(CTWSRO): Pacific Lamprey Passage Evaluation and Mitigation Plan

Transcription

Pacific Lamprey Passage Evaluation and
Mitigation Plan:
Phase I - Habitat Assessment for Potential
Re-introduction of Pacific Lamprey Upstream of
Pelton-Round Butte Hydroelectric Project
Final
Confederated Tribes of the Warm Springs Reservation of Oregon, Branch of
Natural Resources, Fisheries Research
March 2012
Contents
Introduction ..................................................................................................................................... 1
Study Area ...................................................................................................................................... 4
Chapter 1: Pacific lamprey overwintering and spawning habitats, and spawn timing in the lower
Deschutes Basin .............................................................................................................................. 6
1.1 Introduction ........................................................................................................................... 6
1.2 Study Area ............................................................................................................................ 6
1.3 Methods................................................................................................................................. 6
Upstream Overwintering and Spawning Migrations .............................................................. 6
Spawning Locations and Habitat ............................................................................................ 9
Data Analyses ....................................................................................................................... 11
1.4 Results ................................................................................................................................. 12
Radio-tagging and Tracking ................................................................................................. 12
1.5 Discussion ........................................................................................................................... 30
Patterns of Migration ............................................................................................................ 30
Pre-holding Migration Relative to Environmental Factors ................................................... 31
Location, Time of Spawning and Redd Characteristics........................................................ 31
Chapter 2: Capture efficiency of standard, ammocoete (larval lamprey) - survey gear under
varying environmental conditions, fish sizes and densities .......................................................... 34
2.1 Introduction ......................................................................................................................... 34
2.2 Study Area .......................................................................................................................... 34
2.3 Methods............................................................................................................................... 37
Electrofishing ........................................................................................................................ 37
Shock Duration ..................................................................................................................... 37
Experimental Enclosures ...................................................................................................... 38
Ammocoete Length and Density .......................................................................................... 40
Substrate................................................................................................................................ 41
Environmental Variables ...................................................................................................... 41
Data Analysis ........................................................................................................................ 43
2.4 Results ................................................................................................................................. 44
2.5 Discussion ........................................................................................................................... 52
Chapter 3: Ammocoete abundance as a function of measured environmental variables in the
field, downstream of PRB ............................................................................................................. 53
3.1 Introduction ......................................................................................................................... 53
3.2 Study Area .......................................................................................................................... 53
3.3 Methods............................................................................................................................... 56
Site Selection ........................................................................................................................ 56
Electro-fishing....................................................................................................................... 56
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Data analysis ......................................................................................................................... 59
3.4 Results ................................................................................................................................. 59
3.5 Discussion ........................................................................................................................... 62
Chapter 4: Theoretical estimate of ammocoete abundance in the Metolius, Crooked, and
Deschutes rivers, based on thermograph and habitat data ............................................................ 66
4.1 Introduction ......................................................................................................................... 66
Literature Review of the Effects of Water Temperature on Lamprey Rearing Ammocoetes
and Spawning Adults ............................................................................................................ 67
4.2 Study Area .......................................................................................................................... 68
4.3 Methods............................................................................................................................... 70
4.4 Results ................................................................................................................................. 71
Water temperature ................................................................................................................. 71
Habitat Area .......................................................................................................................... 83
Theoretical abundance estimate of ammocoetes in habitats suitable for re-introduction
upstream of PRB ................................................................................................................... 86
4.5 Discussion ........................................................................................................................... 89
Conclusions ................................................................................................................................... 91
References ..................................................................................................................................... 93
Appendices .................................................................................................................................... 98
Appendix 1. Pacific lamprey redd survey measurements. ....................................................... 99
Appendix 1 (cont.). Pacific lamprey redd survey measurements. ......................................... 100
Appendix 1 (cont.). Pacific lamprey redd survey measurements. ......................................... 101
Appendix 2. Group membership and overwinter locations of radio-tagged lamprey............. 102
Appendix 2 (cont.) . Group membership and overwinter locations of radio-tagged lamprey. 103
Appendix 3. Group membership and spawning locations of radio-tagged larmpreys. .......... 104
Appendix 3 (cont.). Group membership and spawning locations of radio-tagged larmpreys.
................................................................................................................................................. 105
Appendix 4. Site descriptions for Capture Efficiency Model development. .......................... 106
Appendix 5. Enclosure design. .............................................................................................. 107
Attachment A – Consultation with the Fish Committee
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Table of Figures
Figure 1. Flow diagram showing the relationships between, and the chronology of, possible
implementation paths for the Pacific Lamprey Passage Evaluation and Mitigation Plan (PGE and
CTWSRO 2006).............................................................................................................................. 2
Figure 2. Map of lower Deschutes Basin adult Pacific lamprey study locations, 2005 –2009. .... 5
Figure 3. Vicinity map of lamprey redd study reaches in Shitike and Beaver creeks, lower
Deschutes River Subbasin, 2008 - 2009. ...................................................................................... 10
Figure 4. Frequency of detections at fixed-site receiving locations in the lower Deschutes and
Warm Springs basins by month, 2005 – 2009. ............................................................................. 14
Figure 5. Frequency of detections at fixed-site receiving locations in the lower Deschutes and
Warm Springs basins by hour, 2005 – 2009. ................................................................................ 15
Figure 6. Pacific lamprey fall migration in response to daily average water temperature, 2005 2009............................................................................................................................................... 19
Figure 7. Pacific lamprey fall migration in response to one-day change in discharge (cfs), 2005 2009............................................................................................................................................... 19
Figure 8. Dendrogram of Pacific lamprey grouped by overwinter locations. ............................. 21
Figure 9. Overwinter locations, by group, for Pacific lamprey in the Deschutes Basin, 2005 2009............................................................................................................................................... 22
Figure 10. Dendrogram of Pacific lamprey grouped by spawning locations. ............................. 24
Figure 11. Spawning locations, by group, for Pacific lamprey in the lower Deschutes Basin,
2005-2009. .................................................................................................................................... 25
Figure 12. Pacific lamprey redd locations in Beaver Creek, lower Deschutes River Subbasin,
2008 – 2009................................................................................................................................... 27
Figure 13. Pacific lamprey redd locations in Shitike Creek, lower Deschutes River, 2008 – 2009.
....................................................................................................................................................... 28
Figure 14. Hydrographs of Beaver and Shitike creeks, lower Deschutes River Subbasin, MayJuly 2008-09.................................................................................................................................. 33
Figure 15. Pacific lamprey ammocoete capture efficiency study sites in the lower Deschutes
River Subbasin, 2007 - 2008. ........................................................................................................ 35
Figure 16. Experimental net enclosures in Badger Creek, November 2007. ............................... 39
Figure 17. Number of ammocoetes captured versus depth (cm) of fine sediments during
distribution surveys in the lower Deschutes River Subbasin, 2002-2006. Seventy-five percent
and 96% of ammocoetes were caught at depths less than 15 cm and 30 cm, respectively. .......... 39
Figure 18. Length frequency of ammocoetes captured during distribution surveys in the lower
Deschutes River Subbasin, 2002-2006. ........................................................................................ 40
Figure 19. Model intercept versus electrofishing pass................................................................. 46
Figure 20. Observed vs. predicted capture efficiency for Pass 1. ................................................ 47
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Figure 25. Ammocoete habitat model study reaches (dark blue) in Warm Springs River, Badger,
Beaver, and Shitike creeks, lower Deschutes River Subbasin, 2009. ........................................... 55
Figure 26. Scatter plot of ammocoete abundance (log10) and water temperature (°C) in Shitike
Creek, 2009. .................................................................................................................................. 61
Figure 27. Length-frequency of ammocoetes in Shitike Creek and streams in the Warm Springs
Subbasin. ....................................................................................................................................... 63
Figure 28. Area of maximum potential re-colonization for Pacific lamprey upstream of Lake
Billy Chinook. ............................................................................................................................... 69
Figure 29. Water temperature in the Metolius River near Grandview (USGS 14091500) May
through September, 2009 with respect to temperature range for lamprey spawning. .................. 73
Figure 30. Water temperature in the Metolius River at Bridge 99 (USFS) June through
September, 2009 with respect to temperature range for lamprey spawning. ................................ 74
Figure 31. Area of potential re-colonization for Pacific lamprey upstream of Lake Billy
Chinook, limited by water temperature (cold springs represented by small circles). ................... 75
Figure 32. Water temperature in Abbot Creek (USFS) June through September, 2009 with
respect to temperature range for lamprey spawning. .................................................................... 76
Figure 33. Water temperature in Lake Creek (USFS) June through September, 2009 with respect
to temperature range for lamprey spawning. ................................................................................ 77
Figure 34. Water temperature in the Deschutes River near Culver (USGS 14076500) May
Figure 35. Water temperature in the Deschutes River at Lower Bridge Road (UDWC DR_13350) May through July, 2009 with respect to temperature range for lamprey spawning and rearing.
....................................................................................................................................................... 79
Figure 36. Water temperature in Whychus Creek downstream of Alder Springs (UDWC
WC001_50) May through September, 2009 with respect to temperature range for lamprey
spawning. ...................................................................................................................................... 80
Figure 37. Water temperature in the Crooked River below Opal Springs (USGS 14087400) May
Figure 38. Water temperature in the Crooked River at Smith Rock State Park near Terrebonne
(USBOR CRSO) May through September, 2009 with respect to temperature range for lamprey
spawning. ...................................................................................................................................... 82
Figure 39. Water temperature in the Crooked River below Bowman Dam (USBOR PRVO) May
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Table of Tables
Table 1. Adult lamprey capture, release sites, and fixed-site telemetry receiver locations ........... 7
Table 2. Dates of aerial surveys to track Pacific lamprey movements in the lower Deschutes
River Subbasin, 2005 - 2009. .......................................................................................................... 9
Table 3. Environmental variables as potential predictors for Pacific lamprey migration rates. .. 11
Table 4. Descriptive statistics for radio-tagged Pacific lamprey in the lower Deschutes River
Subbasin, 2005 - 2008................................................................................................................... 13
Table 5. Number of days from release site past fixed-site antennae for fall migrating Pacific
lamprey, 2005 - 2009. ................................................................................................................... 15
Table 6. Pacific lamprey detected at fixed-site antennae during post-holding migration, 2005 2009............................................................................................................................................... 17
Table 7. Model predictors with sensitivity and tolerance values for Pacific lamprey in the lower
Deschutes River Basin, 2005 - 2009. ............................................................................................ 18
Table 8. Overwintering locations, as determined by the dendrogram, for Pacific lamprey
overwintering locations in the lower Deschutes River Subbasin, 2005 - 2009. ........................... 21
Table 9. Spawning locations, as determined by the dendrogram, for Pacific lamprey
overwintering locations in the lower Deschutes River Subbasin, 2005 - 2009. ........................... 24
Table 10. Descriptive statistics for Pacific lamprey redd physical characteristics, Beaver and
Shitike creeks, lower Deschutes River Subbasin, 2008 – 2009. ................................................... 29
Table 11. Pacific lamprey capture efficiency sample sites, Warm Springs River, Badger, Beaver,
and Shitike creeks, lower Deschutes River Subbasin, 2007 - 2008. ............................................. 36
Table 12. Pacific lamprey electrofishing shock duration and rest periods for development of the
CE model, lower Deschutes River Subbasin, 2007 - 2008. .......................................................... 38
Table 13. Environmental variables measured before and immediately after electrofisher
efficiency trials in Warm Springs River, Badger, Beaver, and Shitike creeks, 2007 - 2008. ....... 42
Table 14. Environmental variables measured during electrofishing trials in the Warm Springs
River, Badger, Beaver and Shitike creeks, 2007 - 2008. .............................................................. 45
Table 15. Study reaches for ammocoete habitat model in Warm Springs River, Badger, Beaver,
and Shitike creeks, lower Deschutes River Subbasin, 2009. ........................................................ 54
Table 16. Variables for ammocoete habitat model development, Warm Springs River, Badger,
Beaver and Shitike creeks, lower Deschutes River Subbasin, 2009. ............................................ 58
Table 17. Habitat conditions in Shitike Creek, April through September, 2009. ........................ 62
Table 18. Summary of temperature thresholds and ranges for Pacific lamprey by developmental
stage. ............................................................................................................................................. 68
Table 19. Total estimated sand and silt habitat area in the Metolius River from the mouth to
Camp Creek. ................................................................................................................................. 84
Table 20. Total estimated sand and silt habitat area in the Deschutes River from Big Falls to
LBC. .............................................................................................................................................. 84
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Table 21. Total estimated sand and silt habitat area in Whychus Creek from Alder Springs to the
Deschutes River. ........................................................................................................................... 85
Table 22. Total estimated sand and silt habitat area in the Crooked River from rkm 6.9, upstream
of Opal Springs, to LBC. .............................................................................................................. 85
Table 23. Estimated potential ammocoete abundance and 95% prediction intervals for habitats
upstream of LBC. .......................................................................................................................... 87
Table 24. Ammocoete density by stream, according to water temperature and substrate. .......... 88
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Table of Equations
Equation 1
............................................................................................ 43
Equation 2
. ............................................................................................... 43
f(X)
ixi ,..................................................................................................... 43
Equation 3
Equation 4 Pass 1; y = -0.006β1 + -0.027β2 + 0.164β3 + 0.378β4 + -0.223β5 + -0.009β6 + 2.90. 45
Equation 5 Pass 2; y = -0.011β1 + -0.048β2 + 0.026β3 + 0.430β4 + -0.257β5 + -0.008β6 +4.34
....................................................................................................................................................... 45
Equation 6 Pass 3; y = -0.015β1 + -0.051β2 + 0.348β4 + -0.113β5 + 4.96 ................................ 45
Equation 7 Pass 4; y = -0.013β1 + -0.0613β2 + 0.334β4 + -0.109β5 + 5.28 ................................. 45
Equation 8 Pass 5; y = -0.014β1 + -0.068β2 + 0.316β4 + -0.173β5 + 5.75 ................................... 45
Equation 9 CP(y) = exp(y) / (1 + exp(y)), where CP is between 0 and 1. ................................ 46
Equation 10
Estimated µ {log10 ammocoete abundance/sample│water temperature, percent
canopy, sand} per 0.5625m2 area ................................................................................................. 59
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Acknowledgements
First we‟d like to thank our funding sources: Warm Springs Power Enterprise, Portland General
Electric, Bonneville Power Administration, and US Fish and Wildlife Service.
Adult overwintering and spawning habitat – Jennifer Graham developed and implemented the
study design, data management, and assisted in writing annual reports. This could not have been
accomplished without Joel Santos who captured adult Pacific lamprey and assisted in all aspects
of the study. Special thanks to Lyman Jim, Aldo Garcia, and other CTWSRO Natural Resources
employees for setting up the infrastructure, tracking, equipment maintenance, and data entry;
Debbie Docherty (BPA) for contract administration; and Bonneville Power Administration for
funding.
Capture Efficiency Model – We would like to recognize biologists, field and GIS technicians at
the Confederated Tribes of the Warm Springs Reservation of Oregon who assisted with various
aspects of this study. Jennifer Graham developed the study design. Abel Brumo assisted with
in-field study design modifications, sampling, data management, and writing annual reports.
Matt Fox and Aldo Garcia assisted with all aspects of the project including field trials, equipment
maintenance, data entry and management. Lyman Jim and Shawn Jim assisted with project
initiation and experimental enclosure construction. Shayla Frank, Sterling Kalama, Rolland
Morningowl, Isaac Santos, and Joel Santos assisted with implementation of electrofishing trials.
Special thanks to Dr. Don Stevens, Jr., Department of Statistics, Oregon State University, who
assisted with study design, statistical analyses, and review.
Ammocoete (Larval lamprey) Abundance Model – Cyndi Baker developed the study design.
Data collection was conducted by Aldo Garcia, Joel Santos, Brandon Smith, and summer youth
workers Johnson Heath, and Britten Lumpmouth. We thank Henry Franzoni, CRITFC, for
writing a macro for the Capture Efficiency Model and transforming data collected from the
Ammocoete Abundance Model (initially capture data) into abundance estimates on a per site
basis.
Potential habitat upstream of the Pelton Round Butte Project and theoretical ammocoete
abundance estimate – We thank the Upper Deschutes Watershed Council for water temperature
data on the Deschutes River and Whychus Creek, especially Lesley Jones for additional data
interpretation. Rick Kittleson, Information Specialist at U.S.G.S. in Portland, provided water
temperature data for U.S.G.S. sites. Steve Casad, U.S. Bureau of Reclamation, Bend, provided
helpful information to access Hydromet data. Alyssa Reischauer, U.S.F.S. Deschutes National
Forest, kindly provided water temperature data for the Metolius River. Cyndi Baker and Aldo
Garcia for data collection and coordinating data collection with the above people and agencies.
Special thanks to Marissa Stradley, CTWSRO GIS Support, for help with assigning random
locations for study design, making maps and providing geographic information.
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We‟d also like to acknowledge and thank the people of the Confederated Tribes of Warm
Springs Reservation of Oregon for their continual support for this project.
Study design, data analyses and authorship were completed by Cyndi Baker, Matt Fox, and Jen
Graham.
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Executive Summary
Since 2003, Pacific lamprey Lampetra tridentata ecology has been documented in the Deschutes
Basin. Local ecological knowledge of lamprey is important, particularly as adult returns
throughout the Columbia Basin continue to decline. This information will be useful in
determining the potential for re-introducing lamprey to inhabit part of its historic range upstream
of the Pelton Round Butte Hydroelectric Project (PRB).
As part of relicensing the Pelton Round Butte Hydroelectric Project, the licensees, Portland
General Electric and Confederated Tribes of Warm Springs, developed a Fish Passage Plan
approved by the Federal Energy Regulatory Commission. A component of the Fish Passage Plan
is the Pacific Lamprey Passage Evaluation and Mitigation Plan (PLEMP). In order to reestablish lamprey upstream of PRB, a series of assessments is called for in the PLEMP. The first
step was to study habitats currently occupied downstream of PRB, then identify potential habitat
upstream of PRB. Both juvenile and adult lamprey downstream of PRB were studied to
ascertain: 1) timing and locations of spawning and overwintering, 2) spawning and rearing
distribution, and 3) habitat associations. The culmination of this assessment was a theoretical
abundance estimate of Pacific lamprey ammocoetes (larval lamprey) in habitat that may be recolonized upstream of PRB.
From 2005 to 2009, radio telemetry was used to determine adult lamprey overwintering and
spawning habitats, and spawn timing in the lower Deschutes River subbasin. Over the course of
four years, we have established migration timing and behavior, and quantified habitat use to
utilize in future recovery efforts. All fish were collected at the Sherars Falls fish ladder from
approximately mid June to mid September with peak of the run occurring at the end of July.
Using a long handled dip-net, 84 lamprey were captured, implanted with a radio transmitter and
released upstream of Sherars Falls. Fifty-two were successfully radio tracked and exhibited
upstream movement or patterns consistent with spawning behavior. The remaining fish were
either mortalities, coded upon release and further movements unknown, or potential tag failures.
Lamprey were intensively tracked via mobile, aerial, boat and fixed receiving sites for
approximately one year after release. Originally presumed west-side tributary spawners, only
27% (n=18) entered west-side tributaries of the Warm Springs Reservation, including the Warm
Springs River, Beaver and Shitike creeks.
Two models were developed to help quantify the potential for habitats upstream of PRB to rear
juvenile lamprey. The first was the Capture Efficiency (CE) Model, which standardizes
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ammocoete catch via electroshocker and transforms the data to abundance so environmental
variability between sites is taken into account. The CE Model identified ammocoete length,
sediment depth, conductivity, and visibility into the water column and on top of the water (wind
ripples) as important variables. The second model is the Ammocoete Abundance Model (AAM)
which quantifies the relationship between abundance and habitat characteristics in the lower
Deschutes River. Significant variables in the AAM are water temperature and whether the
habitat patch is silt or sand. The two models, used in conjunction with water temperature and
habitat data upstream of PRB, resulted in a theoretical estimate of ammocoete abundance. The
extent of potential ammocoete rearing habitat upstream of PRB includes the Metolius River from
the mouth to Camp Creek (rkm 13.8), the Deschutes River from the head of Lake Billy Chinook
(rkm 193) to Big Falls (rkm 213), Whychus Creek from the confluence with the Deschutes River
to Alder Springs (rkm 2.4) and the Crooked River from the head of Lake Billy Chinook to Opal
Springs (rkm 6.9). It is estimated that these habitats could support approximately 4.8 million
ammocoetes (95% prediction interval = 3.7 to 7.5 million ammocoetes).
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Introduction
A major component in the issuance of the 50-year operating license for Pelton-Round Butte
Hydroelectric Project (PRB) in 2005 was to provide passage for anadromous fishes. In
conjunction with relicensing PRB, a Fish Passage Plan (Plan) was developed by the licensees,
Portland General Electric (PGE) and Confederated Tribes of Warm Springs (CTWSRO), and
approved by the Federal Energy Regulatory Commission (FERC). A fundamental piece of the
Plan is to design and construct downstream passage facilities, test and verify the performance of
the downstream passage facility, and evaluate and implement volitional upstream passage at
PRB (if volitional passage is determined to be feasible and appropriate). The primary goal of the
Plan is to maximize ecosystem integrity by supporting connectivity, biodiversity, and natural
production. A key objective of the Plan is to, “[p]rovide access to and through Project waters for
Pacific lamprey, summer-run / fall-run Chinook salmon, rainbow (redband) trout, bull trout, and
other native fish species” (Portland General Electric and Confederated Tribes of Warm Springs
Reservation of Oregon 2004).
The Pacific Lamprey Passage Evaluation and Mitigation Plan (PLEMP) was developed by
licensees with the approval of the appropriate Fish Agencies pursuant to their respective
statutory authorities (Portland General Electric and Confederated Tribes of Warm Springs
Reservation of Oregon 2006). The PLEMP has five sections (Figure 1), including: 1) habitat
assessment to further define lamprey spawning and ammocoete (larval) rearing habitat in the
Deschutes River Basin and use that information to quantify habitats suitable for production of
lamprey both upstream and downstream of the Project; 2) passage assessment to assess the
potential for outmigrant and adult Pacific lamprey passage through PRB with existing fish
passage facilities; 3) experimental reintroduction of lamprey will occur after the assessment of
lamprey passage through the Project; 4) alternative lamprey mitigation may be developed if
passage is determined by the Fish Committee to be infeasible with existing facilities; and 5) reinitiation of passage efforts will be implemented if alternative lamprey mitigation occurs and
new information demonstrates that passage is feasible.
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Figure 1. Flow diagram showing the relationships between, and the chronology of, possible
implementation paths for the Pacific Lamprey Passage Evaluation and Mitigation Plan (PGE and
CTWSRO 2006).
Historically, the range of Pacific lamprey upstream of PRB was documented in the Crooked
River through oral histories (not fish sampling activities), but it is assumed they had a similar
historic distribution as salmon and summer steelhead throughout the Columbia Basin (Portland
General Electric and Confederated Tribes of Warm Springs Reservation of Oregon 2004). Reestablishing Pacific lamprey above PRB requires adequate habitat for all developmental stages
such as appropriate substrate and water temperature. Also key is passage opportunities for
upstream and downstream migrants.
Ecological understanding of Pacific lamprey in the Pacific Northwest is limited. Recent studies
on adult and larval habitat use in the Columbia River Basin have provided important information
(Close 2002; Graham and Brun 2007; Robinson and Beyer 2005; Stone and Barndt 2005), but
information specific to the Deschutes Basin is sparse. Beginning in 2003, the CTWSRO began
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estimating Pacific lamprey adult escapement and documenting juvenile distribution and habitat
associations in the Deschutes Basin (Graham and Brun 2004). Development for adult studies
began in 2004. Subsequently, the PLEMP expanded efforts to assess lamprey habitat in the
Deschutes Basin to better understand habitat requirements and use patterns throughout all life
history stages in local populations.
To determine whether and/or to what extent re-establishment of Pacific lamprey upstream of
PRB is feasible, juvenile and adult lamprey habitat was studied downstream of PRB, in the
current, reduced range of Deschutes Basin Pacific lamprey. Based on findings from this work
and from current habitat conditions upstream of PRB, potential juvenile and adult lamprey
habitats were assessed and a theoretical abundance estimate of ammocoetes in habitats suitable
for re-introduction upstream of PRB is presented. Objectives of this study included:
1. Determine Pacific lamprey overwintering and spawning habitats, and spawn timing in the
lower Deschutes Basin (Chapter 1);
a. Conduct radio-telemetry surveys in the Deschutes River and tributaries, and
b. Conduct redd surveys in Shitike and Beaver creeks;
2. Model capture efficiency of standard, ammocoete-survey gear under varying
environmental conditions, fish sizes and densities (Chapter 2);
3. Model ammocoete abundance with measured environmental variables in the field,
downstream of PRB (Chapter 3); and
4. Quantify potential rearing habitat for ammocoetes and spawning habitat for adults in the
Metolius, Crooked (to Bowman Dam), and Deschutes rivers, and calculate theoretical
abundance estimates of ammocoetes in habitats suitable for re-introduction upstream of
PRB, based on habitat and thermograph data (Chapter 4).
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Study Area
The lower Deschutes River Subbasin (HUC 17070306, approximately 5945 km2; Oregon
Geospatial Enterprises shape file, 1:24,000 4th field HUC) is located in central Oregon and drains
the east slope of the Cascade Mountain Range (Figure 2). Pelton Reregulating Dam is the
uppermost point in the subbasin, at rkm 161. The Deschutes River has a unique flow regime
among other eastern Oregon rivers as seasonal and inter-annual flow is relatively stable due to
groundwater flow through porous volcanic soils and lava formations (Gannett et al. 2003;
Northwest Power and Conservation Council 2004).
Majority of perennial tributaries within the lower Deschutes River Subbasin originate within the
boundaries of the CTWSRO. The Reservation covers approximately 240,000 ha on the eastern
slopes of the Cascade Mountains (Northwest Power and Conservation Council 2004).
Reservation boundaries are the crest of the Cascades to the north and west, the Deschutes River
to the east, and the Metolius River to the south. The Warm Springs River is the largest
watershed within the Reservation, flowing 85 km and draining 54,394 ha into the lower
Deschutes River. Major tributaries to the Warm Springs River are Beaver, Badger, and Mill
creeks. Shitike Creek is the third largest tributary to the lower Deschutes River, flowing for 48
rkm and draining 36,000 ha.
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Figure 2. Map of lower Deschutes Basin adult Pacific lamprey study locations, 2005 –2009.
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Chapter 1: Pacific lamprey overwintering and spawning habitats, and spawn
timing in the lower Deschutes Basin
1.1 Introduction
To further ecological understanding of Pacific lamprey in the Deschutes Basin, adult lamprey
overwintering and spawning habitats, spatial and temporal patterns of use, and spawn timing
downstream of Pelton-Round Butte Hydroelectric Project (PRB) were studied from 2005 through
2009. Much of the limited information on upstream migrating Pacific lamprey behavior, timing,
and habitat use patterns has come from British Columbia (Beamish 1980; Beamish and Levings
1991; Beamish and Northcote 1989). In the Columbia River, lamprey migration has largely
focused on passage through hydroelectric facilities (Moser and Close 2003; Moser et al. 2002a;
Moser et al. 2002b). However, Robinson et al. (2005) studied adult Pacific lamprey in the John
Day Basin, providing a local example of upstream migration timing and habitat use patterns.
General patterns of overwinter and spawning migrations have emerged from literature reviews
(Kostow 2002; Wydowski and Whitney 2003) and more inaccessible theses and dissertations
(Kan 1975; Pletcher 1963; Richards 1980) cited in the aforementioned literature. Returning
adult Pacific lamprey generally migrate to freshwater between February and October (mostly
during spring), become sedentary and overwinter in deep pools with cover (e.g., boulders,
organic debris). Migration resumes to spawning grounds the following spring and spawning
occurs between March and July. Objectives of this chapter are to describe patterns of upstream
migrating Pacific lamprey overwinter and spawning behavior, habitat use and timing of
migration in the lower Deschutes Basin (HUC 17070306).
1.2 Study Area
The project was implemented in the main stem Deschutes River from its confluence with the
Columbia River to rkm160, the location of PRB, and includes west-side tributaries entering this
reach (Figure 2). A fish ladder around Sherars Falls (rkm 70.4) provides a convenient site for
collecting and marking lamprey.
1.3 Methods
Upstream Overwintering and Spawning Migrations
Adult Pacific lamprey were captured at Sherars Falls fish ladder (rkm 70.4) from mid June to
mid September and surgically implanted with radio tags. Tagged fish were typically (92%)
released at Lower Blue Hole recreation site (rkm 77.3) and tracked with mobile receivers and at
fixed site receiving locations (Table 1, Figure 2).
Adult lamprey were collected from the Sherars Falls fish ladder using a long handled dip net and
transported upstream for holding and transmitter implantation. Individuals were held up to 48
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hours prior to surgery. Sex, total length (cm), weight (g) and mid-girth (cm) measurements were
recorded prior to surgery.
Table 1. Adult lamprey capture, release sites, and fixed-site telemetry receiver locations
in the lower Deschutes River Sub-basin, 2005 - 2009.
Site Name
Stream
Rkm1 Status
1
Sherars Falls
Deschutes
70.4
Capture Location
White River Campground
Deschutes
74.9
Release Site
Lower Blue Hole Rec. Site
Deschutes
77.3
Release Site
Dant
Deschutes
99.0
Fixed Site
Mouth of Warm Springs
Warm Springs River
135.1
Fixed Site
Warm Springs Fish Hatchery
Warm Springs River
152.0
Fixed Site
Island
Beaver Creek
164.7
Fixed Site
Warm Springs Forest Products
Shitike Creek
159.4
Fixed Site
PRB Reregulating Dam
Deschutes
160.0
Passage Barrier
B-100
Badger Creek
182.5
Fixed Site
From mouth of the Deschutes River
______________________________________________________________________________
7
PLEMP Phase I Final
Unique frequency radio transmitters (Lotek Engineering, Inc., Ontario, Canada; model NTC-6-2)
were surgically implanted using methods developed by National Oceanic and Atmospheric
Administration Fisheries (Bayer et al. 2001; Robinson and Beyer 2005). Lamprey were
anesthetized prior to the implantation procedure. After being anesthetized, lamprey were placed
into a large cooler with a cylindrical tube to hold individuals during surgical procedures.
Lamprey were placed ventral side up in the trough. An incision approximately 2 cm in length
was made longitudinally, just off the mid-line. A sheathed catheter was inserted into the incision
and pierced through the musculature, approximately 1 - 3 cm posterior of the incision. The
catheter was removed, leaving the sheath. Antenna first, transmitters, were inserted through the
sheath, into the body cavity and the sheath removed. Three evenly spaced sutures using 4/0
absorbent suture material closed the incision. Once suturing was completed, oxytetracycline
(100 mg·ml-1) was injected under the sutures. Antibacterial ointment was placed along the
incision. Lamprey were moved into a covered, aerated holding box to recover and released
during or post sunset.
Fixed-site telemetry receiving stations were used to monitor movement of radio-tagged lamprey
in the lower Deschutes River Subbasin (Table 1). Six fixed receiving sites captured transmitter
signals from passing lamprey along the lower Deschutes River, Warm Springs River, Badger,
Shitike and Beaver creeks. Data collected included tag code, date, time, and signal strength.
Data were downloaded from receivers as needed (e.g., weekly during movement periods,
monthly during holding periods). Fixed-site receivers recorded data continuously throughout the
year. Water temperature data loggers (Hobo Water TempPro®, Onset Computer Corporation,
Pocassett, MA) were located adjacent to fixed receiving sites. Data were logged continuously
through the completion of spawning to record seasonal variations in water temperature.
Ground surveys consisted of a mobile tracking receiver and hand-held antenna. After the first
release of radio-tagged lamprey, ground surveys were conducted 2-4 times a week while fish
were moving. Once holding was established, surveys were conducted weekly or biweekly.
Ground tracking was accomplished by vehicle, foot and kayak to pinpoint lamprey locations.
Global Positioning System (GPS) coordinates were logged at the location of highest signal
strength. Additional data collected included: time, date, location (rkm, to the nearest tenth),
general river channel description, weather, and digital photograph.
A Citabria 150 aircraft was contracted to conduct aerial tracking. A directional antenna was
situated on the right wing strut and an omni-directional antenna was located on the belly. The
two antennae were monitored simultaneously using a Lotek wireless receiver. Frequency of
______________________________________________________________________________
8
PLEMP Phase I Final
aerial surveys was determined by rate of migration with a total of 12 aerial surveys flown
throughout the course of the study (Table 2). Aerial surveys consisted of the entire lower
Deschutes River (Pelton Reregulation Dam to Heritage Landing (rkm161.8-0), Warm Springs
River (upstream 32 km), Beaver (upstream 13 km) and Shitike (upstream 10 km) creeks.
Spawning Locations and Habitat
Redd surveys were conducted weekly in Shitike and Beaver creeks during spring and early
summer 2008 and 2009. Three adjacent reaches were surveyed in Shitike Creek, from the mouth
to rkm 11 (Figure 3). In 2008, redd surveys in Shitike Creek began April 17 and ended July 25.
In 2009, redd surveys in Shitike Creek began April 27 and ended July 30. In 2008, two reaches
in Beaver Creek were surveyed; the Highway 9 crossing (rkm 13) and Robinson Park (rkm 32,
Figure 3). In 2009, only the Highway 9 reach was surveyed, including an additional 2.4 km on
the downstream end. Robinson Park was not surveyed in 2009 due to disturbance of spawning
gravels from human activity. However, Robinson Park was spot-checked in 2009. In 2008,
redd surveys in Beaver Creek began April 22 and ended July 22. In 2009, redd surveys in
Beaver Creek began May 15 and ended July 27.
Pacific lamprey redds are similar in size to large rainbow trout or small steelhead (Onchorhychus
mykiss), and spawn timing and locations are also similar (Stone 2006; Wydowsi and Whitney
2003). However, they have a characteristic feature that distinguishes them; an anchor rock
Table 2. Dates of aerial surveys to track Pacific lamprey movements in the lower
Deschutes River Subbasin, 2005 - 2009.
2005
2006
2007
2008
2009
Nov 2
July 10
June 25
Feb 12
May 15
July 26
May 29
June 23
Aug 31
July 7
July 13
Dec 3
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9
PLEMP Phase I Final
Figure 3. Vicinity map of lamprey redd study reaches in Shitike and Beaver creeks, lower
______________________________________________________________________________
10
PLEMP Phase I Final
where lamprey attach is located on the upstream end of the redd and they place course substrate
(e.g. cobble) at the downstream edge of their nests (Kostow 2002). Surveyors visited the South
Fork Coquille River during lamprey spawning in 2007 where several hundred to over onethousand Pacific lamprey spawn (Brumo 2006) for training in redd identification. When
evidence of redd excavation was observed, locations were recorded (GPS location) and flagged
for further observation through multiple weekly passes. Habitat measurements of redds
presumed to be used for spawning were recorded included water velocity, stream width (wetted
and bank full), redd location relative to right and left banks, redd dimensions (width, internal and
external length, Appendix 1), redd depths (head, mid way, and tail), substrate, canopy cover, and
notes about riparian vegetation. Substrate measurements included the maximum diameter of 15
neighboring (touching) stones along lateral and vertical transects, originating at the top, thalwegcorner of the redd (Appendix 1).
Data Analyses
To determine what environmental factors influenced Pacific lamprey migrations, migration rates
from tagging to fixed-site antennae locations were related to environmental variables at the time
of detection. Average migration rate for each lamprey was calculated as kilometers per day,
which was the response variable. Predictors include quantitative and categorical variables (Table
3). Nonparametric multiplicative regression (NPMR in HyperNiche version 1.12, McCune and
Mefford 2004) was used to represent migration response of Pacific lamprey to multiple
interacting environmental factors.
Hierarchical agglomerative cluster analysis using Euclidean distance measure and Ward‟s
method for group linkage in PC-ORD, version 5.06 (McCune and Mefford 2006) grouped
lamprey by overwinter and spawning locations. A dendrogram of distance relationships based
on similarities of overwinter and spawning locations was created to facilitate deciding group
membership. Overwinter location was determined by the last location in the fall documented for
a lamprey within the calendar year that it was tagged. Lamprey used in the overwinter cluster
analysis also must have been tracked the following spring. Spawning locations were determined
by the uppermost location detected in the spring, if water temperatures were between 10°C and
16°C.
Table 3. Environmental variables as potential predictors for Pacific lamprey migration
rates.
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11
PLEMP Phase I Final
Quantitative variables:
Water temperature
 Daily average
 2-d maximum
 2-d minimum
Discharge
 Log of daily average
 1-d change in discharge
Lunar phase
 Percent luminosity (-100 to +100, depending on waxing or waning)
Categorical variables:



Month of detection
Time of day of detection
Main stem or tributary
1.4 Results
Radio-tagging and Tracking
Eighty-four Pacific lamprey were radio-tagged from 2005 through 2008 (Table 4). Except for 7
lamprey released at White River Campground in 2007, tagged lamprey were released at Lower
Blue Hole recreation site. Of the 84 tagged lamprey, 32 had either tag failures (e.g. expelled
tags), were presumed dead after showing only slow downstream movement, or left the system,
leaving 52 fish to track.
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12
PLEMP Phase I Final
Table 4. Descriptive statistics for radio-tagged Pacific lamprey in the lower Deschutes
River Subbasin, 2005 - 2008.
Year
n
Length (cm)
Avg.
Range
Weight (g)
Avg.
Range
Girth (cm)
Avg.
Range
Male to
Female1
2005
26
7/19 to 8/19
66.7 62.5-72.1 502.7 400.0-700.0
11.7
11.3-12.5
1:1.6
2006
8
7/21 to 8/9
71.5 66.0-77.0 520.0 350.0-680.0
12.2
11.5-13.0
1:3
2007
36
7/11 to 8/22
65.7 61.0-71.0 464.3 350.0-560.0
11.0
10.5-13.0
1:1.6
2008
14
7/21 to 9/18
65.8 61.5-70.0 452.9 370.0-530.0
11.2
10.5-13.0
1.3:1
66.6 61.0-77.0 479.6 350.0-700.0
11.1
10.5-13.0
1:1.5
Total 84
1
Release
Dates
Sex unknown for some lamprey.
From 2005 through 2009, there were 60 tag detections at fixed-site antennae, representing 31
fish. Some of the tagged lamprey were detected at multiple fixed-site receiving stations as they
moved upstream; 15 were detected at two fixed-site antennae, 3 lamprey were detected at 3
different fixed sites and 3 lamprey were detected at 4 fixed sites. Lamprey were detected at fixed
sites most frequently from June through September (Figure 4). Lamprey were most frequently
detected from midnight to 3:00 a.m. and 9:00 p.m. to 11:00 p.m. (Figure 5).
______________________________________________________________________________
13
PLEMP Phase I Final
Frequency
Figure 4. Frequency of detections at fixed-site receiving locations in the lower Deschutes
and Warm Springs basins by month, 2005 – 2009.
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14
PLEMP Phase I Final
Frequency
Figure 5. Frequency of detections at fixed-site receiving locations in the lower Deschutes
and Warm Springs basins by hour, 2005 – 2009.
Among the 60 lamprey detections at fixed site receiving locations, overwinter (or pre-holding)
and spawning (or post-holding) migrations were identified. Fifty-six percent (34) of lamprey
detected at fixed sites passed detections sites before fall (<90 days) after fish were tagged (Figure
4), and they appeared to be moving upstream to overwintering locations. The overwinter
migrants moved at an average rate of 1.6 km/d. Twenty-four lamprey are represented in this
group. Seven were detected multiple times as they moved upstream and passed as many as four
fixed-site receiving stations in the Warm Springs River (Table 5). Only one lamprey passed the
antennae at the mouth of Shitike Creek (22 d after release, average 3.7 km/d). Eighteen
detections appeared to be associated with spawning, representing eight fish, detected at Dant and
three fixed sites in the Warm Springs River (Table 6).
Table 5. Number of days from release site past fixed-site antennae for fall migrating
Pacific lamprey, 2005 - 2009.
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15
PLEMP Phase I Final
Fixed site (number of detections)
Average days from release
Range days from release
Dant (n = 22)
26
6 - 104
Mouth (n = 7)
30
17 - 46
Hatchery (n = 3)
40
29 - 47
Island (mouth Beaver Ck, n = 3)
47
33 - 58
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PLEMP Phase I Final
Table 6. Pacific lamprey detected at fixed-site antennae during post-holding migration,
2005 - 2009.
Tag Code
Date Released
Detection Date
Detection Site
Days Since Release
18
7/12/2005
2/22/2006
WSM1
225
6/3/2006
DFS2
297
6/18/2006
WSM
312
6/23/2006
WSNFH3
317
6/19/2006
DFS
313
6/30/2006
WSNFH
324
6/21/2006
DFS
306
6/29/2006
WSM
314
7/3/2006
WSNFH
318
5/25/2007
DFS
308
6/6/2007
WSM
320
6/10/2007
WSNFH
324
6/13/2007
Island
327
6/10/2006
DFS
305
8/17/2006
WSNFH
373
6/2/2008
WSM
304
5/17/2009
DFS
295
7/19/2009
WSM
358
25
32
54
68
74
8/10/2005
8/10/2005
8/19/2005
7/21/2006
8/9/2006
20
8/3/2007
131
7/26/2008
1
WSM = Warm Springs River mouth fixed site
2
DFS = Dant Fixed Site
3
WSNFH = Warm Springs National Fish Hatchery
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PLEMP Phase I Final
Average migration rates of lamprey in fall during pre-holding migration after fish were tagged,
was moderately correlated with daily average water temperature and one-day change in
discharge (xR2=0.29). Predictors were evaluated by means of their sensitivity to differences in
quantitative predictors (environmental variables, Table 7). The greater the sensitivity to changes
in the variables, the more influence that variable has in the model. Tolerance is the standard
deviations used in Gaussian smoothers, so the greater the tolerance, the poorer the predictor. Fall
migration rates of Pacific lamprey were greatest when water temperatures were warm (14°C to
20°C, Figure 6) and increased with decreasing discharge (Figure 7).
Table 7. Model predictors with sensitivity and tolerance values for Pacific lamprey in the
lower Deschutes River Basin, 2005 - 2009.
Predictor
Sensitivity
Tolerance
% Tolerance
Daily average water temperature
1.34
0.72
5
1-d change discharge
0.26
54.0
20
Daily average discharge
0.07
1862.8
40
Lunar phase
0.03
124.8
65
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PLEMP Phase I Final
Figure 6. Pacific lamprey fall migration in response to daily average water temperature,
2005 - 2009.
Figure 7. Pacific lamprey fall migration in response to one-day change in discharge (cfs),
2005 - 2009.
Radio-tracking data from the fall from 2005 through 2008 revealed overwinter locations for 35
of the 52 Pacific lamprey being tracked. Cluster analysis of overwinter locations resulted in a
dendrogram with 4.02% chaining. The dendrogram of overwinter locations was split into four
groups, retaining approximately 92.5% of the information as distance between groups (Figure 8,
Table 8). Of the 35 lamprey that apparently overwintered, 74% (26) were in the Deschutes
River, 20% (7) were in the Warm Springs River, and only one lamprey was found in Beaver
Creek and one in Shitike Creek (Figure 9).
Radio-tagged lamprey typically spawned where they overwintered; 19 (of the 26) spawned in the
Deschutes River; 7 (of the 7) in Warm Springs River, one in each of Beaver and Shitike creeks.
Three lamprey that overwintered in the Deschutes River appeared to spawn in Warm Springs
River. One lamprey that apparently overwintered in the Deschutes River spawned in Shitike
Creek.
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PLEMP Phase I Final
Figure 8. Dendrogram of Pacific lamprey grouped by overwinter locations.
See Appendix 2 for details of lamprey tagging, detection data and group membership.
Table 8. Overwintering locations, as determined by the dendrogram, for Pacific lamprey overwintering locations in the lower
Group
Distance from release site (rkm)
Area
1
79.0 to 89.9
Deschutes R. near Shitike Creek, lower Shitike Creek, in WSR near the mouth of Beaver
Ck., lower Beaver Ck.
2
57.1 to 75.5
Deschutes River near the mouth of WSR and WSR from the mouth to WSNFH
3
-1.8 to 8.8
Deschutes River near White River to Boxcar Rapids
4
22.7 to 43.3
Deschutes River from Dant to North Junction
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21
PLEMP Phase I Final
Figure 9. Overwinter locations, by group, for Pacific lamprey in the Deschutes Basin, 2005
- 2009.
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22
PLEMP Phase I Final
Radio-tracking data in the spring from 2006 through 2009 indicated spawning locations of 49 of
the 52 radio-tagged Pacific lamprey. Cluster analysis of spawning locations resulted in a
dendrogram with 2.65% chaining. The dendrogram of spawning locations was split into three
groups, retaining approximately 90% of the information as distance between groups (Figure 10,
Table 9). Three of the 52 tagged lamprey were not included in the analysis of spawning
locations; they remained in the vicinity of the tagging location and therefore did not make large
movements to spawning locations so spawning was difficult to document on these fish (Figure
11). Of the 49 lamprey with more obvious spawning migration patterns, apparent spawning
locations included the Deschutes River (n = 31), Shitike Creek (n = 3), Warm Springs River
(n=13) and Beaver Creek (n = 2, Figure 11).
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PLEMP Phase I Final
Figure 10. Dendrogram of Pacific lamprey grouped by spawning locations.
See Appendix 3 for details of lamprey tagging, detection data and group membership.
Table 9. Spawning locations, as determined by the dendrogram, for Pacific lamprey overwintering locations in the lower
Group
Distance from release site (rkm)
Area
1
57.1 to 104.1
Deschutes River near mouth of WSR to Shitike Creek and tributaries, including WSR,
Shitike and Beaver creeks
2
0.6 to 13.4
Deschutes River from Blue Hole, just above release site, upstream of Harpham Flat near
Long Bend
3
20.9 to 43.3
Deschutes River from Dant to North Junction
______________________________________________________________________________
24
PLEMP Phase I Final
Figure 11. Spawning locations, by group, for Pacific lamprey in the lower Deschutes Basin,
2005-2009.
______________________________________________________________________________
25
PLEMP Phase I Final
In 2008 and 2009, 8 redds were identified in Beaver Creek and 23 redds were identified in
Shitike Creek (Figures 12 and 13). In 2008, there were 1.7 times more redds in Beaver Creek
(5/3) and 2.8 times more redds in Shitike Creek (17/6) than in 2009. The average Pacific
lamprey redd in study reaches in Shitike and Beaver creeks in 2008 and 2009 were 38 cm wide
by 41 cm long (internal length) or 78 cm long (including coarse substrate at tail, Table 10).
Pacific lamprey spawned in water about one-third meter deep, with very little detectable flow at
the substrate and about one-half meter per second 60% up the water column. Substrate size
ranged broadly, but averaged approximately 50 cm both vertically and laterally. In Shitike
Creek, Pacific lamprey redds were excavated as individual nests, while in Beaver Creek, they
were excavated in groups, appearing as windrows, particularly near the Highway 9 reach.
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26
PLEMP Phase I Final
Figure 12. Pacific lamprey redd locations in Beaver Creek, lower Deschutes River
Subbasin, 2008 – 2009.
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27
PLEMP Phase I Final
Figure 13. Pacific lamprey redd locations in Shitike Creek, lower Deschutes River, 2008 – 2009.
______________________________________________________________________________
28
PLEMP Phase I Final
Table 10. Descriptive statistics for Pacific lamprey redd physical characteristics, Beaver
and Shitike creeks, lower Deschutes River Subbasin, 2008 – 2009.
Variable
Average
Minimum
Maximum
Width
38
20
56
Internal length
42
22
85
External length
78
29
160
Depth at head
37
8
84
Depth midway
37
13
72
Depth at tail
29
5
71
At substrate
0.08
-0.03
0.31
60% above substrate depth
0.54
0.08
0.93
Average
51
22
94
Minimum
11
2
35
Maximum
132
55
298
Average
53
14
107
Minimum
13
1
42
Maximum
141
38
261
Redd dimensions (cm)
Water depth (cm)
Water velocity (m/s)
Substrate size – vertical (mm)
Substrate size – lateral (mm)
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29
PLEMP Phase I Final
In Beaver Creek, average date of redd excavation was June 23 in 2008 (range June 17 to July 16,
n = 5) and June 12 in 2009 (all on June 12, n = 3). Corresponding daily average water
temperatures ranged from 10.2°C to 16.2°C in Beaver Creek (Dahl Pine, approximately 9.5 km
upstream of Highway 9 crossing and 7.5 km downstream of Robinson Park) in 2008 and
averaged 11.7°C on June 12 when three redds were identified in 2009. In Shitike Creek, average
date of redd excavation was June 21 in 2008 (range June 6 to July 8, n = 17) and July 23 in 2009
(range July 14 to July 30, n = 6). Corresponding daily average water temperatures in Shitike
Creek (approximately 1 km upstream from mouth) ranged from 8.3°C to 16.2°C in 2008 and
from 15.2°C to 22.6°C in 2009.
1.5 Discussion
Patterns of Migration
Detections of radio-tagged Pacific lamprey at fixed-site receiving locations were most frequent
from June through September and at hours between dusk and dawn (chiefly from midnight to
3:00 a.m. and 9:00 p.m. to11:00 p.m.). These detections represent both pre-holding and postholding migrations (sensu Robinson and Beyer 2005). Detections from lamprey associated with
pre-holding migrations ranged from July (less than 1 week after tagging) to early December
(over three months after tagging). Detections from post-holding movements ranged from late
February (222 days after tagging) to mid-August (over 1 year after tagging).
Observed patterns broadly agree with other reports of Pacific lamprey migrations in the Pacific
Northwest, although sparse. Pacific lamprey counts at Columbia River dams indicate the
upstream migration period extends from April through August, with median dates beginning at
Bonneville Dam in early July, mid-July at The Dalles Dam, with a general pattern of
successively later median dates as distance of dams increased from the mouth of the Columbia
River (Keefer et al. 2009). Upstream migration through Columbia River dams is assumed to
represent lamprey engaged in pre-holding migrations. Robinson and Bayer (2005) report preholding migrations of Pacific lamprey in the John Day River from July, after fish were radio
tagged, until September when lamprey began holding. After overwinter holding, Pacific lamprey
resumed upstream migration beginning in mid-March 2001 with spawning movements ended by
early May 2001. Fixed-site receiving locations on the John Day River also recorded lamprey
moving between sunset and sunrise. In the Nicola River, a tributary of the Fraser River, preholding Pacific lamprey migration occurred late July through early August (Beamish and
Levings 1991).
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PLEMP Phase I Final
Pre-holding Migration Relative to Environmental Factors
In the Deschutes Basin, Pacific lamprey migration rates were loosely correlated with water
temperature and change in discharge; migration rates increased with rising daily average water
temperatures and declining river discharge. This corresponds to results in Keefer et al. (2009), in
which in-river environmental conditions influenced upstream progression of adult Pacific
lamprey in the Columbia River. Aggregate run timing of Pacific lamprey in the Columbia River
system was earliest in warm and low-flow years and later in cold and high-flow years.
Associations of Pacific lamprey migration characteristics and environmental variables are likely
related to metabolic costs of migration. Metabolic rate increases with increasing activity (e.g.
migration) providing sufficient energy for blood O2 and CO2 transport; the higher the water
temperature (up to a point of decreasing return), the higher the metabolic rate (Burggren et al.
1991). Alternatively, energy is conserved when migration occurs during lower flows.
Location, Time of Spawning and Redd Characteristics
At the onset of this study, it was thought that Pacific lamprey would primarily be observed
spawning in tributaries of the Deschutes River, particularly in Shitike Creek and Warm Springs
River. Only three (<6%) radio-tagged lamprey of the 52 tagged fish were detected in Shitike
Creek and 15 (29%) tagged lamprey were detected in Warm Spring River and Beaver Creek. An
unexpectedly high number of radio-tagged Pacific lamprey, 60% (31) of the 52 radio-tagged
lamprey, appeared to have spawned in the Deschutes River. However, no redds were
documented or measured in the mainstem Deschutes River. In the John Day River, 39 of 42
radio-tagged lamprey appeared to spawn in the mainstem (Robinson and Beyer 2005). The
conceptual model of lamprey spawning in small-order tributaries is likely the result of studies
constrained by methods of observation to view adult lamprey and/or redds in smaller streams
(e.g. Beamish 1980; Stone 2006) and from incidental catch of ammocoetes in screw-traps located
in tributaries (Kostow 2002).
Temporal patterns of observations of newly excavated redds in Beaver and Shitike creeks
correspond with other reports in the Pacific Northwest. Newly excavated Pacific lamprey redds
were observed in the study reach in Beaver Creek from June 17 to July 16 in 2008 when daily
average water temperatures were between 10.2°C to 16.2°C. In 2009, new redds in Beaver
Creek were observed on June 12 when daily average water temperature was 11.7°C. Freshly
constructed redds in Shitike Creek were observed from June 6 to July 8, 2008 with
corresponding water temperatures between 8.3°C to 16.2°C. In western Washington, Pacific
lamprey nests in Cedar Creek were first observed during the first week of May and were last
observed in early July (Stone 2006). Corresponding water temperatures for observations in
Cedar Creek were 9.4 °C and 16.0 °C. In southern Oregon, redd counts in the South Fork
______________________________________________________________________________
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PLEMP Phase I Final
Coquille River peaked on May 5, 2004 (Brumo 2006). In 2009, Pacific lamprey redds were not
observed in Shitike Creek until mid-July. Daily average water temperatures were
correspondingly higher as well, from 15.2°C to 22.6°C. The apparent late timing of redd
excavation in Shitike Creek in 2009 may have been due, at least in part, to hydrologic conditions
(e.g. high flows, turbidity) that interfered with redd surveys. A peak in flow June 2, 2009 in
Shitike Creek (450 cfs, USGS 14093000, Figure 14) was above the level that surveyors were
able to wade (200 cfs). Wading Shitike Creek was not possible until mid-June in 2009 but
lamprey redds were not observed until mid-July. In Beaver Creek, an early peak in spring
discharge in 2008 was later (mid-May) than in 2009 (early May) but surveyors were able to wade
the stream by late May in both years (USGS 14096850, Figure 14). If index reaches for Pacific
lamprey redds are indicative of spawning populations in Beaver and Shitike creeks, there were
2.4 times greater spawning activity in 2008 than in 2009, 22 and 9 redds, respectively.
Pacific lamprey redds in Shitike and Beaver creeks were slightly larger than that summarized by
Wydowski and Whitney (2003), in which Pacific lamprey redds were reported up to 61 cm in
diameter, 20 to 30 cm wide and 3 to 8 cm deep. In Shitike and Beaver creeks, redds averaged 78
cm (including coarse substrate at tail) long by 38 cm wide, and average substrate diameter of 55
mm. Pacific lamprey redds in the Smith River in southern Oregon averaged 39 cm in length, 36
cm wide, 7.6 cm depth, in water 44 cm deep, with an average velocity of about 1m/s and
substrate 48.1mm average diameter (Gunckel et al. 2006). Wydowski and Whitney (2003)
reported that Pacific lamprey spawning sites are usually in riffles and tails of pools with water
velocity between 0.5 and 1.0 m/s and depths between 0.4 and 1 m. In Shitike and Beaver creeks,
Pacific lamprey spawned in water about one-third meter deep, which flowed near zero at the
substrate and about one-half meter per second 60% up the water column. Similar to large
clusters of redds in Beaver Creek, Pacific lamprey redds were observed in high densities on the
South Fork Coquille River, in which large areas (20 m by 5 m) were disturbed, making
individual redds impossible to distinguish (Brumo 2006).
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32
PLEMP Phase I Final
Beaver Ck. near Quartz Ck.
2008
Discharge (cfs)
2009
200 cfs
spawning period
Shitike Ck. near Museum
2008
Discharge (cfs)
2009
200 cfs
spawning period
Figure 14. Hydrographs of Beaver and Shitike creeks, lower Deschutes River Subbasin,
May-July 2008-09
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33
PLEMP Phase I Final
Chapter 2: Capture efficiency of standard, ammocoete (larval lamprey) survey gear under varying environmental conditions, fish sizes and densities
2.1 Introduction
The most common approach to monitor lamprey habitat use and abundance is by capturing
ammocoetes (Pajos and Weise 1994) because they remain in sediments of their natal streams
from four to seven years before migrating seaward (Wydowski and Whitney 2003). Since
ammocoetes filter feed near the surface (Wydowski and Whitney 2003), electrofishing gear is
used to apply stimulus to initiate emergence from the substrate (Steeves et al. 2003). With the
exception of a study evaluating the effects of fish density and size on Pacific lamprey
ammocoete detection and capture efficiency (CE, Luzier et al. 2006), little effort has been made
to understand the effectiveness of capturing ammocoetes by electrofishing in the Pacific
Northwest. Without quantifying CE and establishing a standard protocol for sampling
ammocoetes, surveys of ammocoete abundance should only be used as a measure of relative
abundance or to describe trends over time. This study modeled CE of lamprey ammocoetes as a
function of lamprey size, substrate depth, shock duration and environmental variables using
standard electrofishing gear. The resulting model can be used to adjust ammocoete capture data
for more accurate estimates of lamprey abundance.
2.2 Study Area
A total of eight study sites were selected in the Warm Springs River, Beaver, Badger, and Shitike
creeks (Figure 15, Table 11). In each stream one site was selected near both the downstream and
upstream ends of the established ammocoete distribution. Due to geographic and elevation
differences, sites represented a broad range in environmental variability so that inferences from
the resulting model may be made to sites with similar characteristics. Locations of individual
enclosures were based on physical stream characteristics (e.g., substrate type, slope) common to
each site, in addition to security and accessibility (Appendix 4). Three sites were relocated
during the study. The site HeHe on the Warm Springs River was moved downstream
approximately 0.6 km in October 2007 due to access; snow made the road impassable so the
location was dependant on the extent the road was plowed. Site B260, on Badger Creek, was
moved upstream about 1.3 km. A beaver constructed a dam just downstream, which raised the
water level beyond a manageable depth for electrofishing. Site Hwy 9, on Beaver Creek, was
moved about 1.1 km downstream in September 2007 after a fire burned the area and safety
became a concern.
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PLEMP Phase I Final
Figure 15. Pacific lamprey ammocoete capture efficiency study sites in the lower Deschutes
River Subbasin, 2007 - 2008.
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Table 11. Pacific lamprey capture efficiency sample sites, Warm Springs River, Badger,
Beaver, and Shitike creeks, lower Deschutes River Subbasin, 2007 - 2008.
Stream
Site1
Rkm
Samples (n)
B100
5.9
22
B260 (a)
13.6
10
B260 (b)
14.9
10
Hwy 9 (a)
14.1
8
Hwy 9 (b)
13.0
14
Robinson Park
32.7
20
Mill
1.1
22
Museum
2.2
20
Heath Bridge
1.0
12
HeHe (a)
53.2
12
HeHe (b)
52.6
24
Badger Ck.
Beaver Ck.
Shitike Ck.
Warm Springs R.
1
(a) and (b) denote original and alternative sample sites, respectively
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PLEMP Phase I Final
2.3 Methods
The general approach of this study was to test CE with a backpack electrofishing unit commonly
used for larval and juvenile Pacific lamprey surveys. The pulse rate and voltage were held
constant, as well as personnel shocking and netting. Lamprey CE was measured in experimental
enclosures at eight sites from May 10, 2007 through April 30, 2008, in which substrate depths,
lamprey densities, and shock duration varied by study design. Uncontrolled environmental
variables were measured and used for model development.
Electrofishing
The AbP-2 backpack electroshocker (Engineering Technical Services, University of Wisconsin,
Madison, WI) was used to capture lamprey ammocoetes. Sampling involved two stages, in
which 125 V direct current (25% duty cycle) was delivered at three pulses/s to induce
ammocoete emergence from substrates (Moser et al. 2007; Pajos and Weise 1994). After
emerging, larvae were stunned with a current of 30 pulses/s for collection (Slade et al. 2003).
The same individuals operated the electrofisher and netted fish during each trial to reduce
sampling variability. To lessen the likelihood of operator bias, the operator did not assist with
collection of experimental fish or know densities within each enclosure during trials.
Shock Duration
During experimental trials, each enclosure was sampled for a total of 360 s. Each trial was
divided into four 45 s electrofishing passes separated by 30 s rest periods and a final 180 s pass,
60 s after the final 45 s pass (fourth pass), for a total of five electrofishing passes (Table 12).
After experimental shocking ceased, any ammocoetes remaining in net pens were recovered
through a combination of post-experimental shocking, agitation of net pens, and sieving of
substrate to verify fish density and determine if any individuals emigrated.
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PLEMP Phase I Final
Table 12. Pacific lamprey electrofishing shock duration and rest periods for development
of the CE model, lower Deschutes River Subbasin, 2007 - 2008.
Electroshocking pass
Shock duration
(seconds)
Cummulative shock
duration (seconds)
Rest period after pass
(seconds)
1
45
45
45
2
45
90
45
3
45
135
45
4
45
180
60
5
180
360
During each pass, ammocoetes were collected with hand nets and wire-mesh baskets fixed to
electrofisher probes. Collected ammocoetes were placed in aerated buckets and held separately
for each pass. Ammocoetes were anesthetized with MS-222 (60 mg/l buffered with 100 mg/l
NaHCO3), measured to the nearest mm, and weighed to the nearest 0.01 g. All captured lamprey
were examined for elastomer marks and tallied by size category. After experimental shocking
ceased, any ammocoetes remaining in net pens were recovered through a combination of postexperimental shocking, agitation of net pens, and/or sieving of substrate to verify fish density
and determine if any individuals emigrated. Individuals recovered after the 360 s sample period
were not part of the CE calculation. Ammocoetes observed but not captured or swimming in the
enclosure, rather than burrowed, before shocking commenced were not enumerated.
Ammocoetes were returned to the site of original collection after the experiment was complete.
Experimental Enclosures
Electrofishing efficiency experiments were conducted in 0.75 m x 0.75 m x 1.0 m (l*w*h)
enclosures consisting of a PVC frame supporting sides and a bottom made of heavy nylon fabric
(Figure 16, Appendix 5). Two enclosures were set up for each sample date/site; one enclosure
was filled with substrate to a depth of 15 cm and the second enclosure was filled to a depth of 30
cm. Data from previous ammocoete distribution surveys (CTWSRO, unpublished) suggested
that 15 cm and 30 cm sediment depths were appropriate for treatments; 75% and 96% of
ammocoetes caught were at depths ≤15 cm and ≤30 cm, respectively (Figure 17). Fish were
introduced into enclosures after sediment settled. Enclosures were covered with plywood to
reduce disturbance until the trials began.
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PLEMP Phase I Final
Figure 16. Experimental net enclosures in Badger Creek, November 2007.
Figure 17. Number of ammocoetes captured versus depth (cm) of fine sediments during
distribution surveys in the lower Deschutes River Subbasin, 2002-2006. Seventy-five
percent and 96% of ammocoetes were caught at depths less than 15 cm and 30 cm,
respectively.
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PLEMP Phase I Final
Ammocoete Length and Density
Ammocoete lengths and densities in experimental enclosures were controlled. Lengths recorded
during previous presence/absence surveys were divided into three categories: 45–70 mm, 71–89
mm, and 90 + mm (Figure 18). Individuals smaller than 45 mm were excluded from experiments
due to increased potential for emigration and difficulty separating small fish from substrate
during post-experimental fish recovery. Ammocoetes were collected near each study site prior to
each electrofishing trial. Before each trial, low (9), medium (24), or high (48) numbers of
ammocoetes were randomly selected and placed into experimental enclosures. Randomization of
lamprey densities was accomplished by stratifying the sampling period into seasons (May-July;
Aug-Oct; Nov-Jan; Feb-Apr). Equal numbers from each density category were available for
selection by season and assigned to each enclosure by sample date. Ammocoetes were marked
with colored elastomer denoting length category, which allowed for easy enumeration of fish in
each size class and detection of immigration or emigration. Marked ammocoetes were placed
into enclosures and allowed to acclimate for 48 hours prior to experimental shocking.
Figure 18. Length frequency of ammocoetes captured during distribution surveys in the
lower Deschutes River Subbasin, 2002-2006.
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PLEMP Phase I Final
Substrate
Pacific lamprey ammocoetes are associated with fine-dominated substrate containing silt sand,
and organic material (Roni 2002; Stone and Barndt 2005). Substrate used in the enclosures was
obtained from Seekseequa Creek. While all substrate used in enclosures was stream-borne, it
was collected from dry areas to avoid potential transfer of disease-causing or exotic organisms.
Collected sediment was sifted through a 3-mm mesh sieve to exclude large debris and ensure
consistency among trials.
Environmental Variables
Physical characteristics, environmental variables, and weather conditions potentially affecting
CE were measured both inside and outside of experimental enclosures pre- and post-experiment
(Table 13). Water temperature, dissolved oxygen, and conductivity were measured with a YSI
85 multiprobe (YSI Inc., Yellow Springs, OH). Water velocity was measured with a MarshMcBirney Flo-Mate flow meter (Marsh-McBirney Inc., Frederick, MD). A meter stick was used
to measure water and sediment depth. Cloud cover, precipitation, and wind speed was estimated
visually. A categorical variable, visibility, was used to indicate the degree to which the observer
could see to net stunned lamprey inside enclosures. The categories were high, medium and low.
Visibility was recorded „high‟ when substrate was clearly visible throughout the entire enclosure,
wind or water velocity did not cause surface ripples on the water, and shade and/or sun glare did
not obscure visibility. Medium visibility was registered when the substrate was visible but the
water surface was partially (>30% of surface) disturbed by wave action, and/or shade and/or sun
glare partially impaired visibility (>30% of surface). Visibility was considered low when the
substrate was not clearly visible due to turbidity, and/or when the majority (>70%) of the water
surface broken, and/or when shade and/or sun glare largely obscured visibility (>70% of
surface).
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PLEMP Phase I Final
Table 13. Environmental variables measured before and immediately after electrofisher
efficiency trials in Warm Springs River, Badger, Beaver, and Shitike creeks, 2007 - 2008.
Variable
Instrument
Description
Water temperature
YSI 85 Instrument
nearest 0.1ºC
Dissolved oxygen
YSI 85 Instrument
mg/l
Conductivity
YSI 85 Instrument
μS/cm
Marsh-McBirney Flo-Mate
m/s
Water depth
Meter stick
nearest 1cm
Sediment depth
Meter stick
nearest 1cm
Handheld thermometer
nearest ºC
Percent cloud cover
Visual estimate
nearest 10%
Precipitation
Visual estimate
none, drizzle, light rain, steady rain,
light snow, flurries
Wind speed
Visual estimate
0-8; 9-16; 17-32 km•hr-1
Water:
Flow
Weather:
Air temperature
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PLEMP Phase I Final
Data Analysis
Ammocoete capture/pass data were re-coded into five binary variables that indicated on which
pass a lamprey was captured. Position one of the binary variable was „1‟ if a lamprey was
captured on Pass 1, and 0 otherwise; position two of the binary variable was „1‟ if captured on
Pass 1 or 2, and 0 otherwise, and so on up to the fifth pass. The capture/pass data was paired
with environmental data (Table 13).
Lamprey ammocoete electrofishing efficiency data was analyzed by modeling the efficiency as a
function of explanatory environmental variables. The underlying assumption is that the
probability of collection of a particular lamprey at a particular site is a binomial random variable
with the probability of success (collection of the lamprey) dependent on values of the
environmental variables for that site, size of the lamprey, and duration of the electric shock.
Capture efficiency data was analyzed using logistic regression (R Development Core Team
2008). The logistic model used a logit link to transform probability into a linear function of the
observed variables.
The logit is represented by the formula:
Equation 1
or equivalently,
Equation 2
.
p
The function f(x) is often referred to as the "log odds", because 1  p is the odds of collection.
The usual approach is then to take f(x) as a linear function of the explanatory variables, i.e.
Equation 3
f(X)
ixi ,
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PLEMP Phase I Final
where the xi's are the explanatory variables. The coefficients βi were estimated from the data.
The fitted model was then be used to predict the efficiency of ammocoete electrofishing with
corresponding environmental variables as predictors.
The model was selected using a step-wise procedure to eliminate variables according to the
Akaike's Information Criterion (AIC), a measure that balances the number of estimated
parameters and a measure of fit (Venables and Ripley 2002). The resulting model was carefully
examined to determine if the indicated statistical significance was consistent with physical and
biological principles.
To evaluate model fit, continuous variables (length, sediment depth, and conductivity) were
converted into categorical variables by splitting their ranges into 3 intervals, chosen so that each
interval had approximately the same number of data points. Observed efficiency and the mean
predicted efficiency for each of the cross-classified categories that had at least five data points
was calculated and the mean predicted efficiency versus the observed efficiency was plotted.
The observed efficiency is the same as an estimate of binomial probability, and was used to
calculate confidence intervals.
2.4 Results
Electrofishing trials were conducted from May 2007 through April 2008. A total of 174
experimental enclosures were set up with two levels of sediment (15 and 30cm depth) and three
densities of ammocoetes (9, 36 or 48) and electroshocked according to the time periods for the
five passes (Table 12). Associated environmental variables measured during electrofishing trials
are summarized in Table 14.
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PLEMP Phase I Final
Table 14. Environmental variables measured during electrofishing trials in the Warm
Springs River, Badger, Beaver and Shitike creeks, 2007 - 2008.
Parameter
Average
Minimum
Maximum
Water temperature (°C)
8.8
0
19.8
Dissolved oxygen (mg/l)
10.8
7.7
17.6,1 next highest 14.2
Conductivity (µS/cm)
48.0
28.7
86.2
Velocity (m/s)
0.1
-0.09
0.18
Average water depth (m)
26.7
8.1
66.3
1
This value is suspect; dissolved oxygen is usually in the range of 7 to 12 mg/l in fresh water to
maintain fish populations
Logistic regression analyses of larval lamprey electrofishing data resulted in a set of five models
(equations 4 through 9), corresponding to electrofishing passes. Variables, wind and
conductivity, that were significant in the first two models (Pass 1 and 2) were dropped from
subsequent models (Pass 3, 4 and 5) as they were not significant (p > 0.05). This improved fit by
removing random noise created by variables that did not explain variability in the observed data.
In this set of models, there was no interaction among variables, eliminating the need to use
electrofishing shock time as a variable.
Equation 4 Pass 1; y = -0.006β1 + -0.027β2 + 0.164β3 + 0.378β4 + -0.223β5 + -0.009β6 + 2.90
Equation 5 Pass 2; y = -0.011β1 + -0.048β2 + 0.026β3 + 0.430β4 + -0.257β5 + -0.008β6 +4.34
Equation 6 Pass 3; y = -0.015β1 + -0.051β2 + 0.348β4 + -0.113β5 + 4.96
y = log odds ration of an individual ammocoete for each electrofishing pass
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PLEMP Phase I Final
β1 = ammocoete length (mm); β2 = sediment depth (cm); β3=wind (numeric value of windspeed
in km-per-hour / 1.609); β4 = high visibility (categorical); β5 = low visibility (categorical; both
are zero if conditions are medium visibility); β6 = conductivity (μS/cm)
To convert log odds ration, y, to capture probability (CP):
Equation 9
CP(y) = exp(y) / (1 + exp(y)), where CP is between 0 and 1.
The intercept is a measure of overall efficiency. Difference in intercept values becomes
increasingly smaller with each successive electrofishing pass but the values continue to increase
and tend to flatten out (Figure 19). This pattern suggests that the maximum efficiency is being
reached.
Figure 19. Model intercept versus electrofishing pass.
Examining plots of observed versus predicted capture efficiency allows evaluation of the model
fit. Observed versus predicted capture efficiency is plotted for passes two through five with a
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PLEMP Phase I Final
1:1 line and horizontal lines indicating 95% confidence intervals (Figures 20-24). Points,
representing observed versus predicted capture efficiency, are rarely outside the confidence
intervals and cluster around 1:1 lines. The 1:1 lines intersect almost every confidence interval,
which is strong evidence that the small amount of variation not explained by the model is
binomial variation.
Observed with 95% CI versus Predicted
0.85
0.80
0.70
0.75
Predicted Efficiency
0.90
1-1 line
0.6
0.7
0.8
0.9
1.0
Observed Efficiency, Pass 1
Figure 20. Observed vs. predicted capture efficiency for Pass 1.
(fine horizontal gray lines are 95% confidence intervals, the sloping blue line is 1:1)
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PLEMP Phase I Final
0.90
0.85
0.75
0.80
0.95
1-1 line
0.70
0.75
0.80
0.85
0.90
0.95
1.00
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PLEMP Phase I Final
0.94
0.92
0.90
0.88
0.84
0.86
0.96
0.98
0.85
0.90
0.95
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PLEMP Phase I Final
0.94
0.92
0.90
0.86
0.88
0.96
0.98
0.85
0.90
0.95
1.00
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PLEMP Phase I Final
0.98
0.94
0.92
0.88
0.90
0.96
1-1 line
0.85
0.90
0.95
1.00
Observed Efficiency, Second 180
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PLEMP Phase I Final
2.5 Discussion
Models developed from lower Deschutes River study sites to calculate electrofishing capture
efficiency of ammocoete are robust enough to use at other like sites. These probability models
predict capture efficiency of individual Pacific lamprey ammocoetes by electrofishing on a perpass basis, given fish length under a measured set of environmental variables. Capture
efficiencies for juvenile lamprey can be transformed into abundance estimates.
To use the models to estimate ammocoete abundance at a new site, record the variables sediment
depth, wind, visibility and conductivity for the site on the day of the survey and record
ammocoete lengths for each of five passes; use shock durations and rest periods as described in
this study (Table 12). A capture probability (CP = 0 to 0.99) for each fish will be estimated for
Pass 1 through 5 using equations 4 through 8. To estimate the abundance of lamprey at a given
site, the value for each captured lamprey gets inflated based on the capture probability (1
lamprey + 1/CP). For example, a fish with a probability of 0.90 becomes 1.11 fish (1/0.90) and
added to the next fish (1/CP) until all of the captured fish are expanded and added together (Pass
1 through 5), giving an abundance estimate. The observed size distribution can be reported as
well as a best estimate of the expanded population size distribution. The size distribution of the
estimated population will shift slightly because the efficiency varies by size; larger fish have
lower capture efficiency, indicated by the sign of the coefficients. Length, depth, and wind
coefficients are negative, indicating that efficiency decreases with increasing length, depth, or
wind.
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PLEMP Phase I Final
Chapter 3: Ammocoete abundance as a function of measured environmental
variables in the field, downstream of PRB
3.1 Introduction
To produce a theoretical abundance estimate of ammocoetes in habitats that may re-colonize
upstream of PRB, the relationship between abundance and habitat characteristics must first be
modeled in habitats where ammocoetes exist, and related to currently vacant habitat. This
chapter develops the ammocoete habitat model from habitats occupied by ammocoetes
downstream of PRB.
Habitat characteristics, such as fine substrate and low-velocity water, have been associated with
Pacific lamprey ammocoetes (Kostow 2002; Stone and Barndt 2005) and habitat associations are
known to vary at different spatial scales (Torgersen and Close 2004). A predictive model for
ammocoete density using habitat characteristics had not previously been developed. In part, the
challenge has been the inability to expand catch, or relative abundance, to an abundance estimate
from electro-fishing (Moser and Close 2003; Stone and Barndt 2005) unless the protocol
included mark-recapture (Pajos and Weise 1994). Sampling ammocoetes typically is done by
electro-fishing (Moser et al. 2007; Pajos and Weise 1994; Steeves et al. 2003). In the previous
chapter, a method for converting ammocoete catch to abundance from electro-fishing surveys
was given. This capture-efficiency model is used to convert ammocoete catch to abundance, the
response variable in the habitat model, and then habitat characteristics where ammocoetes were
collected were used as predictors.
3.2 Study Area
The study area for the ammocoete habitat model is in the same vicinity as for the capture
efficiency model (Figure 15), however the sites differ. Three study reaches per stream were
established in Warm Springs River, Badger, Beaver and Shitike creeks (Table 15, Figure 25).
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PLEMP Phase I Final
Table 15. Study reaches for ammocoete habitat model in Warm Springs River, Badger,
Beaver, and Shitike creeks, lower Deschutes River Subbasin, 2009.
River/Creek
Badger
Beaver
Shitike
Warm Springs
1
Reach
Description
Length1 (m)
1
US 26 to B260
5,480
2
Waterhole #2 to Waterhole #3
1,480
3
Waterhole #3 to MP6
3,580
1
Mouth to Fawn Flats
1,390
2
Power lines to old bridge
1,300
3
Dahl Pines to Beaver Butte Cr
12,750
1
Mouth to community center
3,620
2
Community Center to Thompson
Bridge
4,090
3
Thompson Bridge to head works
3,090
1
Heath Bridge to WSNF Hatchery
16,500
2
End of E-120 road
1,570
3
McKinley-Arthur to power lines
3,520
Approximate length, to the nearest 10 m.
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PLEMP Phase I Final
Figure 25. Ammocoete habitat model study reaches (dark blue) in Warm Springs River,
Badger, Beaver, and Shitike creeks, lower Deschutes River Subbasin, 2009.
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PLEMP Phase I Final
3.3 Methods
Site Selection
Study reaches were sampled in three periods throughout the study: April through June; July to
mid-August; and late-August through October 2009. Repeat sampling of sites was avoided. For
each sample period, six sites from each reach were surveyed (Table 15). Two of the six sample
units were randomly selected to guard against unforeseen bias. The remaining four sample units
were non-randomly selected based on surveyor experience. These sites were chosen to produce
a range of densities and habitat characteristics. Targeted habitat characteristics were based on a
previous study in the same study streams which indicated ammocoete presence was correlated
with depositional areas with fine substrates (silt/fine sand) containing organic debris, low
velocity (0.18 m/s), woody debris, and canopy cover (Graham and Brun 2007).
To randomly select sites, study reaches were divided into 10-m segments in GIS and assigned
numbers (1 through x). Two of the six sample units from each reach were randomly selected
from the list of possible segments using a list randomizer (http://www.random.org/lists). From
the mid-point of the 10-m randomly-selected segment, mid-point GPS coordinates were provided
to field crew from which the nearest potential habitat was sampled.
Electro-fishing
The AbP-2 backpack electrofisher (Engineering Technical Services, University of Wisconsin,
Madison, WI) was used to capture ammocoetes. Sampling involved two stages, in which 125 V
direct current (25% duty cycle) was delivered at three pulses/s to induce ammocoete emergence
from substrates (Moser et al. 2007; Pajos and Weise 1994). After emerging, larvae were stunned
with a current of 30 pulses/s for collection (Slade et al. 2003). According to the CE protocol
(Chapter 1), a 0.56-m2 (0.75 m x 0.75 m) PVC frame was used as a visual boundary for
shocking. Five electrofishing passes within the boundary were delivered according to CE model
protocol (Table 12). Ammocoetes were netted as they came out of the sediment within the
boundary. Missed fish were assigned an average length based on measured fish from that pass,
and analyzed. Captured ammocoetes were held in separate buckets for each pass.
After shocking, ammocoetes were measured to length, using appropriate protocols for anesthesia
(Prentice 1990), and returned to the stream. Habitat measurements were recorded after fish were
sampled. Habitat measurements and other variables for model development included a
combination of those required to adjust number of ammocoetes shocked in a sample unit to
abundance (capture efficiency model, chapter 1), ODFW stream survey variables (ODFW 2006),
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PLEMP Phase I Final
and others (Table 16). Water depth (cm) and sediment depth (cm) were measured using a depth
gage in three transects within the shock boundary with three points per transect. Water velocities
were measured just above the sediment and at 60% depth (Model 2000 Flo-mate flow meter,
Marsh-McBirney, Inc., Frederick, MD). Unit type, channel type, dominant and sub-dominant
substrate type and vegetation type (nearest bank or both if unit is mid-channel) was recorded
according to ODFW stream survey protocols (ODFW 2006). Notes included whether the sample
unit was depositional, located at the margin or in mid channel, or if woody debris was present.
Canopy closure (percent) was measured with a densiometer (ODFW 2006) when standing in the
middle of the shock boundary. Water temperature, pH and conductivity were measured with a
multi-probe (Model G, Quanta Inc., Loveland, Colorado). Wind speed was measured using a
hand-held portable wind meter (Dwyer Instruments, Inc., Michigan City, IN). The categorical
variable „visibility‟ was used to indicate the degree to which the observer could see to net
stunned lamprey, from capture efficiency model development. The categories were high,
medium and low. Visibility is recorded „high‟ when substrate is clearly visible throughout the
water column, wind or water velocity do not cause surface ripples on the water, and shade and/or
sun glare do not obscure visibility. Medium visibility is registered when the substrate is visible
but the water surface is partially (> 30% of surface) disturbed by wave action, and/or shade
and/or sun glare partially impairs visibility (> 30% of surface). Visibility is considered low
when the substrate is not clearly visible due to turbidity, and/or when the majority (> 70%) of the
water surface is broken, and/or when shade and/or sun glare largely obscures visibility (> 70% of
surface).
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Table 16. Variables for ammocoete habitat model development, Warm Springs River,
Badger, Beaver and Shitike creeks, lower Deschutes River Subbasin, 2009.
Variable
Units/Category
Data Type
cm
continuous
m·s-1 at 60% depth
continuous
cm
continuous
Silt and fine organic matter, sand, gravel (pea to
baseball (2-64mm)
categorical
percent
continuous
μmhos·cm-1
continuous
ºC
continuous
High, medium, low
categorical
(km/hr)/1.609
continuous
mm
continuous
Water depth3

average

min.

max.
Water velocity2,3
Sediment depth2,3

average

min.

max.
Dominant substrate type1
Canopy closure1,2
Conductivity2,4
Water temperature2
Visibility4
Wind speed4
Ammocoete length4
1
ODFW habitat variable (ODFW 2006); 2Torgersen and Close 2004; 3Presence/absence model
variable (Graham and Brun 2007); 4 Capture efficiency model variable, Chapter 2.
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Data analysis
Multiple linear regression was used to model the mean response of larval lamprey densities
(abundance estimate/sampling area) as a function of environmental variables (Statgraphics
Centurian XV, Statpoint Technologies, Inc., Warrenton, VA). Ammocoete abundance by sample
unit was the response variable. Independent variables to build the multiple regression model
were selected from those measured during the study (Table 16) using the model selection
procedure in Statgraphics. The model selection procedure considers all possible regressions
involving different combinations of the independent variables. It compares models based on the
adjusted r2, Mallows‟ Cp statistic, and the mean squared error. The final model was chosen on
the basis of the highest adjusted r2 value (compensates for the number of independent variables
in the model by adjusting for degrees of freedom) and low Cp criterion (focuses on trade-off
between bias due to excluding important variables and extra variance from including too many).
3.4 Results
The final model to predict Pacific lamprey ammocoete abundance from habitat characteristics
involved only samples from Shitike Creek (n = 44, adjusted r2 = 48.6%, Equation 10). In Shitike
Creek, there was strong evidence ammocoete abundance was associated with water temperature
(one-sided p-value < 0.0001) and negatively associated with sand as dominant substrate (onesided p-value = 0.01). Samples from the Warm Springs Watershed (Warm Springs River,
Beaver and Badger creeks) were excluded from the final model because ammocoete densities
were poorly correlated with habitat characteristics (best model produced adjusted r2 of 6.1%). A
comparison of regression lines among ammocoete abundance by stream (n = 172) against water
temperature, the most influential variable, indicated the mean response in Shitike Creek was
significantly different from Warm Springs River Watershed (one-sided p-value slope =0.0001).
Mean response of ammocoete abundance in samples in Warm Springs River, Beaver and Badger
creeks to water temperature was not significantly different from each other (one-sided p-value =
0.18). Ammocoete abundance per sample differed among streams (p-value = 0.0005; analysis of
variance F-test). A multiple range test indicated ammocoete abundance in Shitike Creek (n = 44,
average 23.5, std. dev 22.0) was greater than Warm Springs River (n = 44, average 12.0, std. dev
13.1), Beaver (n = 43, average 15.9, std. dev 14.2) and Badger creeks (n = 41, average 10.1, std.
dev 10.4).
Equation 10 Estimated µ {log10 ammocoete abundance/sample│water temperature,
percent canopy, sand} per 0.5625m2 area
= 0.379 + 0.066 water temperature – 0.302 sand
SE (0.19)
(0.013)
(0.12)
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PLEMP Phase I Final
Note: If sand is the dominant substrate, sand=1, if not, sand=0; sample area is 0.75m by 0.75m
(0.5625 m2); to convert to density, take the inverse log (10^log ammocoete abundance) to
convert log abundance back to abundance, divide ammocoete abundance/sample by 0.5625m2,
which yields ammocoetes/m2.
To satisfy statistical tests and prediction intervals based on least-squares estimates, features of
the linear regression model were inspected, including linearity, constant variance, normality, and
independence. Predictors in the reduced model included a continuous variable, water
temperature, and a binary variable, sand as the dominant substrate. Lamprey abundance was
transformed (log10) to reduce kurtosis bringing the distribution closer to normality. A linear
pattern of points in the scatter plot of lamprey abundance and water temperature have fairly
equal spread (variability does not increase as the mean of log10 lamprey abundance increases,
Figure 26). Predictors were independent; they were correlated with the response variable but not
to each other (ammocoete abundance and water temperature, r = 0.66, one-sided p-value < 0.001;
ammocoete abundance and sand, r = -0.43, one-sided p-value 0.004; water temperature and sand,
r = -0.23, one-sided p-value 0.12). Percent canopy (shade) was positively associated with
ammocoete abundance and was a significant variable when lamprey abundance was not logtransformed (one-sided p-value 0.012) but narrowly fell out when lamprey abundance was logtransformed (one-sided p-value 0.058), but it was highly correlated to water temperature (r = 0.40, one-sided p-value 0.0065), violating the assumption of independent predictors.
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Figure 26. Scatter plot of ammocoete abundance (log10) and water temperature (°C) in
Shitike Creek, 2009.
Habitat conditions, under which this model applies, according to conditions in Shitike Creek
from which it was developed, are summarized in Table 17. Applying the model to habitat
dominated by anything other than silt or sand would be inappropriate, as well as conditions
outside those described in Table 17. Types of habitat units that were sampled in Shitike Creek
were 75% pools and 25% glides of the 44 samples. Of the pool habitats sampled, 70% (23/33)
were lateral pools; the remaining 30% (10/33) were beaver, dammed, plunge or scour pools.
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Table 17. Habitat conditions in Shitike Creek, April through September, 2009.
Parameter
Average
Minimum
Maximum
Water temperature (°C)
13.3
5.1
22.7
Water depth (cm)
22.4
1
55
Sediment depth (cm)
14.8
01
63
Velocity (bottom)
0.03
-0.07
0.37
Velocity (60%)
0.11
-0.09
1.3
Percent canopy
24.9
10.4
30.1
1
a portion of the 0.75m by 0.75m sampling boundary did not have enough sediment to measure
depth (e.g. depth meter contacted a rock)
3.5 Discussion
The relationship between habitat characteristics and Pacific lamprey ammocoete abundance in
Shitike Creek was different than study streams in the Warm Springs Watershed. Inherent in this
study design is that ammocoete abundance is independent of reproductive activity or success
(e.g. redds, egg to larvae survival) and that habitat characteristics represent most of the
variability in ammocoete abundance (e.g. ammocoete habitat is fully seeded). Since lamprey
redd counts are not available in study reaches for the period that eggs may have been deposited,
only current habitat conditions were considered in the model. These data suggest ammocoetes in
the Warm Springs River Watershed may be under seeded; given similar habitat conditions
ammocoetes were lower in abundance than in Shitike Creek.
Distributions of ammocoete lengths in Shitike Creek and streams in the Warm Springs River
Watershed appear similar (Figure 27); both are unimodal with about the same range and average
lengths. Ammocoete lengths in Shitike Creek samples averaged 70 mm (range 25 to 155 mm)
and 73 mm (range 12 to 180 mm) in Warm Springs River, Beaver and Badger creeks.
Histograms suggest age classes overlap (Figure 27). Mean length at age data for Pacific lamprey
ammocoetes from the Middle Fork John Day River, determined from statoliths, were as follows:
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Figure 27. Length-frequency of ammocoetes in Shitike Creek and streams in the Warm
Springs Subbasin.
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age 1 = 46 mm; age 2 = 51 mm; age 3 = 79 mm; age 4 = 85 mm and age 5 = 102 mm (Meeuwig
and Bayer 2005). Therefore, the histograms indicate multiple age classes are represented in both
Shitike Creek and study streams in the Warm Springs Subbasin, so successful reproduction has
likely occurred annually.
The most influential variable of ammocoete abundance in Shitike Creek was water temperature.
Only one other study cited water temperature as an important factor in predicting ammocoete
abundance. Based on electrofishing surveys conducted in Cedar Creek, a tributary to the North
Fork Lewis River in the lower Columbia Basin, temperature was the primary predictor of
ammocoete presence at the macro-scale (60 m, Stone et al. 2002).
Sand as the dominant substrate was negatively associated with lamprey abundance in Shitike
Creek. Conversely, ammocoete abundance was greater in habitats with silt and organic material
as the dominant substrate. In 2009, depositional sites were targeted for sampling and woody
debris was present in 88.6% of sampling sites in Shitike Creek. Sixty-six percent of the sites
were dominated by silt and organic material and had nearly three times the lamprey abundance
(average of 29.9 and 10.9 lamprey, respectively) as sites dominated by sand (34% of the sites).
Presence/absence sampling in the same study streams, although different sites, from 2003
through 2006 corresponded with the current study and indicated a positive relationship with
presence of wood (one-sided p-value <0.01), depositional area (one-sided p-value = 0.068), fine
substrate (one-sided p-value = 0.009), and availability of canopy cover (one-sided p-value =
0.039, (Graham and Brun 2007). The association between ammocoetes and substrate dominated
by silt and organic material has been noted at other sites in Oregon and Washington (Stone and
Barndt 2005; Torgersen and Close 2004)
Percent canopy was narrowly ruled out as a predictor in the model but indicates some
relationship with ammocoete abundance. A positive correlation with shade was also reported in
a study of larval lamprey (Geotria australis) in southwestern Australia (Potter et al. 1986).
Potter et al. (1986) explained that ammocoetes are photophobic and referred to some of his
earlier work in which ammocoetes in shallow artificial burrows exposed to light were more
stressed than to dark regimes. Alternatively, Torgersen and Close (2004) found that canopy
closure was negatively correlated with Pacific lamprey ammocoete abundance on the Middle
Fork John Day River, but only at large scales (5-10 km). The negative correlation with riparian
shade (or conversely positive correlation with increased light) at this large scale may have more
to do with increased water temperature from an open canopy than ammocoetes directly
responding to light. In Cedar Creek, Washington, high relative abundance of ammocoetes was
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PLEMP Phase I Final
also associated with fine substrates and negatively associated with canopy cover at the sub-reach
(1-m transect and 1-m2 quadrant) scale (Stone and Barndt 2005).
Under strict statistical interpretation, the multiple regression model of ammocoete abundance in
Shitike Creek can be used only to predict ammocoete abundance in Shitike Creek. However, this
model was developed for predicting theoretical abundance of Pacific lamprey ammocoetes in
habitat that is known to be part of their historic range upstream of PRB. For this purpose, with
appropriate qualifications, the multiple regression model from Shitike Creek can be used to
predict mean ammocoete abundance in reaches in the Metolius, Deschutes, and Crooked rivers
that meet habitat requirements of ammocoetes. A prediction interval can be calculated that
indicates a likely range of values for ammocoete abundance, given that substrate is dominated
either by silt or sand, and that environmental conditions are similar to those in which the model
was developed.
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Chapter 4: Theoretical estimate of ammocoete abundance in the Metolius,
Crooked, and Deschutes rivers, based on thermograph and habitat data
4.1 Introduction
Manufactured (e.g. construction of PRB restricting fish passage) and environmental (e.g. water
temperature, substrate) factors act as a series of „filters‟ that restricts species at the regional scale
from occurring at the local scale (Angermeier 1998; Poff 1997). After removing the „filter‟ of
passage restriction through PRB, a series of „filters‟, thermal and habitat availability, were
applied to the maximum potential area for Pacific lamprey re-colonization upstream of PRB.
This produced a theoretical range, restricted by current environmental conditions, which Pacific
lamprey ammocoetes may re-colonize if re-introduction were to occur. Because most fishes,
including Pacific lamprey, are obligate ectotherms, temperature is a controlling factor governing
the rate of metabolism, thus can limit spatial and temporal range of a population if beyond the
thermal preferendum or lethal limit of the species (Wooton 1998). After applying the thermal
„filter‟ to vacant habitats upstream of PRB, which restricted the maximum potential range, the
next step was to place the habitat „filter‟ (e.g. area of silt and sand from habitat surveys) onto the
range restricted by temperature and calculate the area that lamprey may re-colonize.
If Pacific lamprey are to be re-introduced, thermal tolerance and habitat preference dictate the
range upstream of PRB that re-colonization could occur. Historic range of Pacific lamprey
upstream of the location of PRB was not documented prior to extirpation, but it was recognized
that their range extended into the Deschutes River, the Crooked River (Portland General Electric
and Confederated Tribes of Warm Springs Reservation of Oregon 2006) and possibly into the
Metolius River, although the Metolius River is known for its cold water temperatures. Since
construction of PRB, the thermal regime of Crooked and Deschutes rivers may have changed
with increasing human demands (e.g. irrigation, urban development). However it is not likely
the thermal regime of the Metolius River has changed significantly from human disturbance due
to the very cold source of water from springs at the headwaters and some west side spring-driven
tributaries. Much of the Metolius River remains in Federal and Tribal ownership, which is
predominantly forested with limited development.
This chapter reviews thermal thresholds (e.g. tolerance, preference) by developmental stage of
Pacific lamprey and compares these thresholds with instream temperature data to determine
potential range for Pacific lamprey for each river and Whychus Creek. The AAM (Chapter 2)
was applied to the total potential rearing area upstream of Lake Billy Chinook (LBC), resulting
in a theoretical abundance estimate upstream of LBC.
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Literature Review of the Effects of Water Temperature on Lamprey Rearing Ammocoetes and
Spawning Adults
Habitat selection, growth rates, and survival of ammocoetes have been related to water
temperature (Table 18). Water temperature was the primary predictor of Pacific lamprey
ammocoetes presence (at macro scale, 60 m) in Cedar Creek, Washington (Stone et al. 2002) and
of ammocoete abundance in Shitike Creek (Chapter 2). Ammocoete (Petromyzon marinus)
growth in many studies has been found to occur faster at warmer stream temperatures than in
colder water (Holmes 1990; Manion and Hanson 1980; Potter 1980; Young et al. 1990). Close
(2002) suggests elevation and water temperatures determine Pacific lamprey developmental
success throughout the Umatilla Subbasin. In lower elevations of the Umatilla River spawning
occurs earlier, larvae hatch quicker, and there was an increase in the amount of time that
ammocoete growth could occur (Close 2002). Ammocoetes collected in the lower sections of
the Umatilla River (rkm 110-120) were larger than ammocoetes collected in the upper sections
(rkm 120-128) suggesting warmer water temperatures in the lower section contributed to greater
growth rates (Close 2002).
Laboratory studies conducted by Meeuwig et al. (2005) examined the influence of temperature
on development, survival, and developmental abnormalities of larval Pacific lamprey at 10°C,
14°C, 18°C, and 22°C. Greatest survival was observed at 18°C, followed by 14°C, 10°C and
22°C (Meeuwig et al. 2005). Based on logistic regression, zero development occurs when water
temperatures are less than 4.85°C (Meeuwig et al. 2005). Due to laboratory study constraints,
Meeuwig et al. (2005) were unable to determine optimal growth rates for Pacific lamprey
ammocoetes. Based on temperature monitoring in the Red River, Idaho, it has been suggested
ammocoetes are able to survive elevated water temperatures that are lethal for salmon and
steelhead (Claire 2004). Ammocoetes have been collected in water temperatures up to 25°C in
Idaho watersheds (Mallet 1983). Van de Wetering and Ewing (1999) reported that ammocoetes
began to die in the laboratory when water temperatures reached 28°C . Elevated stream
temperature may negatively impact ammocoete survival due to increased metabolic rates while
metamorphosis is occurring and decreases in stream microbial activity (van de Wetering and
Ewing 1999). Mallett (1983) suggests lamprey prefer water temperatures less than 20°C.
Multiple habitat characteristics determine spawning behavior of lamprey, (e.g., substrate, current,
water depth and quality) but water temperature may be the most important (Table 18). Water
temperature has been found to determine Pacific lamprey spawning location, timing, embryonic
development and hatch timing (Applegate 1950; Kan 1975; Manion and Smith 1971; Mattson
1949; Pletcher 1963; Russell et al. 1987). Maximum stream temperatures may also limit
available spawning habitats, especially in degraded habitats (e.g. riparian cover removal,
irrigation water withdrawals, Close et al. 1995; Jackson et al. 1997; Jackson et al. 1996). In
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British Columbia, Pacific lamprey spawning was documented in waters between 10°C and 15°C
(Beamish 1980; Beamish and Levings 1991). Pacific lamprey were observed spawning during
May when water temperatures were between 10°C to 15°C in Oregon Coastal streams (Kan
1975). In the Coquille River on the Oregon Coast, spawning occurred from early April to early
July in water temperatures between 12°C to 18°C, and peak spawn timing was correlated with
14°C (Brumo 2006). From 2000 to 2004, in Cedar Creek, a tributary of the North Fork Lewis
River in the lower Columbia Basin, Pacific lamprey were observed spawning from April to early
July in water temperatures between 7.8°C to 22°C (Le et al. 2004; Luzier and Silver 2005; Pirtle
et al. 2003; Stone et al. 2002; Stone et al. 2001). During 2002, peak spawning occurred in
Meacham Creek, Umatilla River Subbasin, during the first two weeks of June when the daily
mean temperature was between 8.8°C and 13.1°C with a mean overall temperature of 10.5°C
(Close et al. 2003).
4.2 Study Area
The PLEMP (Portland General Electric and Confederated Tribes of Warm Springs Reservation
of Oregon 2006) identified potential range for lamprey re-colonization above PRB in which
upstream boundaries were defined by natural or constructed barriers (Figure 28). There is no
physical barrier to fish migration on the Metolius River but its water temperatures may pose a
cold-water thermal barrier. The Deschutes River enters Lake Billy Chinook at rkm 193. Big
Falls on the Deschutes River (rkm 213) is considered to be a barrier for anadromous salmonids;
however it is likely lamprey can climb the 9-m falls. Water temperature at Big Falls was
Table 18. Summary of temperature thresholds and ranges for Pacific lamprey by
developmental stage.
Observed1 (°C)
Optimal (°C)
Limits (°C)
Adult - Spawning
7.8 to 22
10 to ~16
not available
Ammocoete – Rearing
up to 25
18
4.85 - 282
Developmental Stage
1
in stream environment
from lab experiment, 4.85°C is lower limit of growth, not survival, and 28°C is upper limit of
survival
2
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Figure 28. Area of maximum potential re-colonization for Pacific lamprey upstream of Lake Billy Chinook.
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determined to be too high and therefore the primary factor in determining potential lamprey
range. Whychus Creek enters the Deschutes River downstream of Big Falls and Steelhead Falls
(rkm 206) at rkm 196. Bowman Dam on the Crooked River at rkm 117 was constructed in 1961
(Nehlsen 1995). It is a fish barrier, with no fish passage facilities, and marks the upper extent of
the maximum potential area that lamprey may re-colonize in the Crooked River.
4.3 Methods
Water temperature data were recorded at USGS gauging stations on the Metolius River near
Grandview (14091500), the Deschutes River near Culver (14076500), and Crooked River below
Opal Springs near Culver City (14087400) at hourly intervals. Data from U.S. Bureau of
Reclamation gauging station on the Crooked River at Smith Rock State Park near Terrebonne
(CRSO) was used. A U.S. Forest Service water temperature monitoring site on the Metolius
River at Bridge 99, just upstream of Jefferson Creek, recorded data hourly using a Hobo© water
temperature logger (Onset Computer Corp., Pocassett MA). Data from May through September
2009 were used to determine the upper extent possible for lamprey spawning. If water
temperature data were not available to define the upper extent of lamprey habitat, data from cold
springs geodatabase (Oregon Geospatial Enterprises Office,
http://www.oregon.gov/DAS/EISPD/GEO/sdlibrary.shtml) was used to demarcate the extent.
Habitat data collected by the U.S. Forest Service on the Metolius River and by Oregon
Department of Fish and Wildlife (ODFW) on the Deschutes and Crooked rivers were used to
determine potential rearing area for ammocoetes, summarized by area of silt and area of sand.
Only pool and glide habitat units were considered because that was the type of habitats where
ammocoetes were found in Shitike Creek and under which the model was developed (Chapter 2).
Since ammocoetes prefer silt/sand substrate, low gradient, low velocity habitats, they would not
be expected in riffles, cascades, rapids or steps. The U.S. Forest Service (USFS) surveyed
habitat on the Metolius River from the mouth to Jefferson Creek in 1989 (data courtesy of USFS
Sisters Ranger District). These data included general habitat units (pool, riffles, glides, side
channels) but no information on substrate. Habitat data from ODFW was recorded in August
1997 on the Deschutes River, September 2008 on Whychus Creek, and July 1997 on the
Crooked River (ODFW Aquatic Inventories Project, GIS data,
http://oregonstate.edu/dept/ODFW/freshwater/inventory/habitgis.html). These data include more
detailed habitat types and vegetation descriptions than the USFS Region 6 protocol and more
measurements of substrate (including % silt/organic detritus and % sand substrate per habitat
unit, (ODFW 2006).
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General characteristics (habitat type, approximate dimensions) of habitat survey data were „spotchecked‟ to confirm gross changes in streams had not occurred since data were recorded. For
each stream, a 95-m to 433-m section of stream was compared to habitat survey data. In all
cases, stream survey data characterized habitat types and general habitat dimensions. There
appeared to be no gross changes in habitat features.
Since the USFS habitat survey in the Metolius River had no data on substrate, an average percent
of silt and sand from pools in the study area of the Deschutes and Crooked rivers from the
ODFW habitat geodatabase was applied to the Metolius River to calculate total area of silt and
sand. The USFS habitat survey on the Metolius River also included side channels, for which
there was none identified in the Deschutes and Crooked River ODFW habitat surveys. The
proportion of pool to riffle in the main stem Metolius River was applied to the side channel
habitat (6% pools). The average percentage of silt and sand in pools from the ODFW survey
was then applied to Metolius River pools in side channels. The result was and estimate of the
total area of silt and sand habitat in side channel pools in the Metolius River. The Ammocoete
Abundance Model (Chapter 2) was then applied to total areas dominated by silt or sand. Water
temperatures used in the model were according to the approximate maximum daily temperature
for the Metolius River at Grandview during summer 2009; this was used to represent the greatest
potential ammocoete abundance that could be expected upstream of LBC if the habitat were fully
seeded.
Stream segments from ODFW habitat surveys (geodatabase available from ODFW,
http://nrimp.dfw.state.or.us/nrimp/default.aspx?pn=dataresources) were clipped according to
extent defined by temperature data, using Geographic Information System (ArcGIS, vers. 9.3,
ESRI, Redlands, CA). Percent silt and sand for pools and glides within the temperature-limited
extent was multiplied by habitat area, resulting in the area dominated by silt and sand for each
habitat unit. Area dominated by sand and silt in each habitat unit were summed for each stream.
The Ammocoete Abundance Model (Chapter 2) was then applied to total areas dominated by silt
and sand. Water temperatures used in the model were according to the highest average daily
maximum during summer 2009.
4.4 Results
Water temperature
The temperature range selected to determine potential range of Pacific lamprey upstream of PRB
was 10°C to 18°C., which encompasses the typical range for spawning and rearing. Maximum
daily water temperatures greater than 22°C are considered too warm for Pacific lamprey
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PLEMP Phase I Final
spawning or rearing. The warmest water temperature recorded for Pacific Lamprey spawning
was 22°C in Cedar Creek, Washington (Le et al. 2004; Luzier and Silver 2005; Pirtle et al. 2003;
Stone et al. 2002; Stone et al. 2001) and developmental abnormalities of larval Pacific lamprey
was greatest at 22°C (Meeuwig et al. 2005). The optimal temperature for rearing larval Pacific
lamprey is 18°C, in which case least abnormalities occurred (Meeuwig et al. 2005). The low
range of water temperatures for spawning Pacific lamprey is generally near 10°C (Beamish
1980; Beamish and Levings 1991; Close et al. 2003; Kan 1975). The upper range of water
temperatures typical for spawning lamprey is between 15°C and 18°C (Beamish 1980; Beamish
and Levings 1991; Brumo 2006; Kan 1975).
In the Metolius River, data from the USGS gage near Grandview indicated temperatures during
June and July, when lamprey spawning occurs, were within the acceptable range for spawning
and rearing (10°C to 18°C) in 2009 (Figure 29). The next upstream monitoring site was Bridge
99 where water temperatures were too cold for spawning (< 10°C, Figure 30). To decide where
the extent of spawning between the USGS gage near Grandview and Bridge 99, a GIS layer of
cold water springs was used to identify areas where cold water enters the Metolius River and
areas that do not likely receive cold water inflow. A cold springs was located near Camp Creek,
which enters the Metolius River at rkm 13.8 and is the lowest known cold water input. Habitats
from the mouth of the Metolius River to first pool below Camp Creek were selected as potential
habitat for lamprey re-colonization (Figure 31).
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PLEMP Phase I Final
Water Temperature (oC)
Max
Min
Max Spawn
MinSpawn
Figure 29. Water temperature in the Metolius River near Grandview (USGS 14091500)
May through September, 2009 with respect to temperature range for lamprey spawning.
Max
Min
Max Spawn Temp
Min Spawn Temp
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PLEMP Phase I Final
Figure 30. Water temperature in the Metolius River at Bridge 99 (USFS) June through
September, 2009 with respect to temperature range for lamprey spawning.
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PLEMP Phase I Final
Figure 31. Area of potential re-colonization for Pacific lamprey upstream of Lake Billy Chinook, limited by water
temperature (cold springs represented by small circles).
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PLEMP Phase I Final
In the upper Metolius Basin, water temperatures in Abbot Creek were within the range for
Pacific lamprey spawning and rearing in 2009 (Figure 32). Water temperatures in Lake Creek
exceeded the acceptable temperature range for lamprey by eleven days in late July to early
August, 2009 (Figure 33). In addition to Abbot Creek, water temperatures during June and July
2009 in Brush, Link and Street creeks were within the acceptable range for lamprey spawning
and rearing (U.S.F.S., Deschutes National Forest, Alyssa Reischauer, Water Temperature
Coordinator, unpub. data).
Max
Min
Max Spawn
MinSpawn
Figure 32. Water temperature in Abbot Creek (USFS) June through September, 2009 with
respect to temperature range for lamprey spawning.
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PLEMP Phase I Final
Min
Max
MinSpawn
Max Spawn
Critical Temp
Figure 33. Water temperature in Lake Creek (USFS) June through September, 2009 with
respect to temperature range for lamprey spawning.
In the Deschutes River, data from the USGS gage near Culver indicated temperatures during
June and July were within the acceptable range for lamprey spawning and rearing in 2009
(Figure 34). The next upstream temperature monitoring site, at Lower Bridge Road, exceeds the
acceptable range (Figure 35). Cold springs near Big Falls contribute to lower water temperatures
downstream of Big Falls (Lesley Jones, Water Quality Specialist, Upper Deschutes Watershed
Council [UDWC], pers. comm.). These cold water springs are present on the geodatabase just
upstream of Big Falls. The maximum potential habitat for lamprey in the Deschutes River
upstream of LBC is up to Big Falls.
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PLEMP Phase I Final
Water Temperature oC
Max
Min
Max Spawn
MinSpawn
Figure 34. Water temperature in the Deschutes River near Culver (USGS 14076500) May
through September, 2009 with respect to temperature range for lamprey spawning.
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PLEMP Phase I Final
Max
Min
Min Spawn
Max Spawn
Critical Temp
Figure 35. Water temperature in the Deschutes River at Lower Bridge Road (UDWC
DR_133-50) May through July, 2009 with respect to temperature range for lamprey
spawning and rearing.
In Whychus Creek, cold water inflow at Alder Springs, approximately 2.4 km from the mouth,
was ultimately a cooling source to the Deschutes River; thermal infrared and color video of
water temperatures in Whychus Creek above Alder Springs were dramatically warmer than
below during summer (Watershed Sciences 2000). The geodatabase indicates these springs are
in the vicinity of Alder Springs. Water temperatures in Whychus Creek downstream of Alder
Springs were in the range that lamprey can spawn (Figure 36), so this marked the upper extent of
potential lamprey habitat in Whychus Creek.
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PLEMP Phase I Final
Max
Min
Max Spawn
Min Spawn
Critical Temp
Figure 36. Water temperature in Whychus Creek downstream of Alder Springs (UDWC
WC001_50) May through September, 2009 with respect to temperature range for lamprey
spawning.
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Water temperatures in Crooked River were within the range for lamprey spawning below Opal
Springs (Figure 37) but were too warm near Terrebonne (Figure 38). The USGS Water
Resources Division in Portland, Oregon conducted a study for the Bureau of Land Management
of water inflow patterns into the Crooked River between Opal Springs and Osborne Canyon in
2005 and found that inflow from springs increased dramatically just upstream of Opal Springs
(pers. comm., Rick Kittelson, Information Specialist, USGS Oregon Water Science Center,
Portland, see also USGS 14087370, 14087380, 14087390, 14087393). The geodatabase
indicates these springs are indeed just upstream of Opal Springs. In addition, ODFW habitat
surveyors indicated where the springs entered Crooked River. The location of the springs
upstream of Opal Springs marked the upper extent of lamprey habitat in Crooked River. Water
temperatures in the Crooked River immediately downstream of Bowman Dam were too cold for
spawning in June and July, 2009 (Figure 39).
Max
Min
Max Spawn
Min Spawn
Figure 37. Water temperature in the Crooked River below Opal Springs (USGS 14087400)
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PLEMP Phase I Final
Water Temperature oC
Max
Min
Max Spawn
MinSpawn
Critical Temp
Figure 38. Water temperature in the Crooked River at Smith Rock State Park near
Terrebonne (USBOR CRSO) May through September, 2009 with respect to temperature
range for lamprey spawning.
Min
Max
MinSpawn
Max Spawn
Figure 39. Water temperature in the Crooked River below Bowman Dam (USBOR PRVO)
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Habitat Area
There were 15 pools and 4 side channels in the Metolius River, from the mouth to the pool
immediately downstream of Camp Creek (13.8 rkm). Total pool habitat in this reach was
377,157 m2 (Table 19); from that, 9,052 m2 were dominated by silt (2.4%) and 116,919 m2 were
dominated by sand (31.0%). In side channels within this reach, total pool habitat was estimated
at 1,117 m2; from that, 27 m2 were dominated by silt (2.4%) and 346 m2 were dominated by sand
(31.0%).
In the Deschutes River, from the head of LBC to Big Falls, total area of pools and glides
dominated by silt was 9,518 m2 and area dominated by sand was 74,103 m2 (Table 20). In this
reach, ODFW classified 13 glides and 55 pools. Types of pools included lateral scour (49.1%),
straight scour (45.5%), and trench (5.5%) pools.
In Whychus Creek, ODFW identified 22 pools from Alder Springs to the mouth. There were no
glides in this reach. Of the pools, 21 were lateral pools and one was a plunge pool. Total Pool
area was 3,752 m2, 36 m2 were dominated by silt and 739 m2 were dominated by sand (Table
21).
In the Crooked River from rkm 6.9, upstream of Opal Springs, to LBC, ODFW identified 14
pools and 10 glides. Of the pools, 11 were straight scour pool; the remaining three were deep,
lateral scour, and plunge pool. None of the area of pools and glides was dominated by silt. Total
area of pools and glides dominated by sand was 45,526 m2 (Table 22).
______________________________________________________________________________
83
PLEMP Phase I Final
Table 19. Total estimated sand and silt habitat area in the Metolius River from the mouth
to Camp Creek.
Habitat Type
Total Area (m2)
ODFW Avg. % of
Habitat Type
Silt
Sand
Area Silt (m2)
Area Sand (m2)
M.C. Pool
377,157
2.4
31.0
9,052
116,919
S.C. Pool
1,117
2.4
31.0
27
346
9,079
117,265
Total
378,274
Table 20. Total estimated sand and silt habitat area in the Deschutes River from Big Falls
to LBC.
Total Area (m2)
Area Silt (m2)
Area Sand (m2)
Pool
154,219
8,288
69,390
Glide
37,704
1,230
4,713
Total
191,923
9,518
74,103
Habitat Type
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PLEMP Phase I Final
Table 21. Total estimated sand and silt habitat area in Whychus Creek from Alder Springs
to the Deschutes River.
Habitat Type
Total Area (m2)
Area Silt (m2)
Area Sand (m2)
Pool
3,752
36
739
Glide
0
0
0
Total
3,752
36
739
Table 22. Total estimated sand and silt habitat area in the Crooked River from rkm 6.9,
upstream of Opal Springs, to LBC.
Habitat Type
Total Area (m2)
Area Silt (m2)
Area Sand (m2)
Pool
89,649
0
2,733
Glide
27,624
0
42,793
Total
117,273
0
45,526
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85
PLEMP Phase I Final
Theoretical abundance estimate of ammocoetes in habitats suitable for re-introduction upstream
of PRB
Total estimated ammocoete abundance in potential habitats that may be re-colonized by Pacific
lamprey upstream of PRB is approximately 4.8 million (95% prediction interval = 3.7 to 7.5
million, Table 23). Ammocoete abundance was dependent upon substrate and water
temperature, the two predictors in the Ammocoete Abundance Model. Maximum water
temperatures used to estimate ammocoete abundance ranged from 12°C to 18°C, depending on
summer 2009 water temperature data (Figures 29 to 37, and Table 24). Ammocoete abundance
(fitted value) in silt ranged from 64.8 ammocoetes/m2 in Whychus Creek to 26.1 ammocoetes/m2
in Metolius River (Table 24). Ammocoete abundance (fitted value) in sand ranged from 56.4
ammocoetes/m2 in Whychus Creek to 13.0 ammocoetes/m2 in Metolius River (Table 24).
______________________________________________________________________________
86
PLEMP Phase I Final
Table 23. Estimated potential ammocoete abundance and 95% prediction intervals for
habitats upstream of LBC.
Stream
Substrate
(Area, m2)
Estimated
Ammocoete
Abundance
Water Temperature (°C)
95% Prediction Intervals
Silt (9,079)
237,277
170,579 to 330,054
Sand (117,265)
1,528,558
997,889 to 2,341,456
Total
1,765,835
1,168,468 to 2,671,511
Silt (9,518)
455,640
328,641 to 631,731
Sand (74,103)
1,769,276
1,084,246 to 2,887,059
Total
2,224,916
1,412,887 to 3,518,790
Silt (36)
2,331
1,589 to 3,421
Sand (739)
23,888
13,688 to 41,689
Total
26,219
15,277 to 45,110
Silt (0)
0
0
Sand (45,526)
808,143
515,247 to 1,251,893
Total
808,143
515,247 to 1,251,893
4,820,114
3,680,877 to 7,487,303
Metolius River
12°C
Deschutes River
16°C
Whychus Creek
18°C
Crooked River
14°C
Total All Streams
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PLEMP Phase I Final
Table 24. Ammocoete density by stream, according to water temperature and substrate.
Stream
Max. Summer Water
Temperature (°C)
Metolius River
Ammocoetes/m2
Substrate
silt
Fitted Value =
26.1
Upper 95% =
36.4
Lower 95% =
18.8
Fitted Value =
13.0
Upper 95% =
20.0
Lower 95% =
18.8
Fitted Value =
47.9
Upper 95% =
66.4
Lower 95% =
34.5
Fitted Value =
23.9
Upper 95% =
39.0
Lower 95% =
14.6
Fitted Value =
64.8
Upper 95% =
95.1
Lower 95% =
44.2
Fitted Value =
32.3
Upper 95% =
56.4
Lower 95% =
18.5
Fitted Value =
17.6
Upper 95% =
27.5
Lower 95% =
11.3
12°C
Metolius River
sand
Deschutes River
silt
16°C
Deschutes River
sand
Whychus Creek
silt
18°C
Whychus Creek
Crooked River
sand
14°C
sand
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88
PLEMP Phase I Final
4.5 Discussion
Based on summer stream water temperatures and habitat features (e.g. area of pool and glide
habitat units dominated by silt and sand) in the Metolius, Deschutes and Crooked rivers and
Whychus Creek there appears to be the potential for rearing between 3.7 and 7.5 million Pacific
lamprey ammocoetes upstream of LBC. This prediction depends on the assumption that habitat
features in streams above PRB where ammocoetes may re-colonize are similar to those in Shitike
Creek, where the AAM was developed. While the ODFW habitat surveys in Deschutes and
Crooked rivers and Whychus Creek had very detailed information, these data were collected at
the habitat unit scale or larger. The ODFW habitat survey was designed so data can be organized
into hierarchical system of regions, basins, streams, reaches, and habitat units to match the
parameters collected in other quantitative (USFS) or historic (U.S. Bureau of Fisheries) surveys
and at different scales (ODFW 2006), but not scaled down to the micro-habitat level. Presence
or absence of Pacific lamprey is determined at the micro-habitat unit scale; within a pool or glide
a habitat patch dominated by silt or sand that conforms to a range of water depth and velocity,
sediment depth, and riparian cover is where ammocoetes are typically found (Chapter 3, Table
17, see also Graham and Brun 2007; Stone and Barndt 2005). The estimated area of silt and sand
patches for ammocoetes to re-colonize in the Metolius River from the mouth to Camp Creek is
more tenuous than estimated habitat patches in the Deschutes and Crooked rivers; the U.S. Forest
Service stream survey in the Metolius River was conducted before the Level II protocol became
established and were not typically done in streams this large (M. Reihle, U.S. Forest Service,
Sisters Ranger District, pers. comm.). In addition, average areas of silt and sand in pools and
glides in the Crooked and Deschutes rivers and Whychus Creek may not be representative of
those in the lower Metolius River.
It is possible additional habitat for re-colonization of Pacific lamprey ammocoetes exists
upstream of that identified for potential re-colonization in the Metolius and Crooked rivers.
However, the potential for thermal barriers that adult lamprey may encounter during migration to
spawning grounds in the Metolius and Crooked rivers precludes the inclusion of these areas in
favor of erring on the conservative. The potential thermal barrier on the Metolius River is the
cold water upstream of Camp Creek to Lake Creek. If adult lamprey were to migrate through
this area, they may find water marginally within temperature tolerance for spawning in Abbot,
Brush and Link creeks. Street Creek, which enters the Metolius River within the reach from the
mouth to Camp Creek, is likely within the temperature range for spawning and rearing but no
habitat data exists. In the Crooked River, water temperatures in the vicinity of Smith Rock State
Park near Terrebonne become very warm (< 22°C) during summer and may pose a thermal
barrier to migration. While water temperatures are too cold for spawning and rearing
immediately downstream of Bowman Dam (Figure 39), data from a thermal infrared imagery
study suggest that there may be water temperatures within the range for Pacific lamprey
spawning and rearing a short distance below Bowman Dam to Prineville and also in Ochoco
______________________________________________________________________________
89
PLEMP Phase I Final
Creek from Ochoco Dam to Crooked River (Oregon Department of Environmental Quality
2006). The lower 6 km of McKay Creek may also fall within the water temperature range for
lamprey spawning and rearing (B. Hodgeson, ODFW, Bend, pers. comm.). If Pacific lamprey
passage through PRB is found possible, then it may be advisable to collect more detailed habitat
data on the Metolius River and Street Creek. In addition, further inquiry into potential thermal
barriers on Metolius and Crooked rivers and additional habitat for lamprey re-colonization may
be addressed.
______________________________________________________________________________
90
PLEMP Phase I Final
Conclusions
Studies of juvenile and adult Pacific lamprey in the Deschutes Basin have advanced ecological
understanding of these fishes locally. This information is valuable as managers decide on
whether and/or to what extent re-establishment of Pacific lamprey upstream of PRB is feasible.
If re-introduction is deemed possible and returning adult lamprey are able to pass upstream
through PRB to spawn naturally, studies of adult lamprey in the lower Deschutes River, which
indicate overwintering and spawning habits of the local population (Chapter 1) can be used to
predict behavior in the newly expanded range. Radio telemetry data suggests broad plasticity in
migration patterns, use of habitat (main stem vs. tributary) and timing in overwintering and
spawning. Although water temperature may be the largest habitat limiting factor above PRB, the
amount of habitat within that limited area would appear adequate for re-introduction. Since
lamprey spawn in substrate sizes similar to resident and anadromous O. mykiss (Stone 2006;
Wydowsi and Whitney 2003), concerns of limited habitat availability are negligible. Successful
lamprey spawning has been observed within steelhead redds in the Umatilla Basin (A. Jackson,
CTUIR, pers. comm.).
In 2003, distribution and habitat associations of Pacific lamprey were first documented by the
CTWSRO (Graham and Brun 2007). Once this baseline information was established, the
Capture Efficiency Model (CE, Chapter 2) was developed so ammocoete catch via electrofisher
could be transformed to an abundance estimate to standardize comparisons among sites and
account for variation in the environment. The CE takes into account ammocoete length,
sediment depth, conductivity, visibility into the water column and on top of the water (wind
ripples). The CE Model was used, in part, to develop the Ammocoete Abundance Model (AAM,
Chapter 3), in which ammocoete catch in habitats downstream of PRB was transformed to
abundance, then ammocoete abundances were related to environmental conditions in habitats
where they were sampled. The relationship between ammocoete abundance in Shitike Creek was
strongly associated with water temperature and whether the habitat patch was dominated by silt
or sand. The AAM was used, in conjunction with water temperature and habitat data, in streams
upstream of PRB to estimate a theoretical abundance estimate of ammocoetes if re-introduction
were to occur (Chapter 4).
According to the PLEMP, the next step is to assess whether passage for outmigrating lamprey
(ammocoetes and macropthalmia) is possible through PRB. Lamprey would have to migrate
from streams flowing into LBC, through LBC, find the opening to the top structure of the
Selective Water Withdrawal (SWW), pass through the screens and into the fish transfer facility.
______________________________________________________________________________
91
PLEMP Phase I Final
However, physiological constraints may reduce or negate outmigrants from doing so. In an
experiment to develop physiologic understanding of downstream migrating Pacific lamprey,
Dauble et al. (2006) judged juvenile lamprey to be weak swimmers by their low burst speed
compared to other fishes and relatively inefficient lateral, undulatory swimming style. They do
not possess gas bladders so buoyancy must be affected by swimming and therefore is an
energetic cost (Orr 1982). Juvenile lamprey migrating downstream in the Columbia and Snake
rivers were found to swim low in the water column (Long 1968). If lamprey actively swim
through LBC, energetic costs would be higher than run-of-the-river downstream migrating
lamprey which are believed to passively move downstream during high water events. It is also
unknown if flow will attract them to the egress.
Declining counts of adult lamprey at Bonneville Dam suggest fewer adults are returning to the
Columbia River every year. Increasing the capacity for the Deschutes River to produce Pacific
lamprey by re-establishing the upper Deschutes Basin as part of their range would be a positive
step for the conservation of this species.
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92
PLEMP Phase I Final
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Appendices
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PLEMP Phase I Final
Appendix 1. Pacific lamprey redd survey measurements.
Redd Habitat Measurements
Stream:________________
Date:____________
GPS (UTM
10T)
Water Temperature:___________
Time:___________
N:
Air Temperature:___________
Crew:___________
E:
Discharge:
Unit
used:
Weather:
(from USGS gage)
Redd
Depths:
Redd Dimensions (cm):
(taken at the
following 3 spots )
(Upstream)
Head (cm):
Mid
(cm):
Tail
(cm):
(Downstream)
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PLEMP Phase I Final
Appendix 1 (cont.). Pacific lamprey redd survey measurements.
Redd Habitat Measurements (cont.)
Redd Location
(measured in
meters)
Site
Characteristic
s
Distance to left bank:
Canopy Cover: N =
Distance to right
bank:
Cover is measured looking N, S, E, W on the
densiometer. Each square represents an area
of canopy opening (unfilled squares). Count
squares/dots of canopy opening.
Distance to next redd:
S=
E=
W=
Dominant Riparian Vegetation:
Flowmeter
Measurements
(make sure unit is on
m/s)
(what types of trees and plants are nearest
redd?)
Take 2 measurements in center of redd
"pot"
1. Bottom flow (base)
Stream
Widths:
2. Mean Flow
Wetted width
(m):
(take at 60% depth)
ie…if water is 1 m deep, take flow @0.6
m)
Bankfull width
(m):
Other Observations on Redd
Location/Shape
______________________________________________________________________________
100
PLEMP Phase I Final
Appendix 1 (cont.). Pacific lamprey redd survey measurements.
Substrate Measurement Datasheet for Lamprey Redds
Measure the maximum diameter of 15 neighboring (touching) stones along both a lateral (A)
and vertical (B) transect originating at the top-thalwag corner of the redd (see below)
Substrate Measurements (mm)
Lateral (A)
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
Vertical (B)
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
______________________________________________________________________________
101
PLEMP Phase I Final
Appendix 2. Group membership and overwinter locations of radio-tagged lamprey.
Group
1
2
3
Code_Year
Release Date
Overwinter River
16_05
7/19/2005
Shitike Ck.
22_05
7/27/2005
Deschutes R.
66_06
7/21/2006
13_07
rkm from
Release Site
82.9
Area Description
near community center
79
near mouth of Shitike Ck
Beaver Ck.
97.4
downstream of powerlines
7/24/2007
Warm Springs R.
89.9
near mouth of Beaver Ck.
126_08
7/23/2008
Warm Springs R.
87.5
near mouth of Beaver Ck.
18_05
7/12/2005
Warm Springs R.
57.8
near mouth
31_05
8/10/2005
Warm Springs R.
74.5
below fish hatchery
30_05
8/19/2005
Warm Springs R.
58.2
near Heath Bridge
15_07
8/2/2007
Warm Springs R.
75.5
below fish hatchery
23_07
8/10/2007
Deschutes R.
59.5
upstream of Andy Dick's house
22_07
8/10/2007
Deschutes R.
62.7
downstream of Trout Ck.
28_07
8/15/2007
Warm Springs R.
57.1
near mouth
129_08
7/24/2008
Deschutes R.
68
Frog Springs
33_05
8/10/2005
Deschutes R.
0
near Blue Hole
27_05
8/10/2005
Deschutes R.
1.6
upstream of Blue Hole
26_05
8/10/2005
Deschutes R.
0.5
near Blue Hole
25_05
8/10/2005
Deschutes R.
-0.7
Surf City Camp Ground
54_05
8/19/2005
Deschutes R.
0.1
upstream of cattle guard
2_07
7/11/2007
Deschutes R.
-1
below Blue Hole
1_07
7/11/2007
Deschutes R.
2.1
near Grey Eagle
10_07
7/24/2007
Deschutes R.
4.5
near Grey Eagle
12_07
7/25/2007
Deschutes R.
8.3
downstream of Boxcar Rapids
19_07
8/3/2007
Deschutes R.
8.8
near Boxcar Rapids
26_07
8/14/2007
Deschutes R.
-1.8
downstream of OSR
24_07
8/14/2007
Deschutes R.
1.1
33_07
8/15/2007
Deschutes R.
7.5
upstream of BLM house
31_07
8/15/2007
Deschutes R.
5.1
near silo
128_08
7/24/2008
Deschutes R.
2.1
near Grey Eagle
131_08
7/26/2008
Deschutes R.
2.1
near Grey Eagle
136_08
8/29/2008
Deschutes R.
0.1
______________________________________________________________________________
102
PLEMP Phase I Final
Appendix 2 (cont.) . Group membership and overwinter locations of radio-tagged lamprey.
Group
4
Code_Year
Release Date
70_06
8/9/2006
Deschutes R.
rkm from
Release Site
27.8
16_07
8/2/2007
Deschutes R.
43.3
Davidson Flat
17_07
8/7/2007
Deschutes R.
37.1
loafer's lair
130_08
7/26/2008
Deschutes R.
28.8
near Forester house
134_08
8/5/2008
Deschutes R.
22.7
hay barn upstream of Dant
Overwinter River
Area Description
near Forester
______________________________________________________________________________
103
PLEMP Phase I Final
Appendix 3. Group membership and spawning locations of radio-tagged larmpreys.
rkm from
Release Site
57.6
Group
Code_Year
Release Date
Spawning River
1
18_05
7/12/2005
Warm Springs R.
1
19_05
7/12/2005
Beaver Ck.
99
1
16_05
7/19/2005
Shitike Ck.
82.9
near Community Center
1
14_05
7/20/2005
Shitike Ck.
80.6
Hwy 26 Bridge
1
22_05
7/27/2005
Shitike Ck.
80.6
downstream of museum
1
25_05
8/10/2005
Deschutes R.
1
31_05
8/10/2005
Warm Springs R.
72.3
below Kahneeta Bridge
1
32_05
8/10/2005
Warm Springs R.
83.5
downstream of Beaver Ck.
1
30_05
8/19/2005
Warm Springs R.
74.4
downstream of hatchery
1
54_05
8/19/2005
Warm Springs R.
74.5
1
66_06
7/21/2006
Beaver Ck.
97.3
in Beaver Ck.
1
68_06
7/21/2006
Beaver Ck.
104.1
in Beaver Ck.
1
74_06
8/9/2006
Warm Springs R.
57.3
near mouth
1
13_07
7/24/2007
Beaver Ck.
100.3
in Beaver Ck.
1
15_07
8/2/2007
Warm Springs R.
75.5
1
20_07
8/3/2007
Warm Springs R.
60.8
near Rattlesnake Springs
1
22_07
8/10/2007
Deschutes R.
62.7
downstream of Trout Ck.
1
23_07
8/10/2007
Deschutes R.
59.5
upstream of Andy Dick's house
1
28_07
8/15/2007
Deschutes R.
68
Frog Springs
1
126_08
7/23/2008
Warm Springs R.
87
downstream from Beaver Ck.
1
129_08
7/24/2008
Deschutes R.
68
Frog Springs
1
131_08
7/26/2008
Warm Springs R.
57.1
near mouth
2
15_05
7/20/2005
Deschutes R.
2.1
Grey Eagle
2
24_05
7/27/2005
Deschutes R.
8.8
Boxcar Rapids
2
26_05
8/10/2005
Deschutes R.
10.5
Wapanitia Rapids
2
1_07
7/11/2007
Deschutes R.
0.6
2
3_07
7/11/2007
Deschutes R.
9.4
2
10_07
7/24/2007
Deschutes R.
-7.7
2
12_07
7/25/2007
Deschutes R.
8.3
upstream of BLM house
downstream Sherars Falls
Bridge
2
18_07
8/2/2007
Deschutes R.
0.8
Oak Springs
2
19_07
8/3/2007
Deschutes R.
8.8
Boxcar Rapids
2
24_07
8/14/2007
Deschutes R.
1.1
2
26_07
8/14/2007
Deschutes R.
13.4
Long Bend
2
27_07
8/15/2007
Deschutes R.
5.6
Maupin City Park
2
31_07
8/15/2007
Deschutes R.
5.7
Imperial
2
33_07
8/15/2007
Deschutes R.
8.5
76
Area Description
near mouth
near power lines
upstream of hatchery
______________________________________________________________________________
104
PLEMP Phase I Final
Appendix 3 (cont.). Group membership and spawning locations of radio-tagged larmpreys.
Group
Code_Year
Release Date
2
36_07
8/22/2007
Deschutes R.
rkm from
Release Site
6.1
2
128_08
7/24/2008
Deschutes R.
2.1
Grey Eagle
2
132_08
7/26/2008
Deschutes R.
8.6
2
135_08
8/29/2008
Deschutes R.
2.1
Grey Eagle
2
136_08
8/29/2008
Deschutes R.
2.1
Grey Eagle
3
28_05
7/27/2005
Deschutes R.
20.9
below Caretaker's house
3
34_05
8/10/2005
Deschutes R.
39.3
3
70_06
8/9/2006
Deschutes R.
24.1
3
16_07
8/2/2007
Deschutes R.
43.3
North Junction
upstream Four Chutes Camp
Ground
Davidson's Flat
3
17_07
8/7/2007
Deschutes R.
37.1
loafer's lair
3
130_08
7/26/2008
Deschutes R.
26.1
Dant
3
134_08
8/5/2008
Deschutes R.
21.7
Caretaker's house
Spawning River
Area Description
upstream of Maupin Bridge
______________________________________________________________________________
105
PLEMP Phase I Final
Appendix 4. Site descriptions for Capture Efficiency Model development.
Stream
Badger
Beaver
Site
Elevation (m)
Wetted Width
(m)
Bankfull Width
(m)
Canopy Cover %
B100
790
16.5
18
4.2
Glide, sand, silt, smaller gravels, soft sediment,
willows, rose, alders, grass, large pine trees
B260 (a)
840
17
18.5
11.7
Glide, sand, silt, sediment, woody debris, alder,
willows, grasses
B260 (b)
860
15
15
27.8
Riffle, alcove, sand, smaller gravel, muddy,
alder, willows, grass, large pine trees
Hwy 9 (a)
680
15.5
18
24.0
Riffle, alcove, small to large rocks, rose, alders,
willows, large pine trees
Hwy 9 (b)
700
22
26
0
Glide, pool, soft sediment with algae, alders,
grass, willows
Robinson Park
800
10.5
12
24.4
Glide, alcove, soft sediment, smaller pebbles,
younger alders, grasses, larger willows
Mill
430
16
20
0
Alcove, small gravels, alders, cottonwoods
Museum
430
15
20
56.1
Glide, sand, silt, large cottonwoods, alders,
grass
Heath
390
110
112
3.1
Glide, sandy bottom, alders and willows
HeHe (a)
770
28
31
50.0
Riffle, small gravel with larger rocks, small
alders and grasses
HeHe (b)
770
22
23
4.7
Riffle, glide, small gravel, few pines, alders and
ninebark
Shitike
Warm Springs
Site Description
____________________________________________________________________________________________________________
106
PLEMP Phase I Final
Appendix 5. Enclosure design.
____________________________________________________________________________________________________________
107
PLEMP Phase I Final
Attachment A
PLEMP Phase I – Habitat Assessment
Consultation with the Fish Committee
Article 402 of the new FERC license, which requires that the Licensees’ implementation of
measures pursuant to the new license be reported to the Fish Committee (FC) as provided in the
Settlement Agreement and any applicable implementation plan. The Licensees are required to
allow a minimum of 30 days for the consulted entities to comment and make recommendations.
The Licensees initiated consultation on October 13, 2011 with the following message:
From:
Sent:
To:
Cc:
Subject:
Attachments:
Scot Lawrence
Thursday, October 13, 2011 1:58 PM
bswift@amrivers.org; Robert.Dach@BIA.gov;
Jimmy_Eisner@or.blm.gov; bhouslet@wstribes.org;
scott.carlon@noaa.gov; LAMB.Bonnie@deq.state.or.us;
Michael.W.Gauvin@state.or.us; mriehle@fs.fed.us;
Peter_Lickwar@fws.gov; Julie Keil
jgraham@wstribes.org; cpenhollow@wstribes.org;
J_Manion@wspower.com; rbrunoe@wstribes.org;
brenda.sanchez@wstribes.org; Brian Clark; Don Ratliff; Greg
Concannon; Megan Hill; Robert Spateholts; Scot Lawrence
PRB - Pacific Lamprey Passage Evaluation and Mitigation Plan: Phase
I
Instructions for Accessing Documents from PGE ftp site.doc
Dear Fish Committee,
Posted to our ftp site for 30-day review is the Pacific Lamprey Passage Evaluation and
Mitigation Plan: Phase I – Habitat Assessment for Potential Re-introduction of Pacific Lamprey
Upstream of Pelton-Round Butte Hydroelectric Project pursuant to Section 18 Fishway
Prescription Condition 18.
I have posted both Word and .pdf versions of the report to the ftp site:
20100816 PLEMP Phase I Review draft.doc
20100816 PLEMP Phase I Review draft.pdf
Please return your approvals to me by Friday November 18, 2011. Please direct any comments
or questions of substance to Jen Graham at 541.553.3585, Don Ratliff at 541.325.5338 and me,
preferably before the 18th. We will also discuss the draft report at the October FC meeting.
Pelton Round Butte Project (FERC 2030)
March 2012
A-1
Consultation Summary
Don’t hesitate to contact me if you have any questions. Instructions for accessing our ftp site is
attached.
Thanks,
Scot
Scot Lawrence
Project Manager - Hydro Licensing
Portland General Electric
Portland, Oregon
503.464.7361
scot.lawrence@pgn.com
The following was received from USFWS on October 24, 2011:
From:
Sent:
To:
Subject:
Peter_Lickwar@fws.gov
Monday, October 24, 2011 12:15 PM
Scot Lawrence
Re: PRB - Pacific Lamprey Passage Evaluation and Mitigation Plan:
Phase I
Greetings;
The USFWS has reviwed the Pacific Lamprey Habitat Assessment Report. We have no comments on
the report.
Thanks,
Peter
Peter Lickwar/USFWS
(541) 312-6422 phone
(541) 383-7638 fax
Peter_Lickwar@fws.gov
-------------------------------------------------------------------------------------------------------
Scot Lawrence <Scot.Lawrence@pgn.com>
10/13/2011 01:58 PM
March 2012
To "bswift@amrivers.org" <bswift@amrivers.org>, "Robert.Dach@BIA.gov"
<Robert.Dach@BIA.gov>, "Jimmy_Eisner@or.blm.gov"
<Jimmy_Eisner@or.blm.gov>, "bhouslet@wstribes.org"
<bhouslet@wstribes.org>, "scott.carlon@noaa.gov"
<scott.carlon@noaa.gov>, "LAMB.Bonnie@deq.state.or.us"
<LAMB.Bonnie@deq.state.or.us>, "Michael.W.Gauvin@state.or.us"
<Michael.W.Gauvin@state.or.us>, "mriehle@fs.fed.us"
<mriehle@fs.fed.us>, "Peter_Lickwar@fws.gov"
A-2
<Peter_Lickwar@fws.gov>, Julie Keil <Julie.Keil@pgn.com>
cc "jgraham@wstribes.org" <jgraham@wstribes.org>,
"cpenhollow@wstribes.org" <cpenhollow@wstribes.org>,
"J_Manion@wspower.com" <J_Manion@wspower.com>,
"rbrunoe@wstribes.org" <rbrunoe@wstribes.org>,
"brenda.sanchez@wstribes.org" <brenda.sanchez@wstribes.org>, Brian
Clark <Brian.Clark@pgn.com>, Don Ratliff <Donald.Ratliff@pgn.com>,
Greg Concannon <Greg.Concannon@pgn.com>, Megan Hill
<Megan.Hill@pgn.com>, Robert Spateholts
<Robert.Spateholts@pgn.com>, Scot Lawrence
<Scot.Lawrence@pgn.com>
Subject PRB - Pacific Lamprey Passage Evaluation and Mitigation Plan: Phase I
Dear Fish Committee,
Posted to our ftp site for 30-day review is the Pacific Lamprey Passage Evaluation and Mitigation Plan: Phase I –
Habitat Assessment for Potential Re-introduction of Pacific Lamprey Upstream of Pelton-Round Butte
Hydroelectric Project pursuant to Section 18 Fishway Prescription Condition 18.
I have posted both Word and .pdf versions of the report to the ftp site:
20100816 PLEMP Phase I Review draft.doc
20100816 PLEMP Phase I Review draft.pdf
Please return your approvals to me by Friday November 18, 2011. Please direct any comments or questions of
th
substance to Jen Graham at 541.553.3585, Don Ratliff at 541.325.5338 and me, preferably before the 18 . We
will also discuss the draft report at the October FC meeting.
Don’t hesitate to contact me if you have any questions. Instructions for accessing our ftp site is attached.
Thanks,
Scot
Scot Lawrence
Project Manager - Hydro Licensing
Portland General Electric
Portland, Oregon
503.464.7361
scot.lawrence@pgn.com
[attachment "Instructions for Accessing Documents from PGE ftp site.doc" deleted by Peter
Lickwar/MOBILE/R1/FWS/DOI]
No other comments were received.
March 2012
A-3

(CTWSRO): Pacific Lamprey Passage Evaluation and Mitigation Plan

Transcription

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