s

333.95657

F2RWS

2003

ivaiige-vvide Status of Yellowstone Cutthroat Trout [Oncorhynchus clarki bouvieri). 2001

Bnice E. May

USD A Forest Service

Bozeman, Montana

Wendi Urie

U.S.D.A. Forest Service

Bozeman, Montana

Bradley B. Shepard

Montana, Fish, Wildlife and Parks

And

Montana Cooperative Fishery Research Unit

Bozeman, Montana

This status update was developed and completed under the oversight of a Yellowstone cutthroat interagency

coordination group that, in addition to the primary authors, contributed information and editorial oversight necessary

to the completion of this status report. Members of that coordination team included the individuals listed below.

New members of the coordination group are Chip Corsi, Idaho Department of Fish and Game, Boise, Idaho, Bob

Snyder, Montana Fish, Wildlife and Parks, and Kate Walker, USDA Forest Service, Missoula, Montana

Steve Yundt and Chip Corsi

Idaho Department of Fish and Game

Boise, Idaho

Ken McDonald and Bob Snyder
Montana Fish, Wildlife and Parks ^f^Jl DOCUMENTS COLLECTION

Helena, Montana

Steve Yekel L.lU C b 2003

Wyoming Game and Fish Department MONTANA STATE LIBRARY

Cody, Wyoming 1515 E- 6th AVE.

HFLFNA MONTAN"* '^''^20

Kate Walker

USDA Forest Service

Missoula, Montana

March 2003

MONTANA STATE LIBRARY

^ \LiU„,.U Wn

3 0864 1002 3893 3

P.O. Box 200701

Helena MT 59620

406-444-7409

October 2, 2003

TO: Cliris Hunter, Montana Fish, Wildlife and Parks

Virgil Moore, Idaho Department of Fish and Game
Mike Stone, Wyoming Game and Fish Department
Randy Radant, Utali Division of Wildlife Resources
Rich Haskins, Nevada Division of Wildlife
Todd Koel, Yellowstone National Park
Grand Teton National Park
Bruce M^y, U.S. Forest Service

FROM: ken McDonald, Montana Fish, Wildlife and Parks

Please find enclosed hard copies and an electronic copy of the Rangewide Status
Assessment for Yellowstone Cutthroat Trout. This assessment incorporates the collective
knowledge of biologists from Wyoming, Idalio, Montana, Utali, Nevada, and
Yellowstone and Grand Teton National Parks. It represents the best available knowledge
on the status and distribution of Yellowstone Cutthroat Trout, and should serve as a
reference for evaluating the future status of the species. A similar effort recently
completed for westslope cutthroat trout was used extensively by the U.S. Fish and
Wildlife Service in their status review of that species, and to support a not- warranted
finding.

Now that this assessment is complete, I recommend the agencies who signed the
Interstate MOU for Conservation and Management of Yellowstone Cutthroat Trout
reconvene in the near future to discuss the results and map out a course of action of
where we want to go from here. I will be in touch in the next couple of months to solicit
your thoughts about such a meeting and topics we should pursue.

Please send copies of this assessment to others on your staff who might find it useful (the
electronic version can be copied or emailed, or can be used to print additional hard
copies). Thanks for helping to ensure this assessment was completed.

YCT Multi-state Assessment February 10, 2003

Executive Summary

The distribution and abundance of Yellowstone cutthroat trout {Oncorhynchus clarki houvieri:
YCT) have declined from historical levels over part or all of their 1 range. For this YCT
assessment we used existing infomiation provided by 43 fisheries professionals applied through
a consistent methodology to assess the extent of YCT historical range, their current distribution,
including genetic status, and evaluated the foreseeable risks to 1 95 populations designated as
"conservation populations" by management agencies.

We estimated that YCT historically occupied about 17,397 miles of habitat in the western U.S.
YCT currently occupy an estimated 7,528 miles of historical habitats (43%). Genetic testing has
been completed across about 1,880 miles of habitat (25% of occupied habitats), but sample sizes
were variable and sample sizes of 25 fish or more (a sample size that likely would detect as little
as 1% introgression at alpha = 0.05) made up 27% of the samples. YCT with no evidence of
genetic introgression currently occupy about 1,300 stream miles ( \1%) of habitat. Another 105
miles of currently occupied habitats (1%) contained YCT that were identified as part of a mixed
stock where the YCT were not introgressed. We suggest that even though genetic sampling was
nonrandom because sampling likely occurred more frequently in YCT populations that appeared
non-introgressed, some, if not much, of the habitats currently occupied by YCT with no genetic
testing likely support populations that are not introgressed. Approximately 3,000 miles of
occupied habitat were identified as containing genetically unaltered YCT based on no record of
stocking or by having no hybridizing species present. Much of the habitat currently occupied by
YCT was located in designated parks (2%), wilderness areas (19%), and other road-less areas
(40''/o), and almost 70'''o of habitats currently occupied lie within federally managed lands.

A total of 195 separate YCT populations currently occupying 6,346 miles of habitat were
designated as "conservation populations" (84.3% of currently occupied habitat). These
conservation populations were spread throughout the historical range, occuring in 35 of the 41
liydrologic units historically occupied by YCT. Most of these conservation populations were
judged to be "isolets" (143 or 73%); however, meta-populations occupied much more of the
habitat (5,515 miles or 73%). Of the 195 designated conservation populations, 133 (68%) had at
least some component that was tested as genetically unaltered or viewed as being potentially
unaltered. Thirty-nine populations (20%) consisted of only tested unaltered YCT. More isolet
populations were at higher risks due to temporal variability, population size, and isolation than
mcta-populations, but these isolets were generally at less risk from genetic and disease factors
than meta-populations.

This assessment clearly shows that YCT currently occupy significant portions of, and are well
distributed across, their historical range. The data suggest that genetically unaltered YCT
occupy at least 1 7"o and possibly up to 58'!o of currently occupied habitats (7 to 25°o of
historical habitats). Conservation population designations suggest that two ditTerent
conservation management strategies are needed and being implemented to conserve YCT. One
strategy concentrates on preventing introgression, disease and competition risks through isolation
of YCT, while the other concentrates on preserving meta-population function and multiple life-
history strategies by connecting occupied habitats.

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YCT Multi-state Assessment February 10, 2003

Table of Contents

Executive Summary ii

Table of Contents ii

List of Tables iv

List of Figures vi

Introduction 1

Analysis Area 1

Methods 3

Geographic Information System 3

Scale issues 4

Assessment Teams and Workshops 5

Historical Range 5

Barriers to Fish Movement 6

Current distribution 6

Genetic Status 6

Abundance Relative to Habitat Potential 8

Designated "Conservation Populations" 9

Risk Classification 10

Genetic Risks 10

Population Risks 1 1

Conservation Activities 13

Land and Resource Management Impacts 13

Summaries from Database 13

Summaries that Linked Database to GIS Layers 13

Results 16

Historical Range 16

Current Distribution 16

Genetic Status 17

Abundance Relative to Habitat Potential 20

Occurrence in Special Land Management Areas 22

Conservation Populations 25

Ranked Risks to Conservation Populations 29

Restoration Activities Implemented for Conservation Populations 29

Land Use Impacts on Conservation Populations 35

Fine-Spotted and Large Spotted Forms 35

Discussion and Conclusions 39

Historical Range 39

Current Distribution 42

Designated Conservation Populations 43

Conclusions 45

Acknowledgements 47

References 47

Appendix A 50

Appendix B 67

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YCT Multi-state Assessment February 1 0, 2003

Appendix C 70

Appendix D 72

Appendix E 77

Appendix F 78

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YCT Multi-state Assessment February 10, 2003

List of Tables

Table 1. Genetic classes used for assessing genetic status of Yellowstone cutthroat trout in 2001.
7

Table 2. Codes and descriptions used for assessing relative abundance of Yellowstone cutthroat
trout in 2001 9

Table 3. Ranks and descriptions used for assessing genetic risks to designated conservation
populations of Yellowstone cutthroat trout in 2001 . Hybridizing species includes any
introduced species or subspecies that could potentially hybridize with Yellowstone cutthroat
trout 11

Table 4. Ranks and descriptions of population risks to designated conservation populations of
Yellowstone cutthroat trout in 2001 12

Table 5. Codes and descriptions for conservation activities applied to designate conservation
populations of Yellowstone cutthroat trout assessed in 2001 14

Table 6. Codes and descriptions for management activities that could potentially impact

designated conservation populations of Yellowstone cutthroat trout assessed in 2001 15

Table 7. Genetic status for Yellowstone cutthroat trout (both spotting forms combined) by

stream length (miles) within their historical range as of 2001 19

Table 8. Miles of habitat currently occupied by Yellowstone cutthroat trout by genetic status and
relative abundance for assessment done in 2001 21

Table 9. Miles (%) of habitats within historical range that are currently occupied by Yellowstone
cutthroat trout by relative abundance classes, data source ratings for the abundance
determination, and presence of competing species (i.e. non-native trout) 21

Table 10. Miles of habitat occupied (% of occupied habitat by Federal land catagory) by
Yellowstone cutthroat trout in Forest Service designated road-less areas (including
wilderness), National Parks and within all federal lands combined 22

Table 1 1. Miles of habitat occupied (% occupied by Federal land category) by abundance rating
for Yellowstone cutthroat trout in Forest Service designated road-less areas (including
wilderness). National Parks and within all federal lands 23

Table 12. Number and miles of designated conservation populations of Yellowstone cutthroat
(both spotting forms combined) along with proportions of those populations by number and
miles within isolets and meta-populations 27

Table 13. Ranked risks to designated conservation populations of Yellowstone cutthroat trout
(both forms combined) that functioned as "isolets", "meta-populations", and combined by
miles of habitat and numbers of conservation populations that conservation populations
occupied by risk factor as of 2001. Bold population composite risk scores are weighted
scores for temporal variability, population size, demographics, and isolation re-classified
into low to high categories (see Methods for details) 30

Table 14. Number and percentage (based on the 195 conservation populations that were

evaluated) of Yellowstone cutthroat trout conservation populations that have had various
types of conservation, restoration, and management actions implemented to conserve them
as of 2001 34

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YCT Multi-state Assessment Febmary 1 0, 2003

Table 15. Number and percentage (based on the 195 conservation populations that were

evaluated) of designated Yellowstone cutthroat trout conservation populations where human
management activities were known or believed (possible) to have impacted the population
by type of management activity 35

Table 16. Number and miles of designated conservation populations of Yellowstone cutthroat
based on spotting pattern along with proportions of those populations by number and miles
within isolets and meta-populations 38

Table 1 7. Ranked risks to designated conservation populations of Yellowstone cutthroat trout
(represented as large spotted, fine spotted or a mixture of both) that functioned as "isolets",
"metapopulations", and combined by number of conservation populations and miles of
habitat that these conservation populations occupied by risk factor as of 2001 . Bold
population composite risk scores are weighted scores for temporal variability, population
size, demographics, and isolation re-classified into low to high categories (see Methods for
details) 40

Page

YCT Multi-state Assessment February 10, 2003

List of Figures

Figure 1. Streams that were included (dark) as part of the historical distribution and excluded
(light) from the stream layer for historically occupied watersheds 2

Figure 2. Genetic status of Yellowstone cutthroat trout populations throughout their range. Gray
lines indicate historical range 18

Figure 3. Genetic status of Yellowstone cutthroat trout expressed as proportion of currently
occupied habitats (in miles) classified within each genetic status category for assessment
done in 2001 19

Figure 4. Distribution of the number offish sampled for genetic tesfing, by level of introgression
detected, for assessment done in 2001 20

Figure 5. Relative abundance related to habitat potential overlaying designated wilderness and
road-less areas and national parks 24

Figure 6. Designated conservation populafions of Yellowstone cutthroat trout (colored streams)
throughout their range shown overlaying their current distribufion (gray streams) as of 2001 .
Different colors were used to distinguish between different conservation populations and
have no other significance 26

Figure 7. Frequencies of the number of miles occupied by designated conservafion populations
of Yellowstone cutthroat trout throughout their range. Mileage bins are uniformly assigned
at 5.0 mile intervals in top graph and non-uniformly assigned in bottom graph 28

Figure 8. Proportions of miles occupied by designated "isolef (top) and metapopulation
(bottom) Yellowstone cutthroat trout conservation populations ranked into low to high
levels of risk by risk factor (vertical axes) 31

Figure 9. Proportions for numbers of designated "isolet" (top) and metapopulation (bottom)
Yellowstone cutthroat trout conservation populations ranked into low to high levels of risk
by risk factor (vertical axes) 32

Figure 10. Distribution of the number of designated Yellowstone cutthroat trout populations by
composite population risk scores and population type (excludes genefics and disease risks).
33

Figure 1 1. Distribution of YCT conservafion populafions based on presence of the large spotted
form only, the fine spotted form only and a combination of both spotting patterns 37

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YCT Multi-state Assessment February 10, 2003

Introduction

Within the last 20 years several status assessments have been conducted for Yellowstone
cutthroat trout {Oncorhynclms clarki bouvieri; YCT) over part' or all of their historic range
(Behnke 1979: Hadley 1984; Varley and Gresswell, 1988; Thurow et al. 1988; Gresswell 1995;
May 1996; Kruse et al. 2000; Meyer et al 2003). Many of these assessments were either
conducted over only a portion of YCT historic range, involved only a few experts with specific
detailed knowledge of the assessment area, or suffered from a lack of consistency in the sources
of information used. TTiis report updates the past assessments using a protocol that was
consistently applied throughout the historical range of YCT. We assessed the historically
occupied range, current distribution, general abundance and genetic status, and risks for YCT
throughout their historical range. Fisheries professionals from Montana, Idaho, Wyoming,
Nevada and Utah (state agencies. Park Service, USPS, BLM, tribal, private, etc.) provided the
information for this assessment. State fisheries staffs identified and designated "conservation
populations", but information from many different sources was used to assess risks and threats to
these populations. TTie information for this status update was primarily compiled during the later
part of 2001. While this assessment provides consistent and relatively current information on
YCT that can be used by the PWS in relation to their responsibilities under ESA. the longer-
term, and probably more significant use of this assessment, is as an information base to be used
by individual states and other agencies, working collaboratively, to assess, plan and prioritize
their ongoing and ftiture YCT conservation efforts.

The five states where YCT occur have the primary responsibility under their respective state
laws to manage and conserve YCT. Within specific portions of YCT range. Tribal governments
and the National Park Service assume managerial authority for conservation and management of
YCT. The Forest Service, BLM and other federal land and resource management agencies play
an essential role because of a responsibility for management of aquatic habitats on federal lands
and for coordination of land uses consistent with laws, rules, and regulations. The FWS is
charged with administration of the federal Endangered Species Act (ESA) and they concluded
that the petition to list YCT did not contain sufficient or substantial information to indicate that a
listing may be warranted. It is mutually beneficial for the above parties to work together to:
further the collective knowledge, implement conservation actions, and provide the best scientific
information to further YCT conservation.

Analysis Area

The analysis area included all of the known historical range of YCT within the western United
States. We relied primarily on Behnke ( 1 992) to delineate the likely historical range (Figure 1 ).
This area includes, from east to west, the upper portions of the Yellowstone River drainage
within Montana and Wyoming and the upper Snake River drainage in Idaho, Wyoming, Nevada
and Utah. This assessment does not provide an assessment of YCT that have been introduced
into areas outside of the historical range.

Executive summary of YCT status assessment completed for Montana in 1999. Author: Bruce E. May.

Page - 1

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Within the assessment area two forms of YCT have been identified, but have not been
differentiated genetically: 1. a large-spotted form that was dominant in most of the upper
Yellowstone River basin and the lower Snake River basin from Palisades Reservoir downstream
to Shoshone Falls; and 2. a fine-spotted form that was dominant in portions of four watersheds in
the upper Snake River basin. We assessed the status of YCT from several perspectives including
a broad overview of the entire assessment area, a review of the relationship of the large and fine-
spotted forms, and a brief summary of specific conservation population status information.

Methods

We developed a standardized approach and consistent protocols that were used by all
participants who gathered together in localized workshops (Appendices A and B). Information
was gathered by the participants at each workshop and entered into a geographic information
system (GIS) and relational databases. Many different sources of information were used in this
assessment, but consistency was maintained by having one or two individuals attend all
workshops and facilitate data entry and answer questions raised by workshop participants. Since
this assessment relied upon exisfing information, sampling was not random, and in many cases
not independent; therefore, there are undoubtedly biases associated with these data. We discuss
the possible consequences of these biases when we present the results. We have attempted to
qualify and disclose the nature of these data through citations and by having the people that
provided infonnation identify the primary source of informafion (e.g. primarily based on
professional judgment, based on a minimum level of field information or linked to extensive
study). Sources of information were also referenced (e.g. field notes, agency files, reports or
publications)

Geographic Information System

We used the 4th code hydrologic unit code (8-digit EPA designation) as the primary unit for
organizing data input from the fisheries professionals. We also summarized historical range and
current status information using this stratification. The U.S. Geological Survey (USGS) created
the hierarchical hydrologic unit code (HUC) system for the United States in the 1970's. This
system divides the country into 21 Regions, 222 Sub-regions, 352 Accounting Units, and 2,149
Cataloging units based on surface hydrologic features. The smallest HUC used in this study was
approximately 448,000 acres (Hydrologic Units Maps of the Conterminous United States.
Reston, VA. United States Geological Survey. August 2002. http://water.usgs.gov/GlS/metadata/
usgswrd/huc250k.html).

We chose to use stream and river distance as measures of YCT occupancy, both for suspected
histoncal and known currently occupied habitats. Consequently, lake occupancy was not
directly assessed; however, all lakes that were located within the stream network were included,
as length values, if the stream network bisected the lake. Our assessment used GIS tools in
Arcview 3.2 along with extensions created for this project (Steve Carson, Montana Fish Wildlife
and Parks, Helena, Montana modified "ddeaccess.avx" and "routetool.avx" extensions that are
available from ESRl at http://arcscripts.esri.com) as well as a relational database within
Microsoft Access (modeled after the Montana Fish Wildlife and Parks' MFISH database that can

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YCT Multi-state Assessment February 1 0, 2003

be found at http://nris.state.mt.us/scripts/esrimap. dll?name=MFISH&Cmd=INST) for organizing
and displaying the data.

A Latitude- Longitude Identifier (LLID) 1 : 100,000 hydrography layer that was edge-matched
across state boundaries was used as the primary base-layer. The Idaho portion of the study area
was obtained from the Pacific Northwest River Reach Files. The U.S. Geological Survey
(USGS) in Portland, in cooperation with Bonneville Power Administration, the Northwest Power
Planning Council, and other Federal and state agencies and NW Indian Tribes produced a
1 : 100,000-scale River Reach data layer for the Pacific Northwest in the early 1990s. The Pacific
Northwest (PNW) River Reach Files are a geo-referenced river reach data layer that
encompasses the Columbia River Basin within the conterminous United States, the coasts of
Oregon and Washington, Puget Sound in Washington, the Klamath and Goose Lake Basins in
southern Oregon and the Bear Lake Basin in southeastern Idaho (PNW Reach File, Gladstone,
Oregon: Stream Net, August 2002. Imp: wa'.w .strL'amnct.oi!.! pnwr nnwrlionichtmn. A
Latitude-Longitude Identifier (LLID) 1 : 100,000 hydrography for the Montana portion of the
study area was obtained from Montana Fish Wildlife and Parks (Streams. Helena, MT: Montana
Fish Wildlife and Parks, March 2001 and are available at

imp. Iw p. stale. ml, LIN iiiskiclwp b\[ilibrar\ m.s ). A Lafitude-Longitude Identifier (LLID)
1 :100,000 hydrography layer was not available for Wyoming; thus we utilized the USGS
National Hydrography Dataset (IMational Hydrography Dataset, Reston, Virginia: United States
Geological Survey, March 2001; available at hup: nhd.ub^s.LioN ). The National Hydrography
Dataset (NHD) uses different stream routing methods and was not immediately compatible with
the LLID stream layer. Steve Carson and Jeff Hutten, Montana Fish Wildlife and Parks, assisted
in the rerouting and editing of Wyoming NHD data to create a Wyoming LLID routed stream
layer. This LLID hydrography layer routes stream segments by uniquely identifying each stream.
Streams missing from the LLID hydrography layer with known YCT populations were added
from the unrouted NHD data. Delineating lower and upper segment boundaries as distances
above each stream's mouth identified each stream segment occupied by YCT. All known fish
barriers were located as points, also using distance upstream from a stream's mouth.

Scale issues

Using a standard 1 : 100,000 base-layer allowed for consistent summaries among states and other
entities. However, summaries based on this scale will underestimate "true" field lengths of
stream habitats due to scale-based error. There are several potential sources of bias associated
with using 1:100,000 scale LLID hydrography. First, map-derived stream lengths under-estimate
actual stream lengths. Firman and Jacobs (2002) found that while hip-chained measurements of
Oregon coastal streams were significantly correlated to stream lengths computed using
MapTech® Terrain Navigator software and 1 :24,000-scale maps, map lengths needed to be
multiplied by about 1 . 14 to estimate measured stream lengths.

Secondly, there are scale-differences between 1 : 1 00,000 and 1 :24,000-scale hydrography. We
evaluated the magnitude of these scale-differences during the Westslope Cutthroat Trout
assessment. We compared lengths of 30 streams from three different 4'^ code HUC's (10 per
HUC) and found that lengths of streams derived from 1 : 100,000-scale hydrography were only
about 1% shorter than estimates of that same stream using 1 :24,000-scale hydrography (Shepard
et al. 2003). However, these were small unnamed streams that are mapped at 1 :24,000 scale that

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YCT Multi-state Assessment February 10, 2003

were not included in the 1:100,000 scale hydrography. In most cases, these small unnamed
streams did not support YCT or any trout. In a few instances YCT were known to exist in
unnamed streams that were mapped at the finer scale but not at the 1 : 100,000 scale. These YCT
streams were not included in this assessment.

Assessment Teams and Workshops

A total of five workshops were held to obtain the pertinent information for this status update.
One workshop was held in each of the five states that have historical habitat and current YCT
populations. At each workshop a systematic application of the assessment protocol was
undertaken (Appendix A) An estimated 43 fisheries professionals from 10 state, federal, and
tribal agencies and private firms (Appendix B) provided the information that was used in this
assessment. In addition to the fisheries professionals, 8 GIS and data management specialists
also participated in these workshops to assist with data entry and display of status information
for on-site editing of data. Information stored in statewide databases was available in hard copy
and on computer for each of these assessment workshops in tabular and map formats. From two
to five information technology and data entry personnel also attended each workshop to provide
technical support and enter information into computer databases. All fisher>' professionals were
asked to bring field data summaries and reports for their areas of responsibility so existing
databases could be updated and used in this assessment. At each workshop fishery professionals
who had relevant information or knowledge within each 4"^ code HUC worked collaboratively to
fill in data forms that were immediately entered into a computer database. Often individuals
worked on several 4' code HUC teams. As data were entered from paper data forms into the
computerized database at least one individual ft-om each 4^ code HUC team ensured that data
were entered accurately. The fisheries professionals that completed these assessments had
experience levels ranging from several months to several decades. Collectively, these fishery
professionals had a combined total of 862 years of professional fisheries experience, of which
(650 were directly applicable to YCT. The majority of participants had Master's of Science
college degrees (3 1 ), one had a PhD degree, and all but one had at least a Bachelor of Science
degree.

Historical Range

For the purposes of this assessment European "discovery" of the west was set as the benchmark
time {- 1 800) for the historical range of YCT. While it is likely that the distribution of YCT has
expanded and contracted over geological time, written documentation of historical distribution
began around 1800. Behnke (1992) states (p. 89), "Yellowstone cutthroat trout had a much
greater distribution before redband trout invaded the middle Columbia River basin in the late-
glaciai period." Behnke (1992) viewed YCT as the original native trout to the entire Snake River
system and subsequently the upper Yellowstone River drainage. Using Behnke's (1 992)
delineation of historical range as a starting point, we included all streams within any 4th code
HUC's that were within the area Behnke idenfified as being potentially part of the historically
occupied habitat. Fishery professionals were then asked to identify stream segments that should
be excluded fi-om historical range based on evidence for exclusion. Evidence for exclusion
included: geological barriers with no evidence that YCT inhabited waters above the barriers;
tectonic events that would have made regions uninhabitable and were likely either not colonized
or ancient populations had gone extinct and not re-colonized prior to 1 800; and habitat judged as

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YCT Multi-state Assessment February 10, 2003

unsuitable based primarily on thermal regime, stream channel gradient, and minimal stream flow
(Appendix A). In a few cases entire 4th code HUC's were excluded. Information sources that
supported inclusion or exclusion of stream segments as historically occupied were noted.
Important information sources included, historical journal entries, scientific reports, and
evidence of basin transfers by headwater stream captures. Current occupancy of streams was
also evaluated as a possible rationale for inclusion. All stream and river habitat was included
within the historical range unless explicitly excluded by the fishery professionals. Our
delineation of historical range refines previous assessments of historical range. The amount of
historical range we estimated was then used as the baseline for comparison to the current status.

Barriers to Fish Movement

Since barriers to upstream fish movement have important implications for both historical range
and current status, known barriers believed to significantly affect distribution of YCT were
located and identified. Geological (i.e. bedrock waterfalls, naturally dry channel segments, etc.)
and anthropogenic barriers were located and classified. Geological barriers were considered
when potentially excluding lotic habitats fi'om the historical range. Anthropogenic barriers were
considered when assessing current distributions and various risks to conservation populations.
Only barriers of believed significance were included; however, much of the area had not been
surveyed for barriers. Significance of barriers as they related to risk and conservation of YCT
was identified (Appendix A).

Current distribution

For the purposes of this assessment, all stream segments currently occupied by YCT within their
historical range were included. Stream segments occupied by YCT outside historical range were
not included. Stream segments where YCT populations were supported or maintained by
stocking were not included in current distribution; however, stream segments that may have been
stocked with YCT in the past, but currently were maintained exclusively by natural reproduction
were included. All waters that supported YCT and appeared on the LLID hydrography layer,
regardless of level of introgression, were included. However, the genetic status of YCT within
each stream segment was classified (see below). In addition to genetic status, biologists ranked
the abundance of YCT inhabifing each stream segment. Additional notations for each occupied
segment included: a determination of which YCT form (i.e. large-spotted, fine-spotted or both)
was present; whether competing species (principally non-native salmonids) were present;
identification of restoration or conservafion activities implemented within each occupied
segment; and identification of land uses and fish management activities believed to be
influencing YCT in the occupied segments. These results were summarized by length of habitat
occupied and not by number of stream segments occupied. Number of stream segments was not
a meaningful measure because this number does not equate to number of populations and lengths
of stream segments varied widely. The stream segment information was aggregated within the
"conservation population" assessment (see below).

Genetic Status

Six classes idenfifying genefic status for stream segments were applied (Table 1). Four classes
were used for those stream segments that had been genetically tested and two classes for those

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YCT Multi-state Assessment February 10, 2003

where no genetic testing had been done (Table 1 ). Genetic sampling involves many complex
issues that can make clear interpretation and reporting of results difficult, especially within
standardized databases. We will briefly address a few of these issues here, but suggest reading
Appendix D in Shepard et al. 2003 for more detail.

Table 1 . Genetic classes used for assessing genetic status of Yellowstone cutthroat trout in 2001 .

Code Description Genetic Report Code

A Genetically unaltered (<1% introgression) - tested via Tested; Unaltered

electrophoresis or DNA

B Introgressed 75% or less and 99% or more - tested via Tested; <=25% to >=1%

electrophoresis or DNA introgressed

C Introgressed more than 75% - tested via electrophoresis or Tested; > 25% introgressed
DNA

H Potentially unaltered with no record of stocking or Suspected Unaltered

contaminating species present

J Suspected hybridized with records of contaminating species Potentially Altered
being stocked or occurring in stream

N Hybridized and Pure populations co-exist in stream (use only Mixed Stock; Altered and
if reproductive isolation is suspected and testing completed) Unaltered co-exist

Genetic tests can detect introgression between YCT and potentially introgressing species or
subspecies by finding alleles unique ("diagnostic alleles") to that potentially introgressing
species or subspecies within YCT populations. The number, and thus the proportion, of
potentially introgressing species or subspecies "diagnostic" alleles within YCT populations, is
used to estimate the level of introgression. One consequence of this approach is that proving a
stock of YCT to be genetically pure is essentially impossible: all individuals in a population
would have to be tested. Therefore, sample size must be considered when evaluating the
reliability of any genetic test. Generally, sample sizes should be large enough to determine, with
a pre-determined level of statistical reliability (95% has often been used), that a 1% or less level
of introgression would be detected. Both the number offish sampled and the number of alleles
that are "diagnostic" between species or subspecies determine the sample size needed for a pre-
determined level of statistical reliability. Thus, when genetic testing finds no evidence of
introgression, sample size is very important for assessing how valid the result may be. For this
assessment we reported results of all genetic testing, regardless of sample size, and then
displayed and summarized sample sizes for all genetic testing.

Different genetics laboratories, and somefimes even the same lab, may report genetic results
differently; consequently, it can be difficult to compare genetic results across broad geographic
areas. Especially when only brief summaries of these data are stored in standardized fish
resource databases. An example of where this type of problem may occur is that of a mixed
stock population, where some individuals within the population may be genetically unaltered
YCT and other individuals may be genetically unaltered rainbow trout (RBT). Unless either the
local fisheries professional or the database indicated that non-random mafing was occurring
(code N; Table 1 ), we assumed genetic results were a fianction of random mating. If random

Page - 7

YCT Multi-state Assessment February 10, 2003

matings were incorrectly assumed to be operating for the above hypothetical mixed stock
population, genetic sample results would indicate introgression at levels in proportion to the
proportion of RBT to YCT for this hypothetical population. Where there was evidence of non-
random mating due to both the presence of some YCT individuals within the population that had
no evidence of introgression and evidence that reproductive isolation was occurring, YCT in
these stream segments were designated as a mixed stock that had both "genetically altered" and
"unaltered" individuals. This situation usually occurred in main rivers and mainstem tributaries
where it was known that YCT spawned in different tributaries or at different times than the
introgressing species (i.e. rainbow trout). However, when evidence to support non-random
mating was lacking, random mating was assumed. This assumption likely introduced bias toward
classifying stream segments as introgressed when some may have been mixed stock populations.

The levels of introgression we assigned for genetically tested stream segments were based, in
part, on the literamre. For our genetically unaltered ("pure") stream segments (code A; Table 1)
we selected less than 1% introgression, based on the most commonly defined level of
introgression that genetic sampling is designed to detect (Anon. 2000). The next two levels (i.e.
<=25% to >=1% and >25% introgression) were assigned based on conservation planning
considerations. The <=25% to >=1% classification was selected as the grouping that would
include conservation populafions that had specific unique attributes important for conservation.
Within this grouping are the stream segments that tested 90 to 99% YCT and there are
indications that meristic counts are not different between individuals ft"om populations that are
not genetically altered and those that are fi-om populafions with 10% or less introgression (Leary
et al. 1996). Stream segments that tested >25% might have appeared to be cutthroat trout to the
untrained eye, but they were treated as primarily having recreational value and were not earned
forward as conservation populations. The class where both hybrids and pure individuals inhabit
the same stream segment (code N; Table 1) indicated some reproductive isolafion and were
identified as a mixed stock

Genetic information was extremely limited for some large geographic areas particularly in the
large tracts of wilderness, road-less, and National Park land in Montana, Idaho, and Wyoming.
The genetic characterization for the occupied stream segments in these areas were primarily
"suspected hybridized" or "potentially unaltered. We suspect that many of these segments
actually support genetically pure YCT. This question was addressed in the westslope cutthroat
status review that was completed in 2002 (Shepard et al. 2003) and we feel that a similar result
could exist for YCT. In addition, recent YCT population monitoring in southeastern Idaho
indicated that a high number of YCT judged to be genetically unaltered based on morphological
inspection were in fact genetically unaltered based on genetic test results (Meyer et al. 2003).

Abundance Relative to Habitat Potential

In addition to classifying genetic status, relafive abundance of YCT in qualitative terms (i.e.
abundant, common, rare or unknown) was also specified for each stream segment. For stream
segments where no quantified population determinations were available, habitat condition was
used as a surrogate to provide likel> abundance for each stream segment occupied by YCT
(Table 2; Appendix A). Relative abundance ranks based on habitat potential were rated in two
ways. First, where abundance data were available, that data was compared to all sites that had
similar habitat potential and rated V^y comparison. Data quality for these segments was usually

Page - 8

YCT Multi-state Assessment February 10, 2003

rated as high or good. Secondly, for those segments where no quantitative fish abundance data
were available, YCT abundance was ranked solely from the condition of habitat relative to its
potential. Data quality for these cases was rated as low. Thus, when quantitative fish abundance
information was available both the measured abundance and habitat condition were used to rank
relative abundance. When no quantitative abundance data were available only habitat condition
was used to rank abundance. These results were also summarized by length of habitat occupied
and not by number of stream segments occupied. Number of stream segments was not felt to be
a meaningful measure because this number does not equate to number of populations and lengths
of stream segments varied widely. Where field data were available, abundance was rated based
on how similar the measured abundance was to measured abundances from areas of similar types
of habitat that were not impacted by human activities. Where no field data were available,
abundance classes were subjective and based, to a large extent, on the quality of the habitats
occupied. Consequently, analyses between the relative abundance levels we assigned and land-
use or other habitat-related variables were not independent.

Table 2. Codes and descriptions used for
assessing relative abundance of
Yellowstone cutthroat trout in 2001 .

Code Description

99 Unknown

A Abundant - viewed as being at site
potential or in high quality habitat

C Common - Possibly slightly below site
potential or habitat less than opfimal

R Rare - Restricted by sub-optimal habitat
or significantly below site potential

Designated "Conservation Populations"

YCT are considered a game fish by all state and federal agencies that manage this subspecies.
Consequently, all YCT populations have sport fish value and are managed as such by the various
states and national parks in which they occur, regardless of their genetic status. Many YCT are
managed as "conservation populafions" with addifional management emphasis placed on
preserving the genetic makeup and/or other important attributes of these populations. Most of
the western states that have management and conservation authority for cutthroat trout
participated in the development of a posifion paper on genetic management (Anon 2000). This
position paper describes a hierarchical classification for conserving cutthroat trout that includes:
1) a core component of genetically unaltered populafions or individuals; 2) designated
conservafion populations that may be either genetically unaltered or slightly introgressed but
have attributes worthy of conservation; and 3) populations that are managed primarily for their
recreational fishery value. Core populations are recognized as having important genetic value
and would serve as donor sources for developing either captive brood or for re-founding

Page - 9

YCT Multi-state Assessment February 10, 2003

additional populations. Management will emphasize conservation, including potential
expansion, of both core and conservation populations.

For this assessment any stream segment that supported YCT could potentially be designated as
either an individual "conservation population", aggregated as part of a larger networked or
connected "conservation population", or be considered as having recreational fishery value, but
not considered within YCT conservation. Designated "conservation populations" that occupied
two or more connected stream segments were viewed as population networks ("meta-
populations") that had the potential to interact with each other (Hanski and Gilpin 1991).
Populations were designated as "conservation populations" based on whether they represented a
core conservation population having no genetic alteration or there were identified unique
attributes such as expression of unique or multiple life-history strategies, adaptation to specific
environmental or habitat conditions, and geographic location (Anon 2000; Allendorf et al. 2001).

Almost all stream segments occupied by YCT where genetic testing found no evidence of
introgression were classified as "core conservation populations". A few isolated stream
segments where YCT were genetically tested and there was no evidence of introgression were
not classed as conservation populations. These populations occupied very little habitat and it
was not deemed effective to invest in expanding them because expanding these populations was
infeasible given current restoration techniques. Some of these populations might be replicated
by moving either fish or gametes in the fiature, but this restoration activity would be speculative
at this time.

Ail conservation populations were classified as either "isolates" or "meta-populations"
depending upon their isolation or connecfivity and likely genetic exchange between stream
segments. We also identified conservation populations that were considered as a "source" to
other conservafion populations. This information was felt to be potentially important to future
conservation decisions.

We summarized information for designated conservation populations based on length of stream
occupied, number of populations, and geographic distribution. Since there was a very wide
range of lengths of habitats occupied by the various conservation populations we chose to
present these data in terms of length occupied and number of populations.

Risk Classification

The risks identified in this assessment are potential risks that could occur in the "foreseeable
future" (considered to be two to tliree decades). Risks were stratified into two major categories:
genetic and general population-level health.

Genetic Risks

GeneUc risk was defined by the risk of future introgression of YCT in a conservation population.
Distance from potential sources of anthropogenic introgression and the presence of documented
barriers between those sources and the conservation population were the two primary
components that were assessed to determine genefic risk (Table 3). In addifion, where there was
documented evidence indicating that potentially introgressing species or subspecies were

Page- 10

YCT Multi-state Assessment February 1 0, 2003

reproductively isolated from YCT, due to either temporal or spatial isolation during spawning,
the genetic risk rating for that conservation population was reduced. Normative salmonids that
could potentially hybridize with YCT. had been stocked, either legally or illegally and, were now
reproducing naturally in the wild were considered as posing a genetic risk to YCT.

Table 3. Ranks and descriptions used for assessing genetic risks to designated conservation

populations of Yellowstone cutthroat trout in 2001 . Hybridizing species includes any
introduced species or subspecies that could potentially hybridize with Yellowstone
cutthroat trout.

Rank Acrivity

1 Hybridizing species CANNOT INTERACT with existing YCT population. Barrier
provides complete blockage to upstream fish movement. No hybridizing species in close
proximity to YCT population.

2 Hybridizing species are in same stream and/or drainage FURTHER THAN 1 0 KM from
YCT population, but not in same stream segment as YCT, or may be WITHIN 10 KM
WHERE BARRIER EXISTS, BUT THE BARRIER MAY BE AT RISK OF FAILURE.

3 Hybridizing species are in same stream and/or drainage WITHIN 10 KM of YCT
population and NO BARRIER EXISTS; however, hybridizing species not yet found in
same stream segment as YCT population.

4 Hybridizing species are SYMPATRIC with YCT population in same stream segment.

Population Risks

Demographic and stochastic population risks were assessed using criteria established by Rieman
et al. (1993). Four separate types of risk were considered including: temporal variability,
population size, population productivity, and isolation (Table 4). These four main factors were
assessed individually and then weighted and summed to derive a final composite risk factor.
Weightings were assigned to each risk factor based on advice from those who developed the
demographic and stochastic population risk matrix (Rieman et al. 1993; D. Lee, U.S.D.A. Forest
Service, Rocky Mountain Research Station, Boise, Idaho, personal communication) as:
Temporal Variability = 0.7; Population Size = 1.2; Population Productivity (Growth/Survival) =
1.6; and Isolation = 0.5. Weighted composite risk scores could potentially range from 4 to 16
and were then ranked into four low to high risk categories by placing them in four nearly equal-
sized bins (4 to < 7; 7 to < 10; 10 to <13; and 13 to 16).

Page - 1 1

YCT Multi-state Assessment

February 10,2003

Table 4. Ranks and descriptions of population risks to designated conservation populations of
Yellowstone cutthroat trout in 2001.

Type of Risk

Rank

Criteria

Population
Productivity

1

Population is increasing or fluctuating around an equilibrium
that fills available habitat that is near potential. No normative
competing or predating species present.

2

Population has been reduced from potential, but is fluctuating
around an equilibrium (population relatively stable and either
habitat quality is less than potential, or another factor - disease,
competition, etc. - is limiting the population).

3

Population has been reduced and is declining (year-class
failures are periodic; competition may be reducing survival;
habitat limiting population).

4

Population has been much reduced and has either been
declining over a long time period or has been declining at a
fast rate over a short time-period (year-class failures are
common; competition or habitat dramatically reducing
survival).

Temporal Variability

1

At least 75 km of connected habitats

2

25-75 km of connected habitats

3

10-25 km of connected habitats

4

< 10 km of connected habitats

Isolation

1

Migratory forms must be present and migration corridors are
open (connectivity maintained).

2

Migratory forms are present, but connection with other
migratory populations disrupted at a frequency that allows
only occasional spawning.

3

Questionable whether migratory form exists within connected
habitat; however, possible infrequent straying of adults from
other populations into area occupied by population.

4

Population is isolated from any other population segment,
usually due to barrier, but may be related to lack of movement
or distance to nearest population.

Population Size

1

> 2,000 adults

2

500-2,000 adults

3

50-500 adults

4

< 50 adults

Page- 12

YCT Multi-state Assessment February 1 0, 2003

Conservation Activities

A listing of potential conservation activities was provided to workshop participants. If any
conservation activity had been applied to any stream segment of a conservation population, that
activity was checked and linked to the conservation population (Table 5; Appendix A). Since we
did not specifically address the significance or effectiveness of various conservation activities,
we summarized these data only by the number of conservation populations affected by each type
of activity. For many conservation populations, especially those that occupied larger areas of
habitat, conservation activities may have only affected a portion of the population.

Land and Resource Management Impacts

Fishery professionals were asked to judge whether various land, water, and/or fish management
activities affected each stream segment and therefore the designated conservation population
(Table 6; Appendix A). Participants were asked whether each acdvity resulted in a "known",
"possible", or "no" (not checked) impact to the stream segment. Similar to the conservation
activities, we did not specifically ask how many miles of habitat occupied by conservation
populations each type of management activity influenced. Thus, we also summarized these data
only by the number of conservation populations affected by each management activity. For
many conservation populations, especially those that occupied larger areas of habitat,
management activities (land uses) likely only affected a portion of the population. Participants
varied in how they rated whether a stream segment was impacted by a particular activity,
especially for stream segments that included relatively large areas of connected habitat and a
particular acdvity was occurring only on a portion of the occupied segment. Thus, ratings for
land management effects on larger meta-populations were inconsistently applied.

Summaries from Database

Data provided by the fishery professionals were summarized directly fi-om the Microsoft Access
database using queries within Access. Summarized data were then copied to Excel spreadsheets
where these data were further reduced to produce summary tables and figures. Most summaries
within this report are summarized over the enfire historical range of YCT. Additional summaries
by 4 code HUC and associated conservation populations are provided in appendices (Appendix
F).

Summaries that Linked Database to GIS Layers

To better assess exisfing regulatory mechanisms associated with land management for the
streams currently occupied by YCT we used Arcview to select ("clip" feature in Arcview) stream
segments occupied by YCT that were within designated Forest Service wilderness areas,
designated Forest Service "road-less" areas, and USDI National Parks. After clipping the stream
segments occupied by YCT using the above polygon layers we computed the length of streams
occupied by YCT that were within the above land management designations using a query in
Arcview ("[Shape]. retumlength" query).

Page- 13

YCT Multi-state Assessment February 10, 2003

Table 5. Codes and descriptions for conservation activities applied to designate conservation
populations of Yellowstone cutthroat trout assessed in 2001.

Code

! Description

3

Water lease/In-stream enhancement

4

Channel restoration

5

Bank stabilization

6

Riparian restoration

7

Diversion modification

8

Barrier removal

9

Barrier construction

10

Culvert replacement

11

Fish screens

12

Fish ladders

13

Spawning habitat enhancement

14

Woody debris

15

Pool development

16

Irrigation efficiency

17

Grade control

22

In-stream cover habitat

24

Riparian Fencing

31

Physical removal of competing/hybridizing species

32

Chemical removal of competing/hybridizing species

72

Population restoration/expansion

73

Angling regulations
Public outreach

99

Other (specify in comments)

Page- 14

YCT Multi-state Assessment February 10, 2003

Table 6. Codes and descriptions for management activities that could potentially impact

designated conservation populations of Yellowstone cutthroat trout assessed in 2001.

Code

Activity

1

Timber Harvest

2

Range (livestock grazing)

3

Mining

4

Recreation (non-angling)

5

Angling

6

Roads

7

Dewatering

8

Fish stocking

10

Other, specify in comments

Page- 15

YCT Multi-state Assessment February 10, 2003

Results

Historical Range

Based on the LLID hydrography layer, a total of about 17,407 miles of lotic habitat were
identified as having been historically (circa 1800) occupied by YCT (Figure 1; Appendix E).
The estimated amount of historical range in each state was about 4,049 miles in Montana (23%),
6,269 miles in Idaho (36%), 6,889 miles in Wyoming (40%), and nearly 100 miles (0.5%) in
both Nevada and Utah. Historically occupied habitat included stream segments occupied by both
large and fine-spotted forms of YCT, and in some instances both forms were present. We
believe that fine spotted YCT occupied only those HUC's (i.e. Snake Headwaters, Gros Ventre,
Greys-Hoback, Salt and Palisades) in the upper most portion of the Snake River basin. In some
instances, it was probable that both forms were present together in the same stream segments
within the upper Snake River basin.

Several 4'*' code river basins, including the Lower Rosebud, Lower Tongue, Dry Creek,
Badwater, and Muskrat in the Yellowstone River system, and the western-most watersheds in the
sinks drainages in the Snake River system were excluded as historical habitats, even though
previous assessments may have included some or parts of these basins within the historical
range. We excluded these watersheds as historically occupied because YCT were not found
during fishery surveys, either in historical or current records, in any waters within these basins;
and/or we found written historical accounts that specifically stated that streams within the basin
were devoid of trout.

Current Distribution

YCT currently occupy about 7,528 miles (43%) of the nearly 17,400 miles of historically
occupied habitats. YCT currently occupy over 2,100 miles in Idaho (35% of historical), over
1,400 miles in Montana (35% of historical), about 3,860 miles in Wyoming (55% of historical),
just over 40 miles in Nevada (45% of historical), and about 42 miles in Utah (41% of historical).

As part of the current distribution assessment an attempt was made to identify, on a stream
segment basis, the presence or absence of the two forms of YCT (i.e. large spotted and fine
spotted YCT). For each stream segment, reviewers were asked to identify which YCT form was
dominant. In addition, many reviewers made comments suggesfing that both spotting forms
were present. The large spotted form of YCT were identified as being present in 6,091 miles
(81% of current) of the 7,528 miles of currently occupied habitat. Of these stream miles, large
spotted YCT were sympatric with fine spotted YCT in 1,084 miles, either as the dominant form
(544 miles; 7.2%) or as the sub-dominant form (540 miles, 7.2%). Fine-spotted YCT were
identified as being the only spotting form in 1 ,438 miles of stream. Due to the use of the fine-
spotted form in recreational fishery management, their distribution has been enlarged to include
portions of 15 HUC's with total occupied habitat estimated at 2,522 miles (34% of current).
There were no HUC's that contained only fine-spotted YCT.

Page - 16

YCT Multi-state Assessment February 10, 2003

Genetic Status

Genetic testing of YCT (both spotting forms combined) across all of the currently occupied area
has not been completed. Most genetic testing was not completed in random fashion.
Consequently, the available genetics information does not constitute a random sample taken
from the entire YCT population. Instead, there was a tendency to sample fish from populations
that appeared to be phenotypical YCT. Genetic sampling has been conducted in over 1 ,880
miles of occupied habitats (25% of occupied habitats). No evidence of introgression was found
from samples covering about 1,300 miles (69% of tested area, 17% of occupied habitats, and 7%
of historical habitats; Table 7; Figures 2 and 3; Appendix F). YCT that made up part of a mixed
stock population and were not introgressed occupied another 105 miles for a total of genetically
tested non-introgressed YCT occupying over 19% of currently occupied habitats. YCT that
inhabited over 3,018 miles (40% of occupied habitats and 17% of historical habitats) are
suspected of being genetically unaltered, based on the absence of introduced hybridizing species
and the lack of records that identify stocking of hybridizing species. YCT in about 2,629 miles
(35% of occupied habitats and 15% of historical habitats) were identified as having the potential
of being hybridized due to the presence, or past stocking, of hybridizing normative species or
subspecies (Table 7).

To better evaluate the quality of genetic sampling, we looked at the sample sizes of genetic
sampling events related to whether more or less than a 1% level of introgression was found
(Figure 4). The number offish sampled represents each sampling event and, in some cases,
more than one sampling event were probably pooled, but we had no way of assessing pooled
samples. Of those samples that indicated a level of introgression of !%> or less, 21% had 25 fish
or more and over 48% had 20 fish or more in the sample. Most genetic testing techniques allow
for a 95% confidence at detecting a 1% level of introgression with a 25 fish sample.

To provide insight into the likely genetic status of YCT within habitats classified as "Potentially
Unaltered" and "Suspected Altered" we refer the reader to the recent westslope cutthroat (WCT)
status review that was completed in February, 2003 (Shepard et al. 2003). For central Idaho
where limited genetic testing has been conducted, the assessment team took a closer look at
classificafion results for 10 separate 4th code HUC's where some genefic tesfing had been
conducted, they compared the level of introgression within tested stream seginents to the
classifications for stream seginents where no genetic tesfing had been done. Seven of these ten
HUC's had the majority of the stream segments classified as "Potentially Altered". Of these
seven, genefic testing in five HUC's found no evidence of introgression, while genetic testing in
one HUC found 65% of tested stream length had no evidence of introgression and testing in
another HUC found evidence of introgression in all tested samples. Conversely, some stream
segments in one HUC that supported WCT classified as being primarily "Suspected Unaltered"
tested as introgressed, while genetic testing in the other two HUC's that were predominated by
streams classified as "Suspected Unaltered" found no evidence of introgression. We feel the
situation for YCT maybe somewhat similar to that of WCT in that the potenfial for introgression
is highest in stream seginents that are connected to waters that support nonnative species or
subspecies that could interbreed with YCT. We caution against drawing specific conclusions
about genefic status of YCT populations identified as potenfially unaltered or suspected altered
from a genefic perspective. The definitive way of determining genetic status is through formal
genefic testing.

Page - 1 7

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35%

41%

I Genetically unaltered (>99.0%) - tested via
electrophoresis or DNA

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to be 75% to 99% YCT |

I Introgressed (hybridized) - tested and found
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stream (use only if reproductive isolation is
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Figure 3. Genetic status of Yellowstone cutthroat trout expressed as proportion of currently
occupied habitats (in miles) classified within each genetic status category for
assessment done in 2001.

Table 7. Genetic status for Yellowstone cutthroat trout (both spotting forms combined) by
stream length (miles) within their historical range as of 2001.

Within historical range

Genetic status

Miles

%of
occupied

%of
historical

Tested; Unaltered (<1%
introgression)

1301.4

17.3

7.4

Tested; <=25% to >=1%
introgressed

394.6

5.2

2.3

Tested; >25% introgressed

79.9

1.1

0.5

Potentially Unaltered

3018.5

40.1

17.2

Suspected Altered

2629.6

34.9

15.0

Mixed Stock; Altered and
Unaltered

104.9

1.4

0.6

TOTAL

7528.0

100.0

43

Page- 19

YCT Multi-state Assessment

February 10,2003

25

Genetic Sample Size

n< = 1% introgression
!■> 1% introgression

10 15 20 25 30

Number of Fish in Each Sample

45

Figure 4. Distribution of the number offish sampled for genetic testing, by level of introgression
detected, for assessment done in 2001.

Abundance Relative to Habitat Potential

A total of almost 2,281 miles of occupied habitats (30% of currently occupied habitats)
supported populations identified as being abundant (i.e. believed to be at or near the habitat's
potential capacity); over 3,302 miles of occupied habitat had population levels viewed as
common (44% of occupied); about 1,505 miles of occupied habitat supported populations
considered as rare (i.e. could be linked to habitat significantly below potential); and, 439 miles of
occupied had unknown population abundance (Table 8). Of nearly 2,281 miles of habitat that
had populations deemed to be abundant, a total of about 465 miles (20% of miles deemed near
capacity and 6% of occupied habitats) also had no evidence of genetic introgression. Over 81%
of habitats classified as abundant had field estimates to support the classification, while only 3%
had data that identified professional judgment as an information source (Table 9).
Approximately 525 miles of occupied habitat (40%) with abundance classified as common was
associated with genetically unaltered YCT. Only 288 miles of occupied habitat (22%)
supporting genetically unaltered YCT had population levels rated as rare.

Page - 20

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YCT Multi-state Assessment

February 10,2003

Occurrence in Special Land Management Areas

Of over 7,528 miles of habitats currently occupied by YCT (both forms combined),
approximately 4,427 miles (59% of currently occupied habitat) were associated with land
administrated by specific Federal agencies. An estimated 764 miles were in designated National
Parks; 1,086 miles occurred within designated Forest Service wilderness areas; and, 2,510 miles
were within Forest Service road-less areas (including wilderness) (Table 10; Figure 5). Since we
did not assess BLM wilderness or road-less areas in this assessment, the estimates of the
proportions of habitat currently occupied by YCT within lands managed as wilderness and road-
less are slight under-estimates.

The genetic status breakdown for YCT that occupy habitats on federal lands having special
management focus is presented in Table 10. YCT tested as unaltered and those identified to be
potentially unaltered occupied almost 2,213 miles of habitat on federal land that are managed as
National Parks or Forest Service road-less, including, wilderness areas. This is about 29% of
the total occupied YCT habitat. The number of miles occupied by YCT tested as unaltered and
those identified to be potentially unaltered for all federal lands was 2,859 miles (38% of
currently occupied habitat). Approximately 541 miles (7%) of currently occupied habitats that
supported YCT with no evidence of introgression occurred within areas administered by the
USDA Forest Service as road-less or by the National Park Service. The amount of occupied
habitat within these special management areas with known genetic alteration was 1 54 miles or
about 2% of currently occupied habitat.

Table 10. Miles of habitat occupied (% of occupied habitat by Federal land category) by

Yellowstone cutthroat trout in Forest Service designated road-less areas (including
wilderness), Nafional Parks and within all federal lands combined.

Nafional Parks

Forest Service
Wilderness

Forest Service
Road-less

All Federal Lands

Genetic status

Miles
170.8

Miles

Miles

Miles

t— ■ - ■ •
Tested; Unaltered

(22%)

206.2

(19%)

370.6

(15%)

695.6

(16%)

Tested introgressed;
75% to 99% YCT

20.0

(3%)

83.0

(8%)

111.4

(4%)

186.2

(4%)

1 „„ — — -■ -■■ ■

Tested; > 25%
introgressed

16.8

(2%)

22.5

(1%)

30.8

(<1%)

Potentially Unaltered

401.3

(52%)

424.0

(39%)

1270.9

(51%

2163.6

(49%)

Suspected Altered

172.3

(23%)

352.2

(32%)

724.2

(29%)

1336.5

(30%)

Mixed Stock; Altered
and Unaltered

4.1

(<1%)

10.6

(<1%)

14.4

(<1%)

. — 1

Total 764.4

1086.3

2510.3

4427

Page - 22

YCT Multi-state Assessment

February 10,2003

Abundance information for YCT occupying 4,427 miles of habitat on federal lands indicated that
approximately 1,373 miles (31%) were rated as abundant. YCT in another 2,021 miles of
occupied habitat were rated as common. YCT in approximately 697 miles of stream were rated
as rare and YCT abundance was unknown in approximately 335 miles of habitat (Table 1 1 ).

The spatial arrangement of YCT whose abundance was deemed "abundant" and "common" were
obviously clumped and appeared related to the presence of areas designated as wilderness, road-
less, or national parks (Figure 5). About 306 miles classified as "abundant" (28% of all miles in
this category) were in wilderness and about 739 miles (29% of all miles in this category) were
within the road-less category that included wilderness (Table 1 1). Because assessments of
abundance, regardless of data quality, were likely linked to quality of habitat, it is not surprising
that many populations located in wilderness and road-less areas would be designated as being at
or near capacity. Except where empirical observations of abundance indicated otherwise, nearly
all habitats in Forest Service road-less areas (wilderness) and National Parks were presumed to
have abundance levels (abundant or common) consistent with pristine conditions.

Table 1 1. Miles of habitat occupied (% occupied by Federal land category) by abundance rating
for Yellowstone cutthroat trout in Forest Service designated road-less areas (including
wilderness). National Parks and within all federal lands.

National Parks

Forest
Wile

Service
emess

Forest Service
Road-less

All Federal
Lands

Abundance

Miles

Miles

Miles

Miles

Abundant

297.1

(39%)

306.2

(28%)

738.6

(29%)

1373.2

(31%)

Common

252.1

(33%)

599.7

(55%)

1242.7

(50%)

2021.5

(46%)

Rare

99.3

(13%)

116.6

(11%)

348.2

(14%)

697.2

(16%)

Unknown

115.8

(15%)

63.9

(6%)

180.7

(7%)

335.1

(7%)

Totals

764.3

1086.3

2510.3

4427

Page - 23

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I

YCT Multi-state Assessment February 10, 2003

Conservation Populations

A total of 195 populations of YCT (both spotting forms combined) occupying about 6,346 miles
of habitat (over 84% of currently occupied habitats; 36% of historical range) were identified as
conservation populations (Figure 6; Appendix F). These designated conservation populations
were spread throughout the historical range, occurring in 35 of the 41 HUC's historically
occupied by YCT. These conservation populations were obviously more densely concentrated
within the core of the historical range than near the fHnges (Figure 6). Individual conservation
populations occupied from 0.3 to over 1,500 miles of habitat (median = approximately 10 miles:
Figure 7). The distribution of lengths of habitat occupied by conservation populations was
skewed with most of the populations (126) occupying 10 miles or less. Most conservation
populations were isolets (143) that occupied a total of 831 miles of habitat (Table 12). A total of
52 meta-populations occupying 5,515 miles of habitat were identified.

Of the 195 designated conservation populations, 39 (20%) were considered as "core"
conservation populations having been tested and found to be genetically unaltered (Table 12).
These core conservation populations occurred as 37 "isolates" and 2 meta-populations that
occupied approximately 236 miles of habitat (11% of current habitat and 5% of historical
habitat). There were an additional 10 conservation populations that were comprised of stream
segments tested as unaltered and segments that were untested but felt to be potentially unaltered.
There were also 84 populations (71 isolates and 13 meta-populations) made up solely of
potentially unaltered stream segments. In combination, conservation populations that were
tested unaltered with those believed to be unaltered would bring the total of "core" conservation
populations to a total of 133. A total of 61 conservation populations included stream segments
suspected of being altered and segments known to be introgressed based on genetic testing

The amount of habitat occupied by "core" populations known to be genetically unaltered was
estimated to at 235 miles (about 3% of currently occupied habitat; slightly more than 1% of the
historical habitat). There were approximately 685 stream miles (9% of current; 4% of historic)
associated with conservation populations believed to be potentially unaltered and another 949
miles (13% of current; 5.4% of historic) composed of a mixture of tested unaltered and
potentially unaltered. In combination, there were 133 potential "core" populations (1,870 miles;
24.8%) of current and 10.7%) of historic) of YCT with stream segments existing as tested
unaltered, or a combination of tested and potentially unaltered or only potentially unaltered.
Conservation populations composed of suspected altered stream segments and those composed
of mixture of tested altered and varying combinations of altered and other genetic makeup
comprised, 580 and 3,896 miles, respectively.

Page - 25

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YCT Multi-state Assessment

February 10,2003

140
120

100

>.

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10 110 210 310 410 510 610 710 810 910 1010 1110 1210 1310 1410 1510

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Miles

Figure 7. Frequencies of the number of miles occupied by designated conservation populations
of Yellowstone cutthroat trout throughout their range. Mileage bins are uniformly
assigned at 5.0 mile intervals in top graph and non-uniformly assigned in bottom
graph.

Page - 28

YCT Multi-state Assessment February 10, 2003

Ranked Risks to Conservation Populations

We rated risks to 195 designated YCT conservation populations by miles of habitat occupied
(Table 13 and Figure 8; Appendix F) and by number of populations (Table 13 and Figure 9;
Appendix F). The two distinct types of conservation populations, "isolets" and "meta-
populations", were separated in the analyses. In general, isolet populations were at higher risk
than due to temporal variability (amount of occupied habitat), population size, and isolation
meta-populations, especially when rated by number of populations (Table 13), but isolet
populations were at less risk than meta-populations due to genetic introgression. Risks
associated with demographic factors were about the same for "isolates" and "meta-populations.
These findings validate the fact that while smaller, isolated populations are usually much more
susceptible to population level risks due to isolation, small population size, and temporal
variability; their isolation makes them less susceptible to genetic introgression. Conversely,
while more meta-populations (larger, connected populations) were less vulnerable to population
risks such as temporal variability, isolation, and small population size, their connectedness made
them more susceptible to genetic introgression risks (Table 13). Composite population risk
scores ranged fi-om a low of 4 to a high of 16 with most scores being over 10 for isolet
populations and under 8 for meta-populations (Figure 10). "Isolets" were at moderately high risk
based on the composite of risk characters. Meta-populations were viewed as being at moderately
low risk when all, non-genetic, risk factors were considered. It is important to note that 101
YCT conservation populations (5 1 .8%) were sympatric with compefitive species of trout. By
convention, the demographic risk factor associated with populations that were sympatric with
competitive species had to be rated down by one to two points.

It is important to understand that population risks are presented in relative terms. Higher genetic
risk ratings for meta-populations do not mean that each of these population is doomed to a fate of
being genetically contaminated. Nor do high isolation risk ratings mean that all isolated
populations will be eventually eliminated. The risks evaluated in tliis review stiould be
viewed in relative terms and not as absolutes.

Restoration Activities Implemented for Conservation Populations

Restoration, conservation, and management activities that have been implemented to conserve
designated conservation populations were evaluated for the 195 conservation populations (Table
14). Angling restrictions have been implemented on waters that affect nearly half of the
designated conservation populations. Angling restrictions often consisted of "catch and release"
fishing for YCT, but other restrictions such as bag and size limits and gear restricdons were also
included. Restoration and enhancement activities, such as physical removal of competing and'or
hybridizing species, populafion restoration and expansion, riparian fencing, pool development,
diversion modification, riparian restoration and stream bank stabilization, have occurred for 5 to
10% of the conser\'ation populations, respectively. In addition, a substantial number of
conservation populations reside within the boundaries of lands with special management (e.g.
road less, wilderness, and national parks, etc.).

Page - 29

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YCT Multi-state Assessment

February 10,2003

1

Isolation

Demographics

1

Population size

Temporal Variability

Genetics

,"■ '':''' ' ' \ ';■ 'i/i'"' '■

Isolets by

% of total

length

occupied (mi.)

--- 1

1

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by % of

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■ Med Low

D Med High;

DHigh

20% 40% 60% 80% 100%

Figure 8. Proportions of miles occupied by designated "isolet" (top) and metapopulation

(bottom) Yellowstone cutthroat trout conservation populations ranked into low to high
levels of risk by risk factor (vertical axes).

Page - 3 1

YCT Multi-state Assessment

February 10,2003

Isolation

Demographics

Population size

Temporal Variability

Genetics

Isolets by

% of Total

Number

DLow
■ Med Low
DMed High
DHigh

0% 20% 40% 60% 80% 100%

Isolation

Demographics

Population size

[Temporal Variability

Genetics

Metapops by

% of Total

Number

DLow
H Med Low
DMed High
DHigh

0%

20% 40% 60% 80% 100%

Figure 9. Proportions for numbers of designated "isolet" (top) and metapopulation (bottom)

Yellowstone cutthroat trout conservation populations ranked into low to high levels of
risk by risk factor (vertical axes).

Page - 32

YCT Multi-state Assessment

February 10.2003

Composite Risk Scores

45

"^^ D Metapopulations
35 , Blsolets

4 5 6 7 8 9 10 11 12 13 14 15 16

Risk

Figure 10. Distribution of the number of designated Yellowstone cutthroat trout populations by
composite population risk scores and population type (excludes genetics and disease
risks).

Page - 33

YCT Multi-state Assessment

February 10,2003

Table 14. Number and percentage (based on the 195 conservation populations that were
evaluated) of Yellowstone cutthroat trout conservation populations that have had
various types of conservation, restoration, and management actions implemented to
conserve them as of 2001 .

[Type of restoration or management activity

Number of populations

[Water lease/Instream enhancement

4

2.1%

Channel restoration

9

4.6%

Bank stabilization

17

8.7%

Riparian restoration

18

9.2%

Diversion modification

9

4.6%

(Barrier removal

3

1.5%

Barrier construction

5

2.6%

iCulvert replacement

7

3.6%

IFish screens

2

1.0%

Fish ladders

3

1.5%

Spawning habitat enhancertfent

3

1.5%

iWoody debris

9

4.6%
5.1%

jPool development

10

Irrigation efficiency

9

1.7%

Grade control

1

2.0%

Instream cover habitat

6

3.1%

Riparian Fencing

20

10.3%

Physical removal of competing/hybridizing species

10

5.1%

Chemical removal of competing/hybridizing species

3

1.5%

Public outreach (Interpretive site)

8

4.1%

Population restoration/expansion

13

6.7%

Angling regulations

70

40.5%

Other

12

6.2%

Page - 34

YCT Multi-state Assessment

February 10,2003

Land Use Impacts on Conservation Populations

The approach taken to address the influences of land uses on YCT was too qualitative to
definitively link land use impacts to specific conservation populafions. Information was
collected for each occupied stream segment and there was a considerable amount of uncertainty
associated with the influence determinations that were made. Survey groups responded to land
use impact questions in different ways; some included past land uses to those currently
occurring. Others only identified current land uses. It was difficult to determine if the response
was related to the whole stream segment or only a portion of a segment. Because of the stated
uncertainties it is suggested that fiiture work to quantify the nature of land use impacts to YCT
conservation populations be undertaken. Even with these uncertainties, the information does
serve to heighten the awareness of the possible influences of land uses on YCT. Livestock
grazing was ranked as having the greatest influence on YCT conservation populations. This was
followed by roads, angling, timber harvest, stream de-watering and non-angling recreation as
major land uses (Table 15). We encourage caution when reviewing this information. At best
it provides a very qualitative picture of the nature of land uses on YCT conservation
populations.

Table 15. Number and percentage (based on the 195 conservation populations that were

evaluated) of designated Yellowstone cutthroat trout conservation populations where
human management activities were known or believed (possible) to have impacted the
population by type of management activity.

Known Impacts

Possible Impacts

Typeof acfivity

Number

Number

Tiniber harvest

31

(15.9%)

35

(17.9%)

tRange (livestock grazing)

45

(23.1%)

97

(49.7%)

Mining

17

(8.7%)

8

(4.1%)

Recreation (non-angling)

34

(17.4%)

42

(21.5%)

lAngling

54

(27.7%)

22

(11.3%)

iRoads

33

(16.9%)

66

(33.8%)

Dewatering

21

(10.8%)

40

(20.5%)

pther

13

(6.7%)

20

(10.3%)

Fine-Spotted and Large Spotted Forms

There are two spotting patterns displayed by YCT within their current range. This assessment
made an attempt to partition the infonnation by asking the assessment teams to identify which
form was present in each stream segment. Additionally, in instances where both forms were
present within a stream segment most reviewers made comments on which form was dominant.

Page - 35

YCT Multi-state Assessment February 1 0, 2003

Of the 195 conservation populations, 138 (71%) were comprised of only the large-spotted form,
39 (20%) were comprised of only the fine-spotted form and 18 (9%) represented a mixture of
both spotting patterns (Figure 1 1; Table 16). Large-spotted YCT conservation populations were
identified as being broadly distributed throughout the range. Large-spotted YCT existing
without the presence of the fine-spotted form occurred in 3,888 miles of stream (61.3% of habitat
occupied by conservation populations). The fine-spotted form exisfing without the presence of
the large-spotted form occurred in 217 miles of stream (3.4%). Conservafion populations having
representatives of both spotting patterns occurred in 2,241 miles of stream (35.3%).
Conservafion populations with only fine-spotted YCT were primarily located within headwaters
of the Snake River. A few fine-spotted YCT conservation populations were identified outside of
the Snake River basin (Figure 11). It should be noted that the fine-spotted form had been widely
used within the recreational fishery management program for Wyoming and because of this they
have been introduced into many watersheds outside the initial area they occupied

Of the 138 large-spotted YCT conservation populations, 38 had sufficient genetic testing to
determine that they were unaltered and could be considered as "core" populations. Another 8
conservation populations were comprised of stream segments containing both tested pure and
segments viewed a potentially unaltered. Forty (40) conservation populations were treated as
potentially unaltered and 25 were suspected of being genetically altered. Another 27 populations
were either tested and found to be genetically altered or they existed as a mixture of altered and
unaltered YCT. Seventy two percent of the large-spotted YCT populations were isolates and
28% were meta-populations.

For the conservafion populations (39) having only the fine-spotted form, most (36) were
identified as being potentially unaltered and three were suspected of being altered. Thirty four of
these fine-spotted YCT conservation populations were isolates and five were meta-populations.
A total of 1 8 conservation populations had both fine and large-spotted YCT present. These
conservation populations were nearly equally split between isolates (56%) and meta-populations
(44%). There was only one "core" conservation population identified in this mixed stock group.
As more genetic testing is completed we anficipate that many of the populations having
potentially unaltered stream segments will be found to be unaltered. Genetic alteration
(introgression) alluded to in this assessment is between YCT, and rainbow trout or other formally
recognized cutthroat subspecies (AFS 1991) with no differenfiation between the spotting
patterns.

Page - 36

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We separated the rated risks to the conservation populations based on spotting pattern by miles
of habitat occupied and by number of populations (Table 1 7). The distinct spotting patterns were
separated in the analyses. In general, spotting pattern did not appear to be related to genetic risks
to the populations. The difference associated with the low genetic risk for the fine spotted
populations was likely a function of the limited genetic sampling completed to date. Few clear
risk differences emerged during the analysis. We believe the risks assessed for YCT in general
also apply equally to the differing spotting patterns. Further comments or discussion of the two
spotting patterns of YCT will not be carried forward in the discussion and conclusions section.

Discussion and Conclusions

Historical Range

The exact evolutionary (phylogenetic) origins and zoogeographical processes taken during the
speciation process for the various cutthroat trout subspecies may not be known for quite some
time, if ever. Numerous theories and much speculation have been tendered (Behnke 1992, Smith
et al. 2002). More recent advances in genetic testing methodologies have offered new insight
into the pre-historical cutthroat trout story. This status update did not attempt to address the pre-
historical picture. Rather we intended to focus on a more recent historical point of reference as a
way of tracking changes that could be validated through written accounts and personal
observations.

Historical habitats of YCT delineated by this assessment differ from previous assessments
(Henzel 1959; Behnke 1979; Hadley 1984; Behnke 1988; Varley and Gresswell 1988; Thurow et
al. 1988; Behnke 1992; Gresswell 1995) for a number of reasons. A notable difference is the
reference period of historical occupancy. Behnke (1979; 1992) indicated that the western extent
of YCT range likely extended to portions of the Snake River, near the Idaho-Washington border.
The type locality for the name bouvieri was Waha Lake in western Idaho. Behnke (1979 and
1992) states that S.c. bouvieri were the original native trout of the entire Snake River some time
prior to the last glacial period (8,000 to 12,000 year ago) and replaced by redband and westslope
cutthroat trout below Shoshone Falls after that time period. Behnke (1979; 1992) notes that all
tributaries between Palisades Reservior and Shoshone Falls have S.c. bouvieri as the native trout.
Expansion into the Yellowstone River basin is felt to be via a connection between Pacific Creek
in the Snake River basin and Atlantic Creek which is a Yellowstone River tributary (Behnke
1992). Behnke (1979 and 1992) discussed eastern expansion within the Yellowstone River basin
and concluded that YCT occupied the mainstem Yellowstone River and tributaries as far as the
Tongue River. This eastern expansion would have occurred during the last 8,000 years. Many
status reports (Hadley 1984; Varley and Gresswell 1988; Gresswell 1995) cite Behnke (1979 and
1992) as the reference source for historical distribution of YCT there by anchoring to a time
period with a pre-historical perspective. A recent status review (May 1996) discussed the
historical range from a more immediate perspective using European exploration of the inland
portion of west (circa 1 800) as a historical benchmark. While it is reasonable to assume that the
pre-historical distribution of YCT likely expanded and contracted over time as environmental
and climatic conditions changed, written documentation that provides a more comparative
reference to current conditions began around 1 800. Kruse et al. (2000) completed a recent status

Page - 39

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YCT Multi-state Assessment February 10, 2003

assessment of YCT in specific drainages of the Bighorn River and primarily anchored to the
more recent time period (May 1996) as a historical reference period.

Another significant difference between this status assessment and many of the previous
assessments is associated with the base representation of occupied habitat across the potential
range. Behnke (1979, 1988 and 1992) used narratives and qualitative maps to describe the outer
most boundaries of YCT historical range. These publications made reference, from field notes
and observations, to specific streams but did not attempt to provide quantification of the amount
of historically occupied habitat. Hadley 1984 provided a very limited qualitafive reference to
historical occupancy by stating: "The Yellowstone cutthroat trout in Montana was at one time
abundant in most waters in the Yellowstone River basin from the Montana- Wyoming border to
the Tongue River system." Varley and Gresswell (1988) cited Behnke's publications relafive to
historic range and then provided further quantitative detail. They mention that original habitat
was comprised of 44,500 ha of lake habitat and 24,000 km (15,000 miles) of sfream
environment. Varley and Gresswell (1988) did not provide an explanafion on how they obtained
these historical estimates. Kruse (2000) in turn cited Varley and Gresswell (1988) when
commenting on the historical distribution. In the USDA Forest Service conservadon assessment
for the inland cutthroat frout subspecies (May 1996) an attempt was made to quanfify YCT
historical range based on mapped stream miles within the geographical area believed to have
been occupied in about 1800.

The generalized boundaries depicted in most assessments (e.g. Behnke 1979 and 1992)
encompassed many 4"' code HUC's that we excluded (e.g. lower Tongue River, lower Rosebud
within the Tongue River basin; Badwater, Muskrat, and Lower Bighorn in the Bighorn River
basin; and, several watersheds on the north side of the mainstem lower Yellowstone River) based
on a focused review by individuals knowledgeable about the specific geographical areas
reviewed. In addition, the lack of historical quantification and site specificity in most status
discussions can imply to many readers that all or most streams within the generalized boundaries
depicted were occupied by YCT.

Our estimates suggest approximately 17,400 miles , located within 39 4"^ code HUC's, were
occupied by YCT at the time of Lewis and Clark's "Corps of Discovery" expedition. This
amount of historically occupied habitat is in contrast to the nearly 32,200 miles of stream
contained in the 1 : 100,000 hydrography associated with these watersheds. Nearly 14,600 miles
of streams were excluded from being historically occupied due to passage barriers (e.g. physical,
temperature, etc.) and inadequate habitat (e.g. minimal flows, excessive gradients, intermittent or
ephemeral flows, etc.). Some stream reaches were excluded because of historical references and
other antidotal observafions indicating that the stream was barren offish (i.e. Jordan 1891).
Habitats were included on the basis of historical journal entries, scientific reports, anecdotal
information on presence, evidence of basin transfers and presence of frout when no barriers were
present.

May (1996) reported that YCT historically occupied just over 16,600 miles of riverine habitat.
Of that total, Wyoming had 10,949 miles (66%), Idaho had 3,587 miles (22%), Montana
contained just over 1,920 miles (12%) and 210 miles (1%) were attributed to occupied habitats in
Utali and Nevada combined. We estimated that about 1 7.400 miles of habitat were historically

Page - 41

YCT Multi-state Assessment February 10, 2003

occupied within the historical geographical boundary (Figure 1). Of our total, Wyoming
contained the most historical habitat (6,886 miles; 40%), Idaho was believed to have 6,267 miles
(36%), Montana contained just over 4,040 miles (23%) , Nevada and Utah had 97 and 103 miles,
respectively (0.5% each). While the total number of historically occupied miles between our
status update and the status review completed in the mid-1 990's were very similar there was a
marked difference in the mileages associated with Wyoming, Idaho and Montana. TTie
difference between our estimate and that developed in the previous assessment (May 1996) was
likely due to two significant factois. First, our assessment used a set 1 : 100,000 hydrography
base layer that was attributed and queried within an ARCView platform and a standardized
database. The status assessment of the mid-1990's relied on area maps having differing scales
and stream designations. Notations were made on each map and stream distances were
calculation using a mileage function on a planimeter. Secondly, the mileage estimate for
Wyoming in the earlier assessment was suspect due to the nature of Wyoming's stream database
at the time (May 1996).

Varley and Gresswell (1988) estimated the historically occupied habitat at 24,000 km (15,000
miles). Since Varley and Gresswell (1988) did not provide a rationale of how they derived the
number of occupied stream miles, it was difficult to compare with our estimate. Their estimate
of about 15,000 miles did not include mileages covered by large lakes, particularly Yellowstone
Lake, and thus their total is reasonably close to the historical occupancy estimates in our status
update and the status review completed by May ( 1 996).

Current Distribution

Based on our assessment, YCT currently occupy about 7,530 miles of habitat (43%) of
historically occupied habitat) within the historical range (Figure 2). YCT currently occupy 3,861
miles (51%)) in Wyoming, 2,174 miles (29%) in Idaho, 1,417 miles (19%) in Montana and
Nevada and Utah have 44 and 42 miles, respectively (0.5% each). In contrast, the assessment
reported in May 1996 reported that approximately 6,817 miles of currently occupied habitat. Of
that total 1,622 (including 3 1 miles in the Goose Creek and Raft River drainages) were in Idaho,
4,624 were in Wyoming and 625 were in Montana. The reason for the significantly large
difference in currently occupied habitat within Montana was because only those YCT that had
been genetically tested were counted in the earlier assessment (May 1996). In addition,
differences could be attributed to mapping and hydrography scales, differences in the individuals
participating the assessments and fact that more YCT had been documented in the six year
period between assessments. Varley and Gresswell ( 1 988) estimated that YCT in their pure form
occupied 38,500 ha of lake environment and 2,400 km (1,500 miles) of stream habitat. A reason
for this estimate being significantly lower could be linked to the notafion that only "pure" YCT
were considered. Varley and Gresswell (1988) did not provide a discussion of how purity was
determined to support their esdmate of current distribution.

Hanzel's (1959) work on YCT distribution in Montana was updated by Hadley (1984). Both of
these efforts relied on visual observation to identify YCT. As referenced in Hadley (1984),
Hanzel made YCT collections within the Yellowstone River basin in the section between
Yellowstone National Park and the mouth of the Bighorn River. These collections indicated that
YCT were present in the Yellowstone River from the park boundary downstream for a distance
of 145 km (90 miles). Menfion was also made that remnant YCT were confined to small

Page - 42

YCT Multi-state Assessment February 10, 2003

headwater streams. Hanzel's assessment was mostly qualitative and he made little effort to
quantify numbers of streams or miles occupied. Hadley (1984) completed an assessment of YCT
using Montana Fish, Wildlife and Parks' computerized database as an information source. Use
of the database allowed for a partitioning of YCT information into categories that were used to
gain a better understanding of YCT populations in Montana. Hadley (1984) reported that YCT
were believe to exist in 324 km (203 miles) of stream based on information contained in the
database at that time. Hadley also stated that the database was likely incomplete because at the
time it didn't contain information from Federal agencies nor have all the information from
department personnel. The significant difference in miles of occupied stream habitat between
the assessment (203 miles) completed by Hadley (1984) and our assessment (1,417 miles) is
likely do to insufficient data being available within the State's database at the time Hadley
completed her review. During the last 20 years there has been a substantial investment of time
and energy to prove better information of YCT distributions within Montana. As a result, many
more stream reaches have been inventoried and tested genetically, fri addition, the statewide
database has been updated on a regular basis of at least by-annually and included data from all
sources.

Kruse et al. (2000) reported on the status of YCT within the Greybull and Shoshone River basin
of northwestern Wyoming. Their assessment was very detailed and provided information on
YCT distribution from 182 streams (1,705 km; 1,066 miles) within the two river basins. As part
of the Wyoming workshop for our assessment, the information collected by Kruse (2000) was
entered into the database which greatly strengthened the information on current YCT
distributions in Wyoming. In similar fashion, the work of Mark Novak, USDA Forest Service
and Wyoming Department of Game and Fish in the upper Snake River basin was included within
our assessment.

Thurow et al. (1988) provided an assessment of YCT status and ecology within the Idaho portion
of the native range. Their work concentrated on many of the major tributary drainages to the
Snake River in Idaho (i.e. Blackfoot River, South Fork of the Snake River, Teton River and
Willow Creek). Specific quanfification of the amount of stream habitat occupied by YCT was
not pro\'ided but there were statements indicating the YCT were present in most streams and
stream reaches within these tributaries but there was a significant effort to quantify population
levels for streams occupied by YCT. Meyer et al.(2003) completed a very important follow up
assessment of many streams sampled in the 1980's by Thurow et al. (1988) and others. This
later sampling repeated population quantification at 77 pair sites following the same sampling
protocol to the extent possible. Meyer et al. (2003) found that population abundance had
remained relatively stable, at most paired sites, over the last 10-20 years. Only five of the sites
sampled in the 1980's did not contain YCT (Meyer et al.(2003). The sampling design of this
recent study made it impossible to provide definitive conclusions regarding YCT distribution and
population abundance outside of the study sites.

Designated Conservation Populations

There were two types of conservation strategies represented by the YCT "conservation
populations" (Appendix F). One strategy was linked to conserving genetic integrity and
reducing the influence of competitive species by isolating YCT populations (Kruse et al. (2001 ).
The other strategy emphasized maintenance of connectivity among YCT populations by

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YCT Multi-state Assessment February 10, 2003

protecting relatively large areas of continuous habitat that allow YCT to express all life-history
traits, especially migratory life histories. As shown, the type of risks inherent in the two
different conservation strategies are dramatically different.

For those YCT conservation populations where genetic integrity and isolation from competing
species is emphasized, risks due to isolation, small population size, and temporal variability are
high, while other types of risk are relatively low. The assumption made in rating these
population risks as high was that YCT populations benefit from occupancy in relatively large
habitats that allow for connection among subpopulations. Some authors have indicated that
cutthroat trout populations need to be supported by an effective population of 500 reproducing
adults based on the 50/500 "rule" (Franklin 1980; Soule 1980), thus they believed that most
isolated small populations of cutthroat trout were at an extremely high risk of extinction (Kruse
et al. 2001 ; Hilderbrand and Kershner 2000). Harig and Fausch (2001 ) found that cutthroat trout
translocations were most successftil when the drainage area was at least 5.6 mi.' (14.7 km'),
which likely translates to inhabited stream lengths of at least 2 to 3 miles. Hilderbrand and
Kershner (2000) estimated that cutthroat trout needed at least 5.7 miles (9.3 km) of habitat at
moderately high densities to persist under the 500 "rule". Rieman and Dunham (2000) provided
data that indicated small, isolated populations of WCT might not be as prone to extinction as
other vertebrates, and even other salmonids, based on their evaluation of the persistence of
isolated headwater populations of WCT in the Coeur d'Alene basin of Idaho. Of the 195 YCT
conservation populations we evaluated (Appendix F), 143 were considered as "isolates" with
majority having either moderately high or low composite risk scores ( weighted toward the
moderately high score). Risk factors of concern for most of the "isolates" were occupancy of
relatively small stream lengths (<10 km), smaller effective population sizes (fewer spawning
adults), and the potential detrimental influence of being isolated. None of the "isolate"
populations had a low composite risk score. Fifty-two (52) of the 195 designated conservation
populations were viewed as meta-populations consisting of several sub-populations having the
opportunity to interact. Most meta-population composite risk scores were at the low end of the
moderate score. The risk factor of most concern for the meta-populations was loss of genetic
identity. There were 1 1 meta-populations that had low composite risk scores. There were a
significantly higher number of "core" conservation populations that were identified as "isolates"
(95%). It is anticipated that the number of "core" conservafion populafions will increase
substantially as more genetic testing is accomplished. There could be as many as 74 additional
core conservation populations dependant upon the results of the genetic testing yet to be
preformed.

Since genetic introgression and nonnative competition threats probably outweigh stochastic risks
over the short-term for many extant YCT populations, isolating remaining non-introgressed YCT
populations may be a prudent, short-term conservation strategy. Replicating and re-founding
existing isolated, non-introgressed YCT populations that may be lost due to stochastic or
demographic pressures, and using humans as the dispersal agent via conservation stocking to re-
found YCT populations that are lost from isolated habitats due to stochastic processes have been
recognized as viable conservation strategies (e.g. Montana Fish, Wildlife and Parks 1999;
Shepard et al. in press).

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YCT Multi-state Assessment Februar>' 1 0, 2003

Land-use implications and application of actions focused on improving the conservation
potential of the conservation populations is viewed was important but due to limited information
and lack of consistency in the information currently available, the significance of these factors
was not validated effectively in our assessment. We did make an effort to acknowledge which
land uses were felt to be influencing the populations and to identify the various conservation
actions that had been applied to the conservation populations.

Conclusions

This assessment clearly shows that YCT currently occupy significant portions of, and are well
distributed across, their historical range. YCT currently occupy a higher proportion of their
historical habitats near the core of their historical range, with sparser occupancy near range
fringe areas, particularly in the Snake River system of Idaho below the Portneuf River and in the
middle Yellowstone River and lower Bighorn River systems. Several studies, both theoretical
and empirical, have suggested a decline in the proportion of sites occupied and in population
densities from the center to the fiinge of a species range for many vertebrate species (e.g. Brown
1984; Caughley et al. 1988; Lawton 1993). Meyer et al. (2003) observed that most YCT
populations in southeastern Idaho had neither declined in abundance nor distribution over the last
two decades.

The precise genetic status of most YCT populations is uncertain because genetic testing has not
been completed for a substantial number of populations. Genetic testing is expensive and time-
consuming. Efforts to gain more genetic information will continue consistent with fiinding and
available workforce. Also, even for some populations where genetic testing has been completed,
sample sizes are so small that the absence of introgression cannot be statistically inferred with
any degree of confidence. Existing genetic infonnation suggests that YCT with no evidence of
introgression currently occupy 17% of the habitats where YCT are currently found (7% of
historical). While it is probable that fijture evidence of introgression will be found in some of the
populations that currently have shown no evidence of introgression, it is also likely that more of
the currently untested populations of YCT will be found to have no evidence of introgression,
once they are genetically tested.

In addition, we know that the data were biased because stream segments were assigned as
introgressed when we could not determine fi-om the database whether a particular sample was
from a population where random or non-random mating occurred. Thus, unless a biologist or
geneticist knew that non-random mating occurred, we assumed random mating had occurred for
all genetic samples where introgression was detected and the level of introgression was
computed based on that assumption.

We are reasonably sure that a minimum of 17% of the currently occupied habitats (7% of
historical range) should be considered as supporting genetically unaltered YCT. This contention
is supported both by the trends observed between assessments done over time, indicating that as
more testing was conducted, more streams were found that support unaltered YCT; and by the
information cited in this assessment indicating that in Idalio basins where limited genetic testing
had been done, most testing found no evidence of introgression. If we assume that half of the
area that we classified as supporting "Potentially Unaltered" and 20% of the areas classified as
"Suspected Altered" YCT are, in fact, supporting unaltered YCT, then the total miles of likely

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YCT Multi-state Assessment February 10, 2003

unaltered YCT increases to over 2,234 miles (30% of currently occupied habitats and 13% of
historical range). We suspect that from 17 to 30% of habitats currently occupied by YCT have
not experienced genetic introgression. All of the agencies and tribes responsible for managing
YCT throughout their range recognize the importance of conserving populations that have no
detectable introgression, illustrated by the inclusion of almost all genetically tested and unaltered
YCT populations within designated conservation populations.

A component of the current YCT conservation effort that was not specifically addressed in this
status update was associated with the coordinated conservation effort that has been initiated. In
2000, the five states (Montana, Idaho, Wyoming, Nevada and Utah with YCT along with the
USDA Forest Service, Yellowstone National Park and Grand Teton National Park entered into a
MOU for the conservation and management of YCT. Parties to the MOU identified a common
conservation goal and seven objectives that would collectively and individually guide future
conservation efforts. The goal included the intent (paraphrased as) to ensure the persistence of
YCT within the historic range and to preserve genetic integrity and provide adequate numbers
and populations to provide for the protection and maintenance of intrinsic and recreational values
of YCT. The objectives included: efforts to identify all existing populations; securing and
enhancing conservation populations; restoration of populations; public outreach; data sharing;
improved coordination; and, a stated intent of implement actions and activities necessary to meet
the stated goal and objectives. At present Montana has developed a state level conservation plan
that is consistent with the MOU. Wyoming likewise has a state level plan in place. Idaho is in
the process of finalizing a similar plan and Idaho, Utah and Nevada provide for YCT
conservation as part of the resident trout management plans that are in place. The Forest Service
and other Federal governmental agencies are implementing conservation actions on an annual
basis. Tribes with management responsibility for YCT are implementing their own management
and conservation actions. Completion of this status update was viewed as a priority coordination
action necessary to provide both a qualitafive and quantitative basis for future conservation
action. Through the coordinated conservation effort state. Federal and tribal managers will
employ recreational fishery management sufficient to regulate sport fisheries on YCT
populafions to ensure that both harvest and incidental hooking mortality do not cause these
populations to decline in a deterministic fashion. Angler-caused mortality should be low enough
to ensure that each YCT population has adequate resiliency to recover rapidly from stochastic
environmental events that could severely reduce that population. Agency fish managers should
confinue their efforts to reduce the potenfial for genefic introgression resulting from fish stocking
practices, and aggressively manage to reduce threats from nonnative species that may hybridize
or compete with YCT. Land management agencies need to conserve aquatic habitats at a habitat
quality level that ensures that remaining YCT populations persist and, preferably, flourish. In
particular, we recommend that existing road-less areas, parks, and wilderness areas continue to
be managed so that aquatic habitats are maintained at or near their potenfial in these areas. Since
so much of the remaining habitat occupied by YCT is located within federally managed lands,
good stewardship of these lands is critical for maintaining YCT.

This assessment will serve as a baseline for measuring fumre conservation progress. In addition,
this informadon will be used for prioritizing YCT conservation efforts and assist in conservation
planning by the states, tribes, and others with fish management responsibility. Updating this
database with data from a well-designed field-monitoring program could serve as a barometer to
monitor the status of YCT over time.

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YCT Multi-state Assessment February 1 0, 2003

Acknowledgements

We would like to thank all the fisheries biologists and data entry and geographical information
technicians who provided information, entered data, and assisted with GIS applications. Their
names can be found in Appendix B. Steve Carson of Montana, Fish, Wildlife and Parks
provided support and applications for the GIS program Arcview. We would like to thank the
Fisheries Administrators and staffs of the: states of Idaho, Montana, Wyoming, Nevada and
Utah; USDA Forest Service, The National Park Service, particularly Grand Teton and
Yellowstone National Parks; the Crow tribe, the tribes of the Wind River Reservation;; U.S. Fish
and Wildlife Service; and U. S. Bureau of Land Management for their participation and support.
Montana Fish, Wildlife and Parks and U.S.D.A. Forest Service supported the main authors'
efforts to collect and summarize status information and prepare this report. Members of the YCT
interagency conservation team reviewed earlier drafts of this report and provided helpful
suggestions.

References

Allendorf, F. W., R. F. Leary, P. Spruell, and J. K. Wenburg. 2001. The problems with hybrids:
setting conservation guidelines. Trends in Ecology and Evolution 16:613-622.

American Fishery Society. 1991. Common and scientific names of fishes in the United States and
Canada. Special Publication 20. 5^ Edition. Bethesda, Maryland. 1 83 pp.

Anon. 2000. Cutthroat trout management: a position paper, genetic considerations associated
with cutthroat trout management. Publication Number 00-26. Utah Division of Wildlife
Resources, Salt Lake City, Utah.

Behnke, R. J. 1979. Monograph of the native trouts of the genus Salmo of western North

America. Final report under contract to BLM, FWS, and USDA Forest Service, Region
2, Lakewood, Colorado.

Behnke, R. J. 1988. Phylogeny and classification of cutthroat trout. In: Status and Management
of Interior Stocks of Cutthroat Trout. American Fisheries Society Symposium 4:1-7.

Behnke, R. J. 1992. Native trout of Western North America. American Fisheries Society,
Monograph 6, Bethesda, Maryland.

Behnke, R. J. 2002. Trout and salmon of North America. The Free Press. 359 pp.

Brown, J. H. 1 984. On the relationship between abundance and distribution of species.
American Naturalist 124:255-279.

Caughley, G., D. Grice, R. Barker, and B. Brown. 1988. The edge of the range. Journal of
Animal Ecology 57:771-785.

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YCT Multi-state Assessment February 10, 2003

Firman, J. C, and S. E. Jacobs. 2001 . Comparison of stream reach lengths measured in the field
and from maps. North American Journal of Fisheries Management 22:1325-1328.

Franklin, I. A. 1980. Evolutionary changes in small populations. Pages 135-150 in M. Soule,

and B. A. Wilcox, editors. Conservation biology: an evolutionary-ecological perspective.
Sinauer Associates, Sunderland, Massachusetts.

Gresswell, R. E. 1995. Yellowstone cutthroat trout. In: Conservation Assessment for Inland

Cutthroat Trout. M.K. Young Technical Editor. USDA Forest Service RM-GTR-256. p.
36-54.

Hadley, K. 1 984. Status report on the Yellowstone cutthroat trout (Salmo clarki bouveri) in
Montana. Montana Department of Fish, Wildlife and Parks Report. 74 pp.

Hanksi, I., and M. Gilpin. 1991. Metapopulation dynamics: brief history and conceptual
domain. Biological Journal of the Linnean Society 42:3-16.

Hanzel, D. A. 1959. The distribution of the cutthroat trout [Salmo clarki) in Montana.
Proceedings of the Montana Academy of Sciences 19:32-71.

Harig, A. L., and K. D. Fausch. 2001. Minimum habitat requirements for establishing
translocated cutthroat trout populations. Ecological Applications 12:535-551.

Hilderbrand, R. H., and J. L. Kershner. 2000. Conserving inland cutthroat trout in small

streams: how much stream is enough? North American Journal of Fisheries Management
20:513-520.

Jordan, D. S. 1891. A reconnaissance of the streams and lakes in the Yellowstone National Park,
Wyoming, in the interest of the United States Fish Commission. Bulletin U. S. Fish
Commission. Vol. 41-63.

Kruse, C. G.„ W. A. Hubert, and F. J. Rahel. 2000. Status of Yellowstone cutthroat trout in
Wyoming waters. North American Journal of Fisheries Management 20:693-705.

Kruse, C. G., W. A. Hubert, and F. J. Rahel. 2001. An assessment of headwater isolation as a
conservation strategy for cutthroat trout in the Absaroka Mountains of Wyoming.
Northwest Science 75:1-11.

Lawton, J. H. 1993. Range, population abundance and conservation. Trends in Ecology and
Evolution 8:409-413.

Leary, R. F., W. R. Gould, and G. K.. Sage. 1996. Success of basibranchial tgeeth in indicating
pure populations of rainbow trout and failure to indicate pure populations of westslope
cutthroat trout. North American Journal of Fisheries Management 16: 210-213.

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YCT Multi-State Assessment February 1 0, 2003

May, B. E. 1996. Yellowstone cutthroat trout {Oncorhynchus clarki bouvieri). In: Conservation
Assessment for Inland Cutthroat Trout. D. D. Duff Technical Editor. USDA Forest
Service, Intermountain Region Report, pp. 11-34.

Montana Fish, Wildlife and Parks. 2000. Cooperative conservation agreement for Yellowstone
cutthroat trout within Montana. MFWP. Helena, Montana. 57 pp.

Meyer, K.A., D. J. Schill, F. S. Elle, and W. C. Schrader. 2003. A long-term comparison of
Yellowstone cutthroat trout abundance and size structure in their hishorical range in
Idaho. North American Journal of Fisheries Management 23 : 1 49- 1 62.

Rieman, B.E., and J. B. Dunham. 2000. Metapopulation and salmonids: a synthesis of life
history patterns and empirical observations. Ecology of Freshwater Fish 9:51-64.

Rieman, B., D. Lee, J. Mclntyre, K. Overton, and R. Thurow. 1993. Consideration of extinction
risks for salmonids. FHR Currents. Fish Habitat Relationships, Technical Bulletin 14
December. USDA Forest Service, Boise, Idaho.

Shepard, B.B., B.E. May, and W. Urie. 2003. Status of westslope cutthroat trout {Oncorhynchus
clarki lewisi) in the United States. Printed Agency Report. 94 pp.

Smith, G. R., T. E. Dowling, D. W. Gobalet, T. Lugaski, D. K. Shiozawa, and R. P. Evans. 2002.
Biogeography and timing of evolutionary events among Great Basin fishes. In: Great
Basin Aquatic History. Editors: Robert Hershler, David B. Madsen and Donald R.
Currey. Smithsonian Contributions to the Earth Sciences. 33:175-234.

Soule, M. E. 1980. TTiresholds for survival: maintaining fitness and evolufionary potenfial.
Pages 151-169 in M. E. Soule, and B. A. Wilcox, editors. Conservation biology: an
evolutionary-ecological perspective. Sinauer, Sunderland, MA.

Thurow, R. F., C. E. Corsi and V. K. Moore. 1988. Status, ecology, and management of

Yellowstone cutthroat trout in the upper Snake River Drainage, Idaho. In: Status and
Management of Interior Stocks of Cutthroat trout. American Fisheries Society
Symposium 4:25-36.

Varley, J. D. and R. E. Gresswell. 1988. Ecology, status, and management of Yellowstone
cutthroat trout. In: Status and Management of Interior Stocks of Cutthroat Trout.
American Fisheries Society Symposium 4:13-24.

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YCT Multi-state Assessment

February 1 0, 2003

Appendix A. Assessment Protocol and Data Forms

Yellowstone Cutthroat Trout Range-wide Assessment

Historical Range, Current Status, and Risk

Protocols

August 6, 2001
An interstate and interagency group of fishery administrators, managers, and biologists
representing the states of Idaho, Montana, Wyoming, Nevada, and Utah, Yellowstone National
Park, U.S. Fish and Wildlife Service, and Forest Service met January 17-18, 2001 in Idaho Falls,
Idaho to initiate a range-wide assessment for Yellowstone cutthroat trout (YCT; Oncorhynchus
clarki bouveri). It was agreed at that meeting to conduct a range-wide assessment for YCT that
included: 1) estimating range that was historically occupied; 2) determining current distributional
and genetic status; and 3) assessing risk using a ranking system approach similar to that proposed
by Rieman et al. (1993). It was recognized that this assessment would be based primarily on
expert opinion and that, particularly when historically occupied range was assessed, the
assessment would be qualitative. However, where field data were available these data would be
used and referenced. An ad hoc committee was formed to develop a protocol for conducting this
assessment. That group was charged with developing a protocol that linked information
developed from this assessment with a geographic information system that would allow the
information to be displayed and queried. The protocol detailed below will be used to conduct
this assessment.

The first issue when conducting any large-scale assessment is determining the map scale that will
be used for the assessment. It was decided that 1 : 1 00,000 scale hydrography (stream layer)
would be used and that any information geo-referenced to this hydrography scale must meet the
needs of the states involved and be useful for federal agencies. The USGS 1 : 100,000 scale
hydrography that is routed using LLID identifiers and that can be transferred to NHD fonnat was
selected as the base hydrography layer. The hydrography layer will primarily include named
streams. The second issue involves data quality and reliability. This assessment will use two
protocols for determining data quality. First, a rating system will be used to indicate the data
quality (DQl; Table 1; tables provide codes and look-up descriptors that will be used in the
database). Second, an effort will be made to document source material for all information used
in this assessment (Table 2) and a text field will allow entering a citation which details where the
mformation can be found. Finally, several issues directly associated with the logistics of keeping
data entry consistent and dealing with a consistent GIS database emerged. The ad hoc committee
strongly recommends that only 1 : 100,000 stream hydrography layer be used to complete this
assessment (some possible data management issues are addressed in Appendix A).

Table 1 . Look-up table for data quality index (DQI) for information entered.

RatinglDl Rating

GeneticValue | UseValue = Data source

PopSurveyValue

1

Low - judgment only

1 -9 fish sample Judgment only

Low quality

2

Med - some
observations

10-24 fish
sample

Extrapolated from surveys

Medium quality

3

High - many
observations

25+ fish sample

Extensive samples or monitoring
sections

Good quality

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YCT Multi-state Assessment February 1 0, 2003

Table 2. Look-up table for type of source information used.

SourceCode Description

1 Judgment

2 Anecdotal Information

3 Letter

4 News Account

5 Data Files

6 Agency Report

7 Published Paper

8 Thesis or Dissertation

This protocol is segregated into three primary components for conducting this assessment. First,
the historical range that was occupied by YCT at the time of the first European exploration of the
Northern Rocky Mountains will be estimated. Second, the current distribution, abundance and
genetic status information for YCT will be displayed. Lastly conservation populations, either as
isolated and meta-populations (networked or connected populations - e.g. interbreeding
populations), will be identified and population viability risk and genetic risk assessments will be
made for each of these populations. Risk will be assessed at two levels: 1) risk of genetic
introgression, and 2) population level risk. Risk assessments represent relative determinations
indicating a higher or lower level of concern. The mapping and risk assessments will be
completed for all populations including those associated with lakes that are maintained by
natural reproduction. Populations supported or augmented by stocking will not be included.
Definitions of terms used for this protocol are provided in italics as they are first used.

Population mapping unit (segment) - each stream, or occupied segment of stream, will be
treated as a separate population (stock) mapping unit or segment and connectivity
between these segments will determine whether these segments function in terms of an
isolate population or as a "metapopulation ".

Conservation Populations - those cutthroat populations existing in a geneticallv unaltered
condition (core consen'ation population with genetic analysis indicating greater than 99%
purity^) and/or populations having unique ecological, genetic and behavioral attribute of
significance that maybe genetically introgressed (See Cutthroat Trout Management: A Position
Paper - Genetic Considerations Associated with Cutthroat Trout Management). Conservation
populations may exist as isolates or networks of subpopulations.

M eta-population- infers that interbreeding between subpopulations (population mapping

segments) can occur within a generation (3-5 years). Also referred to as a connected or
networked population.

Isolated Population - Some populations occupy isolated habitat fragments (isolates) and these
populations likely operate independently from connected groups of subpopulations.

Genetic Risk - risk of initial or on-going genetic introgression (hybridization).

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YCT Multi-state Assessment February 1 0, 2003

Population Risk - risk of deterministic or stochastic declines in a population that could lead to a
reduced probability of viability for that population. Linked to temporal, population
size, production considerations and degree of isolation.

Genetic and abundance information will be provided for each population mapping segment.
Genetic and population risk assessments will be done for each conservation population.

Historical Range

Tlie historically occupied range of YCT will be assessed based on their believed distribution at
the time Europeans first entered the Rocky Mountain West. This assessment was done at a
relatively coarse level (Fourth-code level Hydrologic Unit Code; HUC) and assumed the entire
hydrography within 4' code HUC was either occupied or unoccupied. While these distributions
will be used as the starting point for assessing historical range, the historical range within each
HUC will be refined. Fishery professionals familiar with each major drainage basin (Fourth-
code HUC) will define historical range for stream mapping segments within each 4'*^ code HUC
by comparing the historical range with their personal knowledge of the area, known anecdotal
information, known habitat restrictions, known geologic barriers, and historical fisheries data and
reports to edit TNC YCT historical range maps at the 1 : 1 00,000 scale. YCT will be assumed to
have occupied all streams within their broad known historical distribufion unless information or
professional judgment indicates YCT likely did not occupy a mapping segment of stream based
on a documented rationale (Table 3). Data sources used to determine whether stream segments
were historically occupied, or not occupied, will be provided (Table 2), along with a reference
documenting why each stream segment was included or excluded, when applicable.

Table 3. Look-up table for reasons to exclude or include a stream segment as historical YCT
habitat.

Description

|Habitat limited - gradient, elevation, temperature
[Known geologic barrier
[Anecdotal information
[Historical scientific survey data

Judgment only

Since barriers to upstream fish movement (either long-term geologic, natural short-term, or
anthropogenic barriers) will be used to assess whether individual stream segments were likely
historically occupied by YCT, or for assessing risk of genefic introgression to exisfing YCT
populations, or whether existing YCT populations are connected with other populations; during
the effort to describe the historical distribution identity those barriers that represent long-term
geologic features that would serve to influence historical distributions. These barrier locations
will be located (as points in ARCVIEW) on the population mapping segments. During current
population distribution mapping identify other significant barrier locafions (as points in
ARCVIEW), including barrier type (Table 4), blockage extent (Table 5), and barrier significance
(Table 6). Identify only those barriers that contribute to the maintenance of populafion isolation.

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YCT Multi-state Assessment

February 10,2003

Table 4. Look-up table for types of barriers to fish movement upstream.

Barrier Type

Water diversion

Fish culture facility/research facility
Temperature

Bedrock

Culvert

Debris

Insufficient flow
Manmade Dam

Pollution

Beaver dams

Unknown

|Velocity barrier

Waterfall

Table 5. Look-up table for extent of blockage caused by barriers.

Blockage Extent

Complete

Partial

Intermittent depending

on flow

Temporary (landslide or woody debris)

N/A

Table 6. Look-up table for barrier significance.

Barrier Significance

Prevents introgression

Prevents ingress of competing species
Migration barrier

[Temporary, but presently prevents introgression

[n/a

[unknown

Current Distribution and Genetic Status

Lower and upper bound of all stream segments presently occupied by naturally self-sustaining
populations of YCT will be located and data quality associated with the locations of these
boundaries of current distribution will be rated (DQI; Tables 1 and 2). Genetic infomiation and
status will be rated for each YCT mapping unit (Tables 7 and 8) along with their DQI. For Table
7, base the category determination on information from the largest sample and/or the most recent
sample. Naturally self-sustaining populations are the only ones that will be assessed in this status
review. Relative abundance for each YCT mapping segment will also be rated (Table 9).

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YCT Multi-state Assessment

February 10,2003

Table 7. Look-up table for genetic status of a population segment.

Genetic Status

Genetically unaltered (>99.0%) - tested via electrophoresis or DNA
Introgressed (hybridized) - tested and found to be 75% to 99% YCT
Introgressed (hybridized) - tested and found to be less than 75% YCT

Potentially unaltered with no record of stocking and contaminating species present

Suspected hybridized with records of contaminating species being stocked or occurring in
stream

Hybridized and Pure populations exist in stream (use only if reproductive isolation is
suspected

Table 8. Tables for genetic analyses. More than one entry can be made for a population
segment.

SAMPL]OJO|COLL_DATE| C0LL_ID J NO_FISH I ANAL_DATE |aNAL_TYPE| % YCT |

Genetic Analysis Type

Allozymes

PINES

|Microsatellites

[dna""

Table 9. Look-up table for relative population abundance.

Abundance

Unknown
Abundant
Common
Rare

For each mapping segment it is important to identify those conservation actions, past or on-
going, that have been intended to protect, conserve and enhance each specific population (Table
11). It is also important to identity those land-uses (Table 12) that are or maybe exerting
negative impacts to the respective mapping segments and the associated habitat. The
information on conservation actions and land-use influences will be important as genetic and
population risks are assessed.

Table 10. Look-up table for conservation/restoration activities.

Restoration Activity

Water lease/lnstream flow enhancement
Channel restoration
Bank stabilization

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YCT Multi-state Assessment

February 10, 2003

Restoration Activity

Riparian restoration

Diversion modification

Barrier removal

JBarrier construction
ICulvert replacement

Installation of fish screens to prevent loss

JFish ladders to provide access

[Spawning habitat enhancement
jWoody debris placement
fPool development

[increase irrigation efficiency

Grade control

Instream cover habitat

Re-founding pure population
Other

Riparian fencing

Physical removal of competing/hybridizing species

Chemical removal of competing/hybridizing species
Public outreach efforts at site (Interpretative site)
Population Restoration/Expansion
[Angling Regulations

Table 1 1 . Land-use and angling activities that might impact a population segment.

Known Impact

J Possible Impact

Activity

Check box

Check box

Timber Harvest

Check box

Check box

Range (Livestock grazing)

Check box

Check box

Mining

Check box

i Check box

Recreation (non-angling)

Check box

Check box

Angling

Check box

[check box

Roads

Check box

[Check box

De-watering

Check box

[Check box

Other

Change in Focus

At this point the assessment will change from the focus on population mapping units (segments)
to a level of assessment related to populations and the risks that influence the well-being of the
identified populations. At this point, a detennination will be made relative to which population
mapping units have a conservation objective and which will be assigned to a recreational fishery
objective. Those segments identified as having a recreational objective, only, will not be carried
forward in the genetic and population risk assessments. Population mapping units having a
conservation objective will be further sub-divided based on connectedness or isolation into meta-
populations or isolated populations (isolates). Both meta-populations and isolates can serve as

Page - 55

YCT Multi-state Assessment

February 10,2003

conservation populations. From this point, only conservation populations will be evaluated for
genetic and population risks.

Genetic Risk Assessment

A Genetic risk assessment will be made for each meta- or isolate population using a ranking of 1
to 4 to indicate low to progressively higher risk (Table 10). Take into consideration those
actions and activities (Tables 10 and 1 1 ) that may have an influence on genetic risk.

Table 12. Look-up table for genetic risk ranking.

Rank

Activity i

1

Hybridizing species cannot interact with existing YCT population. Barrier provides
complete blockage to upstream fish movement.

2

Hybridizing species are in same stream and/or drainage further than 10 km from YCT
population, but not in same stream segment as YCT, or within 10 km where existing
barriers exist, but maybe at risk of failure.

3

Hybridizing species are in same stream and/or drainage within 10 km of YCT
population and no barriers exist between hybridizing species and YCT population.
However, hybridizing species have not yet been found in same stream segment as YCT
population.

4

Hybridizing species are sympatric with YCT in same sfream segment.

Population Risk Assessment

Population risk assessments will be done for each meta- or isolate population using a ranking
that includes consideration of four factors. Risks will be ranked from low to high by using a 1 to
4 ranking system for four variables identified by Rieman et al. (1993) (Table 12). These four
main factors will be weighted to derive a final risk factor as follows: Temporal Variability = 0.7;
Population Size = 1 .2; Population Productivity (Growth/Survival) = 1 .6; and Isolation = 0.5.

Table 13. Ranks of various types of viability risk to populafions.

Variable

Descrlption [Rank

Criteria

Temporal
Variability -

Influence of

stochastic

catastrophic

events on a

whole

population

Stream length occupied will be used to index
temporal variability. However, if
environmental and hydrologic events are
unlikely to markedly influence the entire
population, then rank should be reduced by
one rank' . Factors that influence ability to
resist catastrophic events are groundwater
systems or systems with complex and high
quality habitats.

1

At least 75 km of connected
habitats

2

25 - 75 km of connected habitats

3

10 - 25 km of connected habitats

4

< 1 0 km of connected habitats

Population
Size-

Defined as the number of mature adults.

1

> 2,000

2

500 - 2,000

Page - 56

YCT Multi-state Assessment

February 10,2003

Variable

Description

Rank

Criteria

Size-
whole
population

50 - 500

<50

Population
Production
(Growth/
Survival)

Influence of

deterministic

demographic

factors on

whole

population

Factors that influence population production
include habitat quality, disease, competition,
and predation.

Isolation

How isolated or connected is the conservation
population from other conservation populations?

i

Population is increasing or
fluctuating around an
equilibrium that fills a habitat
that is near potential

Population has been reduced,
but is fluctuating around an
equilibrium value that
indicates the population is at a
level that is less than its
potential (i.e. habitat quality is
less than potential or another
factor is limiting the
population - competition
and/or disease)

Population has been reduced
and is declining (year-class
failures may be periodic; e.g.
competition reducing survival
and/or disease)

Population has been much
reduced and declining over
long-term or at a fast rate
(year-class failures common;
e.g. competition dramatically
reducing survival)

Migratory forms must be
present and migration
corridors must be open
(connected)

Migratory forms are present,
but connection with migratory
populations disrupted at a
frequency that allows only
occasional genetic exchange.

Questionable whether
migratory form exists within
connected habitat; howe\er.
possible infrequent stra>ing of
adults into area occupied by
population

Page - 57

YCT Multi-state Assessment

February 10,2003

Variable

Description

Rank

Criteria

4

population is isolated from
any other population segment,
usually due to a barrier, but
possibly due to lack of
movement.

" For example, if you have a 60 km length of connected habitat that is very complex and high
quality it would receive a rank of "1" (original rank of "2" due to length decreased to "1"
because of high quality habitat).

Two other variables that Rieman et al. (1993) suggested evaluating were population replication
and synchrony between populations. At this time we believe that these variables are somewhat
less important because the majority of YCT populations occupy dispersed habitats across the
range. It will likely be important to assess the variables in the future as conservation actions are
taken to restore populations. Subsequent assessment of these variable could best be ranked using
spatial queries within a GIS application after all other data is entered in a spatially explicit GIS
database.

The ad hoc committee also discussed whether it was important to acknowledge the source/sink
relationships that may exist between headwater YCT population and those YCT populations that
might exist lower in a drainage, especially where barriers to upstream movement might exist.
While headwater YCT populations that are isolated by impassible barriers to upstream fish
movement and thus could not be re-founded if they went extinct, these headwater populations
may be important sources for re-founding and augmenting lower populations. The ad hoc
committee felt it was important to capture in a database where these types of relationships
between populations occur. This will be handled by a simple identifier check indicating that a
given population operates as a source. Any downstream population would then automatically
become a "sink" recipient.

Page - 58

YCT Multi-state Assessment

February 10, 2003

I BARRIERS

Mark Geologic Barriers on Both Maps and Give Unique Number with a square around it.

Mark all other Barriers on Current Map and Give Unique Number with a square around it.

All known geologic barriers - waterfalls- use HIGH for DQ Rating and Judgment for Source

BarrlerTYpe

Water diversion

Fish culture

facility/research

facility

Temperature

Bedrock

Culvert

Debris

Insufficient flow
Manmade Dam

Pollution

Beaver dams

Unl<nown
Velocity barrier
Waterfall

Hue Number:

Barrier Number:

Barrier Type (Circle One)
One)

Blockage Extent (Circle

BlockageExtent

Complete

Partial

Intermittent depending on flow

Temporary (landslide; woody debris, etc.)
N/A

Barrier Significance (Circle One)

BarrSlgnlf

Prevents introgression

Prevents ingress of competing species

Migration barrier

Temporary, but presently prevents
introgression

N/A

Unknown

Data Quality Rating (Circle one)

DQ Rating

Low
only

Judgment

IVIed

-Medium

High

-High

Source (Circle One)

Source

Judgment

Anecdotal
Information

Letter

News Account

Data files

Agency Report

Published Paper

Thesis or
Dissertation

Other

Page - 59

YCT Multi-state Assessment

February 10,2003

II HISTORICAL DISTRIBUTION

All streams are assumed to be included by reason of "Judgment Only" to start.

Highlight all areas to exclude, label all highlighted streams with an E and a unique number

. Fill out form below.

Highlight all areas to include for reasons other than "Judgment Only", label all highlighted

streams with an I and a unique number. Fill out form below.

HUC Number:

Historic Distribution Mapping Circle Number:.
INCLUDE or EXCLUDE (Circle)

Reason (Circle)
(Circle one)

Data Quality (Circle one) Source

DQ Rating

Source

Reason to Include/Exclude

Low - Judgment
only

Judgement

Habitat limited - gradient, elevation, temperature

Anecdotal
Information

Known geologic barrier at lower boundary

f^ed -Medium

Anecdotal information

High -High

Letter

Historical scientific survey data

News Account

Judgement only

Data files

Agency Report

Published Paper

Thesis or
Dissertation

Other

HUC Number:

Historic Distribution Mapping Circle Number:.
INCLUDE or EXCLUDE (Circle)

Reason (Circle)
(Circle one)

Reason to Include/Exclude

|Habitat limited - gradient, elevation, temperature
|Known geologic barrier at lower boundary
Anecdotal information

|Histoncal scientific survey data
[judgement only

Data Quality (Circle one) Source

DQ Rating

Low - Judgment
only

Med -Medium
High -High

Source

Judgement

Anecdotal
Information

Letter

News Account

Data files

Agency Report

Published Paper

Thesis or
Dissertation

Other

Page - 60

YCT Multi-state Assessment

February 10,2003

III CURRENT DISTRIBUTION

Highlight all stream segments currently occupied by cutthroat trout. Give each population
mapping unit (segment) a unique number, circle the number and fill out form below. Also
complete genetic analysis information if samples are available.

HUC Number:

Population Mapping Unit (segment) Number:

Species: Large Spot YCT/ Fine Spot YCT (Circle one)
Competing Species Present: Y or N

Genetic Status (Circle one)

Genetic Status

|Genetically unaltered (>99.0%) - tested via electrophoresis or DNA
[introgressed (hybridized) - tested and found to be 75% to 99% YCT
[introgressed (hybridized) - tested and found to be less than 75% YCT

|Potentially unaltered with no record of stocking and contaminating species present

iPotentially hybridized with records of contaminating species being stocked or occurring in stream
[Hybridized and Pure populations exist In stream (use only if reproductive Isolation is suspected)

Genetic Analyses

Fill in form below for each sample associated with the above mapping unit:
Mark sample location on map and label with sample number.

SAMPLE_NO

COLLECTOR

COLL_DATE

NO.FISH

ANAL.DATE ANAL_TYPE

%YCT

1

1

i

GenAnalType

lAllozymes

IPINES _

[Microsatellltes

[dna

Page -61

YCT Multi-state Assessment

February 1 0, 2003

Abundance (Circle one)

Data Quality (Circle one)

Source (Circle one)

Abundance

Unknown
Abundant
Common
Rare

DQ Rating

Low - Judgment
only

Med -Medium
High -High'

Source

Judgement

Anecdotal
Information

LetteT

News Account
Data

lies

Agency Report
Published Paper
Thesis or
Dissertation

Restoration Activities (Circle all which apply and complete
quality and source using tables below)

Other

data

Restoration Activity

X

Water lease/lnstream enhancement

Channel restoration

Bank stabilization

Riparian restoration

Diversion modification

Barrier removal

Barrier construction

Culvert replacement

Fish screens

Fish ladders

Spawning habitat enhancement

Woody debris ■

Pool development

Irrigation efficiency '

Grade control

Instream cover habitat

Other 1

Riparian Fencing

Physical removal of competing/hybridizing species

Chemical removal of competing/hybridizing species

Public outreach (Interpretive site)

Population Restoration/Expansion

Angling Regulations

Page - 62

YCT Multi-state Assessment

February 10, 2003

Land-use activities: (Check all that apply and complete data quality rating and source
information using above tables)

Land Use Activity

Known Impact
X

Possible Impact
X

Timber Harvest

Range (livestock grazing)

Mining

Recreation (non-angling)

Angling

Roads 1

Dewatering

.

Other, specify using comments

Page - 63

YCT Multi-state Assessment

February 10,2003

IV CONSERVATION POPULATION RISK ASSESSMENT

For each mapping unit managed as a conservation population determine whether it is part of a

meta-population or an isolet. Draw circles around the meta-population or isolate. Give unique

numbers to each circle and draw a triangle around each number. Fill out form below.

HUC Number: Meta-population/isolet unique

number:

Meta-Population or Isolet (Circle one)

Downstream source Y or N (Circle one)

Genetic Risk Assessment: (Circle one taking into consideration those actions and activities
checked above that may influence genetic risk)

Genetic Risk

Hybridizing species CANNOT INTERACT with population. Barrier provides complete blockage to
upstream fish movement.

Hybridizing species are In same stream and/or drainage FURTHER THAN 10 KM from population, but not
in same stream segment as population, or WITHIN 10 KM WHERE BARRIER EXISTS, BUT MAY FAIL.

Hybridizing species are in same stream and/or drainage WITHIN 10 KM of population and NO BARRIER
EXISTS; however, hybridizing species not in same area as population.

Hybridizing species are SYMPATRIC with population In same stream segment.

Circle DQ Rating for Genetic Risk

Population Risk Assessment: (Circle response for each risk
give a data quality rating based on table below)

DQ Rating

Low - Judgment
only

Med -Medium
High-High

factor and

Variable

Description

Rank

Criteria

Data Quality

Temporal
Variability -

Influence of

stochastic

catastrophic

events on a

whole

population

Stream length occupied will be
used to index temporal
variability. However, if
environmental and hydrologic
events are unlikely to markedly ■
influence the entire population,
then rank should be reduced by
one rank . Factors that
influence ability to resist
catastrophic events are
groundwater systems or systems
with complex and high quality
habitats.

1

At least 75 km of connected
habitats

2

25 - 75 km of connected
habitats

3

10 - 25 km of connected
habitats

4

< 10 km of connected habitats

Page - 64

YCT Multi-state Assessment

February 10,2003

Variable

Description

JRank

Criteria | Data Quality

Population
Size-
whole
population

Defined as the number of
mature adults.

1

> 2,000

2

500-2,000

3

50 - 500

4

<50

Population
Production
(Growth/
Survival)

Influence of

deterministic

demographic

factors on

whole

population

Factors that influence
population production include
habitat quality, disease,
competition, and predation.

1

Population is increasing or
fluctuating around an
equilibrium that fills a
habitat that is near potential

2

Population has been
reduced, but is fluctuating
around an equilibrium
value that indicates the
population is at a level that
is less than its potential (i.e.
habitat quality is less than
potential or another factor
is limiting the population -
competition and/or disease)

3

Population has been
reduced and is declining
(year-class failures may be
periodic; e.g. competition
reducing survival and/or
disease)

4 '

Population has been much
reduced and declining over
long-term or at a fast rate
(year-class failures
common; e.g. competifion
dramafically reducing
survival)

Isolation

How isolated or connected is the |
conservation population from other!
conservation populatons?

1 1

Migratory forms must be
present and migration
corridors must be open
(connected)

2

Vligratory forms are
sresent, but connection
with migratory populations
disrupted at a frequency
that allows only occasional
spawning

Page - 65

YCT Multi-state Assessment

February 10,2003

Variable

Description

Ranli

Criteria

Data Quaiity

3

Questionable whether
migratory form exists
within connected habitat;
however, possible
infrequent straying of
adults into area occupied
by population

4

population is isolated from
any other population
segment, usually due to a
barrier, but possibly due to
lack of movement.

Circle donunant source of population risli data.

DQ Rating [

Low
only

■Judgment

Med

-Medium

High

-High

Source

Judgement

Anecdotal
Information

Letter

News Account

Data files

[Agency Report

Published Paper

JTfiesis or
[Dissertation

(other

Page - 66

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YCT Multi-state Assessment

February 1 0, 2003

Appendix C - GIS scale issues

Differences between 1 : 100,000 scale stream layer and
1 :24,000 scale stream layer stream lengths

Wendi Urie

Gallatin National Forest

Bozeman, Montana

December 2001

We conducted a comparison of stream lengths on the 1 : 100,000 scale LLID layer and the
1 :24,000 scale National Elevation Dataset available for portions of the study area. We selected
1 0 streams each from the Jefferson, South Fork Flathead and Lower North Fork Clearwater
watersheds for both scales. Lengths were compared using regression analysis. The 1 : 100,000
scale streams were found to be only 1% shorter than their equivalent 1 :24,000 scale
representation. Thus the streams included in the 1 : 1 00,000 scale LLID stream layer represent
approximately the same number of stream miles as the corresponding streams in the 1 :24,000
scale National Elevation Dataset.

Spatial Variability in Streams Represented in the LLID Streams Layer

The LLID stream layer contained some variability in the selection of streams represented across
the study area. The streams represented in Idaho and Montana (with a few exceptions in MT) are
only the named streams. All unnamed streams were not included in the LLID layer. In
Washington, Oregon and those watersheds spanning the boarder with Idaho unnamed streams
were included. Thus the density of stream miles in a watershed was much greater in these
watersheds. To compare two watersheds we looked at the Priest (on the border between ID and
WA) and the Upper Coeur d'Alene (ID). There are approximately 1.86 miles of stream per 1000
acres in the Priest watershed and 1 .20 miles of stream per 1000 acres in the Upper Coeur d'Alene
watershed. There is approximately 35% more stream miles represented in the Priest watershed
and thus 35% more potential habitat to include in historic or current range. Therefore the
watersheds with unnamed streams represented had the potential for approximately 35% more
historically and currently occupied range. The following tables list the miles of unnamed
streams in these watersheds that were included in the historically and currently occupied habitat.

NAME

Miles of Unnamed Stream
Included in Historic Range

Pend Oreille Lake

313.07

Priest

233.08

Pend Oreille

483.74

Coeur d'Alene Lake

236.64

Upper Spokane

110.15

Methow

231.93

Lake Chelan

209.50

Upper John Day

282.47

Page - 70

YCT Multi-state Assessment

NAME

Miles of Unnamed Stream
Included in Current Range

Pend Oreille Lake

334.32

Priest

211.58

Pend Oreille

447.79

Coeur d'Alene Lake

222.85

Upper Spokane

107.13

Hangman

1.77

Methow

20.64

Lake Chelan

6.61

Upper John Day

4.99

February 10, 2003

TTius the historically occupied range for these watersheds may be as much as 35% more than in
watersheds without mapped unnamed streams. In the Pend Oreille Lake, Priest, Pend Oreille,
Coeur d'Alene Lake and Upper Spokane watersheds many unnamed streams were considered
occupied where as in other watersheds unnamed streams may have been assumed to be habitat
limited.

Page -71

YCT Multi-state Assessment February 10, 2003

Appendix D. Genetic Considerations for Fish Managers

Factors that influence hybridization and introgression between introduced non-native trout

and indigenous westslope cutthroat trout: Genetic considerations and management

implications

Matthew Campbell

Fishery Geneticist, Idaho Department of Fish and Game

Introductions of non-native trout for fisheries management purposes have occurred throughout
the range of westslope cutthroat trout for more than 100 years. It has been well documented that
these introductions have often led to hybridization and introgression, a potentially serious, on-
going genetic hazard throughout much of the species present range (Weigel et al. 2002, Sage et
al. 1992, Leary et al. 1995). However, there is also research that has failed to show evidence of
hybridization and introgression within populations even though non-native trout have been
previously stocked (Williams et al. 1996, Mays 2001).

There are many factors that determine whether non-native trout (e.g. rainbow trout, Yellowstone
cutthroat, golden trout) introductions will result in hybridization (i.e., the interbreeding of
introduced non-native trout with indigenous westslope cutthroat trout) and introgression (i.e., the
incorporation of genes of non-native trout into the gene pool of a westslope cutthroat
population).

One or more of the following factors may influence levels of hybridization and introgression:

• The number of non-native trout stocked;

• The number of times stocked, time of year stocked, time since last stocking, age/size at
stocking, strain or subspecies stocked, survival of stocked fish, size of the indigenous
westslope cutthroat population, and fishing pressure on stocked streams;

• Presence/ Absence of isolating mechanisms (both pre-mating and post-mating
mechanisms). For instance, the presence or absence of isolating mechanisms may depend
on whether rainbow trout are stocked on westslope cutthroat populations that are
naturally sympatric with native populations of O. niykiss, or whether they are stocked on
westslope populations that have not previously lived in sympatry with O. mykiss);

• Dispersal patterns and reproductive success of introduced trout and hybrids;

• Ecological conditions can influence many aspects of stocked rainbow trout sur\'ival, the
presence/ absence of isolating mechanisms, fitness of hybrids, gene flow between
populations, as well as the geographical distribution of introduced non-native trout,
native trout, and hybrids within an area.

There are also numerous complicating factors that determine whether the percentage of non-
native alleles within a population, the number of hybrids in a population, or the number of
hybridized populafions will increase, decrease, or remain unchanged over fime. The fate of non-
native trout alleles introduced into a westslope cutthroat trout population depend on the extent to
which introduced trout and westslope cutthroat trout hybridize, the subsequent reproductive
fitness of hybrids and the extent to which the hybridizing populafions depart ft-om Hardy-
Weinberg expectations of an ideal populafion.

For example, if 20 rainbow trout (breeding adults) are introduced onto a cutthroat populafion (80
breeding adults, no other individuals), before any mating, the sample offish is composed of 20%
rainbow trout (RBT) alleles and 80% westslope cutthroat trout (WCT) alleles. If the introduced

Page - 72

YCT Multi-state Assessment February 10, 2003

RBT randomly mate with the WCT and the subsequent hybrids are as fit as the parents, then the
percentage of RBT alleles and WCT alleles will not change from generation to generation. What
will change, early on, is the number of hybrids in the population. Before any mating the number
of hybrid individuals is zero. As random mating progresses, the number of hybrids in the
population increases each generation until eventually all of the individuals are hybrids and the
RBT alleles are randomly distributed throughout the population (a hybrid swarm). The
percentage of RBT alleles does not increase, however (the potential effects of drift are ignored
for this example). Sample observations would indicate 20% RBT alleles and 80% WCT alleles,
which is the true fi"equencies for the population. If enough diagnostic genetic markers are
available to detect introgression in the individual (requiring ~15 loci, 30 alleles to detect 20%
RBT introgression) then a genetic screen will likely demonstrate that all individuals sampled are
hybrids to some degree and the level of introgression among the individuals will be consistent
with a binomial distribution of RBT alleles across the population. The more diagnostic loci
available, the greater power to detect introgression at low levels in the population and individual.

The increase or decrease of RBT introgression (the percentage of RBT alleles within a
population) depends on whether new RBT alleles are continually introduced into the population,
the relative fitness of hybrid genotypes, genetic drift, and the potential for the increased mating
among related individuals (phenotypic advantage). As new RBT alleles enter the population
(stocking) and if hybridization and introgression occurs, the percentage of RBT alleles in the
population will increase. If hybrid genotypes/RBT alleles are more fit than WCT
genotypes/alleles (outbreeding enhancement or heterosis), then the percentage of RBT alleles in
the population will increase even after stocking has stopped due to this selective advantage.
Alternatively, if hybrid genotypes/RBT alleles are less fit than WCT genotypes/alleles
(outbreeding depression or negative heterosis), then the percentage of RBT alleles in the
population will decrease after stocking has stopped, depending on the level in which they are
expressed and selected against within the populafion. Genetic drift (change in allele ft-equency
from generation to generation due to statistical chance) may also change the percentage of RBT
alleles within a population, especially if the populafion is small. However, genetic drift is non-
directional, providing equal opportunity for RBT or WCT allele frequencies to change
significantly. Rainbow trout alleles will also increase in the WCT population if rainbow trout or
hybrid phenotypes are preferred partners for mating (both equally or unequally among sexes).
The increase in mating success will result in an overall increase in RBT alleles in the population
and a departure from random mating evidenced by examining linkage and/or gametic
disequilibrium ainong individuals.

Whether the number of populations that are introgressed in an area increases, depends on a
number of factors including the stocking history (how long ago were non-native trout stocked,
whether non-native trout are stocked in places now that they were not in the past), whether the
stocking of non-nafives has resulted self-sustaining populations, the dispersal of stocked trout
and hybrids, and the amount of natural gene flow that occurs between WCT populations. If
stocking took place in areas that had not been stocked prior to the first study, then subsequent re-
sampling and genetic analysis may find an increase in the number of populations that show
introgressive hybridization. If RBT are introduced into an area with WCT and there is
subsequent introgressive hybridization, gene flow will move RBT alleles into surrounding
populations. In some areas, stocking has resulted in self-sustaining RBT populations (Hitt et al.
submitted). If these introduced populations increase in size and/or individuals disperse and
immigrate, both the percentage of RBT alleles within populations, as well as the number of
introgressed populations can increase, if those immigrants are reproductively successful.

Page - 73

YCT Multi-state Assessment February 10, 2003

It is important that managers continue to screen WCT populations for hybridization and
introgression and they also continue to investigate the ecological and genetic factors that
influence the consequences of non-native introductions. In some cases the outcome of stocking
non-native trout on indigenous WCT populations has been severe enough as to have led to the
formation of hybrid swarms (Hitt et al. submitted). However, it is likely that a number of factors,
including existing reproductive isolating mechanisms (e.g. those found in naturally sympatric
populations) or environmental conditions which select against non-native trout and hybrids, have
limited the incidence of hybridization and spread of introgression in a number of drainages, and
has thus preserved genetic integrity of the native parental populations. This is not to suggest that
the practice of stocking fertile, non-native trout on indigenous WCT populations should
continue. The States of Idaho, Montana, Oregon, and Washington have already adopted policies
focused either on the cessation of stocking non-native trout in WCT waters, or the use of sterile
triploid rainbow trout in hatchery supported fisheries which are adjacent or connected to waters
supporting westslope cutthroat trout.

It is also important that managers monitor and document possible changes in the level of
introgression within a population or changes in the number of populations in which hybridization
and introgression is observed. Populations in which introgression has increased over time should
not receive the same conservation status and should be managed differently than populations in
which introgression levels have remained stable or are decreasing. Documenting areas in which
population-level introgression is increasing or where the number of hybridized populations is
increasing is essential because it may highlight areas in which management actions should
change {e.g. stopping further introductions of hatchery rainbow trout, Rubidge et al. 2001).

Ideally, research studies that examine temporal changes among vagile animals should attempt to
compare samples collected from the exact same location and at the same time of year.
Additionally, samples sizes should be similar and the genetic methods used should be similar in
their precision and accuracy of detecting hybridization and introgression. Preferably, the exact
same diagnostic loci would be used so that frequencies of specific diagnostic alleles could be
monitored over time in the population.

Recent research in the Flathead River system in Montana (Hitt et al. submitted), and in the
Kootenay River drainage in British Columbia (Rubidge et al. 2001) has reported the rapid
spread of RBT introgression into WCT populations previously reported as free from detectable
levels of introgressive hybridization. Some researchers, who have addressed the question of how
to defme a 'pure' WCT population, have argued that management plans that attempt to set some
arbitrary limit of admixture (introgressive hybridization) below which a population will be
considered 'pure' (e.g. 1%, 10%) are problematic because, as cited above, the amount of
admixture in many WCT populations is rapidly increasing. Research reporting the rapid spread
of introgression is significant and will have to be considered carefully by the agencies
responsible for managing these particular WCT populations. However, as reviewed previously,
it is highly unlikely that every WCT population that has experienced some level of hybridization
and introgression would experience an increase in the percentage of RBT introgression over time
or that introgression would spread rapidly from one population to many populations throughout a
drainage. Importantly, the reportedly continuing spread of RBT introgression within the
Flathead River system is likely due to the establishment of self-reproducing populations of
introduced rainbow trout and the dispersal of hybrids into areas containing pure cutthroat
populations (Hitt et al. submitted). In the case of the observed increase in hybridization and
introgression within the tributaries of the upper Kootenai River, those authors mention that "the

Page - 74

YCT Multi-state Assessment February 1 0, 2003

most likely reason for the apparent increase is the continued and expanded introductions of
rainbow trout into the Koocanusa Reservoir and adjacent tributaries" (Rubidge et al. 2002).

It is also important to separate out two different issues with regards to setting limits of
introgression. One issue would be the scientific rigor and precision associated with estimating
the level of introgression in a population using molecular genetic information. It may be
reasonable to set a limit of introgression below which a population will be considered 'pure' if it
is appropriate to be conservative due to imprecision associated with the genetic markers.
Genetic markers used to detect introgressive hybridization are often assumed to be "fixed"
between RBT and WCT (meaning that a certain marker is only observed in RBT and never
observed in WCT or vice versa). However, markers continually have to be tested to ensure that
they are in fact fixed within populations. The recent work by Rubidge et al. (2001) reports that
the nuclear DNA marker Ikaros (IK) digested with Hinf-I yields fixed differences between RBT
and WCT. Work by IDFG on WCT populations in the Middle Fork of the Salmon River
indicates that the IK/Hinf-I marker is not fixed within these populations, stressing the importance
of using multiple diagnostic genefic markers when assessing introgressive hybridization.

Hitt (2002) (using dominant PINE markers) described procedures for being conservative in
describing a population as admixed or not following procedures outline by Forbes and Allendorf
(1991). When individuals fi^om a population only show a "RBT" band (based on its
electrophoretic mobility through a gel) at one marker/locus, then the population is considered
pure and the observed "RBT" band is considered to be a WCT allele with the same
electrophorefic mobility as the true diagnostic RBT allele. Hitt (2002) described 6 populafions as
being unhybridized WCT populations despite that fact that they exhibited "RBT" bands. These
"RBT" bands were used as evidence for RBT introgression in other populations when other
diagnostic markers also demonstrated RBT introgression.

A second issue regarding setting limits of admixture involves the setting of introgression levels
at some level ft-om which populations should be prioritized and conservation and management
decisions made (e.g. Cutthroat Trout Management: A Position Paper, Genetic Considerations
Associated with cutthroat trout management UDWR 2000;

http: wu\\.nr.uiah.uu\/dwr PDF cuttpos.PDF). This document was developed by the states of
Colorado, Idaho, Montana, Nevada, New Mexico, Utah, and Wyoming, to help guide managers
working with cutthroat trout. Cutthroat trout with a measured introgression level of less than 1%
are designated as "core conservation populations", and are considered pure. The less than 1%
limit allows for possible imprecision associated with genetic markers. A second category,
"conservation population", is used for populations with less than 1 0% introgression (but may
extend to a greater amount depending upon circumstances and the values and attributes to be
preserved). The less than 10% criterion is not suggesting that populations with introgression
levels between 1% and 10% be considered 'pure' or managed as a 'pure' populations, rather it is
an agreed upon decision to manage populations a certain way given that a particular level of
introgression is observed (in this case, <10%). Importantly, the primary management goal of the
"conservation population" designation is to protect and conserve populations that, while existing
in a introgressed condition, still contain a unique or essential portion of ecological, behavioral,
physiological, or genetic diversity found within the subspecies.

A concern with setting such threshold criteria based on percentages is that those criteria may not
accurately describe the true hybridization status of a sample location. The percentage
corresponds to the number of non-native alleles observed among the total alleles examined, and
is only useful in situations where the researcher is using dominant markers and can determine

Page - 75

YCT Multi-state Assessment February 1 0, 2003

there is no evidence the sample consists of more than one population. Certainly in the cases of
sympatric populations of native RBT and native WCT, even those in which a certain level of
hybridization and introgression has occurred, the documentation of the percentage RBT alleles
out of the total examined does not accurately describe the status of the population. The same is
true in situations where Fl hybrids are observed, but no backcross hybrids are observed. For
instance, if 30 individuals are sampled, and 10 of them have genotypes indicative of Fl hybrids,
10 have genotypes indicative of WCT, and 10 have genotypes indicative of RBT, the results
could be interpreted to say the population is introgressed at a level of 50%, when in fact, these
results demonstrate no RBT introgression. This particular situation would be important to
document and manage since it represents a loss in reproductive effort for both species, but it has
very different management and conservation implications than a hybrid swarm consisting of a
mixture of 50% WCT alleles and 50% RBT alleles. A more informative way of describing
hybridization and introgression within sympatric populations is to first delineate populations and
then to describe the observed genotypes and their ft^equencies within those populations.

References

Hitt, N.P, C. A. Frissell, C. Muhlfeld, and F. W. Allendorf. Submitted. Spread of hybridization
between native westslope cutthroat trout, Oncorhynchus clarki lewisi, and non-native
rainbow trout, O. mykiss, in western Montana. Canadian Journal of Fisheries and Aquatic
Sciences.

Leary, R. F., F. W. Allendorf, and G. K. Sage. 1995. Hybridization and introgression between
introduced and native fish. Amer. Fish. Soc. Symposium 15:91-101.

Mays, J.D. 2002. RAPD and mitochondrial DNA analyses of cutthroat trout ft^om four streams
in the Salmon River Breaks, Idaho. Thesis. University of Idaho. Department of Fish and
Wildlife Resources. Moscow, ID.

Rubidge E., P. Corbett, E.B. Taylor.2001. A molecular analysis of hybridization between native
westslope cutthroat trout and introduced rainbow trout in southeastern British Columbia,
Canada. J. Fish. Biol. 59:42-45.

Sage, G.K., R.F. Leary, and F.W. Allendorf. 1992. Genefic analysis of 45 populations in the
Yaak River Drainage, Montana. Wild Trout and Salmon Genetics Laboratory Report
92/3, University of Montana, Missoula.

Weigel, D.E., J.T. Peterson, P. Spruell. 2002. A model using phenotypic characterisfics to detect
introgressive hybridization in wild westslope cutthroat trout and rainbow trout. Trans.
Am. Fish. Soc. 131:389-403.

Williams, R. N., D. K. Shiozawa, J. E. Carter, and R. F. Leary. 1996. Genetic detection of

putative hybridization between native and introduced rainbow trout populations of the
Upper Snake River. Transactions of the American Fisheries Society 125:387-401.

Page - 76

YCT Multi-state Assessment

February 10,2003

Appendix E - Miles of Habitat Historically (circa 1800) Occupied by Yellowstone Cutthroat Trout in the

U.S.

River Basin Name

Basin Number

Occupied

Unoccupied

Total

Yellowstone Yellowstone Headwaters 10070001

907.8

460.0

1367.8

Upper Yellowstone

10070002

1057.6

1194.7

2252.3

Shields

10070003

645.3

80.3

725.6

Upper Yellowstone-Lake

Basin

10070004

262.2

577.4

839.7

Stillwater

10070005

401.2

326.4

727.6

Clarks Fork Yellowstone

10070006

500.6

1227.7

1728.3

Upper Yellowstone-

Pompeys Pillar

10070007

255.6

687.3

942.9

Pry or

10070008

191.0

238.4

429.4

Upper Wind

10080001

871.1

341.8

1212.9

Little Wind

10080002

217.6

269.9

487.5

Popo Agie

10080003

161.9

302.4

464.2

Lower Wind

10080005

31.7

473.8

505.6

Upper Bighorn

10080007

599.8

1003.9

1603.7

Nowood

10080008

579.2

399.2

978.4

Greybull

10080009

344.8

307.8

652.6

Big Horn Lake

10080010

287.6

574.6

862.2

North Fork Shoshone

10080012

332.0

215.3

547.4

South Fork Shoshone

10080013

191.8

161.9

353.7

Shoshone

10080014

331.5

329.8

661.2

Lower Bighorn

10080015

160.6

1197.1

1357.7

Little Bighorn

10080016

426.7

574.6

1001.3

Upper Tongue

10090101

280.9

1644.1

1925.0

Snake Snake headwaters

17040101

449.7

115.4

565.1

Gros Ventre

17040102

269.4

110.7

380.1

Greys-Hobock

17040103

668.6

154.5

823.1

Palisades

17040104

348.2

207.1

555.3

Salt

17040105

453.3

194.8

648.1

Idaho Falls

17040201

213.5

0.0

213.5

Upper Henrys

17040202

568.9

195.1

764.0

Lower Henrys

17040203

432.6

9.0

441.6

Teton

17040204

611.0

104.0

715.0

Willow

1 7040205

375.1

0.0

375.1

American Falls

17040206

527.6

37.0

564.5

Blackfoot

1 7040207

595.3

0.0

595.3

Portneuf

17040208

807.5

64.3

871.7

Lake Walcott

1 7040209

261.7

265.5

527.2

Raft

17040210

641.4

195.9

837.3

Goose

17040211

544.1

151.5

695.6

Beaver-Camas

17040214

422.7

133.3

556.1

Medicine Lodge

17040215

140.4

229.4

369.8

Totals

17369.5

14755.8 32125.3

Page - 77

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YCT Multi-state Assessment

February 10,2003

Yellowstone Headwaters 10070001

Barriers

Conpli* / \ J Hibrbjioccipkd naami

Itt C04« MllkOttdf

Page - 79

YCT Multi-state Assessment

February 10,2003

10070001 Yellowstone Headwaters Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments w/
competitive
species

10070001-1

No

16.2

10070001-2

No

28.1

10070001-110

No

7.2

10070001-13

No

13.2

10070001-14

Yes

15.6

1.2

1

10070001-15

Yes

80.4

1.8

2

10070001-16

No

115.8

10070001-17

No

477.2

10070001-18

No

4.3

10070001-19

No

6.7

10070001 Yellowstone Headwaters. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

10070001-1

1

1

16.2

10070001-2

2

3

1

28.1

10070001-110

1

7.2

10070001-13

1

13.2

10070001-14

1

1

15.6

10070001-15

6

4

4

5

80.4

10070001-16

4

4

1

4

115.8

10070001-17

14

28

5

8

477.2

10070001-18

1

4.3

10070001-19

1

6.7

Page - 80

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YCT Multi-state Assessment

February 1 0, 2003

Watershed Yellowstone Headwaters Number 10070001

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Composite
Score

Temporal

Factors

Score

Population

Size

Factor

Score

Demographic

Factors

Score

Isolation
Factor
Score

10070001-1

1

2

2

1

4

7.4

10070001-2

1

1

2

1

2

5.7

10070001-110

1

3

3

2

4

10.9

10070001-13

1

3

3

1

4

9.3

10070001-14

2

3

3

2

4

10.9

10070001-15

4

1

1

1

1

4

10070001-16

3

1

1

1

1

4

10070001-17

1

1

1

2

1

5.6

10070001-18

1

4

3

2

4

11.6

10070001-19

1

3

3

2

4

10.9

Page - 82

YCT Multi-state Assessment

February 10,2003

Upper Yellowstone 10070002
Shields 10070003

Barriers

coapiiH f^\ j KfebmioccipMa H9t)iat

HYdognptv -I'lODOtia lean
C^ 3 iU Coo* Wrtnltoi

Shields River

Upper Yellowstone
River

Page - 83

YCT Multi-state Assessment

February 1 0, 2003

10070002 Upper Yellowstone Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10070002-1

Yes

12.8

12.8

2

10070002-10

Yes

7.0

10070002-11

Yes

356.9

10070002-12

No

4.0

10070002-13

Yes

24.0

10070002-2

Yes

15.7

10070002-3

Yes

45.2

10070002-35

No

2.8

10070002-36

No

3.3

10070002-38

No

2.2

10070002-39

Yes

7.3

10070002-4

Yes

42.3

10070002-42

No

10.0

10070002-43

Yes

6.4

10070002-46

No

3.8

10070002-48

No

3.6

10070002-5

No

12.3

10070002-50

Yes

14.6

10070002-51

No

7.2

10070002-52

No

6.5

10070002-6

Yes

19.2

10070002-7

No

2.2

10070002-8

Yes

3.1

10070002-9

No

1.6

Page - 84

YCT Multi-state Assessment

February 10,2003

1 0070002. Upper Yellowstone Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10070002-1

2

12.8

10070002-10

1

7.0

10070002-11

9

19

23

11

356.9

10070002-12

1

1

4.0

10070002-13

3

1

24.0

10070002-2

1

1

15.7

10070002-3

2

3

2

45.2

10070002-35

1

2.8

10070002-36

1

3.3

10070002-38

1

2.2

10070002-39

1

7.3

10070002-4

2

5

2

42.3

10070002-42

1

10.0

10070002-43

1

6.4

10070002-46

1

3.8

10070002-48

1

3.6

10070002-5

1

12.3

10070002-50

2

14.6

10070002-51

1

7.2

10070002-52

1

6.5

10070002-6

2

1

19.2

10070002-7

1

2.2

10070002-8

1

3.1

10070002-9

1

1.6

Page - 85

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YCT Multi-state Assessment

February 10,2003

Watershed Upper Yellowstone

Number 10070002

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10070002-1

1

3

3

3

4

12.5

10070002-10

4

3

3

3

4

12.5

10070002-11

4

1

1

1

2

4.5

10070002-12

1

4

3

3

4

13.2

10070002-13

3

2

3

3

3

11.3

10070002-2

3

3

2

1

3

7.6

10070002-3

4

2

2

1

3

6.9

10070002-35

1

4

4

4

4

16

10070002-36

1

4

3

2

4

11.6

10070002-38

1

4

4

3

4

14.4

10070002-39

2

4

3

1

4

10

10070002-4

4

1

2

2

2

7.3

10070002-42

2

3

3

1

4

9.3

10070002-43

2

4

2

1

4

8.8

10070002-46

1

4

3

2

4

11.6

10070002-48

1

4

3

2

4

11.6

10070002-5

1

2

3

2

4

10.2

10070002-50

2

2

3

2

4

10.2

10070002-51

1

4

3

1

4

10

10070002-52

1

4

3

1

4

10

10070002-6

4

3

3

3

3

12

10070002-7

1

4

4

2

4

12.8

10070002-8

2

4

3

2

4

11.6

10070002-9

1

4

4

2

4

12.8

Page - 87

YCT Multi-state Assessment

February 10,2003

10070003 Shields Conservation Populations with competitive Species.

Conservation
Population
Idenfification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10070003-1

Yes

303.4

264.0

44

10070003-2

No

8.0

10070003-3

Yes

10.9

8.0

1

1 0070003. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10070003-1

6

31

19

5

303.4

10070003-2

1

8.0

10070003-3

1

10.9

Page - 88

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YCT Multi-state Assessment

February 10, 2003

Watershed Shields

Number 10070003

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10070003-1

4

1

1

2

2

4

10070003-2

3

3

2

2

4

3

10070003-3

3

3

2

2

4

3

Page - 90

YCT Multi-state Assessment

February 10,2003

Upper Yellowstone -

Lake Basin 10070004

Stillwater 10070005

Upper Clarks Fork 1 0070006

1

Hyangqvkv ' 1 100,000 f elk

Bftit — -^

V^ _J iX\ Coot WiterrMM

Page -91

YCT Multi-state Assessment

February 10, 2003

10070004 Upper Yellowstone-Lake Basin

There were no identified conservation populations within this HUC.

10070005 Stillwater Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10070005-1

Yes

4.4

4.4

1

10070005-2

No

7.0

10070005-3

No

5.5

10070005-4

Yes

18.8

16.7

1

10070005-5

Yes

32.9

32.2

7

10070005-6

Yes

5.1

5.1

1

10070005-7

Yes

6.2

6.2

1

10070005-8

Yes

6.9

6.9

1

10070005 Upper. Abundance by Conservadon Populafion

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

10070005-1

1

4.4

10070005-2

4

7.0

10070005-3

1

5.5

10070005-4

1

1

18.8

10070005-5

7

1

32.9

10070005-6

1

5.1

10070005-7

1

6.2

10070005-8

1

6.9

Page - 92

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YCT Multi-state Assessment

February 10,2003

Watershed Stillwater

Number 10070005

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10070005-1

1

4

4

4

4

16

10070005-2

1

3

3

4

9.3

10070005-3

1

3

3

4

9.3

10070005-4

3

3

2

3

7.6

10070005-5

3

2

2

3

6.9

10070005-6

2

4

3

4

10

10070005-7

3

4

3

4

10

10070005-8

1

4

3

4

10

Page - 94

YCT Multi-state Assessment

February 10,2003

1 0070006 Clarks Fork Yellowstone Conservation Populations with competitive
Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10070006-1

Yes

3.6

3.1

1

10070006-2

Yes

24.2

18.8

3

10070006-3

Yes

8.9

8.9

1

10070006-4

Yes

32.8

32.8

2

10070006-5

No

5.0

10070006-6

No

55.9

10070006. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

10070006-1

I

3.6

10070006-2

4

24.2

10070006-3

1

8.9

10070006-4

2

32.8

10070006-5

1

5.0

10070006-6

1

1

55.9

Page - 95

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lation
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ber

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1

^

^

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NO

o

o

o

o

o

o

o

o

o

o

o

o

o

o

o

o

o

o

Cons
Popu
Ident
Num

r-

r-

r^

r-

t^

r~

o

o

o

o

o

o

o

o

o

o

o

o

NO
I

ca

a.

YCT Multi-state Assessment

February 10, 2003

Watershed Clarks Fork Yellowstone

Number 10070006

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10070006-1

2

4

3

4

4

14.8

10070006-2

3

2

2

1

3

6.9

10070006-3

3

3

3

1

4

9.3

10070006-4

1

3

2

1

3

7.6

10070006-5

1

4

2

1

4

8.8

10070006-6

3

2

1

2

1

6.3

10070006-1

2

4

3

4

4

14.8

Page - 97

YCT Multi-state Assessment

February 10,2003

Upper Yellowstone -
Pompeys Pillar 10070007

Pryor 10070008
Lower Bighorn 10080015

Page - 98

YCT Multi-state Assessment

February 10,2003

1 0070007 Upper Yellowstone Pompey's Pillar

There no conservation populations identified in this HUC.

10070008 Pryor Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10070008-1

Yes

6.2

6.2

1

10070008. Abundance by Conser\'ation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10070008-1

1

6.2

Page - 99

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YCT Multi-state Assessment

February 10, 2003

Watershed Prvor

Number 1 0070008

Conservation
Population

Identification
Number

Genetic
Risk
Score

Population Risk Scores |

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10070008-1

3

4

3

2

4

11.6

Page- 101

"*i'CT Multi-state Assessment

February 10,2003

10080015. Little Bighorn Abundance by Conservation Population

*

Conser\-ation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segm.ents)

Unknown
(Segments)

10080015-1

1

6.8

1 008001 5. Conservation Populations with competitive Species.

Conservation

Population

Idenfification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Compefitive
Species

Number of
Stream
Segments
Occupied

10080015-1

No

6.8

Paae - 1 01

O

o

>-,

^
o

o
o

00

o
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3

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YCT Multi-state Assessment

February 10, 2003

Watershed Lower Bishom

Number 10080015

Conservation

Population

Identification

Number

Genetic
Posk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080015-1

1

3

2

2

4

9.7

Pase- 104

YCT Multi-state Assessment

February 10, 2003

Upper Wind River 10080001
Little Wind River 10080002
Popo Agie River 10080003

Lower Wind River 10080005

V_

Paae- 105

YCT Multi-state Assessment

February 10,2003

1 0080001 Upper Wind River Consen-ation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles

with

Competitive

Species

Number of
Stream
Segments
Occupied

10080001-1

Yes

10.1

10.1

1

10080001-10

Yes

143.5

143.5

20

10080001-11

Yes

7.8

7.8

1

10080001-12

Yes

11.9

4.3

2

10080001-2

Yes

4.4

4.4

1

10080001-3

Yes

28.2

28.2

5

10080001-4

Yes

14.0

14.0

2

10080001-5

Yes

8.8

8.8

1

10080001-7

Yes

12.4

12.4

1

1 008000 1 , Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

10080001-1

1

lO.I

10080001-10

3

6

11

143.5

10080001-11

1

7.8

10080001-12

3

1

11.9

10080001-2

1

4.4

10080001-3

1

28.2

10080001-4

2

14.0

10080001-5

1

8.8

10080001-7

1

12.4

Pase- 106

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ential
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c

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Tested
>75%
YCT
(Segme

, ^

0^ c

Cn 0

•00 c

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YCT
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c

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2 .2

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—

r-j

r^,

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m

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1

1

1

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0

0

0

0

0

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3

^

h re 'x: «

0

0

0

^-*^

^,

^^

r^

^

0

P -^ •— X

^

0

^

^

'»— •

^

^

^

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r- "^ "^ 3

oc

oc

a:

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oc

oc

2S

sc

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YCT Multi-state Assessment

Februar}' 10,2003

Watershed Upper Wind

Number 10080001

Conservation

Population

Identification

Number

Genetic
Risk
Score

PoDulation Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite

Score

10080001-1

1

3

2

1

4

8.1

10080001-10

4

1

1

2

1

5.6

10080001-11

2

4

3

2

4

11.6

10080001-12

3

3

2

2

4

9.7

10080001-2

1

3

3

1

4

9.3

10080001-3

1

2

1

1

4

6.2

10080001-4

1

2

2

1

4

7.4

10080001-5

1

3

1

2

4

8.5

10080001-7

1

3

2

1

4

8.1

Pase- 108

YCT Multi-state Assessment

February 10, 2003

10080002 Little Wind Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080002-1

Yes

4.1

4.1

1

10080002-10

Yes

2.1

2.1

1

10080002-11

Yes

J.J

3.3

1

10080002-12

Yes

2.5

2.5

1

10080002-13

No

3.0

10080002-2

Yes

2.0

2.0

1

10080002-3

Yes

16.8

2.0

1

10080002-4

No

2.4

10080002-5

Yes

11.3

11.4

2

10080002-6

Yes

25.3

25.3

2

10080002-7

Yes

6.0

6.0

1

10080002-8

Yes

4.5

4.5

1

10080002-9

Yes

25.7

25.7

2

10080002. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080002-1

1

4.1

10080002-10

1

2.1

10080002-11

1

J.J

10080002-12

1

2.5

10080002-13

1

3.0

10080002-2

1

2.0

10080002-3

2

16.8

10080002-4

1

2.4

10080002-5

2

11.3

10080002-6

2

25.3

10080002-7

1

6.0

10080002-8

1

4.5

10080002-9

2

25.7

Paae- 109

o

o

o
o
o

CO

o
o

3

z

CO

<

-a
c

olal
liles

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r-i

r-1

r^

rN

OC

r<-,

^

H ->

v^

c

■3^^

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>< y H

u<

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2 00 E.

0
~a

00

^_^

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yi

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C/5 0 J^

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u

5 M <

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^^

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YCT Multi-state Assessment

February 10, 2003

Watershed Little Wind

Number 1 0080002

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080002-1

1

3

3

3

4

12.5

10080002-10

1

3

3

2

4

10.9

10080002-11

1

4

3

3

4

13.2

10080002-12

1

4

3

3

4

13.2

10080002-13

1

4

3

2

4

11.6

10080002-2

1

4

3

1

4

10

10080002-3

1

2

1

1

3

5.7

10080002-4

1

4

3

2

4

11.6

10080002-5

2

2

2

1

1

5.9

10080002-6

4

3

2

3

2

10.3

10080002-7

1

3

2

1

4

8.1

10080002-8

1

3

2

2

4

9.7

10080002-9

1

2

2

4

2

11.2

10080003 - Popo Agie and 10080005 - Lower Wind. These HUC's had no conservation
populations identified.

Paae - 1 1 1

YCT Multi-state Assessment

February 10. 2003

Paae- !12

YCT Multi-state Assessment

February 10, 2003

10080007. Upper Bighorn. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

10080007-1

1

11.1

10080007-2

2

36.9

Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080007-1

None

11.1

10080007-2

None

36.9

Paae- 113

o

O
00

o
o

-a
03

00

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U

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C^

v;

c

<

—1

^

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<;■

r'*".

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VI

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x; 0 <U h S

.

■- 0 •= i^ D

^, ^

~o ^

-a 0 c

2 0 -o <^
■^ w 0 P

5 c^ < se

-^

(N

>^ . t/J

— -a -t-

tested
cntia!
alterei
gmen

D c2 D 5^

0

'^

^

(l>

(•^

i— >

3

a

Tested
>75%
YCT
(Segme

, ^

2> C

Cn 0

Tested
75%-9
YCT
(Segm.

>^ '-^

— M

^— -*-!

■^ C

.y T3 0

-= U P

0 t- rv

r- 0 M

u - W

0 < 5£

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0

^

c

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GO

2

z

c

c

0

C3

1 -2

3 0

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2 a

^ ^

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r-i

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^ •^ c: 0

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^^

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^^

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-^ £: 2 z

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so

YCT Multi-state Assessment

February 10,2003

Watershed Upper Bighorn

Number 10080007

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080007-1

3

4

3

2

4

11.6

10080007-2

3

3

3

3

1

11

Pase- 115

YCT Multi-state Assessment

Februar\' 10,2003

10080008 Nowood Conservation Populations with competitive Species.

Conser\'ation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080008-1

No

1.0

10080008-2

No

2.8

10080008-3

Yes

5.2

5.2

1

1008000-4

No

1.4

10080008. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Comjnon
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080008-1

1

1

1.0

10080008-2

1

2.8

10080008-3

1

5.2

10080008-4

1

1.4

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YCT Multi-state Assessment

February 10, 2003

Watershed Nowood

Number 1 0080008

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080008-1

1

4

3

1

4

10

10080008-2

1

4

3

1

4

10

10080008-3

1

4

1

1

4

7.6

10080008-4

1

4

3

1

4

10

Page -lis

YCT Multi-state Assessment

February 10, 2003

Upper Tongue 10090101
Little Bighorn 10080016
Bighorn Lake 10080010

Page- 119

YCT Multi-state Assessment

February 10.2003

lOOSOOlO Bighorn Lake CcnserN'ation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
v/ith

Competitive
Species

Number of
Stream
Segments
Occupied

10080010-1

No

1.5

1 00800 lO-Uv

Yes

8.4

8.4

1

10080010-2

No

5.0

1 00800 10-2W

No

3.5

10080010-3

No

6.1

1 00800 10-3W

No

1.2

10080010-4

No

7.3

1 00800 10-4W

No

0.7

10080010-5

No

2.8

1008001 0-5 w

No

4.0

10080010-6

No

4.8

10080010. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080010-1

1

1.5

10080010-lw

1

8.4

10080010-2

1

5.0

1 00800 10-2W

1

3.5

10080010-3

1

6.1

1 00800 10-3w

1

1.2

10080010-4

1

7.3

1 008001 0-4w

1

0.7

10080010-5

1

2.8

1 00800 10-5w

1

4.0

10080010-6

1

4.8

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YCT Multi-state Assessment

February 10,2003

Watershed Bishom Lake

Number 10080010

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080010-1

2

4

4

4

4

16

1008001 0-1 w

2

4

(-1

o

2

4

11.6

10080010-2

2

3

3

2

4

10.9

1 008001 0-2w

1

4

3

1

4

10

10080010-3

2

4

2

1

4

8.8

1 008001 0-3w

1

4

3

1

4

10

10080010-4

2

4

4

2

4

12.8

1 008001 0-^w

1

4

3

1

4

10

10080010-5

2

4

4

2

4

12.8

1 008001 0-5w

1

4

3

1

4

10

10080010-6

2

d

d

2

4

12.8

Paee- 122

YCT Multi-state Assessment

February 10, 2003

10080016 Little Bighorn Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080016-1

No

3.4

10080016-2

No

0.3

10080016-3

Yes

1.8

1.5

1

10080016-4

Yes

0.4

0.4

12

10080016-5

Yes

8.8

8.8

2

10080016. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080016-1

1

3.4

10080016-2

1

0.3

10080016-3

2

1.8

10080016-4

1

0.4

10080016-5

2

8.8

Paae - 123

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YCT Multi-state Assessment

February 10, 2003

Watershed Little Bighorn

Number 10080016

Conserv'ation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080016-1

1

4

3

1

4

10

10080016-2

1

4

3

1

4

10

10080016-3

1

4

3

2

4

11.6

10080016-4

3

4

3

2

4

11.6

10080016-5

3

4

2

2

4

10.4

Paae- 125

YCT Multi-slate Assessment

February 10,2003

Watershed Upper Tongue

Number 10090101

Conservation
Population
Identificatioi:
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
witli

Competitive
Species

Number of
Stream
Segments
Occupied

10090101-1

Yes

0.5

0.5

1

1 0090 101. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Com.mion
(Segments)

Rare
(Segments)

Unknown
(Segments)

10090101-1

1

0.5

Paoe- 126

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YCT Multi-state Assessment

February ] 0, 200:

Watershed Upper Tongue

Number 10090101

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10090101-1

1

4

3

2

4

11.6

Pase- 128

YCT Multi-state Assessment

Februairv 10,2003

Shoshone 10080014
North Fork Shoshone 10080012
South Fork Shoshone 1 008001 3

Greybull 10080009 k

^^^^■X-'^^i v/

Page- 129

YCT Multi-state Assessment

Febnjary 10, 2003

10080009 Greybull Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080009-11

Yes

42.0

17.3

10080009-12

Yes 165.2

51.9

-^
J

10080009-13

No 5.4

10080009-14

Yes

4.8

4.8

2

1 0080009. Abundance by Conservation Population

Conser\-ation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080009-11

3

5

1

42.0

10080009-12

7

9

5

165.2

10080009-13

1

5.4

10080009-14

2

4.8

PaK- 130

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YCT Multi-state Assessment

Februar>' 10,2003

Watershed GreybuU

Number 10080009

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Faciors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080009-11

1

1

1

1

1

4

10080009-12

1

1

1

1

1

4

10080009-13

1

3

3

2

4

10.9

10080009-14

1

4

2

3

4

12

Paae- 132

YCT Multi-state Assessment

February 10,2003

10080012 North Fork Shoshone Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080012-11

Yes

7.0

7.0

1

10080012. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080012-11

1

7.0

Paae- 133

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YCT Multi-state Assessment

February 10, 2003

Watershed NF Shoshone

Number 10080012

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080012-11

4

4

3

2

4

11.6

Page- 135

YCT Multi-state Assessment

Februarv- 10,2003

10080013 South Fork Shoshone Consen-'ation Populations with competitive Species.

Conser\"ation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
\^•ith

Competitive
Species

Number of
Stream
Segments
Occupied

10080013-1

Yes

23.3

23.3

4

10080013-2

No

9.5

10080013. Abundance by Conservation Population

Consen'ation Population
Identification Number

Abundance

Abundant
(Segnients)

Common
(Segments)

Rare

(Segments)

Unlmown
(Segments)

Total

Miles

10080013-1

1

->

23.3

10080013-2

1

9.5

Paae

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O

o

00

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Total
Miles

r-5
(N

3
(U

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c

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Mixed
Stock -
pure &
altered
(Segments)

Untested
Suspected
Altered
(Segments)

Untested
Potentially
Unaltered
(Segments)

Tested
>75%
YCT
(Segments)

Tested
75%-99%
YCT
(Segments)

Genetically

Altered

(Segments)

'^

H

3
O
C/3

z

o
Z

Population
Type

Meta-
population

o

c/o

!

Lonscrvation
Population
Identification
Number

1

1

x

2

00

YCT Multi-state Assessment

February 10,2003

Watershed SF Shoshone

Number 10080013

Conser\-ation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080013-1

2

2

1

1

3

5.7

10080013-2

2

3

2

3

4

11.3

Paae

YCT Multi-state Assessment

February 10, 2003

10080014. Shoshone Abundaiice by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

10080014-1

1

4.0

Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

10080014-1

None

4.0

Page- 139

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YCT Multi-state Assessment

February 10,2003

Watershed Shoshone

Number 10080014

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

10080014-1

1

4

3

2

4

11.6

Page- 141

YCT Multi-Slate Assessment

Februar>- 10,2003

Page- 142

YCT Multi-state Assessment

February 10,2003

17040101 Headwaters Snake River Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040101-2

Yes

180.7

83.8

6

17040101-3

No

7.9

1 7040 101. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040101-2

9

1

8

180.7

17040101-3

1

7.9

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YCT Multi-state Assessment

February 10,2003

Watershed Snake Headwaters

Number 17040101

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040101-2

1

1

1

2

1

5.6

17040101-3

1

4

3

1

4

10

Paee - 145

YCT Multi-state Assessment

February 10,200^^

17040102 Gros Ventre Conserx-ation Populations with competitive Species.

Conser\'ation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040102-1

^'es

1521.2

890.4

95

17040102-10

No

0.7

17040102-11

Yes

2.8

2.8

1

17040102-12

Yes

4.2

4.2

1

17040102-2

No

2.7

17040102-3

Yes

18.1

16.5

5

17040102-5

No

0.5

17040102-6

Yes

3.0

3.0

1

17040102-7

No

3.1

17040102-S

No

5.6

17040102-9

No

0.6

17040102. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unlcnown
(Segments)

17040102-1

41

135

46

34

1521.2

17040102-10

■■

0.7

17040102-11

1

2.8

17040102-12

1

4.2

17040102-2

1

2.7

17040102-3

6

1

18.1

17040102-5

1

0.5

17040102-6

1

3.0

17040102-7

1

3.1

17040102-S

2

5.6

17040102-9

1

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YCT Multi-state Assessment

February 10,2002

Watershed Gros Ventre

Number 17040102

Conservation

Population

Identification

Number

Genetic
Risk
Score

PoDulation Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040102-1

1

4

3

2

4

11.6

17040102-10

1

4

3

4

10

17040102-11

1

4

4

4

11.2

17040102-12

1

4

3

4

10

17040102-2 1

2

2

2

6.4

17040102-3

1

4

4

4

11.2

17040102-5

1

4

3

4

10

17040102-6

1

4

3

2

4

11.6

17040102-7

1

4

3

2

4.

11.6

17040102-8 1

4

4

2

4

12.8

17040102-9

1

4

3

2

4

11.6

Paae - 148

YCT Multi-state Assessment

February 10.2003

/

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Page - 149

YCT Multi-state Assessment

February 10, 2003

. 7040 1 03 Cjreys-I loback Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040103-1

Yes

7.2

7.2

1

17040103-10

No

0.5

17040103-11

No

4.8

17040103-12

No

5.3

17040103-13

No

3.0

17040103-14

No

1.4

17040103-15

Yes

9.6

3.5

1

17040103-16

No

1.8

17040103-17

No

1.4

17040103-18

No

0.9

17040 103- 18a

No

0.9

17040103-19

No

0.9

17040103-2

No

4.6

17040103-20

No

2.1

17040103-21

No

3.7

17040103-22

Yes

13.3

10.7

1

17040103-23

Yes

2.0

2.0

1

17040103-24

Yes

1.4

1.4

1

17040103-3

Yes

23.9

7.4

1

17040103-4

No

6.8

17040103-5

No

2.2

17040103-6

No

2.5

17040103-7

Yes

10.9

8.5

1

17040103-8

No

0.4

17040103-9

No

3.7

.50

YCT Multi-state Assessment

February 10, 2003

1 7040103 Greys-Hoback Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040103-1

Yes

7.2

7.2

1

17040103-10

No

0.5

17040103-11

No

4.8

17040103-12

No

5.3

17040103-13

No

3.0

17040103-14

No

1.4

17040103-15

Yes

9.6

3.5

1

17040103-16

No

1.8

17040103-17

No

1.4

17040103-18

No

0.9

17040103-18a

No

0.9

17040103-19

No

0.9

17040103-2

No

4.6

17040103-20

No

2.1

17040103-21

No

3.7

17040103-22

Yes

13.3

10.7

1

17040103-23

Yes

2.0

2.0

1

17040103-24

Yes

1.4

1.4

1

17040103-3

Yes

23.9

7.4

1

17040103-4

No

6.8

17040103-5

No

2.2

17040103-6

No

2.5

17040103-7

Yes

10.9

8.5

1

17040103-8

No

0.4

17040103-9

No

3.7

Paae- 151

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YCT Multi-state Assessment

February 10,2003

Watershed Greys Hoback

Number 17040103

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040103-1

4

4

2

4

12.8

17040103-10

4

4

2

4

12.8

17040103-11

4

4

2

4

12.8

17040103-12

4

4

2

4

12.8

17040103-13

4

4

2

4

12.8

17040103-14

4

4

2

4

12.8

17040103-15

3

3

2

4

10.9

17040103-16

4

4

2

4

12.8

17040103-17

4

4

2

4

12.8

17040103-18

4

4

2

4

12.8

170401 03-1 8a

4

4

2

4

12.8

17040103-19

4

4

2

4

12.8

17040103-2

4

4

2

4

12.8

17040103-20

4

4

2

4

12.8

17040103-21

4

4

2

4

12.8

17040103-22

3

3

2

4

10.9

17040103-23

4

4

2

4

12.8

17040103-24

4

4

2

4

12.8

17040103-3

2

3

2

4

10.2

17040103-4

4

4

2

4

12.8

17040103-5

4

4

2

4

12.8

17040103-6

4

4

2

4

12.8

17040103-7

3

3

2

4

10.9

17040103-8

4

4

2

4

12.8

17040103-9

4

3

2

4

11.6

Pase- 153

YCT Multi-state Assessment

February 10, 2003

17040104 Palisades Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040104-1

Yes

170.0

139.7

17

17040104-3

No

4.7

] 7040104-4

^'es

28.9 28.9

5

17040104-5

Yes

5.5

5.5

2

1 7040 1 04. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Uriknown
(Segments)

17040104-1

16

5

7

170.0

17040104-3

1

4.7

17040104-4

5

28.9

17040104-5

2

5.5

Paae - 154

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YCT Multi-state Assessment

February- 10.2003

Watershed Palisades

Number 17040104

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040104-1

4

1

1

2

1

5.6

17040104-3

1

4

3

2

4

11.6

17040104-4

1

2

2

2

4

9

17040104-5

1

4

3

1

4

10

i-'aee - no

YCT Multi-state Assessment

February 10,2003

17040105 Salt Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040105-1

Yes

6.5

6.5

1

17040105-2

Yes

4.6

4.6

1

17040105. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040105-1

1

6.5

17040105-2

1

4.6

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YCT Multi-state Assessment

February 10,2003

Watershed Salt

Number 17040105

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040105-1

1

4

4

1

4

11.2

17040105-2

1

4

3

1

4

10

Page

159

YCT Multi-state Assessment

Februan/ 1 0. 2003

1

Upper Hen rys170402C2
Lower Henrys 17040203
Tetcn 17040204

Pase- 160

YCT Multi-state Assessment

February 10, 2003

1 7040202 Upper Henrys Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040202-1

Yes

20.6

20.6

6

17040202- lb

Yes

16.7

16.7

5

17040202-2

No

3.5

17040202-3

Yes

1.6

1.6

1

17040202-4

No

4.2

17040202-5

Yes

13.5

13.5

3

17040202-6

Yes

12.8

12/8

2

1 7040202 Upper Henrys Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040202-1

Yes

20.6

20.6

6

17040202-lb

Yes

16.7

16.7

5

17040202-2

No

3.5

17040202-3

Yes

1.6

1.6

1

17040202-4

No

4.2

17040202-5

Yes

13.5

13.5

'>

0

17040202-6

Yes

12.8

12/8

2

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YCT Multi-state Assessment

Februaiy 10,2002

Watershed Upper Henrys

Number 17040202

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040202-1

4

2

1

3

1

7.9

1 7040202-1 b

3

3

3

3

4

12.5

17040202-2

1

4

2

1

4

8.8

17040202-3

3

4

4

3

4

14.4

17040202-4

4

4

4

1

1

9.7

17040202-5

4

3

3

3

4

12.5

17040202-6

3

4

3

3

4

13.2

Page- 163

YCT Multi-state Assessment

Febmarv 10.2003

17040203 :Lower Henn's Conservation Populations with competitive Species.

Consen^ation
Population
Identilication
Number

Competitive
Species Present

Total Miles of
^'CT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occuoied

17040203-4

Yes

96.1

91.2

9

17040203-5

Yes

4.1

4.1

1

17040203-6

Yes

20.4

20.4

->

17040203-7

Yes

30.1

30.1

2

1 7040203. Abundance by Conservation Population

Conser\'ation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040203-4

3

7

96.1

17040203-5

1

4.1

17040203-6

3

20.4

17040203-7

2

30.1

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YCT Multi-state Assessment

Februar>- 10,2003

Watershed Lower Henn-'S

Number 17040203

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040203-4

4

2

2

3

10.1

17040203-5

4

4

3

3

4

13.2

17040203-6

4

3

4

4

4

15.3

17040203-7

4

1

2

2

3

7.8

Pase - 166

YCT Multi-state Assessment

February 10, 2003

17040204 Teton Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
"^'CT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040204-1

Yes

21.3

21.3

4

17040204-2

Yes

409.1

379.3

40

1 7040204. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040204-1

2

2

21.3

17040204-2

16

16

11

409.1

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YCT Multi-state Assessment

February 10, 2003

Watershed Teton

Number 17040204

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population
Size

Score

Dem.ographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040204-1

1

3

2

2

3

9.2

17040204-2

4

1

1

3

1

7.2

Page- 169

YCT Multi-state Assessment

Februai-v 10.2003

Beaver-Camas 17040214

Medicine Lodge 17040215

Idaho Falls 1704020-!

f

a

arr'ers

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Paije- 1 '0

YCT Multi-state Assessment

February 10, 2003

17040201 Idaho Falls Conservation Populations with competitive Species.

Consenation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040201-1

Yes

29.5

29.5

1

1 7040201 . Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

17040201-1

1

29.5

Pase- 171

CN

o
o
o

3
Z

o
S

o

o

Total
Miles

u
o

a

Mixed
Stock -
pure &
altered
(Segments)

Untested
Suspected
Altered
(Segments)

Untested
Potentially
Unaltered
(Segments)

Tested
>75%
YCT
(Seginents)

Tested
75%-99%
YCT
(Segments)

Genetically

Altered

(Segments)

Source

V.

>-

Population
Type

Meta-
population

( 'onservation
Population
Identillcation
Number

17040201-1

1

l

00

K

YCT Multi-state Assessment

February 10,2003

Watershed Idaho Falls

Number 17040201

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040201-1

4

2

1

2

1

6.3

Page- 173

VCT Multi-state Assessment

February 10,2003

17040214 Bea\-er-Camas Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Streain
Segments
Occupied

17040214-1

Yes

12.3

3.1

1

17040214. Abundance by Conservation Population

Conserx'ation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040214-1

1

J

1

12.3

Pase- 174

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YCT Multi-state Assessment

February 10,2003

Watershed Beaver Camas

Number 17040214

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040214-1

4

2

3

3

3

11.3

Pase- 176

YCT Multi-state Assessment

February 10, 2003

1 70402 1 5 Medicine Lodge Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040215-1

Yes

8.1

8.1

2

17040215-2

Yes

93.6

93.6

15

17040215. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040215-1

2

8.1

17040215-2

15

93.6

Page- 177

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YCT Multi-state Assessment

February 10, 2003

Watershed Medicine Lodge

Number 17040215

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040215-1

1 ■

4

4

3

4

14.4

17040215-2

4

1

3

4

3

12.2

Paee- 179

YCT Multi-state Assessment

February 10, 2003

Willow 17040205
Blackfoot 17040207
Fortneuf 170402C8

k^^-^^l^ \

v^

-4

t

Barriers

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Pase- ISO

YCT Multi-state Assessment

February 10,2003

17040205 Willow Conser\'ation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040205-1

Yes

187.1

145.8

11

17040205. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040205-1

4

7

7

187.1

Page- 181

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YCT Multi-state Assessment

February 10, 2003

Watershed Willow

Number 1 7040205

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040205-1

3

1

1

4

1

8.8

Paee- 183

YCT Multi-state Assessment

February 10,2003

17040207 Blackfoot Conservation Populations with competitive Species.

Conservation
Popukuion
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Streani
Segments
Occupied

17040206-1

Yes

161.7

139.4

16

17040206-2

Yes

118.0

92.8

5

17040207. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040207-1

10

•-1

-)

5

161.7

17040207-2

6

1

1

118.0

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YCT Multi-state Assessment

Februarv 10,2003

Watershed Blackfoot

Number 1 7040207

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040207-1

4

1

1

2

1

5.6

17040207-2 4

1

1

2 1

5.6

Paae - 136

YCT Multi-state Assessment

February 10, 2003

17040208 Portneuf Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040208-1

Yes

9.7

4.1

1

17040208-10

No

5.7

17040208-11

No

5.0

17040208-2

No

5.5

17040208-3

No

6.4

17040208-4

No

6.8

17040208-5

No

12.6

17040208-6

No

7.4

17040208-7

Yes

18.4

5.0

2

17040208-8

Yes

30.1

10.2

2

17040208-9

No

5.6

1 7040208. Abundance by Conservation Population

Conservation Population
Identification Num.ber

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040208-1

1

1

9.7

17040208-10

■1

5.7

17040208-11

1

5.0

1 7040208-2

1

5.5

17040208-3

1

6.4

17040208-4

1

6.8

17040208-5

1

12.6

17040208-6

1

7.4

17040208-7

3

2

18.4

17040208-8

4

ji

30.1

1 7040208-9

1

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YCT Multi-state Assessment

February 10, 2003

Watershed Portneuf

Number 17040208

Conservation

Population

Identification

Number

Genetic
Risk-
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040208-1

3

4

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1

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10

17040208-10

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17040208-11

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4

11.6

17040208-2

3

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11.6

17040208-3

3

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11.6

17040208-4

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11.6

17040208-5

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11.6

17040208-6

3

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4

11.6

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2

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8.2

17040208-8

3

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7.5

17040208-9

3

4

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4

11.6

17040208-1

3

4

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10

Page- 189

YCT Mulli-state Assessment

February 10, 2003

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YCT Multi-state Assessment

February 10,2003

1 7040206. American Falls Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total

Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

UnknowTi
(Segments)

17040206-1

1

1

9.4

17040206-2

1

1

6.8

Conservation Populations with competitive Species.

Conservation

Population

Identification

Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040207-1

None

9.4

17040207-2

None

6.8

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YCT Multi-state Assessment

Februar>- 10,2003

Watershed American Falls

Number 17040206

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040206-1

1

3

3

2

4

10.9

17040206-2

1

4

3

2

4

11.6

17040209
HUC.

Lake Walcott. There were no conservation populations identified in this

Page- 193

YCT Mulii-state Assessment

February 10,2003

Goose 17040211

r -- "-'040210

Earners

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Paae- 194

YCT Multi-state Assessment

February 10, 2003

170402 10 Raft River Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040210-1

Yes

43.2

43.2

10

17040210-10

No

3.0

17040210-2

No

3.1

17040210-3

No

2.9

17040210-4

No

2.7

17040210-5

No

3.5

17040210-6

No

15.2

17040210-7

No

1.7

17040210-8

Yes

7.5

7.5

3

17040210-9

Yes

7.0

7.0

2

1 70402 1 0. Abundance by Conservation Population

Conservation Population
Identification Number

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare
(Segments)

Unknown
(Segments)

17040210-1

8

1

1

43.2

17040210-10

2

3.0

17040210-2

1

3.1

17040210-3

1

2.9

17040210-4

1

2.7

17040210-5

2

3.5

17040210-6

2

1

15.2

17040210-7

1

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17040210-8

1

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YCT Multi-state Assessment

February 10, 2003

Watershed Raft

Number 17040210

Conservation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040210-1

4

2

2

2

4

9

17040210-10

4

3

1

4

10

17040210-2

4

3

1

4

10

17040210-3

4

3

1

4

10

17040210-4

4

3

1

4

10

17040210-5

4

3

2

4

11.6

17040210-6

3

1

1

1

5.4

17040210-7

4

3

1

4

10

17040210-8

3

1

2

1

7

17040210-9

3

3

1

2

4

8.5

Paae- 19'^

^'CT Multi-state Assessment

Febraarv 10.2003

1 704021 1 Goose Conservation Populations with competitive Species.

Conservation
Population
Identification
Number

Competitive
Species Present

Total Miles of
YCT

Total Miles
with

Competitive
Species

Number of
Stream
Segments
Occupied

17040211-1

No

19.0

17040211-2

Yes

69.2

53.2

A

*~i'

1 70402 1 1 . Abundance by Conservation Population

Conservation Population
Identification Num/cer

Abundance

Total
Miles

Abundant
(Segments)

Common
(Segments)

Rare

(Segments)

Unknown
(Segments)

17040211-1

1

19.0

17040211-2

5

2

69.2

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"V'CT Multi-state Assessment

February 10,2002

Watershed Goose

Number 17040211

Conscr\"ation

Population

Identification

Number

Genetic
Risk
Score

Population Risk Scores

Temporal

Factors

Score

Population

Size

Score

Demographic

Factors

Score

Isolation
Factor
Score

Composite
Score

17040211-1

1

2

2

2

4

9

17040211-2

2

2

2

3

2

9.6

Page - 200

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