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AQUATIC EVALUATION

AND INSTREAM FLOW RECOMMENDATIONS

FOR SELECTED REACHES OF GERMAN GULCH CREEK

SILVER BOW COUNTY, MONTANA

STATE DOCUMENTS COLLECTION

OCT 1 5 1985

MONTANA STATE LIBRARY 1515 E. 6th AVE. Prepared by HELENA, MONTANA 59620

MONTANA DEPARTMENT OF FISH, WILDLIFE AND PARKS 8695 Huffine Lane, Bozeman, MT 59715

Prepared for

MONTANA DEPARTMENT OF STATE LANDS Helena, MT 59601

December 1984

MONTANA STATE LIBRARY

S 333.952 F2aei 19B4C.1

Aquatic evaluation and instream flow rec

3 0864 00051568 7

JO 3

ACKNOWLEDGEMENTS

Able assistance in the collection and compilation of field data was provided by Bruce Rehwinkel, Jim Brammer, Dick Oswald, and Fred Nelson. The figures in this report were prepared by Sharon Tiller. The University of Montana Genetics Laboratory performed electrophoretic analysis of westslope cutthroat trout. Bruce Rehwinkel and Dick Vincent conducted the fish population analysis. Fred Nelson performed the computer analysis of the cross-sectional data for the instream flow analysis. Dick Oswald conducted and wrote the aquatic invertebrate portion of the evaluation. Glen Phillips conducted and wrote the water quality portion of the evaluation with the assistance of Kurt Hill. Duane Klarich of Systems Technology, Inc. conducted and wrote the periphyton portion of the evaluation. The manuscript was compiled by Jerry Wells and Fred Nelson and prepared by EXECUTEC documentation service and Wanda Myers.

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TABLE OF CONTENTS

Page

LIST OF TABLES AND FIGURES ill

INTRODUCTION 1

FISH POPULATIONS 2

Methods 2

Results 4

Durant Section 4

Below Beefstraight Creek Section 4

Below Edward Creek Section 5

Discussion 5

INSTREAM FLOW RECOMMENDATIONS 7

German Gulch-Below Beefstraight Creek 8

German Gulch-Below Edward Creek 9

Discussion of Flow Recommendations 10

WATER QUALITY 12

Water Quality Methods 12

Water Quality Results 12

Chlorophyll Methods 13

Chlorophyll Results 14

PERIPHYTON 15

Periphyton Methods 15

Periphyton Results 17

AQUATIC MACROINVERTEBRATES 24

Study Area 24

Methods 24

Results 25

Species Richness and Community Composition 25

Macroinvertebrate Abundance 26

REFERENCES 28

TABLES AND FIGURES 31

APPENDIX A

APPENDIX B

APPENDIX C

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LIST OF TABLES AND FIGURES

Table Page

1 Summary of electrof ishing survey data collected for the 1000-ft Durant Section of German Gulch Creek (T3N, R10W,

SI 2, 13) on July 26 and August 7, 1984. 31

2 Estimated standing crop of trout in the 1000-ft Durant Section of German Gulch Creek (T3N, R10W, S12.13) on

July 26, 1984 (80% confidence intervals in parentheses). 31

3 Average length and weight of cutthroat and brook trout by age class in the Durant Section of German Gulch Creek

(T3N, R10W, S12.13). 32

4 Summary of electrof ishing survey data collected for the 1000-ft Below Beefstraight Creek Section of German Gulch

Creek (T3N, R10W, S26) on July 26 and August 6, 1984. 32

5 Estimated standing crop of trout in the 1000-ft Below Beefstraight Creek Section of German Gulch Creek (T3N, R10W, S26) on July 26, 1984 (80% confidence intervals in parentheses). 33

6 Average lengths and weights of westslope cutthroat and brook trout by age class in the Below Beefstraight Creek

Section of German Gulch Creek (T3N, R10W, S26) . 33

7 Summary of electrof ishing survey data collected for the 1000-ft Below Edward Creek Section of German Gulch Creek

(T3N, R10W, S34) on July 26 and August 6, 1984. 34

8 Estimated standing crop of trout in the 1000-ft Below Edward Creek Section of German Gulch Creek (T3N, R10W, S34) on

July 26, 1984 (80% confidence intervals in parentheses). 34

9 Average lengths and weights of westslope cutthroat and brook trout by age class in the Below Edward Creek Section

of German Gulch Creek (T3N, R10W, S34) . 35

10 Estimated standing crops of trout in 1000-ft study sections of streams in the German Gulch vicinity (P denotes presence in numbers too low to make reliable estimates) (Data from

Oswald 1981) 36

11 High flow recommendations based on the dominant discharge/ channel morphology concept (USGS flow gage record data) . 37

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LIST OF TABLES AND FIGURES (continued) Table Page

12 Instreatn flow recommendations (cfs) for German Gulch at the Below Beef straight Creek study site compared to the 10th,

50th and 90th percentile monthly flows (cfs). 38

13 Means, ranges, and standard deviations of chemical and physical parameters for German Gulch Creek, Montana (samples collected on July 18, August 6, and September 4, 1984). 39

14 Concentrations of chlorophyll a, b, and c (ug/cm~) for

three locations in German Gulch Creek, July 18, 1984. 40

15 Floral richness and Shannon-Wiener diatom diversity characteristics of natural substrate periphyton scrapings

from three locations on German Gulch Creek, July 18, 1984. 41

16 Analysis of macroinvertebrate species richness (numbers of separable taxa) observed at the Upper, Middle and Lower

sample sites on German Gulch Creek in May and August, 1984. 42

17 Analysis of aquatic macroinvertebrate abundance in square foot samples collected at the Upper, Middle and Lower

sample sites on German Gulch Creek in May and August, 1984. 42

18 Systematic checklist and distribution among sample sites (Upper, Middle and Lower) of aquatic macroinvertebrates collected from German Gulch Creek in May and August, 1984. 43

19 Numbers of macroinvertebrates collected per square foot Surber sample from the Upper Site on German Gulch Creek

in May and August, 1984. 46

20 Numbers of macroinvertebrates collected per square foot Surber sample from the Middle Site on German Gulch Creek

in May and August, 1984. 48

21 Numbers of macroinvertebrates collected per square foot Surber sample from the Lower Site on German Gulch Creek

in May and August, 1984. 50

Figures

1 Map of German Gulch. 52

2 The relationship between wetted perimeter and flow for a composite of five riffle cross-sections in Cerman Gulch

below the confluence of Beefstraight Creek. 53

3 The relationship between wetted perimeter and flow for a composite of five riffle cross-sections in German Gulch

below the confluence of Edward Creek. 54

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INTRODUCTION

This study was initiated to provide the State of Montana with baseline aquatic resource data on German Gulch Creek and to provide recommended minimum instream flow to protect this resource. The study was funded by the Montoro Gold Company via the Montana Department of State Lands utilizing funds collected under MEPA.

German Gulch Creek is a tributary of Silver Bow Creek, which in turn flows into the Clark Fork River. This study was initiated in response to a proposed surface mine, ore processing plant, and tailings disposal facility in the German Gulch drainage by the Montoro Gold Company of Reno, Nevada.

Information provided in this report includes quantification of fish populations, quantification of instream flows necessary for maintaining the existing fishery resource, and baseline water quality, periphyton and macroinvertebrate data.

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FISH POPULATIONS

Methods

Fish populations in the study sections were sampled using a bank electro- fishing unit basically consisting of a 110-v Kawasaki gas generator, a Fisher shocker box, a 500-ft cord, a stationary negative electrode, and a hand-held mobile positive electrode. A mild electric shock temporarily immobilizes the fish located in the immediate vicinity of the positive electrode, allowing them to be dip netted. The fish capturing efficiency of the unit is highly variable, since efficiency rates are influenced by stream size, the magnitude of the flow, water clarity, specific conductance, water temperature, cover types, and the species and size of the fish.

The fish population was estimated using a mark-recapture method which allows for the estimation of the total numbers and pounds (the standing crop) of fish within a stream section. For German Gulch, standing crop estimates were obtained for three 1000-f t study sections (Figure 1) .

The standing crop estimates require at least two electrof ishing runs through each study section. During the first (marking) run, all captured fish are anesthetized, marked with a partial caudal fin clip so they can be later identified, and released after individual lengths and weights are recorded. It is desirable to make the second (recapture) run at least two weeks after the marking run. This two-week period allows the marked fish to randomly redistribute themselves throughout the population. During the recapture run, all captured fish are again anesthetized and released after the lengths and weights of all new (unmarked) fish, and the length only of all marked fish,

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are recorded. The population estimate is basically obtained using the formula

*■¥

where P = estimated number of fish,

M = number of initially marked individuals,

C = number of marked and unmarked fish collected during the recapture run, and

R = number of marked fish collected during the recapture run. This formula, although somewhat modified in its final form for statistical reasons, is the basis of the mark-recapture technique.

The numbers of fish were estimated by length groups. Those 0.5-inch length intervals having similar or equal recapture efficiencies comprise a length group. This grouping is necessary because recapture efficiencies are dependent on fish size. Generally, electrof ishing is more effective for capturing larger fish due to their greater surface area and higher visibility when in the electrical field. Because recapture efficiencies are length- related, the number of fish must be estimated by length groups, then added to obtain the total estimate. Generally, at least seven recaptures are needed per length group in order to obtain a statistically valid estimate.

Pounds of fish are obtained by multiplying the average weight of the fish within each length group by the estimated number, then adding to obtain the total pounds. Estimates can also be obtained for different age groups of fish. This mark-recapture technique, which is thoroughly discussed by Vincent (1971 and 1974), has been adapted for computer analysis by the Montana Department of Fish, Wildlife and Parks (MDFWP) .

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Results Durant Section

A 1000-ft section of German Gulch Creek near the confluence with Silver Bow Creek was electrof ished on July 26 and August 7, 1984. Game fish captured were westslope cutthroat trout, brook trout and brown trout. No non-game fish were captured. Table 1 summarizes the electrof ishing survey data for the Durant Section.

The standing crop of trout in this section was estimated using a mark- recapture method (Table 2). This section supports about 346 trout weighing 42 pounds. Westslope cutthroat trout accounted for 67% of the total trout numbers and 76% of the total biomass; brook trout accounted for 33% of the trout numbers and 24% of the biomass.

Average lengths and weights of westslope cutthroat and brook trout by age class are shown in Table 3.

Below Beefstraight Creek Section

A 1000-ft section of German Gulch Creek below the confluence of Beef- straight Creek was electrof ished on July 26 and August 6, 1984. Game fish captured were westslope cutthroat trout and brook trout. No non-game fish were captured. Table 4 summarizes the electrof ishing survey data for this section.

The standing crop of trout in this section was estimated using a mark- recapture method (Table 5). This section supports about 301 trout weighing 33 pounds. Westslope cutthroat trout accounted for 43% of the total trout numbers and 64% of the total trout biomass; brook trout accounted for 57% of the trout numbers and 36% of the biomass.

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Average lengths and weights of wcstslope cutthroat and brook trout bv age class are shown in Table 6.

Below Edward Creek Section

A 1000-ft section of German Gulch Creek below the confluence of Edward Creek was electrof ished on July 26 and August 6, 1984. Game fish captured were westslope cutthroat trout and brook trout. No non-game fish were captured. Table 7 summarizes the electrof ishing survey data for the Below Edward Creek Section.

The standing crop of trout in this section was estimated using a mark- recapture method (Table 8). This section supports about 209 trout weighing 16 pounds. Westslope cutthroat trout accounted for 80% of the total trout numbers and 88% of the biomass; brook trout accounted for 20% of the trout numbers and 12% of the biomass.

Average lengths and weights of westslope cutthroat and brook trout by age class are shown in Table 9.

Discussion

German Gulch Creek supports a unique and productive fishery. Of primary significance is the presence of a healthy population of genetically-pure westslope cutthroat trout. Tests conducted by the University of Montana Genetics Laboratory confirmed both the purity of this population and genetic distinctions from other populations of westslope cutthroat trout that have been examined (see Appendix A) .

Westslope cutthroat trout arc classified as a species of special concern by the State of Montana due to declining numbers, loss of habitat and inter- breeding with other species. Pure westslope populations have been documented

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for only 25 Montana streams, representing 1.1% of the historic range (Liknes 1984) . Liknes speculates that approximately 4% of the historic Montana range may still be occupied by pure westslope populations. A perusal of the popu- lation densities of pure-strain westslope cutthroat described by Liknes suggests German Gulch Creek supports one of the highest biomasses per stream of any of the pure westslope streams in Montana.

The trout population of German Gulch Creek is compared with those of 13 streams found on the adjoining Mount Haggin Wildlife Management Area in Table 10. German Gulch supports the second highest biomass of all of these streams, and the sixth highest numbers of trout. While German Gulch and Willow Creek are the only two streams in the area supporting cutthroat populations, the cutthroat population of Willow Creek has been determined to be of the Yellowstone strain (Oswald 1981).

The numbers, biomass and genetic purity of the westslope cutthroat population indicate a valuable fishery resource. Given the rarity of pure- strain westslope cutthroat trout populations and the presence of a biological barrier downstream (Silver Bow Creek) to prevent upstream migration and potential introgression of rainbow trout, every effort should be made to protect and enhance this population.

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INSTREAM FLOW RECOMMENDATIONS

The instream flows needed to maintain the fish populations of German Gulch at their current level were quantified using the wetted perimeter/ inflection point method (Nelson 1984) (see Appendix B) . Basically, the method provides a range of flows from which a single recommendation is selected. The flow at the high end of the range (the flow at the uppermost inflection point on the wetted perimeter-flow curve) is intended to maintain the high level of aquatic habitat potential. High level aquatic habitat potential is that flow regime which will consistently produce abundant, healthy and thriving aquatic populations. In the case of game fish species, these flows would produce abundant game fish populations capable of sustaining a good to excellent sport fishery for the size of stream involved. For rare, threatened or endangered species, flows to accomplish the high level of aquatic habitat maintenance would: I) provide the high population levels needed to ensure the continued existence of that specie, or 2) provide the flow levels above those which would adversely affect the specie.

The flow at the low end of the range (the flow at the lowermost inflection point on the wetted perimeter-flow curve) provides for a low level of aquatic habitat potential. Flows to accomplish a low level of aquatic habitat maintenance would provide for only a low population of the species present. In the case of game fish species, a poor sport fishery could still be provided. For rare, threatened or endangered species, populations would exist at low or marginal levels. In some cases, this flow level would not be sufficient to maintain certain species.

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The final recommendation is selected from this range of flows on the basis of the stream resource rating. The critical component of this rating is the fish population data. A marginal or poor fishery would likely justify a flow recommendation at or near the lower inflection point unless other considerations, such as the presence of species of special concern, warrant a higher flow. In general, only streams with exceptional resident fish popu- lations or those providing crucial spawning and/or rearing habitats for migratory populations would be considered for a recommendation at or near the upper inflection point.

Because German Gulch supports exceptionally high numbers of genetically pure westslope cutthroat trout, a species of special concern in Montana, the flow at the uppermost inflection point on the wetted perimeter-flow curve is recommended for the period of June 16 through May 15.

For the high flow or snow runoff period of May 16 through June 15, the dominant discharge/channel morphology concept (Montana Department of Fish and Game 1979) was used to derive instream flow recommendations. The high flow recommendations are intended to flush the annual accumulation of bottom sediments and to maintain the existing channel morphology.

Recommendations were derived for two sites on German Gulch as described in the following sections.

German Gulch - Below Beefstraight Creek.

Cross-sectional measurements for use in the wetted perimeter/inflection point method were made in a 96-ft section of German Gulch (SW, NW, NE, Sec. 26, T3N, R10W) located downstream from the confluence of Beefstraight Creek (Figure 1). Five riffle cross-sections were established in this section.

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The wetted perimeter (WETP) computer program was calibrated to field data collected at flows of 13.3, 34.2 and 72.6 cfs.

The relationship between wetted perimeter and flow for the composite of five riffle cross-sections is shown in Figure 2. A prominent upper inflection point occurs at an approximate flow of 12 cfs. A flow of 12 cfs is therefore recommended for the low flow period of June 16 through May 15.

For the high flow or snow runoff period of May 16 through June 15, the dominant discharge/channel morphology concept was applied using USGS flow records for the gage on German Gulch (No. 12323500) located 0.5 miles upstream from the mouth. These high flow recommendations are shown in Table 11.

German Gulch - Below Edward Creek.

Cross-sectional measurements for use in the wetted perimeter/inflection point method were made in an approximate 30-ft section of German Gulch (SW, NW, SE, Sec. 34, T3N, R10W) located downstream from the confluence of Edward Creek (Figure 1). Five riffle cross-sections were established in this section. The WETP computer program was calibrated to field data collected at flows of 2.7, 9.4 and 25.3 cfs.

The relationship between wetted perimeter and flow for the composite of five riffle cross-sections is shown in Figure 3. A prominent upper inflection point occurs at an approximate flow of 2.5 cfs. A flow of 2.5 cfs is there- fore recommended for the low flow period of June 16 through May 15.

Flow recommendations for the higli flow period cannot be derived due to the absence of long-term USGS gage records for this site.

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Discussion of Flow Recommendations

A policy of the MDFWP when deriving flow recommendations for unregulated mountain streams supporting fish is to prohibit flow depletions in winter. The justification for protecting winter flows is primarily based on the fact that winter is the period most detrimental to trout survival in mountain streams exposed to icing and other severe weather conditions. For these streams, the harsh winter environment ultimately limits the numbers and pounds of trout that can be maintained indefinitely by the aquatic habitat. Winter flow depletions would only serve to aggravate an already stressful situation, leading to even greater winter losses and the possible devastation of fish populations.

The fact that the flows in Montana's mountain streams are lowest in the winter further justifies the policy of protecting winter flows. The assump- tion that more water provides space for more fish has led to the well-accepted conclusion that the period of lowest stream flows is most limiting to fish. The coupling of the low flow period with harsh winter weather conditions, as occurs in Montana, greatly increases the severity of the stream environment in winter.

The recommended instream flows for German Gulch will preclude all water depletions in winter (November through March) and some other periods as well. This is demonstrated in Table 12, which compares the flow recommendations for the Below Beefstraight Greek study site to the 10th, 50th and 90th percentile monthly flows at the USGS gage located 0.5 miles upstream from the mouth. The 10th, 50th and 90th percentile flows provide a measure of stream flows during a very wet, typical and drought year, respectively.

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During a very wet year (10th percentile flows), the recommendations equal or exceed the available flows for the months of October through March. Therefore, water would be unavailable for consumptive uses during these six months. During a typical or normal water year (50th percentile flows), the recommendations equal or exceed the available flows for the months of August through March, making water unavailable for consumptive uses during these eight months. During a drought year (90th percentile flows), the recommen- dations exceed the available flows for all months, thus preventing depletions year-round .

Given the extremely high aquatic resource value of German Gulch and the Department's policy of recommending flows that will maintain the fisheries resource at its present level, lesser recommendations cannot be justified for German Gulch.

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WATER QUALITY Water Quality Methods

Water quality of German Gulch Creek was monitored on July 18, August 6, and September 4, 1984. Locations sampled were downstream from the confluence with Edward Creek, downstream from the confluence with Beefstraight Creek, and near the mouth.

Water temperature and electrical conductivity were measured in the field. Surface grab samples were also taken and were later analyzed for calcium, magnesium, bicarbonate, sulfate, nitrate and nitrite (as N) , hardness (as CaCO ) , zinc, iron, and copper. Finally, a depth integrated sample was taken and total suspended solids concentration was later determined.

Metals samples were acidified in the field with concentrated nitric acid; nutrient samples were preserved with sulfuric acid. Standard procedures were used for all analytical measurements (APHA 1975). The Laboratory Division of the Montana Department of Health and Environmental Sciences, an EPA-certif ied laboratory, performed the laboratory analyses.

Water Quality Results

The quality of water in German Gulch Creek is presently excellent (Table 13). Calcium is the predominant cation and bicarbonate is the predominant anion. The upper reaches in the vicinity of Edward Creek are relatively low in hardness and alkalinity. Below Beefstraight Creek, both the alkalinity and hardness more than doubled in concentration. Because of the above, pH increased from an average of 7.80 below Edward Creek to 8.30 near the mouth.

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All analyzed metals were present at low concentrations. Zinc and copper concentrations were near or below detection limits on all three sampling dates; iron concentrations were also low. Concentrations of all three metals were well below established criteria for protection of aquatic life (EPA 1976). Similarly, concentrations of nitrate and nitrite (as nitrogen) were near or below detection.

Water quality concerns raised in association with the proposed mine include acid mine drainage, metals pollution, and increased nutrient additions. The relatively low buffering capacity and hardness of the upper reaches of German Gulch Creek render it vulnerable to acid mine drainage and metals pollution if they were to occur. Usage of nitrogenous blasting compounds at the mine could also significantly increase nutrient loading in the drainage.

Chlorophyll Methods

Natural stream substrates (small rocks having dimensions on the order of 3 to 9 cm length, 2 to 5.5 cm width, and 1 to A cm height) with attached periphyton were collected on July 18, 1984 from German Gulch Creek near Butte. Samples were collected from the same three locations chosen for water monitor- ing. Rocks were randomly removed from the stream bottom and were placed in pint canning jars; typically, five rocks were placed in each jar. The jars were then capped, labeled, and wrapped in aluminum foil to prevent light from entering. Jars were transferred in ice to the laboratory where the samples were frozen to prevent breakdown of chlorophyll.

Jars were later removed from the freezer and a known volume of 90% v/v acetone was added to each. The jars were then recapped and stored for 21 to 22.5 hours under refrigerated conditions (occasional agitation was provided)

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to provide time for the chlorophyll and other pigments to leach into the acetone. Previous work has shown that 90% of the periphytic pigments are leached into solution after 20 to 24 hours (Weber et al 1980). Next, an aliquot of the acetone was transferred to a curette and absorbance was measured using a Bausch and Lomb Spectronic 70 Spectrophotometer. Finally, surface area of the rocks was estimated by the method of Kaiser et al (1977), and periphyton standing crop was estimated via the chlorophyll levels accord- ing to the chromatic equations that are presented in Weber et al (1980).

Chlorophyll Results

In general, there was good agreement between replicates from all three locations (Table 14). The stream reach below Beef straight Creek appears to be less productive than either of the other two sampling locations. Greatest production of periphytic biomass occurred near the mouth.

Periphyton productivity of German Gulch Creek is relatively high compared to other Montana streams (Ingman et al 1979, Bahls et al 1981), and was in a range similar to that reported for the Yellowstone River near Billings

(Klarich 1976). Estimated average standing crop of chlorophyll for Montana

2 waters (assuming an asymptote at 35 days) is 1 . 7 ug Chi a/cm . Periphyton

2 standing crops in German Gulch below Edward Creek (3.19 ug CHI a/cm ) and near

2 the mouth (4.16 ug Chi a/cm ) were well above this average. Nitrogen

compounds measured during the water monitoring were present at very low

concentrations. Perhaps German Gulch Creek is nitrogen limited.

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PERIPHYTON Periphyton Methods

Periphyton samples were collected from each of the three German Gulch Inventory sites by scraping natural stream bottom materials (primarily gravel and larger rock substrates) with a sharp utensil. The scrapings were then immediately transferred on site to small, labelled vials, and they were preserved with Lugol's solution for transport and storage until laboratory analyses could be undertaken of the gulch's periphyton communities.

The laboratory evaluations of the natural substrate scrapings from the German Gulch stations were separately initiated by first removing the obviously non-diatomaceous plant matter from the vials for a microscopic taxonomic examination and generic identification. As an added step, temporary wet mounts of a small portion of the less well-defined part of the same collections were prepared to further check for the presence of any soft-bodied algal filaments and cells. This accessory manipulation led to the initiation of supplemental generic identifications, and qualitative abundance estimates were also made for each of the soft-bodied algal forms that were encountered in the three project samples. Subsequently, permanent mounts were prepared from the scrapings from each of the sites for use in conducting the diatom species and variety taxonomic assessments and for use in completing the diatom percent relative abundance (PRA) tabulations.

To prepare the permanent slides for each of the project's periphyton collections, aliquots of the collected periphytic materials from the three sites were separately oxidized and treated in accord with the procedures that

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are presented in Standard Methods (American Public Health Association et al 1975). This was done to clean the diatom frustules for the purpose of facili- tating the essential taxonomic work, and the cleansing technique resulted in the production of three randomly strewn mounts that are directly amenable to a microscopic evaluation. These slides were then surveyed microscopically in a preliminary fashion in order to develop taxa listings of the stations' diatom assemblages. This particular analytical step required the application of a taxonomic keying effort by referencing the appropriate literature sources (e.g., Patrick and Reimer 1966), and the diatoms were identified to the generic, specific, and varietal systematic levels as this proved to be feasible in any particular case.

Following such preliminary applications, the diatoms on each of the slides were partially and randomly counted by taxa in a formal manner until a total of about 415 frustules had been tabulated for each of the preparations. The modified short-count approach that was used has been described by Weber (1973), and PRA values were ultimately calculated for each of the diatom taxa that had been formally counted from any one of the permanent slides. However, a "trace" designation had to be assigned to those diatoms of a mount that were spotted in the various preliminary scans but then not actually tabulated during the formal counts.

The raw data of the inventory's periphyton community analyses therefore consist of the diatom and non-diatom taxa listings plus the diatom's PRA values and the qualitative abundance estimates of the soft-bodied forms. These raw data can be obtained from the collecting agency. But as a final analytical step, the project's diatom count data were later reduced and refined for the interpretive and descriptive needs of this report by calcu- lating Shannon-Wiener diversity and index values for each of the station's

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periphyton collections. The mathematical manipulations that are involved in producing such indices are extensively described in Weber (1973).

Periphyton Results

Four soft-bodied algal genera (the blue-green Nostoc and Oscillatoria, and the green algae Closterium and Ulothrix) and a minimum of 82 species and varieties of diatoms were identified through the three German Gulch samples. A list of periphyton species and calculations of percent relative abundance for the German Gulch study sites are included in Appendix C. A breakdown of the taxa numbers by site and the diversity and equitability characteristics of the stations are presented in Table 15. The number of different taxa that were recognized in the scrapings from a site provides a general indication of the stations' floral richness, while the diversity and equitability expres- sions function to illustrate the overall structure of a periphyton community.

Of the non-diatomaceous algae, Oscillatoria and Closterium were found to be relatively rare through all three of the project sites, while Nostoc was seen to be fairly abundant at the upper and middle locations on the gulch but non-abundant in its lower reach. In opposition, Ulothrix was observed to be quite common at the gulch's downstream station but rare at its upstream locales. However, the low or high abundances of these particular soft-bodied forms do not necessarily point to the existence of any distinct environmental problems; rather, Nostoc, as one example, is oftentimes prevalent in waters that can be described as having a largely pristine nature (Ingman et al 1979).

Of the many diatom taxa, a significant proportion (82%) proved to be relatively uncommon components of the gulch's periphytic associations with mean PRA's across the stations at less than 2.0%. But the low abundances of this particular group of diatoms are again not necessarily suggestive of

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environmental perturbations since a large coterie of miscellaneous species is almost always typical of a healthy ecological system. At the same time, the occurrence of a small selection of abundant forms is also descriptive of most periphyton communities. In keeping with this theme, fifteen of the German Gulch diatom taxa with mean PRA values in excess of 2.0% can be classified as being conspicuous and common periphytic representatives of the project water- way by demonstrating high abundances at one or more of the sites.

The more common of the German Gulch diatoms can be listed as follows in the order of their relative abundance levels and their mean PRA values: Fragilaria vaucheriae (11.1%), Gomphonema olivaceum (9.1%), Cocconeis placentula (9.1%), Achnanthes lanceolata (9.0%), Nitzschia dissipata (6.9%), Navicula cryptocephala variety veneta (5.4%) , Hannaea arcus (3.8%) , Fragilaria pinnata (3.1%), Rhoicosphenia curvata (3.1%), Achnanthes minutissima (2.8%), Synedra ulna (2.5%), Nitzscia kutzingiana (2.5%), Cymbella affinis (2.3%), Diatoma hiemale variety mesodon (2. 1%) , and Navicula tripunctata (2. 1%) .

Ten examples of the 67 less common German Gulch diatoms with some recorded in trace (t) amounts can be listed as follows: Amphipleura pellucida (0.07%), Cymbella sinuata (1.3%), Didymosphenia geminata (t) , Eunotia perpu- silla (0.17%), Meridian circulare (0.7%), Navicula lanceolata (t) , Nitzschia palea (1.5%), Pinnularia borealis (0.1%), Stauroneis smithii (t) , and Suri- rella ovata (1.0%). Furthermore, extremely large numbers of diatom species and varieties (and genera) were not observed in the German Gulch samples (e.g., Biddulphia laevis, Epithemia sorex, and Gyrosigma acuminatum) . However, such broad-ranging absences can be judged as commonplace through all of the earth's biological assemblages, and the occurrence of missing taxa thereby is certainly not unique to the German Gulch periphyton communities.

-18-

The fifteen common German Gulch diatoms accounted for about 72% of the study's total frustule counts, and the remaining tabulations were thinly spread among the 67 remaining, less common forms. Such a dominance by a disproportionately small assortment of species is in agreement with the community structures that can be recognized in most of the natural biological systems. In the case of extensively polluted streams, this dominance would be more thickly spread across a much smaller set of periphytic organisms with a much reduced level of floral richness, i.e., with a much narrower selection of the rarer diatom species, and such pollutive restrictions do not appear to be evident in the German Gulch collections.

The environmental status of German Gulch was additionally judged by reviewing the Shannon-Wiener diversity numbers of the three periphyton samples. To set the stage for making such evaluations, the refined data of this kind that are now on hand for numerous Montana streams as available in Tngman et al (1979), Bahls et al (1979), and Bahls et al (1981) were first assessed for comparative purposes. As revealed by these reports, a statewide average of 42.7 diatom taxa was secured for the summer season with an average Shannon-Wiener diversity value for this same period of 3.99. These mean values can then be used as a reference point for judging the biological aspects and the structures of the German Gulch periphyton scrapings.

In conjunction with such statewide means, Montana's streams also produced a typically high taxa count of 63.6 species with a maximum of 67, and 12% of the collections produced taxa numbers in excess of 60 species. The streams further produced a typically high diversity of A. 87 with a maximum of 5.00, and 12% of the samples provided diversities in excess of 4.77 units. Contrariwise, these same Montana waters produced typically low taxa numbers and diversity levels of 25.1 and 2.85 respectively with minimums of 22 and

-19-

2.55, and 12% of the statewide collections demonstrated taxa numbers and diversities below 30 and 3.20 units during the warm weather season.

In terms of interpretation as outlined by Ingman et al (1979) and Weber (1973), stream periphyton samples with diatom species numbers and Shannon- Wiener diversities around or in excess of the statewide means (i.e., greater than about 40 taxa to a maximum near 67 with a diversity greater than 4.00 to a maximum of about 5.00 units) would tend to be indicative of an excellent biological health with the absence of any marked pollutive stress or other perturbations. In general, periphyton collections with somewhat lower taxa numbers between 25 and 40 and with somewhat lower diversities between 3.00 and 4.00 units are also indicative of fairly good environmental conditions. How- ever, values in these latter ranges could be suggestive of the occurrence of comparatively mild instream problems, and the likelihood and severity of such a potential stress would be expected to be enhanced to some small degree as the taxa numbers and diversities fall to the 25 and 3.00 level respectively.

But as a more consistent and accurate reference guideline, periphytic taxa numbers and diversities that lie below the 25 and 3.00 levels respective- ly have been found to be more definitely suggestive of a pollutive problem. Furthermore, a progressively greater severity of instream stress might be anticipated with the lower diversity values in those instances where diver- sities are found to reside in the 3.00 to zero range. Periphytic diversities below 2.00, in turn, are particularly demonstrative of an extreme perturbation with the zero value representative of the diagnostic limit.

Periphytic evidence of somewhat marked environmental difficulties has been uncovered for a small number of Montana's streams as revealed by the minimum statewide taxa number and diversity readings that were listed previously. However, the below 2.00 diversity extreme was not uncovered while

-20-

conducting the statewide biological inventories, and this fact points to the overall good environmental health that is evident in most of the State's waters. As will be described below, German Gulch would appear to fall into this same "good-health" category.

With regard to the German Gulch periphyton collections, diatom taxa numbers and diversities as summarized in Table 15 were found to be typically above or near the state averages, and they were observed to be well above the diagnostically critical 25 and 2.00 or 3.00 levels. These juxtapositions thereby are indicative of a generally good biological health along the gulch with absence of any significant environmental degradations. In relation to the lower German Gulch site near its mouth, taxa numbers and diversities were calculated to be somewhat lower than those upstream, but they remain adequate- ly high so as to be also suggestive of a fairly good biological condition. For the most part, therefore, German Gulch can be readily distinguished from those few Montana streams that demonstrated relatively low diversity values and that demonstrated the potential for facing adverse environmental stress.

Nevertheless, the fact that the taxa numbers and diversities of the lower gulch site fell into the 25 to 40 and 3.00 to 4.00 ranges points to the possible occurrence of some very mild environmental problems in the bottom section of the waterway. Thus, another statistical evaluation was performed leading to the calculation of equitability indices in order to shed additional light on the environmental status of the lower gulch station.

Along with diversity, equitability is another community index that can be used as a check to further assess the ecological shape of a periphyton collection. This equitability index (e) basically compares the number of taxa that were actually retrieved from a sampling site with a theoretical taxa number that should have been obtained in response to the sample's diversity on

-21-

the basis of a mathematical model (Weber 1973). Values for e that are near one show a close correspondence of the field data to the theoretical model with a highly equitable distribution of abundances among the collected taxa. Values of e near zero show the opposite trend and a distinctively inequitable distribution of abundances among the collected organisms. In the main, healthy and unpolluted ecosystems tend to demonstrate a highly equitable abundance distribution with index values above 0.50, while degraded and disturbed ecosystems tend to show a poor equitability with index values below 0.50 and approaching zero.

Most commonly, equitability numbers between 0.60 and 0.80 are obtained from nondegraded streams, and higher e values near 1.00 are rarely found in the real world. As a result, periphytic samples exhibiting e readings between 0.60 and 0.80 are definitely indicative of good environmental conditions and a lack of severe pollution. In a few rare occasions, e values above 0.80 can be obtained; such high indices are also suggestive of non-polluting situations, although they typically refer to a natural physical stress as might be subjected in a torrential stream.

At the other end of the scale, low e numbers between 0.00 and 0.30 are fairly accurately diagnostic of some types of instream disturbance that causes an inequitable distribution of abundance among the taxa, and even fairly slight degradations can depress a community's equitability rating to such a low level (Weber 1973). In response, periphyton collections that produce poor equitabilities and index values in this lower 0.00 and 0.30 range are suggestive of environmental perturbations in the associated stream reach. Equitabilities in the 0.30 to 0.60 range, which affords an intermediate condition, are representative of borderline or marginal situations as follows: values of e above 0.50 but less than 0.60 would tend to delineate the somewhat

-22-

low probability of a very small impact, while e values below 0.50 but above 0.30 would tend to delineate the greater likelihood of some adverse but largely mild environmental effect.

With reference to the German Gulch equitability calculations, both the species and the varietal equitabilities in Table 15 were observed to lie in the 0.60 to 0.80 range for all three of the German Gulch stations, and these observations point to a good environmental health with the absence of any significant pollutive stress. Equitabilities were seen to decline to a small extent to the lower gulch site in parallel with this station's reduced Shannon-Wiener diversities, and this downstream drop in diversity was inter- preted to illustrate the development of a very mild perturbation in the lower reach of the gulch. But the fact that the bottom station's periphyton equit- ability was greater than 0.60 acts to confirm the mildness of the potential effect, if such an effect actually exists.

Based on these diversity and equitability index assessments, German Gulch appears to be in an excellent to good environmental and biological condition at the present time. Therefore, the prediction of the absence of any marked pollutive inputs into the waters of the gulch would seem to be a valid judgment that can now be put forth for the project's waterway.

•23-

AQUATIC MACROINVERTEBRATES

Study Area

Aquatic macroinvertebrate sample sites were located at three stations (Upper, Middle and Lower), which correspond to the same stations at which fish population data were collected. The Upper, Middle and Lower stations corre- spond to the Below Edward Creek, Below Beef straight Creek and Durant Sections, respectively, described in the Fisheries section.

Methods

Aquatic macroinvertebrates were collected with a modified Surber sampler which had a one square foot sample surface area. Three square foot samples were collected from each of the three sample sites on May 21, 1984 and August 6, 1984. The sampler was placed in riffle habitats which had cobble substrates (3" to 6") and depths of approximately 6 inches. Invertebrates were collected by scrubbing the larger cobble with a brush and disturbing the finer substrate with a three-pronged garden claw. Samples were concentrated in a series 30 sieve, transferred to labelled containers and preserved in 10% formalin. The samples were returned to the laboratory where macroinverte- brates were separated from the gravel and detritus by order and transferred to labelled vials containing 70% ethanol.

Macroinvertebrates were identified to the lowest practicable taxon, usually genus or species, and enumerated. Identifications were made by using keys written by Allen and Edmunds (1962 and 1963), Bauman et al (1977), Brinkhurst and Jamieson (1971), Brown (1972), Edmunds et al (1976), Hamilton

-24-

and Saether (1970), Jensen (1966), Johannsen (1934 and 1935) and Wiggins (1977). Chironomid larvae and microdrile oligochaetes were mounted on glass microscope slides in Hydramount. Microdrile oligochaetes were cleared in Amman's lactophenol prior to mounting.

Results

Species Richness and Community Composition

A total of 70 taxa were identified from the German Gulch samples. Samples collected at the Upper, Middle and Lower Sites yielded 41, 51 and 52 taxa, respectively. Twenty-eight taxa were common to all three sites while each of the three stations yielded taxa unique to the site (7 at the Upper, 6 at the Middle and 10 at the Lower) . Summer samples exhibited an increase in species richness over spring samples at all three sample sites (Table 16).

Mean numbers of taxa collected per sample are presented by sample site and by sample site and season in Table 17. Mean numbers of taxa per square foot sample are related to species distribution and species diversity in the sample habitat. The highest mean numbers of taxa per sample occurred at the Middle Site while the lowest means occurred at the Upper Site. Mean numbers of taxa per sample showed an increase in the summer samples over the spring samples at all three stations. Spring numbers of taxa per sample at the Lower Site were nearly identical to those observed at the Upper Site, while numbers observed at the Lower Site approximated the mean for the Middle Site.

A checklist of the taxa collected from German Gulch Creek and their distributions among the three sample sites is presented in Table 18. The fauna of German Gulch Creek was dominated by rheophilous forms typical of small montane tributaries. The rheophile community is extremely constant and

-25-

enjoys a worldwide uniformity. The rheophile habitat is marked by steep gradient, swift current velocity, boulder-rubble-cobble substrates, cold thermal regime and a periphyton-detritus production base. Examples of rheo- philous organisms collected in German Gulch Creek included: Cinygmula, Epeorus spp., I), doddsi, D^. spinif era, C_. hystrix, R.. robusta, Amphinemura, Zapada, P_. expansa, Parapsyche, Rhyacophila, Glossosoma, Apatania, Heterlimnius Diamesa , Stempel line 11a, C_. nostocicola, etc. The fauna observed at the Upper and Lower Sites was generally limited to rheophile forms; however, the fauna of the Lower Site included facultative forms collected only at that station. Such facultative forms are common inhabitants of larger rivers and lowland streams of the region and are tolerant of a wider range of substrate type, current velocity, dissolved oxygen and water temperature than the rheophile community. Facultative forms collected only at the Lower Site included: Pseudocloeon sp., P_. badia, Hydropsyche sp., Narpus sp., Brillia sp., Cardio- cladius sp., Cricotopus (Cricotopus) sp., Eiseniella sp. and Haplotaxis sp.

Macroinvertebrate Abundance

A total of 3,847 aquatic macroinvertebrates were collected in the German Gulch samples of which 30% were collected from the Upper Site, 52% from the Middle Site and 18% from the Lower Site. Summer samples from the Upper and Lower Sites exhibited marked increases in abundance over the spring samples (Table 17); however, spring and summer abundance was equal at the Middle Site.

Mean numbers of macroinvertebrates per square foot are presented by

sample site and by sample site and season in Table 17. Macroinvertebrate

2 abundance was lowest at the Lower Site (115/ft ), intermediate at the Upper

Site (191 /ft2) and highest at the Middle Site (335/ft2). The Middle Site

represented a relatively productive habitat characterized by a dense growth of

•26-

filamentous algae on the cobble substrate, while substrates at the Upper and Lower Sites were colonized by diatoms.

Summer numbers of macroinvertebrates per square foot averaged 213% higher at the Lower Site and 220% higher at the Upper Site than spring numbers at either station, while spring and summer abundance was equal at the Middle Site. This, in conjunction with the suggested increased productivity of the Middle Site, was probably related to the presence of a large beaver dam located immediately upstream from the Middle Site. The dam may have afforded protection from harsh winter ice conditions, thus maintaining high spring numbers of macroinvertebrates, while providing some nutrient enrichment to stimulate production.

Macroinvertebrate numbers per sample by individual taxon are given in Tables 19, 20 and 21 for the Upper, Middle and Lower Sites. Macroinvertebrate numbers were dominated by Diptera and Ephemeroptera at all three stations. While numbers of Ephemeroptera were relatively evenly distributed among the species, numbers of Diptera were markedly dominated by the chironomid, Cricotopus c.f. nostocicola. This dominance occurred only at the Upper and Middle Sites. Cricotopus c.f. nostocicola is a midge larva which lives symbiotically in colonies of the blue-green alga Nostoc and is characteristic of rheophile habitats.

-27-

REFERENCES

Allen, R.K. and G.F. Edmunds Jr. 1962. A revision of the genus Ephemerella (Ephemeroptera: Ephemerellidae) . V The subgenus Prunella in North America. Misc. Pub. Ent. Soc. Amer. 3:147-179.

1963. A revision of the genus Ephemerella (Ephemeroptera: Ephemer-

ellidae). VI The subgenus Seratella in North America. Ann. Ent. Soc, Amer. 56:583-600.

American Public Health Association, American Water Works Association and Water Pollution Control Federation. 1975. Standard methods for the examina- tion of water and wastewater. 14th Edition, American Public Health Assoc, Washington, D.C. 1193 pp.

Bahls, L. , M. Fillinger, R. Greene, A. Horpestad, G. Ingman, and E. Weber. 1981. Biological water quality monitoring, eastern Montana, 1979. WQB Report No. 81-3, Water Quality Bureau, Montana Department of Health and Environmental Sciences, Helena, Montana. 93 pp.

Bahls, L.L., G.L. Ingman and A. A. Horpestad. 1979. Biological water quality

monitoring, southwest Montana, 1977-78. Water Quality Bureau, Montana

Department of Health and Environmental Sciences, Helena, Montana. 60 pp.

Bauman, R.W., A.R. Gaufin, and R.F. Surdick. 1977. The stoneflies (Plecoptera) of the Rocky Mountains. Mem. Amer. Ent. Soc. 31:1-208.

Brinkhurst, R.O. and B.G.M. Jamieson. 1971. Aquatic Oligochaeta of the world. Oliver and Boyd, Edinburgh. 860 pp.

Brown, H.P. 1972. Aquatic Dryopoid beetles (Coleoptera) of the United States. Biota of freshwater ecosystems, Ident. Manual No. 6, Water Poll. Con. Res. Series 18050 ELD, USEPA. 81 pp.

Edmunds, G.F. Jr., S.L. Jensen, and L. Berner. 1976. The mayflies of North and Central America. U. of Minn. Press, Minneapolis. 330 pp.

Environmental Protection Agency. 1976. Quality criteria for water. Office of Water and Hazardous Materials, U.S. Environmental Protection Agency, Washington, D.C. 256 pp.

Hamilton, A.L. and O.A. Saether. 1970. Key to the genera of midge larvae. (Unpub.) Freshwater Inst., FRBC, Winnipeg, Manitoba, Canada.

Hart, D.S. and M.A. Brusven, 1976. Comparison of benthic insect communities in six small Idaho Batholith streams. Melanderia 23:1-18.

•28-

Hurlbert, S.H. 1971. The non-concept of species diversity: a critique and alternative parameters. Ecology 52:577-586.

Hynes, H.B.N. 1970a. The ecology of running waters. U. of Toronto Press, Toronto. 555 pp.

. 1970b. The ecology of stream insects. Ann. Rev. of Ent. 15:25-42

Ingman, G.L., L.L. Bahls, and A. A. Horpestad. 1979. Biological water quality monitoring, northcentral Montana, 1977-1978. Water Quality Bureau, Montana Department of Health and Environmental Sciences, Helena, Montana. 64 pp.

Jensen, S.L. 1966. The mayflies of Idaho. (Unpub.) M.S. Thesis, U. of Utah, Salt Lake City. 367 pp.

Johannsen, O.A. 1934. Aquatic Diptera part 1. Nemocera exclusive of Chiro- nomidae and Ceratopogonidae. Mem. Cornell U. Ag. Exp. Sta. 164:1-71.

. 1935. Aquatic Diptera part 2. Orthorrapha-Brachycera and Cyclor-

rapha. Mem. Cornell U. Ag. Exp. Sta. 177:1-62.

Kaiser, G.L., D.A. Klarich, and J.L. Thomas. 1977. Agricultural non-point source water quality monitoring and sampling. Middle Yellowstone Areawide Planning Organization FWPCAA Section 208 Final Report, Independent Consultants, Billings, Montana. 115 pp.

Klarich, D.A. 1976. Estimates of primary production and periphyton community structure in the Yellowstone River (Laurel to Huntley, Montana) . Water Quality Bureau, Montana Department of Health and Environmental Sciences, Billings, Montana.

Liknes, G.A. 1984. The present status and distribution of the westslope cutthroat trout (Salmo clarki lewisi) east and west of the Continental Divide in Montana. Montana Department of Fish, Wildlife and Parks, Helena, Montana. Draft. 163 pp.

Lowe, R.L. 1974. Environmental requirements and pollution tolerance of fresh- water diatoms. EPA-670/4-74-005, Environmental Monitoring Series, Office of Research and Development, National Environmental Research Center, Environmental Protection Agency, Washington, D.C. 333 pp.

Montana Department of Fish and Game. 1979. Instream flow evaluation for selected streams in the upper Missouri River Basin. Montana Department of Fish, Wildlife and Parks, Helena, Montana. 254 pp.

Montana Department of Fish, Wildlife and Parks. 1981. Instream flow evaluation for selected waterways in western Montana. Montana Department of Fish, Wildlife and Parks, Helena, Montana. 340 pp.

Nelson, F.A. 1984. Guidelines for using the wetted perimeter (WETP) computer program of the Montana Department of Fish, Wildlife and Parks. Montana Department of Fish, Wildlife and Parks, Helena, Montana. 55 pp.

-29-

Oswald, R.A. 1981. Aquatic resources inventory of the Mount Haggin Area. Montana Department of Fish, Wildlife and Parks, Helena, Montana. 89 pp.

Patrick, R. and C.W. Reimer. 1966. The diatoms of the United States. Volume 1. Monograph No. 13, The Academy of Natural Sciences of Philadelphia, Philadelphia, Pennsylvania. 688 pp.

Vincent, E.R. 1971. River electrof ishing and fish population estimates. Prog. Fish Cult. 33(3): 163-169.

1974. Addendum to river electrof ishing and fish population

estimates. Prog. Fish Cult. 36(3): 182.

Weber, C.I., L.A. Fay, G.B. Collins, D. Rathke, and J. Towbin. 1980. The status of methods for the analysis of chlorophyll in periphyton and plankton. Environmental Monitoring and Support Laboratory, Environ- mental Protection Agency, Cincinnati, Ohio. 87 pp.

Weber, C.I., Ed. 1973. Biological field and laboratory methods for measuring the quality of surface waters and effluents. EPA-670/4-73-001 , Environ- mental Monitoring Series, Office of Research and Development, National Environmental Research Center, Environmental Protection Agency, Cincinnati, Ohio.

Wiggins, G.B. 1977. Larvae of the North American caddisfly genera (Trichop- tera) . U. of Toronto Press, Toronto. 401 pp.

-30-

Table 1. Summary of electrof ishing survey data collected for the 1000-ft Durant Section of German Gulch Creek (T3N, R10W, S12.13) on July 26 and August 7, 1984.

Species

Westslope cutthroat

Brook trout Brown trout

No. Captured

201

79

1

Length Range (inches)

2.5 - 11.3

2.3 - 8.6 8.3

Table 2. Estimated standing crop of trout in the 1000-ft Durant Section of German Gulch Creek (T3N, R10W, S12.13) on July 26, 1984 (80% con- fidence intervals in parentheses).

Species

Length Group (inches)

Per 1000 Feet Number Pounds

Westslope cutthroat 4.0 - 5.9

6.0 -11.3

Brook trout

4.0 - 5.9 6.0 - 8.6

84 149 233 (+ 34)

67 46 113 (+ 29)

4 28

32 (+4)

3

_7

10 (+4)

Total Trout

346 (+ 45)

42 (+ 4)

-31-

Table 3. Average length and weight of cutthroat and brook trout by age class in the Durant Section of German Gulch Creek (T3N, R10W, S12.13).

Species

Westslope cutthroat

Brook trout

Average Average

Age Class	Leng	th (inches)	We:	Lght (pounds)
I		5.0		0.05
II		7.0		0.13
III		8.2		0.21
IV+		9.2		0.30
I		4.6		0.04
II		6.3		0.09
III+		7.8		0.19

Table 4. Summary of electrof ishing survey data collected for the 1000-ft Below Beefstraight Creek Section of German Gulch Creek (T3N, R10W, S26) on July 26 and August 6, 1984.

Species No. Captured Length Range (inches)

Westslope cutthroat 112 2.3 - 10.5

Brook trout 125 1.9 - 9.6

-32-

Table 5. Estimated standing crop of trout in the 1000-ft Below Beefstraight Creek Section of German Gulch Creek (T3N, R10W, S26) on July 26, 1984 (80% confidence intervals in parentheses).

Species Length Group (inches)

Westslope cutthroat 4.0 - 5.9

6.0 -10.5

Brook trout

4.0 - 5.9 6.0 - 9.6

Per 1000 Feet Number Pounds

30 101 131 (+ 25)

109 61 170 (+ 42)

1 20 21 < + 4)

4 _8 12 (+2)

Total Trout

301 (+ 42)

33 (+ 4)

Table 6. Average lengths and weights of Westslope cutthroat and brook trout by

age class in the Below Beefstraight Creek Section of German Gulch Creek (T3N, R10W, S26).

Species

Westslope cutthroat

Brook trout

			Average		Average
Age CI	ass	Length (inches)	We	ight (pounds)
I			4.8		0.04
II			6.9		0.13
III			8.3		0.22
IV+			9.7		0.35
I			6.4		0.10
II			8.3		0.21
III			9.4		0.32

33-

Table 7. Summary of electrof ishing survey data collected for the 1000-ft below Edward Creek Section of German Gulch Creek (T3N, R10W, S34) on July 26 and August 6, 1984.

Species Westslope cutthroat Brook trout

No. Captured

147

43

Length Range (Inches) 2.8 - 10.6 2.0 - 8.1

Table 8. Estimated standing crop of trout in the 1000-ft Below Edward Creek Section of German Gulch Creek (T3N, R10W, S34) on July 26, 1984 (80% confidence intervals in parentheses) .

Species

Length Group (inches)

Per 1000 Feet Number Pounds

Westslope cutthroat

Brook trout

4.0 - 5.9 6.0 -10.6

3.2 - 5.9 6.0 - 8.1

123 6

45 _8

168 (+ 23) 14 (+ 1)

30 1

11 1

41 (+ 10) 2 (+ 0)

Total Trout

209 (+ 25) 16 (+ 1)

•34-

Table 9. Average lengths and weights of westslope cutthroat and brook trout by age class in the Below Edward Creek Section of German Gulch Creek (T3N, R10W, S34).

Species

Westslope cutthroat

Brook trout

	Average		Average
Age Class	Length	(inches)	We:	Lght (pounds)
I		5.1		0.05
II		7.1		0.14
III		8.6		0.22
IV+		9.3		0.30
I		4.0		0.03
II		6.2		0.10
III+		7.1		0.15

-35-

Table 10. Estimated standing crops of trout in 1000-ft study sections of streams in the German Gulch vicinity (P denotes presence in numbers too low to make reliable estimates) (Data from Oswald 1981).

Location

Brook Trout No. Lbs.

Rainbows No. Lbs.

Cutthroat No . Lbs .

Total Trout No . Lbs .

Seymour	519	41
Sullivan	602	29
Twelve-mile	314	27
Slaughterhouse	182	19
Ten-mile	353	31
Seven-mile	183	13
Deep	166	18
Six-mile	392	13
Oregon	265	24
American	160	12
California	130	16
French1	P	—
Willow	677	37
German Gulch	113	10

(Durant)

P

18

20

P

8 30 P

3

1

1 3

63 233

8 32

519	41
602	29
314	27
182	19
353	31
183	13
184	21
412	14
265	24
168	13
160	19

740 346

45 42

Montana Department of Fish, Wildlife and Parks (1981)

-36-

Table 11. High flow recommendations based on the dominant discharge/channel morphology concept (USGS flow gage record data).

Time Period Flow Recommendations (cfs)l

May 16 - 31 53

June 1-15 58

1 Plus the dominant discharge of approximately 139 cfs, which should be main- tained for one 24-hour period during May 16 - June 15.

-37-

Table 12. Instream flow recommendations (cfs) for German Gulch at the Below Beef straight Creek study site compared to the 10th, 50th and 90th percentile monthly flows (cfs) .

Percentile Flow (cfs)

Time Period

January

February

March

April

May 1-15

May 16 - 31

June 1 - 15

June 16-30

July

August

September

October

November

December

Recommendations (cfs)

12 12 12 12

122

532 58

12

I

10th 50th 90th (Wet Year) (Typical Year) (Dry Year)

8.0	6.0	5.0
9.0	6.5	4.3
11.7	7.5	5.0
25.7	15.5	9.3

109. A

150.1

64.0

70.5

41.3

43.3

48.8	26.5	10.6
17.4	12.0	6.3
13.4	9.0	8.0
12.0	9.0	7.0
10.0	8.0	5.3
10.0	7.0	5.0

Derived using the wetted perimeter/inflection point method and the dominant discharge/channel morphology concept.

Plus the dominant discharge of approximately 139 cfs, which should be main- tained for one 24-hour period during May 16 - June 15.

Derived by the USGS using recorded and reconstituted flows at the gage site on German Gulch located 0.5 miles upstream from the mouth (No. 12323500), 1951 - 1982.

The 10th percentile is the flow that is exceeded in 1 of 10 years; in other terms, in 1 year out of 10 there is more water than the 10th percentile flowing in the stream.

The 50th percentile is the flow that is exceeded in 5 of 10 years; in other terms, in 5 years out of 10 there is more water than the 50th percentile flowing in the stream.

The 90th percentile is the flow that is exceeded in 9 of 10 years; in other terms, in 9 years out of 10 there is more water than the 90th percentile flowing in the stream.

38-

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•39-

Table 14. Concentrations of chlorophyll a, b, and c (ug/cm^) for three loca- tions in German Gulch Creek, July 18, 1984.

Chlorophyll ug/cm^

Location

Below Edward Creek Replicate 1 Replicate 2 Mean

3.06 3.31 3.19

0.216 0.175 0.196

0.550 0.687 0.619

Below Beefstraight Creek Replicate 1 Replicate 2 Mean

Near Mouth

Replicate 1 Replicate 2 Mean

0.98 1.45 1.21	0.007 0.012 0.010	0.103 0.129 0.116
3.54 4.77	0.329 0.271	0.419 0.636

4.16

0.300

0.528

-40-

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-41-

Table 16. Analysis of species richness (numbers of seperable taxa) observed

at the Upper, Middle and Lower sample sites on German Gulch Creek in May and August, 1984.

Upper Middle Lower

Total No. Taxa Per Site 4U Ert 52

Total No. Taxa Per Season SP SU SP SU SP SU

By Sample Site 27 32 37 41 27 49

Mean No. Taxa Per Sample

By Sample Site 20.5 29.3 24.8

Mean No. Taxa Per Sample SP SU S£ SU SP SU

By Sample Site and Season 17.0 24.0 25.3 33.3 17.7 32.0

Table 17. Analysis of aquatic macroinvertebrate abundance in square foot samples collected at the Upper, Middle and Lower sample sites on German Gulch Creek in May and August, 1984.

	Upper 1145	Middle 2010	Lower
Total Numbers Per Site	692
Total Numbers Per Season	SP SU	SP SU	SP SU
By Sample Site	273 872	1005 1005	167 525
Mean Numbers Per Square Ft
By Sample Site	191	335	115
Mean Numbers Per Square Ft	SP SU	SP SU	SP SU
By Sample Site and Season	91 291	335 335	56 175

-42-

Table 13. Systematic checklist and distribution among sample sites (Upper, Middle

and Lower) of aquatic macroinvertebrates collected from German Gulch Creek in May and August, 1984.

SPRING

SUMMER

TAXA

Upp Mid Low Upp Mid Low

EPHEMEROPTERA

Siphlonuridae Ameletus sp.

Baetidae

Baetis bicaudatus Baetis sop. Pseudocloeon sp.

Heptaqeniidae Cinygmula spp. Epeorus deceptivus Epeorus grandis Epeorus lonqimanus Tfliithrogena robusta Rhithrogena sp.

Leptophlebiidae

Paraleptophlebia sp. Ephemerell idae

Caudatella hystrix

X	X	X	X	X	X
-	X	X	:	X	X X
X	X	X	X	X	X
-	-	-	X	X	X
-	-	-	X	X	-
X	X	X	X	X	-
X	X	X	X	X	X
-	X	X	-	-	X

Drunella	coloradensis
Prunella Prunella Ephemere	doddsi spinifera lla infrequens
Seratelli	i tibialis

PLECOPTERA Nemouridae

Amphinemura so.

Nemoura sp.

Zapada sp. Taeniopteryqidae

Taenionema sp. Capniidae

Capnia group*

Eucapnopsis brevicauda Pel toper! idae

Yoraperla brevis Pteronarcydae

Pteronarcella badia Perlodidae

Cultus sp.

Kogotus sp.

Meqarcys sp.

Pictetiella expansa Perl idae

Poroneuria theodora Chloroperlidae

Chloroperl inae**

X X

X

X X

X X X

X X

X X X

X X

-43-

Table 18. Continued,

TAXA

SPRING Upp Mid Low

corpulentus

TRICHOPTERA Philopotamidae

Pol ophi lodes sp. Hydropsychidae

Arctopsyche sp.

Hydropsyche sp.

Parapsyche sp. Rhyacophilidae

Rhyacophila^sppv i Glossosomatidae

Glossosoma sp. Hydroptilidae

Aqraylea sp.

Ochrotrichia sp. Brachycentridae

Brachycentrus sp.

Micrasema so. Limnephilidae

Apatania sp.

Ecclisomyia sp.

COLEOPTERA Elmidae

Heterlimnius _

Narpus sp. Hal iplidae

Brychius sp.

DIPTERA Tipulidae

Antocha sp.

Hexatoma sp.

Limnophila sp. Chironomidae

Diamesa sp.

Pseudokiefferiella sp.

Micropsectra sp.

Stempell inel la sp.

Bril 1 ia sp.

Cardiocladius sp.

Cricotopus (C.) sp.

Cricotopus c.f. nostocicola

Cricotopus (C.) / Orthocla'dius (0.)

Eukiefferiella spp.

Orthocladius (Eudactylocladius) spp.

Orthocladius (Euorthocladius) spp.

Parametriocnemus sp.

Paraphaenocladius sp.

X X

spp,

Simul iidae Pros i mu liuin Simul ium so.

	SUMMER
Upp	Mid	Low
	X	X
—	X	X
-	-	X
X	X	-
X	X	X
X	X	X

-	X	X	X	-	X
-	X	X	X X	X	X
.		X	X
-	-	-	X	X	X
X	X	X	-	X	X
X	-	™	X	-	X X X X
X	X	X	X	X
X	X	-	X	X	X
X	X	-	X	X	X
-	-	-	X	X	-
X X	X	-	-	-	X

so.

-44-

Table 18. Continued
	SPRING		SUMMER
TAXA	Upp Mid	Low	Upp Mid	Low

NEMATODA

TURBELLAR1A

OLIGOCHAETA Lumbricidae

Eiseniella sp. Haplotaxidae

Haplotaxis sp. Naididae

c.f. Homochaeta naidina	X	X	X	X	X	X

Total Number of Taxa Collected	27	37	27	32	41	49

* Capnia group = Capnia, Mesocapnia and Utacapnia unseperable in larval staqe.

** Subfamily Chloroperl inae = Alloperla, Suwallia, Sweltsa and Triznaka unseperable in larval stage.

*** Most species of Cricotopus (Cricotopus) and Orthocladius (Orthocladius) are unseperable in larval staqe.

-45-

Table 19. Numbers of macroinvertebrates collected per square foot Surber sample from the Upper Site on German Gulch Creek in May and August, 1984.

		Spri	ng Sampl	e		Summer SamD	le
TAXA	A	B	C	TOTAL	A	B	C	TOTAL
EPHEMEROPTERA
Baetis bicaudatus	1	3	2	6	4	20	29	53
Cinyqmula spp.	6	8	11	25	11	1	11	23
Epeorus deceptivus	-	-	-	-	13	6	26	45
E. grandis	-	-	-	-	-	-	15	15
E. longimanus	-	-	1	1	6	1	5	12
Rhithrogena robusta	2	1	2	5	6	2	18	26
Drunella coloradensis	-	10	2	12	2	3	1	6
D. doddsi	-	1	-	1	4	3	2	9
D. spinifera	-	-	-	-	-	2	-	2
Seratella tibialis	-	-	-	-	4	3	7	14
Total Ephemeroptera	9	23	18	50	50	41	114	205
PLECOPTERA
Zapada sp.	1	-	-	1	5	6	19	30
Taenionema sp.	1	3	2	6	-	-	-	-
Capnia group	-	-	-	-	1	1	-	2
Eucapnopsis brevicauda	2	2	1	5	-	-	-	-
Yoraperla brevis	1	-	1	2	-	-	-	-
Meqarcys sp.	-	1	-	1	1	5	2	8
Chloroperlinae	1	1	-	2	1	-	1	2
Total Plecoptera	6	7	4	17	8	12	22	42
TRICHOPTERA
Paraosyche sp.	-	2	-	2	-	3	1	4
Rhyacophila spp.	1	5	1	7	6	6	5	17
Glossosoma sp.	8	7	1	16	2	1	8	11
Agraylea sp.	1	-	-	1	-	-	-	-
Brachycentrus sp.	-	1	-	1	-	-	-	-
Micrasema sp.	-	1	-	1	1	-	1	2
Apatania sp.	-	-	-	-	-	1	-	1
Ecclisomyia sp.	1	-	-	1	-	-	-	-
Total Trichoptera	11	16	2	29	9	11	15	35
COLEOPTERA
Heterlimnius corpulentus	-	-	-	-	3	4	3	10
Total Coleoptera	-	-	-	-	3	4	3	10
DIPTERA
Antocha sp.	-	-	-	-	-	1	-	1
Hexatoma sp.	-	-	1	1	1	-	1	2
Limnophila sp.	-	-	-	-	1	-	-	1
Diamesa sp.	-	-	-	-	1	1	-	2
Pseudokiefferiella sp.	-	-	-	-	1	-	-	1
Micropsectra sp.	1	-	-	1	-	-	-	-
Stempel linella sp.	1	-	-	1	-	1	-	1
Cricotpus c.f. nostocicola	13	56	64	133	118	351	43	512
Cricotopus / Orthocladius spp.	-	1	-	1	10	-	2	12
Eukiefferiella spp.	1	2	1	4	4	3	1	8

-46-

Table 19. Continued.

		Spring Sample		Summer Sample
TAXA	A	B	C TOTAL	A	B	C TOTAL
DIPTERA (Continued) Orthocladius (Eudact.) sp. Parametriocnemus sp. Paraphaenocladius sp.	1	1	1 1	8	4	2 14
Total Diptera	17	60	66 143	144	361	49 554
TURBELLARIA	1	-	1	2	-	2
Total Turbellaria	1	-	I	2	-	2
OLIGOCHAETA c.f. Homochaeta naidina	5	22	6 33	13	7	4 24
Total Oligochaeta	5	22	6 33	13	7	4 24
TOTAL TAXA	18	19	14	25	24	23
TOTAL NUMBERS MACROINVERTS.	49	128	96 273	229	436	207 872

-47-

Table 20. Numbers of macroinvertebrates collected per square foot Surber sample from the Middle Site on German Gulch Creek in May and August, 1984.

		Spr	ing Sampl	e		Summer Sampl	e
TAXA	A	B	C	TOTAL	A	B	C	TOTAL
EPHEMEROPTERA
Ameletus sp.	2	-	-	2	-	-	-	_
Baetis bicaudatus	20	12	13	45	23	4	14	41
Baetis spp.	7	7	5	19	9	3	9	21
Cinygmula spp.	10	19	12	41	8	4	8	20
Epeorus decent ivus	-	-	-	-	6	10	12	28
E. qrandis	-	-	-	-	1	-	2	3
E. longimanus	6	31	9	46	-	-	1	1
Rhithrogena robusta	2	-	-	2	3	1	1	5
Rhithrogena sp.	1	3	4	8	-	-	-	-
ParaleDtophlebia sp.	1	1	-	2	3	-	1	4
Caudatella hystrix	4	1	1	6	33	7	11	51
Drunella coloradensis	37	33	43	113	3	2	2	7
D. doddsi	2	1	3	6	12	24	36	72
D. spinifera	-	-	2	2	25	7	7	39
Ephemerella infrequens	51	21	25	97	2	-	-	2
Seratella tibialis	-	-	-	-	22	5	9	36
Total Ephemeroptera	143	129	117	389	150	67	113	330
PLECOPTERA
Amphinemura sp.	-	-	-	-	2	-	4	6
Nemoura sp.	-	2	-	2	-	-	-	-
Zapada sp.	-	-	-	-	2	-	1	3
Taenionema sp.	4	2	2	8	-	-	-	-
Capnia group	-	-	-	-	-	-	3	3
Cultus sp.	2	-	1	3	-	-	1	1
Kogotus sp.	-	1	2	3	-	-	-	-
Megarcys sp.	-	-	-	-	1	-	-	1
Pictetiella expansa	-	1	-	1	-	-	-	-
Doroneuria theodora	-	1	-	1	-	-	-	-
Chloroperl inae	-	-	-	-	13	1	1	15
Total Plecoptera	6	7	5	18	18	1	10	29
TRICHOPTERA
Dolophilodes sp.	-	-	-	-	1	1	1	3
Arctopsyche sp.	7	-	4	11	13	4	16	33
Parapsyche sp.	5	-	3	8	4	5	5	14
Rhyacophila spp.	9	2	9	20	7	6	12	25
Glossosoma sp.	1	4	1	6	1	1	-	2
Ochrotrichia sp.	-	-	-	-	-	-	1	1
Brachycentrus sp.	3	7	-	10	-	6	2	8
Micrasema sp.	4	-	1	5	22	3	15	40
Apatania sp.	-	-	-	-	1	1	1	3
Total Trichoptera	29	13	18	60	49	27	53	129
C0LE0PTERA
Heterlimnius corpulentus	5	5	14	24	54	16	11	81
Brychius sp.	-	-	1	1	-	-	-	-
Total Coleoptera	5	5	15	25	54	16	11	81

-48-

Table 20. Continued

		Spring Sampl	e		Summer Sampl	e
TAXA	A	B	C	TOTAL	A	B	C	TOTAL
DIPTERA
Antocha sp.	-	1	3	4	-	-	-	-
Hexatoma sp.	-	-	1	1	-	1	-	1
Pseudokiefferiella sp.	-	-	-	-	4	8	3	15
Micropsectra sp.	2	-	-	2	11	-	6	17
Cricotopus c.f. nostocicola	144	247	96	487	77	110	66	253
Cricotopus / Orthocladius spp	. 8	3	1	12	9	2	3	14
Eukiefferiella spp.	1	-	-	1	56	24	24	104
Orthocladius (Eudact.) sp.	-	-	-	-	1	2	2	5
Orthocladius (Euorth.) spp.	-	-	1	1	-	-	-	-
Simul ium sp.	-	-	-	-	-	6	2	8
Total Diptera	155	251	102	508	158	153	106	417
NEMATODA	-	1	-	1	2	-	2	4
Total Nematoda	-	1	-	I	2	-	2	4
TUBELLARIA	2	-	-	2	5	1	3	9
Total Turbellaria	2	-	-	2	5	1	3	9
OLIGOCHAETA
c.f. Homochaeta naidina	1	1	-	2	3	1	2	6
Total Oligochaeta	1	1	-	2	3	1	2	6
TOTAL TAXA	27	24	25		34	29	37
TOTAL NUMBERS MACROINVERTS.	341	407	257	1005	439	266	300	1005

-49-

Table 21. Numbers of macroinvertebrates collected per square foot Surber sample from the Lower Site on German Gulch Creek in May and August, 1984.

		Spri	ng Sampl	e		Summer Sample
TAXA	A	B	C	TOTAL	A	B	C TOTAL
EPHEMEROPTERA
Ameletus sp.	-	-	-	-	2	-	2
Baetis bicaudatus	2	4	3	9	-	-	2 2
Baetis spp.	1	4	4	9	6	4	1 11
Pseudocloeon sp.	-	-	-	-	-	2	2
Cinygmula spp.	31	16	19	66	-	4	2 6
Epeorus deceptivus	-	-	-	-	10	2	6 18
E. longimanus	1	4	7	12	1	-	1
Rhithrogena robusta	1	1	2	4	-	3	7 10
Rhithrogena sp.	-	-	2	2	4	6	6 16
Paraleptophlebia sp.	-	-	-	-	-	-	1 1
Caudatella hystrix	-	1	-	1	5	2	2 9
Drunella coloradensis	3	3	1	7	2	11	2 15
D. doddsi	-	-	-	-	9	6	7 22
D. spinifera	-	-	-	-	1	-	1 2
Ephemerella infrequens	3	3	1	7	1	-	1
Seratella tibialis	-	-	-	-	1	-	1
Total Ephemeroptera	42	36	39	w	42	40	37 119
PLECOPTERA
Amphinemura sp.	-	-	-	-	9	7	14 30
Capnia qroup	-	-	-	-	-	-	1 1
Pteronarcella badia	-	-	-	-	-	1	1
Megarcys sp.	-	-	-	-	2	6	3 11
Taenionema sp.	-	-	1	1	-	-	-
Doroneuria theodora	2	1	1	4	1	1	2
Chloroperlinae	-	4	-	4	1	2	6 9
Total Plecoptera	2	5	2	9	13	17	24 54
TRICHOPTERA
Dolophilodes sp.	-	-	-	-	14	1	15
Arctopsyche sp.	-	1	-	1	15	11	11 37
Hydropsyche sp.	-	-	-	-	-	-	1 1
Rhyacophila spp.	-	-	-	-	9	3	2 14
Glossosoma sp.	2	1	3	6	2	-	2
Brachycentrus sp.	-	-	-	-	1	2	3
Micrasema sp.	-	1	-	1	-	1	1 2
Apatania sp.	-	1	-	1	-	1	1
Total Trichoptera	2	4	3	9	41	19	15 75
COLEOPTERA
Heterlimnius corpulentus	2	-	2	4	12	89	13 114
Narpus sp.	-	-	-	-	-	2	2
Total Coleoptera	2	-	2	4	12	91	13 116
DIPTERA
Antocha sp.	2	-	-	2	-	3	3
Hexatoma sp.	1	1	-	2	-	1	1

-50-

Table 21. Continued

		Spri	nq Sample		Summer Sample
TAXA	A	B	C TOTAL	A	B	C TOTAL
DIPTERA (Continued)
Diamesa sp.	3	2	1 6	-	-	-
Pseudokiefferlella sd.	-	-	-	-	2	2
Micropsectra sp.	-	1	1	-	2	2 4
Brill ia sp.	-	-	-	-	1	1
Cardiocladius sp.	-	-	-	-	6	6
Cricotopus (CRIC.) sp.	-	-	-	2	1	1 4
Cricotopus c.f. nostocicola	-	-	1 1	1	12	3 16
CricotoDus / Orthocladius spp.	-	-	-	-	13	2 15
Eukiefferiella spp.	-	-	-	7	11	8 26
Orthocladius (Euorth.) spp.	-	-	-	-	8	1 9
Simul ium sp.	-	1	1	15	6	7 28
Total Diptera	6	5	2 13	25	66	24 115
NEMATODA	1	-	1	1	1	2
Total Nematoda	I	-	I	1	1	2
TUBELLARIA	-	3	3	1	6	3 10
Total Turbellaria	-	3	3	I	6	3 10
OLIGOCHAETA
Eiseniella sp.	0 L.	3	3 8	-	-	1 1
Haplotaxis sp.	-	-	-	-	2	2
c.f. Homochaeta naidina	1	1	1 3	6	22	3 31
Total Oliqochaeta	3	4	4 11	6	24	4 34
TOTAL TAXA	16	21	16	28	38	30
TOTAL NUMBERS MACROINVERTS.	58	§1	52 167	141	264	120 525

-51-

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-52-

FLOW (CFS)

Figure 2. The relationship between wetted perimeter and flow for a composite of five riffle cross-sections in German Gulch below the confluence of Beef straight Creek.

-53-

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-54-

ATPKNDIX A

„o->MVi

University of Montana

Department <ii /.oolo}-.> • Missoula, Montana >')XI2 • (4(td) 2-13-5122

August 27, 1984 Mr. Bruce Rehwinkel Box 251 Whitehall, MT 59759

Dear Bruce:

We have completed the electrophoretic analysis of the Salmo sample you collected from German Gulch Creek (N=39, S 26, T 3N, R 10W) on 27 July 1984. We examined the protein products of 45 loci in all the fish (Table 1). Thirteen of these loci can be used to differentiate westslope cutthroat (S. clarki lewisi), Yellowstone cutthroat (S. c. bouvieri), and rainbow trout (S. gairdneri ) (Table 2). There is no evidence of rainbow or Yellowstone cutthroat trout genetic material in the sample at any of these loci. With this sample size, we would detect even as little as one percent rainbow or Yellowstone genes in the population over 99 percent of the time. Thus, this is almost certainly a genetically 'pure' population of westslope cutthroat trout.

There is evidence of genetic variation at seven of the loci examined (Table 3). We have detected the Idh3(71) allele only at low frequencies (i.e. less than 0.10) in a few other populations of westslope cutthroat trout. This allele, however, is present in the German Gulch Creek westslope cutthroat trout at a very high frequency (0.974). This indicates that this population is genetically distinct from the other populations that we have examined, and thus, represents an extremely valuable resource.

We have not detected many pure populations of westslope cutthroat trout among the numerous samples that we have analyzed from western Montana. Most populations suspected to be pure westslope cutthroat trout also contain rainbow or Yellowstone cutthroat trout genetic material. The available data indicate that the westslope cutthroat is in danger of extinction. In order to ensure the continued existence of this native species, it is important to preserve all pure populations that are identified.

Sincerely,

r

X4& f rjUu

Robb F. Leary Genetics Laboratory

/

(JW.ft

Fred W. Allendorf Professor

H

RFL/pkf Enclosures

Equal Opportunity in Education and Employment

Enzyme

TABLE 1 Loci and enzymes examined (E=eye, L=liver, M=muscle)

Loci

Tissue

Adenylate kinase (AK) Alcohol dehydrogenase (ADH) Aspartate aminotransferase (AAT)

Creatine kinase (CK)

Glucose phosphate isomerase (GPI) Glyceraldehyde-3-phosphate dehydrogenase (GAP) Glycerol-3-phosphate dehydrogenase (G3P) Glycyl-leucine Peptidase (GL) Isocitrate dehydrogenase ( I OH )

Lactate dehydrogenase (LDH)

Leucyl-glycyl-glycine peptidase ( LGG ) Malate dehydrogenase (MDH)

Malic enzyme (ME)

Phosphoglucomutase (PGM) 6-Phosphogluconate dehydrogenase (6PG) Sorbitol dehydrogenase (SDH) Superoxide dismutase (SOD) Xanthine dehydrogenase (XDH)

Note: The protein products of the pairs of loci in ( ) are electrophoretically indistinguishable. Thus, they are considered to be single tetrasomic loci in all analyses.

Akl,2	M
Adh	L
Aatl,2	L
Aat(3,4)	M
Ckl,2	M
Ck3,CkCl,2	E
Gpil,2,3	M
Gap3,4	E
G3pl,2	L
Gil, 2	E
Idhl,2	M
Idh3,4	L
Ldhl,2	M
Ldh3,4,5	E

Lgg

Mdh(l,2)	L
Mdh(3,4)	M
Mel, 2, 3	M
Me4	L
Pgml,2	M
6Pg	M
Sdh	L
Sod	L
Xdh	L

TABLE 2

Loci that can be used to differentiate rainbow, westslope cutthroat, and Yellowstone cutthroat trout. Alleles are designated as the proportional migration distance in the gel relative to the distance traveled by the common allele in rainbow trout which is given a mobility of 100.

Alleles

Loci Rainbow Westslope Yellowstone

Aatl 100 200,250 165

Ck2 100 84 84

CkCl 100,38 100,38 38

Gil 100,115,90 100 101

Gpi3 100 92 100

Idhl 100 100 -75

Idh3,4 100,114,71,40 100 , 86 , 71 , 40 , Null 100,71

Lgg 100,135 100 135

Mel 100,55 88 100

Me3 100,75 100,75 90

Me4 100 100 110

Pgml 100, Null 100, Null Null

Sdh 100,200,40 40,100 100

TABLE 3

Allele frequencies at the variable loci in the German Gulch Creek population of westslope cutthroat trout.

Locus Alleles Frequencies

CkCl 100 0.885

38 0.115

Gap4 100 0.974

Null 0.026

Idh3 71 0.974

Null 0.026

Idh4 100 0.321

40 0.679

Ldh4 100 0.974

112 0.026

Mdhl,2 100 0.942

125 0.013

40 0.045

Proportion Polymorphic Loci 0.143

Average Heterozygosity 0.024

APPENDIX B

GUIDELINES FOR USING THE WETTED PERIMETER

(WETP) COMPUTER PROGRAM

OF THE

MONTANA DEPARTMENT OF FISH, WILDLIFE AND PARKS

By

Frederick A. Nelson

Montana Department of Fish, Wildlife and Parks

8695 Huffine Lane

Bozeman, Montana 59715

Rovi sod luly, 1984

TABLE OF CONTENTS

INTRODUCTION 1-1

DERIVING RECOMMENDATIONS USING WETTED PERIMETER 2-1

DESCRIPTION OF THE WETP PROGRAM 3-1

FIELD DATA REQUIREMENTS 4-1

FIELD METHODS 5-1

Equipment 5-1

Selecting Study Areas and Placing Cross-sections 5-3

Establishing Bench Marks 5-3

Surveying Techniques 5-3

Measuring Water Surface Elevations 5-4

Measuring Stream Discharges 5-4

Measuring Cross-sectional Profiles 5-5

OFFICE METHODS 6-1

WETP Data Format 6-1

Selecting Flows of Interest 6-1

WETP Data Output 6-2

OTHER USES FOR THE WETP OUTPUT 7-1

FINAL CONSIDERATIONS 8-1

LITERATURE CITED 9-1

APPENDICES

A. Calculation of stage height at zero flow (zf) from Rantz (1982) IS. Example of WETP input format C. Example of WETP data output

INTRODUCTION

The vetted perimeter and discharge relationships for selected channel cross-sections are a useful tool for deriving instream flow recommendations for the rivers and streams of Montana. Wetted perimeter is the distance along the bottom and sides of a channel cross-section in contact with water (Figure 1). As the discharge in a stream channel decreases, the wetted perimeter also decreases, but the rate of loss of wetted perimeter is not constant throughout the entire range of discharges. Starting at zero discharge, wetted perimeter increases rapidly for small increases in discharge up to the point where the stream channel nears its maximum width. Beyond this break or inflection point, the increase of wetted perimeter is less rapid as discharge increases. An example of a wetted perimeter-discharge relationship showing a well-defined inflection point is given in Figure 2. The instream flow recommendation is selected at or near this inflection point.

The MDFWP developed in 1980 a relatively simple wetted perimeter predictive fWKTP) computer model for use in its instream flow program. This model eliminates the relatively complex data collecting and calibrating procedures associated with the hydraulic simulation computer models in current use while providing more accurate and reliable wetted perimeter predictions.

The WKTP computer program was written by Dr. Dalton Burkhalter, aquatic consultant. 1429 S. 5th Ave., Bozeman, Montana 59715. The program is written in FORTRAN IV and Is located at the computer center, Montana State University, Bozeman. Direct all correspondence concerning the program to Fred Nelson' Montana Department of Fish, Wildlife and Parks, 8695 lluffine Lane, Bozeman, Montana 59715.

1-1

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190-

180-

170-

160-

150-

200 400 600 800 1000

FLOW (cfs)

1200

1400

1600

Figure 2. An example of a relationship between wetted perimeter and fl for a riffle cross-section.

1-3

ow

DERIVING REG0MMENDAT10NS USING WETTED PERTMETER

When formulating flow recommendations for a waterway, the annual flow cycle Is divided into two separate periods. They consist of a relatively brief runoff or high flow period, when a large percentage of the annual water yield is passed through the system, and a nonrunoff or low flow period, which is characterized hy relatively stable base flows maintained primarily by groundwater outflow. For headwater rivers and streams, the high flow period generally includes the months of May, June and July while the remaining months encompass the low flow period.

Separate instream flow methods are applied to each period. Further, it is necessary to classify a waterway as a stream or river and to use a somewhat different approach when deriving low flow recommendations for each. A waterway is considered a stream if the mean annual flow is less than approximately 200 cfs.

Method for the Low Flow Period - Streams

The wetted perimeter/inflection point method is presently the primary method being used by the MDFWP for deriving low flow recommendations for streams. This method is primarily based on the assumption that the food supply is a major factor influencing a stream's carrying capacity (the numbers and pounds ot fish that can be maintained indefinitely by the aquatic habitat). The principal food of many of the juvenile and adult game fish inhabiting the streams of Montana is aquatic invertebrates, which are primarily produced in stream riffle areas. The method assumes that the game fish carrying capacity is proportional to food production, which in turn is proportional to the wetted perimeter in riffle areas. This method is a slightly modified version of the Washington Method (Collings, 1972 and 1974), which is based on the premise that the rearing of juvenile salmon is proportional to food production and in turn is proportional to the wetted perimeter in riffle areas. The Idaho Method (White and Gochnauer, 1975 and White, 1976) is also based on a similar premise.

The plot of wetted perimeter versus flow for stream riffle cross-sections generally shows two inflection points, the uppermost being the more prominant . In the example (Figure 3) , these inflection points occur at approximate flows of 8 and 12 cfs. Beyond the upper inflection point, large changes in flow cause only very small changes in wetted perimeter. The area available for food production is considered near optimal beyond this point. At flows below the upper inflection point, the stream begins to pull away from the riffle bottom until, at the lower inflection point, the rate of loss of wetted perimeter begins to rapidly accelerate. Once flows are reduced below the

2-1

10 15

FLOW (CFS)

20

25

30

Figure 3. An example of a relationship between wetted perimeter and flow for a stream riffle cross-section.

2-2

lower Inflection point, the riffle bottom is being exposed at an accelerated rate and the area available for food production greatly diminishes.

The wetted perimeter-f low relationship may also provide an index of other limiting factors that influence a stream's carrying capacity. One such factor is cover. Cover, or shelter, has long been recognized as one of the basic and essential components of fish habitat. Cover serves as a means for avoiding predators and provides areas of moderate current speed used as resting and holding areas by fish. It is fairly well documented that cover improvements will normally increase the carrying capacity of streams, especially for larger size fish. Cover can be significantly influenced by streamflow.

Tn the headwater streams of Montana, overhanging and submerged bank vegetation are important components of cover. The wetted perimeter-flow relationship for a stream channel may bear some similarity to the relationship between bank cover and flow. At the upper inflection point, the water begins to pull away from the banks, bank cover diminishes and the stream's carrying capacity declines. Flows exceeding the upper inflection point are considered to provide near optimal bank cover. At flows below the lower inflection point, the water 1s sufficiently removed from the bank cover to severely reduce its value .is fish shelter.

It has been demonstrated that riffles are also critical areas for spawning sites of brown trout and shallow inshore areas are required for the rearing of brown and rainbow trout fry (Sando, 1981). It is therefore assumed that, in addition to maximizing bank cover and food production, the flows exceeding the upper inflection point would also provide the most favorable spawning and rearing conditions.

Riffles are the area of a stream most affected by flow reductions (Bovee, 1974 and Nelson, 1977). Consequently, the flows that maintain suitable riffle conditions will also maintain suitable conditions in pools and runs, areas normally inhabited by adult fish. Because riffles are the habitat most affected by flow reductions and are essential for the well-being of both resident and migratory fish populations, they should receive the highest priority for instream protection.

The wetted perimeter/inflection point method provides a range of flows (between the lower and tipper inflection points) from which a single instream flow recommendation can be selected. Flows below the lower inflection point are judged undesirable based on their probable impacts on food production, hank cover and spawning and rearing habitat, while flows exceeding the upper inflection point are considered to provide a near optimal habitat for fish. The lower and upper inflection points are believed to bracket those flows needed to maintain the low and high levels of aquatic habitat potential. These flow levels are defined as follows:

2-3

1. High Level of Aquatic Habitat Potential - That flow regime which will consistently produce abundant, healthy and thriving aquatic populations. In the case of game fish species, these flows would produce abundant game fish populations capable of sustaining a good to excellent sport fishery for the size of stream involved. For rare, threatened or endangered species, flows to accomplish the high level of aquatic habitat maintenance would: ]) provide the high population levels needed to ensure the continued existence of that species, or 2) provide the flow levels above those which would adversely affect the species.

2. Low Level of Aquatic Habitat Potential - Flows to accomplish a low level of aquatic habitat maintenance would provide for only a low population of the species present. In the case of game fish species, a poor sport fishery could still be provided. For rare, threatened or endangered species, their populations would exist at low or marginal levels. Tn some cases, this flow level would not be sufficient to maintain certain species.

The final flow recommendation is selected from this range of flows by the fishery biologist who collected, summarized and analyzed all relevant field data for the streams of interest. The biologist's rating of the stream resource forms the basis of the flow selection process. Factors considered In the evaluation include the level of recreational use, the existing level of environmental degradation, water availability and the magnitude and composition of existing fish populations. The fish population information, which is essential for all streams, is a major consideration. A marginal or poor fishery would likely justify a flow recommendation at or near the lower inflection point unless other considerations, such as the presence of species of special concern (arctic grayling and cutthroat trout, for example), warrant a higher flow. Tn general, only streams with exceptional resident fish populations or those providing crucial spawning and/or rearing habitats for migratory populations would be considered for a recommendation at or near the upper inflection point. The process of deriving the flow recommendation for the low flow period thus combines a field method (wetted perimeter/inflection point method) with a thorough evaluation by a field biologist of the existing stream resource.

It is recommended that at least three and preferably five riffle cross-sections are used In the analysis. The final flow recommendation is derived by averaging the recommendations for each cross-section, or the computed wetted perimeters for all riffle cross-sections at each flow of interest averaged and the recommendation selected from the wetted perimeter-flow relationship for the composite of all cross-sections. The latter method is preferred.

A study evaluating the wetted perimeter/inflection point method for small trout streams was completed at the Cooperative Fisheries Research Unit, Montana State University, as a thesis project (Randolph and White, 1984). An

2-k

Innovative approach in which stream sections were isolated with weirs and wild rainhow trout added during the high flow period, saturating the habitat, was used. Changes in trout carrying capacity, as determined by the movement of trout out of the sections, were measured as the flow decreased. The derived relationships between flow and trout carrying capacity were then compared to the relationships between flow and various habitat parameters, including the riffle wotted perimeter. The authors reported that in the pool-riffle habitats of their study stream the wetted perimeter/inflection point method worked well, while in run-riffle habitats the method underestimated the flow that was needed to maintain rainbow trout at a reasonable level. In no case did the method overestimate the summer instream flow needs.

Method for the Low Flow Period - Rivers

The Montana Department of Fish, Wildlife and Parks completed a study in 1980 that validated the wetted perimeter method as applied to the trout rivers of southwest Montana (Nelson, 1980a, 1980b and 1980c). In this study, the actual trout standing crop and flow relationship were derived from long-term data collected for five reaches of the Madison, Gallatin, Big Hole and Beaverhead Rivers, all nationally acclaimed wild trout fisheries. These relationships provided a range of flow recommendations for each reach. Flows less that the lower limit were judged undesirable since they led to substantial reductions of the standing crops of adult trout or the standing crops of a particular group of adults, such as trophy-size trout. Flows greater than the upper limit supported the highest adult standing crops during the study period. Flows hetween the lower and upper limits are broadly defined as those flows supporting intermediate standing crops or those standing crops that normally occur within each reach. The final recommendation was selected from this range of flows.

The range of flows derived from the trout-flow relationships for the five river reaches were compared to those derived from the wotted perimeter method as applied to riffle areas. The study results showed that the inflection point flows had a somewhat different impact on the trout standing crops of rivers than previously assumed for streams. For rivers, the flow at the upper inflection point is a fairly reliable estimate of the lower limit of the range of flows derived from the trout-flow relationships or, in other terms, flows loss than the upper inflection point are undesirable as recommendations since they appear to lead to substantial reductions of the standing crops of adult trout .

The flow at the upper inflection point is not necessarily the preferred recommendation for all trout rivers. The "Blue Ribbon" rivers may require a higher flow in order to maintain the sport fishery resource at the existing level. In general, flows less than the upper inflection point are undesirable as tlow recommendations regardless of the rating of the river resource.

2-5

DF.SCRTPTTON OF THE WETP PROGRAM

The WKT1' program uses ? to 10 sets of stage (water surface elevation) measurements taken .it different known discharges (flows) to establish a rating curve. Tliis curve has the equation, 0 = p(S - zf)n where:

0 = discharge

S = stage height

zf = stage height at zero flow

p = a constant

n = a constant exponent.

The relationship of measured points, if perfect, would plot as a straight line on log - log paper with r equal to the slope of the line and p equal to the discharge when (S - zf) 1. The actual line is determined by least squares regression using the measured points. Once the stage-discharge rating curve for each cross-section is determined, the stage at a flow of interest can be predicted. This rating curve, when coupled with the cross-sectional profile, is all that is needed to predict the wetted perimeter at most flows of interest .

The stage height at y.oro Flow (zf) may be taken as the lowest elevation on the cross-sectional prolile for riffles but is more diffic.lt to determine for non-ntflesi, particularly pools, in which case the procedures of Rantz (1982) should be consulted. The applicable portions of that paper are included in Appendix A.

The zf value for a non-riffle cross-section can also be measured in the field II is the highest elevation of the thalweg (as referenced to the bench mark elevation) at the downstream control, which is typically the head of a riffle The control is a channel feature which causes water to backup in an upstream

di reel ion.

The value of zf is controlled by use of an option record (OPTS) in the input uata. M the option is set to one, zf is either set to a value supplied bv the us,., or in the absence of a supplied value, zf is automatically set to the lowest elevation in the cross-sectional profile. If the user does not want zf to equal the lowest elevation in the cross-sectional profile, the values t"< zf are entered on the XSEC records. The option record must be the first entry in the data file and is illustrated in Appendices B and C.

rhe option of setting zf to zero by setting the option record to zero is also available. Prior to this program revision, all results were obtained with zf automatically set to zero. Option zero is included solely for the purpose of comparing results. Because the program now incorporates zf into the calculations, the accuracy of the hydraulic predictions for those flows of

3-1

interest tliat are less tlian the lowest measured calibration flow should improve over calculations previously made with zf = 0.

The program should be run using three sets of stage-di scharge data collected at a high, intermediate and low flow. Additional data sets are desirable, but not necessary. The three measurements are made when runoff is receding (high flow), near the end of runoff (intermediate flow) and during late summer-early fall (low flow). The high flow should be considerably less than the bankfull flow, while the low flow should approximate the lowest flow that normally occurs during the summer-fall field season. Sufficient spread between the highest and lowest calibration flows is needed in order for the program to compute a linear, sloping rating curve.

The WETP program will run using only two sets of stage-discharge data. This practice is not reconmended since substantial "two-point" error can result.

In addition to wetted perimeter (WETP), the program also predicts other hvdraullc characteristics that can be used in deriving flow recommendations for selected time periods and life I unctions. These are the moan depth (DRAT) in ft, mean velocity CVHAP.) in ft/sec, top width (WDTH) in ft, cross-sectional area (AREA) in ft', stage (STCE) in ft, and maximum depth (DMAX) in ft.

A useful program option, termed the width-at-given-depth (WAGD) option, will calculate for up to 10 given depths the width (in ft) and percentage of the top width having depths greater than or equal to the given values. The width and percentage of the longest, continuous segment having the required depths is also listed for each flow of interest. This option is illustrated in Appendices B and C.

FIELD DATA REQUIREMENTS The required inputs to the WETP program for each cross-section are:

1. Three sets of stage-discharge data measured at a high, intermediate and low flow. The stage height at zero flow (zf) is mandatory only when the program is applied to non-riffle areas.

2. The cross-sectional profile which consists of channel elevations (vertical distances) and the horizontal distance of each elevation measurement from the headstake Czero point). Up to 150 sets of measurements per cross-section are accepted hy the program.

The following are needed to document field work:

1 . Slides or photographs of the study area and cross-sections at the time field data are collected.

7. Field notebooks containing all surveying data, notes and calculations, recorded in a neat, consistent manner.

4-1

FIELD METHODS Equipment

I. Level (a self-leveling or automatic level such as a Wild NAK1 is preferred).

?. 25-ft, telescoping, fiberglas level rod.

3- c°Hb0"«eV°oT, 'ft! " """ SUl"ble "MS"rI"8 "■»• ■*<"" Sh™" »*

4. Rebar cut in 30-incl, pieces (stakes). Two stakes are needed per

cross-section. F

5. Tv/o clamps (modified vise grips with flat jaws).

6. Engineers field notebook.

7. Pencils.

K,

Current meter and rod, stopwatch and beeper box. Gurley or Price AA current meters are preferred. A Marsh-McBirney instantaneous readout

IZlTl a "X*"* Can ^ US6d ^ Pl3Ce °f 3 Gurle^ or Prlce ^ "eter, provided the instantaneous meter is correctly calibrated.

9. Small sledge hammer.

10. Camera.

11 12

Fluorescent spray paint and flagging.

Forms for recording stream discharges and cross-sectional profiles.

13. A rod fitted with a porcelain, enameled, iron gage (Part No. 15405 Leupold and Stevens, Inc., P.O. Box 688, Beaverton, Oregon 97075) for measuring water depths. A current meter rod can be substituted

Selecting Study Areas and Placing Cross-sections

Follow these guidelines when selecting study areas and placing cross-sections.

I- It is best to locate study areas and stake cross-sections durinc low water prior to the onset of runoff. It will be difficult to .pW ^ sites during the high water period when data collection begins ^ theSG

2. Place the cross-sections in riffle area.; If n,„ .. j ""-"'"""-'»» P°'»' -** »"> be"-, " derive'rece^pdat^

5-1

5.

8.

"eCtlr0nS Ca" bE Placed ln a sJn*le riff le or a number of different rif es Cross-sections should describe the typical riffle habitats within the stream reach being studied. Other critical habitat tv also be used, depending on your chosen method. ™

?h^bt%eastrl3ffied USlfng LV0 Cr°SS-SeC t±0nS- IC is -contended that at least 3 and preferably 5 riffle cross-sections are used The program accepts 1 to 10 cross-sections per study area.

Ihe WETP model assumes that the water surface elevations at the water's edge on the left bank (WEL) and right bank (WER) of a cros -section ar^ always equal at a given flow. This is a valid assumption since the water surface elevations at WEL and WFF. generally remain within 0. If t of each other as the flow changes, provided the water surface eleva ions at WEL and WER were matched when the cross-section was established Avoid pacing cross-sections in areas where this assumption is like y to be Isl n ^ ' TfCh T SharP bendS ? rlVPrS ^ mu]tiP^ channels con'tainin:

Place the headstake marking each cross-section well up on the bank

addition t M6 alm°St flUSh Wlth the gr°Und and m-k -11 In

addttion to marking the cross-section, the headstake is also your zero

reference point for measuring horizontal distances across the cross-section. Headstakes for all the cross-sections within a study area should be located on the same bank. V

Another stake is driven directly across from the headstake on the opposite bank Place this stake so that the water surface elevations at

withTn o"' ft °fTMC 'V'"18^ —-section are equal or SiUr (w thin 0.0J it). Ibis will require the use of a level and level rod

1 stake is used to mark the cross-section on the bank opposite the headstake and also to attach the measuring tape when the channel prof le is measured, so should not be driven to ground level. Cross-section' when established, should be roughly perpendicular to the banks! SeCti°tU"

6. Number the cross-sections consecutively from downstream to upstream (the downstream-most cross-section is #1). upstream (the

Measure the distances between cross-sections. This is an optional measurement that might be useful in locating cross-sections during're^n

Remember, the WETP model is invalidated if channel changes occur in the study area during the data collecting process. For this reason the collection of all field data should be completed during S per beginning when runoff is receding and ending with the onset of runorf the

5-2

following year. The stream channel is expected to he stable during this period .

Establishing Bench Marks

Establish a bench mark at or near your study area. The bench mark is a point that will not be disturbed or moved. A nail driven into the base of a tree, a fixed spot on a bridge abutment and a survey stake driven into the ground are examples of bench marks. Designating one of the cross-sectional headstakes within a study area as the bench mark is an acceptable practice. Bench marks should be well marked and described in your field notebook so they can be easily located during return trips. All channel and water surface elevations are established relative to the bench mark, which is assigned an elevation of 100.0(1 or 10.00 ft. Use 10.00 ft whenever possible.

For streams having "heavy" vegetative cover, the use of a single bench mark may not be practical. In this case, the individual headstakes can be used as bench marks. For example, the headstake for cross-section #1 could serve as the bench mark for cross-sections #1 and 2, while the headstake for cross-section #3 could serve as the bench mark for cross-sections #3, 4 and 5. F.ach headstake could also serve as the bench mark for that individual cross-section. While this is not the best surveying technique, certain stream reaches may require its use. Be sure to carefully record in your notebook which headstakes are used as bench marks to avoid confusion and errors on return trips.

Remember, channel and water surface elevations for all cross-sections within a study area do not have to be tied to a single bench mark for the WETP program to run properly. However, the use of a single bench mark enhances your field technique.

Surveying Techniques

The reader is referred to Spence (1075) and Bovee and Milhous (1978) for a discussion of the surveying techniques used to measure cross-sectional profiles and water surface elevations. Both papers should be read by those unfamiliar with the mechanics of surveying. All investigators must receive field training before attempting any measurements.

It is Important to be consistent and to use good technique when collecting and recording data. Record all data in your notebook and complete all calculations while in the field, so that any surveying errors can be detected and corrected. Remember, your field notebooks may be examined in court or hearing proceedings. Good quality equipment such as an automatic level is also an asset.

5-3

Measuring Water Surface Elevations (Stages)

Water surface elevations should be measured for each cross-section at three different flows. If cross-sections are established prior to runoff, then you must return to the study area at least three more times, when runoff is receding (high flow), near the end of runoff (intermediate flow) and during late summer or early fall (low flow).

It should be noted that it is unnecessary to collect surface elevation measurements for all of the cross-sections within a study area at the same flows. For example, if another cross-section is added to the study area at a later date, the calibration flows for this new cross-section do not have to match those for the remaining cross-sections. It is also unnecessary to have the same number of calibration flows for all of the cross-sections within a study area.

Water surface elevations are measured at the water's edge directly opposite the stake marking the cross-section on each bank. The stretching of a tape across the cross-section is unnecesary, since the horizontal distances from the headstake to the WEL and WER are not needed. Measure water surface elevations to the nearest 0.01 ft. The mechanics of this measurement are discussed in Bovee and Milhous (1978). Once water surface elevations are calculated, repeat the measurements and check for surveying errors. If a single bench mark is used, then water surface elevations should increase with the upstream progression of cross-sections.

As previously discussed, the WETP model assumes that the water surface elevations at WEL and WER are always equal at a selected flow of interest. In a stream channel, the surface elevations at the WEL and WER of a cross-section should remain fairly equal as the flow varies, provided the elevations at WEL and WER were matched when the cross-section was established. Consequently, it is necessary to measure the water surface elevations at both WEL and WER during all return trips to verify this assumption. These two measurements should always be within approximately 0.1 ft of one another. For the larger waterways, a greater difference is allowable. Average these two measurements to obtain the water surface elevation that Is entered on the coding sheets.

Measuring Stream Discharges

The flow through the study area must be measured each time water surface elevations are determined. On the larger waterways, it is best to locate study areas near USCS gage stations to eliminate a discharge measurement.

Use standard USGS methods when measuring discharges. Publications of Bovee and Milhous (1978), Buchanan and Somers (1969), and Smoot and Novak (196R) describe these methods and provide information on the maintenance of current meters. Read these publications before attempting any discharge measurements. Field training is also mandatory.

5-4

Measuring Cross-sectional Profiles

The channel profile has to be determined for each cross-section. Unlike the measuroinent of water surface elevations, this has to be done only once. It is best to measure profiles at the lowest calibration flow when_wading is easiest. For the unwadable, larger waterways that require the use of a boat, profiles are best measured at an intermediate calibration flow.

For wadable streams, a measuring tape is stretched across the cross-section with the zero point set on top of the headstake. Setting the headstake at zero, while not mandatory, is a good practice that provides consistency in your field technique. Never attach the tape directly to the headstake. The tape is attached with a vise grip to a stake that is driven behind the headstake. A vise grip can be attached directly to the stake on the opposite bank to stretch and hold the tape in place.

Elevations are now measured betweeen the headstake and water's edge using the level rod. Elevations are measured at major breaks in the contour. The horizonatal distance of each elevation measurement from the headstake (zero point) is also recorded. Elevations are also measured between the water's edge at the opposite bank and the opposite stake and the horizontal distance from the headstake recorded for each measurement. Elevations of the exposed portions of instream rocks and boulders are also measured in this manner. Measure elevations to the nearest 0.01 ft and horizontal distances to the nearest 0.1 ft.

Be sure to collect profile measurements for points well above the water's edge. It is a good practice, although not mandatory, to begin at the headstake (0.0 distance) and end at the stake on the opposite bank. Remember, the highest elevations on both banks of the cross-sectional profile must be substantially higher than the stage at the highest calibration flow, if predictions are to be made for flows of interest that exceed the highest calibration flow.

For the segment of the cross-section containing water, a different approach involving the measurement of water depth is used. Water depth is measured using a current meter rod or a rod fitted with a porcelain, enameled, iron Rage. Do not use your level rod. Measure depths at all major breaks in the bottom contour. Generally, 10-30 depth measurements are needed for streams and creeks. Measure depths to the nearest 0.05 ft (current meter rod) or 0.01 it (rod fitted with gage). For each depth measurement, record the horizontal distance from the headstake (zero point). The bottom elevation at each distance from the headstake is determined by subtracting the water depth from the water surface elevation (average for WEL and WER) . For example, if the average water surface elevation is 9.26 ft and at 10.2 ft from the headstake the water depth is 0.90 ft, then the bottom elevation at this distance is 8.36 ft (9.26 ft minus 0.90 ft). The elevations for all points covered by water are calculated in this manner.

5-5

using'" boItdabd:n,t,'arRerHWaterWfyS' —-Clonal profiles arc .ensured describe ^\eZVe *" *"» "^ G™h™ "nd ^ ^978)

The WETP program will handle vertical hanks. When recording these data the

ve°r ic°" 'will heTH6 ^ T ^^ t0 b°th ^ *°P and bottom of' h vertical will be the same, but the elevations will be different.

The program will not handle undercut banks. These data have to be adiusted before being entered on the coding sheets. The best method is to treat

distance to the ton of H °„ ""^^ 1S substitut^ for the horizontal distance to the top of the undercut, creating a vertical bank.

The program will handle islands, bars and multiple channels, provided the these areas should be avoided when establishing cross-sections. "nlikely«

5-6

OFFICE METHODS WETP Data Format

An example describing the WETP format is given in Appendix B. Much of the form.it is self-explanatory. Carefully examine this example and the explanatory notations before attempting to code your data on the coding sheets.

The five cross-sections in the example were located in riffles. The stage height at zero flow (zf) was therefore set to the lowest elevation in the cross-sectional profile for each.

All elevations in the example were established relative to a single bench mark, which was assigned an elevation of 100.00 ft for illustration only. A bench mark elevation of 10.00 ft would be more appropriate and should be used whenever possible.

Enter the WETP data on the coding sheets in the following manner:

1. Flows of interest (up to 100 flows are accepted by the program)

Integers in cfs or with decimal points (not to exceed six characters, including decimal point, if used)

2. Cross-sectional profile data (up to 150 sets of measurements are accepted)

Distances from headstake - nearest 0.1 ft Channel elevations - nearest 0.01 ft

3. Stage-discharge data (2 to 10 sets of measurements are accepted)

Stages (water surface elevations) - nearest 0.01 ft Discharges (flows) - nearest 0.1 cfs

4. Stage height at zero flow (zf) data (1 for each cross-section if desired)

zf - nearest 0.01 ft

If the cross-sectional profile, stage-discharge and zf data are entered in the above manner, decimal points are not needed. However, decimal points can be used if desired.

Selecting Flows of Interest

You will be extrapolating data for flows of interest that are less than the lowest measured calibration flow for a particular cross-section. The

6-1

extrapolation of data beyond the highest calibration flow is a less desirable option since our main interest is to derive minimum flow recommendations. Remember, the stage-discharge rating curve generally flattens out at extremely high (above bankfull) and extremely low flows. At these flows, the predicted stages from the measured rating curve are inaccurate and will lead to inaccurate hydraulic predictions.

Use the following guidelines when selecting flows of interest (Bovee and M: lhous, ] 978) :

1. Two point stage-discharge rating curve

Hydraulic predictions should not be made for flows which are less than 0.77 times the minimum measured flow, nor for flows higher than 1.3 times the maximum measured flow.

2- Three point (or greater) stage-discharge rating curve

Hydraulic predictions should not be made for flows which are less than 0.4 times the minimum measured flow, nor for flows higher than 2.5 times the maximum measured flow.

WETP Data Output

The output for the input example in Appendix B is given in Appendix C Carefully examine this output.

When reviewing your outputs, consider the following: 1 . Errors

Carefully check the profile and stage-discharge data on the printouts for errors. The keypunch operators occasionally make errors, even though they carefully proof the data files. The vast maloritv of errors, however, are the result of format and recording errors on the coding sheets. If corrections are needed, mark all changes on the coding sheets in red ink or pencil and return to Fred Nelson so the file can be corrected and your data rerun.

2. Error messages

The vast majority of error messages that occasionally appear on the

printouts are a result of undetected format errors on the coding sheets

These are easily corrected and the file rerun before the printout is sent to the cooperator.

An error message will appear when predictions are requested for flows of Interest having stages higher than the highest elevations in the

6-2

cross-sectional profile. Additional profile measurements collected higher up on the banks will correct this problem, if deemed necessary.

r2 values

If the r2 value for a stage-discharge rating curve is less than approximately 0.90, the cross-section should be eliminated from the analysis. Low r2 values may be due to errors, so recheck the stage and discharge measurements before eliminating these cross-sections. For those cross-sections having only two sets of stage-discharge measurements (remember, this practice is not recommended), r2 values are automatically 1.000 and consequently of no use in assessing the reliability of the hydraulic predictions.

6-3

OTHER USES FOR THE WETP OUTPUT

The wetted perimeter/inflection point method, as previously described, is the primary method the MDFWP is presently using to derive instream f recommendations for the waterways of Montana. The WETP program and output can also be used in other ways for deriving recommendations. Some of these uses are discussed in the following examples.

Passage of Migratory Trout

Many streams, particularly those in northwest Montana, provide important spawning and rearing habitats for migratory salmonids. Efficient stream ows are needed not only to maintain the spawning and rearing habitats but .lso to pass adults through shallow riffle areas and other natural barriers while moving to their upstream spawning areas. carriers

Trout passage criteria relating to stream depth have been developed in Oregon and Colorado (Table 1). These criteria, when used in conjunction with the

nows° C exUl rifflG areaS' C3n ^ USGd t0 derlve -lnl»™ P- W IHli'f/f eX.ample' 0PftaSfSa8e "iterla developed by the Colorado Division of W lid fe for streams 70 ft and wider indicate that the minimum average depth needed to pass trout through riffles is 0 5-0 6 fr Tfca „ , -7 u Tobacco River (Table 2) shows that the^-ver.^Vpth f« sTf iJWf It cross-sections exceeds 0.5 ft, the approximate minimum average depth required for pass age, at a flow of approximately 120 cfs. A flow of at lest is therefore recommended during the spawning period to facilitate the Passage of adult trout to upstream spawning areas. Passage

Table 1. Trout passage criteria (from Wesche and Rechard, 1980).

Species Large Trout 20 inches

Source

Thompson

1972

Minimum Depth (ft) 0.6

Average Depth (ft)

Where

Developed

Oregon

Other Trout 20 inches

Thompson 1972

0.4

Oregon

Trout

(on streams 20 ft or greater)

Colo. Div. of Wild. 1976

0.5-0.6

across

riffles

Colorado

Trout

(on streams 10-20 ft wide)

Colo. Div. of Wild. 1976

0.2-0.4

across

riffles

Colorado

7-1

44	.65	.79	.68	.47
49	.69	.85	.72	.52
54	.73	.91	.75	.57

Table 2. Average depths for five riffle cross-sections in the Tobacco River, Montana, at selected flows of interest. Average depths were derived using the WETP computer program.

Average Depth (ft)

Flow (cfs) Riffle Riffle Riffle Riffle Riffle cs #1 cs #2 cs //3 cs #4 cs #5

Too

110

120 i

The minimum depth criteria developed in Oregon could also be used in conjunction with the WAGD option of the WETP program to derive passage recommendations. For this evaluation, criteria are developed requiring at least a certain percentage of the top width of a cross-section to have water depths greater than or equal to the minimum needed for fish passage. In Oregon, at least 25% of the top width and a continuous portion equaling at least 10% of the top width are used (Thompson, 1972). The flow that satisfies these criteria for all cross-sections is recommended.

Coose Nesting Requirement

The maintenance of adequate flows around islands selected by Canada geese for nesting is necessary to insure that the nests are protected from mammalian predators. Under low flow conditions, these predators have easy access to the islands and can significantly reduce goose production. The security of the islands is a primary factor in their selection as nest sites by geese. This security is provided by adequate side channel flows, which are a function of depth, width, and velocity. Since wetted perimeter is a function of both width and depth, its relationship to discharge is believed to be the best Indicator of the minimum flows that are needed to maintain secure nesting islands.

The wetted perimeter/inflection point method is applied to the shallowest area of the side channel bordering each nesting island. A wetted perimeter-side channel discharge curve is generated for each cross-section and the inflection point determined. A curve correlating the side channel flow to the total river flow is also derived during the field season. From these curves, the total river discharge that would provide the inflection point flow in each side channel is determined. The final recommendation is derived by averaging the recommendations for each island or choosing the river flow that would maintain at least the inflection point flow around all the islands being sampled in the study area. The latter method is preferred.

7-2

Depth and width criteria could also be developed and used in conjunction with the WACD option of the WETP program to formulate flow recommendations for nesting.

Maintenance of Spawning and Rearing Habitats in Side Channels

Side channels provide important and sometimes critical spawning and rearing habitats for many cold and warm water fish species. The maintenance of tbese habitats is dependent on adequate side channel flows.

The wetted perimeter/inflection point method, when applied to the riffle areas of critical side channels, will provide a measure of the side channel flow that is needed to maintain the spawning and rearing habitats at acceptable levels. When this side channel recommendation is used in conjunction with a rurve correlating the side channel flow to the total river flow, the total river flow that would maintain adequate side channel flow can be determined.

This method is applied to a series of side channels and the final

recommendation derived by averaging the recommendations for each or choosing

the river flow that would maintain at least the inflection point flow in all the sampled side channels. The latter method is again preferred.

Recreational Floating Requirement

Minimum depth and width criteria have been developed for various types of boating craft by the Cooperative Instream Flow Service Group of the U.S. Fish and Wildlife Service (Hyra, 1978). These are listed in Table 3.

Table 3. Required stream width and depth for various recreation craft.

Recreation Craft Required Depth (ft) Required Width (ft) Canoe-kayak 0.5 A

Drift boat, row boat-raft 1.0 6

Tube 1.0 4

Power boat 3.0 6

Sail boat 3.0 25

These criteria are minimal and would not provide a satisfactory experience if the entire river was at this level. However, if the required depths and widths are maintained in riffles and other shallow areas, then these minimum conditions will only be encountered a short time during the float and the remainder of the trip will be over water of greater depths.

Cross-sections are placed in the shallowest area along the waterway. The WACD option of the WETP program is used to determine the flow that will satisfy the minimum criteria for the craft of interest. For example, if deriving a recommendation for power boats, the flow providing depths ° 3.0 ft for at

7-3

least a 6.0 ft, continuous length of top width is recommended. When a series of cross-sections are used, the results for each cross-section are analyzed IT" ! IL ^ the f l0W "tisfying the criteria for all cross-sections" if

recommended.

2£?H 7 X CT e*Panded "»ing additional criteria. For example, in addition to the above criteria for power boats, it can also be required that a certain percentage of the top width, such as 25%, has depths > 3.0 ft. Remember, you will have to justify all criteria used in your analysis

7-4

FINAL CONSIDERATIONS

Re sure to compare your instream flow recommend a t i oris to the water availability. For Raged streams, many summary flow statistics, such as the mean and median monthly flow of record, are available for comparison. For ungaged streams, instantaneous flow measurements collected by various state and federal agencies and simulated data are useful. The primary purpose is to determine if the recommendation is reasonable based on water availability. It is also desirable, for future planning, to define the period in which water in excess of the recommendation is available for consumptive uses and to quantify this excess.

It is common for the low flow recommendations for many of the headwater rivers and streams to equal or exceed the normal water availability for the months of November through March. This is the winter period when the natural flows are lowest for the year. These naturally occurring low flows, when coupled with the adverse effects of surface and anchor ice formation and the resulting scouring of the channel at ice-out, can impact the fishery. Consequently, water depletions during the winter have the potential to he extremely harmful to the ,-ilready stressed fish populations. For headwater rivers and streams, it is generally accepted that little or no water should be removed during the critical winter period if fish populations are to be maintained at existing levels.

The recommendations derived from the wetted perimeter/inflection point method only apply to the low flow or nonrunoff months. For the high flow or runoff period, flow recommendations should be based on those flows judged necessary for flushing bottom sediments and maintaining the existing channel morphology. This method, termed the dominant discharge/channel morphology concept (Montana Department of Fish and Came, 1979), requires at least ten years of continuous USCS gage records for deriving high flow recommendations, so cannot he applied to most streams.

8-1

LITERATURE CITED

Bovee, K. D. 1974. The determination, assessment and design of "instream value" studies for the Northern Great Plains region. Univ. of Montana Final Report. Contract No. 68-01-2413, Envir. Protection Agency. 204 pp.

Bovee, K. D. and R. Milhous. 1978. Hydraulic simulation in instream flow studies: theory and techniques. Cooperative Instream Flow Service Group, 2625 Redwing Rd . , Fort Collings, CO 80526. 131pp.

Buchanan, T. J. and W. P. Somers. 1969. Discharge measurements at gaging stations. Techniques of Water Resources Investigations of the United States Geological Survey, Book 3, Chapter A8.

Collings, Mike. 1972. A methodology for determining instream flow recommendations for fish. In Proceedings of Instream Flow Methodology Workshop. Washington Dept. of Ecology, Olympia, WA. pp. 72-86.

— . 1974. Generalization of spawning and rearing discharges

for several Pacific salmon species in western Washington. USGS, Open File Report. 39pp.

Colorado Division of Wildlife. 1976. Required instream flows Crystal River

AnJn n8 The Creek* °P6n Flle Letter' Colo«do Division of Wildlife, 6060 Broadway, Denver, CO 80216. 33pp.

Graham, P. J. and R. F. Penkal. 1978. Aquatic environmental analysis in the lower Yellowstone River. Montana Department of Fish, Wildlife and Parks Helena, MT 59620. 102pp. '

Hyra, R. 1978. Methods of assessing instream flows for recreation. Instream Flow Information Paper: No. 6. FWS/OBS - 78/34. 44pp.

Montana Department of Fish and Game, 1979. Instream flow evaluation for

Tf IT! tuZTl ^ ,the ?Per Mlssouri River basin. Montana Department offish, Wildlife and Parks, 1420 East Sixth Avenue, Helena, MT 59620.

Nelson F. A ,977. Beaverhead River and Clark Canyon Reservoir fishery study. Montana Department of Fish, Wildlife and Parks. 118pp.

1980a.

Evaluation of four instream flow methods applied u 1^7/ ^ , VGr ln Bouthwes' Montana. Montana Dept. of Fish, Wildlife and Parks, 8695 Huffine Lane, Bozeman, MT. 105PP.

9-1

. 1980b. Supplement to evaluation of four instream flow

methods applied to four trout river in southwest Montana. Montana Dept of Fish, Wildlife and Parks, 8695 Huffine Lane, Bozeman, MT. 55pp.

_ . 1980c. Evaluation of selected instream flow methods in

Montana. In Western Proceedings 60th Annual Conference of the Western Association of Fish and Wildlife Agencies. Western Division, American Fisheries Society. pp. 412-432.

Randolph C. L. and R. G. White. 1984. Validity of the wetted perimeter method for recommending instream flows for salmonids in small streams Research Project Technical Completion Report, Montana Water Resources Research Center, Montana State University, Bozeman, Montana. 103pp.

Rantz, S. E. (and others). 1982. Measurement and computation of streamflow Volume 2. Computation of discharge. Geological Survey Water-Supply Paper 2175. U.S. Government Printing Office, Washington, D. C.

Sando, S. K. 1981. The spawning and rearing habitats of rainbow trout and brown trout In two rivers in Montana. M.S. Thesis, Montana State University, Bozeman. 67pp.

Smoot, G. F. and C. E. Novak. 1968. Calibration and maintenance of

vertical-axis type current meters. Techniques of Water Resources

Investigations of the United States Geological Survey, Book 8, Chapter B2 .

Spence, L. E. 1975. Guidelines for using Water Surface Profile program to determine instream flow needs for aquatic life. Montana Dept. of Fish, Wildlife and Parks, Helena, MT 59620. Prelim. Draft. 22pp.

Thompson, K. E. 1972. Determining streamflows for fish life. In Proc. Instream Flow Requirement Workshop, Pacific NW River Basins"" Coram " Portland, OR. pp. 31-50.

Wesche, T. A. and P. A. Rechard. 1980. A summary of instream flow methods for fisheries and related research needs. Eisenhower Consortium Bulletin

9. Water Res. Research Inst., Univ. of Wyoming, Laramie, WY. 122

pp.

White, Robert G. 1976. A methodology for recommending stream resource maintenance flows for large rivers. In Proceedings of the Symp. and Spec. Conf. on Instream Flow Needs, ed. J. F. Orsborn and C. H. Allman. Vol. II, pp. 367-386. Amer. Fish. Soc, Bethesda, MD.

White, Robert and Tim Cochnauer. 1975. Stream resource maintenance flow studies. Idaho Dept. of Fish and Game and Idaho Coop. Fishery Research Unit Report. 136 pp.

305/os6. i9

9-2

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APPENDIX C

APPENDIX C Green and Bluegreen Algae German Gulch Creek

Station 1 (Below Beefstraight Creek)

Nostoc abundant

Oscillatorla rare

Closterium rare

Station 2 (Below Edward Creek)

Nostoc abundant

Oscillatoria rare

Closterium rare

Ulothrix rare

Station 3 (Mouth)

Nostoc sparse

Closterium rare

Ulothrix abundant

DIATOM COUNT DATA German Gulch Below Beefstraight Creek

Taxon

Relative Count Abundance

Achnanthes

lanceolata Breb. ex Kutz. 56 ^*^f

lanceolata var exlgua Grun. 8

minutissima Kutz.

11 2.7%

Araphipleura

pelluclda (Kutz.) Kutz. 1

Amphora

ovalis var pedlculus (Kutz.) V.H. ex DeT. T

perpusilla (Grun.) Grun. 1

2%

44	10.6%
1	.2%
11	2.7%
	T
1	.2%
10	2.4%

Caloneis

bacillum (Grun.) CI. 2 .5%

Cocconels

placentula Ehr.

placentula var euglypta (Ehr.) CI.

Cymbella

af finis Kutz.

cistula var. gibbosa Brun.

minuta Hilse

sinuata Greg.

Cyclotella

meneghiniana Kutz. 1 «2*

Diatoma

hiemale (Roth.) Heib. 4 1.0%

hiemale var. mesodon (Ehr.) Grun. 9 2.2%

Didymosphenia

geminata (Lyngb.) M.Schmidt. T

Diploneis

smithii var. pumila (Grun.) Hust. T

Fragilaria

construens var venter (Ehr.) Grun. 12 2.9%

leptostauron (Ehr.) Hust. 12 2.9%

pinnata Ehr. 11 1.1 A,

vaucheria (Kutz.) Peters. 41 9.9%

Frustulia

vulgaris (Thwaites) DeT. T

German Gulch Below Beef straight Creek (Continued)

Taxon

Gomphonema

angustatum (Kutz.) Rabh. angustatura var intermedia Grun. angustatum var productum Grun. dichotomum Kutz.

Count

Relative Abundance

4 3 5

1

1.0% .7%

1.2% .2%

Gotnphoneis

herculeana (Ehr.) CI.

Hannea

arcus (Ehr.) Patr.

1.9%

Hantzschia

amphioxys (Ehr.) Grun.

.2%

Melosira

varians granulata

Meridian

circulare (Grev.) Ag.

circulare var constrictum (Ralfs) V.H.

Navicula

bacillum Ehr.

capitata Ehr.

dementis Grun.

cryptocephala var veneta (Kutz.) Rabh.

elginensis (Greg.) Ralfs

lanceolata (Ag.) Kutz.

pupula Kutz.

tripunctata (O.F. Mull.) Bory

viridula (Kutz.) Kutz. emend. V.H.

viridula var avenacea (Breb. ex Grun.) V.H.

sp.

Neidium

kozlowii var parvum Mereschk.

1 2

32

19 1 2

1

.5%
.5%
.5%
.5%
.2%
.5%
T
7.7%
T
T
T
4.6%
.2%
.5%
.2%

Nitzschia

amphibia

dissipata (Kutz.) Grun.

fonticola (Grun.) Grun.

f rustulum

kutzingiana

linearis (Ag. ex W.Sm.) W.Sm.

palea

sp.

3 7

5 4 4 8

7

.7% 1.7%

T 1.2% 1.0% 1.0% 1.9% 1.7%

German Gulch Below Beefstraight Creek (Continued)

Taxon

Pinnularia

biceps Greg, borealis Ehr. burkii Patr. maior (Kutz.) Rabh.

Rhoicosphenia

curvata (Kutz.) Grun. ex Rabh. 24 5.8%

	Relative
Count	Abundance
2	.5%
	T
1	.2%
	T

Surirella angu ovata Kutz. 5 1.0%

angustata • 2a

Synedra

ulna (Nitz.) Ehr. 17 4.1%

ulna var contracta Ostr. 1_ .2%

TOTAL 413

DIATOM COUNT DATA German Gulch Below Edward Creek

Taxon

Achnanthes

lanceolata Breb. ex Kutz. lanceolata var dubla Grun. minutissima Kutz.

Amphora

ovalis var pediculus (Kutz.) V.H. ex DeT.

Caloneis

bacillum (Grun.) CI.

Cocconeis

placentula Ehr.

placentula var euglypta (Ehr.) CI.

Cyirbella

minuta Hilse muelleri Hust. sinuata Greg.

Dlatoma

anceps (Ehr.) Kirchn. hiemale (Roth.) Heib. hlemale var. mesodon (Ehr.) Grun.

Diatomella

balfouriana Grev.

Fragilarla

leptostauron (Ehr.) Hust.

pinnata Ehr.

pinnata var capitellata (Grun.) Patr.

vaucheria (Kutz.) Peters.

Frustulia

vulgaris (Thwaites) DeT.

Gomphonema

angustatum (Kutz.) Rabh. dichotomum Kutz. parvulum Kutz. sp.

Gomphoneis

herculeana (Ehr.) CI.

Count

48

8

22

62 2

11 4

2

1 17

4 19

5 58

2

14

2

Relative Abundance

11.2% 1.9% 5.1%

,2%

14.4%
.5%
2.6%
T
.9%
.5%
.2%
4.0%

9%

.9%

4.4%

1.2%

13.6%

,2%

.5% ,2% .5% ,5%

1.9%

German Gulch Below Edward Creek (Continued)

Taxon

Count

Relative Abundance

Hannea

arcus (Ehr.) Patr.

,9%

Meridian

circulare (Grev.) Ag.

Navicula

arvensis Hust.

cryptocephala var veneta (Kutz.) Rabh.

pupula Kutz.

viridula (Kutz.) Kutz. emend. V.H.

sp.

Nitzschia

dissipata (Kutz.) Grun.

fonticola (Grun.) Grun.

kutzingiana Hilse

linearis (Ag. ex W.Sm.) W.Sm.

palea (Kutz.) W.Smith

romana

sp.

Pinnularia

biceps Greg, borealis Ehr. stomophora (Grun.) CI

Rhoicosphenia

curvata (Kutz.) Grun. ex Rabh.

Synedra

ulna (Nitz.) Ehr.

TOTAL

7

14

3

1

23

2 17

3 10

3

8

13

_±

428

1.6%

3.2%

.7%

.2%

5.4% .5%

4.0% .7%

2.3% .7%

1.9%

2%

3.0%

2%

DIATOM COUNT DATA Mouth of German Gulch

Taxon

Achnanthes

lanceolata Breb. ex Kutz. minutissima Kutz.

Cocconeis

placentula Ehr.

placentula var euglypta (Ehr.) CI.

Cymbella

affinis Kutz. cistula (Ehr.) Kirchn. minuta Hilse prostrata (Berk.) CI sinuata Greg.

Diatoma

hiemale (Roth.) Heib.

hiemale var. mesodon (Ehr.) Grun.

Fragilaria

leptostauron (Ehr.) Hust.

pinnata Ehr.

vaucheria (Kutz.) Peters.

Frustulia

vulgaris (Thwaites) DeT.

Goraphonema

angustatum (Kutz.) Rabh.

olivaceum

parvulum Kutz.

Comphoneis

herculeana (Ehr.) CI.

Hannea

arcus (Ehr.) Patr.

Hantzschia

amphioxys (Ehr.) Grun.

	Relative
Count	Abundance
9	2.2%
2	.5%
9	2.2%
1	.2%
17	4.1%
	T
	T
	T
2	.5%
1	.2%
1	.2%
3	.7%
9	2.2%
41	9.8%

2	.5%
114	27.3%
11	2.6%

36

11

8.6%

2%

Mouth of German Gulch (Continued)

Taxon

Navicula

arvensis Hust.

capitata Ehr.

cryptocephala var veneta (Kutz.) Rabh,

salinarum Grun.

tripunctata (O.F. Mull.) Bory

Nitzschia

dissipata (Kutz.) Grun. fonticola (Grun.) Grun. kutzingiana Hilse linearis (Ag. ex W.Sm.) W.Sm. palea (Kutz.) W. Smith

Pinnularia

borealis Ehr. sp.

	Relative
Count	Abundance
3	.7%
1	.2%
22	5.3%
2	.5%
7	1.7%
57	13.7%
4	1.0%
11	2.6%
2	.5%
1	.2%
	T
	T

Rhoicosphenia

curvata (Kutz.) Grun. ex Rabh.

.5%

Rhopalodia

gibba var ventricosa (Kutz.) H and M. Peraq

Stauroneis

smithii Pant.

Surirella

ovata Kutz.

ovata var Pinnata W. Sm.

1.9% T

Synedra

ulna (Nitz.) Ehr.

ulna var contracta Ostr.

14 21

3.3% 5.0%

TOTAL

417

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