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Baseline Assessments and Analysis of Fish,

Macroinvertebrates and Herpetofauna in the Otter Creek

Coal Tracts Area of Powder River County

Prepared for:

Pat Farmer, Project Manager/Director

Westech Environmental Services
Helena Field Office

Prepared by:

David Stagliano, Aquatic Ecologist
Montana Natural Heritage Program

a cooperative program of the
Montana State Library and the University of Montana

January 2012

MONTANA

Natural Heritage

Xm> Program

Executive Summary

We summarize the first year of baseline surveys for the Aquatic Assessment of Fish,
Macroinvertebrates, and Herpetofauna in the Otter Creek coal tracts area. Project goals were: 1)
to conduct standardized surveys and collect baseline information on the aquatic and riparian
communities occurring in Otter Creek and three tributaries (seasonally and spatially oriented)
prior to coal development, 2) to assess aquatic community integrity and condition by interpreting
key indicators recorded at sites using standardized protocols and biotic thresholds, and to
compare these against reference condition standards. These data collected represent pre-
development (i.e. pre-impact, BACI design) conditions at the local reach scale.

Habitat assessments, herpetofauna, macroinvertebrate and fish surveys were performed
seasonally at three predetermined mainstem Otter Creek reaches (control, impact and
downstream) and three tributaries coinciding with established surface water quality stations during
2011. Additionally, we added fish sampling visits to Otter Creek Impact #2 (upstream of the
Threemile Creek confluence) because Threemile Creek remained "dry" during all visits. In total,
we performed 15 surveys for fish during the visits: 11 at four mainstem Otter Creek reaches and
four surveys at two tributary streams. Fifteen macroinvertebrate samples were collected during
the visits; neither taxa survey was conducted at Threemile Creek in any season due to lack of
surface water present. All six a priori stream reaches were visually surveyed for amphibians or
reptiles during all visits. Biological community integrity was calculated for 15 fish surveys using
Fish Integrated Biotic Indices (IBI's) and Observed/Expected Models (O/E), while the 15
macroinvertebrate samples were assessed with Montana DEQ's multi-metric indices (MT MMI).

Habitat Evaluations. Of the seven sampling reaches evaluated in the study area, we found three
in Proper Functioning Condition (PFC) with a stable trend and four were Functional at Risk (FAR).
Reasons that sites ranked FAR were likely due to anthropogenic habitat alteration by cattle (Home
Creek {Otter_lA} and Threemile Creek {Otter_3m}) or stream manipulation (Otter Creek JT-
Trussler and Otter Creek #16). Highest site integrity scores using both the BLM Habitat and PFC
Assessment methods were recorded at the Otter Creek sites #23 (Tenmile Creek) and #22 (control-
Denson reach). Sites with lower habitat scores were structurally degraded predominately by cattle
use and had high associated Livestock Use Indices (LUI) (Home Creek, Threemile and Otter Creek
#16-fall). Point conductivity measurements recorded at all Otter Creek mainstem sites across
most seasons were above the threshold for impairment levels (>500ps, DEQ 2006), and Home
Creek site 1A had visible signs of natural gas seepage from the sediments.

Macroinvertebrate Communities: Overall, 104 unique macroinvertebrate taxa were reported from
the 15 macroinvertebrate assessment samples. One known Montana species of concern (SOC),
the mayfly, Caenis youngi was collected in fair numbers at the control site, Otter Creek #22.
Average macroinvertebrate taxa richness per site was 29.5 and the highest taxa richness was 41
taxa reported at the Otter Creek JT site. Using the Montana DEQ macroinvertebrate multimetric
index (MMI), four of the five sites (12 of 15 samples) were ranked non-impaired (good to excellent
biological integrity), while all three samples from Tenmile Creek were ranked marginally impaired.
Stream sites that maintained flowing, connected water scored higher with the MMI than sites with

interrupted pool areas. Overall, mainstem sites evaluated in the Otter Creek study received
significantly higher macroinvertebrate MMI scores than those in the tributaries (T-test, p <0.01).
MMI's did not significantly differ on Otter Creek mainstem Pre-lmpact Control, Impact or
Downstream Sites (T-test, p >0.05), despite the fish communities reflecting a decrease in biotic
integrity.

Fish Communities. Overall, nine fish species (five native/four introduced) were identified from
37,679 individuals collected from 15 site visits (Table 4). One potential species of concern (PSOC),
the brassy minnow, was collected at five of six sites. Average fish species per Otter Creek
mainstem site across all seasons was 6.5 (± 0.8 SE), while the tributary sites averaged 1.75 species
(Table 4). All fish presence sites also reported at least one species of amphibian. Lake chubs had
the highest site occupancy rate at 93% (14 of 15 visits) followed by fathead and brassy minnows at
80% (12 of 15 visits). Fish data collected in previous years from three sites within the study area
showed similar biological integrity over time. The most diverse site in the study area was Otter
Creek JT site with nine species, while the most intact sites were Otter Creek Site #22 at Denson's
(four native) and the Tenmile Creek spring survey (two native spp.). Using Montana's Prairie Fish
IBI, 9 of the 15 fish sites were ranked non-impaired (good biological integrity), two were slightly
impaired (moderate integrity) and four were moderately impaired (poor biotic integrity). Fish IBI's
decreased going downstream on Otter Creek, and the Pre-lmpact Control Site scored significantly
higher than Impact or Downstream sites (T-test, p <0.05).

Amphibian and Reptile Incidentals. Eight herpetofauna species were observed, collected in
dipnets/seines or incidentally recorded in conjunction with the fish, habitat and macroinvertebrate
surveys. We reported four amphibian species, of which, Woodhouse's Toad (Bufo woodhousii)
had the highest site occupancy, occurring at six of seven sites, followed by the Northern Leopard
Frog (Rana pipiens) and Tiger Salamander (Ambystoma tigrinum) recorded at five and four sites,
respectively. Boreal Chorus Frog (Pseudacris maculata) was detected at three sites during the
spring visits only. We also recorded four reptile species (in order of site occurrence): Western
Rattlesnake (Crotalus viridis), Painted Turtle (Chrysemys picta), Terrestrial Garter Snake,
(Thamnophis elegans) and Snapping Turtle (Chelydra serpentine) (SOC).

Conclusions. The aquatic community sampling sites chosen for pre-impact baseline data were
representative of the range of stream classes found in the Otter Coal Tracts project area:
Ephemeral, Intermittent and Perennial Prairie Streams. Despite this having been an unusually high
water year for the region, stream communities that we sampled encompassed the range of
expected species to occur in these stream types. Biotic integrity of sites was initially higher in the
upstream control reaches of Otter Creek. One extraordinary finding was the high density and large
biomass of fish inhabiting the stream reach below Trusler's Ranch road crossing (~20,000 fish in
the 300 m reach fall survey, 15 fish/m 2 ); this was most likely an artifact of the impassible culvert
located here and the fish "stacking up" downstream of this barrier. Density dependent fish
anomalies (lesions and parasites, i.e., yellow grub and anchorworm) were prevalent at this site,
indicating the fish were likely experiencing stress from overcrowding. Benthic macroinvertebrate
densities at this site were low, but, more diverse than other sites, indicating that the fish may have
been consuming large portions of the available insect production, having a top-down community
effect.

Table of Contents

INTRODUCTION 6

METHODS

Study Area 6

Habitat Assessments 7

Macroinvertebrate Community Surveys 9

Fish and Amphibian Surveys Surveys 10

RESULTS

Habitat Assessments 11

Macroinvertebrate Community Surveys 12

Fish Communities 14

Hepetofauna Communities 18

CONCLUSIONS 19

SITE PHOTOS 21

LITERATURE CITED 25

APPENDIX A. Fish data and IBI metric calculations collected from Otter Creek Project Sites

APPENDIX B. Macroinvertebate taxa list, abundance and metrics for the 15 collection sites

List of Figures

gure 1. USGS gage data for Otter Creek at Ashland in 2011 8

gure 2. Macroinvertebrate D-net Sampling procedure 9

gure 3. Brassy minnows and lake chubs in the seine at Otter 22 10

gure 4. Photo of a structurally cattle-damaged, functional-at-risk (FAR) stream reach 11

gure 5. DEQ MMI scores by site and season 13

gure 6. Average macroinvertebrate MMI scores by site type 14

gure 7. Fish IBI seasonality recorded during 2011 surveys 16

gure 8. Comparison of the Fish IBI and O/E scores between sites and season 17

gure 9. Average fish IBI scores by BACI design site type 17

List of Tables

Table 1. Otter Creek Study site GPS locations of reach 7

Table 2. Impairment determinations from the MMI and O/E (RIVPACS) models 9

Table 3. Fish metrics and classification offish species captured in the study area 11

Table 4. Macroinvertebrate sample characteristics and metrics used for the DEQ MMI 13

Table 5. Fish abundance, IBI and O/E scores for the 12 surveys reporting fish 15

Table 6. Species of vertebrates collected during the aquatic surveys in 2011 18

Table 7. Otter Creek Temporal Habitat Scores, Fish IBIs and MMIs 19

Acknowledgements

We would like to thank Pat Farmer of Westech Environmental Services of Helena for funding this
project under agreement # L08AC13222. Report review and editing was provided by Stephen
Fernandes and Linda Vance. Field work coordination, landowner contacts and logistics were
greatly expediated by Carl Lenz and Heidi Kaiser (Hydrometrics, Inc.). Fieldwork assistance
provided by Stephen Fernandes (MTNHP) was invaluable.

All photos in the report were taken by MTNHP personnel, unless otherwise noted

Introduction

The Otter Creek basin in southeast Montana is currently undergoing exploration for a large, open-
pit coal mine. Baseline data on the condition of the ecosystem prior to coal mine development
(pre-impact) is essential to determine what effects the coal extraction might have on the fish and
wildlife in, and downstream of, the effected extraction area (post-impact). The initial mining rights
transfer determined that no Federally Listed species under the ESA would be affected in the coal
tracts area (BLM EA 2002). But this EA did not take into account the presence of Montana species
of concern (SOC) or other ecologically sensitive native species assemblages. Despite numerous
projects undertaken to document and monitor biological communities in the Powder and Tongue
River watersheds in the wake of CBNG development (Confluence Consulting Inc. 2003, 2004;
Stagliano 2006; Davis et al. 2009; Maxell 2009; Petersen et al. 2009; Senecal 2009, Stagliano 2011),
large gaps still exist in basic baseline surveys for riparian macroinvertebrate, fish, and
herpetofauna in the Otter Creek basin. Fish communities have been documented to be seasonally
variable in prairie streams (Bramblett and Fausch 1991), thus sampling across all seasons is a good
strategy to document baseline community differences. Many of the remaining data gaps involve
small prairie streams that constitute the Northwestern Great Plains Intermittent Prairie Stream
ecological system (Stagliano 2005). This stream system may have downstream connectivity early
in the season for potential fish spawning and nursery areas (Smith and Hubert 1989, Bramblett
2000) or no fish colonization at all, but by summer often becomes a string of isolated pools that
are important breeding and rearing areas for amphibians (Stagliano 2011). Identifying baseline
communities and conditions in streams of the coal tracts area (i.e., the presence of fish,
macroinvertebrate, and herpetofauna) prior to coal development is essential to understanding and
potentially mitigating impacts to habitats and species during and after coal extraction.

Methods

Study Sites

The aquatic community sampling sites chosen for pre-impact baseline data are representative of
the range of streams found in the Otter Coal Tracts project area: Ephemeral, Intermittent and
Perennial Prairie Streams. Three predetermined mainstem Otter Creek reaches (control, impact
and downstream) and three tributaries coinciding with established surface water quality stations were
visited seasonally (May, July, October) during 2011 (Table 1). Additionally, we added fish sampling
visits to Otter Creek site #2 near the Threemile Creek confluence, since Threemile Creek remained
"dry" during all visits (see Site Photos). Study site visits were timed with season and discharge
(Figure 1); although we tried to coordinate field visits with baseflow water levels, 2011 was an

Table 1. Otter Creek Coal Study Site GPS Locations at the top (T) and bottom (B) of the assessment
reach. Aquatic Ecological System (AES) code described in text followed Stagliano (2005).

Elev

Site Code

Site Name

Type

AES code

Latitude

Longitude

(m)

Comment

Spring survey for fish

Otter_23

Tenmile Creek (T)

Control

D005/E005

45.43409

-106.13403

961

above the road reach,
dry during July, Oct.

Otter_23

Tenmile Creek (B)

Control

D005/E005

45.43465

-106.13253

958

visits

Top of reach began

~60m below Tenmile

Otter_22

Otter Creek 22 (T)

Control

D005/C005

45.43035

-106.14428

951

Creek road,
proceeded 300m

Otter_22

Otter Creek 22 (B)

Control

D005/C005

45.43274

-106.14366

948

downstream

Top of reach began

Otter_16

Otter Creek 16 (T)

Impact

C005

45.48514

-106.16487

938

~60m above the
stream crossing and

Otter_16

Otter Creek 16 (B)

Impact

C005

45.48365

-106.16725

937

went 240m below

Spring survey

Otter_3m

Threemile Creek (T)

Impact

E005

45.51054

-106.16288

933

contained standing

water in cattle hoof

prints, dry during July,

Otter_3m

Threemile Creek (B)

Impact

E005

45.50955

-106.16960

928

Oct. visits

Site added for fish

Otter_2

Otter Creek 2 (T)

Impact

C005

45.50475

-106.17493

929

surveys during July

visit (unseinable in

Spring), downstream

Otter_2

Otter Creek 2 (B)

Impact

C005

45.50561

-106.17561

928

of road crossing

Top of reach began

~80m below the ranch

OtterJT

Otter Creek JT(T)

Down

C005

45.55675

-106.21798

910

road/impassable
culvert, proceeded

Otter JT

Otter Creek JT(B)

Down

C005

45.55782

-106.21770

909

300m down

Bottom of reach

Otter_lA

Home Creek (B)

Down

D005/E005

45.54483

-106.18717

952

began ~500m above
the Otter Creek road
crossing, proceeded

Otter_lA

Home Creek (T)

Down

D005/E005

45.54422

-106.18947

950

300m upstream

extreme high water year (avgerage yearly discharge 14.9 vs. 3.96 cfs in 2010). Therefore, we had
to take advantage of sampling conditions as they presented themselves, sometimes not during the
most ideal sampling periods (e.g., May visit @ 19 cfs between two high water pulses, Figure 1).
Summer and fall visits were closer to base flow at 11 and 7 cfs, respectively. Habitat assessments,
herpotofauna, macroinvertebrate and fish surveys were performed during the same site visit. In
total, we surveyed 15 reaches for fish during the visits: four mainstem Otter Creek reaches (11
surveys) and two tributary streams (4 surveys). Fifteen macroinvertebrate samples were collected
during the visits; neither survey was conducted at Threemile Creek in any season due to lack of
surface water present. Spring and fall macroinvertebrate samples were collected outside of the
MTDEQ recommend sampling time frame (June l st -September 15 th ) (MTDEQ 2006), but this period

was largely derived for mountain streams. All six a priori stream reaches were visually surveyed for
amphibians or reptiles during all visits.

Figure 1. Discharge reported at the USGS gage in Ashland, MT. Arrows indicate sampling dates.

^ 300.0
8 200.

_l
H

19.0

Jan
2611

USGS ©6307749 Otter Creek at Ashland MT

Har
2011

Hay
2011

Sep
2611

Mow
2011

Daily nean discharge • Flow at station affected by ice

— Estinated daily nean discharge ^—Period of provisional data

^^ Period of approved data

Riparian Assessments

The assessment stream reach was divided into 10 equally spaced transects according to BLM and
EMAP protocols (BLM 2008b; Lazorchak et al. 1998). The downstream transect was marked (GPS,
flagging and photo point) as the bottom of the reach and all ecological assessment protocols
started from this point and continued upstream for 300m (designated the assessment area or
"AA") to the top of the reach which was also marked. Parameters recorded at each transect
were: wetted width, three channel depth measurements, % large woody debris and riparian
shading. On-site habitat assessments were conducted using the rapid assessment protocol
developed for the EPA by Barbour et al. (1999) with modifications for the BLM by the National
Aquatic Assessment Team (scores 0-24) (BLM 2008). The process for determining Proper
Functioning Condition followed Pritchard et al. (1993). Basic water parameters (temperature, pH,
conductivity) were recorded prior to biological sampling using a Horiba H-10 water monitor,
calibrated for the higher conductivity range. The Livestock Use Index ("Cowpie" CPI) was assessed
by walking a randomly chosen 75m reach on both sides of the stream channel in the riparian area
within the assessment area and counting all the old and new cowpies (high CPI equals high cow
usage). The goal of these evaluations is to characterize local reach geomorphology, riparian and

in-stream habitat, and characteristics that influence aquatic community integrity. The sites
ranking higher using these protocols are determined to have higher quality local-scale habitat.
Habitat assessments were performed during the same visit as the biological sampling.

Macroinvertebrate Communities

Macroinvertebrate communities were sampled qualitatively from the 10 transects within the
300m assessment reach using the EMAP Reach-Wide protocol (Lazorchak et al. 1998). Sampling
started at the downstream transect (A) or #10 in the BLM protocol, and proceeded upstream
alternating sampling with the 500-micron D-frame net to the left, right or center of the stream
channel, so a random sampling of all habitats is achieved (Figure 2). Ten multi-habitat kicks were
composited from the net into a 20 liter bucket. All organisms and organic matter in the bucket

were elutriated from the inorganic portion

Figure 2. Macroinvertebrate EMAP Sampling procedure .

and washed onto a 500-micron sieve. The
inorganic portion was washed and examined
until no further organics or organisms were
present and discarded. The organic portion
on the sieve was transferred to one or two 1
liter Nalgene bottles (unless field sub-
sampling was needed), labeled and preserved
in 95% ethanol and brought to the MTNHP lab
in Helena for processing (sorting,
identification and data analysis) following
protocols outlined by the BLM (2008a) and MTDEQ (2006). Macroinvertebrates were identified to
the lowest taxonomic level (MTDEQ 2006), counted, imported into EDAS (Jessup 2006), and
biological metrics were calculated from the data using the Montana Department of Environmental
Quality's newest multimetric macroinvertebrate (MMI) protocols (Jessup et al. 2005, Feldman
2006). Metric results were scored using the MTDEQ bioassessment criteria and each sample
categorized as nonimpaired or impaired according to threshold values (Table 2). The
macroinvertebrate MMI score is based upon a series of metrics that measure attributes of benthic

macroinvertebrate communities that are
sensitive to condition changes in the stream
(in the form of pollution or pollutants). The
index score represents the condition of the
macroinvertebrate community at the time
the sample was collected within that past
year. If the index score is below the
impairment threshold, the individual metrics
can be used to provide insight as to why the
communities are different from the reference condition (Barbour et. al 1999, Jessup et. al. 2005).

Table 2. Impairment determinations from the MTDEQ MMI

anri n/F (RI\/PZir<;\ mnriolc

Ecoregion

RIVPACS

MMI

Impairment Determination

Mountain

> 0.8 or < 1.2

>63

Not impaired

< 0.8 or > 1.2

<63

Impaired

Low Valley

> 0.8 or < 1.2

>48

Not impaired

< 0.8 or > 1.2

<48

Impaired

Eastern Plains

> 0.8 or < 1.2

>37

Not impaired

< 0.8 or > 1.2

<37

Impaired

The impairment threshold set by MTDEQ is 37 for the Eastern Plains Stream Index, thus any scores
above this threshold are considered unimpaired.

Fish and Amphibian Surveys

Fish sampling within the 300m stream channel assessment reach was conducted with 6 and 9
meter straight seines in 25-30m increments seining in a downstream direction toward the block
seine (protocols outlined in Bramblett et al. 2005). Fish captured in a blocked section were
transferred to holding buckets until the reach was completed, unless the reach was broken up by
riffles, impassable or dry sections; in this case, fish were worked up and released within the
section of capture. Fish holding in the buckets were identified to species (Holton and Johnson
2003), enumerated, examined for external anomalies (e.g. deformities, eroded fins, lesions, and

tumors), and then released. At least 10% of

the individuals of a species were measured

for total length in millimeters (TL mm) to

I obtain size structure data. Young-of-the-

year fish less than 20 mm (TL) were noted
on the field sheet (not included in the
totals) and released. Baited minnow traps
were deployed and fished overnight (12
hour minimum) during the spring visits when seining conditions were toughest. Voucher
specimens were only taken in the case of uncertain field identifications, and were preserved in
10% buffered formalin. These will be deposited with the Montana State University Collections.
Adult amphibians or reptiles seen while seining or walking the designated stream reach were
counted and recorded even if they were not captured in the seine.

Analysis of the sampled fish communities used Integrated Biotic Indices (IBI) designed for wadable
prairie streams (Bramblett et. al 2005) and derived Observed/Expected (O/E) Fish Models
(Stagliano 2011) to detect impairment in the biological integrity of the sites. The expected number
of native fish species for a D005 classified reference stream is 2.5-3.75, while the number of fish
for a C005 stream in 5.5-8.5 depending on watershed area, dividing the observed number of native
fish species at a site by the expected number derives a percentage compared to reference

condition (>0.8 or 80% = unimpaired) (Table 1). The IBI originally proposed by Karr (1981)
involved the calculation of a series of 12 metrics evaluating different attributes of the fish
community (i.e. species richness, tolerance to pollutants, trophic status) (Table 3). The 10 metrics
used for the prairie streams were adjusted for watershed area to calculate an overall score
between and 100. Bramblett et al. (2005) did not propose threshold criteria for good, fair, and
poor biological integrity for these scores. Therefore, we applied percentiles above the null criteria
(no fish present score) at >30% indicates good to excellent biological integrity, 10-30% fair/good
biological integrity, 0-10% indicated poor to fair biological integrity and scores below the null are
indicative of poor biological integrity or severely impaired.
Table 3. Fish metrics and classification of fishes captured during the Otter Creek Study (2011).

Species

Scientific Name

Trophic

Feeding

Repro

General

Origin

Total

Habitatt

Guild*

Tolerance

Length
3 years

Catostomidae

White sucker

Catostomus commersoni

TOL

229

Cyprinidae

Common Carp

Cyprinus carpio

TOL

381

Brassy minnow

Hybognathus hankinsoni

MOD

Fathead Minnow

Pimephales promelas

TOL§

TOL

Lake Chub

Couesius plumbeus

MOD

140

Sand Shiner

Notropis stramineus

MOD

Centrarchidae

Green Sunfish

Lepomis cyanellus

TOL§

TOL

102

Pumpkinseed

Lepomis gibbosus

TOL§

MOD

Ictaluridae

Black Bullhead

Ameiurus melas

TOL§

TOL

152

*HB = herbivore (> 90% plants or detritus); IC = invertivore/carnivore (>25% both invertebrates and vertebrates); IN = invertivore; OM =

omnivore(25-90% plants or detritus)

f BE = benthic; GE = generalist; WC = water column: Brown (1971); Scott and Crossman (1973); Becker (1983)

% LO=Litho-obligate Reproductive Guild; Scott and Crossman (1973); Pflieger (1997); Barbour et al. (1999)

§ Tolerant reproductive strategists are not litho-obligates, use parental care at spawning site: Scott and Crossman (1973); Pflieger (1997)

** INT = intolerant; MOD = moderately tolerant: TOL = tolerant; Barbour et al. (1999);

ft N = native; I - introduced; Brown (1971); Holton and Johnson (2003)

Results

We evaluated seven stream reaches in the study area: four Otter Creek mainstem sites were
classified as Great Plains Perennial Prairie Stream types (C005), and the three tributaries were the
Great Plains Intermittent Prairie Stream systems (D005, E005) (Stagliano 2005). Proper

classification is important when determining biological integrity (Hawkins and Norris 2000) and
expected species richness. The Intermittent Prairie Stream (E005) in Montana is naturally fishless
about 80% of the time; therefore, absence of fish, in itself, should not be viewed as a biological
impairment (Threemile and Tenmile Creek). Likewise, stream reaches of Otter Creek have become
dry in previous years (Stagliano, personal observation 2005-2008), thus placing this stream section
within the D005 classification. We have identified and characterized reference condition indicator
assemblages for these ecosystem types previously (Stagliano 2005), and used these here to
compare to our site-specific observed species.

Habitat Evaluations. Of the seven sampling reaches evaluated within the study area, we found
three in Proper Functioning Condition (PFC) with a stable trend and four were Functional at Risk
(FAR) (Table 7). Reasons that sites ranked FAR were due to structural habitat alteration by cattle
with associated high CPI values (Home Creek {Otter_lA}, Threemile Creek {Otter_3m} and Otter
#16-fall) (Figure 4) or anthropogenic stream manipulation (Otter Creek JT-Trussler and Otter Creek

#16). Highest site integrity scores using both the
BLM Habitat and PFC Assessment methods were
recorded at the Tenmile Creek (Otter_23) and
Otter Creek #22 (control-Denson reach) (Table 7).
Point conductivity measurements recorded at all

Otter Creek mainstem sites and tributaries across
all seasons were above the threshold for
impairment levels (>500ps, DEQ 2006), and
Home Creek site had visible signs of natural gas
seepage from the sediments.

Macroinvertebrate Communities: Overall, 104 unique macroinvertebrate taxa were reported from
the 15 macroinvertebrate assessment samples (Appendix B). One known Montana species of
concern (SOC), the mayfly, Caenis youngi was collected in fair numbers at the control site, Otter
Creek #22. Stoneflies (P) were not present at any sites, so the EPT taxa per site usually consisted of
two species of tolerant mayflies (E), and one or two species of caddisfly (T); the highest EPT
richness at any site was six species at the Otter JT site spring (Table 4, Appendix B). Average

macroinvertebrate taxa richness per site was 29.5 and the highest taxa richness was 41 taxa
reported at the Otter Creek JT site. Using the MTDEQ multimetric index (MMI), four of the five
sites (12 of 15 samples) were ranked non-impaired (good to excellent biological integrity), while all
three samples from Tenmile Creek were ranked marginally impaired (Figure 5).

Table 4. Macroinvertebrate sample characteristics and various metrics used for the DEQ MMI.

Plains

Total Ind.

Total

MMI

EPT

% Non-

Site ID

CollDate

ID'ed

Sample

Taxa

Index

Taxa

%EPT

HBI

Insect

Otter_23

5/16/2011

605

4,840

36.8

0.3

7.7

6.9

Otter_23s

7/17/2011

515

2,060

35.2

0.0

7.3

15.2

Otter_23f

10/15/2011

617

2,468

35.6

0.0

7.1

15.9

OTTER_22

5/17/2011

628

5,024

46.3

2.7

7.4

56.2

OTTER_22s

7/14/2011

879

10,548

54.3

36.2

7.9

40.7

OTTER_22f

10/14/2011

725

5,800

65.9

22.3

7.7

43.5

OTTER_16

5/17/2011

564

4,512

44.4

3.2

7.5

55.3

OTTER_16s

7/16/2011

686

8,232

51.2

25.4

7.7

43.0

OTTER_16f

10/15/2011

603

4,824

46.2

22.9

7.2

50.3

OTTERJT

5/17/2011

610

2,440

64.6

17.4

7.4

30.2

OTTERJTs

7/18/2011

605

3,630

65.8

18.2

7.5

37.7

OTTERJTf

10/15/2011

606

2,424

43.4

7.6

6.6

10.9

0TTER_1A

5/16/2011

639

5,112

57.4

2.5

6.8

17.8

OTTER_lAs

7/17/2011

626

5,008

43.2

0.2

7.2

11.8

OTTER_lAf

10/14/2011

617

4,936

37.9

0.3

7.0

21.7

Figure 5. DEQ MMI scores across sites and seasons. Line is the impairment threshold at 37.

■ Spring

□ Summer

□ Fall

Tenmile Otter_22 Otter_16 OtterJT HomeCr.
Downstream >

Stream sites that maintained flowing, connected water scored higher with the MMI than sites with
interrupted pool areas. Overall, mainstem sites evaluated in the Otter Creek study received
significantly higher macroinvertebrate MMI scores than those in the tributaries (T-test, p <0.01).
MMI's did not significantly differ on Otter Creek mainstem Pre-lmpact Control, Impact or
Downstream Sites (T-test, p >0.05), despite the fish communities reflecting a decrease in biotic
integrity. No site had consistently high macroinvertebrate scores across all seasons.

Figure 6. Average MMI scores by site type, (a) = no baseline differences between treatments.

Otter Creek mainstem sites 2011

8 60

| 50

v 40

>
c

O 30

i_
u
a

S 20

(a) W

(a)

57.9

55.5

47.3

Control

Impact

Downstream

Fish Communities. Overall, nine fish species (five native/four introduced) were identified from
37,679 individuals collected from 15 site visits (Table 5). One potential species of concern (PSOC),
the brassy minnow, was collected at five of six sites and in very high numbers at the control site,
Otter 22. Dominance by brassy minnows and lake chubs at the upstream sites shifts to a tolerant
fathead minnow and sand shiner dominated community at the downstream site, Otter JT (Table
5). Otter Creek site 16 was heavily infested by introduced species during the summer and fall
visits representing 41% and 93% of the fish sampled, respectively. Average number of fish species
collected at Otter Creek mainstem sites across all seasons was 6.5 (± 0.8 SE), while the tributary
sites averaged 1.75 species (Table 5). All fish presence sites also reported at least one species of
amphibian (Table 6). Lake chubs had the highest site occupancy rate at 93% (14 of 15 visits)
followed by fathead and brassy minnows at 80% (12 of 15 visits), but fathead minnows
contributed to the highest proportion of individuals (56%, see Table 5), followed by lake

chubs at 17%. The most diverse site in the study was Otter Creek JT site with nine species, while the most intact sites were Otter Creek
Site #22 at Denson's (four native spp.) and the Tenmile Creek spring survey (two native spp.).

Table 5. Fish abundance, IBI"s and O/E results for the 6 sites reporting fish, ns =not seined during visit (dry) or us =unseinable conditions.
Underlined values are fish communities ranked biologically unimpaired.

OTTER_

.16

OTTER.

OTTER_

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

Total

Black Bullhead*

186

228

Brassy Minnow

2400

588

104

549

154

364

143

4554

Common Carp*

432

1314

213

138

2184

Fathead Minnow

2008

2995

17810

22978

Lake Chub

153

2785

1059

105

103

4457

Green Sunfish*

Pumpkinseed*

Sand Shiner

2755

2840

White Sucker

140

108

388

Total # species

Native Species

Total Individuals

240

5330

1674

184

1072

1653

372

546

2257

3384

20899

37,698

IBI

75.6

66.1

67.3

69.2

62.3

50.7

44.4

62.7

63.1

44.9

43.8

48.9

70.8

46.5

O/E

0.82

0.80

1.07

0.73

0.91

0.73

0.59

0.82

0.41

O/E %

81.6

80.0

106.7

72.7

90.9

72.7

58.8

81.6

40.8

Using the Prairie Fish IBI, 9 of the 15 fish sites were ranked non-impaired (good biological
integrity), two were slightly impaired (moderate integrity), three were moderately impaired
(poor biotic integrity) and the Home Creek fall survey was ranked severely impaired (Figure 7).
The O/E models tracked the IBI scores quite well at most sites (13 of 15), except two where the
O/E ranked the site as slightly impaired and the IBI ranked the sites as non-impaired (Figure 8).

Figure 7. Fish IBI scores across sites and seasons. Line is the null IBI threshold (fish absent).

O 50

ISi

m 4

■ Spring
HSummer
□ Fall

Tenmile Otter_22 Otter_16 Otter_2 OtterJT Home Cr.
Downstream >.

Fish IBI's decreased going downstream on Otter Creek, and the Pre-lmpact Control Site scored
significantly higher than either the Impact or Downstream sites (T-test, p =0.05) (Figure 9).
Within the Great Plains Intermittent Prairie Streams, the species expected to occur most often at
reference condition sites are the fathead minnow and brook stickleback, but the upper Tongue
and Powder River Basins are slightly out of the range of this latter species; therefore, we did not
collect them or expect them to occur at these sites and revised the Observed /Expected (O/E)
Fish Model predictors accordingly. The O/E scores agreed with the IBI scores in most cases,

except for the Otter Creek stream reaches that could be classified as Perennial vs. Intermittent
Prairie Streams (C005) (Table 5).

Figure 8. Fish IBI compared to O/E model (%) scores across sites and seasons.

100

oS 60

i—

O
u
(/» 40

May Jul Oct
Tenmile

May Jul Oct
OTTER 22

May Jul | Oct
OTTER 16

May| Jul | Oct
OTTER 2

May Jul Oct
OTTER JT

May, Jul | Oct
HomeCr

Figure 9. Average fish IBI scores by site type, (a) = no baseline differences between treatments.

Otter Creek mainstem sites 2011

80
70

<u
o 50

u
lO

5 40
!§ 30

LL.

(a)

67.5

(b)

56.7

(c)

45.9

Control

Impact

Downstream

Amphibian and Reptile Incidentals. Overall, Jab|e 6 vertebrates (Species Code) recorded during

eight herpetofauna species were observed, the Otter Creek Surveys. Frequency of Occurrence

(FO) was calculated from the # of site visits detected /
collected in dipnets/seines or incidentally # of visits capable for detection: Herps (n=21) and Fish

(n=15). * = Introduced Species
recorded in conjunction with the fish, habitat

and macroinvertebrate surveys. Otter Creek #22

and #16 were the most diverse sites reporting

five herpetofuana species cumulatively across all

seasons. We reported four amphibian species, of

which Woodhouse's Toad (Bufo woodhousii) had

the highest site occupancy, occurring at six of

seven sites, followed by the Northern Leopard

Frog (Rana pipiens) and Tiger Salamander

(Ambystoma tigrinum) (Figure 10) recorded at

five and four sites, respectively (Table 6). Boreal

Chorus Frog (Pseudacris maculata) was detected

vocally calling at three sites during the spring

visits only and one incidental sighting during a

summer visit. We also recorded four reptile species (in order of site occurrence): Western

Rattlesnake (Crotalus viridis), Painted Turtle (Chrysemys picta) (Figure 10), Terrestrial Garter

Snake (Thamnophis elegans) and Snapping Turtle (Chelydra serpentina) (SOC).

Figure 10. Tiger Salamander (left) from Home (Otter_lA) and Painted Turtle from OtterJT (right).

Herpetofauna

Visits Det

Woodhouse's Toad (BUWO)

0.43

Northern Leopard Frog(RAPI)

0.33

Tiger Salamander (AMTI)

0.24

Boreal Chorus Frog (PSMA)

0.19

Painted Turtle (CHPI)

0.19

Western Rattlesnake (CRVI)

0.19

SnappingTurtle (CHSE)

0.10

Terrestrial Gartersnake (THEL)

0.10

Fish

Lake Chub (LACH)

0.93

Fathead Minnow (FAMI)

0.80

Brassy Minnow (BRMI)

0.80

White Sucker (WHSU)

0.67

Black Bullhead* (BLBU)

0.53

Common Carp* (CARP)

0.53

Green Sunfish* (GRSU)

0.33

Pumpkinseed* (PUMP)

0.33

Sand Shiner (SASH)

0.27

Conclusions

The aquatic community sampling sites chosen for pre-impact baseline data were representative
of the range of stream classes found in the Otter Coal Tracts project area: Ephemeral,
Intermittent and Perennial Prairie Streams. Despite this being an unusually high water year for
the region, stream communities that we sampled across the seasons encompassed the range of
expected species to occur in these stream types, and fish and macroinvertebrate community
assessment scores were similar to biological assessments performed in previous years (Table 7).

Table 7. Otter Creek Temporal Habitat Scores, Fish IBIs and MMIs. Metric Score Ranks (+):
unimpaired, (-): impaired, (=): marginal, (na)= not applicable, taxa group not collected. Spat
relationship in river miles (rm) to them adjacent Coal Tract Study Site

Site Code

Site Name

Spatial
Relation

Date

BLM
PFC

BLM

Hab

Score

Fish
IBI

MT
MMI

Metric
Score
Ranks

ATG_203

Otter Creek at Camp Creek Road

~16 rm ups

7/11/2010

PFC

58.4

+ ,+,+

ATG_235

South Fork Taylor Creek

~13 rm ups

7/11/2010

PFC

73.5

+ ,+,+

ATG_202

Otter Creek at Taylor Creek Road

~12 rm ups

7/11/2010

PFC

36.3

+ ,+,-

ATG_CCC

Otter Creek at CCC Camp USFS

~3 rm ups

7/11/2010

PFC

37.9

+ ,+,=

ATG_201

Otter Creek at Ten mile Cr Road

100m ups

7/11/2010

PFC

44.6

+ ,=,+

OTTER_23

Ten mile Creek @ Denson Ranch

5/10/2011

FAR

36.8

-,+,-

OTTER_23

Ten mile Creek @ Denson Ranch

7/18/2011

FAR

35.2

- , na, -

OTTER_23

Ten mile Creek @ Denson Ranch

10/10/2011

FAR

35.6

-, na,-

OTTER_22

Otter Creek at Ten mile Cr Road

5/10/2011

PFC

66.1

46.3

+ ,+, +

OTTER_22

Otter Creek at Ten mile Cr Road

7/18/2011

PFC

67.3

54.3

+ ,+, +

OTTER_22

Otter Creek at Ten mile Cr Road

10/10/2011

PFC

69.2

65.9

+ ,+, +

OTTER_16

Otter Creek at Ranch Road x

5/19/2011

PFC

62.3

44.4

+ ,+, +

OTTER_16

Otter Creek at Ranch Road x

7/16/2011

PFC

50.7

51.2

+ ,-,+

OTTER_16

Otter Creek at Ranch Road x

10/15/2011

FAR

44.4

46.2

= ,-,+

OTTER_2

Otter Creek at Ranch Road x

7/16/2011

FAR

62.7

=,+,na

OTTER_2

Otter Creek at Ranch Road x

10/15/2011

FAR

63.1

=,+,na

YL_S70REM

Otter Creek at 3mile creek

400m dns

7/18/2000

59.7

na , na , +

OTTERJT

Otter Creek J Trusler site

5/17/2011

PFC

44.9

64.6

+ ,-,+

OTTERJTs

Otter Creek J Trusler site

7/18/2011

PFC

43.8

65.8

+ ,-,+

OTTERJTf

Otter Creek J Trusler site

10/15/2011

PFC

48.9

43.4

+ ,-,+

YL_S0070dn

Otter Creek below Trusler site

300m dns

6/2/2003

56.2

na , na , +

OTTER_lA

Home Creek

5/16/2011

FAR

70.8

57.4

- ,+,+

OTTER_lA

Home Creek

7/17/2011

FAR

70.8

43.2

- ,+,+

OTTER_lA

Home Creek

10/15/2011

FAR

46.5

37.9

/ " / —

Biotic integrity of the upstream control reaches of Otter Creek was initially higher during this
baseline study. One extraordinary finding was the high density and large biomass of fish
inhabiting the stream reach below Trusler's Ranch road crossing (20,000 fish in the 300 m reach

fall survey, 15 fish/m2); this is largely an artifact of the impassible culvert located here and the
fish "stacking up" downstream of this barrier. Density dependent fish anomalies (lesions and
parasites, i.e., yellow grub and anchor worm) are prevalent at this site, indicating the fish are
likely experiencing stress from overcrowding. Benthic macroinvertebrate densities at this site are
low, but, more diverse than other sites, indicating that the fish may be consuming large portions
of the available insect production having a top-down community effect. Outside of coal
extraction, threats to this stream system, which can be managed, include grazing and livestock
use around the riparian areas. Moderate occurrences in these basins can have strong local
effects resulting in sedimentation, stream widening at cattle crossings and loss of functional
channel hydrology. Introductions of game (green sunfish, bullheads or pumpkinseeds) or forage
fish in stock ponds anywhere in the watershed can pose potential problems for native fish as
these introduced fish become permanent residents, outcompete or prey upon the native fish and
contribute to overall community degradation. Diverse aquatic communities with high biological
integrity are usually correlated with good riparian condition and habitat quality (Allen et al.
1997). Thus, effective riparian zone management of cattle grazing would contribute to intact
vegetation buffers and less sediment in the aquatic environment (George et al. 2002). In this
study, macroinvertebrate communities ranked few sites as impaired, even those with an obvious
impaired riparian condition, but the effectiveness of macroinvertebrates in assessing prairie
stream impairment is still under debate in Montana. Community results from the habitat, fish
and macroinvertebrate surveys combined to rank the following sites from highest biological
integrity to lowest within their aquatic ecological classification codes:

Northwestern Great Plains Perennial Prairie Stream (AES code C005)-l) Otter Creek #22, 2)
Otter Creek #2, 3) Otter Creek #16, 4) Otter Creek -J Trusler site

Site Photos

Otter Creek #22 (control) during spring visit: pools (left) and riffle (right)

Otter Creek #2 (impact): fall visit looking downstream to block net (left) and upstream (right).

Site Photos

Otter Creek #16 (impact) spring visit: pool (left) and shallow stream crossing (right).

Otter Creek #16 (impact) during summer visit: downstream pool (left) and drill trucks using the
stream crossing (right).

Site Photos

Otter Creek JT (downstream): summer visit looking downstream (left) and upstream (right)

Northwestern Great Plains Intermittent Prairie Stream-(AES code D005)-l) Home Creek 1A, 2)
Tenmile Creek,

Home Creek (Otter 1A) during the Spring (left) and Summer (right) Visits

^^H^

Site Photos

Tenmile Creek (Otter_23) in the Spring (left) and Summer (right)

Great Plains Intermittent Fishless Prairie Stream (AES code E005)-l) Threemile Creek
Site Photos: Threemile Creek (Otter 3m) during the spring (left) and summer (right) Visits

Literature Cited

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Integrity Across Multiple Spatial Scales. Freshwater Biology 37:149-162.

Barbour, M., J. Gerritsen, B.D. Snyder, and J.B. Stribling. 1999. Rapid Bioassessment Protocols

for Use in Streams and Wadable Rivers: Periphyton, Benthic Macroinvertebrates and Fish,
Second Edition. EPA 841-B-99-002. United States Environmental Protection Agency; Office
of Water: Washington, D.C.

BLM 2008. Standard Methods for Laboratory Sample Sorting Procedures of Macroinvertebrate
Samples. http://usu.edu/buglab/SampleProcessing/labProcedures.cfm Bureau of Land
Management/USU National Aquatic Monitoring Center, Logan, Utah.

BLM 2008b. Standard Methods for Field Surveys of Macroinvertebrate Samples.
http://www.usu.edu/buglab/Monitoring/fieldForms.cfm Bureau of Land
Management/USU National Aquatic Monitoring Center, Logan, Utah.

Bramblett, R. G., T. R. Johnson, A. V. Zale, A. V., and D. Heggem. 2005. Development and

Evaluation of a Fish Assemblage Index of Biotic Integrity for Northwestern Great Plains.
Transactions of the American Fisheries Society 134:624-640, 2005.

Bramblett, R. G., and K. D. Fausch. 1991. Variable Fish Communities and the Index of Biotic

Integrity in a Western Great Plains River. Transactions of the American Fisheries Society
120:752-769.

Dodds, W. K., K. Gido, M. R. Whiles, K. M. Fritz, and W. J. Matthews. 2004. Life on the Edge:
The Ecology of Great Plains Prairie Streams. BioScience 54: 205-216.

DOI Bureau of Land Management 2002. Environmental Assessment.
http://dnrc.mt.gov/Trust/MMB/OtterCreek/2General/TransferDocuments/BLMTransferEA.pdf

Feldman, D. 2006. Interpretation of New Macroinvertebrate Models by WQPB. Draft

Report. Montana Department of Environmental Quality, Planning Prevention and
Assistance Division, Water Quality Planning Bureau, Water Quality Standards
Section. 1520 E. 6 th Avenue, Helena, MT 59620. 14 pp.

George, M.R., R.E. Larsen, N.K. McDougald, K.W. Tate, J.D. Gerlach, Jr., and K.O. Fulgham.

2002. Influence of Grazing on Channel Morphology of Intermittent Streams. J. Range
Management. 55:551-557.

Hawkins, C. P. and R. H. Norris. 2000. Performance of different landscape classifications

for aquatic bioassessments: introduction to the series. Journal of the North American
Benthological Society.l9:3 (367-369).

Holton, G. D., and H. E. Johnson. 2003. A Field Guide to Montana Fishes, 3rd edition. Montana
Fish, Wildlife, and Parks, Helena.

Jessup, B., J. Stribling; and C. Hawkins. 2005. Biological Indicators of Stream Condition in
Montana Using Macroinvertebrates. Tetra Tech, Inc. November 2005 (draft).

Jessup, B. 2006. Ecological Data Application System (EDAS) Version MT 3.3.2k A User's Guide.
Tetra Tech, Inc.

Karr, J. R. 1981. Assessment of Biotic Integrity Using Fish Communities. Fisheries 6(6):21-27.

Lazorchak, J.M., Klemm, D.J., and D.V. Peck (editors). 1998. Environmental Monitoring and

Assessment Program - Surface Waters: Field Operations and Methods for Measuring the
Ecological Condition of Wadeable Streams. EPA/620/R-94/004F. U.S. Environmental
Protection Agency, Washington, D.C.

Montana Department of Environmental Quality (DEQ). 2006. Sample Collection, Sorting, and

Taxonomic Identification of Benthic Macroinvertebrates. Water Quality Planning Bureau.
Standard Operation Procedure (WQPBWQM-009).

Montana Department of Environmental Quality (DEQ). 2006. ADMINISTRATIVE RULES OF
MONTANA 17.30.670. Chapter 30 Surface Water Quality Standards and Procedures.
www.deq.mt.gov/dir/Legal/Chapters/Ch30-06.pdf

Peterson, D.A., Clark, M.L., Foster, Katharine, Wright, P.R., and Boughton, G.K., 2010,

Assessment of Ecological Conditions and Potential Effects of Water Produced From
Coalbed Natural Gas Development on Biological Communities in Streams of the Powder
River Structural Basin, Wyoming and Montana, 2005-08: USGS Scientific Investigations
Report 2010-5124, 84 p. http://pubs.usgs.gov/sir/2010/5124/pdf/SIR10-5124.pdf

Pritchard, D., F. Barret, H. Berg, W. Hagenbuck, R. Krapf, R. Leinard, S. Leonard, M. Manning,

C. Noble, Tippy, D. 1993. Riparian Area Management: A User Guide to Assessing Proper
Functioning Condition. Technical Reference 1737-9. USDI Bureau of Land Management
Service Center. Denver, Colorado. USA. 109 pp.

Stagliano, David, M. 2011. Baseline Assessments for Fish, Macroinvertebrates, and Herpetofauna
in the Headwaters of Otter and Hanging Woman Creeks within the Tongue Powder CBNG
Area. Report to the Bureau of Land Management. Montana Natural Heritage Program,
Helena, Montana. 17 pp. http://mtnhp.org/reports/CBNG TonguePowder.pdf

Stagliano, David, M. 2005. Aquatic Community Classification and Ecosystem Diversity in
Montana's Missouri River Watershed. Report to the Bureau of Land Management.
Montana Natural Heritage Program, Helena, Montana. 65 pp. plus appendices.
http://www.mtnhp.Org/reports.asp#Ecology

Appendix A. Raw data and IBI metric calculation from fish data collected from Otter Creek Coal Tract Sites

Spring 2011

Otter23

Otter22

Otter16

OtterJT

OtterIA

Black Bullhead
Brassy Minnow
Common Carp
Fathead Minnow
Lake Chub
Green Sunfish
Pumpkinseed Sunfish
Sand Shiner
White Sucker

0.0
25.0
0.0
0.0
12.0
0.0
0.0
0.0
0.0

0.0
81.0
0.0
0.0
153.0
0.0
0.0
0.0
6.0

0.0
100.0
4.0
16.0
40.0
0.0
0.0
0.0
20.0

12.5

142.5

20.0

2007.5

5.0

2.5

0.0
37.5
27.5

0.0
0.0
0.0
10.0
20.0
0.0
0.0
0.0
0.0

Total # species
Native Species
Native Families
Total Individuals

2.0
2.0
1.0
37.0

3.0

2.0

240.0

5.0

4.0

2.0

180.0

8.0

5.0

2.0

2255.0

2.0
2.0
1.0
30.0

# Minnow Species Thrive
Proportion of tolerant
individuals

2.0
0.00

2.0
2.50

3.0
22.22

4.0
91.80

2.0
33.33

# Sucker + Catfish Species

0.0

1.0

2.0

0.0

% Insectivorous Minnows

32.4

63.8

22.2

1.9

66.7

# Benthic Invertivore Species

0.0

1.0

0.0

% Litholphilic Spawners

0.0

2.5

11.1

2.9

0.0

% Parental Care

0.00

8.89

89.58

33.33

% Native to Montana

100.0

97.8

98.4

100.0

# Long Lived Species

2.0

1.0

2.0

4.0

1.0

Otter23

Otter22

Otter16

OtterJT

OtterIA

Metrics

Adjust Value

Score

Adjust Value

Score

Adjust
Value

Score

Adjust
Value

Score

Adjust
Value

Score

Numberof Native Fish Species
to Montana

13.6

75.8

9.3

51.8

10.1

56.0

10.8

59.9

13.3

73.7

Numberof Native Fish Families
to Montana

3.1

58.0

3.2

58.7

3.1

57.8

3.1

56.8

3.1

56.7

Proportion of tolerant
individuals

0.0

100.0

2.5

97.4

22.2

76.5

91.8

2.9

33.3

64.7

Numberof Sucker and Catfish
Species

7.1

77.1

4.9

53.3

4.8

51.7

5.6

60.7

6.9

74.7

Proportion out of the Total
Numberof Fish That Were
Insect eating Minnows

32.4

44.5

63.8

87.6

22.2

30.5

1.9

2.6

66.7

91.6

Total Numberof Species That
Prefer to Eat Insects That Live
on the Stream Bottom

5.5

93.1

3.0

51.3

4.9

83.3

4.8

81.0

5.3

90.2

Proportion of the Total
Numberof Fish That Require
Rocks to Lay Eggs

0.0

2.5

3.0

11.1

13.4

2.9

3.5

0.0

Proportion of the Total
Numberof Individuals That Do
Not Require Rocks, But Have
Parental Care of Eggs

0.0

100.0

0.0

100.0

8.9

89.9

89.6

-1.9

33.3

62.1

Proportion of the Total
Numberof Fish Sampled That
Were Native to Montana

100.0

97.8

98.4

98.5

100.0

Numberof Long-Lived Native
Species

10.5

107.4

5.7

58.1

6.5

66.5

8.3

84.9

9.2

94.5

756.0

661.2

623.5

448.9

708.4

IBI Score

75.60

66.12

62.35

44.89

70.84

Appendix A. Raw data an

d IBI metric calculation from fish data collected from Otter Creek Coal Tract Sites

Summer 2011

Otter23

Otter22

Otter16

Otter2

Otter JT

OtterIA

Black Bullhead
Brassy Minnow
Common Carp
Fathead Minnow
Lake Chub
Green Sunfish
Pumpkinseed Sunfish
Sand Shiner
White Sucker

0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0

5.0
2400.0

0.0

0.0
2785.0

0.0

0.0
140.0

0.0
549.0
432.0
3.0
84.0
0.0
3.0
0.0
0.0

7.0

154.0
14.0
56.0
105.0
0.0
7.0
22.0
7.0

2.5

30.0

212.5

2995.0

7.5

2.5

0.0

25.0

107.5

0.0
0.0
0.0
10.0
20.0
0.0
0.0
0.0
0.0

Total # species
Native Species
Native Families
Total Individuals

0.0
0.0
0.0
0.0

4.0

3.0

2.0

5330.0

5.0

3.0

1.0

1071.0

8.0

5.0

2.0

372.0

8.0

5.0

2.0

3382.5

2.0
2.0
1.0
30.0

# Minnow Species Thrive
Proportion of tolerant
individuals

0.0
0.00

2.0
2.72

3.0
40.62

4.0
22.58

4.0
98.15

2.0
33.33

# Sucker + Catfish Species

0.0

2.0

0.0

2.0

0.0

% Insectivorous Minnows

0.0

52.3

7.8

34.1

1.0

66.7

# Benthic Invertivore Species

0.0

1.0

0.0

1.0

0.0

% Litholphilic Spawners

0.0

2.6

0.0

7.8

3.9

0.0

% Parental Care

0.00

0.09

0.28

16.94

88.62

33.33

% Native to Montana

0.0

99.9

59.4

92.5

93.6

100.0

# Long Lived Species

0.0

1.0

2.0

1.0

4.0

1.0

Otter23

Otter22

Otter16

Otter2

Otter JT

OtterIA

Metrics

Adjust
Value

Score

Number of Native Fish Species
to Montana

11.6

64.7

9.3

51.8

9.1

50.4

11.1

61.5

10.8

59.9

13.3

73.7

Number of Native Fish Families
to Montana

2.1

39.5

3.2

58.7

2.1

39.4

3.1

57.8

3.1

56.8

3.1

56.7

Proportion of tolerant
individuals

0.0

100.0

2.7

97.1

40.6

57.0

22.6

76.1

98.2

-3.9

33.3

64.7

Number of Sucker and Catfish
Species

7.1

77.1

5.9

64.2

3.8

40.8

5.8

62.6

5.6

60.7

6.9

74.7

Proportion out of the Total
Number of Fish That Were
Insect eating Minnows

0.0

' 0.0

52.3

71.8

7.8

10.8

34.1

46.9

1.0

' 1.3

66.7

91.6

Total Number of Species That
Prefer to Eat Insects That Live
on the Stream Bottom

5.5

93.1

4.0

68.3

4.9

83.3

4.9

83.3

4.8

81.0

5.3

90.2

Proportion of the Total
Number of Fish That Require
Rocks to Lay Eggs

0.0

2.6

3.2

0.0

7.8

9.4

3.9

4.7

0.0

Proportion of the Total
Number of Individuals That Do
Not Require Rocks, But Have
Parental Care of Eggs

0.0

100.0

0.1

99.9

0.3

99.7

16.9

80.7

88.6

-0.8

33.3

62.1

Proportion of the Total
Number of Fish Sampled That
Were Native to Montana

0.0

99.9

59.4

92.5

93.6

100.0

Number of Long- Lived Native
Species

8.5

86.9

5.7

58.1

6.5

66.5

5.5

56.3

8.3

84.9

9.2

94.5

561.4

673.0

507.4

627.2

438.3

708.4

IBI Score

56.14

67.30

50.74

62.72

43.83

70.84

Appendix A. Raw data and IBI metric calculation from fish data collected from Otter Creek Coal Tract Sites

Fall 2011

Otter23

Otter22

Otter16

Otter2

Otter JT

OtterIA

Black Bullhead
Brassy Minnow
Common Carp
Fathead Minnow
Lake Chub
Green Sunfish
Pumpkinseed Sunfish
Sand Shiner
White Sucker

0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0

3.0
588.0

0.0

3.0
1059.0

3.0

0.0

15.0

186.0
51.0
1314.0
12.0
9.0
6.0
30.0
0.0
45.0

7.0
364.0
49.0
35.0
84.0
0.0
0.0
0.0
7.0

5.0

65.0

137.5

17810.0

102.5

2.5

10.0

2755.0

10.0

0.0
0.0
0.0
10.0
0.0
0.0
0.0
0.0
0.0

Total # species
Native Species
Native Families
Total Individuals

0.0
0.0
0.0
0.0

7.0

4.0

2.0

1674.0

8.0

4.0

2.0

1653.0

6.0

4.0

2.0

546.0

9.0

5.0

2.0

20897.5

1.0
1.0
1.0
10.0

# Minnow Species Thrive
Proportion of tolerant
individuals

0.0
0.00

3.0
1.43

3.0
94.56

3.0
17.95

4.0
85.97

1.0
100.00

# Sucker + Catfish Species

0.0

2.0

0.0

% Insectivorous Minnows

0.0

63.3

0.5

15.4

13.7

0.0

# Benthic Invertivore Species

0.0

1.0

0.0

% Litholphilic Spawners

0.0

0.9

2.7

1.3

13.2

0.0

% Parental Care

0.00

0.36

11.98

7.69

85.25

100.00

% Native to Montana

0.0

99.5

7.1

89.7

99.3

100.0

# Long Lived Species

0.0

4.0

1.0

Otter23

Otter22

Otter16

Otter2

OtterJT

OtterIA

Metrics

Adjust
Value

Score

Number of Native Fish Species
to Montana

11.6

64.7

10.3

57.4

10.1

56.0

10.1

56.0

10.8

59.9

12.3

68.2

Number of Native Fish Families
to Montana

2.1

39.5

3.2

58.7

3.1

57.8

3.1

57.8

3.1

56.8

3.1

56.7

Proportion of tolerant
individuals

0.0

100.0

1.4

98.5

94.6

-0.1

17.9

81.0

86.0

9.0

100.0

-5.8

Number of Sucker and Catfish
Species

7.1

77.1

5.9

64.2

5.8

62.6

5.8

62.6

5.6

60.7

6.9

74.7

Proportion out of the Total
Number of Fish That Were
Insect eating Minnows

0.0

63.3

86.9

0.5

0.7

15.4

21.1

13.7

18.8

0.0

Total Number of Species That
Prefer to Eat Insects That Live
on the Stream Bottom

5.5

93.1

4.0

68.3

4.9

83.3

4.9

83.3

4.8

81.0

5.3

90.2

Proportion of the Total
Number of Fish That Require
Rocks to Lay Eggs

0.0

0.9

1.1

2.7

3.3

1.3

1.5

13.2

16.0

0.0

Proportion of the Total
Number of Individuals That Do
Not Require Rocks, But Have
Parental Care of Eggs

0.0

100.0

0.4

99.6

12.0

86.4

7.7

91.3

85.2

3.0

100.0

-13.7

Proportion of the Total
Number of Fish Sampled That
Were Native to Montana

0.0

' 0.0

99.5

7.1

' 7.1

89.7

89.8

99.3

100.0

Number of Long-Lived Native
Species

8.5

86.9

5.7

58.1

8.5

87.0

8.5

87.0

8.3

84.9

9.2

94.5

561.4

692.2

444.2

631.4

489.4

464.9

IBI Score

56.14

69.22

44.42

63.14

48.94

46.49

Appendix C . Habitat and Water Quality

Parameters measured for the Otter Creek sites visited

NA =

not visited or sampled during this visi

, dry.

OTTER_23

OTTER_

OTTER_16

OTTER_

OTTER_JT

OTTERJA

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

May

Jul

Oct

Water Temp©

17.4

30.8

3.8

12.3

28.5

7.5

12.9

24.6

8.8

14.5

26.6

9.2

13.1

26.8

10.7

18.6

27.8

9.1

Conductivity (us/cm)

1880

>4,000

3660

3790

3590

>4,000

3920

3790

170

3890

3700

3860

3608

3540

1950

>4,000

3209

8.2

8.4

8.2

8.1

7.6

7.8

8.2

8.1

8.2

PFC

FAR

PFC

FAR

PFC

FAR

BLM HBI

Avg wetted width (m)

6.2

0.6

8.7

8.2

8.6

11.9

12.1

11.2

1.8

4.2

2.8

5.0

4.8

4.6

2.4

2.1

2.0

Avg Left CHD (cm)

103

104

Avg Center CHD (cm)

136

128

106

Avg Right CHD (cm)

% Fines in Reach

100

% Gravel Reach

% Cobble Reach

Livestock Use (CPI)

Avg. Riparian Shade

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