm @ 20 oC
4.77
46.2
6.77
19.22
8.64
1.37
mg/L
189.00
13.00
3.08
20.00
5.70
155.00
Nitrite NO2
mg/L
0.11
12
0.04
9.50
0.19
0.54
Ammonium NH4+
mg/L
0.57
14
1.19
59
0.94
0.400
Phosphates PO4^3-
mg/L
<.015
26.3
1.14
15.4
<0.06
<0.1
Total P
mg/L
<0.044
24
<0.08
28
<0.08
<0.02
Total N
mg/L
40.15
58
2.70
912
<2.5
39.55
BOD5
mg/L
5.00
11.00
<5
17.00
18.00
44.00
TOC
mg/L
2.10
9.90
15.40
20.00
10.90
2.03
Cd
μg/L
<0.004
<0.04
<0.008
<0.02
<0.01
<0.002
Ni
μg/L
<0.004
<0.04
<0.008
<0.02
<0.01
<0.002
μg/L
<0.010
<0.10
<0.020
<0.05
<0.025
<0.005
μg/L
<5
<10
<5
<5
<5
<5
/100 mL
38
980
71
71
ND
91
Pb
Hg
E.Coli
Figure 11: Water Quality
Flow Measurements
Fasouri
Figure 12: Flow measurement on point 46 (measurements in metters - m)
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Figure 13: Flow measurement at point 46.
Zakaki Marsh (Bridge)
Figure 14: Flow measurement at Zakaki Marsh (Bridge) .
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No Flow
No Flow
Figure 15: Flow measurement on Zakaki Marsh (bridge).
Figure 16: Flow measurement on Zakaki Marsh (bridge).
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Port flows
Port Water level (h) = 0.15m
Port Flow = 0.8m/sec
Urban (Zakaki) flows
Urban Water level (h) = 0.25m
Left flow = 0.0 m/sec
Center flow = 0.1m/sec
Right flow = 0.1m/sec
Average Urban flows = 0.067m/sec
Port and Urban (Zakaki) outflows
Outflow water level (h) = 0.28m
Maximum flow = 0.8m/sec
Average flow = 0.7m/sec
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Port flows
Urban (Zakaki) flows
Figure 17: Flow measurements on Urban and Port flows. Combined outflow through Zakaki
trench to Akrotiri Salt Lake.
The values of water temperature, salinity, oxygen and pH during the visits in January
2012 are presented on Table 2. The majority of the salinity measurements were
made using an optical refractometer, and only during the last field trip, we were able
to use a digital conductometer.
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Table 2: Values of water salinity, conductivity, oxygen, pH at the sites visited during the
fieldtrips of December 2011 and January 2012 in relation to the Phallocryptus (Branchinella)
spinosa component of the study. Numbers represent sampling locations as per Table 2
Optical Refractometer
Chemical
Conductometer WTW
Lovibond
analysis
Cond 3110
Oxi200
pH
330i
Salinity
Salinity
Salinity
[%]
[%]
Surface
Depth
5
2.7
2.7
10
6
1.3
1.3
2
7
3
3
10
8
3
3.2
10
1-L
9
1.2
1.6
10
2-P
10
0.8
0.8
3
11
0.5
0.8
20
12
3
3
10
13
2.4
2.4
3
14
0
0
10
15
0
0
10
16
6.4
7
15
17
1
1
10
18
1.2
1.3
19
3
20
2.7
No.
WTW
Depth
Water
[%]
Conductivity
O2
[cm]
sample
10cm
[mS/cm]
[mg/l]
0.79
13.99
10
1.192
3.3
10
2.7
10
O2 [%]
pH
9.01
92
7.86
19.89
11.92
121
8.06
2.74
43.2
11.39
116.7
7.82
2.37
38.1
12.16
123.9
7.92
depth
1-P
2-L
1-P
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Table 3: Information of the sites visited during the fieldtrips of December 2011 and January
2012 in relation to the Phallocryptus (Branchinella) spinosa component of the study.
Number
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
Date
18-Dec2011
18-Dec2011
27-Dec2011
27-Dec2011
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
4-Jan2012
5-Jan2012
5-Jan2012
5-Jan2012
8-Jan2012
8-Jan2012
8-Jan2012
8-Jan2012
Time
(hr)
Coordinates
E
Coordinates
N
11:36
32° 57' 52.00"
34° 36' 12.08"
In the small pond near the
road/airstrip
16:27
32°56'12.46"
34°36'23.67"
Pond near Agios Georgios Church
10:45
32° 57' 52.00"
34° 36' 12.08"
15:19
32° 59' 9.62"
34° 40' 30.19"
9:10
32°56'12.46"
34°36'23.67"
9:53
32° 57'
40.9716"
34° 36'
10.7526"
After small pond, on the way to lake
10:36
32° 57' 42.64"
34° 36' 34.48"
Lake, across Environmental Centre
10:47
32° 57'
42.7644"
34° 36'
38.3184"
12:27
32° 57' 52.00"
34° 36' 12.08"
12:55
32° 57' 51.92"
34° 36' 6.11"
Lake, area where the flamingos
were feeding
road/airstrip
Flooded plain between small pond
and road
13:30
32° 57' 48.75"
34° 36' 0.52"
Pond near airstrip
14:51
32° 59' 9.62"
34° 40' 30.19"
Lake, near Zakaki Marsh, where the
flamingos were feeding
34° 37' 47.03"
Flooded plain with tracks
15:22
9:00
9:47
11:12
32° 59'
31.6026"
33° 53'
53.8074"
33° 53'
51.7992"
33° 37'
36.8934"
34° 58'
11.406"
34° 58'
12.0072"
33° 37'
36.8934"
10:28
32° 57' 48.75"
34° 36' 0.52"
12:13
32° 57' 52.00"
34° 36' 12.08"
13:49
32° 58' 76.00"
34° 36' 40"
14:27
32°56'12.46"
34°36'23.67"
Location
road/airstrip
Lake near Zakaki Marsh, where the
flamingos were feeding
Vernal pond Phallocryptus
Vernal pond
Near Water Tank (Artemidos Ave.)
Pond near airstrip
road/airstrip
Lake, near Fisheries Department
monitoring station
A regression between values from the two instruments was high but not significant
(Fig. 17), advising for caution when using only the optical refractometer.
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Figure 18: Regression between the salinity values measured with the optical refractometer and the digital
conductometer. Even though there is an apparent strong correlation, it is not significant.
The transparency or turbidity of the water at the ponds and Lake varied considerably
between the dates of visit, the flamingos’ activities, the water reservoirs, and the
predominant substrate. For example, the water was almost transparent at the small
ponds between the road and the main body of the Lake (Fig. 18A), reddish or darkbrown at the pond between the road and the airstrip (Fig. 18B), murky or milky where
the flamingos were actively feeding (Fig. 18C). While the reddish colour probably is
the result of tannins in the water, the brownish to yellowish colour was only observed
where extensive mats or crusts of biofilms were in contact with the water (Fig. 18D).
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Figure 19: Conditions of the water at the Salt Lake during the sampling: almost transparent, small pond,
site #6 (A), stained red probably by tannins, small pond near the airstrip, site #9 (B), milky or cloudy due to
resuspended sediments and disturbance of the bottom by feeding flamingos, site #19 (C). Extensive areas
around the lake with thick biofilm layers, site #18 (D). Number of the sites according to Table 2.
In addition to the site observations, ground level depth data were collected from the
Water development department. In particular a series of measurements in the Akrotiri
and Asomatos area have been collected covering the period btween 1961 and 2011.
The collected timeseries (Appendix IV) include four to six depth measurements per
year for each monitoring site.
Initial analysis of the timeseries shows an increasing trend in depth with time which
indicates a gradual lowering of the groundwater levels at all monitoring sites with the
exception of the Asomtos 1935/006 location. Though the gradual decline can be
attributed to a combination of climatic changes, increased water abstraction and the
construction of the Kourris dam, no analysis can be made as to the relative
contributions of these factors.
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4.2.4
Geology
Geologic reports held by the Cyprus American Archaeological Research Institute
(CAARI) in Nicosia describe the evolution of the Akrotiri Peninsula as consisting of
three components: a former island of Late Miocene sandstone and marl cliffs, PlioPleistocene marine beach sediments, and Holocene lacustrine sediments (Wessel
archaeology, 2002). The sequence of geological events can be summarised as
follows (Table 4):
·
Sediments and the former island of Akrotiri were brought closer to their current
position during severe tectonic uplift during the Pleistocene (Chapman 1989, 59).
·
Input from the Kouris River and long-shore transport of beach material caused
spit development initially on the west side of the peninsula, southward to Akrotiri
island (Stanley Price 1979, 8). This formed an embayment open to the east.
·
A physical link existed to Akrotiri island existed by at least 10,000 BC. as
evidenced by pygmy hippo bones in the Aetokremnos rock-shelter at the
southern cliffs of the peninsula (Simmons 1991).
·
Sand spit development on the east side of Akrotiri gradually closed off the
opening to the sea, thereby forming the present Salt Lake. A visitor to the area in
1589 (Villamont, in Heywood 1982) noted that, “fish entered the lake from the sea
‘through one little entrance” implying that spit development was nearly complete
by the end of the sixteenth century.
·
Lake processes contributed to sediment infilling and an increasingly paludal
environment.
The Akrotiri Peninsula forms a shallow north-south synclinal basin underlain by
sedimentary Pliocene rocks of the Nicosia-Athalassa formation and Miocene rocks of
the Pakhna
formation. The respective formations consist of; i) calcareous
sandstones, grits and conglomerates; and, ii) gypsum beds, chalk and chalk marls.
On parts of the southern sea shore of Akrotiri the sedimentary sequence is broken by
a volcanic intrusion which in places sub-crops at the foot of the sea cliffs.
The Pliocene rocks are discontinuously overlain by Pleistocene deposits consisting of
pebble beds, sandstone and marl and this deposit extends just north of Limassol.
Much of the synclinal basin is covered by recent alluvium. This generally consists of
fine grained sands, silts and clays in the main basin but flanking this, seawards on
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both sides, located within the relict spits the deposits comprise much coarser grained
material, typically consisting of sands and gravels.
During the field visit on 11 November 2011, soil samples were collected from the Salt
Lake. At that time, due to the fact that a car got stuck in the lake, a bulldozer
excavated an access road, giving us the opportunity to have a clear cross section of
the salt lake (Figure 19 - 23).
Table 4: Description of the composition of the sediments in the three visible layers.
Depth below
Description
surface (cm)
0 – 7cm
Silty fine grained sands
Interpretation
Lacustrine deposit
Figure 11
7 – 20cm
20 - 150cm
Brown-grey Silty sands with shells Lacustrine deposit
and some clay
Figures11 and 12
Light fey clays and dark grey silts
Lacustrine deposit
Figures 12 and 13
These three layers are considered as recent alluvium. The top layer was obviously
grey fine grained sands with the presence of a small percentage of silt. The middle
layer can be described as brown-grey silty sands with the presence of shells and clay.
This layer macroscopically is obvious due to its brown colour. The lower layer is
characterized by layers of light grey clays and dark grey silts.
From the boundary between these brown-grey sands and the lower layer which is
consisted of silts and clays the team collected a water sample which was analyzed.
This is due to the fact that water moves easily in the sand particles and flow above
the clay-silt layer surface.
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Figure 20: View of the cross section
Figure 21: Cross section
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Figure 22: Top and middle soil layer
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Figure 23: Middle and lower soil layer
Figure 24: Lower Soil layer
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4.3
Birds
More than 370 bird species have been recorded in Cyprus (Flint and Stewart 1992).
At least 308 of these have been observed at Akrotiri Peninsula (Table 3, pages 10-15
of Nature Conservation Component Plan). Akrotiri Salt Lake and the surrounding
wetlands constitute the largest wetland complex in Cyprus (Iezekiel et al. 2004) and
are of major importance as a staging area during spring and autumn passage for
hundreds to thousands of waterbirds. Flocks numbering internationally important
numbers of the Demoiselle Crane (Grus virgo) roost at the lake from mid-August to
early September (Charalambidou et al. 2008, Kassinis et al. 2010, SBAA
Environment Department), while hundreds to thousands of Red-footed Falcon (Falco
vespertinus), European Honey Buzzard (Pernis apivorus), and Harriers (Circus spp.)
stop over during migration (Iezekiel et al. 2004). In winter, many duck (Anas) and
wader species use the area as feeding and roosting grounds, including internationally
important numbers of Greater Flamingo (Phoenicopterus ruber roseus) and
endangered species such as the Greater Sandplover (Charadrius leschenaultii)
(Charalambidou et al. 2008, Kassinis et al. 2010) (Appendix I – Map 02).
During spring and summer, the Peninsula supports important breeding populations
(Appendix - Map 01) of Black-winged Stilt (Himantopus himantopus), Kentish Plover
(Charadrius alexandrinus) and Ferruginous Duck (Aythya nyroca) (Kassinis 2007,
2008). Moreover, Akrotiri and Episkopi sea cliffs are important breeding sites for the
Eleonora’s Falcon (Falco eleonorae), Peregrine falcon (Falco peregrinus), and
Mediterranean Shag (Phalacrocorax aristotelis desmarestii) while Episkopi cliffs is
the most important breeding site for the Griffon Vulture (Gyps fulvus) in Cyprus
(Iezekiel et al. 2004). Designations at Akrotiri Peninsula relating to the ornithological
importance of the area include:
4.3.1
Ramsar designation
Large parts of the wetlands at Akrotiri were designated in 2003 as the Akrotiri
Ramsar Site, for which they qualified due to the wintering populations of the Greater
Flamingo. These birds arrive in autumn as the Salt Lake fills with water to feed upon
the abundant invertebrate biomass that rapidly colonises the water, in particular the
brine shrimps. These crustaceans are able to tolerate the high salinity encountered in
the lake during the summer as it dries and hatch from cyst-like eggs lying dormant in
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the lake bed as the water returns. It is noted that data collected since 2003 may
support a revision of the Ramsar site boundaries.
4.3.2
Important Bird Area designation
The Akrotiri Peninsula has been identified as one of the Important Bird Areas (IBA) of
Cyprus, according to the qualifying species listed in Table 4. It is noted that the
Akrotiri IBA includes areas not included in the SPA designation and vice versa.
Table 5: Qualifying species for the identification of Akrotiri Peninsula – Episkopi Cliffs as an
Important Bird Area (taken from Iezekiel et al. 2004).
Common name
Scientific name
Squacco heron
Glossy ibis
Greater flamingo
Ardeola ralloides
Plegadis falcinellus
Phoenicopterus ruber
Estimated
Population
100-250
250-500
4000-10000
Eleonora’s falcon
Red-footed falcon
Common crane
Black-winged stilt
Falco eleonorae
Falco vespertinus
Grus grus
Himantopus
himantopus
Glareola pratincola
Charadrius
alexandrinus
50-65p
1100-1500
3000-5000
300-350ind
5-10p
100-200
300-500ind
20-40p
Slender-billed gull
Larus genei
1200-1500
Gull-billed tern
Demoiselle crane
Shelduck
Gelochelidon nilotica
Grus virgo
Tadorna tadorna
80-100
400-560
800-2000
Greater Sandplover
Charadrius
leschenaultii
Merops apiaster
Falco peregrinus
Larus ridibundus
5-10
Phalacrocorax
aristotelis desmarestii
Gyps fulvus
Burhinus oedicnemus
35-40p
Vanellus spinosus
5-10p
30,000-70,000
Resident breeder
Passage breeder
Passage migrant
Migrant breeder
Passage migrant
3900-7300
Passage migrant
Collared pratincole
Kentish plover
Bee-eater
Peregrine Falcon
Black-headed gull
European Shag
Griffon vulture
Eurasian thick-knee
Spur-winged Lapwing
86 species of
waterbirds
13 species of raptors
20,000-30,000
4-6p
5000-6000
5-8p
5-10p
Status
Passage migrant
Passage migrant
Winter visitor
Passage migrant
Migrant breeder
Passage migrant
Passage migrant
Passage migrant
Occasional breeder
Passage migrant
Migrant
(resident?)
breeder
Passage migrant
Winter visitor
Passage migrant
Winter visitor
Passage migrant
Passage migrant
Passage migrant
Winter visitor
Passage migrant
Winter visitor
Passage migrant
Resident breeder
Passage Migrant
Winter visitor
Resident breeder
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4.3.3
Special Protection Areas (SPA) designation.
Akrotiri Wetlands and Akrotiri Cliffs were designated as SPAs in 2011. Out of the 308
bird species recorded at Akrotiri Peninsula (Table 3, pages 10-15 of Nature
Conservation Component Plan), 100 species are listed in Schedule 1 to the Game
and Wild Birds Ordinance, requiring protection through the designation of SPAs.
From the Schedule 1 species, 28 have been identified as qualifying species for the
SPA designation of Akrotiri Wetlands and Akrotiri Cliffs (Table 5). It is noted that
further survey work is necessary to establish whether the SPA designation should
cover two more Schedule 1 species, namely Cyprus Warbler (Sylvia melanothorax)
and Eurasian Thick-knee (Burhinus oedicnemus). Besides individual species, the
Akrotiri SPA designation includes the groups of raptors, cranes and waterbirds as
qualifying features.
Table 6: Qualifying species, listed in Schedule 1 of the Game and Wild Birds Ordinance, for the
SPA designation of Akrotiri Wetlands and Akrotiri Cliffs.
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
Common name
Demoiselle Crane
Purple Heron
Squacco Heron
Ferruginous Duck *
Little Stint
Kentish Plover *
Greater Sandplover
White-winged (Black) Tern
Western Marsh-harrier
Pallid Harrier
Saker Falcon
Eleonora’s Falcon *
Peregrine Falcon *
Red-footed Falcon
Collared Pratincole
Common Crane
Black-winged Stilt *
Slender-billed Gull
European Bee-eater
Great White Pelican
European Honey Buzzard
European Shag *
Ruff
Greater Flamingo
Glossy Ibis
Gull-billed Tern
Shelduck
Spur-winged Lapwing *
Scientific name
Grus virgo
Ardea purpurea
Ardeola ralloides
Aythya nyroca
Calidris minuta
Charadrius alexandrinus
Charadrius leschenaultii
Chlidonias leucopterus
Circus aeruginosus
Circus macrourus
Falco cherrug
Falco eleonorae
Falco peregrinus
Falco vespertinus
Glareola pratincola
Grus grus
Himantopus himantopus
Larus genei
Merops apiaster
Pelecanus onocrotalus
Pernis apivorus
Phalacrocorax aristotelis desmarestii
Philomachus pugnax
Phoenicopterus ruber roseus
Plegadis falcinellus
Sterna nilotica
Tadorna tadorna
Vanellus spinosus
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The species marked with an asterisk (*) are important breeding species in the SPAs,
some also in the general area of the Peninsula. The species not marked with an
asterisk, are important non-breeding species in the SPAs and the general area of the
Peninsula. These use Akrotiri Peninsula for wintering and migration, including
roosting, resting, staging and thermalling to gain lift before flying offshore.
Data on birds that frequent the terrestrial part of Akrotiri Peninsula and its wetlands is
abundant. Detailed data is also available on bird species found in the coastal part of
the site (see Table 1). For seabird species which are mostly pelagic and which have
been recorded offshore in Cyprus, such as Cory’s Shearwater (Calonectris
diomedea), Yelkouan Shearwater (Puffinus yelkouan), European Storm Petrel
(Hydrobates pelagicus), and Northern Gannet (Morus bassanus) (Flint and Stewart
1992), there are no data from this area.
As a result of the above, the distribution ranges of most species, excluding the
pelagic ones, are known. Additionally, the population status of many, but not all,
species is also known. Waterbirds are fairly well monitored due to systematic,
monthly, waterbird counts being carried out since 2003 by the Research Unit of the
Cyprus Game Fund, Ministry of Interior of the Republic of Cyprus, in cooperation with
the
wardens
at
Akrotiri Environmental Education
and
Information
Centre
(Charalambidou et al. 2008, Kassinis et al. 2010). Further data is collected as part of
species specific monitoring, which includes annual surveys of the breeding colonies
of the Eleonora’s Falcon since 2002 (Wilson 2005), of migrating birds of prey, with
detailed annual monitoring of migrating Red-footed Falcons, since 2006 (BirdLife
Cyprus 2006-2009), of breeding Black-winged Stilt and Kentish Plover, with detailed
annual surveys conducted by the Game Fund Service since 2003 (Kassinis et al.
2010). Further data is available in publications by birdwatchers and the nongovernmental organisation BirdLife Cyprus (Flint and Stewart 1992, BirdLife Cyprus
2003-2009, Gordon 2004, Iezekiel et al. 2004, Richardson 2005-2009).
Special attention afforded to species that use Akroriti Peninsula in internationally
important numbers, such as migrating Demoiselle Cranes and Red-footed Falcons,
wintering Greater Flamingo, and breeding Ferruginous Duck and Kentish Plover,
make it possible to estimate population sizes. For other species using the site in
numbers that are important at a European level, such as migrating and wintering
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Greater Sandplover, and breeding Black-winged Stilt, Eleonora’s and Peregrine
Falcons and Griffon Vulture, it is also possible to estimate population sizes.
On the other hand, data on population sizes of other important species, such as
breeding, wintering and migrating populations of Mediterranean Shag, Cyprus
Warbler and Eurasian Thick-knee are not sufficient.
Overall, the majority of data from the area has focused on the presence / absence of
bird species in the area, and on calculating population sizes. Information on bird use
around the antennas has also been studied. However, ecological studies of the
requirements of particular species, e.g. of their breeding and feeding biology, or of
food-web structures in the area, are lacking, apart from one study investigating the
bird-habitat relationship of the bird species occurring at Akrotiri Peninsula. In this
study, thirteen habitat types representing all habitat types found in the area, were
identified and mapped, and monitored regularly for one year. One hundred and
fifteen bird species were recorded throughout the duration of the study (Hadjikyriakou
2011).
4.4
Phallocryptus (Branchinella) spinosa
4.4.1
Status of the taxonomy of Phallocryptus (Branchinella) spinosa
The anostracan family of crustaceans known as Thamnocephalidae, particularly the
genus Branchinella, has long been a convenient drawer to keep fairy shrimps with
dubious affinities. It is only recently that Rogers (2003, 2006) made a major revision
of the Branchinella genus and changed to Phallocryptus. We collected live
specimens and shipped them to C. Rogers (world specialist in anostracan taxonomy)
for positive ID.
4.4.2
Status of Phallocryptus (Branchinella) spinosa in the IUCN Red List
P. spinosa appear to be broadly distributed and without immediate threats to their
continued existence, and it is categorized under the IUCN criteria as “Species of
Least Concern” (Rogers 2006, and http://www.iucnredlist.org/apps/redlist/search).
4.4.3
Status of Phallocryptus (Branchinella) spinosa in Cyprus and elsewhere
The general distribution of Phallocryptus spinosa is a disjunct mosaic of populations:
west to the Iberian Peninsula, through the Mediterranean Basin, Ukraine,
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Afghanistan, Kazakhstan, Uzbekistan, Iran, south to Oman, north Africa, south to
Botswana (Rogers 2003 and references therein).
In Cyprus, P. Spinosa has been reported only for the Salt Lakes of Larnaka and
Akrotiri (Mura & Hadjistephanou 1987), in the former coexisting with another
anostracan species, Artemia salina. However, Phallocryptus can also be found
coexisting with other species at smaller water bodies such as the vernal ponds at the
Potamos tou Liopetri and Cape Greco areas (Jimenez and Sour, unpublished).
4.4.4
Salt Lake
During December 2011 and January 2012, a total of four field trips were made to the
Salt Lakes of Akrotiri, Larnaka and the vernal ponds of Potamos tou Liopetriou (Table
1), aiming to survey the emergence/hatching and abundance of Phallocryptus at
particular sites (Table 2). Additionally, observations on the presence/absence of the
toothcarp Aphanius fasciatus in the Agios Georgios Pond and at the Salt Lake.
All the available information and our own field observations regarding Phallocryptus
(Branchinella) spinosa in Akrotiri points out to its important role in the ecosystem,
starting from the nutrient cycle (e.g. carcasses and faecal material) sustaining the
primary production, and its contribution in the food chain by grazing phytoplankton
and prey for waterfowl, aquatic insects and possibly fish.
Such an important species is poorly adapted to fend off predation from fish or aquatic
insect larvae, particularly during the filling and freshening of the Lake when the
salinity is not extremely high. The toothcarp Aphanius fasciatus is already present in
the aquatic environments around the Salt Lake and occasionally can be observed in
the main body of the lake (see Other Observations). A. fasciatus is an active predator
of aquatic invertebrates, has a high tolerance to salinity variations from fresh to hyper
saline water and is suspected to be resistant to drought. Predatory insect larvae,
such as dragonflies, are also present in the ponds around the Lake, together with
voracious diving beetles (see Other Observations).
The presence of several larval stages (e.g. metanauplii, post-metanauplii) and adult
individuals of P. Spinosa during our first visit (Table 2), is indicative of an early
hatching time. It also suggests that there is an asynchronous hatching of the cysts
bank in Akrotiri. The erratic hatching pattern in most anostracan is thought to be an
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adaptation to the variable temporary habitat (Brendonck 1996). Hatching is generally
spread over several days or even weeks even under favorable environmental
conditions and not all cysts will terminate the diapauses (Hulsmans et al. 2006).
Live specimens (sweep samples with a standard hand net, mesh 1mm) were
collected at all visited localities in the Lake, except where the flamingos were actively
feeding: the birds totally depleted the fairy shrimp populations at the feeding patches.
Only one single specimen of Phallocryptus was captured in dozens of sweeps at the
feeding patches.
Individuals are kept alive in aquaria (Nicosia) in order to produce a cyst bank for
future physiological and taxonomical studies and to record their longevity, at least in
vitro. Additionally, an underwater high definition camera (GoPro) was used to record
abundances and behaviour of P. spinosa at two ponds of the Lake (Fig. 25).
The advantage of such method is the non-destructive evaluation of the populations.
A limitation is the lack of a scale to measure the size of the individuals. However, the
proportion of sexes (Fig. 25B), aggregations (Fig. 25C) and behaviour (Fig. 25D) are
relatively easy to study. Densities can be determined if the observations are made at
a specific place (e.g. camera stationed in one point and records made by time) or
following a pre-determined distance and time.
At one site (#19, Table 2), bottom sediments were collected with a hand held grab
(15x20cm square frame) at the feeding patch of a large group of flamingos. The
sediments were sorted to determine the presence and abundance of P. spinosa cysts.
Only three cysts were found, indicating how efficient is the flamingos’ feeding
mechanisms in removing particles (e.g. cysts, seeds) together with organic matter as
biofilm and also mud.
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Figure 25: Underwater observations of the Phallocryptus (Branchinella) spinosa populations at
the Salt Lake: underwater high definition video camera, GoPro, site #18 (A), snapshot of a
female P. Spinosa with a full egg pouch visible in the upper part of the abdomen, site #17 (B),
snapshot of an aggregation of numerous individuals (male and female) of P. spinosa near the
submerged vegetation, site #18 (C), snapshot of a male P. spinosa feeding between the shoots of
Ruppia maritima, site #18 (D). Number of the sites according to Table 2.
4.4.5
Other observations (flamingos, Aphanius fasciatus, dragonflies and
diving beetles)
In relation to the P. Spinosa abundance and distribution in the Lake and ponds, we
made realized direct observations where the flamingos were actively feeding (Fig.
26A). It is notorious the impact of the feeding behaviour on the water transparency
(Fig. 26C) and bottom sediments (Fig. 26B). The flamingos leave traces of their
activities (trackways, crater-like depressions, foot-prints), which significantly modify
the bottom sediments, to a degree that can be found in the fossil record of lakes
(Melchor et al. 2012).
Additionally, at the feeding patches, the flamingos depleted the Phallocryptus
communities and the bank of cysts, as mentioned before.
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The bottom modification by flamingos (and perhaps other birds) at the feeding
patches is made primarily by the actual feeding (ingestion of mud) and the trampling,
as has been observed elsewhere (Johnson 1997, Rodríguez-Pérez et al. 2007). That
flamingos ingest significant quantities of mud rich in organic matter and that their
young can grow on this kind of diet, is well known since a long time (Allen 1956,
Jenkin 1957, MacDonald 1980), activity that affects also macrophytes (RodríguezPérez et al. 2007). In consequence, the impact on the cysts bank of Phallocryptus by
the feeding activities of the fowl birds in the Lake is far from negligible and it needs to
be considered in any attempt to study and to monitor this fairy shrimp populations at
Akrotiri (see Monitoring Program). It is important to remember that the notion that
flamingos are the only waterfowl preying on Phallocryptus at the Salt Lake is not
correct. Phallocryptus is preyed upon by several other bird species such as
shelducks, ibises and avocets (Akrotiri Peninsula Nature Conservation Component
Plan v.1.1 2011).
The influence of the waterfowl in the abundance and dispersal of Phallocryptus
between water bodies (e.g. Larnaka, Akrotiri, Oroklini) is crucial to understand the
population dynamics of this brine shrimp in an open system where assisted-dispersal
contributes to the gene flow. Migrating birds such as flamingos, have the potential to
transport viable eggs and cysts in their digestive track and feathers (Charalambidou
& Santamaria 2002, Figuerola et al. 2005, McCullogh et al. 2008), a significant
proportion of which might contribute to the colonization or repopulation of water
bodies visited by the waterfowl during the annual migrations. These migrations might
be the link between extremely disjunct distribution patterns of P. spinosa, such as the
populations in Cyprus (Ketmeier et al. 2008) and South to Africa, in Botswana
(Hulsmans et al. 2006).
To conclude reviewing some of the most prominent interactions between
Phallocryptus and the waterfowl, flamingos in this case, the transmission of parasites
must be considered. Cestodes (parasitic worms) of at least 15 species are known to
utilize anostracans as intermediate hosts in their life cycle (Georgiev et al. 2005,
Sánchez et al. 2006), they all use flamingos and other waterfowl as final host.
Cestoda in Phallocryptus spinosa was first reported by Bondarenko & Kontrimavicus
(1976, cited in Mura 1995). Bacteria also attack brine and fairy shrimps producing the
notorious “black disease” in commercially cultured specimens (Saejung et al. 2011).
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However, parasitic cestodes have attracted more research attention due to the effect
on the behaviour and reproduction of the intermediate host. Parasitized individuals
tend to be of larger size, live longer, have a higher lipid and carotenoid level
(Amarouayache et al. 2009). The parasites also make the brine and fairy shrimps
more buoyant making them more prone to predation by birds and reduce the fertility
or castrate (Mura 1995, Georgiev et al. 2005, Sánchez et al. 2006).
Given the important effect of cestodes on the anostracans, the dispersion of the
parasites by the flamingos visiting different water bodies with brine and fairy shrimps,
needs to be considered in any attempt to study Phallocryptus in the Salt Lake.
Of particular interest is the nutrient influx to the Lake from the birds (Fig. 26C). For
any study aiming to determine the flow of energy in the food web of the Lake, the
contribution of the birds must be considered. Same care must be exercised with the
terrestrial and atmospheric inputs such as litter, insects with aquatic larvae, African
dust deposition, just to mention a few examples.
At this same study site, during the second fieldtrip (Tables 1, 2), two juveniles of the
toothcarp or killifish Aphanius fasciatus were observed inside small ponds of wheeltracks (Fig. 24D). A. fasciatus is of particular interest since it is an endemic species
of the Mediterranean (Leonardos 2008) and it is listed in Annex II (Strictly protected
fauna species) of the Convention on the Conservation of European Wildlife and
Natural Habitats (Bern Convention).
Fish in what is now the Salt Lake is not an uncommon sight. The water body of the
Lake had a substantial population of fish in late medieval times, during the Ottoman
domination of the Island. Accounts published in the 16th century by travellers visiting
the area, indicate that there was no salt production from the lake. But it was used as
a huge fishery for “dorade” (tsipoura) and water was brought into it from the sea by a
channel.
In relation to P. spinosa, it is traditionally considered the anostracan crustaceans as
an easy prey for insects’ aquatic larvae and fish in particular (McCulloch et al. 2008).
In consequence, the temporal presence of Aphanius during the periods of low salinity
and high precipitation (see below), can be considered (together with the predation by
flamingos) as a major disturbance or selective force for the Phallocryptus populations.
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Figure 26: General observations at the site #12, where flamingos tend to aggregate more often
(A), bottom modification by the feeding activities of the flamingos (B), input of nutrients (e.g.
feathers, droppings, carcasses) to the Salt Labe by the birds (C). At the same site, we confirmed
the presence of two juveniles of the toothcarp (killifish) Aphanius fasciatus in the ponds formed
by wheel tracks (D). The site (see Table 2 for coordinates) is near the drainage canal from the
Zakaki Marsh.
Our recent observation of Aphanius in the Lake is not the first one. There are three
previous sightings of this fish in the logbook of the monitoring program of the Lake by
the Fisheries Department. Interestingly, all sightings were made during longer-thanaverage rainy periods (Fig.27). Water salinity was low during the rainier-than-normal
(indicated by positive anomalies) weeks/months, and the values were within the
tolerance range of the fish (Fig. 27).
Other sightings of the toothcarp in the ponds around the Lake during periods of
heavy rain (P. Charilaou, com. pers. 2011) suggests that in principle, Aphanius is
another important, although temporal, component of the fairy shrimp P. spinosa
predation pressure.
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Figure 27: Reported and firsthand sightings of the Mediterranean toothcarp (killifish) Aphanius fasciatus in
the Salt Lake in relation to rainfall monthly anomalies (Akrotiri Meteorological Station) and water salinity
(data from the Fisheries Department). Arrows denote the conditions before/during the observations of the
fish: algae bloom (green), rainy days (white), rainy days and firsthand report (orange). Rainfall monthly
anomalies were produced by subtracting the long-term average (1966-2011) of a given month from the total
rainfall for that month, and smoothed with an 11-point filter. Horizontal grey area denotes the salinity
range of A. fasciatus in the Mediterranean area (Triantafyllidis et al. 2007).
We could not capture the fish due to their evasive behavior: they swim extremely fast
into the bottom sediments avoiding capture/predation. A similar evasive behavior was
performed by an adult Aphanius in the Agios Georgios Pond, near the Salt Lake (S.
Michaelides, com. pers. 2012). In order to capture this specimen after the evasive
maneuver, it was necessary to dig a significant amount of the bottom sediments.
Aquatic larvae of dragonflies (Odonata) and diving beetles are another potential, but
important, predators of P. Spinosa. Carnivorous insects have been neglected on
previous reports of predators of the fairy shrimp in Akrotiri and in consequence, a
simplistic food chain is proposed for the Lake (see Revised Food Web-Phallocryptus’
perspective). During three field trips, many Odonata of at least two species (Anax
ephippiger and Sympetrum cf. fonscolombii), were observed coupling and laying
eggs in the ponds with abundant Phallocryptus. Exuviae were observed in February
confirming breeding in the ponds that eventually connected with the Lake at the peak
of the rain period. Diving beetles were also observed in the ponds containing
Phallocryptus. These kinds of beetles is known to prey avidly on small individuals of
fairy shrimps and are also considered to be an agent of dispersal, though limited, for
the anostracans (Beladjal & Mertens 2009).
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Even though the low biodiversity and the apparently simple food web of the Salt Lake,
the feedback between the aquatic and terrestrial components of the ecosystem is
significant. For example, we observed many diving or water beetles in the ponds
associated to the main Lake. Diving beetles are voracious insects known to prey on
fairy shrimps but also, assist in the anostracans’ dispersion by ingesting eggs which
eventually would be defecated in the same or different water body as the insect
emigrates (Beladjal & Mertens 2009). If the eggs are not damaged by the mandibles
of the insect during mastication nor digested, hatching of viable eggs occurs after
being for several days in the digestive tract of the water beetles.
There are other examples in which the presence of the predator not necessarily
means the automatic depletion or disappearance of the prey, fairy shrimps in the
present case. The ingestion of ovigerous females and cysts by vertebrate predators,
such as amphibians (Bohonak & Whiteman 1999), fish (Beladjal et al. 2007) and
waterfowl (Green et al. 2005), facilitates the dispersal of anostracans, provided the
eggs and cysts are not damaged. The relevance of such facilitated dispersal for the
life history of the fairy shrimps (e.g. net gain by being predated) varies among
species and successional environment of the pond/water body (e.g. changes in
salinity) (Bohonak & Jenkins 2003, Herbst 2006).
Insects with aquatic larvae link adjacent water bodies and ecosystems in general by
transporting nutrients, energy and material as they migrate. An extreme example is
the mass emergence of aquatic insects such as midgets as the move into the
terrestrial habitats, making thus, an extraordinary pulse of energy flowing into
different food pathways (Dreyer et al. 2012).
4.4.6
Aphanius fasciatus
The introduction (assisted or natural) of Aphanius to the Salt Lake during the months
when the low salinity is triggering the hatching of the first generation of Phallocryptus,
will eventually cause an unknown but most probably, significant impact on the Salt
Lake’s food web. It could be a text book case of disruption and alteration of
ecological webs. There is a precedent on the failure in 1991 of the hatching of
another anostracan, the brine shrimp Artemia salina, and its consequences for the
Larnaka Salt Lake’s ecosystem (Hadjichristophourou 2005). A more recent hatchling
failure occurred during the 2008 severe drought (I. Tziortzis, com. Pers. 2011).
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Aphanius is an avid predator of aquatic larvae of insects, being thus an effective
biocontrol of mosquitoes and other undesirable pests. It would be interesting to
investigate in the archives of the mosquito control program of the Akrotiri Military
Base to find out if aside from the use of Eucalyptus trees, Aphanius was intentionally
introduced to control larvae in the marshes around the Salt Lake.
4.4.7
Revised Food Web - Phallocryptus’ perspective
The Salt Lake has been considered devoid of fish and carnivorous insect larvae by
previous authors (Ortal 1992, Kerrison 2002). In consequence, a simple linear food
web has been proposed (Fig. 28). In that model, the biofilm, which is sustained by the
faecal and carcasses material from Phallocryptus, make nutrients available
stimulating thus the primary production and phytoplankton growth. The latter will
sustain the primary consumers (fairy shrimps) which in turn are consumed by the top
predators, the flamingos. It is suggested that bottom-up influences dominate the food
web: the abundance of Phallocryptus would control the flamingos’.
Figure 28: Original food web proposed for the Akrotiri Salt Lake. Flamingos are the top consumers feeding
exclusively on Phallocryptus.
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The proposed linear food web model would be correct only if the system is built on
those few components and such clear cut energetical pathways. However, our field
observations suggest that the food web pathways in the Salt Lake are more complex
than expected. The interactions are diverse and may vary in complexity during the
seasonal cycle of inundation and evaporation. Based on the new data, a revised
model of the food web pertaining Phallocryptus is proposed here (Fig. 29).
Figure 29: Revised food web proposed for the Akrotiri Salt Lake. White arrows indicate possible
interactions if the waterfowl consumes fry, eggs or small juveniles and adult aquatic insects and fish.
Several observations can be drawn from this model with a higher complexity. Firstly,
the presence of numerous potential predators (dragonfly nymphs, diving beetles and
the toothcarp Aphanius) in the Lake and associated ponds where Phallocryptus
thrives, suggests that these predators don’t necessarily drive to local extinction the
populations of Phallocryptus as it is often suggested in the literature.
Secondly, the position of the flamingos as the top consumers is redefined. Since
flamingos, and other waterfowl, are also known to feed on mud, which is the biofilm
(by gulping) and diatoms (by filtering), the flamingos should be positioned as
secondary consumers together with Phallocryptus. As said before, flamingos are not
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the only bird species consuming Phallocryptus and biofilm; several other birds are
known or suspected to share the same type of diet (e.g. Kuwae et al. 2012, see also
Birds in this report).
Thirdly, the waterfowl also shares the third trophic level in the model with the other
predators of Phallocryptus, but it can be also placed in the top level, fourth, if the
flamingos’ occasional ingestion of the small fry and eggs of Aphanius, and eggs and
recently hatched larvae of dragonflies is considered. For other bird species, the
ingestion of juveniles and adult individuals of fish and insects could be more often if
not the norm.
Additionally, the trophic dynamics in the Lake must be also strongly affected by the
annual and interannual variations in the onset of the flooding (changes in salinity and
nutrients) and the consequent algal blooming, hatching of Phallocryptus, and arrival
of predators. Such complex variations have been observed elsewhere (e.g. Herbst
2006) with seasonal changes of salinity producing strong influences in the
dominating trophic levels and dynamics.
4.4.8
Aquatic biotic components
The aquatic ecosystems incorporated in Akrotiri wetlands have not been extensively
studied in the past. Especially biotic components such as submerged macrophyte
flora and benthic macro-invertebrate fauna have been neglected, despite the fact that
wetland ecosystems are scarce in Cyprus and subsequently the species found in
these wetlands should be considered as rare for Cyprus flora and fauna. Only limited
records can be found related to benthic invertebrate fauna of Akrotiri wetlands (Ortal
1992, Kerrison 2002) and despite the huge amount of work done for terrestrial and
halophilous flora, the study of submerged aquatic macrophytes has been very
restricted (Meikle 1985, Christia et al. 2011). A short review of the existing data is
attempted, to highlight the most significant finding so far in the area.
4.4.9
Aquatic Macrophytes
The existing data on submerged aquatic macrophytes are limited to a few project
reports and only two publications. Aquatic Macrophytes from Akrotiri peninsula had
been first studied by Meikle. He only refers to the euryhaline angiosperm Ruppia
maritima, which he recorded near the salt lake (Flora of Cyprus Vol.2, 1985). On the
other hand, Ortal (1992) recorded only the less tolerant horned pondweed
(Zannichellia palustris) in the salt lake. Moreover, in the list of natural habitats of
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European interest at the peninsula, habitat code 3140 (Hard oligo-mesotrophic
waters with benthic vegetation of Chara formations) is present, suggesting the
existence of Charophyte species in the area.
A detailed study dated to the years 2007 and 2008, was published recently (Christia
et al. 2011). According to this study extensive submerged macrophyte beds cover a
major part of the wetland, especially areas with oligohaline or mesosaline waters,
providing food and shelter to invertebrates and birds. The authors described among
others, many macrophyte species from the Akrotiri salt lake and the adjacent
Phasouri marsh and Zakaki lake. In total 13 aquatic macrophyte species were
recorded, most of them described for the first time in Cyprus or in Akrotiri peninsula
(Table 6). Only Najas marina ssp. armata is listed in the Red Data Book of Cyprus,
since it is one of the few aquatic species that were previously recorded in Cyprus
wetlands. Another species, Althenia filiformis which shows fragmented distribution
throughout the Mediterranean, North Africa and Eurasia is considered endangered
due to the fragile ecosystems that it is met.
Table 7: Submerged aquatic macrophyte species recorded in the Akrotiri peninsula (VU:
Vulnerable, EN: Endangered, UN: Unknown)
Species name
Status
First described in Akrotiri wetland
Chaetomorpha sp.
UN
Christia et al. 2011
Cladophora sp.
UN
Chara aspera
UN
Chara canescens
UN
Chara vulgaris
UN
Lamprothamnium papulosum
UN
Spirogyra sp.
UN
Najas marina subs. armata
VU
Potamogeton pectinatus
UN
Potamogeton pussilus
UN
Ruppia maritima
UN
Meikle 1985
Althenia filiformis
EN
UN
Ortal 1992
Zannichellia
palustris
L.
ssp.
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Species name
Status
First described in Akrotiri wetland
pedicellata
4.4.10 Benthic Macroinvertebrates
Benthic macroinvertebrate communities have also been neglected by studies
conducted in the wetlands, in favour of terrestrial invertebrates. In a study of possible
impacts on Akrotiri salt lake and wetland ecosystems from damming on the Kouris
river (Ortal 1992), biological samples were collected from the lake and the
surrounding wetlands twice a month, with 0.5-mm and 0.2-mm mesh nets between
November and April. According to those results, the wetland supports a restricted
fauna, associated mainly with the water phase and comprising small crustaceans
such as Ostracoda, Copepoda and Cladocera as well as the fairy shrimp
Phallocryptus spinosa). This is a halophilic species typical of brackish continental
waters and is an important component of the diet of migrating flamingo that visit the
lake. Springtails (Collembola) which colonize the margins and emergent vegetation,
were also recorded as were various fly larvae (Diptera). In the freshwater Phasouri
marsh, faunal composition was found to be more diverse, with Ostracoda, Copepoda,
Cladocera, Oligocheta Nematoda, Diptera, Coleoptera and Acarea (water mites)
being found in several sampling surveys.
In the same context, a macroinvertebrate study taking place strictly in the salt lake
(Kerrison 2002), concluded that bivalve molluscs, gastropods, oligochaete worms
and fly larvae often visible to the naked eye in the sediments of permanent lakes and
saline water bodies, are largely absent from the Akrotiri salt lake. The most important
species in the complex is considered to be the fairy shrimp (P. spinosa) which is the
key component of the food wed in the Akrotiri salt lake. It is the main food source for
the greater flamingo (Phoenicopterus ruber) and other migratory birds that visit the
wetlands (Ortal 1992, Kerrison 2002, Hatzichristoforou 2004).
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4.5
Flora
4.5.1
Reference Conditions and Bioindicators
Reference conditions or high ecological status is a state of a water body or other
natural element where no or only minor changes can be found due to anthropogenic
disturbance. The determination of the reference conditions of biological quality
element, such as the vegetation, requires the determination of certain biological
values of the element in undisturbed status. These biological values, otherwise
bioindicators, are selected so as to have a dose-response relationship with one or
more disturbance factors. This dose-response relationship should be also determined
based on the values of the bioindicator in various degrees of disturbance. The
classification of the ecological status can then be based on an ecological quality ratio
(EQR) of the observed biological value to the reference biological value. A relative
ordinance scale of bad to poor, moderate, good and high can be constructed based
on the deviation of the values of the bioindicator from the reference conditions in
each case. This said, vegetation is better assessed by a combination of indicators,
depending a lot on the community type, and this is the practice followed below.
4.5.2
Vegetation - Habitats
Methodology
The determination of the reference conditions for the sclerophyllous shrub vegetation,
phrygana (habitat type 5420), juniper matorral (habitat type 5210), and maquis (9320)
as well as for the Mediterranean tall humid grasslands (habitat type 6420) was based
on the published literature and expert knowledge of the attributes of these habitats in
Cyprus (consise review in Delipetrou & Christodoulou 2010) and the proposed
bioindicators are mainly qualitative.
The determination of the reference conditions of the halophytic (habitat types 1310,
1410, 1420, 1430, 92D0 and reed beds and sedges) and the sand dune habitats
(habitat types 2110, 2190, 2250, 2260) was based on a preliminary review analysis
of the datasets (vegetation quadrats or réleves) authored and compiled by
Christodoulou (2003) and Hadjichambis (2005) by field work in the area of Akrotiri
peninsula. It must be stressed that any reference on this data and of their analysis in
the present project should also cite the above mentioned published works. It must
also be noted that since the above samplings were not designed in order to establish
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the reference conditions and ecological quality ratio, the analysis was exploratory
and the applicability and validity of each index remains to be proved by monitoring.
The vegetation classification of the quadrats by the above authors is presented in
Appendix II. The quadrats were also classified at a scale of disturbance of 0 (no
disturbances) to 6, based on the data provided. The following bioindicators of
vegetation quality were used:
Species-indicators of disturbance and other environental variables. The datasets
were combined and analysed for possible relationships of environmental variables to
particular species by Principal Component Analysis (PCA), Redudancy Analysis
(RDA), and Canonical Correspondece Analysis (CCA) by the software packages
Canoco 4.5©
ter Braak & Smilauer, 1997-2002 Biometris, Wageningen) and
CanoDraw 4.0© (ter Braak & Smilauer, 1999-2002 Biometris, Wageningen). Only
models deemed significant at the 0.05 % level by the Monte Carlo permutation test
(unrestricted permuations) were further analysed. The determination of the
explanatory environmental variables was made by automatic forward selection and
again only variables important at the 0.05 % level were taken into account. The
response of the species to these variables was analysed was explored by the
General Linear Model (GLM, see example in Figure 27) and the Generalized Additive
Model (GAM, see example in Figure 28). The species for which the response to an
environmental variable was significant at the 0.05% level were selected as
candidates for bioindicators for this variable. The environmental variables in both
datasets explained significantly but not fully the species data. The environmental
variables which explained significantly the species data were fire and disturbance
(recorded as presence or absence of recent events) in the acacia invasion study
dataset (Christodoulou 2003), and waste, disturbance by vehicles, and grazing in the
halophytic and sand dune vegetation dataset recorder at a scale of 1 to 6
(Hadjichambis 2005). The edaphologic parameters of organic matter, sand proportion,
moisture, electric conductivity (EC), PO3-, Cl-, which were provided only for the sand
dune data (Hadjichambis 2005), were also significant. For further analysis (see below)
each candidate bioindicator species was assigned a positive (1) or negative (-1)
value depending on whether its abundance was positevely or negatively correlated to
the increasing values of the variable (Appendix III).
Biodiversity indices. Species diversity consists of two different aspects of species
relative abundance: the actual number of species included in any particular sample,
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and the evenness of the distribution of individuals between the species encountered.
The following metrics differ in the extent at which they are influenced by the above
aspects. Diversity at species level was determined by the Shannon-Wiener index H'
(H' = −Σ Pi ln Pi, where Pi is the relative abundance of each species the quadrate)
and the related equatability or evenness index Rs = H’/lnN (where N=total species
number in the quadrat), a parameter of species competition (Krebbs 1999, Mai-He &
Kräuchi 2004). In addition, Hill’s indices (calculated by CanoDraw) were used. These
are N0 (species richness, i.e. number of species), N1 (exponential of Shannon-Weiner
Index) and N2 (reciprocal of Simpson’s Index, D = 1− Σ Pi2). N1 is more sensitive to
the number of species recorded in the sample, where as N2 is more sensitive to the
evenness of the distribution of individuals between species.
Floristic composition indices. For each species recorded in the quadrats the following
attributes were recorded (Appendix II): chorology (Cyprus endemics, native and
introduced species), conservation and protection status, Ellenberg indicator values
for Light (L), moisture (F), nutrients (N), and salt (S) (based largely on the indicators
for plants of the Aegean Böhling et al., 2002). Species were also assigned to
vegetation classes if they were characteristic of the class (and of the habitat types
defined by these classes) mainly according to Mayer (1995), Mucina (1997), and
Rivas-Martínez et al. (2002) and also based on expert opinion. Based on this they
were grouped as ammophilous, halophilous, wetland, dry grassland, shrub and
woodland species, synanthropic vegetation species, and uknworn.
The following
indices were calculated per quadrat and per habitat: number and relative abundance
of important (endemic and/or threatened and/or protected) and of introduced invasive
species, number and relative abundance of the characteristic species of each broad
vegetation group, number of positive or negative disturbance indicators, number of
indicators of ecological parameters in sand dunes, and average Ellenberg indicator
scores.
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AcaSalt
ArtMac
Response
InuCri
ElyElo
LimVir
AcaSall
PolMar
-2.0
PlaCor
SarPer
CenSpi
LimMuc
-0.4
Fire
1.4
Figure 30: GLM model of species response graph for the environmental variable Fire.
Acacia saligna trees (Acasalt) and seedlings (Acasall) have a positive response and the
8
other species have a negative response
Response
Junpho
Zygalb
Cakmar
Plamar
Limvir
Plaalb
Parmac
-2
Artmac
Urgmar
Beltri
-1
rovOrg
7
Figure 31: GAM model of species response graph for the environmental variable
Organic Matter. Juniperus phoenicea has a strong positive almost linear response,
Zygophyllum album and Cakile maritima have negative response. Plantago maritima
and Arthrocnemum macrostachyum present a unimodal response
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The proposed bioindicators and their known values for communities at various impact
categories are presented in Table 8.
Table 8: General Principles for the Reference Conditions of habitats
Index
Habitat area
Number and relative cover
of characteristic species
of alien and especially of
invasive species
of synanthropic vegetation
species
of disturbance indicator
species
4.5.3
1.
Reference condition
No change or positive change of total habitat area
No change or positive change of the ratio
area/perimeter of the habitat polygons
At least 1 species, dominant or co-dominant
0 and 0%
0 – 1 and 0 – 4 %
0 – 1 and 0 – 1 %
Halophytic Vegetation
Habitat type 1310: Salicornia and other annuals colonizing mud and sand. There
are two types of vegetation in this habitat. The first is vegetation of coastal salt
marshes dominated by annual succulents of the class Thero-Salicornietea and
occurs at the lowest levels of salt-marshes which dry up late bordering the
transition to aquatic vegetation. The second type is characterised by pioneer
usually dwarf annuals of the class Saginetea maritimae at loamy and sandy soils
which may be only innundated for only small periods.
Characteristic species: Thero-Salicornietea: Halopeplis amplexicaulis (tolerant
to trumbling by vehicles), Salicornia europaea, Suaeda maritima. Saginetea
maritimae: Polypogon maritimus, Hordeum marinum, Cressa cretica (a positive
waste indicator) etc. (see Appendix III).
Reference Conditions: This is a community with naturally low number of
species, especially the Thero-Salicornietea type, which often include only one
species. So the diversity index values should not be included in the reference
conditions. Moreover, the community type of Saginetea maritimae naturaly
establishes at disturbed site, so some of the characteristic species may be
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disturbance indicators. The important parameter is the comparative abundance
of halophytic vegetation species and the high average of the salt indicator value.
2.
Habitat type 1410: Mediterranean salt meadows (Juncetalia maritimi). Perennial
herb communities usually including tall rushes or grasses. The develop in
periodically, often deep, wet brackish or saline sites.
Characteristic species: Juncetea maritimi: Centaurium tenuiflorum, Elytrigia
elongata subsp. haifensis, Imperata cylindrica, Limbarda crithmoides, Plantago
maritima
subsp.
crassifolia,
Saccharum ravennae, Schoenus nigricans,
Triglochin bulbosa, the threatened species Linum maritimum and Juncus
maritimus, etc. (see Appendix III).
Reference Conditions: Biodiversity indices should remain high, but the quality
of floritstic composition is of higher importance. The participation of synanthropic
vegetation species in the “undisturbed” communities hint that the condition of the
habitat in the area of Akrotiri may not be satisfactory as a whole. The protected
Orchis fragrans may occur at less saline stations of this habitat.
3.
Habitat type 1420: Mediterranean and thermo-Atlantic halophilous scrubs
(Sarcocrnietea fruticosi). Perennial communities of the class Salicornietea
fruticosae mainly consisting of shrubs and subshrubs occurring at the drier parts
of the salt marshes.
Characteristic
species:
Salicornietea
fruticosae:
Arthrocnemum
macrostachyum, Salicornia fruticosa, Salicornia perennis, Atriplex portulacoides,
Halocnemum strobilaceum, Inula crithmoides, Spergularia marina, Suaeda vera,
and Limonium meyeri.
of floritstic composition is of higher importance. The participation of synanthropic
vegetation species in the “undisturbed” communities hint that the condition of the
habitat in the area of Akrotiri may not be satisfactory as a whole. The threatened
species Juncus maritimus occasionally occurs in this habitat.This community is
the one most often invaded by Acacia saligna since it occurs at the margins of
the salt marshes. The acacia communities recorded in the area have replaced
halophytic scrub and reed beds.
4.
Reed beds and sedges (habitat code CY02). Tall herb communities of brackish
and fresh water swamps of the class Phragmito-Magnocaricetea.
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Characteristic species: Phragmito-Magnocaricetea: Phragmites australis,
Juncus subulatus, and the threatened Cladium mariscus and Scirpus lacustris
subsp. tabernaemontani.
of floritstic composition is of higher importance. The acacia communities
recorded in the area have replaced halophytic scrub and reed beds and Oxalis
pes-caprae often invades this habitat, too. On the other hand, the threatened
species Linum maritimum and Crypsis factorovskyi occasionally occur in this
habitat. The characteristic species Phragmites australis has a large ecological
niche regarding moisture and pH and high tolerance to pollutants and it is a
negative indicator of disturbance.
5.
Habitat type 92D0: Southern riparian galleries and thickets (Nerio-Tamaricetea
and Securinegion tinctoriae). In the area of Akrotiri this habitat occurs either
sporadically along canals or at wet dunes, so it is not representative.
Characteristic species: Nerio-Tamaricetea: Tamarix tetragyna, Polygonum
equisetiforme.
Reference Conditions: There was a single quadrat in this habitat type in
Akrotiri, so only the general principles apply in this case.
6.
Habitat type 3170 (Halonitrophilous shrubs has been recorded in the coastal
dune areas of Akrotiri, so it is included in the sand dune communities).
4.5.4
7.
Fresh Water Wetlands
Habitat type 6420: Mediterranean tall humid grasslands of the MolinioHoloschoenion. The habitat includes communities of fresh or brackish water, in
meso- to eutrophic, basic soils reaching full bloom in summer. In Cyprus they
almost always occur at the riparian zone, but in the area of Akrotiri there is a
unique representative wet grassland at the Fasouri Marsh. These communities
have not been studied adequately.
Characteristic species: The characteristic species occurring at Fasouri marsh
are: Scirpoides holoschoenus, Schoenus nigricans, Pulicaria dysenterica subsp.
uliginosa, Teucrium scordium subsp. scordioides, Lotus corniculatus and the
rare species: Mentha aquatica (threatened) and Euphorbia pubescens. Another
three hygrophilous (emergent rhizophytes) species, Scirpus lacustris subsp.
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tabernaemontani (threatened), Orchis palustris, and Persicaria lapathifolia
(=Polygonum lapathifolium) belong to different vegetation classes but can be
considered as typical species of the habitat in Cyprus.
The very rare and threatened in Cyprus Baldellia ranunculoides has also been
found in the area of this habitat, but it most probably belongs to another
vegetation unit of dwarf amphibious plants of the class Isoeto-Littorelletea which
has never been recorded in Cyprus (possibly corresponding to Annex I habitat
type 3130).
In Fasouri marsh species indicating anthropogenic disturbance including grazing
and such as Ononis spinosa, Trifolium fargiferum subsp. bonannii, and Centaura
calcitrapa subsp. angusticeps. Also part of the area is dominated by Panicum
repens and Saccharum spp. indicating increased drought.
Reference Conditions: Due to the limited knowledge on the habitat, only the
general principles apply in this case. In general, the wetlands of Fasouri Marsh
need to be studied in more detail.
8.
Habitat type 7210*: Calcareous fens with Cladium mariscus and species of the
Caricion davallianae. Helophytic communities with Cladium mariscus beds in the
littoral zone of lakes or other wetlands in contact with reedbeds or other wetland
communities. This habitat has not been recorded in Cyprus up to now and
Cladium mariscus is a rare and threatened species. The habitat has been
mapped at the only known extant location of Cladium mariscus north of the salt
lake of Akrotiri within Phragmites beds (CY02). The locals used to make baskets
with the plant and its area used to be ferquently burned. A phytosociological
study of the community is needed in order to confirm the presence of the habitat
in Cyprus.
Characteristic species: Cladium maricscus.
Reference Conditions: The presence and abundance of the typical species
Cladium mariscus and the other the general principles.
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Figure 32: Vegetation of the habitat type 3170 with Juncus ambiguus and Isolepis cernua in
Akrotiri (14/05/2011).
4.5.5
Sand Dune Vegetation
The proposed bioindicators and their known values for communities at various impact
categories are presented in tables 9, 10 and 11.
9.
Habitat type 1210: Annual vegetation of drift lines. Nitrophilous, low cover
communities on sand or shingle consisting the first zone of vegetation of the
class Cakiletea maritimae. In Cyprus this habitat type includes one more
vegetation type, which is the one occurring in Akrotiri, communities with the
threatened endemic species Taraxacum aphrogenes on single and pebble.
Characteristic species: Cakiletea maritimae: Cakile maritima, Salsola tragus
(=Salsola kali), Matthiola tricuspidata. Unknown class (possibly CrithmoStaticetea): Taraxacum aphrogenes.
Reference Conditions: There was a single quadrat in this habitat type in
Akrotiri, so only the general principles apply in this case.
10. Habitat type 1430: Halo-nitrophilous scrubs (Pegano-Salsoletea). This is a semidesert habitat, occurring very sporadically and not well known in Cyprus
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Characteristic species: Pegano harmalae-Salsoletea vermiculatae: Atriplex
halimus, Mesembryanthemum nodiflorum. In Cyprus the species Asparagus
stipularis, Lycium schweinfurthii and Zygophyllum album are characteristic of
this habitat.
Reference Conditions: This is little known and possibly fragmentaty habitat in
Cyprus.
11. Habitat type 2110: Embryonic shifting dunes. Communities that form the first
dune vegetation zone including sand binders such as Elytrigia juncea and
Medicago marina. Some of the communities identified by Hadjichambis (2005)
cannot be easily assigned to this habitat type, the rather approach habitat type
2210 (grey dunes of the Crucianetallia maritimae, not recorded in Cyprus, yet) or
are close to habitat types 2190 and 1430 (see below). This is the main habitat
type of the sand sunes of Cyprus.
Characteristic species: Ammophiletea: Elytrigia juncea, Medicago marina,
Sporobolus virginicus, the near threatened Pancratium maritimum, the
threatened Achillea maritima (=Otanthus maritimus), etc. (see I II). In Cyprus
Zygophyllum album is also a characteristic species and a sand binder.
Reference Conditions: The most important parameter is the quality of the
floristic composition, which should include ammophilous species of the
Ammophiletea or of the class Thero-Brachypodietea (order Malcolmietalia) or at
most clayey stations halophilous wetland species. The threatened species
Juncus maritimus, Aegilops bicornis, and Lotus cytisoides also occur
occasionally in this habitat.
12. Habitat type 2230*: Malcolmietalia dune grasslands. Annual communities
characterised of usually small ammophilous plants occurying vegetation
openings of deep sands, especially among the habitats 2250, 2260.
Characteristic species: Thero-Brachypodietea (order Malcolmietalia): the
threatened Triplachne nitens and Coronilla repanda subsp. repanda, Medicago
littoralis, Avellinia michellii, Corynephorus articulatus.
Reference Conditions: This community has been recorded from the area of
Akrotiri, but there are no avaialable quadrats, so the general reference
conditions are applied.
71
Consulting CYPRUS
13. Habitat type 2240: Brachypodietalia dune grasslands. Annual communities
characterised by the typical dry grassland plants occurying at vegetation
openings of shallow sands, especially among the habitats 2250, 2260..
Characteristic
species:
Thero-Brachypodietea
(order
Brachypodietalia):
Trachynia distachya, Coronilla scorpioides, Trifolium spp., etc. (see Appendix
III).
Reference Conditions: The biodiversity indices are important in this
community.
14. Habitat type 2190: Humid dune slacks. Communities at humid depressions of
the dunal systems, usually including tall grasses, rushes and sedges.
Characteristic species: Juncetea maritimi (more saline stations): Schoenus
nigricans, Plantago maritima subsp. crassifolia, and the threatened Juncus
maritimus. Mollinio-Arrhenatheretea (less saline stations): Blackstonia perfoliata
and the protected Orchis fragrans. Also the threatened Lotus cytisoides and the
protected Serapias vomeracea.
Reference Conditions: The threatened species Aegilops bicornis occurs
occasionally in this habitat.
15. Habitat type 2250*: Coastal dunes with Juniperus spp. A habitat of stabilised
back dunes with Juniperus phoenicea.
Characteristic species: The shrub Juniperus phoenicea and other tall shrubs of
the class Quercetea ilicis (Pistacio-Rhamnetalia alaterni) (see 5210, 9320
below), especially Pistacia lentiscus, Asparagus stipularis, Prasium majus,
Ephedra phoeminea. Otherwise, the floristic composition is very similar to the
one of habitat 2260 below.
Reference Conditions: The biodiversity indices are particularly important. The
threatened species Aegilops bicornis, Lotus cytysoides, and Coronilla repanda
subsp. repanda occur occasionally in this habitat.
16. Habitat type 2260: Dune sclerophyllous scrubs. In Cyprus this habitat includes
low shrub (phrygana) of the class Cisto-Micromerietea or taller shrub (matorral,
maquis) of the order Pistacio-Rhamnetalia alaterni. It is a back dune habitat on
stabilised and occasianlly wetter dunes.
72
Consulting CYPRUS
Characteristic species:
Cisto-Micromerietea: Coridothymus capitatus, the
endemic species Teucrium micropodioides, Asperula cypria, Odontites liknii
subsp. cypria and Anthemis tricolor, Helianthemum stipulatum (this is an
ammophilous species in Greece and Cyprus), Cistus spp., Thymelaea hirsuta,
Noaea
mucronata,
Phagnalon
rupestre,
Fumana
thymifolia,
Pistacio-
Rhamnetalia alaterni: Pistacia lentiscus, Asparagus stipularis, Rhamnus
oleoides ssp. graecus, Lycium schweinfurthii. The floristic composition is also
characterised by the frequent participation of ammophilous species such as
Achillea maritima.
Reference Conditions: The biodiversity indices are particularly important. The
threatened species Aegilops bicornis, Lotus cytysoides, and Coronilla repanda
subsp. repanda occur occasionally in this habitat.
17. Habitat type 2270*: Wooded dunes colonized by Pinus pinea and/or Pinus
pinaster. This habitat was recorded in the area of Akrotiri (Agroktima Agiou
Nikolaou, Fenced Area) based on the occurence of Pinus brutia and Pinus
halepensis stands on sand dunes. The code 2270 is used in Tables 3 and 4 and
in Appendix I to denote these communities. However, it is apparent that of these
none stands is natural . Although the habitat type 2270 includes non-natural but
established pine stands, we believe that Pinus brutia and Pinus halepensis
represent a threat for the native communities of the dunes. In both cases these
stands occur near Juiperus phoenicea communities on sand dunes. The stands
of Pinus halepensis (aleppo pine) which is an alien species in Cyprus planted in
the area of Akrotiri since 1900 certainly represent invasion of the pine in the
juniper dune vegetation (habitat 2250*). Pinus brutia is native in Cyprus but it is
a very aggressive species with post-fire regeneration mechanisms which is
known to invade juniper sand dunes elsewhere (Thanos et al. 2011) and it
seems that the stands in Akrotiri also represent an invasion to the habitat 2250*.
4.5.6
Thermo-Mediterranea Shrub Vegetation
18. Habitat type 5420: Aegean phrygana (Sarcopoterium spinosum). Low,
hemisphaerical shrubs, usually spiny and aromatic belonging to the East
Mediterrean class Cisto-Micromerietea.
73
Consulting CYPRUS
Cisto-Micromerietea: Coridothymus capitatus, the
endemic species Teucrium micropodioides, Asperula cypria and Odontites liknii
subsp. cypria, Cistus spp., Thymelaea hirsuta, Noaea mucronata, Phagnalon
rupestre, Fumana thymifolia. Thero-Brachypodietea dry grasslands usually form
at large openings.
Reference Conditions: The representative shrub communities have a woody
vegetation cover of at least 40 %. Biodiversity indices are usually very high and
the number of endemic, threatened and protected species (especially orchids) is
also usually high. Invasions are rare if any and then restricted at the margins of
the communities, hence the presence of aliens in this habitat is a sign of serious
degradation. The communities are quite resistant to grazing and mild grazing
may even favour them, but over-grazing causes the degradation of the floristic
composition (increased number and abundance of synanthropic dry grassland
species).
19. Habitat type 5210: Arborescent matorral with Juniperus spp. In Akrotiri this
habitat includes matorral with Juniperus phoenicea. Cisto-Micromerietea.
Tall shrub layer of Quercetea ilicis (Pistacio-
Rhamnetalia alaterni): Juniperus phoenicea, Pistacia lentiscus, Rhamnus
oleoides subsp. graecus, Prasium majus, Rubia tenuifolia, Olea europaea subsp.
oleaster, Ephedra foeminea.
Cisto-Micromerietea phrygana and
Thero-
Brachypodietea dry grassland understorey of the same series of species as in
habitat 5420.
Reference Conditions: The representative communities have a Juniperus
phoenicea cover higher than 10 % and a total tall shrub cover of at least 20 %
the the height of the heighest shrubs is at least 2 m. Nevertheless, in Cyprus the
habitat also includes “wind-shaped” communities of a height of less than 1 m
growing at exposed locations.
Biodiversity indices are usually very high (this is maybe the habitat with the
higher number of species per m2) and the number of endemic, threatened and
protected species (especially orchids) is also usually high. Invasions are rare if
any and then restricted at the margins of the communities, hence the presence
of aliens in this habitat is a sign of serious degradation. The communities are
less resistant to grazing, although Juniperus phoenicea is not grazed. Over74
Consulting CYPRUS
grazing causes the degradation of the floristic composition (increased number
and abundance of synanthropic dry grassland species). Juniperus phoenicea is
not resistant to fire so this is a serious threat.
20. Habitat type 6220*: Pseudo-steppe with grasses and annuals (TheroBrachypodietea). The habitat includes dry grasslands with annuals and grasses
which develop on oligotrophic, alkaline soils. They are considered as a precursor
to the Mediterranean shrub vegetation and usually occur in large shrub openings
or coulonize burned areas. In the area of Akrotiri they occur only in juniper shrub
openings (habitat 5210).
Characteristic species: Thero-Brachypodietea: Species occurring in Akrotiri
are Trachynia distachya, Stipa capensis, Avena barbata, Bellevalia spp.,
Biscutella didyma, Briza maxima, Catapodium rigidum, Psilurus incurvus,
Hedysarum spinosissimum, Hedypnois rhagadioloides, Hyacynthella millingenii,
Hypochaeris achyrophorus, Avellinia michelii,
Lagurus ovatus, Onobrychis
crista-galli, Poa bulbosa, Plantago afra, Plantago cretica, Silene spp., Trifolium
campestre, T. scabrum., Valantia hispida, Linum strictum, Rostraria cristata,
Biscutella
diduma,
Helianthemum
salicifolium,
Asterolinon
linum
stellatum.Lygeo-Stipetea tenasissimae: Hyparrhenia hirta, Dactylis glomerata.
Reference Conditions: The representative communities have a plant cover of
at least 30 %. Biodiversity indices are quite high and represent an important
criterion for the habitat, especially the evenness indices. Floristic composition
indices are also important, a large participation of synanthropic species usually
indicates grazing or increased nutrient content due to other reasons (e.g. waste
disposal).
21. Habitat type 9540: Mediterranean pine forests with endemic Mesogean pines. In
Akrotiri this habitat includes Pinus brutia forest. It does not include Pinus
halepensis forests which originated from plantations.
Tall shrub layer of Quercetea ilicis (Pistacio-
Rhamnetalia alaterni): Juniperus phoenicea, Pistacia lentiscus, Rhamnus
oleoides subsp. graecus, Prasium majus, Rubia tenuifolia, Olea europaea subsp.
oleaster, Ephedra foeminea. Cisto-Micromerietea phrygana understorey of the
same series of species as in habitat 5420 but especially Cistus spp.
75
Consulting CYPRUS
Reference Conditions: The representative pine forests have a Pinus brutia
cover of 50 – 100 %, a shrub undestorey cover of at least 20 % and a herb
understorey cover of 5 – 25 %. Biodiversity indices may not be high, even at
representative forests. The dominance of a single herb species in the herb
understorey, especially of synanthropic grasses, indicates possible habitat
degradation.
Biological quality index values for the various habitats are presented on Tables
8-10.
76
Consulting CYPRUS
Table 9: Biological quality index values for the Halophytic habitats of the area of Akrotiri. The working reference conditions are illustrated by the values of the indices in the undisturbed
Introduced
Invasive
species
Indicators of
Ellenberg Indicator Values
Halophytic Wetland Synanthropic
Disturbance (No)
(average)
0
5.5
0.2
1.5
1.7 0.9 1.0 4.5 5.6 4.2 5.3
0.0
0.0
0.0
1.5
5.5 100.0 0.0
0.0
8.4
8.5
8.8
6.9
7.0
1310
1
2.0
0.1
0.0
0.8 0.0 0.8 1.0 2.3 1.0 1.9
0.0
0.0
0.5
0.5
2.0 100.0 0.0
0.0
9.0
8.5
9.0
7.0
8.0
1410
0
6.6
0.3
0.5
2.9 0.7 1.0 1.6 17.8 1.4 16.7
0.0
0.0
2.1
1.6
3.8 79.5 0.5 23.5
0.3
4.3
8.2
6.6
8.5
5.7
5.0
1410
1
10.8
0.4
0.7
2.8 0.9 1.0 2.0 16.2 1.9 14.9
0.4
8.2
7.9
6.1
8.4
5.9
4.6
1410
2
8.0
0.3
2.0
2.0 1.0 1.0 7.3 7.3 6.6 6.6
0.0
8.3
3.8
8.3
5.2
1.7
1420
0
4.9
0.2
0.0
2.4 0.0 1.0 1.0 10.8 1.0 10.6
0.2
1420
1
9.2
0.2
0.0
2.6 0.0 1.0 1.0 13.4 1.0 12.1
1420
2
7.8
0.2
0.3
1420
3
14.0
0.3
2.4
1420
5
7.9
0.2
92D0/
2260
acacia
invasion
(1420)
CY02
1
7.5
5
Type
species)
1310
Habitat
impact
min max min max min max min max
Salt (S)1
Important
species
Nutrient
(N)
N2
Reaction
(R)
N1
Moisture
(F)
Rs
Light (L)
H'
sp per m2
N0 (Number of
communities (Impact=0).
No
Cover
3.2
No
Cove
Negative
Cove
Cove
Positive
No
No
r
r
r
No
Cover
0.0
4.2
3.8
6.8 73.9 1.1 17.8
0.2
0.0
3.0
0.0
2.0 64.5 1.0
4.8
0.0
4.8
0.0
1.6
2.4
3.9 84.6 0.2 41.9
0.1
2.4
8.4
6.9
8.6
6.5
6.0
0.7
1.8
0.0
3.6
5.1
7.0 84.5 0.8 15.9
0.7
5.7
7.9
7.1
8.5
6.3
5.2
2.4 0.5 0.9 1.4 10.6 1.2 9.2
0.4
1.1
0.2
1.1
2.8
3.8
5.6 92.8 1.0
0.6
2.7
8.0
7.3
8.5
6.2
5.8
2.4 0.9 0.9 11.1 11.1 9.3 9.3
1.0
1.2
1.0
1.2
7.0
9.0
12.0 96.4 0.0
2.0
3.6
7.7
6.7
8.4
6.0
5.3
1.6
2.3 0.9 0.9 4.8 9.6 4.0 8.0
0.0
1.0
48.9
4.4
3.8
5.5 49.3 0.4
1.2
1.8
50.0 7.6
6.7
8.4
6.1
4.0
0.3
1.9
2.0 0.9 1.0 6.5 7.1 6.1 6.5
0.0
0.0
2.5
3.5
4.5 49.5 2.0 48.6
0.5
2.3
8.3
6.9
8.4
6.6
4.8
3.0
0.0
1.0
1.6 0.8 0.9 2.6 4.8 2.3 3.9
0.0
1.0
93.1
2.1
0.3
1.4
1.1
1.4
94.0 7.1
6.5
8.1
5.8
2.9
0
10.6
0.2
1.9
2.4 0.8 0.9 6.7 11.3 5.1 9.4
0.6
0.3
1.6
2.3
5.3
6.1 29.7 2.9 66.9
1.1
4.3
7.5
6.8
8.2
5.8
4.5
CY02
1
11.0
0.2
2.1
2.2 0.9 0.9 8.4 9.1 7.5 7.6
0.0
0.5
0.7
2.0
7.0
7.0 68.0 2.5 30.9
1.5
2.2
7.6
6.9
8.3
6.1
4.8
CY02
2
10.0
0.2
2.1
2.1 0.9 0.9 8.5 8.5 7.8 7.8
0.0
1.0
1.0
4.0
7.0
7.0 88.5 2.0 10.4
1.0
1.0
7.8
6.7
8.3
6.0
5.6
CY02
5
4.3
0.1
1.4
1.7 0.8 0.9 3.9 5.6 3.3 4.5
0.0
1.0
86.8
3.8
1.8
1.8
1.5
87.5 7.2
7.8
8.2
5.9
3.8
1.3
5.8
3.9
0.1
1.0
6.0
8.6
Consulting CYPRUS
Table 10: Biological quality index values for the Sand Dune habitats of the area of Akrotiri. The working reference conditions are illustrated by the values of the indices in the undisturbed
Habitat
Type
impact
N0 (Number
of sp)
sp per m2
communities (Impact=0). Part I.
1420/2190
1420/2190
1420/2190
1430
1430
1430
2110
2110
2110
2110
2110/1430
2110/1430
2110/1430
2110/2210
2110/2210
2190
2190
2190/2240
2190/2240
2240
2240
2240/2230
2250
2250
2260
2260
2260
0
1-2
3-4
1-2
3-4
5-6
0
1-2
3-4
5-6
0
1-2
3-4
0
1-2
0
1-2
0
1-2
0
1-2
1-2
0
1-2
0
1-2
3-4
8.5
13.7
14.0
9.5
9.0
7.0
5.4
7.1
5.3
7.7
7.0
10.0
11.0
6.6
13.9
11.5
12.0
14.9
17.8
10.0
1.0
17.8
9.1
19.1
11.5
14.7
25.0
0.2
0.2
0.1
0.1
0.1
0.1
0.2
0.2
0.1
0.1
0.4
0.1
0.3
0.3
0.4
0.9
0.5
0.8
0.7
0.4
0.0
0.8
0.4
0.7
0.5
0.5
1.0
H'
Rs
N1
N2
min
max
min
max
min
max
min
max
1.8
2.0
2.4
1.8
1.6
1.8
0.0
0.0
1.4
1.7
1.9
2.2
2.3
1.0
1.7
1.7
1.7
2.3
2.6
1.4
0.0
2.7
0.0
2.3
1.3
2.2
3.1
2.2
3.0
2.4
2.4
2.4
1.8
2.4
2.6
1.7
2.2
1.9
2.2
2.3
2.2
3.1
2.8
2.8
2.9
2.9
2.9
0.0
3.0
2.8
3.2
3.0
2.8
3.1
0.9
0.9
0.9
0.9
0.9
0.9
0.0
0.0
0.9
0.9
1.0
1.0
0.9
0.8
0.9
0.9
0.9
0.9
0.9
1.0
0.0
1.0
0.0
1.0
0.9
0.9
1.0
1.0
1.0
0.9
1.0
1.0
0.9
1.0
1.0
1.0
0.9
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
0.0
1.0
1.0
1.0
1.0
1.0
1.0
5.9
7.6
11.5
6.0
4.8
6.2
1.0
1.0
4.0
5.3
6.4
9.3
9.7
2.8
5.7
5.5
5.3
9.9
14.1
4.0
1.0
15.2
1.0
9.9
3.6
9.3
22.5
9.1 5.3 8.1
19.2 6.6 16.9
11.5 9.9 9.9
11.1 5.4 10.0
11.0 4.6 9.7
6.2 5.7 5.7
10.7 1.0 9.7
13.6 1.0 12.3
5.5 3.4 5.1
8.7 4.9 7.5
6.4 6.1 6.1
9.3 8.7 8.7
10.0 8.5 9.2
9.0 2.7 8.2
21.3 4.8 18.9
16.6 5.1 15.4
16.4 4.7 15.2
18.8 8.2 17.2
18.5 12.5 17.2
18.4 4.0 16.7
1.0 1.0 1.0
19.6 13.8 18.3
16.1 1.0 15.1
25.1 9.0 22.9
19.6 3.3 18.2
17.1 7.7 15.9
22.5 20.2 20.2
Introduced
Indicators of
Ammophilou
Invasive
Disturbance
s
species
(No)
Cove No Cover Positiv Negativ No Cover
r
e
e
Important
species
No
0.0
0.0
0.3 1.9 0.0
1.0 2.1 0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.3 14.6 0.0
0.4 9.1 0.0
0.0
0.0
0.3 5.4 0.0
0.0
0.0
1.0 6.4 1.0
0.5 4.2 0.0
0.2 4.1 0.0
0.7 6.6 0.0
0.4 5.5 0.0
0.0
0.0
0.8 3.1 0.0
0.6 2.3 0.0
0.3 2.9 0.0
1.0 100.0 0.0
1.3 6.6 0.0
0.4 4.1 0.0
1.3 7.4 0.0
1.0 9.0 0.0
0.8 12.6 0.0
2.0 2.0 0.0
6.4
2.0
3.7
5.0
2.0
0.3
0.0
0.7
0.5
0.0
0.3
3.0
0.0
0.5
0.5
2.6
2.6
4.5
2.6
4.2
2.7
0.0
3.5
1.2
1.6
2.1
2.3
1.0
2.5
3.7
4.0
1.5
1.3
0.0
0.2
0.1
0.0
1.0
2.0
2.0
2.5
0.0
1.2
1.5
4.5
1.7
2.0
0.3
0.0
0.5
0.3
0.0
0.3
0.8
1.0
1.0
1.7
1.0
4.5
5.0
4.0
3.1
4.4
4.0
4.7
0.0
3.0
1.5
3.4
5.4
1.3
1.0
1.5
2.4
0.7
0.0
2.0
1.3
2.4
2.4
4.5
3.0
6.1
3.3
2.1
27.4
36.6
20.9
63.7
70.7
40.6
49.1
17.0
20.8
69.1
46.1
11.3
7.5
8.5
10.0
13.5
18.1
11.9
11.4
15.8
17.9
5.3
Shrub
Halophytic
Wetland
No
Cover
No
Cover
No
1.5
0.3
1.0
1.5
1.3
1.0
0.5
0.4
0.0
0.0
0.0
0.0
0.0
1.1
2.1
1.8
0.5
3.2
3.2
1.3
0.0
4.5
5.0
10.0
4.8
4.0
6.0
8.2
1.9
1.1
7.8
32.4
41.9
13.0
3.5
5.0
8.3
8.0
3.0
2.5
2.0
0.9
0.8
1.0
2.3
4.0
4.0
6.5
0.4
2.6
3.7
6.5
3.5
3.6
1.0
0.0
2.8
0.8
0.5
1.5
2.0
0.0
90.9
84.1
84.2
62.5
30.5
37.2
46.7
39.8
57.2
47.3
58.6
66.0
77.4
18.9
30.0
56.3
78.4
37.3
31.4
20.5
0.0
0.7
0.0
0.0
0.0
0.0
0.0
0.1
0.0
0.3
1.0
1.0
0.5
0.0
0.0
0.8
1.5
0.4
0.8
1.0
0.0
0.0
0.2
0.1
0.2
0.5
0.0
7.2
13.1
15.1
4.5
40.3
29.1
9.8
24.7
82.9
75.8
56.9
45.1
19.2
14.3
10.0
1.6
21.6
12.2
Cover
2.5
4.9
5.4
3.4
6.4
4.2
6.2
5.2
3.9
2.1
32.6
13.4
3.3
14.3
2.9
S
ynanthropic
No
Cover
1.0
1.3
3.0
0.5
0.0
0.0
0.1
0.3
0.0
0.0
1.0
1.0
1.5
0.2
0.6
1.1
0.5
2.4
3.2
1.7
0.0
1.0
0.5
1.8
0.8
0.8
2.0
2.0
11.0
11.6
4.5
29.7
8.9
10.3
6.4
11.3
3.6
5.4
12.4
6.0
9.7
17.5
15.4
11.3
3.4
4.1
7.4
7.3
4.0
Habitat
Type
impact
N0 (Number
of sp)
sp per m2
Consulting CYPRUS
2260/1430
2260/1430
2260/2190
2260acacia
2270
2270
2270
aleppo
0
1-2
0
5-6
0
1-2
1-2
20.8
19.0
17.0
12.3
23.0
14.0
20.7
0.8
0.8
0.7
0.1
0.9
0.1
0.8
H'
Rs
N1
N2
Introduced
Indicators of
Ammophilou
Invasive
Disturbance
s
species
(No)
Cove No Cover Positiv Negativ No Cover
r
e
e
Important
species
min
max
min
max
min
max
min
max
No
2.8
2.7
2.7
2.3
3.1
2.6
2.2
3.0
3.0
2.7
2.4
3.1
2.6
3.4
1.0
1.0
1.0
0.9
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
16.4
15.1
15.3
10.3
21.5
13.1
9.4
20.5
20.2
15.3
11.5
21.5
13.1
29.4
14.9
14.3
13.8
8.8
20.0
12.3
8.7
18.8
18.4
13.8
10.3
20.0
12.3
26.5
0.5
1.0
1.0
0.7
1.0
0.0
1.7
2.2
4.8
1.9
6.8
2.2
4.1
0.0
0.0
0.0
1.0
0.0
0.0
1.0
53.1
27.6
5.5
5.0
3.0
3.3
2.0
1.0
0.3
2.0
1.0
0.0
0.0
1.0
0.0
0.0
2.5
2.5
2.0
5.0
0.0
4.0
3.7
9.1
13.6
4.8
11.6
16.8
13.7
Shrub
Halophytic
Wetland
S
ynanthropic
No
Cover
No
Cover
No
Cover
No
Cover
5.0
5.5
4.0
4.0
10.0
9.0
10.3
45.6
38.0
25.0
26.3
73.5
80.9
75.5
4.8
3.0
1.0
0.3
2.0
0.0
0.0
16.3
21.0
36.5
1.3
5.1
1.0
1.0
1.0
0.0
2.0
0.0
0.0
4.8
3.3
1.9
4.3
4.0
4.0
2.0
3.0
1.0
1.7
16.7
16.0
14.4
56.1
5.9
2.3
4.2
3.7
Consulting CYPRUS
Table 11: Biological quality index values for the Sand Dune habitats of the area of Akrotiri. The working reference conditions are illustrated by the values of the indices in the undisturbed communities (Impact=0).
Part II.
Habitat Type
Impact
Ellenberg Indicator Values (average)
1420/2190
1420/2190
1420/2190
1430
1430
1430
2110
2110
2110
2110
2110/1430
2110/1430
2110/1430
2110/2210
2110/2210
2190
2190
2190/2240
2190/2240
2240
2240
2240/2230
2250
2250
2260
2260
2260
2260/1430
2260/1430
0
1-2
3-4
1-2
3-4
5-6
0
1-2
3-4
5-6
0
1-2
3-4
0
1-2
0
1-2
0
1-2
0
1-2
1-2
0
1-2
0
1-2
3-4
0
1-2
Light (L) Moisture Reaction Nutrient
(F)
(R)
(N)
8.1
4.4
8.4
6.0
7.9
5.9
8.3
6.0
7.8
4.4
8.2
5.5
8.5
3.5
8.4
6.5
8.6
3.4
8.5
6.9
8.4
3.2
8.3
6.9
8.5
3.4
8.5
6.5
8.4
3.1
8.5
6.5
8.3
3.3
8.6
6.5
8.2
3.9
8.5
6.3
8.0
4.5
8.6
5.8
8.6
4.8
8.3
6.7
7.9
5.4
8.4
6.3
8.3
3.5
8.3
6.1
8.2
3.8
8.3
5.9
7.8
4.3
8.3
5.6
8.0
5.9
8.4
6.1
7.9
3.6
8.2
5.5
7.8
3.7
8.2
5.5
7.5
4.1
7.9
5.8
7.0
5.0
8.0
7.0
7.9
3.7
8.0
5.4
7.7
3.0
8.1
5.5
7.8
2.8
8.0
5.1
7.9
3.4
8.2
5.4
8.1
3.5
8.2
5.7
7.6
3.0
8.1
5.9
7.9
3.4
8.1
5.6
7.8
3.3
8.0
5.4
Indicators of Indicators of Indicators of Indicators of
Indicators of
Sand
Drainage
Moisture
Organic
EC(No)
Content (No)
(No)
(No)
Matter(No)
Salt Positi Negat Positi Negat Positi Negat Positi Negat Positi Negative
(S)
ve
ive
ve
ive
ve
ive
ve
ive
ve
4.2
0.5
0.0
0.5
5.0
4.0
0.5
0.0
0.5
4.0
0.0
4.0
0.7
1.3
1.0
7.7
6.3
0.7
0.0
0.7
6.0
0.3
3.9
1.0
1.0
1.0
9.0
7.0
1.0
0.0
2.0
7.0
0.0
3.9
4.5
0.5
3.0
1.5
2.5
3.5
0.0
3.5
3.5
1.0
4.3
4.3
0.3
3.5
1.3
2.3
3.8
0.0
3.8
3.0
1.3
4.6
3.0
0.0
4.0
0.0
1.0
3.0
0.0
3.0
2.0
1.0
4.1
2.8
0.0
2.9
0.5
0.5
2.8
0.0
2.0
1.5
1.5
3.9
3.1
0.0
2.9
0.8
0.3
3.1
0.0
3.0
1.5
2.3
4.4
3.7
0.0
3.3
0.0
0.3
4.3
0.0
4.3
2.3
2.0
4.5
3.7
0.3
4.0
1.0
2.0
3.7
0.0
4.0
2.7
2.0
4.4
1.0
0.0
1.0
4.0
3.0
1.0
0.0
1.0
5.0
0.0
5.1
3.0
0.0
4.0
2.0
4.0
3.0
0.0
4.0
3.0
1.0
4.5
1.0
0.5
1.0
3.5
3.5
1.5
0.0
2.0
3.5
1.0
2.9
2.4
0.1
2.6
0.4
0.3
2.3
0.1
1.5
0.7
2.7
2.6
3.5
0.7
2.7
3.9
1.8
3.0
0.1
2.6
2.3
3.2
2.6
0.6
2.0
0.7
6.2
4.0
0.7
0.6
0.5
5.0
0.2
3.9
0.0
2.0
0.0
7.0
5.5
0.0
0.0
0.0
5.0
0.0
2.4
0.4
2.4
0.5
8.2
3.5
0.4
0.8
0.5
4.8
0.2
2.2
0.4
2.4
0.6
9.2
4.6
0.4
0.8
0.4
6.2
0.2
1.3
0.7
0.3
0.7
2.0
1.0
0.3
0.0
0.0
1.0
0.3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
1.7
0.8
1.5
1.3
2.3
1.5
0.3
0.5
0.0
1.3
1.0
1.7
0.5
1.4
1.9
1.4
1.1
0.7
2.5
0.3
0.5
2.1
1.5
0.8
2.9
1.9
1.8
0.8
0.5
3.6
0.1
0.5
2.4
1.7
0.8
0.8
1.3
2.3
0.9
1.0
0.8
0.4
1.0
1.4
2.4
1.9
1.1
2.1
3.7
2.3
1.6
0.6
1.2
2.5
1.5
1.4
0.0
2.0
0.0
2.0
0.0
0.0
3.0
0.0
0.0
0.0
2.2
1.0
1.5
1.0
8.0
4.0
1.0
1.5
1.0
5.0
0.0
1.7
0.5
2.0
0.5
6.5
2.0
0.5
1.0
0.5
3.5
0.5
Indicators of Cl(No)
Positive Negative
4.5
6.3
8.0
4.0
3.8
2.0
1.5
1.5
2.3
3.0
4.0
4.0
3.5
0.7
2.2
4.9
6.0
5.2
6.6
1.0
0.0
1.3
0.7
0.3
0.8
2.3
1.0
6.0
3.5
0.5
0.7
1.0
0.5
0.8
1.0
1.1
1.5
1.0
1.3
0.0
1.0
0.5
1.6
2.0
0.8
0.0
1.1
1.4
0.3
0.0
2.3
2.6
2.8
2.0
2.2
1.0
2.0
2.0
Indicators of PO3(No)
Positive
Negative
0.5
1.0
1.0
1.5
1.3
1.0
0.9
0.6
0.3
0.7
0.0
1.0
0.0
0.8
1.1
0.5
0.0
0.5
0.6
1.0
0.0
1.5
0.7
1.0
1.0
1.6
1.0
1.0
1.0
3.0
5.3
6.0
2.0
1.8
1.0
0.6
1.1
2.0
2.3
4.0
3.0
4.0
0.7
2.6
3.7
4.5
5.3
5.6
0.7
0.0
1.3
0.5
0.4
0.8
1.9
0.0
3.5
2.0
Consulting CYPRUS
Habitat Type
Impact
Ellenberg Indicator Values (average)
2260/2190
2260acacia
2270
2270
2270aleppo
0
5-6
0
1-2
1-2
Light (L) Moisture Reaction Nutrient
(F)
(R)
(N)
7.7
3.2
8.2
5.1
8.1
2.6
8.2
5.5
7.6
3.6
8.0
5.2
7.5
2.8
8.0
4.3
7.7
3.1
8.0
5.0
Indicators of Indicators of Indicators of Indicators of
Indicators of
Sand
Drainage
Moisture
Organic
EC(No)
Content (No)
(No)
(No)
Matter(No)
Salt Positi Negat Positi Negat Positi Negat Positi Negat Positi Negative
(S)
ve
ive
ve
ive
ve
ive
ve
ive
ve
1.3
0.0
0.0
0.0
2.0
0.0
0.0
0.0
0.0
1.0
1.0
2.4
1.3
1.7
3.0
0.7
1.3
1.7
2.3
1.0
1.0
2.3
1.4
0.0
3.0
1.0
3.0
3.0
0.0
4.0
0.0
3.0
1.0
1.3
1.0
0.0
2.0
1.0
0.0
1.0
1.0
0.0
0.0
2.0
1.6
0.7
3.0
2.0
1.0
1.0
1.0
4.7
0.7
0.3
2.7
Indicators of Cl(No)
Positive Negative
0.0
1.0
2.0
0.0
0.3
1.0
3.3
3.0
3.0
2.7
Indicators of PO3(No)
Positive
Negative
2.0
2.0
1.0
2.0
1.0
1.0
0.3
2.0
0.0
1.0
Consulting CYPRUS
The flora of Akrotiri peninsula has not been studied in detail, however there is a
considerable amount of data in Meikle (1977, 1985), in the “Additions to the Flora of
Cyprus” (Hand 2000-2006) and in the study of the orchid flora by Kreutz (2004).
There has yet been no published comprehensive list of the flora.
The ecological quality elements usually used for the evaluation of the flora of an area
are:
· biodiversity indices at the level of species (as those cited for the habitats) applied
at the level of the whole region (γ-diversity), or estimated as mean diversity of
habitat level (α-diversity) or as species turnover among habitats (β-diversity)
· biodiversity indices at higher taxonomic levels (genus, family)
· chorological spectra and numbers of endemic plants or native versus alien
(introduced) plants
· functional attribute spectra, using attributes such as the life cycle, growth form and
life form (the most commonly used), Grime’s CSR strategy, dispersal mode etc.
· numbers and conservation status of threatened plants
The application of most of the above indices requires the knowledge of the total flora.
While their interpretation and the study of their changes at large time spans provides
valuable insights on the ecology of an area, it is difficult to establish reference
conditions at regional level. Reference conditions at habitat level have accounted for
at the section of the habitats.
The numbers and conservation status of the rare and threatened plants provide a
useful tool for the evaluation of the ecological status of the flora regarding the impact
of anthropogenic disturbance. The conservation status of a species is considered
favourable when:
· The population dynamics of the species indicate that it will survive in its natural
habitat in the long term.
· The range is its natural distribution is not reduced and won’t be reduced in the
foreseable future.
· There is adequately large available habitat for the conervation of the population of
the species in the long term
82
Consulting CYPRUS
Based on the above, the general principles for the reference conditions of the
plants are:
Population size: stable or increasing, larger than the minimum
viable population (MVP)
Distribution range and number of locations and subpopulations:
stable or increasing
Habitat: stable or increasing, high or good ecological status
A general scheme for the assessment of MVP (regarding the total population of a
plant in a region) is presented in Table 11. However, a reliable determination of the
MVP and of the population trends requires long-term or intense short term monitoring
data (see Delipetrou & Andreou 2005). Thus, it is not possile to define definitive
reference conditions neither for the population size nor for the number of locations
without adequate monitoring data.
Table 12: Minimum viable population assessment scheme (Primack 1996)
MVP
50
→
2500
Life cycle:
Perennial
→
Annual
Reproduction system
Self-pollination
→
Cross-pollination
Growth form:
Woody
→
Herb
Fertility:
High
→
Low
Frequent
→
Rare or none
Survival:
High
→
Low
Seed longevity:
High
→
Low
Environmental fluctuation:
Low
→
High
Vegetation succession:
Climax
→
Pioneer
staged
Production
units:
of
reproduction
or
not
83
Consulting CYPRUS
For the area of Akrotiri, Tsintides et al. (2007) identified 26 threatened plants (IUCN
categories VU, EN, CR); 1 probaly regionally extinct plant (IUCN category RE?); 1
nearly threatened plant (IUCN category NT) and one rare but of inadequate data for
the characterisation of its conservation status plant (IUCN category DD). During a
recent (2011) SBA survey, one more threatened in Cyprus plant was found in
Akrotiri, Silene maritime var. kotschyi.
The available data for these plants for the Peninsula of Akrotiri regarding the general
reference conditions, i.e. population size, number of locations and habitat are
presented in Table 13. An approximation of the possible minimum viable population
(MVP) has been made by applying the standards of table 5 and the available data for
the plants. According to this, a total of nine threatened plants currently have a
regional population that is lower than the MVP in Akrotiri Peninsula: all the critically
endangered plants and another three species, namely Herniaria hemistemon, Phyla
nodiflora, and Serapias parviflora. It should however be stressed that this is not a
definite estimation, all the more since the current population sizes are in most cases
based on a single count.
The distribution range is illustrated in Figure 4 for 5 plants and their locations are
included in the attached shapefile Akrotiri_RDB plants.shp (source Forestry
Department of Cyprus, data for Tsintides et al. 2007). New data for the distribution of
some of these plants have been mapped by a recent (2011) SBA survey. Additional
location data can be found in the releve database compiled by Christodoulou (2003)
and Hadjichampis (2005) (under permission of the authors).
The presented MVP, number of locations and distribution range can be
considered as working reference conditions for the population of the 30 plants.
Regarding their habitats, the reference conditions coincide with the reference
conditions of the habitats (for the plants that occur in natural habitats).
84
Consulting CYPRUS
IUCN
cate gory
Taxon
endemic
Table 13: List and current data for 30 rare and threatened plants in Akrotiri Peninsula (Data Tsintides et al. 2007).
No
location
s/
stands
Populatio
n Size
MVP
Vegetation class
>250
Ammophiletea
ammophilous
2110
>500
Thero-Brachypodietea:
Malcolmietalia?
Isoeto-Littoreletea
ammophilous
2240/2230
Achillea
maritima
subsp. maritima
Aegilops bicornis
VU
1
VU
2
Baldellia
ranunculoides
Cistanche phelypaea
Cladium mariscus
RE?
CR
VU
1
8
3
5000-10000
Convolvulus lineatus
VU
8
2000
Coronilla
repanda
subsp. repanda
Crypsis factorovskyi
VU
21
9000-12000
VU
17
5000
Herniaria hemistemon
Ipomoea imperati
Ipomoea sagittata
VU
EN
CR
1
2
3
100-150
<1000
20
>500
>250
Isolepis cernua
Juncus littoralis
Juncus maritimus
EN
VU
VU
11
4
6
>500
>2000
>500
Linum maritimum
Lotus cytisoides
VU
EN
12
35
Mentha aquatica
VU
4
<600
Habitats in
which
Characteris
tc
Vegetatio
n group
>250
>250
500010000
2000
900012000
5000
Salicornietea fruticosae
PhragmitoMagnocaricetea
Poetea bulbosae/TheroBrachypodietea
Malcolmietalia
Isoeto-Nanojuncetea?
wetland
halophytic
wetland
1420
CY02?
wetland
2110, 2110/2210, 2260
2110/2210,
2240/2230
Fasouri
2190,
2250,
1420
CY02?
5420?
dry grassland
ammophilous
Habitats in Akrotiri
Peninsula
2230
1310?,
3170
>500
2000
500
Ammophiletea
Galio-Urticetea:
Calystegion sepium
Isoeto-Nanojuncetea
Juncetea maritimi
Juncetea maritimi
dry grassland
ammophilous
wetland/synan
htropic
wetland
halophilous
halophytic
3170
1410
1410
>2000
970
2000
970
Juncetea maritimi
Crithmo-taticetea
halophytic
aerohaline
1410
1240
700
700
PhragmitoMagnocaricetea/MolinioArrhenatheretea
wetland
6420
2110
2230,
2240,
2260,
2270aleppo
1310?, 3170?, CY02 in
acacia invasion
5420 very open and dry
2110, 1210-Taraxacum
CY02 in acacia invasion,
6420?
3170 in Eucalyptus plantation
1410
1410, 1420, 1430, 2190,
2110
1410, CY02
2110,
1430,
2190,
2190/2240, 2250, 2260
6420, CY02?
Consulting CYPRUS
IUCN
cate gory
Ophrys kotschyi
Orchis palustris*
Pancratium
maritimum
Phyla nodiflora
Saccharum strictum
Scirpus
lacustris
subsp.
tabernaemontani
Serapias aphroditae
endemic
Taxon
+
VU
CR
NT
8
2
4
>500
10-20
500
>250
>250
VU
DD
EN
2
14
1
<400
150-200
>500
>250
>250
VU
1
52
>250
dry grassland
CR
1
25
>250
VU
11
dry to humid
grassland
aerohaline?
VU
5
VU
CR
4
1
+
Serapias parviflora
Taraxacum
aphrogenes
Triplachne nitens
Urtica membranacea
Vulpia brevis
No
location
s/
stands
+
Populatio
n Size
Habitats in
which
Characteris
tc
Habitats in Akrotiri
Peninsula
MVP
Vegetation class
Vegetatio
n group
Molinio-Arrhenatheretea
Ammophiletea
wetland
ammophilous
6420
2110
5420, 5212 openings
6420
2110, 1430, 2260
Isoeto-Nanojuncetea
wetland
wetland
wetland
3170
6420?
CY02
6420?, 14010?, 2190?
6420, ?92D0
CY02 (Fasouri), 6420?
>250
Crithmo-Staticetea?
500-1000
1000
2000-2300
150
2000
Cutandietalia maritimae
Galio-Urticetea
Malcomietalia?/Cutandie
talia?
ammophilous
synanthropic
ammophilous
Wetland?,
olive
5420?, thin 9540?
Thin 9540
grove?,
1210
1210 on single and pebble
2230,
2240
2230, 2240, 2250, 2260
2230?,
2240?
6420 margins? (Fasouri)
2230?, 2240?, 2250?
*Data for the second location: Christodoulos Makris 2011, personall communication. The plant was rediscovered in May 2011, 1.5 km from the single
previously known location (1-3 individuals).
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Figure 33: Distribution range of 5 threatend plants in Akrotiri Peninsula.
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5
Model
Conceptualization
and
Definition
of
Monitoring objectives
Below is a brief description of the project area conceptualization which has been
constructed for the purposes of defining the monitoring objectives. In particular the
conceptualisation sets the geographic boundaries, the ecological characteristics and
the physical parameters that should be monitored in order to provide relevant and
timely information to the management plan of the area.
5.1
Geographic scope
The project concerns the formulation of a monitoring plan for the Akrotiri Peninsula
wetland complex, which comprises of the Akrotiri salt lake, the Zakaki Marsh and the
Fasouri Marsh (Figure 7, Chapter 3.2) As described below, land use within the
Akrotiri Peninsula can affect the water balance of the wetlands but can also have a
direct impact on the ecological status of the area and should be considered in the
monitoring plan.
At the same time it is noted that water practices concerning abstraction and irrigation
within the Kourris river catchment and especially downstream of the Kourris dam can
also affect the water balance and water quality in the Akrotiri Peninsula as river flows
and the groundwater flows from the Akrotiri aquifer feed the wetlands. Water sources
also include sections of the Western urban area of Limassol, the storm water of
which drains to the Zakaki Marsh. Lastly, it is expected that urban sewerage flows
from Akrotiri village may end up into the salt lake. As these sources, however, cannot
be controlled through the Akrotiri Peninsula Management Plan they are treated in this
study as boundary conditions.
5.2
Hydrological network / water sources
As described in chapter 4, the hydrological network is comprised by three main water
bodies, with the Akrotiri salt lake, being the major one. It is also the final area to
which the whole catchment of the area directs its water to.
The following topological map (Figure 31) clearly represents the water flow.
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Figure 34: Conceptual model of the hydrology of the project area
Key features of the Akrotyri Peneynsula are presented in Appendix I, Maps 03 & 04.
5.3
Land use, water uses and pollutant sources to be considered
The surroundings of the project area are mainly used for agricultural purposes as
also support a small number of farming units. It also has military uses and several
military installations are preset with various projects (e.g. the Pluto project) being built
inside the study area.
A detailed analysis of abstraction and recharge rates is outside the scope of this
report. It must however be considered that the water balance of the Akrotiri aquifer is
at present negative as a result of abstraction, reduced flows after the construction of
the Kourris Dam, and a reduction in average annual rainfall over the last years. The
aquifer is believed to be hydraulically connected to the Fasouri Marsh (SCP
Feasibility report (Iakovides 1982). In this case, the groundwater level in the aquifer
will be directly influencing the presence of water in the marsh. Maintaining
appropriate water levels in the aquifer is therefore an important issue of concern. The
Marsh also receives rain water runoff as well as irrigation return flows from upstream
agricultural land.
Sewerage flows from Akrotiri village as well as dispersed developments are disposed
of in septic tanks and thus are a potential source of pollutant flows into the salt lake.
In accordance with the Akrotiri Peninsula Environmental Management Plan (March
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2011) the restaurants situated at Lady’s Mile are equipped with sub-standard
systems.
Zakaki Marsh receives significant amounts of storm water from the western urban
areas of Limassol, which in turn feeds into the Salt Lake. From the project research it
was concluded that there are no historical data on the water quality of storm waters
entering the salt lake. The project has undertaken monitoring of the water quality of
the incoming water within the scope of the present project. Though limited in number
the collected data can provide indications of water quality issues as well as can
constitute a basis for future monitoring activities.
In addition to the abovementioned human influences, the Peninsula supports a large
range of activities including leisure visits, off road driving, dog walking, hunting and
others. Such activities cause various types of disturbances and direct impacts on
land such as habitat degradation, noise, dust and erosion/ siltation. The presence of
a very dense network of dirt roads causes fragmentation of the area’s habitats.
Vehicle movements on dirt roads also results in direct kills of reptiles (Akrotiri
Peninsula Environmental Management Plan, March 2011). Off road racing is
reported by the above study to have had a direct impact on habitats 2260, 5420,
1420, 1210, 2110, 2250 and 2120.
Harvesting of wild plants is a common occurrence in the Akrotiri area. As reported by
the above study, picking of Cladium mariscus, Juncus littoralis and Juncus maritimus
is common.
5.4
Management Goals and Objectives
Several
parameters
such
as
physical,
chemical,
hydromorphological
or
physicochemical can have an effect, positive or negative on aquatic communities.
Some can have both positive and negative, depending on how intense the influence
becomes. For instance nutrients such as nitrogen and phosphorus tend to be limiting
resources in standing water bodies. Therefore, slight increase in concentrations,
tends to result in positive effects such as increased productivity, abundance and
diversity. However if nutrients are in excess, eutrophication effects occur with shifts in
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communities’ structure and dynamics, reduction of diversity and in extreme cases,
anoxic events.
Besides nutrients, a crucial factor in the case of Akrotiri wetlands is obviously the
water regime. Water levels have decreased the last decades due to construction of
dams but also due to intensive agriculture that results in over pumping of the aquifer.
Decreased freshwater quantities flowing into the area, resolve in the reduction of
waterbodies size and elevation of salinity values. The latter also occurs from the
saline intrusion caused by aquifer overexploitation. Reduction of inflows and the
subsequence lowering of water level increases suitable growth zones for reeds
intensifying their aggressive expansion. Reedbeds expansion can limit free water
surface and eventually cover the whole area.
Agricultural activities, besides nutrients leakage, create adverse effects by excessive
use of pesticides and insecticides which in turn have negative effects on biotic
components. Furthermore, ABATE, an organophosphorous insecticide used by SBA
to control mosquito populations, is reported to be non-selective and affecting aquatic
communities (Sanders et al. 1981, Frost & Sinniah 1982). Therefore, a more
selective method should be used for this purpose.
Activities such as cattle grazing or inflow of untreated urban stormwater, increase
organic loads in waterbodies. This can lead to eutrophic phenomena and
accumulation of organic matter which in the long term results in anoxic sediment
conditions and in some cases, dystrophic crises. Moreover such effects can increase
water turbidity which also affects communities, by limiting light penetration in the
water column and consequently reducing primary productivity.
In addition to organic loads, untreated storm water can be a source of heavy metals.
Military activities, illegal hunting, waste dumping and vehicle trespassing in the
wetland can also be considered as potential sources of heavy metals. High
concentrations in the aquatic environment can become a severe thread for aquatic
life and if the problem insists, heavy metals can reach toxic levels and eventually
affect the whole ecosystem. Such substances bioaccumulate in estuarine wetlands,
causing deformities, cancers, and death in aquatic animals and their terrestrial
predators. Heavy metal ingestion by benthic organisms (including many shellfish) in
estuarine wetlands occurs because the metals bind to the sediments or the
suspended solids that such organisms feed on or settle on the substrate where such
organisms live. Therefore bioaccumulation or accumulation in the sediments
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introduces heavy metals in the food web and by this path, can become a thread for
human life.
Finally communities can be affected by habitat loss and degradation, caused by land
reclamation. Wetlands close to areas under development are facing urbanization
pressures that results in encroachment of the wetland and limitation in available
natural resources for communities.
In accordance with the Akrotiri Wetlands Water Level Management Plan (March,
2009) the management objectives should be as follows:
·
Ground water flows to the Fasouri Marsh should be sufficient to create shallow
surface water flooding in the Marsh area. Water depth at the sluice should be
between defined limits throughout the autumn and winter November – April
(dates and depths at sluice to be determined based on data obtained from the
WDD/Sewage Board).
·
Ground water flows to the Zakaki marsh should be sufficient to maintain up to
40cm of surface water in the vicinity of the saw-sedge fen throughout the winter.
·
Combined surface and ground water flows to the Salt Lake should be sufficient to
ensure the Salt Lake contains open water by end October in any year (extent and
limits of variation to be determined from existing data sources based upon flows
over 10 year period 1990 - 2000).
·
Salinity levels in the Salt Lake should be maintained within limits (winter low and
summer high levels) determined from data provided by the Forestry Service.
·
Information on surface and ground water levels and water quality should be
regularly collated by the SBAA to monitor if objectives are being met.
·
Action should be taken in conjunction with the Republic of Cyprus to ensure water
levels and quality are maintained within defined limits.
In addition to the considering the above management goals, the project team
considers vital that the mobnitoring plan can support the following additional
management goals:
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5.5
Proposed management objectives in relation to Branchinella and
Aphanius
Based on the information provided in the Nature Conservation Component Plan, the
proposed management objectives in relation to Important Conservation Features [i.e.
Important Invertebrates [Phallocryptus (Branchinella) spinosa], Important Fish
(Aphanius fasciatus), and Important Ecological Role (both)] include:
·
Updating of available Phallocryptus and Aphanius data
·
Assessment of status Phallocryptus and Aphanius in the Salt Lake and marshes
To retain a favourable conservation status of natural habitats (marshes for Aphanius,
Salt Lake for Phallocryptus) and population size for Phallocryptus and Aphanius
5.6
Proposed management objectives in relation to birds
Based on the information provided in the Nature Conservation Component Plan, the
proposed management objectives in relation to birds include:
·
Updating of available bird data
·
Possible revision of designated (Ramsar and SPA) site boundaries
·
Assessment of status of Cyprus Warbler (Sylvia melanothorax) and Eurasian
Thick-knee (Burhinus oedicnemus) in designated SPAs
·
To retain a favourable conservation status of natural habitats and population
size for breeding bird species listed in Table 1, bearing in mind the possible
future inclusion of Cyprus Warbler (Sylvia melanothorax) and Eurasian Thickknee (Burhinus oedicnemus) in the species list.
·
To retain a favorable conservation status of natural habitats and population size
for wintering and migrating groups of raptors, cranes and water birds, including
species listed in Table 1, bearing in mind the possible future inclusion of Cyprus
Warbler (Sylvia melanothorax) and Eurasian Thick-knee (Burhinus oedicnemus)
in the species list.
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6
Reference Conditions
6.1
Defining the Akrotiri wetland character
For many decades there has been a confusion concerning the coastal wetlands of
Cyprus (Larnaca salt lake and Akrotiri wetland), whether they should be considered
as saline lakes or transitional waters. Water Framework Directive 2000/60/EC
defines transitional waters as ‘’bodies of surface water in the vicinity of river mouths
which are partly saline in character as a result of their proximity to coastal waters but
which are substantially influenced by freshwater flows’’ (figure 32).
The definition of the main characteristics of Transitional water bodies is:
1. "...in the vicinity of a river mouth" meaning close to the end of a river where it
mixes with coastal waters;
2. "...partly saline in character” meaning that there is an evident gradient in salinity
values;
3. "...substantially influenced by freshwater flow" meaning that freshwater flows
occur, mixing with coastal waters.
Figure 35: Characterization of waterbodies according to WFD 2000/60/EC
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Moreover Biodiversity Action Plans define lagoons as “areas of shallow, coastal salt
water which are wholly or partially separated from the sea by sandbanks, shingle or,
less frequently, rocks or other hard substrata. They retain a proportion of their water
at low tide and may develop as brackish, fully saline or hyper-saline water bodies”.
The term “Saline lake” was incorrectly used for the characterization of Akrotiri
wetland complex, which mostly refers to athalassic salt lakes, met in dry, inland,
closed watersheds (endorheic basins). On the other hand, characteristics of the
wetland such as:
·
Its proximity and interaction with the sea,
·
Its shallow, coastal character
·
The dynamic sedimentary processes affecting the area
·
The freshwater inflows from the northern parts
·
The salinity gradient observed – despite today’s fractured nature - moving from
the northern part towards the sea
·
The historical background of interconnection to the sea and alluvial depositions
mostly from Kouris and Garyllis rivers,
reveals the transitional character of the wetland. Moreover Akrotiri habitats, as well
as Larnaca ¨salt lakes¨, have been declared as Coastal lagoons (1150*) for the
implementation of several European Directives such as Habitats directive
(92/43/EEC) and WFD (2000/60/EC).
However, the construction of Kourris dam and in less degree Polemidia dam in
Garyllis catchment, as well as urban development in the city of Limassol, have
minimized freshwater flows to the lower parts of the rivers that supplied Akrotiri
aquifer. As a consequence Phasouri marsh and the entire wetland accepts
significantly lower quantities of freshwater than the past decades. These human
interventions disrupted the sequence of natural processes taking place for thousands
of years in the ecosystem. Therefore, according to WFD legislation the ecosystem
could be considered as Heavily Modified.
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6.2
Setting of Reference conditions – Typological issues
The ‘’biological reference condition’’ is a description of the biological quality elements
that exist, or would exist, at high status; that is, with no or very minor disturbance
from human activities. The objective of setting reference condition standards is to
enable the assessment of ecological quality against these standards. In defining
biological
reference
conditions,
criteria
for
the
physicochemical
and
hydromorphological quality elements at high status must also be established.
Akrotiri wetland is a mosaic of habitats with different types of biotic communities. It is
clear that salinity, ranging from slightly brackish to hypersaline, is the key factor
controlling the biotic components of the waterbodies, acting as fine‐mesh filter in
selecting potential colonizer species and therefore creating a peculiar ecosystem.
This heterogeneity in water conditions generates multi-habitat biotopes with rare
species and diverse species composition, in a relatively restricted area.
Despite the fact that common typological descriptors have been defined for
stream, lake and coastal areas, a typology for transitional waters has not yet
been defined, and its implementation by the European countries is still under
development (Lucena-Moya et al. 2009). Consequently, although this kind of
wetlands should be fitted in ¨Transitional waters¨, the absence of a well
defined and widely accepted typology for Transitional waters, results in areas
such as Akrotiri wetland -as well as similar waterbodies such as Larnaca
complex- remaining unclassified in any typological scheme. Therefore, no
methods or indices of ecological classification have been developed referring
to such waterbody type, for the implementation of WFD. Nevertheless, attempts
for development of a typology framework are ongoing.
Considering all of the above and since reference conditions are type-specific, no
reference conditions have been established at Mediterranean scale or even
European sale, for any BQE. In these terms no type specific reference
conditions can be recalled or re-created for Akrotiri wetland; only general
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conclusions and suggestions can be made, based on the current knowledge
and expertise.
According to WFD, the approaches for establishing reference conditions include
methods such as:
·
Existing undisturbed sites or sites with only very minor disturbance
·
Historical data and information
·
Use of models
·
Expert judgment
Since there are no similar wetlands or sites in Cyprus such as Akrotiri that can be
considered undisturbed, nor any historical data and information are available, the first
two options are not under consideration. The use of a model can also not be used,
since such models are currently unavailable and the development of such can be
done after extensive and time consuming studies of relevant ecosystems. Therefore
the last option is to use expertise in order to establish as realistic as possible,
reference conditions. To do so, general species ecological preferences can be
considered in relation to the prevailing local conditions.
The wetland is characterized by a strong directional salinity gradient ranging from
freshwater to hypersaline conditions. This highlights the need for classifying the
wetland’s components in different types according to the salinity ranges which as
already said, is the key factor for the ecosystem’s processes. This is considered
necessary since changes in salinity affect spatial and temporal aquatic communities’
composition. A similar approach has been already successfully investigated in other
Mediterranean countries (Lucena-Moya et al. 2009).
Such discrimination can well be applied between Fasouri marshes and Zakaki Lake
on the one hand and Akrotiri Salt Lake on the other. According to the available data,
as well as data recorded from field surveys in the context of the current project,
salinity values differ significantly between these water bodies and aquatic
communities’ composition is expected to differ as well.
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6.2.1
Hydrology
The hydrological conditions of the Akrotiri area have been in constant change in
response to the dynamic nature of its determining factors which are the
meteorological and hydrogeological conditions and human activity. Several man
made interventions have profoundly altered the hydrological conditions of the area in
recent years. The construction of the Kourris dam in 1988 is most likely the most
significant intervention. Other manmade inputs with significant impact include the
prior drying out of the Marsh with the construction of drainage canals and the planting
of Eucalyptus trees, increased storm water inputs to the zakaki Marsh from through
the development of drainage works and increased water abstraction from the Akrotiri
aquifer.
Climate change is another significant factor as storm flows constitute the main source
of water in the Akrotiri wetlands. Reduced annual average rainfall over the last
decades as well changes to rainfall patterns such as rainfall frequency and intensity
produce complex changes to storm water flows which may not be easily assessed or
anticipated.
Considering the above factors it is unclear at present what the appropriate reference
hydrological conditions should be
6.2.2
Macrophytes Reference conditions
Benthic aquatic macrophytes (angiosperms and macroalgae) are key structural and
functional components of some of the most productive ecosystems of the world,
including transitional and coastal waters. As photosynthetic sessile organisms being
at the base of food web, they are vulnerable and adaptive to human and
environmental stress of water and sediment. They respond to aquatic environment
representing reliable indicators of its changes. Extensive studies have provided
mechanistic explanations of their community-environment interactions. For example,
the excess of nutrients in shallow ecosystems shift the species composition from the
angiosperms/late-successional to the dominance of opportunistic and often bloom
forming seaweeds due to rapid growth and colonization ability of the latter, under
abundant nutrient conditions.
Angiosperms and different algal species or functional groups have different nutrient
demands. Therefore changes in nutrient concentration affect dominance patterns of
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benthic vegetation as well as dominance pattern between opportunistic algae and
benthic vegetation. Floating macroalgae (and phytoplankton) are generally favored
by high nutrient concentration. When their biomass increases, depth distribution of
angiosperms and perennial macroalgae decreases due to shading. Consequently,
the absence of rooted angiosperms, turbidity increases creating a feedback effect.
Ultimately benthic plants may completely disappear (Duarte 1995).
The presence of angiosperms and charophytes in macrophyte aquatic communities
as a trademark of good ecosystem quality has been well documented (Orfanidis et al.
2001, Garcia et al. 2009, Falace et al. 2009). On the other hand, opportunistic free
floating macroalgae, are known as rapid colonizers characterized by short life cycles
and high net productivity, resulting in macroalgal blooms which are well known to
reduce habitat quality (Krause Jensen et al. 2007, Odum 1985). These
characteristics of macrophytes and shifts in their communities, from long live/late
successional species to opportunistic species, have been used to develop several
ecological quality indices dealing with water quality (Orfanidis et al. 2001, Falace et
al. 2009, Sfriso et al. 2009).
In this framework, the presence/absence of extended communities of soft sediment
angiosperms/Charophytes and absence or restricted abundance of floating
macroalgae (especially chlorophytes) and epiphyta on angiosperm leaves, can be
used as an indication of healthy aquatic ecosystem in good or high status as
prescribed by WFD 2000/60/EC. On the other hand if angiosperm/Charophyte
communities in waterbodies, are restricted or completely absent and/or beds of
floating macroalgae are extensively recorded, this is a severe indication of a
degraded ecosystem with adverse effects that in extreme cases, could lead to anoxic
events.
As already mentioned, in the absence of pristine sites that could be compared /
attributed as similar to Akrotiri waterbodies, only general considerations can be made
in order to derive reference conditions. Therefore, in the case of Akrotiri wetland,
reference conditions can be considered as the case of extended presence of soft
bottom angiosperms and charophytes in the majority of the area covered with water
and absence or very limited cover (less than 10%) of opportunistic macroalgae.
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6.2.3
Macroinvertebrate Reference conditions
Τhe absence of sufficient data does not allow the derivation of reliable Reference
conditions for macroinvertebrates that can be used as the ideal conditions for the
wetland. In the absence of this information an attempt to re-construct the reference
status can only be done in terms of general guidelines based on current knowledge.
These guidelines have been exported from numerous studies in Europe and USA
and have been applied as a part of indices in wetlands and rivers (Hilsenhoff 1988,
Burton et al. 1999, Buffagni et al. 2006). The majority of invertebrate taxa have been
attributed with tolerance values reflecting to their tolerance in human disturbance
such as nutrient enrichment, organic pollution or habitat degradation. The presence
of intolerant taxa such as Ephemeroptera, Plecoptera and Trichoptera, is of major
importance in defining the ecosystem status. On the contrary, high proportions of
tolerant taxa such as Chironomidae, Culicidae, Oligohaeta and Hirudinea, indicate
severe habitat degradation and need for management measures.
According to their ecological strategies, taxa characterized as filter feeding and
collectors, are abundant in degraded sites based on the assumption that organic
enrichment favorites their feeding habitats. On the other hand, shredders and
scavengers are mostly found in high quality waters. Finally, community descriptors
such as richness and diversity (i.e Shannon Diversity Index) can help in defining
reference conditions. In such pristine sites high species richness and diversity is
anticipated.
In hypersaline waterbodies such as the salt lake, it is possible according to previous
studies (Ortal 1992, Kerrison 2002), that invertebrate communities are depoverate,
with low number of taxa and limited number of individuals. This is caused by high
salinity values which act as environmental pressure creating harsh environment for
invertebrates and do not allow the evaluation of the waterbody using common
macroinvertebrate practices. In this perspective, if the above is finally confirmed,
hypersaline waterbodies could be assessed by using fairy shrimp data in connection
with bird populations.
Macrophyte and Macroinvertebrate Reference Conditions as set can be used as a
tool to briefly evaluate Akrotiri waterbodies status in a superficial way. Nevertheless
it must be highlighted that these are again general remarks that are based on
worldwide trends in aquatic ecosystems. Solid and site-specific reference conditions
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can be set only after detailed and time consuming studies in the area as well as in
similar ecosystems with complete pressure gradient. These studies must include
pressure analysis in the watershed, hydro-morphological alterations, hydrological
state, physicochemical and substrate analysis. Figure 33 shows a generalized model
of the impact status of aquatic communities.
Figure 36: Generalized model of aquatic communities in reference and impacted ponds (Coleman,
2009)
6.2.4
Characterization of the Salt Lake water properties and Phallocryptus
(Branchinella) spinosa population
In order to understand the phenology (seasonal timing of life cycle events) in relation
to of the cysts banks, hatching periods, development and maturation of P. spinosa in
the Lake, it is necessary to characterize the seasonality of the water properties and
to place them in context by comparing the Salt Lake with the one in Larnaka and the
vernal ponds where Phallocryptus is present.
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Water samples for chemical analysis will give us an indication of how particular is the
Akrotiri Salt Lake for the fairy shrimp. While at the vernal ponds of Potamos tou
Liopetriou, Phallocryptus is under extremely different conditions (e.g. low salinity,
abundant predators such as amphibians and possible turbellarians), at the Salt Lake
in Larnaka, the shrimp is at the upper limit of its salinity tolerance. (At the Salt Lake of
Larnaka, Phallocryptus co-occurs with another brine shrimp, Artemia salina [Mura &
Hadjistephanou 1987]). Therefore, it is important to include in any monitoring
program the connection between these environments and the potential exchange of
Phallocryptus mediated by the dispersion from waterfowl (e.g. Charalambidou &
Santamaria 2002, 2005, Ketmaier et al. 2008).
Ketmaier et al. (2008) found that the migratory routes of the greater flamingo, a
species bound to shallow lagoons and salt lakes, almost perfectly overlap with the
distribution of a haplotype of Phallocryptus, including the population of shrimps at the
Larnaka Salt Lake.
Utilizing the data derived from the monitoring program of the Lake by the Fisheries
Department
and
the
information
from
the
Akrotiri
Meteorological
Station
(precipitation), we constructed graphics (Figs. 34, 35) of the seasonal changes in
salinity, temperature and pH which will contribute to the study of the Phallocryptus
populations in the Lake. Ideally, similar seasonal averages should be produced for
the Larnaka Salt Lake in order to study, monitor and compare the anostracans of
both lakes.
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Figure 37: Monthly average and standard deviation of precipitation (Akrotiri Meteorological
Station) and water salinity (data from the Fisheries Department) of the Salt Lake. Averages
derived from the time period 1966-2011 (precipitation) and 1988-2011 (salinity)
Figure 38: Monthly average and standard deviation of water temperature and pH of the Salt
Lake. Averages derived from the time period 1988-2011 (data from the Fisheries Department).
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6.2.5
Reference
conditions
for
Phallocryptus
(Branchinella)
spinosa
population
In the absence of an adequate baseline data and a long-term time series of the
abundance and phenology of P. Spinosa at the Salt Lake or anywhere in Cyprus, it is
difficult to define what is natural, normal or optimal in relation to Phallocryptus.
However, there are two previous descriptions in Ortal (1992) and Kerrison (2002) of
the abundance of Phallocryptus which may serve as a starting point in the efforts to
find realistic reference conditions.
The monthly evaluation of Ortal (1992), even though is the only encompassing the
flooding cycle, is inadequate due to poor description of the methodology and lack of
consistency in the sampling effort (e.g. volume of water, quantity of sweep samples,
duration of sampling). Such deficiency in the description of the methods utilized
prevents any attempt to replicate the study to compare tendencies or temporal trends.
However, it has important information on the environmental parameters during the
Phallocryptus monitoring (Fig. 36).
Figure 39: Abundance (individuals) of Phallocryptus (Branchinella) spinosa in one sampling
station (“Lake-Recorder”, November 1991 to May 1992) at the Akrotiri Salt Lake (data from
Ortal 1992) in relation to water parameters (temperature, salinity, and pH).
On the other hand, the evaluation of Kerrison (2002) was carefully planned and
performed at five stations; however, it was limited to one month. Since this data set
was the result of a proper methodology, it is possible to analyze it statistically (Fig.37).
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An important message from this evaluation is the spatial variability of the abundance
of Phallocryptus suggesting that for any monitoring program, an adequate number of
replicates and stations must be considered in order to increase the robustness of the
analysis.
It is necessary to place both evaluations in a temporal context where the
environmental variables during the studies can be related to the results (Fig. 38).
Both sampling periods were quite distinct in relation to each other: one drier and
more saline than the other (Fig. 39). When all the data is plotted together, the
seasonal variability during the sampling periods and in the long term is evident.
Figure 40: Abundance (mean and standard deviation) of Phallocryptus spinosa in six sampling
stations (PLUTO II, March 2002) at the Akrotiri Salt Lake (data from Kerrison 2002). There are
differences statistically significant between stations, Kruskal-Wallis P=0.0001698, Mann-Whitney
pairwise comparisons (P<0.005): A ≠ B, E, F; B ≠ C, F; C ≠ E; F ≠ E.
One promising method is the evaluation of the cysts banks of Phallocryptus in the
bottom sediments of the Lake. Cysts banks can be considered the archive of the
local habitat, since the pattern of changes in anostracan species assemblage and
genotypes from the past up to the present, would reflect changes due to natural or
anthropogenic impact (Brendonck 1996, Brendonck & De Meester 2003). This
information can be used to reconstruct evolutionary processes or even to restore the
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local habitat (Hulsmans et al. 2006). Failing to consider the relevance of the cysts
bank as an important component of zooplankton communities of the Lake in Akrotiri,
may lead to erroneous interpretations in the analysis of community and potential
population genetic structure of Phallocryptus. For example, in a study comparing the
resting community in the sediments with the active one in the water, the cysts bank
contained more species even though a multi-year sampling project of the water
column was conducted (Moscatello & Bellmonte 2009).
Figure 41: Periods (arrows) when the abundance of Phallocryptus spinosa was studied (Ortal
1992, Kerrison 2002) and monthly averages of water temperature, salinity, and pH of the Salt
Lake (data from the Fisheries Department) and monthly precipitation (Akrotiri Meteorological
Station). Averages derived from three to four monitoring stations during the time period 19882011.
Figure 42: Periods (arrows) when the abundance of Phallocryptus spinosa was studied (Ortal
1992, Kerrison 2002) and monthly averages of water salinity of the Salt Lake (data from the
Fisheries Department) and rainfall monthly anomalies (Akrotiri Meteorological Station). Salinity
averages derived from three to four monitoring stations during the time period 1988-2011.
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Rainfall monthly anomalies were produced by subtracting the long-term average (1966-2011) of a
given month from the total rainfall for that month.
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7
Proposed Monitoring Programme
The following monitoring programme has been structured in line with the predefined
management targets for the Akrotiri Penynsoula wetlands and in accordance with the
area characterisation as defined from the literature and visits undertaken within the
scope of this study.
The water balance and quality monitoring subgroup deals with the physical/abiotic
variables and pollutants that have been found to be of relevance to the quality of the
enbvironement and in particular to the viability of the wetalant ecosysetems and the
preservation of wetland function.
Sampling methodologies follow widely used methods and rely heavily on the use of
specialised laboratories. Especially in the water quality monitoring subgroup, it is
generally specified that filed sampling is undertaken and samples are analysed at
approved laboratories. Sampling can be undertaken by trained technicials or other
scientific personnel. The size of samples and method of storage is not specified in
detail as such direction will be provided by the selected laboratories. Monitoring of
biotic parameters need to be done by specialised and experienced personnel. Clear
training and directions need to be provided personnel
Monitoring of hydrological parameters will help to assess trends in the hydrological
conditions and associated pressures. It is strongly suggested that the proposed
monitored is complemented by modelling or specialised GIS applications. It is also
important that monitoring methods are frequent and systematic in order to facilitate
the identiofiction of trends. In order to enable future modelling activities it is also
suggested that meteorlogical variables are tracked. An hourly temporal resolution is
recommended. The main variables include precipitation, evaporation, wind speed
and direction, water level, bathymetry and water inflows.
Soil and sediments monitoring can help assess the impacts of current practices as
well as provide indication of trends in sedimentation and pollutant buildup. As in the
case of water quality, monitoring will include the analysis of samples at specialised
laboratories.
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7.1
Hydrology
7.1.1
Water balance
In accordance to existing data and studies the water balance of the Akrotiri salt lake
is determined by the following inputs:
·
Surface flows from the Zakaki Marsh
·
Surface flows from the Phasouri Marsh
·
Surface flows from the Eucalyptus forest are
·
Possible (but not verified) ground water flows from the Akrotiri aquifer
·
Surface flows from Akrotiri village
·
Direct rainfall on the salt lake area
·
Occasional seawater inflows
Evaporation constitutes the main water loss mechanism. As already discussed it is
possible that the lake is hydraulically linked to the Akrotiri aquifer. In this case,
ground water outflow to the aquifer may occur in periods when the salt lake water
level is higher than the aquifer water level and at the same time is sufficiently high to
produce northward groundwater flows.
After the evaluation of all the hydrological conditions, the project team members
propose the installation of four flow meters (Figure 43). Note that the two
northeasternmost measurement points are within close proximity and appear as one
point on the following figure.
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Figure 43:Flow measurement locations
Since Zakaki Marsh constantly receives water from the two sewage pipes coming
from the Zakaki urban area as also from the Limassol port, the installation of two flow
meters is proposed.
Water from the Zakaki marsh flows west towards the salt lake. At the location viewed
on figures 44 and 45, the installation of the third flow meter is proposed.
Figure 44:Zakaki and Port flow meters
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Figure 45: Flow measurement locations near Zakaki Marsh
The fourth and final location of a flow meter is proposed at the Pluto project under the
old bridge (Fig 46). The flow meter can operate from Late August until early June,
since during the visit no water was visible.
Figure 46: Flow measurement location near Fasouri Marsh
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During the visit the team noticed that under the current road bridge, there is an
elevation difference between the two road sides, which obstructs the water from
freely flowing towards the salt lake and causes flooding of the area. This situation
should be studied further to decide whether ground works should be undertaken to
facilitate easier water drainage towards the salt lake, or whether the situation should
remain as it is, thus providing another source of surface water to the area. Such
ground works will be connected with the design and construction of a monitoring weir
at the site.
Complementary to water flows it is proposed that the following meteorological
parameters will be monitored. It is suggested that data are collected via continuous
measurement equipment and should provide hourly average values. Existing stations
in the Akrotiri area can be considered to be sufficiently close to the project area and
therefore representative.
·
Precipitation
·
Potential Evapotranspiration
·
Relative humidity
·
Air Temperature
·
Wind speed
·
Solar Radiation
·
Dew point temperature
In addition, the following parameters are considered useful for the assessment of the
water balance of the water bodies and to support hydrological modeling and water
level management.
·
Surface water evaporation at the Akrotiri lake and the Zakaki and Phasouri
marshes.
·
Soil evaporation rates in periods when the lakes are dry
·
Water temperature
The above data can facilitate the assessment of climate change trends as well as
enable the use of hydrological models.
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7.1.2
Water levels
It is proposed that water levels are monitored as follows:
·
Water depth and flooding zone area at the salt lake and in the Fasouri and
Zakaki Marshes
·
Seawater level
·
Ground water level at Akrotiri aquifer. The existing wells can be monitored for
this purpose.
It is proposed that monthly measurements are taken. Water depth should be taken at
the deepest location of each water body. For this purpose it is suggested that
permanent water level meters are installed. The flooding zone can be obtained from
the processing of satellite images.
Hydrology Monitoring Summary Table:
Parameter
Groundwater level
Surface Water depth
Surface water extent
Water flows
· Precipitation
· Potential
Evapotranspiration
· Relative humidity
· Air Temperature
· Wind speed
· Solar Radiation
· Dew point temperature
Monitoring
Method
Well depth
monitoring
Fixed staff gauge
GIS processing of
satellite imagery
or field generated
GPS locations of
flooded
boundaries
Calibrated weirs
Fixed
Meteorological
station
Monitoring locations
At all existing wells already
monitored
· At the instream flow meter
locations (Fig. 40)
· At the deepest part of the salt
lake
· At the deepest part of the
Fasouri Marsh
· At the deepest part of the
Zakaki Marsh
· Seawater level
· Akrotiri salt lake
· Fasouri Marsh
· Zakaki Marsh
As indicated on Fig. 40.
Existing SBA Meteorlogical
Stations
Monitoring
Frequency
Annual
Monthly
Monthly
Monthly
Hourly /
daily
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7.1.3
Water Quality
It is suggested that the full range of the water quality parameters presented below
are monitored in all four water bodies for a period of two years in order to establish a
comparable
database
and
common
framework
for
interpretation.
Monthly
measurements of water quality parameters and annual measurements of sediment
parameters are to be taken during this period. Sediment measurements should be
taken in early April of each year. In accordance with the results, a more targeted set
of monitoring parameters will be able to be determined for each water body.
It is proposed that water quality monitoring is undertaken at the four locations where
water flow monitoring is proposed. One measurement station should also be
established in each of the Zakaki and Phasouri Marshes. It is proposed that sampling
is undertaken in the vicinity of the deepest area. It is however noted that access
difficulties may necessitate the sampling ad shallower locations. Lastly, a minimum of
four measurement points are proposed for the Akrotiri salt lake. Three stations
should be placed at the northwest, northeast and southeast sections to capture the
influence of the inputs from the Zakaki marsh, Phasouri marsh and Akrotiri village,
respectively. The stations should be at sufficient depths to enable sampling for the
longest possible period of the year. An additional station will be placed at the deepest
section of the salt lake.
Samples should be kept cold (4oC) and dark until processing is possible. Processing
should be undertaken as soon as possible after sampling, on the same day as
collection. Water samples should not be stored with other samples of high nutrient
content e.g. sediments. With regard to analytical quality assurance, the laboratory
should use techniques which are consistent with HMSO Blue Book methods (The
Standing Committee of Analysts) or other proved methods and should have high
standards of accuracy and precision, good sensitivity, and in the case of TP,
preferably a limit of detection of 1.0 μg P l-1. Measurement of pH should be
undertaken in the laboratory, with a calibrated and accurate bench-top meter and
probe. Alkalinity should be measured by titration of the sample with hydrochloric acid,
to a pH 4.5 end point, using an indicator solution.
Sampling campaigns should be systematic and documented. At each sampling
campaign standardized data should be collected. A sample field data form is
presented below.
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Monitoring form
Date of visit: ……………………………………………..
Location Name : ……………………………………………………………………………..
Name of Surveyor: …………………………………………………………………………..
GPS location: ……………………………………
MAP indicating location of monitoring
Background information at time of monitoring (hour of day)
Rainfall
Intense, moderate to light, none
Temperature
_____ oC
Wind
Strong, light, none
Cloudcover
cloudy, partially cloudy, sunny
Water depth
(cm)
Turbitity
clear, turbit
Level of activity of flamingos in
the vicinity of the monitored area
Heavy, light, none
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Water Quality Monitoring Summary Table
Parameter
BOD, e-coli, enterococci
Nutrients (NO2, NO3, NH4,
PO4, Total P), NH3, TOC
DO
·
·
·
·
·
·
Lead, Mercury, Nickel,
Cadmium
pH, T
EC, Salinity
Pesticide residues:
organophosphorous,
organochlorine,
carbamate, Sub-Urea,
Triazine) Insecticides
Turbidity, suspended
solids, dissolved solids
Alkalinity
Chloride salinity
Monitoring
Method
Field
sampling.
Analysis at
approved
laboratory
Field
sampling.
Analysis at
approved
laboratory
At
approved
laboratory
Monitoring
Frequency
Monthly
At the deepest section of the Akrotiri
salt lake, Fasouri Marsh, Zakaki
Marsh and Agios Georgios pond.
At the stream flow monitoring
locations (Gig. 40)
Akrotiri Aquifer
Monthly
Anual
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Sediment Quality Monitoring Summary Table:
Parameter
Monitoring
Method
Monitoring
Frequency
· Content of sand, clay and
organic matter
· Permeability1
Field
At the deepest section of the Akrotiri
· TP, TKN
sampling.
salt lake, Fasouri Marsh, Zakaki
· Lead, Mercury,
Analysis at
Marsh and Agios Georgios pond.
approved
At the stream flow monitoring
laboratory
locations (Gig. 40)
Nickel,Cadmium
· pH
3- Monthly
· Pesticide residues
1
Since the salt lake is characterized by the present of a marl substrate of depth in the order of 10m, the
usefulness of monitoring this psrameter needs to be reassessed and perhaps replaced.
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7.2
Flora and habidats monitoring
The vegetation and habitat types of the area of Akrotiri Peninsula were described and
mapped at a scale of 1:50 000 in 1999-2000 (Hadjikyriakou et al. 2000) and in 2009
by Cox et al. (Jonathan Cox 2009). In addition, the halophytic and sand dune
vegetation were studied in the 1980s (Arnold et al. 1984, Costa et al. 1984) and later
in more detail including an assessment of the conservation status by Hadjichambis
(2005). The aquatic vegetation has been studied in the framework of the application
of the Water Directive 2000/60 and there is data on the benthic vegetation of
transitional waters (Christia et al. 2011). Finally, the impact of the invasion of Acacia
saligna in the area of Akrotiri was studied by Christodoulou (2003).
The first habitat map (Hadjikyriakou et al. 2000) was based on aerial photos and
topographic maps, was constructed at a scale of 1:50,000 and then digitised. It was
made after extensive field survey in 1998-2000 and is accompanied by a detailed
description of the habitats. Habitat coding was made according to the Annex I Dir.
92/43 habitat codes and, for those habitats not included in the Annex, according to
the draft Cyprus codes used in the BioCyprus database for the Natura 2000 sites.
The second map (Cox et al. 2009) is large scaled and was apparently based on a
georeferenced satellite image and constructed by GIS. It was made after quite
extensive field survey and is accompanied by a less detailed habitat description.
Habitats were coded according to the EUNIS system and according to the Annex I
habitat codes. Both studies and maps are of good quality. However, the datasets are
not compatible, not only due to technical reasons and the different time of
construction (2000-2009), but also apparently due to different habitat identification by
the authors. Moreover, the detailed relevé survey data and community identification
by Christodoulou (2003) and Hadjichambis (2005) have not been used in either study.
A list of the habitats identified in the vegetation Akrotiri by the above sources and
during field work is provided in Table 14.
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Table 14: Habitats identified in Akrotiri peninsula. Map 2000: Hadjikyriakou et al. 2000; Map
2009: Cox et al. 2009.
Vegetation
Habitat name
Group
Coastal lagoons
Salt
lake/lagoon
Sand
Dune &
Shingle
Coastal
rocks
Annex I
EUNIS
Map
code
code
2000
1150* C1.51, A2.2 +
Map
2009
+
Notes
Annual vegetation of drift lines
Vegetation of single or pebble beach
with Taraxacum aphrogenes
Embryonic shifting dunes
White dunes
Dune-slack pools
1210
1210
B1.1, B2.13 +
B2.13, B2.3 + (as
2110
2120
2190
+
+
+
+
+
+
Grey dunes
2210
B1.31
B1.32
B1.81, ?B1.
85
B1.4
-
-
Malcolmietalia dune grasslands
Brachypodietalia dune grasslands
Coastal dunes with Juniperus spp.
2230
2240
2250*
B1.48
B1.47
B1.63
+
+
+
-
Dune sclerophyllous scrubs
Vegetated
sea
cliffs
of
the
Mediterranean
coasts
with
angiosperms
Salicornia
and
other
annuals
colonizing mud and sand
Mediterranean
salt
meadows
(Juncetalia maritimi)
Mediterranean and thermo-Atlantic
halophilous scrubs
Halo-nitrophilous scrubs (PeganoSalsoletea)
2260
1240
B1.6, B1.64
B3.331
+
+
+
+
1310
+
-
+
+
1420
A2.51,
A2.55
A2.532,
A2.522
A2.526
+
+
1430
F6.82
-
+
Southern riparian galleries and
thickets (Nerio-Tamaricetea)
Reedbeds
and
sedgebeds
(Phragmition
australis,
Scirpion
maritimi)
92D0
F9.31
+
-
C3.21.
C3.23
+
+
BioCyprus
code CY02
Saccharum ravennae communties
C3.31
-
+
Arundo donax beds
C3.32
-
+
BioCyprus
code CY17
BioCyprus
code CY17
Doubtful
presence of
the habitat,
in Akrotiri it
corresponds
to
Chara
beds
in
saline water
(C1.512)
Doubtful
presence of
the habitat in
Fasouri
+
-
1210a)
1410
The
presence of
the
habitat
needs
confirmation
+ (including
5210 invaded
by pine)
Halophytic
Wetland
Hard oligo-mesotrophic waters with
benthic vegetation of chara formations
?3140
C1.14,
C1.25
+
-
Oligotrophic to mesotrophic standing
waters
withvegetation
of
the
Littorelletea uniflorae
?3130
C3.4, C3.5
-
-
Freshwater
Wetland
The
presence of
the
habitat
needs
confirmation
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Vegetation
Group
Habitat name
Annex I
EUNIS
code
code
Mediterranean temporary ponds
3170 C3.42
Mediterranean
tall
humid
herb
6420 E3.1
grasslands
of
the
MolinioHoloschoenion
Cladium
Calcareous
fens
with
mariscus and species of the Caricion
davallianae
Arborescent matorral with Juniperus
spp.
Thermo- Sarcopoterium spinosum phryganas
Mediterran Olea and Ceratonia forests
ean Shrub
& Forest
Grassland
Map
2009
+
Notes
The
presence of
the
habitat
needs
confirmation
7210
C3.28
-
+
5210
F5.1321
+
+
5420
9320
F7.34
F5.1, F5.5
+
+
+
+ (as oleolentisc
brush/matorral)
Mediterranean pine forests with
endemic Mesogean pines
East Mediterranean xeric grasslands
Asphodel fields
Subnitrophilous annual grassland
(synanthropic grassland)
Native pine plantations (Pinus brutia)
Exotic conifer plantations (including
Pinus halepensis)
Highly
artificial
vegetation Other evergreen broadleaved tree
plantations (Acacia saligna)
Eucalyptus plantations
7.2.1
Map
2000
+
9540
G3.75
+
+
6220*
E1.33
E1.C1
+
-
+
+
E1.6
-
+
G3.F12
G3.F2
?
?
+ (mainly as
BioCyprus
code CY08
BioCyprus
code CY14
pine forest
9540)
G2.83
+
+
G2.81
+
+
Aims and objectives of Monitoring – General Methodology
Habitats - Vegetation
The main aim of habitat monitoring is the assessment of the ecological status in
order to ensure that high and good quality status is retained where it has been
recorded and in order to decide whether and what measures should be taken in the
cases of less than good ecological status (surveillance monitoring). The available
data on halophytic and dune habitats have allowed for the proposal of reference
values, ecological quality indices, and bioindicator species. However, these values
and indices need to be confirmed. Also, the deviations of the observed values from
the reference values (EQR) for the characterisation of the status of a habitat as less
than high quality need to be determined. On the other hand, there is a lack of data on
the vulnerable fresh water habitats which, moreover, do not include species which
are used as bioindicators in other European countries, except from Phragmites
australis. Due to the above, an initial more intense monitoring scheme is
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recommended for at least two monitoring sessions. This scheme should incorporate
the assessment of positive and negative impacts and of abiotic parameters,
especially and in the fresh water ecosystems. In addition, all the ecosystems of the
site offer habitat to a significant number of threatened plant species for the survival of
which habitat conservation is essential. So habitat monitoring should incorporate, as
much as possible, the particular habitats of these species.
The landscape of the area of Akrotiri is complex and dominated by the wetlands and
the transition from the wetland to the non-wetland habitats and from high to minor
disturbance sites. The larger part of the site consists of an inner dunal ecosystem, an
halophytic ecosystem and a fresh water ecosystem which are related by the factor of
the water and their spatial distribution transition zones depend on annual and
seasonal changes in water level and salinity. The coastal dunal ecosystem is
apparently mostly influenced by the deposition of sand from the sea, related to winds,
sea currents and topography but there are large areas of transition to the halophytic
wetllands. Those ecosystems which include azonal habitats, i.e. not related to the
altitudinal vegetation zonation, neighbour elevated areas with thermo-Mediterranean
shrub ecosystems, and there is again a narrow transition zone. Agricultural
ecosystems and cultivations are concentrated at the south of Alyki. However,
anthropogenic disturbance is widespread throughout the site and there are also large
areas with plantations of naturalised acacias, eucalypt and Pinus halepensis and
semi-natural Pinus brutia forest interspersed within the natural ecosystems.
Monitoring at landscape level requires monitoring of the distribution and range of the
habitats and ecosystems and area is also a good indicator of the conservation status
of a habitat. The existing habitat maps are either too small scaled (Hadjikyriakou et
al. 2000) for the assessment of small area and small width habitats or missing
habitats (Hadjikyriakou et al. 2000, Cox et al. 2009). Most importantly they are not
compatible and differ in the identification of the plant communities and the
interpretation of the coding systems. However, both contain important information.
Thus, the construction of a large scale habitat map (e.g., 1:1000 or 1:5000) based
on a revision of all the available data is necessary for monitoring the distribution and
range of the habitat.
The ecological status assessment requires collection of the data necessary to
determine the biodiversity and floristic composistion indices, including the abundance
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of bioindicator species, which define the reference conditions. So, the assessment of
the floristic composition of the habitats is the main monitoring parameter. This
should be combined with recording of abiotic parameters and threats so as to
enable the statistical evaluation of their influence on the plant community data. The
selection of abiotic parameters for the halophytic and sand dune habitats is indicated
by those factors that have been identified as significant for the determination of their
floristic composition.
The characteristics of the landscape indicate the method of monitoring for the
collection of bioindicator data and for the in-depth assessment of the ecological
status. Monitoring in transects is certainly indicated for all the habitats of the fresh
water and halophytic wetlands and for the dunes since they develop in zones which
depend on the abiotic factors of water and sea. Moreover, the patchy distribution of
disturbances and especially of the impact of plantations, justify the method of
transects for the thermo-Mediterranean shrub habitats as well. Separate quadrats
would only be indicated for the extended and relatively undisturbed coastal juniper
shrubs on the shoutheast and southwest part of the site. Further, the transects
should be combined with quadrats in order to better illustrate the succession of plant
communities and their quality. This combination obtains better results regarding the
biodiversity indices and the floristic composition indices which are essential in habitat
monitoring and define the reference conditions.
The selection of the locations of the transects needs to be made so as to cover:
· All the natural habitat types occurring in the area of Akrotiri, especially the
protected and the wetland ones. The different community types recorded in each
habitat and the need of more detailed study of certain fresh water communities
should also be taken into account.
· The variation range of the basic abiotic parameters influencing the habitats, that is
water level, salinity, distance from sea, substrate.
· The range of the degrees and types of the main anthropogenic disturbances, so
as to monitor habitats in the whole range of ecological status classes.
· The habitats of the threatened plants recorded in the area.
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Finally, regarding the frequency of monitoring, vegetation is a good but slow
reacting index of environmental conditions. Annual monitoring is not necessary and a
period of three years is the generally proposed minimum for vegetation assessment
at habitat and ecosystem level. At landscape level, a decade should be adequate for
the update of habitat mapping.
7.2.2
Flora
Monitoring of the total flora of Akrotiri Peninsula is incorporated in habitat monitoring,
since the results will produce a measure of both á-diversity and â-diversity in the
monitored habitats.
The main aim of the monitoring of a threatened species is to assess whether its
population in a region is viable. This entails population viability analysis (PVA) by:
a) long-term(for at least 10 years, with indicative results in 6 years) monitoring using
a diffusion approximation model or b) short term (for at least 3 years) intensive
monitoring using modelling at stages or metapopulation models (Dennis et al. 1991,
Brigham & Thomson 2003). Both approaches are time and resource demanding. The
former approach is generally simpler. The latter approach is more complex and
requires drawing up a separate study for each plant including the application of
preliminary monitoring. In the framework of the monitoring of a region with 29
threatened plant species such as Akrotiri Peninsula, maybe the effort is justified only
for the 8 species identified as apparently having a population lower than the MVP
(Table 6). Moreover, the use of the simpler diffusion approximation model which
simply demands population counts of the species, not necessarily in consecutive
years, is proposed as the monitoring method for the critically endangered species.
The possibly extinct (status RE?) Baldellia ranunculoides which was last observed in
Fasouri marsh in 1997, should be searched for.
The distribution range of the species and the number of locations and
subspopulations (sensu IUCN 2008) as well as the conservation status and area of
its habitat are two important parameters. Their monitoring cannot produce a viability
analysis but it can indicate whether the population of the species is faring well or not
and whether measures for its conservation are demanded. So, operationally they can
be used for the assessment of the conservation status of a species. Moreover, the
distribution of all the threatened species has been recorded and can be used as a
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base for monitoring. The parameter of habitat status and area is largely covered by
the general habitat monitoring. Thus, distribution mapping is proposed for the 27
threatened species (status VU, EN, CR) and for the two not threatened but nearly or
possibly so (status NT and DD). Further, the possibly regionally extinct species
Baldellia ranunculoides and the endangered species Cynanchum acutum which may
have gone extinct from the area of Akrotiri should be searched for annually.
According to the above, the following general monitoring plan is proposed:
Monitoring Objectives
· Assessment of ecological status at landscape level
· Assessment of ecological status at habitat level.
· Developement of classification scheme for the ecological status at habitat
level.
· Assessment of the conservation status of threatened species
· Assessment of the habitats of threatened species.
Monitoring parameters
1. Area of habitats (update of habitat map).
2. Floristic composition of habitats at transects.
3. Recording of threats at the locations of the transects.
4. Assessment of abiotic parameters: water level, soil moisture and electric
conductivity at transects. Additional parameters (optional: soil sand/silt/clay
content, organic matter, total N, total P, CL-)
5. Number of locations and distribution range of the threatened (status VU, EN,
CR) and near or possibly threatened (status NT, DD) species.
6. Population size of the species having a population lower than the MVP.
Duration of monitoring:
6 years with the proposed scheme
20 – 30 years in total
Transects at 3 year intervals
Mapping at 9 year intevals
Analysis of Results:
every 6 years
Update of monitoring plan:
6 years
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7.2.3
Monitoring plan - Habitat mapping
Mapping of all natural and artificial habitats (including various land uses, such as
habitations, agricultural cultivations, roads) in the whole site of Akrotiri.
Maps to be produced by Geographic Information System (GIS) technology with the
use of satellite images and with the help of Global Positioning System (GPS). Map
scale should be at least 1:5000 – 1:15000 for various land uses (agricultural areas,
habitations etc.) and shrub and forest habitats and at least 1:1000 – 1:5000 for the
halophytic and fresh water wetland , the sand dune habitats and grasslands.
All habitats (including land uses) to be coded according to the EUNIS system
(http://eunis.eea.europa.eu/habitats.jsp) and according to the Annex I habitat codes,
where applicable. The identification of the vegetation type and the assignement to a
particular code for each polygon or for a group of polygons with similar vegetation
units will be supported by sampling, i.e. recording of the typical species or of all the
species, as necessary for each habitat type. Mapping polygons may include only one
habitat or two habitats (mixed polygons). The latter case may arise when mapping of
two habitat types in separate polygons is not possible because they occur in a
mosaic form, as it sometimes happens with the annual communities of habitat 1310
among halophytic scrub (1420) or with dry grasslands (6220) in shrub openings
(5420 or 5210). An Annex I habitat identification guide for Cyprus as well as detailed
instructions for mixed polygons and for minimum size polygons for each habitat are
provided in Delipetrou & Christodoulou (2010).
The GIS database of the polygons will include at least the fields listed in Annex I.a.
Samplings will be recorded in a customised TURBOVEG database (see data
digitisation and analysis in vegetation transects below). Sampling points and other
points of interest should be recorded in separate GIS files along with TURBOVEG
releve numbers and notes, as necessary. The GPS coordinates of the sampling
points and points of interest will be downloaded from the GPS to a PC and not written
down during field work in order to avoid mistakes.
Equipment
· Printed satellite photo of the area to be surveyed (scale 1:2000 Þ 1:5000) with the
borders of the polygons of the habitat map made by Cox et al. (2009).
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· It helpful for the field work to mark points for guidance and points of interest in the
GIS map and download them to the GPS in order to check them on site.
· Printed sampling forms (Annex I.b) and notes forms (Annex I.c). Alternatively the
notes can be recorded in a digital recorder.
· GPS device, fine highlight marker, photographic and/or video camera, binoculars,
plastic bags and tags for plant samples.
Field Survey
The field team should include a habitat specialist for at least some of the visits. It is
advisable to hold 1 – 2 training sessions for the personnel who will perform the
mapping.
On site habitat identification and confirmation or correction of the polygons of the
existing map. The demarcation of new polygons and corrections should be drawn on
the satellite image on site.
For each polygon or group of neighbouring polygons, record the characteristic
species and dominant species in the sampling form. Sampling should be made at all
different vegetation units. Assignment of each vegetation unit to a habitat type is not
necessary to be done on site. However, if there is doubt regarding the habitat type it
is advisable to perform a full phytosociological sampling (recording of all species in
appropriate sized quadrates).
.Frequency
Detailed mapping of land uses: once
Update of natural habitat mapping: every 10 – 12 years
Season:
Late summer (July – August) for most of the halophytic, fresh water
wetland and dune habitats. Visits in spring may be necessary for the
identification of habitats 2230, 2240 and in autumn (October) for the
identification of habitat 1310. Also, visits in late spring or early summer
may be necessary for the identification of some fresh water wetland
species and for 3170 species.
Spring (April) for the shrub and forest habitats and for the dry
grasslands.
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7.2.4
Monitoring plan - Vegetation Transects
Subjective selection of the location of 20 – 30 permanent transects of a length of 100
– 300 m. The specifications in section I should be taken into account. Proposed
transect locations are shown in figure 5 (attached shapefile diatomes_1.shp).
Additional transect locations may have to be selected based on the results of
mapping.
The selected transects include the habitat types 1210, 1310, 1410, 1420, 1430,
2110, 2190, 2230, 2240, 2250, 2260, 3170, 5420, 5210, 6420, CY02 with
representatives of 2 – 3 community types per habitat, at anthropogenic pressure level
of none or minor to high, throughout the area of Akrotiri, but mainly in wetlands and
sand dunes. They also cover 19 threatened plant species and several endemics, but
not all the locations of these plants. The localisation of the transects was made using
the existing mapping data (habitat map, threatened species’ maps, releve points,
field work) and a satellite image. The locations of several of the transects were
confirmed on site. The locations of the rest of the transects should be confirmed and
re-adjasted on site. The attributes of each proposed transect are presented in Table
8.The final number of transects should be decided upon after careful assessment of
the feasibility of this work regarding the effort and expenses.
Figure 47: Location of 35 transects (yellow lines). Black triangles: species with threat category
EN, VU, DD, and NT. Blue stars: species with threat category CR.
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Table 15: Attributes of the proposed transects.
name
T1
T2
confirmed
Habitats
*
yes
CY02/6420
yes
CY02/6420
T3
T4
T5
T6
T7
T8
T9
T10
yes
yes
T11
T12
T13
yes
yes
T14
T15
T16
T17
T18
T19
T20
T21
T22
T23
T24
yes
T25
yes
T26
yes
T27
T28
T29
Impacts/Threats
Red Data Book Plants
moderate to high Mentha aquatica
moderate to high Mentha aquatica, Scirpus
lacustris, Linum maritimum,
Baldellia
CY02/6420, ?3140
moderate to high
1420/acacia
high
Juncus maritimus
acacia, CY02, ?7210
moderate to high Orchis palustris
CY02, acacia, 1420
moderate to high Linum maritimum
CY02/6420, Arundo beds
moderate to high Saccharum strictum
CY02, acacia, 1420, 7210
moderate to high Cladium mariscus, Crypsis
factorovskyi, Isolepis cernua
3170, CY02/Saccharum beds moderate to high Isolepis cernua,
1410, 5420, 5212
moderate
Ophrys kotschyi, Coronilla
repanda
?1150, 1210a, ?1419,
moderate
Taraxacum aphrogenes
2260/5420
1210, 2110, 1420, ?1150
minor to high
Achillea maritima
1210, 2110, 1420, ?1410
minor to
moderate
?2110, 5420/2260, 2250
minor to
Pancratium maritimum, Coronilla
moderate
repanda
5212, 9540
minor to
moderate
2240, 2250, 5420, 6220
minor to
Coronilla repanda
moderate
5212, 6220
minor to
moderate
5212, 6220
minor to none
5210, 5420
minor to
Vulpia brevis
moderate
5210, 6210
moderate to high Convolvulus lineatus
5420, 5212
moderate to high Herniaria hemistemon
1210, 2110, 2230, 2250
minor to
Pancratium maritimum
moderate
1210, 2110, 2250, acacia
moderate to high Triplachne nitens
1410, 1420, 5420, pine
moderate to high Ophrys kotschyi, Serapias
plantation
aphroditae
?1310, 1410, 1420,
minor to
Juncus littoralis
2260/5420
moderate
1310, 1420
minor to
moderate
1310, 1410, 1420
minor to none
?1410, 1420, ?1430
moderate
Lotus cytisoides, Aegilops
(Lycium), 2240, 2260/5420
bicornis
?1410, 1420, 1430 (Lycium), minor to
2260/5420
moderate
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name
T30
T31
T32
confirmed
Habitats
*
yes
1210, 1420, 2110, 2260
yes
yes
T33
T34
T35
Impacts/Threats
2110, 1430, 1410, 1420
2110, 1150, 1420, 2260
moderate to
high? to minor
minor to high
moderate to high
1310, 1420, 2260?
1310, 1420
CY02, 1420
minor to high
moderate to high
moderate to high
Red Data Book Plants
Cistanche phelipaea, Juncus
maritimus
Pancratium maritimum
Silene maritima var. kotschyi,
?Lotus cytisoides
* “yes” is noted for the transects whose exact locations have been confirmed in the field.
Equipment
· Printed sampling forms (Annex II.a). Lists of species encountered in similar
habitats and/or of the most frequent species of the habitats may be included in
printed forms after the first surveys.
· GPS device, photographic and/or video camera, plastic bags and tags for plant
samples
· Wooden (or other material) poles, tape measure, rope for the establishment of
transects
Field survey
The transects will be divided into zones of different habitat types. Square shaped
quadrats 5 – 10 m2 will be placed along the transects every 5 – 20 m2 (figure 6). The
distance between consecutive quadrats depends on the succesion of habitat zones
and in general should not be larger than the width of the habitat with the narrowest
zone. Quadrats should be spaced evenly at each habitat zone but the distance may
change from one zone to another so as not to place one quadrate into two different
zones
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Figure 48: Diagram of transect and quadrats.
The size of the quadrats at each case depends on the habitat type but should remain
stable for each transect. In general, a side of 5 m is adequate for habitats 1210,
1310, 1410, 2190, 2230, 2240, 3170, 6420, CY02, and a side of 10 m is necessary
for habitats 2110, 2250, 2260, 5420, 5210. It is necessary to keep the same size of
quadrats at each transect and at each habitat type.
On site establishment of transects will be made by locating the start and end of the
transect by a GPS. The start and the end of the transects will be marked by
permanent poles. During sampling, a line (rope or tape measure) between the poles
will mark the transect. The first quadrat should be placed at the start of the transect.
Use additional tape measures or wooden sticks for marking each quadrat. The first
quadrat of transects in coastal dunes should be placed at the first vegetation zone
from the sea (usually habitat type 1210 or 2110).
At each quadrat the following should be recorded:
· Total plant and plant cover and cover per vegetation layer.
· All the plant species and their cover-abundance using the 9grade Braun-Blanquet
scale.
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· All types of disturbance.
· Altitude, slope, aspect, geological substrate. Altritude changes between quadrats
should also be recorded.
· Threats that can be identified by direct observation or by reliable information
should be recorded. Such threats identified at the area of Akrotiri are waste
disposal, foot and vehicle trumbling, habitat fragmentation by roads or buldings,
grazing, intentional (management) or accidental fire, tar deposition, sand
extraction, harvesting of plants. An objective scale of 1 – 3 or 1 – 5 should be
devised for these threats, depending on their frequency and/or cover in the area of
the transects. Alternatively, presence/absence can be recorded but this is fact
weakens the use of this data in the subsequent analysis of the results.
· Special notes for the status of threatened species (e.g., phenological stage, signs
of consumption, etc.).
Further instructions for sampling:
· Printed forms for data recording.
· The forms with the raw data must be stored (they can be scanned) even after
digitisation of the data, at least until the analysis of the results.
· Field teams should include at least 2 persons, at least one of them experienced in
this work.
· The correct season for sampling is very important so as not to miss the
characteristic and indicator species of each habitat. Because transects include
several different habitats, timing requirements may be reconciled with visits before
or after the transect sampling for species survey and identification.
Data digitisation and analysis
The sampling data will be recorded in a customised TURBOVEG© 1998-2009
Stephan Hennekens database. Data digitisation in word processor or spreadsheets is
not suggested because it is bound to be plagued by high frequency of mistakes and it
does not facilitate data analysis.
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GPS points of the transect locations will be downloaded from the GPS to a PC and
stored in GIS files.
Data analysis can be made by any statistical software. The use of software packages
specially adapted for vegetation data such as CANOCO is suggested.
Frequency Every 3 years.
Season:
Habitat types 5420, 5210: mid March to early April
Habitat types 2230, 2240, 2250, 2260, 3170: May (visit may be
necessary for species’ identification in April)
Habitat types 1210, 2110: May to early June
Habitat types 1410, 1420, 2190: late June to July
Habitat type 6420: end July to August
Habitat type 1310: October
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7.2.5
Monitoring of abiotic parameters
The abiotic parameters that should be measured preferably at all transects of the
halophytic and fresh water wetland habitats are water level (water depth), soil
moisture and electric conductivity. The two latter parameters should also be
measured at sand dune habitats. Additional parameters that can be estimated are
soil , sand/silt/clay content content, organic matter, total N, total P, and Cl-.
Samplings should be made as necessary when conditions along the transect change,
so that these parameters will be known for each quadrat.
The data will be recorded in sampling forms on site or downloaded, depending on the
device type (form Annex II.b).
These measurements can be combined with the general water monitoring
measurements. In case measuring is not feasible for all transects, a selection should
be made in order to cover adequately the variation of these parameters in the site.
Water depth (WD)
· Water level can be measured by installing a water level gauge (either purchased
or made by hand) at the deepest point of the transect. Installation should be done
by a topographer. Otherwise, there are permanent recording devices and also
hand-held laser marked meters.
· In case a gauge or a hand-held device are used, readings should be made at least
monthly during the flooding period at most 2 days after rain. In any case, the
length of the part of the transect which is flooded should be checked monthly.
Soil moisture (SM)
· A soil moisture probe is used. Since the transects are long, continuous
measurement devices are not practical.
· Ideally, measurements should be made monthly at the non-flooded part of the
transects.
Electric Conductivity (EC)
· An electric conductivity sensor for water is used for flooded sites and a sensor for
soil is used for non-flooded sites. There are sensors measuring simultaneously
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SM and EC.
· Ideally, measurements should be made monthly at the non-flooded part of the
transects.
Frequency monthly (ideally) every 3 years for the first 6 years of monitoring
Afterwards the measurements of the general water monitoring should
be adequate.
Season:
WD and water EC are measured only during the flooding period and SM
and soil EC are measured at the non-flooded parts of the transects.
7.2.6
Distribution mapping of threatened species
Distribution mapping consists in checking the known locations of the 30 species
(Table 6) and recording the limits of the population at each location by GPS. The
points will be used for producing occupation area polygons in GIS maps.
The plants should also be searched for in neighbouring locations with suitable
habitat.
· On site data will be recorded in printed forms (Annex III.a)
· The field team should include at least one person capable of identifying the plants
with certainty.
Frequency annualy (ideally) or every 3 – 6 years
Season:
flowering and/or fruiting season (depending on when the plant is
identifiable).
7.2.7
Population size of species having a population lower than the MVP
The targeted species are: Cistanche phelypaea, Herniaria hemistemon, Ipomoea
saggitata,
Orchis
palustris,
Phyla
nodiflora,
Scirpus
lacustris
subsp.
tabernaemontani, Serapias aphroditae, Serapias parviflora, Vulpia brevis.
The population size of all these species is very small (Table 6) and direct population
counts are indicated at all the known locations. The plants should also be searched
for in neighbouring locations with suitable habitat.
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The population size unit is the number of adult individuals. This unit can be used in
all the above species, except in Scirpus lacustris subsp. tabernaemontani. This
species forms tufts and it may be difficult to separate individuals from clones, so the
population unit can be the number of visibly separated tufts.
· On site data will be recorded in printed forms (Annex III.b)
· Wooden frames of 1x1 m2 for short grasslands, i.e. grasslands with Herniaria
hemistemon, Vulpia brevis, may be useful in counting the plants.
· The delimitation of consecutive corridors with lines is helpful in all grasslands,
especially for tall grassland species such as Scirpus lacustris subsp.
tabernaemontani.
· The field team should include at least one person capable of identifying the plants
with certainty.
Frequency annualy (ideally) for 10 years
Season:
flowering and/or fruiting season (depending on when the plant is
identifiable).
Figure 49: Orchis palustris, plant and habitat in Akrotiri (14/5/2011).
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7.3
Fauna
7.3.1
Proposed
monitoring
objectives
and
indicators
in
relation
to
Phallocryptus
Objective: To ensure the stability of the Phallocryptus population in the Salt Lake
·
Indicator 1: Weekly monitoring to study the phenology (e.g. abundance, size
classes, proportion sexes, maturity) of Phallocryptus in relation to the Salt Lake’s
seasonality.
·
Where: Ideally, the same four stations in the Lake used by the Fisheries
Department. That will allow the comparison of the Phallocryptus data with the
environmental variables. One station is not enough due to significant variations
(standard deviations) of the measured parameters (Fig. 44). Alternatively, two
stations of the Fisheries Department and stations 6-8 proposed in section 7.3.6
Aquatic Macroinvertebrates, Table 16, to monitor biotic components.
Figure 50: Standard deviation of monthly averages (three to four stations) of water
salinity, pH and temperature of the Akrotiri Salt Lake (data from the Fisheries
Department). Arrows indicate the sampling periods when the abundance of
Phallocryptus was studied (Ortal 1992, Kerrison 2002).
·
How:
Following the methods described in Kerrison (2002). Sweep samples
collected with a standard hand net of 0.35m x 0.25m frame size, net depth 0.3m
and mesh 1mm, five replicate samples per station with 1m sweeps, net mouth
“just” below the water. Determine the water volume sampled according to the
above specifications (net size and depth, 1m sweep), which should be 315 litres.
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Specimens should be preserved according to Ortal (1992): In the field with
formalin (40% aqueous solution of formaldehyde). The formalin needs to be
neutralized by using Sodium bicarbonate. In the laboratory, samples should be
transferred to 70% alcohol solution.
·
Data format: Data base with (1) number of Phallocryptus in each sample, (2)
mean for each station derived from the five replicates, (3) density of individuals
calculated as the mean/water volume (individuals/l), (4) development and
maturity stage of specimens by sample.
·
Samples for ID: Since different species of fairy shrimps can be present in the
Lake and surrounding ponds and they might be active for a few weeks, a
selection of collected individuals need to be sent to Anostracan taxonomists for
further identification.
·
Indicator 2: Assessment of the cysts bank of Phallocryptus at the end of Spring
or the flooding/evaporating cycle.
·
Where: Ideally, the same four stations in the Lake used by the Fisheries
Department. Alternatively, two stations of the Fisheries Department and stations
6-8 proposed in section 7.3.6 Aquatic Macroinvertebrates, Table 16, to monitor
biotic components.
·
How: Following the methods described in Kerrison (2002), Moura et al. (2001)
and Hulsmans et al. (2006). Bottom sediment should be collected when the Lake
and ponds are dry using a simple core sampler made from PVC pipe (50cm long,
internal diameter 10cm, two plugs or cups of the same material). The total
surface sediment area would be 0.0079m2. Five replicate samples (cores) should
be collected from each station, producing a total of 0.0393m2 sampled surface.
The core sampler should penetrate the sediment down to a depth of at least
2.5cm (Mura et al. 2001, cited in Maffei et al. 2002). In the laboratory, cysts need
to be isolated from the sediment by a series of sonification, centrifugation, sieving
and filtration. The suggested protocol is a combination of methods discussed in
Hulsmans et al. (2006): Initial filtration (48-50 μm sieve) followed by sonification
(2-3min), second filtration (48-50 μm sieve), centrifugation (3000 rpm) in a 1:1
sucrose distilled water solution for 3min, and final filtration of supernatant through
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a 50 μm sieve. The remaining material needs to be transferred to petri-dishes
with tap water and the counting of cysts done under a microscope or high
magnification stereoscope.
·
Data format: Data base with (1) number of Phallocryptus’ cysts in each sample,
(2) mean for each station derived from the five replicates, (3) density of cysts per
station calculated as the mean/area (cysts/m2).
·
Samples for ID: Since different species of fairy shrimps can be present in the
Lake and surrounding ponds and they might be active for a few weeks, a
selection of collected cysts and other material, such as exuvia (e.g. Beladjal &
Mertens 2003), needs to be sent to Anostracan taxonomists for further
identification by means of scanning electronic microscopy (SEM).
7.3.2
Proposed bird monitoring programme
Whereas a number of surveys currently being carried out at Akrotiri Peninsula
provide a wealth of information (Table 16), it is crucial that the methods being used
and the recording of data become standardized. Standardization of data and
calculation of indexes of breeding and non-breeding bird populations facilitates
comparisons between years and sites. The following suggestions are based on two
sets of guidelines. One is ‘Bird Census Techniques’ outlined by Bibby et al. (1992).
The development of standard census forms for recording data for each type of bird
survey would greatly enhance the standardization of data collection, and may also be
used by volunteers. The second one is the ‘Common Standards Monitoring guidance
for birds’ (JNCC 2004). This provides guidance on the identification of attributes,
targets and methods of assessment for birds.
Table 16: Bird Survey Schemes
Scheme
Wetland bird survey
counts
Migrating
Demoiselle Crane
Organiser
Data
Monthly counts of
Game Fund
waterbirds at wetland
areas
Game Fund
Annual counts of
migrating Demoiselle
Geographical
Scope
Up to 20 wetlands
in Cyprus
Akrotiri Peninsula
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Scheme
Organiser
Census
Data
Geographical
Scope
Cranes in AugustSeptember
Black-winged Stilt
Breeding Survey
Kentish Plover
Breeding Survey
Game Fund
Game Fund
Raptor Migration
BirdLife
Census
Cyprus
Eleonora’s Falcon
Breeding Survey
SBAA
Annual breeding
Akrotiri Peninsula
surveys
Oroklini Lake
Annual breeding
Akrotiri Peninsula
surveys
Larnaca Salt Lake
Annual counts of
migrating raptors
Akrotiri Peninsula
during autumn
Annual breeding
Akrotiri and
survey
Episkopi sea cliffs
Griffon Vulture
Forestry
Annual breeding
Akrotiri and
Breeding Survey
Department
survey
Episkopi sea cliffs
When designing a monitoring programme, this should be based on the conservation
objectives for birds at the designated sites. In our case, these should be outlined in
the Management Plan for Akrotiri Peninsula.
The attribute tables in this report targets that should be used to aid in monitoring
whether conservation objectives are being met for particular bird species or bird
assemblage at Akrotiri Peninsula. For each bird species or assemblage, the table
identifies those attributes that must be measured, known as mandatory attributes, in
order to gather the necessary information for judging the condition of the bird species
or assemblage. Against each attribute are the details of targets to be met.
7.4
Distribution studies
Distribution studies specify where birds do and do not occur. As a result of available
data on the birds that frequent the terrestrial part of Akrotiri Peninsula, including its
wetlands and coastal area, the distribution ranges of most species found on the
Peninsula are known. Distribution maps have been drawn both from systematic and
casual records. However, it is possible that a lack of standardization of data
collection over a number of years may result in the maps also reflecting the
distribution of observer effort as much as the distribution of birds.
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Overall, more systematic and standardized data collection on distributions of species
is necessary, particularly for species which are data deficient such as the Cyprus
Warbler and the Eurasian Thick-knee. The mapped presence or absence of species
may be recorded in specified areas of equal size, e.g. by map units ranging between
2 or 10 km squares. Various kinds of counts might be based on separate and
recognized areas so that results can be expressed as maps of relative density as
well as tabulation of numbers (Bibby et al. 1992).
7.5
Population monitoring
Trends in bird population numbers over time are of particular interest to nature
conservation. Some bird species, for instance the Demoiselle Crane and the RedFooted Falcon, are inherently rare and in need of surveillance. However, more
detailed monitoring of common species such as the Common Coot and Common
Moorhen is recommended as an integral part of a comprehensive monitoring
programme for the area. Common birds are reliable candidates for recognizing
trends and adverse effects on sites, such as pesticides, pollution or drought. The
Spur-winged Lapwing for example, is a good candidate for monitoring habitats known
to be changing, such as Zakaki and Fassouri wetlands.
It is important to bear in mind that population numbers of birds also fluctuate
naturally, usually because of the effects of weather on reproduction and survival, but
also because of the density-dependent effects of population level itself. An essential
attribute of a successful monitoring scheme is the ability to understand such
fluctuations and to distinguish them with those attributable to human beings (Baillie
1990). Therefore, the fluctuations due to weather or population level need to be
measured with some confidence if they are to be recognized. Importantly, monitoring
of populations and demographic rates provides information not only on the status of
species but also on their response to management objectives. The study of various
factors, such as the extent of habitat management, recreational disturbance,
conservation management, effects of military training, etc, may identify improved
conservation measures.
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In Tables, the targets for bird population size are set according to two approaches:
known natural fluctuation at the site level for a species, and a generic threshold
system. Wherever possible, known natural fluctuation should be adopted as the
means for target setting as it will provide a more appropriate level of sensitivity for
rarer species.
·
Known natural fluctuation – to derive population size targets from known
fluctuation a minimum of five counts, each from a different relevant season, is
required - these do not need to be from consecutive seasons, but should be from
within a period of no more than 7 years. Ideally the counts should be from the
time of designation of the feature – when the feature was known to be in
favourable condition. If data are not available from the time of designation the first
suitable series of good quality data should be used, or the generic threshold
approach should be adopted. The minimum population size recorded during the
five counts can be taken as the target for maintaining the population – if the
population at assessment (taken from either a single count or a mean of counts)
falls below this size then it is in unfavourable condition. When data from five
years are not available to set the target the generic threshold approach must be
used. Care should be taken in using natural fluctuation, as there may be cases
where the fluctuation seen in a population is the result of non-natural phenomena,
for example the effects of human disturbance. In cases where there is some
doubt as to whether observed fluctuation is natural then the generic threshold
approach should be used.
·
The generic threshold approach is widely used to assess the conservation
status of individual bird species and to guide the setting of conservation priorities.
The adoption of this system at the site level is a robust way of defining a common
and easily used standard. A simple threshold system works by comparing
population sizes at different times and deriving the change (expressed as a
proportion of the initial population). If this change represents an absolute loss of
25%, or more, of a breeding population or 50%, or more, of a non-breeding
population then the feature will be in unfavourable condition.
7.6
Monitoring migrating and over-wintering birds
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Migrating raptors
Akrotiri Peninsula including ‘Akrotiri Salt Lake, Phasouri Marsh, citrus groves,
vineyards and areas with high maquis’ has been identified as the only watch-site in
Cyprus listed in the Raptor Watch Global Directory (Zalles and Bildstein 2000). The
Directory includes 388 bird of prey-migration watch-sites or hot-spots globally, along
corridors used by migratory birds of prey. Nineteen or 20 species of birds of prey are
listed as regular migrants at Akrotiri Peninsula.
Importantly, one-third of 3,722 raptors recorded in the area during 116 hours of
counts from 21 September to 11 October 1996 appeared to be Red-footed Falcons
(Zalles and Bildstein 2000). Large numbers of this species pass through the area
during their autumn migration in September-October. This falcon uses Akrotiri
Peninsula as a staging site, especially the citrus plantations at the north part of the
peninsula for roosting and occasional hunting. Other than the citrus plantations, birds
can be observed feeding in smaller numbers around Zakaki and Fassouri wetlands.
Table 17: Guidance on mandatory attributes for migrating raptors
Attributes
Targets
Method of
assessment
Comments
Maintain population within
acceptable limits (in this
context population is the
Existing data
total population of an
from Raptor
assemblage):
Bird
♦ The limits of natural
population
fluctuations are not known,
size
maintain the population
above 50% of that
at designation - loss of
50% or more
unacceptable.
Migration Census
Counts or
organized by
estimates of
BirdLife Cyprus
numbers of
since 2006
individuals
Also, counts
made by
birdwatchers
Estimated at 3900-7300
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Attributes
Targets
Method of
assessment
Comments
birds (Iezekiel et al. 2004)
Maintain assemblage
diversity:
♦ If the number of passage
species falls by 25% or
more then the feature is in
Variety of
unfavourable condition
Species
(passage periods are
August to October and
March
Existing data
Record presence /
from Raptor
absence of all
Migration Census
species (not just
organized by
waterbirds) within
BirdLife Cyprus
the site during the
since 2006
relevant periods.
Also, counts
to April).
made by
birdwatchers
Estimated at 13 species of
raptors (Iezekiel et al.
2004)
Maintain the areas of
Akrotiri Salt Lake, Phasouri
Marsh, citrus groves,
Habitat
extent
vineyards and areas with
Record the extent
high maquis, that are used
of all habitat types
by migrating raptors in the
used by
site, within acceptable
the migrating
limits:
raptors, preferably
according to
♦ Extent of all habitats
methods
used by the migrating
recommended in
raptors should be
JNCC (2004).
Some habitat
mapping to date
maintained - losses of 5%
or more of any relevant
habitat type unacceptable.
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Table 18: Guidance on mandatory attributes for the Red-footed Falcon
Attributes
Targets
Method of
assessment
Comments
context population is that
Existing data
of an individual species):
Bird
population
size
above 50% of that
from Raptor
Migration Census
Counts or
organized by
estimates of
BirdLife Cyprus
numbers of
since 2006
individuals
Also, counts
50% or more
made by
unacceptable.
birdwatchers
Estimated at 1000-3000
birds
Maintain assemblage
diversity:
Variety of
Species
Record presence /
absence of all
species (not just
waterbirds) within
the site during the
N/A
relevant periods.
March
to April).
Maintain the area of citrus
Record the extent
Habitat
plantations, Zakaki marsh
Some habitat
extent
and
used by
mapping to date
Fassouri wetland that are
this species,
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Attributes
Targets
Method of
assessment
used by this species in the
preferably
site, within acceptable
according to
limits:
methods
Comments
recommended in
JNCC (2004).
used by this species
should be maintained losses of 5% or more of
any relevant habitat type
unacceptable.
In general, Akrotiri Peninsula is an ideal location for counting migrating raptors.
Concerning the setting up of a systematic monitoring programme, the most complete
migration-route counts are usually made over the entire migration period (Bibby et al.
1992) which in Cyprus starts from the end of August and lasts until mid-November to
the beginning of December (Flint and Stewart 1992). The guidance on mandatory
attributes for migrating raptors and for the Red-footed Falcon are found in Tables 17
and 18.
As part of the Raptor Migration Census taking place in the area since 2006, and
organized by BirdLife Cyprus, systematic data is collected every autumn and spring.
All birds of prey observed from the roof observatory of Akrotiri Environmental
Education and Information Centre, and during patrols to various locations throughout
Akrotiri Peninsula are recorded. Counts are conducted by BirdLife Cyprus staff,
wardens working at Akrotiri Environmental Education and Information Centre, Game
Fund personnel and visiting birdwatchers. In general, the counts take place daily
from the end of August to mid-November, from 8 am to 5 pm. From the vantage point
on the roof observatory, the horizon is scanned from East to North and South and
then vice versa, to locate individuals or flocks of birds of prey that are flying. When
birds are seen to land in certain areas, an observer drives to those areas to record
the exact location and behaviour of the birds. In addition, observers drive along roads
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throughout Akrotiri Peninsula to locate birds that are roosting, hunting or resting, and
that are not observed from the roof observatory (Miltiadou 2008).
The Raptor Migration Census provides a good basis for a long-term raptor monitoring
programme in the area. As a general rule, it is important to consider that for raptor
migration counts it is usually possible for 80-90% of birds to be recorded over 2-3
week windows, when the dates are known for the most important passage times
(Bibby et al. 1992). A suggested improvement on the current scheme is to include
teams of observers consisting of one to three individuals counting birds, plus one
identification checker and one transcriber. Ideally, one observer would count to the
north, one to the south and one overhead, with counts recorded in specific time units.
If there is a wide migration front, it is recommended that teams of observers are
spaced 6-8 km apart, to avoid the likelihood of double counting birds. Suggested
locations include Akrotiri Merra, the Salt Lake, and along the citrus plantations north
of the Salt Lake, and Zakaki and Fassouri wetlands. The exact location of the
counting sites should give the best available view of the centre of bird movement,
and the best possible views of the birds (Bibby et al. 1992). While such locations are
usually areas of higher ground, the roof observatory of Akrotiri Environmental
Education and Information Centre does not necessarily provide the best possible
views of the migrating birds.
Additionally, populations of raptors may also be assessed by counting birds at their
roosting sites (Bibby et al. 1992). A co-ordinated programme of watches of roosts is
recommended at Akrotiri Peninsula, at the eucalyptus forest and citrus plantations
north of the Salt Lake which are suitable roosting habitat for migrating raptors.
Migrating Demoiselle Cranes
Demoiselle Cranes are common passage migrants from late August to early
September (Flint and Stewart 1992). Akrotiri Peninsula is their most important stopover site in Cyprus, and one of the most important in Europe (BirdLife International
2004). It is also a site of international importance for this species which has an
international threshold of 1 to 7 individuals (Wetlands International 2006). The birds
are observed predominantly at Akrotiri Salt Lake, but also at Akrotiri Merra, Fassouri
wetland and Bishop’s pool where they tend to arrive at dusk, and leave early the next
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morning (Charalambidou et al. 2008, Kassinis et al. 2010, SBAA Environment
Department). For this reason, this species is best counted as it flies to or from its
roost sites at dawn or dusk, usually at times of high turnover, when large numbers
occur for just a few days.
The current scheme provides a good basis for a long-term monitoring programme. A
suggested improvement on the scheme should aim for standardization of the census
methods and recording of data. Ideally, teams of one to two observers should survey
the sites with point counts and the ‘look-see’ methodology, whereby an observer
stands in one place, surveys a predefined area with a spotting scope and binoculars
and counts all birds seen and heard (Bibby et al. 1992). The counts should be
conducted at dawn and dusk, on a daily basis, from the third week of August to the
second week of September, to ensure adequate coverage of the migrating
population. Suitable vantage points for the point counts should selected in
cooperation with Game Fund personnel and marked on a map so that the counts are
repeated annually from the same locations. The guidance on mandatory attributes for
migrating Demoiselle Cranes is found in Table 19.
Table 19: Guidance on mandatory attributes for the Demoiselle Crane
Attributes
Targets
Method of
assessment
Comments
Existing data
Bird
population
size
above 50% of that
50% or more
from annual
Counts or
counts organized
estimates of
by Game Fund
numbers of
individuals
Also, counts
made by
birdwatchers
unacceptable.
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Attributes
Targets
Method of
assessment
Comments
Estimated at up to 400
individuals
Maintain assemblage
diversity:
Population
density
Record presence /
absence of all
species (not just
waterbirds) within
the site during the
N/A
relevant periods.
March
to April).
Maintain the area of
Akrotiri Merra, Akrotiri Salt
Habitat
extent
Lake, Fassouri wetland
Record the extent
and Bishop’s pool that are
used by this species in the
used by
site within acceptable
this species,
limits:
preferably
according to
methods
used by the feature should
recommended in
be maintained - losses of
JNCC (2004).
Some habitat
mapping to date
5% or more of any relevant
Wintering Greater Flamingo
The populations of Greater Flamingo are fairly well documented, at least since the
1990s, by Game Fund personnel and birdwatchers. The range of this species is well
known at Akrotiri Peninsula and its whole population can be located with reasonable
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Consulting CYPRUS
confidence. Systematic, monthly, waterbird counts being carried out since 2003 by
the Game Fund, in cooperation with wardens at Akrotiri Environmental Education and
Information Centre, BirdLife Cyprus and birdwatchers (Flint and Stewart 1992,
BirdLife Cyprus 2003-2009, Gordon 2004, Iezekiel et al. 2004, Richardson 20052009, Charalambidou et al. 2008, Kassinis et al. 2010) have provided accurate
population estimates of this species.
Counts are made using point counts and the ‘look-see’ methodology (Bibby et al.
1992). Suitable vantage points selected by Game Fund personnel are used, the
whole surface of the water is scanned slowly and carefully from side to side and all
visible birds are counted. This method is useful when all birds can be easily seen
although there are several ways in which the results can become biased. The most
important are a failure to ensure even effort and coverage between sites or years,
resulting in data that are not comparable. Other factors such as the weather during
the counting, the people undertaking the counts and whether the naked eye,
binoculars or telescopes were used will all influence the accuracy and comparability
of the counts (Bibby et al. 1992).
The current scheme provides a solid basis for a long-term monitoring programme. A
suggested improvement on the scheme should aim for standardization of the census
methods and recording of data. This should include marking of the vantage points on
a map so that the counts can be repeated monthly and annually from the same
locations. The guidance on mandatory attributes for wintering Greater Flamingo is
found in Table 20.
Table 20: Guidance on mandatory attributes for the Greater Flamingo
Attributes
Targets
Method of
assessment
Bird
population
size
Comments
Existing data
Counts or
from monthly,
estimates of
waterbird counts
numbers of
organized by
individuals
Game Fund
♦ Based on the known
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Attributes
Targets
Method of
assessment
Comments
natural fluctuations of the
Also, counts
population in the site,
made by
maintain the population at
birdwatchers
or above the minimum for
the site.
Estimated at 5,000-12,000
birds
Maintain assemblage
diversity:
Population
density
♦ If the number of wintering
Record presence /
absence of all
species (not just
waterbirds) within
the site during the
N/A
relevant periods.
(winter is November to
February).
Maintain the area of the
Salt Lake,
Habitat
extent
saline pools by Lady’s Mile
Record the extent
coast, and Zakaki marsh
that are used by this
used by
species in the site, within
this species,
acceptable limits:
preferably
according to
methods
used by the feature should
recommended in
be maintained - losses of
JNCC (2004).
Some habitat
mapping to date
5% or more of any relevant
Wintering Greater Sandplover and Kentish Plover
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Consulting CYPRUS
The Greater Sandplover uses Akrotiri Peninsula as a staging area during migration,
while some birds choose to overwinter here. All fresh and salt water wetlands and
pools in the area are used by the species as well as the two coasts of the peninsula.
Kentish Plovers are found at Akrotiri Peninsula all year round, with larger numbers
during the winter when birds from northern populations use the area as wintering
grounds. Outside the breeding season, and especially during the summer and
autumn months when the Salt Lake is dry, Kentish Plovers depend largely on small
saline pools near the northern edge of Lady’s Mile coast for foraging.
Table 21: Guidance on mandatory attributes for the Greater Sandplover
Attributes
Targets
Method of
assessment
Comments
Existing data
Bird
population
size
from monthly,
Counts or
estimates of
numbers of
above 50% of that
individuals
waterbird counts
organized by
Game Fund
Also, counts
made by
50% or more
birdwatchers
unacceptable.
Estimated at 5-10 birds
Maintain assemblage
diversity:
Population
density
Record presence /
absence of all
species (not just
waterbirds) within
N/A
the site during the
relevant periods.
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Attributes
Targets
Method of
assessment
Comments
February).
Maintain the area of all
fresh and salt water
Habitat
extent
wetlands and pools that
Record the extent
are used by this species in
the site within acceptable
used by
limits:
this species,
preferably
according to
methods
should be maintained -
recommended in
losses of 5% or more of
JNCC (2004).
Some habitat
mapping to date
unacceptable.
Table 22: Guidance on mandatory attributes for the Kentish Plover
Attributes
Targets
Method of
assessment
Comments
Existing data
from monthly,
Bird
population
size
above 50% of that
Counts or
estimates of
numbers of
individuals
waterbird counts
organized by
Game Fund
Also, counts
made by
50% or more
birdwatchers
unacceptable.
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Attributes
Targets
Method of
assessment
Comments
Estimated at 100-150 birds
Maintain assemblage
diversity:
Record presence /
absence of all
Population
density
species (not just
waterbirds) within
the site during the
relevant periods.
N/A
February).
Maintain the area of all
fresh and salt water
Habitat
extent
wetlands and pools that
Record the extent
are used by this species in
the site within acceptable
used by
limits:
this species,
preferably
according to
methods
should be maintained -
recommended in
losses of 5% or more of
JNCC (2004).
Some habitat
mapping to date
unacceptable.
The migrating and wintering populations of Greater Sandplover and Kentish Plover
are monitored mainly through the monthly, waterbird counts of the Game Fund (Flint
and Stewart 1992, BirdLife Cyprus 2003-2009, Gordon 2004, Iezekiel et al. 2004,
Richardson 2005-2009, Charalambidou et al. 2008, Kassinis et al. 2010). Both these
species, however, are widespread, with suitable habitat located at the fresh and saltwater wetlands and pools at Akrotiri Peninsula. In addition, they are not numerous,
although much higher numbers of Kentish Plover are recorded compared to Greater
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Consulting CYPRUS
Sandplover (Charalambidou et al. 2008, Kassinis et al. 2010). As a result, the current
monitoring scheme does not ensure complete counting of the populations of either
species despite their conservation status (Greater Sandplover: Endangered; Kentish
Plover: Declining; BirdLife International 2004) requiring more careful and effective
population monitoring.
More accurate estimates of the population status of both species are necessary in
order to adequately protect and conserve them. When complete counts of
populations are not possible, samples are required which may then be extrapolated
to estimate population sizes (Bibby et al. 1992). The habitat preferences for roosting
and feeding of both the Greater Sandplover and the Kentish Plover throughout
Akrotiri Peninsula are known. Therefore, random sampling of specified units within
their known distribution range (i.e. 10 km squares) is possible. Proposed surveying
methods are point counts and the ‘look-see’ methodology (Bibby et al. 1992).
Suitable vantage points for the point counts should be selected in cooperation with
Game Fund personnel and marked on a map so that the counts can be repeated
from the same locations. The guidance on mandatory attributes for both these
species are found in Tables 21 and 22.
7.7
Monitoring breeding bird populations
Ferruginous Duck
The Ferruginous Duck is restricted to fresh-water wetlands with adequate
surrounding vegetation. The species prefers fairly shallow expanses of water, rich in
submerged vegetation, and fringed by dense stands of emergent plants. It nests on
anchored floating vegetation or on islands and banks with immediate access to
water. Zakaki and Fassouri wetlands are its two breeding sites. Fassouri is used
when there is adequate standing water, while Zakaki has more availability of water
from storm sewage. The guidance on mandatory attributes for this species is found in
Table 23.
Table 23: Guidance on mandatory attributes for the Ferruginous Duck
Attributes
Targets
Method of
assessment
Comments
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Consulting CYPRUS
Attributes
Targets
Method of
assessment
Comments
Counts of nesting
Maintain population of this
females.
species within acceptable
limits
Counts of off-duty
males.
Bird
Counts of duck
population
broods.
size
above 75% of that at
designation - loss of 25%
At least every 7-14
or more unacceptable.
days during
breeding season,
Population size estimated
March to June
Data consists of
counts of duck
broods observed
during monthly,
waterbird counts
by Game Fund
Also, counts
made by
birdwatchers
at up to 10 pairs.
Maintain density of
breeding birds within
acceptable limits:
Population
density
♦ A decline in the breeding
No estimates to
density of the relevant
date
species of 25% or more is
unacceptable.
Population density of this
species is unknown
The total area of
Zakaki marsh and Fassouri
the relevant habitat
Habitat
wetland that are used by
should be mapped
extent
this species within
using one of or a
acceptable limits:
combination of
No detailed
habitat mapping
to date
techniques
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Attributes
Targets
Method of
assessment
The extent of all habitats
outlined in JNCC
(2004).
Comments
should be maintained.
Losses of 5% or more of
unacceptable
Breeding populations of Aythya duck species are difficult to count as they nest in
dense vegetation and often move their broods to other areas as soon as they hatch.
According to Bibby et al. (1992), three counting methods are commonly used:
(1)
Counts of nesting females. The counting unit is the female with a nest. A
disadvantage of this method is that locating nests involves rigorous searches in
suitable habitat, which is extremely labour intensive and may result in nest
desertion. Consequently it is best avoided unless an efficient line transect
method is developed to count the number of flushed females per unit area.
(2)
Counts of off-duty males. The counting unit is the male duck. The number of
males in small groups are counted just after the females have started to
incubate their eggs and have become highly secretive. Groups of males
counted should comprise fewer than five birds in order to exclude flocks of nonbreeding or later wintering birds.
(3)
Counts of duck broods. The counting unit is the female duck with a young
brood. Counts can be made by direct observation of a site over a designated
period, or by flushing broods onto the open water by walking the banks (with
dogs). Flush counts are generally more successful and quicker than
observations, except on larger or more vegetated waterbodies.
Information on breeding Ferruginous Ducks at Akrotiri Peninsula consists of counts of
duck broods observed during the monthly, waterbird counts of the Game Fund
(Charalambidou et al. 2008, Kassinis et al. 2010) and on other observations (Flint
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Consulting CYPRUS
and Stewart 1992, BirdLife Cyprus 2003-2009, Gordon 2004, Iezekiel et al. 2004,
Richardson 2005-2009). A suggested improvement on the current situation should
aim for standardization of the census methods and recording of data, particularly
when considering the conservation status of this species which is globally Near
Threatened and in Europe evaluated as Vulnerable (BirdLife International 2004).
Ideally, teams of observers should survey Zakaki and Fassouri wetlands at least
every 7 to 14 days during the breeding season, from March to June, to ensure
adequate coverage of the breeding population. The proposed survey method is to
carry out point counts of duck broods from standard locations, as this method causes
the least disturbance to the birds. Suitable vantage points for the point counts should
be selected in cooperation with Game Fund personnel and marked on a map at the
beginning of the breeding season.
Black-winged Stilt and Spur-winged Lapwing
The site is one of the five most important sites in Cyprus for breeding populations of
Black-winged Stilts (Iezekiel et al. 2004). This species is a ground nester and has a
confined breeding area within the peninsula. Its breeding depends on water level and
in some dry years it will choose not to nest at all. Annual breeding surveys of Blackwinged Stilt have been conducted by the Game Fund since 2003 (Kassinis et al.
2010). The transect method, which is generally recommended for surveying breeding
waders (Bibby et al. 1992) is used. Depending on time constraints of staff, one to two
visits are usually organized per breeding season. A suggested improvement on this
scheme should aim for standardization of the census methods and recording of data.
This should include a large scale map of the study site, which is located at Zakaki
wetlands, showing the site boundaries and the locations of nests every year. Suitable
transect routes should be selected every breeding season, in cooperation with Game
Fund personnel and marked on a map, to enable comparable counts to be conducted
on all visits within the season. The monitoring scheme should also include any
breeding Spur-winged Lapwing observed, either at Zakaki or Fassouri wetlands. The
guidance on mandatory attributes for both species are in Tables 24 and 25.
Table 24: Guidance on mandatory attributes for the Black-winged Stilt
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Attributes
Targets
Proposed method
of assessment
Comments
Annual breeding
surveys
conducted by
limits
Game Fund
since 2003
Transect counts
Bird
population
and individuals
size
observed during
monthly,
waterbird counts
Counts of pairs
by Game Fund
at 100-150 pairs
Counts made by
birdwatchers
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
The total area of
Zakaki marsh that are used
Habitat
by this species within
should be mapped
extent
acceptable limits:
using one of or a
combination of
No detailed
habitat mapping
to date
techniques
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Attributes
Targets
Proposed method
of assessment
outlined in JNCC
(2004).
Comments
unacceptable
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Table 25: Guidance on mandatory attributes for the Spur-winged Lapwing
Attributes
Targets
Method of
assessment
Comments
Counts of pairs
limits
and individuals
Transect counts
observed during
Bird
population
waterbird counts
size
by Game Fund
monthly,
Counts made by
birdwatchers
at up to 5 pairs
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
The total area of
Zakaki marsh and Fassouri
Habitat
wetland that are used by
should be mapped
extent
this species within
using one of or a
acceptable limits:
combination of
No detailed
habitat mapping
to date
techniques
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Consulting CYPRUS
outlined in JNCC
(2004).
unacceptable
Three counting visits are recommended, with successive visits conducted at least
one week apart:
Visit 1 – between 1 and 15th April
Visit 2 – between 16th and 30th April
Visit 3 – between 1 and 21st May
Transects should be located between 50 and 200 m apart, depending on the
‘anticipated’ density of breeding birds. All birds should be recorded and marked on
maps. Counting should be conducted between 09.00 and 17.00 hours, as this avoids
the confusing periods of maximal bird activity in the early morning and evening. The
method can be modified either to cover larger areas by using one observer to
traverse transects 200 m apart, and by having less visits during the breeding season
from March to May. Ideally, the transect to be walked should come within 100m of all
points, and scanned 200-400m ahead to check for displaying waders.
The counting unit should be the incubating bird and/or the flying bird (parents)
showing alarm. Counts are recommended when the birds are sitting on eggs, from
late March to late April (Flint and Stewart 1992). At later dates, juveniles, finished and
failed breeders flock and confuse the count (Bibby et al. 1992). Incubating birds are
located by carefully scanning the study area. The mean number of birds recorded
during the recommended period, equates to the maximum number of nests present.
However, the population can be estimated by halving the number of flying birds
recorded on a single survey visit. The maximum of a series of counts made during
the period when most pairs are incubating gives a good estimate of the number of
birds breeding (Green 1985).
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Kentish Plover
The site is one of the two most important sites in Cyprus for breeding populations of
Kentish Plover (Iezekiel et al. 2004). This species is a ground nester and has a
confined breeding area within the peninsula. Salt meadows around the salt lake and
gravel pits with proximity to saline lagoons are used as breeding sites. Annual
breeding surveys of Kentish Plover have been conducted by the Game Fund since
2003 (Kassinis et al. 2010). The transect method, which is generally recommended
for surveying breeding waders (Bibby et al. 1992) is used. Depending on time
constraints of staff, one to two visits are usually organized per breeding season. A
suggested improvement on this scheme should aim for standardization of the census
methods and recording of data. This should include a large scale map of the study
site, which is located at Akrotiri Merra, showing the site boundaries and the locations
of nests every year. Suitable transect routes should be selected every breeding
season, in cooperation with Game Fund personnel and marked on a map, to enable
comparable counts to be conducted on all visits within the season. The guidance on
mandatory attributes for this species is in Table 26.
Table 26: Guidance on mandatory attributes for the Kentish Plover
Attributes
Targets
Method of
assessment
Comments
Annual breeding
surveys
limits
conducted by
Game Fund
Bird
population
size
Transect counts
since 2003
Counts of pairs
and individuals
observed during
monthly,
waterbird counts
by Game Fund
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Attributes
Targets
Method of
assessment
Comments
at up to 150 pairs.
Counts made by
birdwatchers
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
Akrotiri Merra that are used
by this species within
acceptable limits:
Habitat
extent
The total area of
should be mapped
using one of or a
combination of
techniques
No detailed
habitat mapping
to date
outlined in JNCC
(2004).
unacceptable
Three counting visits are recommended, with successive visits conducted at least
one week apart:
Visit 1 – between 1 and 15th April
Visit 2 – between 16th and 30th April
Visit 3 – between 1 and 21st May
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The counting unit is the territorial bird which is best counted when it is incubating
(Parrinder 1989, Prater 1989). The recommended counting technique is to scan 50100 m ahead and count all visible birds, then walk on rapidly and repeat the process.
Because the birds are inconspicuous, careful scanning is important. Little attempt is
generally made to prove breeding by finding nests or broods as this causes
disturbance and is very time consuming. There are also problems with keeping track
of all the birds during the count; individuals may undertake fast pursuit flights over
large areas which can lead to overestimation (Bibby et al. 1992).
Eurasian Thick-knee
The Eurasian Thick-knee is a ground nesting bird of open arid areas, with low
precipitation and vegetation. In general the species favours areas adjacent to
wetlands or surface water. It is mainly nocturnal and crepuscular, therefore its
observation and accurate population estimation is hard. There is no scheme currently
in place to monitor possible breeding or wintering populations of Eurasian Thick-knee
on Akrotiri Peninsula.
Birds can be found in various areas of the peninsula including RAF Akrotiri, the salt
meadows surrounding the salt lake and Akrotiri Merra.
In monitoring of breeding populations, the counting unit is the incubating bird. Birds
can be located by playing tapes of their call from a slowly moving vehicle, at dusk
and during the night. If the taped call is within 500 m of an incubating bird it will
answer and can be counted (Bibby et al. 1992). Alternatively, transects can be
walked in daytime, in all potential habitats where this species may be found, to flush
incubating birds (Bealey et al. 1999). In Cyprus, site visits during the breeding
season should be made between April to August (Flint and Stewart 1992), and
locations of all breeding and non-breeding pairs, singletons, and their nest sites
recorded.
To find nests, these can be located by watching the parents from a distant vantage
point and then checked at intervals of 1-2 weeks to obtain information on the timing
and success of breeding. If nests can be viewed from a distance, it is advisable not to
disturb incubating adults. Nests should be marked on a map. At visits to the nest, the
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number of eggs and chicks and the presence and behaviour of adult birds can be
recorded (Bealey et al. 1999).
For nocturnal roost counts of Eurasian Thick-knees, the counting unit is the individual
bird. These are counted as they fly to or from roost sites, at dusk or dawn. Counts
can be undertaken throughout the year and allow indices of population level to be
produced (Bibby et al. 1992).
Cyprus Warbler
The Cyprus Warbler is associated with areas covered with shrubs and scrub. It
prefers maquis habitats vegetated with Pistacia lentiscus, Rhamnus, Cistus and
Cypressus species, where it nests under the dense cover provided by such plants.
The main areas used by this species at Akrotiri Peninsula are at its southern part,
where Pistacia and juniper dominate the vegetation. There is no scheme currently in
place to monitor the breeding populations of Cyprus Warbler in the area. A starting
point for such a scheme should be based on information gathered during a study
investigating the bird-habitat relationship of the bird species occurring at Akrotiri
Peninsula (Hadjikyriakou 2011).
Potential habitats in which this species may occur should be surveyed. In general,
breeding populations of passerine birds are counted using mapping methods, point
counts or transects (Bibby et al. 1992). During the breeding season, many species
are territorial. Especially among passerines, territories are often marked by
conspicuous song, display and periodic disputes with neighbours. Often, the area is
not completely filled with territories because of low densities or gaps in suitable
habitat. In such cases, mapped registrations of birds should fall into clusters
approximately coinciding with territories. The mapping approach relies on locating all
these signs on a series of visits and using them to estimate locations and numbers of
clusters or territories. The mapping method is the most time consuming of the
general bird count methods for a fixed number of birds finally counted.
Eleonora’s Falcon, Peregrine Falcon, Griffon Vulture and Mediterranean Shag
Counting breeding raptors and seabirds that use specialized nesting habitat in
inaccessible areas, such as coastal cliffs and islets, pose special problems. Some
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Consulting CYPRUS
species, e.g. Peregrine Falcons, are found at low densities. For colonially nesting
species, difficulties include locating the colonies on rugged coastal sites, assessing
the proportion of breeding and non-breeding birds, evaluating the proportion of birds
that have left the nest to obtain food, and defining the effects of harsh weather on
numbers of birds at the colony (Bibby et al. 1992).
‘Look-see’ methods are commonly used to assess breeding populations. The
counting unit is the Apparently Occupied Nest-site which is defined as an individual
sitting tightly on a reasonably horizontal area large enough to hold an egg (Nettleship
1976). Two birds on a site, apparently paired, count as one site. Proof of occupancy
by a pair should be (1) seeing two birds together, (2) finding moulted feathers or
droppings, or preferably (3) finding a nest containing eggs or young, or seeing adults
carrying food or hearing the begging calls of young birds.
Pairs of Peregrine Falcon and colonies of breeding Eleonora’s Falcon, Griffon Vulture
and Mediterranean Shag are distributed along the extensive sea cliffs and shorelines
of Akrotiri and Episkopi area. Current schemes provide information on the breeding
populations of the raptors, with less detailed information relating to Mediterranean
Shags. The current schemes can be used as a basis for long-term monitoring
programmes.
Suggested
improvements
on
the
schemes
should
aim
for
standardization of the census methods and recording of data. The guidance on
mandatory attributes for these species are in Tables 28-31.
As a first step, it is necessary to describe in more detail than previously, and mark on
a map, the study area by dividing the cliff or shore into easily countable sections.
These are best defined by the features of the area (e.g. vertical cliff, boulders, sandy
beach, etc.), the availability of suitable vantage points from which the birds can be
counted, and the ease with which each section can be counted. It is important that all
sections and vantage points are marked on a base-map of the study area at 1:
10.000 scale and the results of the counts are presented according to the various
sections.
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In continuation, the breeding colonies should be described and kept on record. A
colony is defined as a concentration of breeding birds separated from others by an
area of cliff, sea or open space. If in doubt, it is usually best to sub-divide a colony,
so long as this can be done unambiguously. Information to be recorded for each
colony or sub-division of a colony is presented in Table 27.
Table 27: The information that should be recorded to describe each colony or sub-division of a
colony.
Colony name
Location
Location
Status
Status
Description
Description
Access
Access
History
Counting history, with bibliography
Counting problems
Indicate approximately what percentage of the
colony can be counted from land, how much can
be seen from the sea and any particular counting
problems, e.g. birds nesting in caves, counted
whilst looking up, broad ledges hiding birds,
restricted view of colony, disturbance of colony
by observer
Other notes
Bibliography
Any details of books, scientific papers, reports
etc. that mention the colony
To obtain the most accurate counts of birds at cliff-nesting colonies, the position of
the observer is important. Ideally, observers should be at the same level, or slightly
above, the birds and should be looking directly at the colony. If this preferred position
cannot be obtained, the observer is forced to count the birds from available locations,
which in the case of surveying Eleonora’s Falcon colonies includes counts from
boats.
Select a suitable vantage point and scan the study area using binoculars. Beware of
counting paired birds standing apart as two territory holders, and of overlooking birds
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that blend against the background. The counts should be repeated on three separate
days spread over the counting period, with all Apparently Occupied Territories
marked on a map.
Counts should be made in the late incubation to early nestling period when colony
attendance is the greatest. Eleonora’s Falcons are summer – autumn visitors which
stay in the area until mid-autumn when they fly back to Madagascar and Africa to
their wintering grounds. Therefore, counts should take place from the end of July to
mid-August. For the other three species nesting in the area, counts should take place
from late March to mid-April for the Peregrine Falcon, and late-February to midMarch for the Griffon Vulture and the Mediterranean Shag. Ideally, several counts
should be made over a period of 3-7 days to reduce problems with colony attendance
varying between days, and a mean number of Apparently Occupied Nest-sites
calculated (Bibby et al. 1992).
The counts which are currently conducted are made from boats in mid-July to midAugust, for the Eleonora’s Falcon, during which all other species observed are also
recorded. Information from these counts is combined with data collected from counts
conducted from the land (Wilson 2005). It is necessary to standardize the count
locations, both from the sea and the land, so that data collected may be comparable
among years. Another option is to use photographs. Photographs are an easy
method to assess the status of a colony as expanding colonies always increase in
area, and declining ones decrease. Photographs can be taken from a boat or the air,
and nest sites counted.
Table 28: Guidance on mandatory attributes for the Eleonora’s Falcon
Attributes
Bird
population
size
Targets
Method of
assessment
Comments
Annual breeding
surveys
limits
conducted by
SBAA
Counts made by
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Attributes
Targets
Method of
assessment
Comments
birdwatchers
at 50-100 pairs.
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
Akrotiri and Episkopi sea
cliffs that are used by this
The total area of
limits:
should be mapped
Habitat
extent
using one of or a
combination of
techniques
outlined in JNCC
(2004).
No detailed
habitat mapping
to date
unacceptable
Table 29: Guidance on mandatory attributes for the Peregrine Falcon
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Attributes
Targets
Method of
assessment
Comments
limits
Counted during
annual Eleonra’s
Falcon breeding
Bird
surveys
population
conducted by
size
SBAA
Counts made by
birdwatchers
at 4 pairs.
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
The total area of
should be mapped
Habitat
using one of or a
extent
limits:
combination of
techniques
outlined in JNCC
(2004).
No detailed
habitat mapping
to date
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Attributes
Targets
Method of
assessment
Comments
unacceptable
Table 30: Guidance on mandatory attributes for the Griffon Vulture
Attributes
Targets
Method of
assessment
Comments
limits
Bird
population
size
Annual breeding
surveys
conducted by
Forestry
Department
Counts made by
birdwatchers
at 2 pairs.
Maintain density of
acceptable limits:
Population
density
No estimates to
date
unacceptable.
species is unknown
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Attributes
Targets
Method of
assessment
Comments
The total area of
limits:
should be mapped
Habitat
extent
using one of or a
combination of
techniques
outlined in JNCC
(2004).
No detailed
habitat mapping
to date
unacceptable
Table 31: Guidance on mandatory attributes for the Mediterranean Shag
Attributes
Targets
Method of
assessment
Comments
limits
Counted during
annual Eleonra’s
Falcon breeding
Bird
surveys
population
conducted by
size
SBAA
Counts made by
birdwatchers
at 15-20 pairs.
Population
density
Maintain density of
acceptable limits:
No estimates to
date
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Attributes
Targets
Method of
assessment
Comments
unacceptable.
species is unknown
The total area of
limits:
should be mapped
Habitat
extent
using one of or a
combination of
techniques
outlined in JNCC
(2004).
No detailed
habitat mapping
to date
unacceptable
Pelagic seabirds
As previously mentioned in this report, no data exist for offshore seabird species
found in this area, such as Cory’s Shearwater, the Yelkouan Shearwater, the
European Storm Petrel and the Northern Gannet (Flint and Stewart 1992). In general,
population estimates are much more difficult with pelagic birds than breeding colony
data. Pelagic seabird survey programs are generally difficult to incorporate into
monitoring programmes, because such programs rely on 'ships of opportunity' rather
than using dedicated ship time (e.g. Brown 1986). As a result, an ideal procedure
such as selecting and repeating a sample of transects chosen to represent marine
habitats in a region (using a randomised or stratified-random design) is unlikely to be
practicable.
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Moreover, it is difficult to convert survey data into absolute populations by counting
birds seen within a fixed-width transect (e.g. Tasker et al. 1984), or from transects of
undefined width (Diamond et al. 1986). Therefore, monitoring programmes to identify
trends rather than absolute numbers are proposed (Diamond 2011). For example,
simple and consistent indexes are used in other parts of the world, e.g. using 'birds
per linear kilometre' to indicate trends (Brown 1986); or counting all birds seen per 10
minutes within a 300m transect either side of a vessel (Tasker et al. 1984). In any
case, a ‘Protocol for Monitoring Seabirds’ which is used in Canada for pelagic
seabird surveys (Diamond 2011) may also be adapted to local conditions and used
as a basis for an offshore monitoring programme in the Akrotiri Peninsula area
7.7.1
Proposed Monitoring Programme for Aquatic biotic components
According to the Nature Conservation Component Plan the generic objective of the
management plan is to maintain or restore all the important features at Akrotiri
Peninsula at a favorable conservation status, taking into account economic, social
and cultural requirements and local characteristics.
In relation to waterbodies, this refers to their restoration in order to achieve at least
Good
status.
Monitoring
of
submerged aquatic
macrophytes
and benthic
macroinvertebrates assemblages is crucial in order to achieve this objective. These
biological components can be used as an assessment tool for the evaluation of
ecological quality of the waterbodies incorporated in Akrotiri peninsula. Long term
monitoring of these quality elements will provide sufficient information for the
ecological status and will guide wetland managers in which direction management
measures should aim, in order to achieve favorable conditions as defined by the
management objectives.
7.7.2
Proposed biotic monitoring indicators
The assessment of aquatic species and communities provides valuable information
about wetlands health. The effects of human induced stressors on aquatic
ecosystems involve a series of hierarchical responses of different biological
organizational levels with the most ecologically relevant ones to occur at species,
population and community level. Pressures on wetlands may lead to changes related
to community attributes such as structure (i.e., species composition, richness, and
abundance), function (i.e., feeding habits and density), and dynamics (i.e., presence
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or absence of sensitive organisms and contribution of dominant taxa), leading
ultimately to changes in the functional integrity of ecosystem. Therefore, population
shifts can be regarded as an early warning signal of the community and ecosystem
impairment.
The aquatic biotic components to be studied in Akrotiri peninsula are Macrophytes
and Benthic Macroinvertebrates. Both groups are designated as Biological Quality
Elements by the Water Framework Directive 2000/60/EC and are being monitored on
European scale in both coastal and inland waters. Since very few data exist
concerning the status of these components in Akrotiri, they will be studied from
baseline level. Therefore samplings will focus among others, on collecting the most
of all taxa present in the peninsula.
7.7.3
Aquatic Macrophytes
As photosynthetic sessile organisms, submerged aquatic macrophytes are
vulnerable and respond rapidly to disturbance in the aquatic environment
representing a reliable ecological bio-indicator. Macrophyte communities will be
investigated in all waterbodies of the peninsula and the following indices will be
addressed:
·
Species composition
·
Species richness
·
Shannon diversity
·
Presence/absence of sensitive taxa as well as other species, indicative of
ecosystem degradation
·
Percentage of algae cover
·
Percentage of angiosperms cover
The calculation of a macrophyte quality index such as EEI-c (Ecological Evaluation
Index - continuous formula), an evolved version of the well established EEI (Orfanidis
et al., 2001), will be also applied in order to assess the quality of the wetlands. The
concept of the EEI is based on the obvious and universal pattern that anthropogenic
disturbance, e.g. pollution-eutrophication, shifts the ecosystem from pristine to
degraded state. Benthic macrophytes (macroalgae and angiosperms) are used as
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bio-indicators of ecosystem shifts, from the pristine state where late-successional
species is dominant, to the degraded state where opportunistic species prevail. In
moderately impacted areas slow growing, shade-adapted calcareous species and
opportunistic macroalgae often co-dominate.
7.7.4
Aquatic Macroinvertebrates
Aquatic benthic macroinvertebrate populations will also be explored as a
supplementary indicator. They are also considered as good bio-indicators of aquatic
ecosystems health because of their low mobility rates and their high variability in
pollution tolerance. In addition, invertebrates live most of their life in the water column
and have adequate life span (a few weeks to a couple of years) which means that
they can express the long term quality of the waterbody they are found in. Benthic
macro-invertebrate communities will be investigated by means of:
·
Species richness
·
Absolute abundance
·
Population and taxa density,
·
Species richness
·
Presence/absence of sensitive taxa
·
Shannon diversity index
·
Richness of groups EPT (Ephemeroptera, Plecoptera , Trichoptera,)
In addition metrics dealing with population dynamics such as percentage of Diptera,
percentage of Trichoptera, percentage of Ephemeroptera, percentage of dominant
taxa and presence/absence of sensitive/tolerant taxa will also be used were indicated.
Finally the application of the Invertebrate Index of Biotic Integrity (IBI) which was
developed for the assessment of coastal wetlands will be attempted. IBI is a
multimetric index using macroinvertebrates as bioindicators which evaluates
ecological condition by combining a series of empirically derived and tested curves
representing species responses to disturbance.
A first evaluation of macrophyte and macro-invertebrate communities will provide us
a first view of the quality status of Akrotiri wetland waterbodies. This preliminary
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evaluation will provide basic information about the taxa present in the wetland, their
distribution and abundance as well as their response to pressures. This information
will set the basis for designing a monitoring plan for the long term monitoring and
management of Akrotiri wetlands.
Monitoring network
Monitoring stations were selected in order to cover all major waterbodies in the
peninsula and to be representative of the whole study area. In total eight (8) sampling
stations were selected based on their location and characteristics (salinity range,
vegetation, water regime). The proposed stations are shown on Table 16.
Nevertheless, addition or removal of stations in the monitoring network is probable,
due to on-spot practical difficulties, such as water scarcity, dense vegetation etc.
Table 32: Proposed sampling locations for the monitoring of biotic components in Akrotiri
waterbodies
No
Station Name
Latitude
Longditude
1
Zakaki marsh
34° 38' 36.13"N
33° 00' 10.22"E
2
Zakaki marsh canal
34° 38' 26.92"N
32° 59' 67.22"E
3
Coastal ponds (Lady's mile)
34° 38' 23.33"N
33° 00' 29.71"E
4
Phasouri marsh
34° 37' 52.73"N
32° 56' 01.53"E
5
Phasouri marsh canal
34° 37' 30.46"N
32° 56' 16.76"E
6
Salt lake
34° 36' 40.00"N
32° 58' 76.00"E
7
Small pond in salt lake
34° 36' 12.08"N
32° 57' 52.00"E
8
Small pond by the road
34° 36' 00.52"N
32° 57' 48.75"E
Sampling frequency
Submerged aquatic macrophytes
Aquatic macrophytes growth depends mainly on hydrological status, temperature and
light intensity (Barko & Smart 1981, Van den Berg et al. 1998). Therefore in a
temporal ecosystem such as Akrotiri, macrophyte emergence is triggered in mid
winter when water accumulates in the wetland, reaches maximum growth and
biomass in late spring and decays during the mid-summer high temperatures or
when eventually the wetland dries out. Therefore the best sampling period is mid- to
late spring depending on the water regime, since in dry years the water bodies are
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expected to dry up earlier and high salinities during the evaporative loss period might
also affect macrophyte growth.
The abovementioned short wet period limits the lifecycle of macrophytes and
consequently the period of macrophytes maximal growth. For this reason sampling
can be conducted only once a year, in mid to late spring when macrophytes are at/or
close to maximum growth, which is considered adequate for the long-term monitoring
of the wetland status.
Benthic macroinvertebrates
In contrast to macrophytes, benthic invertebrates are characterized by rapid growth
rates and short life cycles. Moreover, flying invertebrates lay their eggs as soon as
the accumulation of water begins in the wetland and therefore they become available
earlier than macrophytes. Therefore two sampling periods can be considered on an
annual basis: first sampling period is proposed for the end of winter period (end of
February - early March) and the second in mid - to late spring.
Supporting elements
Biological monitoring must be supported by physicochemical data for the
interpretation of possible changes in aquatic communities. Therefore variation of
several water parameters must be monitored during the period of water presence in
the wetland. It is suggested that these parameters are monitored twice a month. In
the cases when these proposals overlap with the ‘hydrology’ parameters it is
suggested that the stations sites coincide to avoid duplication of effort.
•
Depth
•
Turbidity
•
Temperature
•
Salinity
•
pH
•
Nutrients (NO2, NO3, NH4, PO4, Total P)
•
BOD
•
TOC
•
Heavy metals
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•
Pesticides
•
Insecticides
•
Chlorophyll-a
Additional Monitoring Parameters
·
Habitat fragmentation
·
Rate of use by offroad vehicles
·
Number of recreational visitors
·
Correlation of groundwater levels to Akrotiri saltlake water depths
·
Correlation of groundwater levels to Fasouri Marsh water depths
7.8
Proposed additional studies
In addition to the monitoring of the above parameters it is suggested that the
following studies are undertaken:
·
Determination of the Hydraulic Conductivity between the Fasouri Marsh and the
Akrotiri Aquifer and and Akrotiri Salt Lake and the Akrotiri Aquifer. The study will
require the following steps:
·
Collection, collation and analysis of all hydrogeological data and studies of the
project area.
·
Geological mapping of the Akrotiri salt lake. Ephasis should be given to
determining the presence of marl and the presence of permeable formations
such as Pahna.
·
Gephysical suevey of the area between the salt lake and the krotiri aquifer.
·
Selection of locations and determination of required depths for boreholes
designed to produce north-south profiles of geological formations.
·
Borehole investigation.
·
Preparing detailed profiles of geological formations.
·
Assessment of the environmental impacts of current pest control practices
·
Development of an Index of Biological Integrity
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7.8.1
Additional studies in relation to Phallocryptus, Aphanius, and aquatic
insects
The following suggestions for additional studies in relation to the fairy shrimps in the
Lake all can be performed in the context of senior and graduate theses of students of
Biology, Ecology and Environmental Chemistry.
Objective:
To
ensure
stability
of
the
ecosystem
that
sustains
the
Phallocryptus/birds/nutrients dynamics
·
Indicator: Weekly monitoring of the water salinity, temperature, dissolved
oxygen, pH, nutrients.
·
Indicator: Weekly monitoring of the primary producers (phytoplankton) in the
water overlaying the benthic communities of the Lake.
·
Indicator: Weekly monitoring of the zooplankton grazing on the primary
producers
·
Indicator: Weekly monitoring to determine the presence/absence of Aphanius
and carnivorous arthropods (larvae, adults) in the Salt Lake.
Objective: To ensure the stability of the Phallocryptus population in the Salt Lake
·
Indicator: Weekly observational study of the feeding habits of birds (flamingos,
shelducks, avocets, glossy ibises) inside the Lake’s basin in relation to
Phallocryptus.
·
Indicator: Assessment of the human impact by trampling on the cysts bank.
·
Indicator: Ex situ experiments (bioassays) to study the potential impact on
Phallocryptus of the granular organophosphorus insecticide Abate, used in
Akrotiri to control mosquito larvae.
·
Indicator: Experiments ex situ on the salinity tolerance of the local population of
Phallocryptus and the cysts’ hatching response.
·
Indicator: Experiments ex situ on the salinity tolerance of Aphanius.
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Consulting CYPRUS
·
Indicator: Evaluation of different methods to study the cysts bank of
Phallocryptus in the Lake and surrounding ponds.
Objective: Ensure the stability of the food web (nutrients/plankton) that enables
Phallocryptus to proliferate and provide food for birds
·
Indicator: Weekly monitoring to determine the initiation and progress of the
primary production component (plankton) of the Salt Lake ecosystem.
·
Indicator: Weekly monitoring of the water chemistry and plankton in relation
to other inputs of nutrients (e.g. birds’ faecal material, carcasses, atmospheric
dust deposition) into the Lake.
·
Indicator: Experiments ex situ on the Phallocryptus tolerance to starvation
periods.
·
Indicator: Ex situ experiments (bioassays) on the potential impact of the
granular organophosphorus insecticide Abate, used in Akrotiri to control
mosquito larvae, on the plankton.
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8
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191
Consulting CYPRUS
9
APPENDICES
192
Consulting CYPRUS
Appendix I
MAPS
193
Consulting CYPRUS
Appendix II
Flora & Habitats
194
Consulting CYPRUS
A. Communities identified in the halophytic wetlands of Akrotiri Peninsula (Christodoulou 2003,
Code
No releve
Hadjichambis 2005)
Vegetation Class
1310
H10
3
SALICORNIETEA FRUTICOSAE Br.-Bl.
et Tx. ex A. de Bolos 1950
1310
H26
1
1410
H02
4
1410
H06a
4
1410
H08
7
1410
H19
2
1410
H20a
2
1410
H23b
4
1410
H24
5
1420
A
2
0
1420
Bi
4
1420
Bii
2
1420
Biii
2
1420
H03
2
1420
H04
5
1420
H05
2
1420
H07
3
JUNCETEA MARITIMI Tx. et Oberd.
1958
1420
H11
1
1420
H12a
2
1420
H12b
1
Habitat
Type
Vegetation Community
THERO-SALICORNIETEA
(Pignatti
1953) Tx. in Tx. et Oberd. 1958
PUCCINELLIO-SALICORNIETEA Topa
1939
THERO-SALICORNIETEA
(Pignatti
1953) Tx. in Tx. et Oberd. 1958
QUERCETEA ILICIS Br.-Bl. ex A. de
Bolos 1950
1958
JUNCETEA MARITIMI Tx. et
1958
Oberd.
1958
Arthrocnemetum
macrostachiHalocnemum
strobilacei-Salicornia
europaea
Halopeplidetum amplexicaulis Burollet
1927
Juncus subulatus-Zygophyllum album L. fil.
Community
Agropyron
elongatum-Aeluropus
lagopoides Community
Halocnemum strobilaceum – Halopeplis
amplexicaulis community
Asparagus
stipularis
Forsskal-Juncus
subulati Community
Juncus subulatus Community
Schoeno - Plantaginetum crassifoliae
Μεταβατική Ζώνη με Schoenus nigricans Asparagus stipularis
Schoenus nigricans L. Community
Arthrocnemum
macrostachyum-Inula
crithmoides com.
Acacia
saligna
(shrub)-Juncus
heldreichianus
com.,
transition
to
community A
Acacia
saligna
(tree)-Juncus
heldreichianus
com.,
transition
to
community A
Acacia saligna -Juncus heldreichianus
com.
Zygophyllum album L. fil. Community
variation with Plantago maritima ssp.
crassifolia
variation with Plantago maritima ssp.
crassifolia
Arthrocnemum macrostachyum (Moric.)
Moris & Delponte variation with Plantago
maritima
Zygophyllum album L. fil. - Plantago
maritime community [Schoenus nigricans Inula crithmoides]
Arthrocnemetum
fruticosi
suaedosum
verae
Arthrocnemetum fruticosi variation with
Salicornia europaea
Sarcocornia
perennis-Arthrocnemum
195
Habitat
Type
No releve
Code
Consulting CYPRUS
Vegetation Class
macrostachyum comm.
Arthrocnemetum glauci - Halocnemetum
strobilacei Oberd. 1952
1420
H13
5
1420
H14
2
1420
H15
3
1420
H16
5
1420
H17
4
1420
H18
4
1420
H21
3
1420
H22
3
1420
H25b
1
1420
H27
2
Puccinelio convolutae- Arthrocnemetum
glauci, Gehu 1984. Variation with
Limonium virgatum (Willd.) Fourr.
92D0/
2260
H01
2
Nerio-Tamaricetea Br.-Bl. et de Bolos
1958
Tamarix tetragyna Community
acacia
B
1
6
CY02
C
7
PHRAGMITO - MAGNOCARICETEA
Klika in Klika et Novak 1941
CY02
Ci
4
CY02
D
4
Limonio virgati – Zygophylletum albi ?
Moris & Delponte - Parapholis incurva (L.)
C. E. Hubbard Community
Arthrocnemetum macrostachyi
Arthrocnemo glauci – Juncetum subulati
Brullo et Furnari 1976
Arthrocnemo – Juncetum subulati variation
with Inula crithmoides & Limonium
mucronulatum
Halocnemum strobilaceum Community
Arthrocnemum
Community
perenne
(Miller)
Moss
Suaeda vera comm.
Acacia saligna-Juncus heldreichianus com.
Invasion
Phragmites
australis-Juncus
heldreichianus com.
Phragmites
australis-Juncus
heldreichianus
com.,
transition
to
community A
Phragmites australis-Acacia saligna com.
196
Consulting CYPRUS
B. Communities identified in the sand dunes of Akrotiri Peninsula (Hadjichambis 2005)
Habitat
Type
1430
Code
S17a
No
releve
7
Vegetation Class
PEGANO
HARMALAESALSOLETEA VERMICULATAE
Br.-Bl. et de Bolòs 1958
AMMOPHILETEA Br.-Bl. et Tx. Ex
Westhoff, Dijk et Passchier 1946
Lycium schweinfurthii U. Dammer
2110
S12
3
2110
S13b
7
2110
S14b
1
2110
S14c
2
2110
S15a
7
2110
S16
7
2110
S21a
4
2110
S29
9
2110
S49
3
2110/
1430
S45
4
2110/
2210
2110/
2210
S10
5
S14a
6
2110/
2210
S18
5
2110/
2210
2110/
2210
S19
5
S36
5
2110/
2210
2190
S37
1
S31
11
1420/
S30
6
SALICORNIETEA FRUTICOSAE
Br.-Bl. et Tx. ex A. de Bolos 1950
AMMOPHILETEA Br.-Bl. et Tx. ex
MOLINIO-ARRHENATHERETEA
Tx. 1937 / JUNCETEA MARITIMI
Tx. et Oberd. 1958
SALICORNIETEA FRUTICOSAE
-
Cyperus capitatus Vandelli – Eryngium
maritimum L. Plantago afra L. Community
Agropyron junceum (L.) Beauv.-Cakile
maritima
Scop.-Medicago
marinaOtanthus maritimus (L.) Hoffmanns. &
Link Community
Agropyron
junceum
(L.)
Beauv.
Community
Agropyron junceum (L.) Beauv. - Echium
angustifolium Miller Community
Agropyron junceum (L.) Beauv. – Cakile
maritima Scop.-Medicago marina L.Zygophyllum album L. fil.
Sporobolus virginicus (L.) Kunth Zygophyllum album L. fil. Community
Echium angustifolium Miller-Sporobolus
virginicus (L.) Kunth Degradation
Zygophyllum album L. fil. - Cakile
maritima Scop. Community
Sporobolus
virginicus
(L.)
Kunth
Community
Moris & Delponte - Zygophyllum album L.
fil. Community
Hyparrhenia hirta (L.) Stapf.-Cyperus
capitatus Vandelli Community
Agropyron junceum (L.) Beauv.-Launaea
resedifolia (L.) O. Kuntze -Echium
angustifolium Miller-Pseudorlaya pumila
(L.) Grande
Cyperus capitatus Vandelli – Centaurea
aegialophila Wagenitz - Medicago marina
L. - Euphorbia cassia Boiss. subsp.
Cassia – Helianthemum stipulatum
(Forsskal) C. Chr. Community
Medicago marina L. - Centaurea
aegialophila Wagenitz Community
Imperata cylindrica (L.) Raeuschel –
Plantago maritima L. - Sporobolus
virginicus (L.) Kunth – Helianthemum
stipulatum - Euphorbia cassia Boiss.
subsp. cassia Community
Imperata cylindrica (L.) Raeuschel Echium angustifolium Miller Community
Schoenus nigricans L. - Plantago
maritima L. Community
197
Consulting CYPRUS
Habitat
Type
2190
Code
2190/
2240
S32
18
2240/
2230
S38
4
2250
S01
1
2250
S02
2
2250
S04
4
2250
S05
6
2250
S09
7
2260
S02
1
2260
S07
9
2260
S11
2
2260
S35
13
2260
S40
8
CISTO-MICROMERIETEA
JULIANAE Oberd. 1954
2260/
1430
S08
6
CISTO-MICROMERIETEA
2260
acacia
2270
S46
3
/
S101
2
S06
3
QUERCETEA ILICIS Br.-Bl. ex A.
de Bolos 1950
de Bolos 1950
2270
aleppo
No
releve
Vegetation Class
Br.-Bl. et Tx. ex A. de Bolos 1950
Moris & Delponte - Parapholis incurva (L.)
C. E. Hubbard – Inula crithmoides L.
Community
Schoenus nigricans L. - Plantago
maritima L. – Bromus rubens Community
MOLINIO-ARRHENATHERETEA
Tx. 1937 / JUNCETEA MARITIMI
Tx. et Oberd. 1958
THERO-BRACHYPODIETEA Br.Bl. ex A. de Bolos 1950
de Bolos 1950 / THEROBRACHYPODIETEA Br.-Bl. ex A.
de Bolos 1950
de Bolos 1950
de Bolos 1950
de Bolos 1950
de Bolos 1950
de Bolos 1950
CISTO-MICROMERIETEA
de Bolos 1950
CISTO-MICROMERIETEA
Aegilops bicornis (Forsskal) Jaub. &
Spach – Aegilops biuncialis Vis. –
Imperata cylindrica (L.) Raeuschel
Community
Juniperus phoenicea Community
Juniperus phoenicea – Myrtus communis
– Olea europea Community
Juniperus
phoenicea
L.–
Pistacia
lentiscus Community
Juniperus phoenicea L. – Coridothymus
capitatus – Paronychia macrosepala
Pistacia lentiscus L.-Rhamnus oleoides–
Prassium majus- με ή χωρίς Juniperus
phoenicea L. Community
Juniperus phoenicea – Myrtus communis
– Olea europea Community
Asparagus stipularis Forsskal-Pistacia
lentiscus L.-Juniperus phoenicea L.
Pistacia lentiscus L.–Asparagus stipularis
Forsskal Degradation
Thymus capitatus (L.) Hoffmanns. & Link
- Helianthemum stipulatum - Schoenus
nigricans L. Community
Thymelaea hirsuta (L.) Endl. - Thymus
capitatus (L.) Hoffmanns. & Link – Lotus
cytisoides Community
Lycium schweinfurthii U. DammerAsparagus
stipularis
ForsskalZygophyllum album L. fil. Community
Acacia saligna (Labill.) Wendl. fil.
Community
Juniperus phoenicea L.– Pinus brutia
Tenore Community
Pinus halepensis Miller – Juniperus
phoenicea L. Community
198
Consulting CYPRUS
Acacia saligna synanthropic
Achillea
maritima
subsp.
maritima
Aegilops
bicornis
Aegilops
biuncialis
Aegilops sp.
Aeluropus
lagopoides
Aetheorhiza
bulbosa
Allium sp.
Allium
trifoliatum
Anacamptis
pyramidalis
Anagallis
ammophilous
Ammophiletea
dry grassland
1
Y
VU
A4c
Y
VU
B1ab(iii,v)
+2ab(iii,v)
9
UNKN
4
8
7
[8] [3]
[7]
[5] [1]
7
5
7
5
0
8
6
8
4
7
5
x
x
5
1
7
6
9#
6
1
7
3
8#
4
0
6
x
8
5
1
1
3
-1
-1
1
UNKN
halophytic
ammophilous
Salicornietea
fruticosae
TheroBrachypodietea:
Cutandietalia
maritimae
1
1
1
1
UNKN
UNKN
phrygana/maquis/ev
ergreen woodland
shrub/Woodland
(Cisto/Woodland
MicromerieteaQuercetea ilicis)
synanthropic
Synanthropic
Y
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Sand Dune Vegetation Indicators
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Synanthropic
(mainly Artemisietea
vulgaris, tellarietea
mediae)
IUCN
category
IUCN
criteria
Vegetation class
threatened
group
endemic
Vegetation
status
Taxon
alien
Attributes of the taxa of sand dune and halophytic vegetation recorded in the datasets of Christodoulou (2003) and Hadjichambis (2005).
-1
1
Anthemis
tricolor
Arisarum
vulgare
Asparagus
horridus
Asperula
cypria
-1
1
1
1
-1
UNKN
phrygana/maquis/ev
ergreen woodland
shrub/Woodland (CistoMicromerieteaQuercetea ilicis)
phrygana/maquis/ev
ergreen woodland
Y
LC
Salicornietea
fruticosae
phrygana/maquis/ev
ergreen woodland
phrygana/maquis/ev
ergreen woodland
phrygana/maquis/ev
ergreen woodland
shrub/Woodland
(CistoMicromerietea-
Y
LC
x
x
x
6
1
9
9°
9#
7
8
[5] [2]
[?]
[?] [1]
8
8
3
1
2
-1
1
1
1
Sand
Content
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
Protected
mediae)
Arthrocnemum
macrostachyu halophytic
m
Asparagus
acutifolius
Indicators
EC
Anthemis sp.
Ellenberg Indicator
Values
Cl-
arvensis
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Quercetea ilicis)
Aster
squamatus
UNKN
synanthropic
Asterolinon
dry grassland
linum-stellatum
Avellinia
michelii
ammophilous
Avena
byzantina
synanthropic
Bellardia
trixago
synanthropic
Bellevalia
nivalis
UNKN
Bellevalia
trifoliata
Biscutella
didyma
Blackstonia
synanthropic
dry grassland
wetland
Synanthropic
mediae)
TheroBrachypodietea
Malcolmietalia
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
TheroBrachypodietea
Isoeto-anojuncetea
alien
Asphodelus
sp.
8
8
8
8
1
7
4°
x
2
1
8
x
8
4
1
8
x
8
7
0
7
5
7
5
1
7
6
7
5
1
8
3
7
5
1
7
7
8
6
4
1
-1
EC
1
1
acuminata
Blackstonia
perfoliata
wetland
Brassica
tournefortii
synanthropic
Briza maxima synanthropic
Bromus
arvensis
synanthropic
Bromus
diandrus
synanthropic
Bromus
fasciculatus
synanthropic
Bromus
rubens
synanthropic
Bromus sp.
Bupleurum
UNKN
UNKN
MolinioArrhenatheretea:
Holoschoenetalia
vulgaris
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
7
x
8
4
1
9
3
8
5
3
6
x
7
3
0
8
7
8
5
1
7
5
8
8
1
8
2°
8
4
2
9
1
8
5
3
1
1
-1
1
Sand
Content
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Calendula
arvensis
synanthropic
Cardopatium
corymbosum
synanthropic
Carduus
argentatus
synanthropic
Carex extensa halophytic
Carex flacca
subsp.
wetland
serrulata
Carex sp.
wetland
Carthamus sp. UNKN
Centaurea
ammophilous
aegialophila
Centaurium
wetland
pulchellum
Centaurium
halophytic
spicatum
Centaurium
halophytic
tenuiflorum
Cistus creticus shrub/Woodland
Cakiletea maritimae
5
9#
8
4
7
4
8
7
0
8
3
8
6
0
8
4°
8
6
0
8
8
8
6
6
MolinioArrhenatheretea
6
6
7
3
1
Ammophiletea
9
3
9#
5
3
Isoeto-anojuncetea
8
5
9#
4
1
Saginetea
maritimae
6
8
9#
5
6
Juncetea maritimi
8
7
8
4
x
phrygana/maquis/ev
7
3
7
2
1
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Juncetea maritimi
1
1
-1
-1
-1
1
1
-1
1
1
1
-1 -1
Sand
Content
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
Protected
IUCN
category
IUCN
criteria
8
Indicators
EC
ammophilous
Vegetation class
threatened
group
Ellenberg Indicator
Values
Cl-
orientale
Cakile
maritima
Vegetation
endemic
Taxon
status
Consulting CYPRUS
1
subsp. creticus
Cistus
shrub/Woodland
monspeliensis
Cistus
parviflorus
shrub/Woodland
Cistus
salviifolius
shrub/Woodland
Clypeola
jonthlaspi
dry grassland
Convolvulus
althaeoides
synanthropic
Convolvulus
oleifolius
shrub/Woodland
Convolvulus
UNKN
ergreen woodland
(CistoMicromerieteaQuercetea ilicis)
phrygana/maquis/ev
ergreen woodland
phrygana/maquis/ev
ergreen woodland
phrygana/maquis/ev
ergreen woodland
TheroBrachypodietea
Synanthropic
mediae)
phrygana/maquis/ev
ergreen woodland
LC
7
4
8
3
1
8
2
8
x
1
7
3
7
1
1
8
3
8
6
0
8
4°
8
8
1
8
3°
8
4
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
sp.
phrygana/maquis/ev
ergreen woodland
Coridothymus
shrub/Woodland (Cistocapitatus
Coronilla
Therorepanda
ammophilous
Brachypodietea:
subsp.
Malcolmietalia
repanda
phrygana/maquis/ev
ergreen woodland
Coronilla
shrub/Woodland (Cistoscorpioides
TheroCorynephorus
ammo
Brachypodietea:
articulatus
Malcolmietalia
TheroCrepis aspera dry grassland
Brachypodietea?
Saginetea
Cressa cretica halophytic
maritimae
Crucianella
Therodry grassland
aegyptiaca
Brachypodietea?
Crupina
Therodry grassland
crupinastrum
Brachypodietea
Crypsis
wetland
Isoeto-anojuncetea?
factorovskyi
TheroCutandia
ammophilous
Brachypodietea:
dichotoma
Cutandietalia
Y
VU
8
3
8
3
1
7
3
8#
5
1
9
1
8
2
2
8
7
9#
5
8
8
3
8
3
1
[7] [2]
[?]
[?] [?]
D2
LC
Y
VU
D2
-1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Cyperus
capitatus
ammophilous
Dactylis
glomerata
wetland
Dittrichia
viscosa
synanthropic
Echium
angustifolium
Elytrigia
elongata
Elytrigia
elongata
subsp.
haifensis
Elytrigia
juncea
Ephedra
fragilis
Erodium
dry grassland
Ammophiletea
MolinioArrhenatheretea/Ly
geo
sparti-tipetea
tenacissimae
Synanthropic
mediae)
Lygeo sparti-tipetea
tenacissimae?
4
8
7
x
9
4
8
5
3
7
x
x
x
x
8
6
8
7
1
8
2
8
7
2
-1
-1
Juncetea maritimi
7
7
halophytic
Juncetea maritimi
7
7
ammophilous
Ammophiletea
8
3
8
5
5
7
2
8
7
2
8
4
8
8
1
1
-1
-1
-1
1
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
Protected
7
halophytic
phrygana/maquis/ev
ergreen woodland
synanthropic
Synanthropic
Indicators
Sand
Content
synanthropic
maritimae?
Synanthropic
mediae)
Ellenberg Indicator
Values
EC
Cynodon
dactylon
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
-1
1
-1
1
-1 -1
laciniatum
Eryngium
maritimum
mediae)
ammophilous
Ammophiletea
phrygana/maquis/ev
Euphorbia
ergreen woodland
cassia subsp. shrub/Woodland (Cistocassia
Euphorbia
ammophilous
Ammophiletea?
terracina
Filago
Therodry grassland
contracta
Brachypodietea?
Filago
Therodry grassland
eriosphaera
Brachypodietea?
Synanthropic
Filago gallica synanthropic
mediae)
Filago sp.
UNKN
phrygana/maquis/ev
ergreen woodland
Fumana
shrub/Woodland (Cistoarabica
phrygana/maquis/ev
ergreen woodland
Fumana
shrub/Woodland (Cistothymifolia
8
4
8
7
3
8
x
8
7
1
8
4
8
x
0
7
3
8
3
0
8
2
7
x
0
8
2
8
2
0
9
2
8
x
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Galium murale synanthropic
Gastridium
phleoides
synanthropic
Geropogon
hybridus
synanthropic
Glebionis
coronaria
synanthropic
Gynandriris
sisyrinchium
Halimione
portulacoides
Halocnemum
strobilaceum
Halopeplis
amplexicaulis
Hedypnois
rhagadioloides
Hedysarum
spinosissimum
Helianthemum
salicifolium
dry grassland
halophytic
halophytic
halophytic
dry grassland
dry grassland
dry grassland
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
mediae)
Poetea bulbosae
Salicornietea
fruticosae
Salicornietea
fruticosae
7
x
7
4
0
8
4
x
4
1
8
5°
9#
6
1
8
5
8
8
1
8
4
8
6
1
8
8
8
7
6
1
8
1
7
4°
8
7
1
8
2
9#
7
2
1
7
3
x
6
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
8
Thero-Salicomietea
TheroBrachypodietea
TheroBrachypodietea
TheroBrachypodietea
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Helianthemum
ammophilous
stipulatum
Ammophiletea?
phrygana/maquis/ev
ergreen woodland
Helianthemum
shrub/Woodland (Cistosyriacum
phrygana/maquis/ev
ergreen woodland
Helichrysum
shrub/Woodland (Cistoconglobatum
Hippocrepis
Therodry grassland
ciliata
Brachypodietea
Hippocrepis
Therodry grassland
unisiliquosa
Brachypodietea
Hordeum
Saginetea
halophytic
geniculatum
maritimae
Synanthropic
Hordeum
synanthropic
glaucum
mediae)
Hordeum
Saginetea
halophytic
marinum
maritimae
Hymenolobus
Saginetea
halophytic
procumbens
maritimae
Hyoseris
Therodry grassland
scabra
Brachypodietea
Hyparrhenia
dry grassland
hirta
tenacissimae
9
0
9#
6
2
9
1
8
1
0
8
3
8
x
1
7
3
8
6
1
8
1
8
5
0
9
8
x
6
x
8
4
8
9
2
9
8
8
7
6
7
5
9#
8
4
7
5°
8
7
1
8
4
8
5
1
1
-1
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Indicators
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Hypochaeris
achyrophorus
Hypochaeris
glabra
Imperata
cylindrica
Juncus acutus
Juncus
bufonius
Juncus
heldreichianus
Juncus
hybridus
Juncus
maritimus
Juncus sp.
Juncus
subulatus
Juniperus
phoenicea
Lactuca
serriola
Lactuca
tuberosa
Lagurus
dry grassland
dry grassland
TheroBrachypodietea
TheroBrachypodietea
7
3
x
4
1
8
4
x
3
1
halophytic
Juncetea maritimi
8
6
8
4
2
halophytic
Juncetea maritimi
8
8
7
7
2
wetland
Isoeto-anojuncetea
7
7
7
5
0
halophytic
Juncetea maritimi
7
8°
8
6
x
wetland
Isoeto-anojuncetea
8
7
8
7
0
halophytic
Juncetea maritimi
8
7
7
6
6
8
8
8
7
3
{8}
2
8
x
x
8
6
x
8
0
Y
VU
D1+2
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Indicators
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
1
1
1
-1
-1
halophytic
phrygana/maquis/ev
ergreen woodland
Synanthropic
synanthropic
mediae)
wetland
dry grassland
Poetea bulbosae?
7
3
7
3
0
dry grassland
Thero-
8
x
8
6
1
1
1
-1 -1
-1
ovatus
Lathyrus
UNKN
blepharicarpus
Launaea
fragilis
Limbarda
crithmoides
Limonium
cyprium
Limonium
echioides
Limonium
meyeri
Limonium sp.
Limonium
virgatum
?
?
?
?
0
phrygana/maquis/ev
ergreen woodland
halophytic
-1
2
9#
7
5
8
1
8
7
3
7
6
8
8
x
8
6
6
7
5
7
7
1
Linum strictum dry grassland
7
x
8
5
1
Lithodora
hispidula
7
1
8
1
1
halophytic
dry grassland
halophytic
Juncetea maritimi
Saginetea
maritimae?
TheroBrachypodietea
Salicornietea
fruticosae
Y
-1
1
1
1
LC
-1
halophytic
halophytic
Linum bienne dry grassland
halophytic
Salicornietea
fruticosae
TheroBrachypodietea
Juncetea maritimi
Y
VU
-1
1
1
1
-1
1
D2
UNKN
TheroBrachypodietea
phrygana/maquis/ev
ergreen woodland
shrub/Woodland
1
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Brachypodietea
9
Linum
maritimum
Linum sp.
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Lolium rigidum synanthropic
Lolium sp.
UNKN
Lotus
corniculatus
wetland
var. tenuifolius
Lotus
aerohaline
cytisoides
Quercetea ilicis)
Synanthropic
mediae)
MolinioArrhenatheretea
Crithmo-taticetea
Synanthropic
Lotus edulis
synanthropic
mediae)
TheroLotus
ammophilous
Brachypodietea:
halophilus
Malcolmietalia?
shrub/Pegano
Lycium
harmalaeshrub/halophytic
schweinfurthii
Salsoletea
vermiculatae
Synanthropic
Malva
synanthropic
parviflora
mediae)
Medicago
UNKN
constricta
TheroMedicago
ammophilous
Brachypodietea:
littoralis
Malcolmietalia
Y
EN
B1ab(iii,v)
+2ab(iii,v)
7
5
8
8
7
4
7
3
8
2
8
7
3
7
4°
8
7
1
8
2
9#
6
3
9
1
8
8
3
7
5
8
8
0
7
4
x
6
0
8
2°
8
7
2
1
-1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Medicago
minima
synanthropic
Medicago
polymorpha
synanthropic
Medicago sp.
UNKN
Medicago
truncatula
Melilotus
indicus
Melilotus
sulcatus
Micromeria
nervosa
Myrtus
communis
Ammophiletea
Synanthropic
mediae)
Synanthropic
mediae)
Synanthropic
synanthropic
mediae)
wetland
Holoschoenetalia
vulgaris
Synanthropic
synanthropic
mediae)
phrygana/maquis/ev
ergreen woodland
phrygana/maquis/ev
shrub/Woodland ergreen woodland
(Cisto-
4
8
8
3
7
3
8
7
1
7
5°
x
7
1
7
3°
x
6
1
8
5
8
7
1
8
6
8
7
2
8
3°
8
4
1
6
8
x
x
1
-1
-1
1
1
1
-1
Sand
Content
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Protected
IUCN
category
IUCN
criteria
Light (L)
9
Indicators
EC
ammophilous
Vegetation class
threatened
group
Ellenberg Indicator
Values
Cl-
Medicago
marina
Vegetation
endemic
Taxon
status
Consulting CYPRUS
1
Nerium
oleander
wetland
Nerio-Tamaricetea
phrygana/maquis/ev
ergreen woodland
Noaea
shrub/Woodland (Cistomucronata
phrygana/maquis/ev
ergreen woodland
Odontites linkii
shrub/Woodland (Cistosubsp. cyprius
phrygana/maquis/ev
ergreen woodland
Olea europaea shrub/Woodland (CistoMicromerieteaQuercetea ilicis)
Ononis
Therodry grassland
reclinata
Brachypodietea
TheroOnonis serrata dry grassland
Brachypodietea
TheroOnonis
Brachypodietea:
ammophilous
Cutandietalia
variegata
maritimae
Orchis
Moliniowetland
fragrans
Arrhenatheretea
Ornithogalum
dry grassland
Poetea bulbosae?
pedicellare
Y
LC
Y
Y
LC
7
7
x
5
1
8
1
9#
7
x
7
3
8#
4
0
7
2°
8
4
1
7
2
8
5
1
9
1
8
5
3
9
6
9#
7
3
7
6
7
5
1
7
5
8
7
0
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
pes-
Pancratium
maritimum
Parapholis
incurva
Parapholis
marginata
Parapholis sp.
Parentucellia
latifolia
Paronychia
argentea
Paronychia
macrosepala
Phagnalon
rupestre
subsp.
rupestre
Phragmites
australis
Pinus brutia
?
?
?
?
?
synanthropic
Synanthropic
ali
(mainly Artemisietea en
mediae)
x
4
8
7
1
ammophilous
Ammophiletea
NT
8
4
9#
5
3
LC
8
6*
9#
6
7
8
6°
9#
6
8
halophytic
halophytic
Saginetea
maritimae
Saginetea
maritimae?
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
Protected
Poetea bulbosae?
Indicators
Sand
Content
Oxalis
caprae
Ellenberg Indicator
Values
EC
Orobanche
minor
var. dry grassland
minor
Orobanche sp. UNKN
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
-1
1
1
-1
1
-1
1
-1
-1
1
1
UNKN
dry grassland
Poetea bulbosae
7
5
7
5
1
dry grassland
Poetea bulbosae
7
2
8
?
1
8
x
8
5
x
1
9
2
8
8
1
1
7
10°
8
7
2
{7}
3
7
2
1
TheroBrachypodietea?
phrygana/maquis/ev
ergreen woodland
Phragmitowetland
Magnocaricetea
phrygana/maquis/ev
shrub/Woodland
ergreen woodland
dry grassland
1
1
-1
-1
-1
1
Pinus
halepensis
phrygana/maquis/ev
ergreen woodland
Synanthropic
synanthropic
mediae)
phrygana/maquis/ev
ergreen woodland
Pistacia
shrub/Woodland (Cistolentiscus
Synanthropic
Plantago afra synanthropic
mediae)
Plantago
dry grassland
Poetea bulbosae
albicans
Plantago
Therodry grassland
amplexicaulis
Brachypodietea
Plantago
Therodry grassland
bellardii
Brachypodietea
Plantago
coronopus
Saginetea
halophytic
subsp.
maritimae
commutata
Piptatherum
miliaceum
alien
7
3
6
2
1
7
4°
8
5
1
{7}
x
8
x
x
7
3°
8
5
1
8
2
8
4
2
9
1
8
4
2
7
3
8
4
1
8
5°
8
6
2
1
1
1
1
-1
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
dry grassland
TheroBrachypodietea?
TheroBrachypodietea
4
8
5
0
7
4
8
6
1
9
7
8
7
5
halophytic
Juncetea maritimi
ammophilous
Ammophiletea?
wetland
Nerio-Tamaricetea
9
7
8
7
6
ammophilous
Ammophiletea
9
5
8
5
2
7
6
x
6
x
x
3
x
5
1
9
3
9#
5
3
7
x
x
3
1
7
x
8#
x
1
Saginetea
maritimae
phrygana/maquis/ev
ergreen woodland
Prasium majus shrub/Woodland (CistoMicromerieteaQuercetea ilicis)
TheroPseudorlaya
Brachypodietea:
ammophilous
pumila
Cutandietalia
maritimae
Synanthropic
Psilurus
synanthropic
incurvus
mediae)
Rhamnus
phrygana/maquis/ev
shrub/Woodland
oleoides
ergreen woodland
halophytic
1
1
Sand
Content
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Protected
IUCN
category
IUCN
criteria
Light (L)
7
Indicators
EC
dry grassland
Vegetation class
threatened
group
Ellenberg Indicator
Values
Cl-
Plantago
cretica
Plantago
lagopus
Plantago
maritima
subsp.
crassifolia
Plantago
sarcophylla
Polygonum
equisetiforme
Polygonum
maritimum
Polypogon
maritimus
Vegetation
endemic
Taxon
status
Consulting CYPRUS
-1
-1
1
-1
-1
-1
1
-1
-1 -1
-1
1
Rostraria
cristata
Rubia
tenuifolia
Saccharum
ravennae
Salicornia
europaea
Salsola tragus
Samolus
valerandi
Sarcocornia
perennis
1
1
Sand
Content
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
Protected
Indicators
EC
Romulea
ramiflora
Ellenberg Indicator
Values
Cl-
subsp.
graecus
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
dry grassland
Poetea bulbosae
Synanthropic
synanthropic
mediae)
phrygana/maquis/ev
ergreen woodland
8
7
8
6
1
8
4°
8
7
x
6
x
8
x
1
halophytic
Juncetea maritimi
7
7
9#
6
1
halophytic
Thero-Salicomietea
9
8
9#
x
8
ammophilous
Cakiletea maritimae
8
4
8
8
4
wetland
Adiantetea
6
8
x
5
2
8
8
9#
6
6
8
4
7
4
1
8
8°
9#
x
x
Salicornietea
fruticosae
phrygana/maquis/ev
ergreen woodland
Sarcopoterium
shrub/Woodland (Cistospinosum
Schoenus
halophytic
Juncetea maritimi
nigricans
halophytic
1
1
1
-1
-1
1
-1
-1
Scirpoides
halophytic
holoschoenus
Scorpiurus
muricatus var. dry grassland
subvillosus
Senecio
leucanthemifoli dry grassland
us
Senecio
vulgaris
synanthropic
Serapias
vomeracea
wetland
Silene
macrodonta
Silene
sedoides
Silene sp.
8
x
x
1
TheroBrachypodietea
7
5°
8
6
1
8
2
8
6
1
7
4
x
7
1
7
5°
8
4
1
9
4
8
7
1
8
4
8
7
2
7
4
8
x
2
8
1
9#
7
7
{4}
6°
7
2
0
TheroBrachypodietea/Crit
hmo-taticetea
Synanthropic
mediae)
Holoschoenetalia
vulgaris
Y
TheroBrachypodietea
LC
Crithmo-taticetea
UNKN
phrygana/maquis/ev
ergreen woodland
Smilax aspera shrub/Woodland
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Light (L)
7
dry grassland
aerohaline
Ellenberg Indicator
Values
Juncetea
maritimi/MolinioArrhenathereteaHoloschoenetalia
vulgaris
Silene apetala dry grassland
Silene colorata dry grassland
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Sonchus
oleraceus
synanthropic
Sonchus sp.
UNKN
Quercetea ilicis)
Synanthropic
mediae)
7
5°
8
8
1
8
5°
8
7
2
8
7
9#
6
9
Ammophiletea
9
6
8
6
5
Stipa capensis dry grassland
TheroBrachypodietea
9
1
9#
7
1
Suaeda
maritima
halophytic
Thero-Salicornietea
8
x
8
7
7
Suaeda vera
halophytic
Salicornietea
fruticosae
8
x
8
6
5
Tamarix sp.
Tamarix
tetragyna
wetland
8
x
1
Sonchus
tenerrimus
Spergularia
marina
Sphenopus
divaricatus
Sporobolus
virginicus
Teucrium
divaricatum
subsp.
canescens
synanthropic
halophytic
halophytic
ammophilous
wetland
Synanthropic
mediae)
Saginetea
maritimae
Saginetea
maritimae
Nerio-Tamaricetea?
phrygana/maquis/ev
ergreen woodland
8
Y
LC
7
2
1
1
1
1
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
1
phrygana/maquis/ev
ergreen woodland
Teucrium
shrub/Woodland (Cistomicropodioides
MolinioTeucrium
Arrhenatheretea:
scordium
wetland
Agrostion
subsp.
stoloniferae
scordioides
phrygana/maquis/ev
ergreen woodland
Thymelaea
shrub/Woodland (Cistohirsuta
Trachynia
Therodry grassland
distachya
Brachypodietea
Synanthropic
Trifolium
synanthropic
angustifolium
mediae)
Trifolium
Therodry grassland
campestre
Brachypodietea
Trifolium
UNKN
pamphylicum
Trifolium
Therodry grassland
scabrum
Brachypodietea
Triglochin
halophytic
Juncetea maritimi
bulbosa
TheroTriplachne
ammophilous
Brachypodietea:
nitens
Cutandietalia
Y
LC
Y
VU
C2a(i)
7
8
7
6
1
8
4
8
5
1
6
x
8
x
1
7
6
7
5
1
7
4°
x
x
1
7
2
8
5
1
7
10
9#
7
5
8
1
8
6
2
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Vehicle
Indicators
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
Urginea
maritima
Valantia
hispida
Verbascum
sinuatum
Vulpia
fasciculata
Vulpia sp.
Zygophyllum
album
maritimae
phrygana/maquis/ev
ergreen woodland
Therodry grassland
Brachypodietea
dry grassland
tenacissimae
ammophilous
Cutandietalia
maritimae
UNKN
Pegano harmalaehalophytic
Salsoletea
vermiculatae
7
4°
8
7
1
7
4°
8
x
2
7
5
8
8
0
8
3
8
6
2
9
0
9#
7
6
1
Sand
Content
EC
Cl-
Organic
matter
PO3-
Moisture
Content
Grazing
Vehicle
Waste
Recent
Disturba
nce
Waste
Fire
Indicators
Vehicle
Moisture
(F)
Reaction
(R)
Nutrient
(N)
Salt (S)
Grazing
Ellenberg Indicator
Values
Light (L)
Protected
Vegetation class
IUCN
category
IUCN
criteria
group
threatened
Vegetation
endemic
Taxon
status
Consulting CYPRUS
1
-1
1
1
1
1
-1
-1
-1
1
1
1
Consulting CYPRUS
Annex A
Habitat monitoring - Forms for habitat mapping
Annex A.a: GIS database fields
Field Title
ID
Mixed
Data Type
Number
Boolean
HBCDAX_1
Text
EUNIScode_1
Text
HBCDAX_2
Text
EUNIScode_2
Text
Area
Area_1
Number
Number
Area_2
ReleveNr_1
Number
Number
ReleveNr_2
Number
Date
Qualifier
Date
Boolean
Author
Comment
Text
Text
Field Description
Polygon Code
YES = mixed polygon (2 habitat types), NO = simple polygon (1
habitat type)
4digit Annex I habitat type code (in mixed polygons it is the code of
the first habitat, the one with the largest cover in the polygon)
EUNIS habitat code, at the highest level possible (in mixed polygons it
is the code of the first habitat, the one with the largest cover in the
polygon)
4digit Annex I habitat type code (in mixed polygons it is the code of
the second habitat, the one with the smallest cover in the polygon)
EUNIS habitat code, at the highest level possible (in mixed polygons it
is the code of the second habitat, the one with the smallest cover in the
polygon)
Polygon area óå m2
% cover of the first habitat (HBCDAX_1) in the polygon (if the
polygon is simple, the value is 100)
% cover of the second habitat (HBCDAX_1) in the polygon
TURBOVEG releve number of the sample (HBCDAX_1) in the first
habitat in the polygon
TURBOVEG releve number of the sample (HBCDAX_2) in the first
habitat in the polygon
Date when the mapping was performed
YES = any of the data of the polygon need confirmation or further
work, NO = the data of the polygon do not need confirmation or further
work
Name of the author of the mapping data
Free text with comments and notes on the polygon
223
Consulting CYPRUS
Annex A.b: Sampling form for habitat identification (species list)
HABITAT IDENTIFICATION FORM
No Sample (Field)
No Releve TW
Type of Sample
GPS point
Releve area (m2)
Altitude (m)
Relief
Exposition (°)
Inclination (°)
Water depth (cm)
P1
P
P2
S
R
R
D
Habitat Code (Annex I)
EUNIS Habitat Code
Location
Author(s)
Date
Substrate
Vegetation Unit
Photos
Cover %
Mean Height
Tree layer (T)
Shrub layer (S1)
Shrub layer (S2)
Herb layer (H1)
Herb layer (H2)
Threat
Trampling (vehicle)
Trampling (foot)
Inert material disposal
Waste disposal
Building
Tar
Cover %
Total T+S
Total H
Total plant cover
Moss
Bare rock
Bare stone/pebble
Cover %
Intensity
Threat
Fire (recent)
Fire (old)
Cultivation (recent)
Cultivation (old)
Grazing (current)
Grazing (old)
Cover %
Intensity/Freq
Last
Threats
Notes
Species
Cover
Layer Species
Cover
224
Layer
Consulting CYPRUS
Field Description of habitat identification form
Field
No Sample (Field)
No Releve TW
Type of Sample
GPS point
Releve area (m2)
Altitude (m)
Relief
Exposition (°)
Inclination (°)
Water depth (cm)
Habitat Code (Annex I)
EUNIS Habitat Code
Location
Author(s)
Date
Substrate
Vegetation Unit
Photos
Tree layer (T)
Shrub layer (S1)
Shrub layer (S2)
Herb layer (H1)
Herb layer (H2)
Total T+S
Total H
Total plant cover
Moss
Bare rock
Bare stone/pebble
Trampling (vehicle)
Trampling (foot)
Waste disposal
Building
Tar
Fire (recent)
Fire (old)
Cultivation (recent)
Cultivation (old)
Grazing (current)
Grazing (old)
Threats
Notes
Species
Explanation
Number of field sample
Releve number in TURBOVEG database (not to be filled on site)
P1=only dominant and characteristic species in the polygon recorded, P2=all species in the polygon recorded,
R=phytosociological relevé (all species recorded)
Name of GPS point
Area of sampling quadrat (for phytosociological relevé only)
Altitude in m (can be retrieved from downloaded GPS points)
P=plane, S=slope, R=ridge, D=depression
Quadrat exposition in degrees (for phytosociological relevé only)
Quadrat inclination in degrees (for phytosociological relevé only)
Water depth at the time of sampling (when relevent)
Annex I habitat code for the polygon/releve
EUNIS habitat code for the polygon/releve
Name or description of location of polygon
Field surveyors
Field survey date
Geological substrate
Description of the vegetation unit
Name/Number of photo
cover % and mean height of woody plants, including climbers, height > 5 m
cover % and mean height of woody plants, including climbers, height < 5 m
cover % and mean height of woody plants, including climbers < 1 m
cover % and mean height of herbs > 1 m
cover % and mean height of herbs < 1 m
Total cover % of woody plants (all layers)
Total cover % of herbs (all layers)
Total cover % of vegetation
Total cover % of mosses
Total cover % of bare rock
Total cover % of stones and/or pebbles
Area % of polygon affected by threat and intensity (in scale 1-5)
Area % of polygon affected by previous year fire incident
Area % of polygon affected by older fire incident, fire frequency, and year of last incident
Area % of polygon affected by previous year cultivation
Area % of polygon affected by older cultivationand year of last incident
Area % of polygon affected by current grazing and intensity (in scale 1-5)
Area % of polygon affected by older grazing incident, intensity (in scale 1-5), and year of last incident
Free text with description or comments on threats
Free text with any additional notes
Taxon name, cover abundance, and vegetation layer where it occurs
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Annex A.c: Mapping notes form
FIELD NOTES
GPS point
Date
Author
Note
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Annex B
Habitat monitoring - Forms for vegetation transects
Annex B.a: Vegetation transect forms
Field Description of vegetation transect forms
Field
Transect
Length (m)
Quadrat size (m2)
GPS point start
GPS point end
Author(s)
Date
Other threat1
Explanation
Name of Transect (e.g., T1)
Transect length
Size of quadrats in transect
Name of GPS point at the start of the transect
Name of GPS point at the end of the transect
Field surveyors
Field survey date
Free text with any notes
Vegetation zone in which the quadrat is located, denoted by habitat code or other
description if ncecessary
Distance of quadrats in the zone (the first quadrat is located at the start of the zone )
Name of GPS point where the vegetation zone starts
P=plane, S=slope, R=ridge, D=depression
Quadrat exposition in degrees
Quadrat inclination in degrees
Geological substrate
Water depth at the time of sampling
cover % and mean height of woody plants, including climbers, height > 5 m
cover % and mean height of woody plants, including climbers, height < 5 m
cover % and mean height of woody plants, including climbers < 1 m
cover % and mean height of herbs > 1 m
cover % and mean height of herbs < 1 m
Total cover % of woody plants (all layers)
Total cover % of herbs (all layers)
Total cover % of vegetation
Total cover % of mosses
Total cover % of bare rock
Total cover % of stones and/or pebbles
Intensity of threat (in scale 1-5)
YES=fire incident the previous year, NO=no fire incident the previous year
Year of the last fire in the quadrat
Year in which the quadrat was last cultivated
Year in which the quadrat was last grazed
Intensity of other type threat (in scale 1-5) (specify the threat)
Other threat1
Species
Intensity of other type threat (in scale 1-5) (specify the threat
Taxon name and cover abundance per transect
Notes
Vegetation zone
Distance of quadrats
GPS zone start
Relief
Exposition (°)
Inclination (°)
Substrate
Water depth (cm)
Tree layer (T)
Shrub layer (S1)
Shrub layer (S2)
Herb layer (H1)
Herb layer (H2)
Total T+S
Total H
Total plant cover
Moss
Bare rock
Bare stone/pebble
Trampling (vehicle)
Trampling (foot)
Waste disposal
Building
Tar
Fire (recent)
Fire (last)
Cultivation (last)
Grazing (current)
Grazing (last)
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VEGETATION TRANSECT FORM 1 - HEADERS
Transect No:
Quadrat size (m)
Length (m)
Author
GPS point start
Date
GPS point end
Q1
Vegetation Zone
Distance of quadrats
GPS zone start
Relief
Exposition (°)
Inclination (°)
Water depth (cm)
Substrate
Tree layer (T) %
Shrub layer (S1) %
Shrub layer (S2) %
Herb layer (H1) %
Herb layer (H2) %
Total T+S %
Total H %
Total plant cover %
Moss %
Bare rock %
Bare stone/pebble %
Trampling (vehicle)
Trampling (foot)
Waste disposal
Building
Tar
Q2
Q3
Q4
Q5
Notes
Q6
Q7
Q8
Q9
Q10
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Fire (recent)
Fire (last)
Fire (frequency)
Cultivation (last)
Grazing (current)
Grazing (last)
Other threat1
Other treat2
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VEGETATION TRANSECT FORM 2 - SPECIES
Transect No:
Author
Notes
Date
Species
Q1
Q2
Q3
Q4
Q5
Q6
Q7
Q8
Q9
Q10
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Annex B.b: Abiotic parameters form
Transect
Quadrat
Date
Parameter
WD SM
Value
Notes
EC
Description
Transect
Quadrat
Date
Parameter
Value
Notes
Number of vegetation transect (i.e. T1)
Number of quadrat in transect (i.e. T2)
Date of survey
WD=water depth, SM=soil moisture, EC=electric conductivity
Value of parameter
Free text with any notes on parameter measurement
233
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Annex C
Forms for flora species monitoring
Annex C.a: Species mapping form
FLORA SPECIES MAPPING FORM
Species Name
Locality
Author
Date
Threats
Notes
Polygon GPS point
Habitat
Photo
234
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Location and polygons scetch
235
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Annex C.b: Species population monitoring forms
FLORA SPECIES POPULATION MONITORING FORM
Species Name
Locality
Author
Date
Notes
Polygon GPS point(s)
Number of individuals
Photo
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Field Description for species mapping form
Field
Species Name
Locality
Author
Date
Threats
Notes
Polygon
GPS point
Habitat
Photo
Description
Name of the plant species
Name of description of locality of survey
Author of survey data
Date of survey
Free text regarding the threats for the plant in the locality
Free text regarding the plant
Name or code of polygon delimiting the distribution of the plant (e.g. P1)
Name of GPS point delimiting the polygon (3 or more points for each
polygon, one row per point)
Habita of the plant at point/points/polygon (detailed description)
Name/number of photo in the camera
Field Description for species population monitoring form
Field
Species Name
Locality
Author
Date
Notes
Polygon
GPS point(s)
Number of individuals
Photo
Description
Name of the plant species
Name of description of locality of survey
Author of survey data
Date of survey
Free text regarding the plant
Name or code of polygon delimiting the distribution of the plant (e.g.
P1), according to the mapping form
Name of GPS point(s) delimiting a partial polygon in case the population
size is estimated in a smaller polygon or point within the distribution
polygon
Number of adult individuals or tufts, depending on the population unit
used for the plant
Name/number of photo in the camera
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Appendix III
Groundwater level depth data
239
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240
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241
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242
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244
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245
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246
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248
884
HRA Runway Lights
884
HRA Runway Lights

Cyprus - Sovereign Base Areas Administration

Transcription

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