s ■ I ■ JLSJI DOCUMENTS CO KOOTENAI FALLS AQUATIC ENVIRONMENT STUDY FINAL REPORT 0.NTANA STATE 930 E Lynda!® Am Helena, Montana 59601 Prepared for Northern Lights, Inc. and The Montana Department of Natural Resources and Conservation by Patrick J. Graham Montana Department of Fish and Game May 1979 MONTANA STATE LIBRARY S 574.5263 F2k 1979 c.1 Graham Kootenai Falls aquatic environment study ■ ■■ ' ■ . ■ JUL 131983 ACKNOWLEDGEMENTS Brad Shepard assisted in field work and data analysis and Bill Martin assisted in field work. Bruce May, Tom Bonde and Bob Rainville provided information and constructive criticism. Jim Sewall and Associates and Harza Engineering also provided technical information on the proposed project and some field measurements. Larry Peterman reviewed the final draft. Funding was provided by Northern Lights, Inc. through a contract with the Department of Natural Resources and Conservation. Cover photo and frontispiece by Lance Schelvan, Figure 13 by Brad Shepard, and all other photos by the author. TABLE OF CONTENTS Page LIST OF TABLES iii LIST OF FIGURES v INTRODUCTION 1 DESCRIPTION OF THE STUDY AREA 1 METHODS 11 Chemical-Physical Data 11 Benthic Invertebrates ..... . 14 White Sturgeon ......... 17 Fish Populations 17 Creel Census 19 RESULTS AND CONCLUSIONS ............. 20 Chemical and Physical Data 20 Benthic Invertebrates 28 White Sturgeon 42 Fish Populations 45 Creel Census 58 LITERATURE CITED 64 APPENDIX A-l 67 APPENDIX A-2 77 APPENDIX A- 3 81 1 1 LIST OF TABLES Table Page 1. Some hydraulic parameters of transects across the Kootenai River upstream from Kootenai Falls at different discharges under present conditions and at the proposed full pool level (elevation 2, 000 ft) ...... . 21 2. Summary of gas saturation data upstream and downstream from Kootenai Falls during different discharge operations at Libby Dam and over a range of flows from 1972 through 1978 . 29 3. Taxa collected in the Kootenai River above and below Kootenai Falls in the spring and summer, 1978 30 4. Number of aquatic macroinverteb rates collected with a modified round square foot sampler in the spring and summer, 1978 above (1,2) and below (3,4) Kootenai Falls 32 5. Number of macroinvertebrates collected in cylindrical substrate samplers upstream (1,2) and downstream (3) from Kootenai Falls and colonized from April 13, 14 to May 30, 1978 37 6. Density of Plecoptera (stoneflies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler 40 7. Density of Ephemeroptera (mayflies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler 41 8. Density of Trichoptera (caddis flies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler 43 9. Density of Diptera (true flies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler - 44 10. Relative abundance of fish species collected upstream and downstream from Kootenai Falls 46 11. Population estimate of mountain whitefish and coarsescale suckers (fish/1000 ft) in the Kootenai River 1.7 to 5.2 miles downstream from Kootenai Falls during May, 1978 48 12. Number of fish per section, percent species composition and average size of fish in the Kootenai River below Kootenai Falls .... 48 in Table 13. Population estimates for rainbow trout in the Flower-Pipe section of the Kootenai River from 1973 through 1977, given in numbers and biomass per 1000 feet of stream Page 49 14. Growth of rainbow trout by year class from Flower-Pipe section of the Kootenai River 15. Growth increments of rainbow trout by age class each year in the Flower-Pipe section of the Kootenai River 52 16. Population estimates for rainbow trout and mountain whitefish in the Kootenai River between China Rapids and Kootenai Falls in September 1978, in numbers and biomass per 1000 feet of stream . 52 17. Population estimates for mountain whitefish in the Flower-Pipe section of the Kootenai River from 1973 through 1977 given in numbers and biomass per 1000 feet of stream 55 18. Growth of mountain whitefish by year class from the Flower-Pipe section of the Kootenai River ..... ■ 56 19. Growth increments of mountain whitefish by age class each year in the Flower-Pipe section of the Kootenai River 56 20. Fishing pressure in total hours and man-days and catch for weekdays and weekend periods during the summer (May to September) and winter (October to April) fishery in a 3.5 reach of river upstream from Kootenai Falls, 1978 59 21. A summary by month of a personal contact survey of anglers in a section of the Kootenai River 0.4 miles upstream from Kootenai Falls in 1977 and 1978 60 22. A summary by month of a postal card survey of anglers in a section of the Kootenai River 0.4 miles upstream from Kootenai Falls in 1977 and 1978 61 23. Residence of anglers contacted in the Kootenai Falls angler survey in 1978 ■ 65 24. Type of gear used by anglers in the Kootenai Falls angler survey in 1978 25. Number of successful anglers contacted on the Kootenai River under high flow ( 10,000 cfs) and low flow ( 10,000) conditions in July and August, 1978 - 63 63 IV Figure LIST OF FIGURES Page 1. Layout of the proposed dam, powerhouse, and return tunnel in the Kootenai Falls area. (From Kootenai River hydroelectric project application no. 2752 to the Federal Energy Regulatory Commission.) 2. Kootenai Falls at a discharge of approximately 20,000 cfs . . . 3 3. Kootenai Falls at a discharge of approximately 4,000 cfs ... . 3 4. A map of Kootenai Falls area located at river mile 193 on the Kootenai River between Troy and Libby, Montana with an aerial 4 photo insert 5. Monthly averages of mean daily discharge downstream from the Libby Dam site prior to impoundment (1970) and following impoundment (1977) 6. Total phosphorus and dissolved orthophosphate measured downstream from the Libby Dam site prior to impoundment (1970 and following impoundment 1977) 7. The pH in the Kootenai River below the present Libby Dam site prior to impoundment (1970) and following impoundment (1977) . . 8 8. Specific conductance measured in the Kootenai River downstream from the Libby Dam site prior to impoundment (1970) and following impoundment (1977) ■ 9 Mean daily water temperatures measured downstream from the Libby Dam site piror to impoundment (1970) and following impoundment (1977) . Water temperatures from January to mid-March and October to December were measured once every 2 weeks - 10. A map of the Kootenai Falls area marking nine cross-sectional transects and two insect sampling sites upstream from falls . . 13 11. A map of the Kootenai Falls area marking two insect sampling sites downstream from the falls 12. White sturgeon were captured with 3 and 5" trammel nets .... 18 13. White sturgeon were tagged with a radio transmitter using a plastic saddle-mount 14. Cross-sectional profile number 5 across the Kootenai River upstream from Kootenai Falls depicting water elevations at three flows under natural conditions and at the proposed full pool level of the reservoir 22 Figure Page 24 Biomass estimates of mountain whitefish per 1000 ft. o, stream in the Flower-Pipe section of the Kootenai River from 1973 through 1977 excluding 1976 25 26 35 15 Percent total gas saturation in the Kootenai River at different dam operations measured below Libby Dam from 1972 to 1975 .... 16 Percent total gas saturation in the Kootenai River at different dam operations measured above Kootenai Falls from 1972 to 19 75. . 17 Percent total gas saturation in the Kootenai River at different dam operations measured below Kootenai Falls from 1972 to 1975. . 27 18 Percent total gas saturation in the Kootenai River at different dam operations measured at Leonia (Mont ana- Idaho border) from 1972-1975 19 Insect species diversity and number of taxa per square foot at sections 1 and 2 upstream from Kootenai Falls and sections 3, 4 downstream from Kootenai Falls, sampled during the spring and summer, 1978 20 Population estimates of rainbow trout in fish/1000 ft of stream in the Flower-Pipe section of the Kootenai River from 1973 through 1977, excluding 1976 21 Biomass estimates of rainbow trout per 1000 ft of stream in the Flower-Pipe section of the Kootenai River from 1973 through 1977, excluding 1976 22 A 7-plus pound rainbow trout captured in autumn sampling in the China Rapids-Kootenai Falls section. This area is known for producing trophy fish by many local fishermen .... 23 Population estimates of mountain whitefish per 1000 ft. of stream in the Flower-Pipe section of the Kootenai River from 1973 through 1977 excluding 1976 38 50 50 53 57 57 VI INTRODUCTION This report contains an analysis of data collected on the aquati c environment in the Kootenai Falls area to assess the probable effects of a proved hydroelectric diversion project, just upstream from the falls onThe aquatic biota. An impact analysis will appear ^ a separate^docu- cfs Figure 2 represents a flow of approximately 20,000 cfs and *W™* Presents a flow of 4,000 cfs. The lowest historical mean daily flow was ^reduce returning water velocities to rear natural conditions. DESCRIPTION OF THE STUDY AREA The Kootenai River draws -majority ^ £ ect y° nT n fcolumbirRleer'after returning to Canada via Idaho Over one'alf (50 miles) of the main stem in ^tana has been inun dated by Libby Dam a power peaking hydroelectric project, which backs water weu " A "regulatory" dam, in the process of construction would inundate 20 percent of the remaining free-flowing river in Montana. Kootenai Falls, located at river mile 193, is a relatively wide falls with wa?er cascading down a series of bedrock faults through the canyon area CFfgurf : .Cai Is the from October 1 through April 30, counts were made on 2 week days and 4 week- end days selected randomly each month. Five counts a day were made every 2 hours. The starting time varied by randomly selecting one of tour halt hour intervals during the first 2-hour block each day. During periods of increased fishing pressure, May 1 through September 30 counts were made on 2 weekend days and 3 weekdays selected randomly during each 15-day period. Because of increased day length, six counts were made each day and the number of 2-hour blocks in a day varied to include sunrise and sunset in the first and last block of the day, respec- tively Counts were made at the midpoint of each 2-hour block (7, 9, 11 a.m., and 1 3 5 7 9 p.m.). On weekdays the last three counts of each day were always included in the census because of increased fishing pressure during that period. Other hourly counts were selected at random without repeating a particular combination of hours until every combination had been used to ensure that all hours would be equally surveyed. On days when counts were made, direct personal contacts and postal card surveys were employed. If fishermen had fished less than one-halt hour when first contacted or if time did not permit direct contact a post- card was left at the angler's vehicle. In direct contacts, the information acquired included starting time and time of the interview, whether or not the trip was complete, number of anglers in a party, whether the anglers were from in-county or out-of-county, or out-of-state, the date, day of week, number of successful anglers, number of fish caught, kept, and released by species, size of fish kept, type of gear used (natural, lure, flies or a combination) and whether they were fishing from shore or a boat. Postcards included the number of anglers, the number of successful anglers, number of each species caught, kept, and released, hours fished, and whether fishing from shore or boat. Cards were pre- stamped and dated. Returns were not mandatory but a card explaining the purpose of the creel census was attached to inform and encourage them to return the cards even if no fish were captured. During periods of low success, such as the winter months when anglers generally fished less than half an hour, fewer cards were returned. Anglers had some problems distinguishing rainbow from cutthroat trout. Some rainbow trout exhibited weak morphological traits of the cutthroat because of some mixed breeding in the past. To minimize complications, I applied the same percent composition of rainbow and cutthroat trout determined from direct contact to the postal card survey. Fishing pressure was determined using stratified count data similar to a method by Neuhold and Lu (1957). Fishing pressure was calculated in hours and converted to man-days by dividing monthly totals by average length of completed trip (2.1 hours). Catch was determined by multiplying monthly pressure in hours by monthly catch rate. RESULTS AND CONCLUSIONS Chemical and Physical Data Chemical or physical parameters of the Kootenai River which could affect or be modified significantly by the proposed Kootenai Falls Dam include the various hydraulic parameters associated with discharge, suspended sediment, and gas supers aturation. Obvious physical changes would occur upon impoundment to over 3 miles of the river upstream from the falls. Current and depth, which are important factors in fish and insect habitat, would be significantly altered. I compared present conditions in what would be the lower pool area (transects 2, 3 and 4) and the upper pool area (transects 5, 6 and 7) to conditions that would be found at the proposed pool elevation. A medium flow of 10,000 cfs was used for both conditions. The river's width would increase by 57 percent in the lower pool area, from 337 feet to 595 feet, and by 36 percent in the upper end to a width of 551 feet (Table 1) . Mean depth would increase by 2.5-fold to a mean depth of 22.6 feet and a maximum depth of approximately 40 feet in the lower end and increase 2.0-fold in the upper end to a mean depth of 16.7 feet. Volume of the river, measured by cross-sectional area would increase nearly 5-fold in the lower end and over 2.5 times in the upper end (Figure 14) . Mean velocity of the river would decrease significantly at all discharges. Under present conditions the mean velocity at 10,000 cfs is 3.93 and 3.12 ft/sec for the lower pool (2, 3, 4) and upper pool (5, 6, 7), respectively. Following impoundment mean velocities would be 0.85 and 1.43 ft/sec for the lower and upper areas, respectively. Downstream from the falls and directly around the falls area the major impact will be a reduction in flows caused by the diversion. Downstream from the falls the aquatic environment is characterized by vertical canyon 20 Table 1. Souse hydraulic parameters of transects across the Kootenai River upstream from Kootenai Falls at different discharges under present conditions and at the proposed full pool level (elevation 2,000 ft) Transects 2,3,1+, and 5,6,7, would be in the downstream and upstream ends of the pool, respectively Discharges (cfs) Transects 2,3,4 Mean velocity (ft/sec) Width (ft) 5,000 10,000 20,000 2.1*9 3-93 5.58 Mean Cross-Sectional depth (ft) Area (ft) 337 380 8.0 8.9 10.2 2,520 3,077 3,690 Full Pool 5,000 10,000 20,000 25,000 0.42 0.85 1.70 2.13 595 22.6 11,867 5,000 10,000 20,000 Transects 5, 6, 7 2.06 360 7.6 2,743 3.12 4o6 8.6 3,^90 4.56 462 10.0 4,583 Full Pool 551 16.7 9,230 5,000 10,000 20,000 25,000 0.56 1.43 2.25 2.81 21 River Section 5 Vertical: 1 sq : 2. 5' Horizontal: 1 sq= 10. 2010.. — 2000.. .2 1990.. a > W 1980.. 1970.. Right bank 20,000 cfs 10,000 cfs-^ 5,000 cfs^ soundings Figure 14. Cross-sectional profile number 5 across the Kootenai River upstream from Kootenai Falls depicting water elevations at 3 flows under natural conditions and at the proposed full pool level of the reservoir walls along both shores with many small coves, a relatively narrow channel and deep pools broken up abruptly by rapids and falls. Two gravel bars are present in the area that would be directly impacted by the project. One is located on the north shore just upstream from the foot bridge. This bar constitutes the largest single insect producing area within the first mile of the canyon. The other bar is on the south shore lust downstream from the out-flow tunnel, and is composed largely of rubble. Because of the unique nature of the area, shallow water fish habitat appears to be limited to cove areas in this section of the river. Coves have formed along the flex lines between fault blocks in the canyon wall and developed after the relaxation of the compression forces which uplifted the bedrock in the falls area. These coves, eroded by glacial floods, provide shallow water fish habitat at flows from 4,000 to 24,000 cfs which was the range of flows observed during the study period. Because these coves are on bedrock blocks they abruptly drop off and provide no habitat at lower flow levels. The minimum flow at which this would occur could not be determined in this study. Suspended sediment can cause changes and reductions in aquatic life if it settles out in significant quantities on the stream bottom and is not flushed out (Cordone and Kelley 1961). The sediment reduces habitat as it fills the interstices or spaces between the river gravel. Where sediment covers the bottom it provides very unstable habitat for insects. Fine gram sediments can also cause physical damage by clogging the external gills of some insects. Mean annual suspended sediment loads in the Kootenai River have decreased considerably since impoundment by Libby Dam. From 1967 through 1971 annual sediment discharge averaged 1.6 million tons and decreased to 62,000 tons between 1973 and 1975. During the years 1967 to 1975 the Fisher River con- tributed an average of 97,000 tons of suspended sediment annually. The pro- posed reregulating dam would reduce this amount somewhat. But the large daily flow fluctuations would probably carry much of it downstream. Reduced water velocities in the pool area of the Kootenai Falls project would cause some sediments to settle out. These sediments would probably be concentrated in the mid-stream and lower end of the pool area. Although the amount of sediments won't be significant from an engineering viewpoint, biologically the accumulation of sediments will significantly alter the benthic invertebrate community. An equilibrium situation will be reached because of the constant pool elevation and the modified range of flows occurring from Libby Dam. Gas supersaturation, when high, has had marked effects on aquatic life in the Kootenai River causing fish kills, limiting whitefish and torrent sculpin populations, and causing flotation of insects clinging to gas bubbles resulting in increased downstream drift and susceptibility to predation. Factors which increase percent gas saturation or prevent the reduction of a high percent gas saturation would damage aquatic organisms downstream from the falls. Gas supersaturation problems occurred in the Kootenai River from 1972 through the fall of 1975 and resulted from the use of sluices, and to a lesser degree, spillways to discharge water from the dam. Beginning in the fall of 1975 water was discharged from turbines or a combination of sluices and turbines which reduced percent gas saturation. 23 Gas supersaturation can result in gas bubble disease in fish which occurs when total dissolved gases in the water exceeds a certain percent of saturation. ihese gas pressures can kill fish if the percent saturation is high or sub-lethal levels can cause reductions in swimming ability and blood calcium, and increase deformities in young-of-the-year fish (Dawley and Ebel 1975) . Blindness and secondary fungal infections in fish can also result from gas supersaturation (Bouck et al . 1976). Death from gas bubble disease usually results from stasis of the blood caused by gas emboli in the vascular system. Chronic exposure to the disease results in a build-up of metabolic wastes in the tissues coupled with low concentrations of dissolved oxygen which causes tissue death from anoxia. Fish can reduce the effects of gas supersaturation by seeking deeper water where hydrostatic pressure is greater. The amount of saturated water discharged, level of discharge in the water column, water temperature and depth of water all contribute to the percent saturation and its toxocity on fish (Adair and Hains 1974, May and Huston 1973). Species of fish is also related to toxicity. Ranked in order of increasing tolerance are: mountain whitefish (Prosopium williamsoni) , rainbow trout (Salmo gaivdneri) , largescale suckers (Catostomus macro eheilus) , torrent sculpin (Cottus rhotheus) (Fickeison and Montgomery 1978, May and Huston 1973 and 1974). Although torrent sculpins were tolerant of supersaturation, gas bubbles would develop and cause them to turn upside down and float down- stream (Fickeison and Montgomery 1978) . Levels of gas saturation in the Kootenai Falls area in 1978 were not in the range considered to be toxic to fish at low and medium flows. Dis- charges from Libby Dam during this period were through the turbines which is the planned mode of operation for the future. However, the Kootenai Falls project could increase gas saturation below the falls when sluices or spillways were used at Libby Dam by diverting the flow around the falls and also in the design and structure of the turbines and tail tunnel. When percent gas saturation was relatively low, as it is presently, gas saturation levels were primarily a function of discharge, water temperature and the plunging and churning actions of the falls and rapids in the area. Upstream from the falls, percent total gas saturation averaged 102.6 percent at discharges of 5,000 to 9,000 cfs, and increased to 104.5 percent at a discharge near 20,000 cfs in 1978. Downstream from the falls, percent gas saturation was higher, averaging 109.5 percent at discharges from 5,000 to 9,000 cfs and increased to 112 percent at 20,000 cfs. Under these conditions, diverting part of the flow around the falls would reduce the natural increases in percent gas saturation unless it is increased in the process of power generation. When percent gas saturation was relatively high, as from 1972 through mid 1975, percent gas saturation in the falls area was also a function of how water was discharged from Libby Dam. Operational differences in Libby Dam were most noticeable immediately below the dam (Figure 15) . Differences in percent gas saturation with different modes of operation were still noticeable above Kootenai Falls although they were approaching equilibrium. Water discharged from turbines and a combination of turbines and sluices resulted in decreased percent gas saturation, while water discharged from the spillways at high flows and the sluices at all flows resulted in increased percent gas saturation (Figure 16) . The range of percent total gas saturation below the falls (110.2 to 111.8 percent) was small compared to the range upstream from the falls, 103.2 to 114.2 percent (Figure 17). 24 "1 150 .. lUO •H .r CO CO C5 cd -p o En -P 0) o 0) 130- 120.- 11a. 100.. 0 9 • 9 xt t t • o t X J- 4- + b— sluice t — turbine S-- spillvay X— sluice & turbine 0- sluice & spillway 8 10 12 Ik 16 18 20 22 , Discharge (cfs x 1,000) 26 28 30 32 3^ Figure 15. Percent total gas saturation in the Kootenai River at different dam operations measured below Libby Dam from 1972 to 1975 a-. 15Q i4o- o •H ■P ctf § 130 -P cd ra CD cd &0 £120 -P -P G CD O CD 110 100 99 X T2" -!-- 4- + 7D~ T? Tb" ^T8" Discharge (cfs x 1,000) o s T2" 24 * 26 i- Legend • — sluice * — turbine s— spillway x — sluice & turbine O — sluice & spillway ~2K 30 ' 32 l TT Figure 16. Percent total gas saturation in the Kootenai River at different dam ooerations measured above Kootenai Palls from 1972 to 1975 130.. Legend • — sluice *■ — "turbine s — spillway X — sluice & turbine O — sluice & spillway a o ■H 1*120. tn to g5 ^3 110+- o S > • t X •• o s 100.- * 8 10 4- 4- 4- 20 lU 16 18 Discharge ( cf s x 1,000) 22 2** 26 £ 30 ->h Figure 17. Percent total gas saturation in the Kootenai River at different dam operations measured belcv Kootenai Falls from 1972 to 19' 75 With large discharges, the percent total gas saturation was smaller after going over the falls, with the reverse occurring at small discharges (Table 2) Downstream from the falls, 21.5 miles at the Montana-Idaho border, there was no difference in gas saturation between modes of operation, and percent gas saturation continued to decrease, although it remained over 110 percent at large discharges (Figure 18) . By routing the major portion of the flow around Kootenai Falls, the equalizing effect of the falls on gas saturation would be significantly reduced. The affect would probably not be detrimental to the aquatic biota downstream from the return tunnels unless Libby Dam discharged from sluice, spillways, or a combination of the two. This would be particularly true at discharges over 15,000 cfs. Benthic Invertebrates Aquatic macro invertebrates are animals without backbones that are large enough to be seen with the unaided eye. These creatures cling to rocks, algae and aquatic macrophytes or burrow into the substrate. Many of the insects are immature forms with a terrestrial adult stage. Other groups include earthworms, snails, clams, flatworms, roundworms, crustaceans, sponges, mites, and adult insects. These creatures eat primarily plant and other organic material and provide fn essential energy link between sunlight and fish. Fish feed almost entirely on macroinvertebrates and the general health of a population depends upon the number and type of macroinvertebrates available for consumption. Macroinvertebrates are also useful in determining past and present water quality because of the sensitivity of some organisms to different types of water pollution, water velocity, and depth. Spring and summer macroinvertebrate samples included a minimum of 10 orders, 26 families and 47 genera (Table 3). Only Hespevoperla paoifioa, a stonefly, (Plecoptera) was found in the qualitative samples and not the quantitative samples, although many genera were poorly represented in the quantitative samples. In general the taxa present reflected a stream of relatively high water quality. However, several major differences were found between the existing invertebrate population and the population prior to impoundment of the river by Libby Dam. Bottom sample sites 1, 2 and 4 were comparable in depth, velocity and substrate size. Site 3 included two samples on a bedrock shelf in the canyon below Kootenai Falls during the spring, although for the summer samples, one was taken on the gravel bar upstream from the foot bridge (sample 6) . Total weight and number of insects were similar at sites 1, 2 and 4 during both the sprine and summer (Table 4) . Standing crop at each site was comparable between seasons with a mean of 0.97 and 0.82 grams for spring and summer samples (1, 2, 4), respectively. Numbers of insects were more variable because of the abundance of small dipterans (true flies) . Site 3 was relatively impoverished, largely because of the bedrock substrate. Sample 6 at site 3 during the summer produced a significantly larger biomass than other samples in the canyon area. This sample was taken on the gravel bar. Substrate baskets were only used during the spring when daily flow fluctuations were smallest. Substrate baskets provided good opportunity for insect colonization; however, they do not accurately represent standing crop or relative abundance of the bottom community because the artificial substrate is selective for insects which prefer it. Because the deep water 28 ' < Table 2, Summary of gas saturation data upstream and downstream from Kootenai Falls during different discharge operations at Libby Dam and over a range of flows from 1972 through 19T& Type of Operation Sluice only Spillway only Sluice & spillway Turbine only Turbine and sluice Kootenai River 1972 - 1975" P.O. j> Sat. Above (n) Below (n] 11^.2 (31) 112,8 ( 5) 115.0 ( 1) 109.1 (10) 109.2 ( 5) 110.7 113.8 112.0 101.0 113.2 (30) ( 5) ( 1) (12) ( 5) Nit t Ar.$ Sat. Above Below 116.0 109.8 117.0 1Q4.2 111.0 113.0 112.0 116.0 113-2 113.0 Tot. Part. Press $ Sat. Above Below 114.2 108.4 115.0 103. 21 109.4 111.1 110.4 114.0, 110. 2£ m. 8 Flow (discharge) Range 0 - 10,000 cfs 10,000 - 20,000 cfs over 20,000 cfs 109.8 (17) 116.5 (14) 114.7 (12) 110.2 (16) 111.7 (14) 112.75(12) 109.9 115.7 119.3 110.7 112.9 115.75 108.4 114.5 116.8 109.2 N — 14 N — 13 Table 3. Taxa collected in the Kootenai River above and below Kootenai Falls in the spring and summer, 1978. Order Family Capniidae Genus Capnia Species Plecoptera Chloroperlidae Alloperla Perlidae Hesperoperla paaifiaa Perlodidae Cultus (Isogenus) Pteronarcydae Pteronaraella badia Ephemeroptera Baetidae Baetis Pseudooloeon Ephemerellidae Ephemerella flavilinea heteroaaadata inermis he cub a doddsi margarita tibialis Heptageniidae Epeorus Heptagenia Cinygmuta Rithrogena hageni Lep tophi ebiidae Paraleptophlebia Trichoptera Brachycentridae Braahyaentrus Glossosomatidae Glossosoma Hydropsy chidae Aratopsyche Cheunatopsyche Hydropsyohe Leptoceridae Ceraclea Lepidostomatidae Lepidostoma Limnephilidae Neophylax Rhyacophilidae Rhyaoophila Diptera Simuliidae Simulium Tanydaiidae Protanydarus Tipulidae An to aha Hexatoma Chironomidae Subfamily Tanypodinae Thienemannimyia Diamesinae Diamesa Potthastia Sympotthastia Chirononiinae Mioropseotra Miorotendipes Polypedilum Rheo tanytarsus Tanytarsus Orthocladiinae Cardiocladi us Criootopus Eukiefferiella Orthocladius Parakiefferie I la Parame trioanemus Synorthoa ladius 30 Table 3 continued. Taxa collected in the Kootenai River above and below Kootenai Falls in the spring and summer, 1978. Order Coleoptera Nematoda Oligochaeta Turbellaria Acari Gastropoda Family Elmidae Lumbriculidae Lumbricidae Naididae Tubificidae Lymnaeidae Genus Eetevelm-is Narpus Optiosevvus Eiseniella Ophidonais Lyrmaea Species serpentia 31 Table 4. Number of aquatic macroinvertebrates collected with a modified round square foot sampler in the spring and summer, 1978 above (1,2) and below [3,4) Kootenai Falls. Taxa Capnia group Alloperla group Cultus (Isogenus) Baetis Vsendooloeon Ephemevella flavilinea Ephemevella inevmis Ephemevella heouba Ephemevella doddsi Ephemevella mavgavita Ephemevella tibialis Epeovus Heptagenia Cinygmula Rithvogena hageni Pavaleptophlebia Bvaohyaentvus Glossosoma Avatopsyehe Chewnatopsyche Hydvopsyahe Cevaolea Lepidostoma Neophy lax Rhyaoophila Spring Summer Site Rl 1 R2 Site R3 2 R4 Site R5 3 R6 Site R7 4 R8 Site Rl 1 R2 Site R3 2 R4 Site R5 3 R6 Site R7 4 R8 1 1 2 1 5 3 4 4 1 4 6 12 18 77 134 1 S 5 157 4 164 12 84 12 99 21 2 4 41 11 117 16 z 1 3 1 1 1 1 48 79 51 62 1 91 56 1 27 1 2 6 17 2 2 1 1 37 15 17 1 3 16 4 5 6 1 11 6 1 5 23 10 46 1 123 10 22 1 13 2 8 2 1 7 2 4 1 11 2 5 10 1 11 1 1 2 1 1 8 4 1 1 7 1 3 6 1 34 2 2 5 1 1 Table 4 continued. Number of aquatic macro invertebrates collected with a modified round square foot sampler in the spring and summer, 1978 above (1,2) and below (3,4) Kootenai Falls. Spring Summe: r Site 1 Site 2 Site 3 Site 4 Site 1 Site 2 Site 3 Site 4 Taxa Rl R2 R3 R4 R5 R6 R7 R8 Rl R2 R3 R4 R5 R6 R7 R8 Simuiium 3 3 3 12 1 1 1 1 12 7 2 8 1 2 1 7 Pvotanydavus 1 Antooha 3 4 40 26 4 1 1 3 Eexatoma 1 1 Thi enemannirny ia 6 12 3 2 17 11 3 19 21 32 1 6 40 lb Diamesa 19 13 5 1 10 3 4 12 18 15 13 1 Potthastia 2 5 Sympotthas tia 1 4 3 y 2 M-ievopseatva Miorotendipes 2 2 Polypedilum 22 7 10 24 39 1 7 11 15 6 Rheo tany tars us Tanytarsus 2 5 Cavdiooladius 1 Cvicotopus 2 8 4 12 1 6 5 Eukieffevie I la 11 6 1 4 1 22 5 6 9 9 8 2 1 7 11 Orthoaladius 503 432 128 61 79 58 1248 584 41 567 102 105 6 23 567 8b/ Papakieffevie I la 2 3 9 4 Pavame triocnemus 1 1 1 1 Synorthoalad-ius 10 1 Chironomid pupae 281 269 52 24 6 5 243 203 14 68 81 34 9 174 66 Heterelmis 1 Narpus 1 1 Opt-Loservus 1 2 3 1 1 Aoari 1 1 Nematoda 4 1 12 15 19 27 17 10 6 18 2 Table 4 continued. Number of aquatic raacroinvertebrates collected with a modified round square foot sampler in the spring and summer, 1978 above (1,2) and below (3,4) Kootenai Falls. Taxa Spring Summe: r Site Rl 1 R2 1 Site 2 R3 R4 5 2 Site 3 R5 R6 Site 4 R7 R8 Site Rl 1 R2 2 Site R3 1 2 R4 3 Site R5 3 R6 Site 4 R7 R8 Turbellavia 1 Lumbriculidae Eiseniella Ophidonais serpentina 3 3 1 1 4 21 7 3 38 5 7 Lymnaea 1 1 3 Total Number 913 850 370 457 91 66 1718 953 350 955 467 456 12 140 987 1196 Total Weight (gr) .776 .647 .819 1.743 .035 .015 .971 .873 .385 .724 .643 1 .504 .003 .329 .963 .671 13a. Legend • -- sluice t — turbine S -- spillway X — spillway and sluice O — turbine and sluice 120. 04 in eg O PL, 110. LOO.. xt 4- +■ Ik 16 18 Flow (cfs x 1,000) 20 2k 26 28 ■igure 18. Percent total gas saturation in the Kootenai River at different dam OT>erations measured at Leonia ( Montana- Idaho border) from 1972-1975 'J0 32 •5L habitat is relatively constant, few samples are needed to obtain good precision for number of t xa and number of individuals per sample in relatively pristine conditions (Rabeni and Gibbs 1978) . There was undoubtedly some loss on retrieval because no bag was placed around the samples before retrieval, Rabeni and Gibbs (1978) estimated loss on retrieval of 26-30 percent for Diptera, Ephemeroptera and Trichoptera from substrate samplers in a deep Maine river. Biomass of insects in substrate baskets was considerably larger at sites 1 and 2 than at site 3 (Table 5). The deeper water at site 3 (24 ft) and the shading by steep canyon walls might explain some of the difference. Some dif- ferences between substrate and bottom samples were more attributable to avail- ability of suitable substrate on the river bottom. Dipterans in general were less abundant in the substrate baskets than bottom samples, and Simuliwn and Eukiefferiella replaced Orthooladius as the dominant species in the substrate samples. Simuliwn larvae prefer more laminar flow as opposed to turbulent flow because the comb-like bristles which they extend into the current to catch food are more efficient in more laminar flow ( Hynes 1970) . The clean gravel sub- strate also provides more surface area for attachment. Mayflies were relatively more abundant in the basket samples than substrate samples, although fewer Baetis larvae were present in the substrate baskets. Hydropsyohe were much more abundant in the substrate samples upstream from the falls than downstream, and more abundant than in bottom samples. They are net spinning filter feeders which have specific current requirements (Philipson 1954) and colonize artificial substrates because of the large amount of surface area available for attachment. Relative abundance of dominant species of may- flies appeared to be correlated. Ephemerella inermis decreased in abundance downstream from site 1 to 3, while Rhithrogena hageni increased in abundance. To further assess the structure of the insect community, calculations were made of species diversity (Shannon-Weaver and Brillouion) (Kaesler and Herricks 1977, Pielou 1977), redundancy (Wilhm and Dorris 1968) evenness (Egloff and Brakel 1973), equitability (Krebbs 1972) and species richness (Orr et al . 1973). In general, species diversity values were intermediate to low. The insect community was generally monotipic and dominated by Orthooladius at all sites except site 2 (Appendix A-l)- Present conditions seem to favor a few of the more tolerant species. Diversity of insects was largest at site 2 in both spring and summer samples (Figure 19). Diversity was larger in summer than spring samples at all sites (Figure 19, Appendix A-l). Diversity was smallest in the canyon area downstream from the falls due largely to generally poor substrate con- ditions. Diversity of insects on the gravel bar just downstream from the falls (site 3 : summer sample) was larger than at either site 1 or 4 (Figure 19). Site 3, was located on bedrock substrate in the canyon area and had the smallest diversity of the spring samples and second smallest diversity during the summer. Site 31 also had the smallest number of taxa during both seasons. The impoundment of the Kootenai River by Libby Dam has resulted in significant decreases in insect diversity and probably standing crop, although studies in areas where pre-impoundment collections were made are needed to quantify the changes. Flow fluctuations have also resulted in the loss of significant amounts of habitat. In a river subject to fluctuation from a hydroelectric facility, Fisher and LaVoy (1973) found that benthic invertebrates increased markedly in density and taxonomic diversity from the high to low water mark. Fall samples near the high water mark in the Kootenai 36 Table 5. Number of macroinvertebrates collected in cylindrical substrate samplers upstream (1,2) and downstream (3) from Kootenai Falls and colonized from April 13, 14 to May 30, 1978. Taxa Alloperla Vteronarcella badia Baetis Ephemevella inermis Ephemevella flavilinea Ephemevella hetevooaadata Rithvogena hageni Pavaleptophlebia Bvaehyoentvus Glossosoma Hydvopsyahe Lepidostoma Simulium Antooha Theinemannemyia Diamesa Mievopseotva Cvicotopus Eukieffevie I la Ovthocladius Chivonomid pupae Nematoda Tuvbellavia Lumbriculidae Lymnaea Total Number Total Weight (gr.) Small Substrate Baskets Site 1 Site 2 Site 3 26 1308 1210 243 9.489 8.790 1.363 Large Substrate Baskets Site 1 Site 2 Site 3 17 38 4 29 24 491 238 57 402 249 2 2 2 7 3 2 63 124 140 27 56 4 7 2 5 4 4 2 1 469 356 22 365 348 7 2 121 374 4 271 628 2 1 1 18 2 1 12 3 2 1 4 2 1 1 3 63 56 47 65 7 4 12 6 6 9 8 4 6 8 3 83 47 1 36 1 1 1193 1403 229 7.158 8.524 1.466 37 5 3H c o c £ SUMMER 7T 1 2 T IT 3 Kootenai Falls 30 r ♦ t ♦ * 7T 4 20 o X a o 10 z lo I — I — I — t ilesfrom Falls f-4-H CD > D c 0 c E a x 1 SPRING Naof Taxa Shannon-Weaver 30 20 a o 10 d z 0 2 T 3 Kootenai Falls Figure 19. Insect species diversity and number of taxa per square foot at sections 1 and 2 upstream from Kootenai Falls and sections 3, 4 downstream from Kootenai Falls, sampled during the spring and : .'"Timer, 1978. 38 River produced few taxa or insects. Therefore, in addition to reduced diversity, and probably abundance, within the wetted area, the area of insect production has also been limited to a much smaller area since impoundment of the river by Libby Dam. The status of the insect population downstream from Libby Dam has not been studied extensively since impoundment. Some work was done during periods of high gas saturation in the river (Fickeison and Montgomery, undated). Results indicated that the flotation of insects resulting from the physical presence of gas bubbles in the river was a more important factor in insect survival than gas bubble disease. Although many changes were observed in the insect population in this study compared to pre- impoundment, they are likely a result of many interrelated changes that occur in a regulated river as discussed by Ward (1976) and Spence and Hynes (1971) . To compare pre- and post-impoundment macroinvertebrate communities, I selected the downstream-most site sampled in pre -impoundment studies at Lowery Gulch (Bonde and Bush 1975 -Appendix ), 19.7 miles upstream from Kootenai Falls. Samples collected from 1969 to 1971 were pooled. Both pre- and post-impoundment samples were made with the same sampler and at sites with similar size substrate, water depth and velocity. Only the four major insect orders were compared. In pre- impoundment studies, 42 genera were collected compared to 26 genera in the present study. Chironomidae were only reported to family in the pre -impoundment study and have therefore been lumped together here for comparison. Standing cro£ after impoundment was 0.894 gr/ft2 (sites 1, 2, 4) compared to 3.38 gr/ft^- in the pre -impoundment study. Number of stonefly genera and density were significantly reduced after impoundment (Table 6). Only 3 genera were collected in this study compared to 13 genera in the pre-impoundment study. Densities ranged from 0-5/ft after impoundment compared to 38/ ft2 prior to impoundment. In pre-impoundment samples (Lowery Gulch) stoneflies comprised 15 percent of the sample by number and 27 percent weight. In this study stoneflies comprised less than 0.5 percent of the sample by number; probably less than 1 percent by weight. Decreases in stonefly densities have occurred in many rivers downstream from impoundments (Spence and Hynes 1971, Ward 1976). Several reasons have been suggested for their absence including changes in thermal regime (Lehmkuhl 1972) and oxygen availability to nymphs (Spence and Hynes 1971). Decreases in the Kootenai River may have occurred during periods of high gas saturation, but presently higher winter and lower spring and early summer temperatures and fluctuating flows probably limit stonefly numbers in the Kootenai River. Completion of the life cycle is dependent on thermal cues for egg development, growth and emergence. Lack of certain maximum and minimum temperatures, or too few degree days could result in elimination of certain species of insects (Lehmkuhl 1972). Number of mayfly genera decreased from 11 genera prior to impoundment to 8 genera post -impoundment. Densities were significantly larger after impoundment ranging from 97 to 184/sq ft compared to 31/sq ft prior to impoundment (Table 7). Although abundant, the mayflies were small in size. In pre-impoundment samples mayflies comprised approximately 12 percent of the sample by number and 7 percent by weight. After impoundment mayflies comprised a larger percent by number (19 percent) . Only total sample weight was calculated from post -impoundment samples, which was only 26 1Q Table 6. Density of Plecoptera (stoneflies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler. Genera Numb sr of insects per square foot Kootenai Falls Lowery Site 1 Spi/ 4 Site 3 Sp Su X Site 4 Sp Su 5 Gulch T3/ 1/ x-L/ Alloiperla Capnia x - - - Cultus (Isogenus) - - - x — Total 1 4 0 x x 5 38 1/ Spring 2/ Summer 3/ Mean for spring, summer and autumn samples 4/ Present, less than 1/square foot 40 Table 7. Density of Ephemeroptera (mayflies) at three sxtes in th e Kootanai Falls area collected during the spring and summer 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler. — Numbei • of insects per s quare foot Kootenai Falls Lowery Tax a Site spi/ 1 & 2 Sul/ Site 3 Sp Su x 3 Site sp 6 4 Su 79 GU$ Baetis 60 126 Ephemerella flavilinea 1 4/ x— ' - X - Ephemere I la he terooaadata - - - - — Ephemerella inermis 60 X - 74 X Ephemerella heovba - X - - - Ephemerella doddsi - X - - - Ephemerella margarita - 12 2 - 3 Ephemerella tibialis - 19 - - 4 Epeorus - - - - X Heptagenia - 5 2 - 8 Rythrogena hageni 51 7 - 16 3 Paraleptophlebia X - - X - Pseudoaloeon - 12 - - 14 Cinygmula X - - - - Total 173 184 x 8 97 Ill 31 1/ Spring 2/ Summer 3/ Average for spring, summei - and autumn 4/ Present, less than 1 per j ;quare foot 41 percent of the p.e- impoundment samples. The decrease in standing crop caused by reductions in stonefly abundance was not significantly compensated for by the mayflies. Hie increase in mayfly abundance seems to conflict with the thermal regime theory by Lehmkuhl (1972); however, in general the mayfly community was dominated by only a few taxa including Baetis spp., Ephemerella vnerrms, and Rythrogena in the spring and Baetis spp. in the summer. Their success in part appears to be due to their ability to reproduce under existing con- ditions and exploit areas and food sources used by insects presently absent in the river. The number of Trichoptera (caddis flies) genera remained the same with nine genera collected from pre- and post -impoundment samples (Table 8). However, density decreased significantly from 56/sq ft at Lowery Gulch to 11/sq ft at Kootenai Falls. One significant factor which may limit the abundance of caddis flies is the amount of suitable habitat. Their numbers in substrate samples were large compared to bottom samples. Hydropsyohe are net-spinners and utilize the current to carry food into their nets. These nets require a definite current to function properly (Philipson 1954) . Some sediments have filled interstices in the gravel and rubble and have reduced the amount of surface area for these net-spinners to attach. This condition in the Kootenai Falls area is probably at near equilibrium and is not likely to improve without flood flows which shift and scour bottom materials and carry sediment downstream. Fluctuating flows from the dam are not sufficient and probably reduce the suitable rearing areas for the caddis flies because of constantly changing water velocities. Impoundment of the area by a dam at Kootenai Falls would cause more sediments to settle out and produce too slow a current for these insects. Number of dipteran (true flies) families decreased from seven families prior to impoundment to three families post-impoundment. Density of dipterans increased after impoundment from 125/sq ft to 494/sq ft (Table 9). In the present study Orthocladius completely dominated the Dipteran community. In the present study Dipterans comprised 61 percent of the samples by number compared to 50 percent prior to impoundment (21 percent by weight) . Chironomids (Tendipedidae) or midges predominated pre- and post- impoundment Dipteran collections, but the complexity of the family and the incompleteness of the data precludes further analysis. White Sturgeon White sturgeon, the largest freshwater game fish in the United States, are limited in their distribution in Montana to the Kootenai River downstream from Kootenai Falls. Limited work was done on the white sturgeon in Montana by the Fish and Game, with six being captured in 1975 and two in 1976, using large mesh gill nets (May and Huston 1977). They ranged in length from 34.0 to 48.0 inches and averaged 18 years in age. No sturgeon were captured using set lines during that period. Sturgeon have probably never been abundant in respect to other game fish in this or any other river. Experienced biologists on the Snake River managed to catch only 0.4 sturgeon per hour from 1973 through 1975 (Coon et al. 1977). However, their large size and fighting ability make for a quality experience. Applegate (1971) documented an angler catch of 30 sturgeon, 42 Table 8. Density of Trichoptera (caddis flies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler, Genera Braehyaentrus Glossosoma Cheumatopsche Hydropsyohe Lepidostoma Rhyaoophila Arctopsyahe Cevaolea Neophylax Total Site. 1 § 2. Su^7 site =5L Number of insects per square foot Kootenai Falls Lowery Site 3 Site 4 Sp Su 1 6 x II 4/ X x 19 sp_ Su 1/ Spring 2/ Summer 3/ Mean for spring, summer and autumn samples 4/ present, less than 1 square foot 10 Gulch TS/ 56 4 3 Table 9. Density of Diptera (true flies) at three sites in the Kootenai Falls area collected during the spring and summer, 1978 and at Lowery Gulch collected from 1969-1971 using a modified round sampler. Numb sr of insects per s quare foot Kootenai Falls Lowery Site 1 5 5 \, Site 3 Site 4 Gulch Genera Su2/ 7 Sp 1 Su 2 sp 1 Su 4 T3/ Simuliwn Protanyderus - - - - X - ■ Antocha & 2 2 - 33 2 Eexatorna 4 X - Thienemannimyia 6 19 X - 14 28 Diamesa 9 12 - - 6 7 Potthastia - - - - 1 - Syrnpotthast-ia - - - 20 - 7 Polypedilum X i <\ - 2 -. 6 Micropseatra - 1 - - - 1 Micvotendipes _ - - - 2 - Rheotany tarsus - - - X - 6 Tany tarsus - 2 - - - 8 Cardioc ladius - X - - - - Criootopus - 6 - X - 6 Eukiefferie I la 6 8 X 2 14 9 Orthoaladius 281 204 68 14 916 717 Pavakieffeviel la X - - - 2 6 Pararne triocnemus - X - X X - Synorthocladius - - - - - 6 Total 305 277 72 93 990 812 125 1/ Spring 2/ Summer 3/ Mean of spring, summer and autumn samples 4/ Present, less than 1 per square foot 44 with five being released from 1968 through 1970 at the canyon mouth, 2.2 miles downstream from the falls. His work was instrumental in determining minimum and maximum size limits for white sturgeon which may not mature until 11 to 22 years of age for males and 26 to 34 years of age for females (Samakula and Larkin 1968). The need for protection of this long-lived species has been recognized in many states. In Idaho, only catch and release fishing is allowed for white sturgeon in the Snake River. In an attempt to determine the present status of white sturgeon in the Kootenai River, we captured and tagged these fish with radio transmitters to follow their movements and document areas of preferred use. Three ditterent white sturgeon were captured a total of seven times. All sturgeon were caught in 3 or 5 inch trammel nets. Seventy- two overnight sets were made during the spring and summer and nine sets were made in the fall. In addition, 80 trotlmes were set overnight and 102 hours were spent fishing during the spring and summer. Little movement of the radio-tagged sturgeon could be documented. Antenna problems developed on two transmitters within 1-7 days after release and the third transmitter could not be picked up after 5 days. Water depths in the canyon area of 70-100 feet were beyond the useful limit of the radio trans- mitters. After release the white sturgeon would position themselves near the mouth of the canyon in this deep water. Netting was restricted to the "sturgeon hole" because of irregular, steep canyon walls and fast water currents in upstream canyon areas. In the sturgeon hole two sturgeon were recaptured after their release. The first one was on June 5 15 days after release. The second sturgeon was recaptured on July 14, 50 days after release and again on October 18, 96 days after the first capture. One angler reported catching a 20-inch sturgeon in the canyon 1.6 miles downstream from the falls on July 20. Another sturgeon was reportedly observed in shallow water just downstream from Troy by a fisherman in a boat during mid- August. Fish Populations Fifteen fish species have been reported in the Kootenai River upstream from Kootenai Falls with four considered abundant and seven uncommon (Table 10). Downstream from Kootenai Falls, 16 species have been reported with five species considered abundant and nine uncommon. White sturgeon and kokanee salmon (Onaorhynahus nerka) were reported below, but not above the falls. Rainbow trout and mountain whitefish were the most abundant game fish in the unimpounded portion of the Kootenai River (May and Huston 1975). Dolly Varden {SalveUnus malma) and kokanee were seasonally abundant below the falls in the spring and fall respectively. Torrent sculpins which were abundant prior to impoundment by Libby Dam are presently considered rare in the 16-mile section downstream from the dam due largely to the effects of gas supersaturation (May and Huston 1975). Mountain whitefish populations also suffered declines for the same reason. The electrofishing section below Kootenai Falls, sampled in 1978 was similar to the Troy section sampled by Fish and Game personnel from 1971 through 1974. In 1978, however, the section extended upstream into the steep 45 Table 10. Relative abundance of fish species collected upstream and downstream from Kootenai Falls Common Name West slope cutthroat trout Rainbow trout Dolly Varden Brook trout Mountain whitefish White sturgeon Burbot Kokanee Torrent sculpin Slimy sculpin Large scale suckers Longnose suckers Northern squawfish Peamouth chub Re&si&e shinier Longnose dace- Scientific Name Salmo clarki lewisi Upstreanfof l/ Downstream of l/ Kootenai Falls Kootenai Falls Salmo gairdneri Salvelinus malma. Salvelirsus fontinalus Fro sop i urn will iamsoni Acipenser t ran smontanu :-:■ Lota lota Oncorhyncbus nerka Cottus rhotheus Cottus cognatus Catostomus macrocheilus Catostomus catostomus Ptychocheilus oregonens: Mylccheilus caurinus Richardsonius balteatus Rhlnichthys cataractae U A U u A N U. R U R A U R R U U A U U A U (J U u R A u u A . R A. -< A -- abundant U -- uncommon. R -- rare, N — not reported 46 canyon area and was shortened on the downstream end. In addition, the Troy section was sampled during the fall and the 1978 section was sampled during the spring. Despite these differences general comparisons can be made. During the 4 years of sampling in the Troy section, the fish population was relatively stable with suckers comprising 50 to 81 percent of the catch (May and Huston 1975). Mountain whitefish were the most abundant game fish comprising 7 to 24 percent of the population. Rainbow trout were the most abundant game fish. In the spring of 1978 a population estimate could only be made of whitefish and suckers (coarsescale) . Coarsescale suckers were the most abundant 746/1000 ft . , followed by mountain whitefish 646/1000 ft. (Table 11). Together whitefish and coarsescale suckers comprised 93 percent of the catch (Table 12). The large number of whitefish could in part be due to a seasonal abundance of whitefish during the spring and summer followed by a subsequent decrease in abundance in the fall as part of the population begins to move on spawning migrations. Whitefish spawning migrations have been documented in the Kootenai River near the Fisher River area (May and Huston 1975) and in other major rivers (Pettit and Wallace 1975, Davies and Thompson 1978). Whitefish eggs were collected in the insect samples made on the gravel bar upstream from the foot bridge below Kootenai Falls. Rainbow trout were the most abundant trout or char during all sampling periods. Dolly Varden abundance was larger in 1978 than 1971-1974. They were concentrated in the upper one-third of the section along the canyon walls. Average size of Dolly Varden was 19.1 inches. In the steep canyon areas the small game fish and rough fish concentrated in cove areas. These areas provided the only gradual sloping bed along the canyon wall. Large numbers of age 1 whitefish were present on the three gravel bars downstream from the mouth of the canyon, indicating that spawning occurred in that area. Population estimates of rainbow trout and mountain whitefish were taken in the Flower-Pipe Section 6.75-11.3 miles miles upstream from Kootenai Falls from 1973 through 19 78, excluding 1976. This section had comparatively fewer suckers than upstream sections and those downstream from the falls (May and Huston 1975). Rainbow trout numbers increased from 24/1000 ft in 1973 to 64/1000 ft in 1974 and remained above 60/1000 ft of stream through 1977 (Table 13 and Figure 20). In 1978, rainbow trout increased to 116/1000 ft of stream. This estimate was taken later in the spring than in previous years, and probably resulted in an underestimate of large rainbow trout. We believed that some of the mature rainbows were still in spawning tributaries. The 1978 estimate was over two times larger than the 1977 estimate for trout between 7.0 and 14.9 inches, but fewer fish over 14.9 inches in length were collected. This decrease could also be related to high fishing mortality on large rainbow trout that was suspected to have occurred during the lower water summer of 1977. Because of the low flows, larger trout were more vulnerable to anglers as determined from reports by numerous anglers. Estimated biomass of yearling and older trout increased from 18 pounds/1000 ft in 1973 to 43 pounds/1000 ft in 1974 and 1975 (Table 13). Biomass continued to increase to 67 pounds/1000 ft in 1977 and 74 pounds/1000 ft in 1978 (Figure 21) The increase in biomass from 1977 to 1978 was only 10 percent compared to an 82 percent increase in numbers. This reflects the small number of larger fish in the 1978 estimate. 47 ion ana coarsescale suckers fiah/lOOO ft) in the Kootenai liver .;.',' to !.'■ miles dovnstr.e.anv,. from Kootenai Falls duri HP" May, 1978 Mountain Whitefish Coars es cale Suckers Group Estimate ;'' Leoc1Lh"(in) fioh/lOOQ ft Group Length ( in) 1TI ,., J. .* v--— J. ,» ." .''jStxiiate ., fish/1000 it 6.6-13.9 IBS 9. 0-11. 9 J&2 1'-' ,0-17.9 2513 12.0-18.7 UO'-i 18 n-P8 0 303 Total 646 4 25^ Total 7^6 f.3# Table 12. Number of fish per section, percent species composition and average size of fish in the Kootenai River below Kootenai Palls No. fish % species - Average , Species per section composition length(rangej Mountain whitefish 530.5 51# 12.3(5.4-18.7) Coarsescale suckers 437.0 42% 16.4(6.6-28.0) Peamouth chubs 30. 8 J>% 10.4(7.4-13.0) Rainbow trout 16.8 2% 12.3(8.7-20.7) Northern squawfish 12.2 1% 13.7(9-7-21.0) Pinescale suckers 4.5 < 1% 14. 4(9-7-16.8) Dolly Varden 2.0 <\% 19.1(13-3-25-4) Cutthroat trout 0.2 <1% 11.5 — 48 Table 13. Population estimates for rainbow trout in the Flower-Pipe Section of the Kootenai River from 1973 through 1977, given in numbers and biomass per 1000 feet of stream. Group length (in) 1973 7.0 - 10.9 li.o - 1-4.9 ^ 14. 9 9-5(39) 15.0(61) Number/1000 ft (percent of total) I97T 1975 1977 22.3(35) 35.8(56) 5-9( 9) 26.1(41) 31.7(49) 6.3(10) 24.1(38) 23-4(37) 16.1(25) Total 24.5+23$ 64.0+13$ 61.1+12$ 63. 6+ 1i 1978 52.7(46) 56.5(49) 6.4( 5) 115.5+20% Biomass/1000 ft (lbs) 18.0+24$ 43.0+13$ 43.2+1* 67.2+22$ 73.9+18% 49 150. 125_ 100 o o 75 50_ 25_ 0 t t + 1977 1978 1973 1974 1975 1976 Figure 20. Population estimates of rainbow trout in fish/1000 ft of stream in the Flower-Pipe Section of the Kootenai River from 1973 through 1977, excluding 1976. 100„ 80 o 60-| o £ 2 3 40_ 20 1973 Figure 21. 1974 1975 1976 1977 1978 Biomass estimates of rainbow trout per 1000 ft of stream in the Flower-Pipe Section of the Kootenai River from 1973 through 1977, excluding 1976. 50 In general, growth rates of rainbow trout in the river have been excellent (May and Huston 1977). Age III rainbow averaged 17.9 inches in 1977 and 16.6 inches in 1978 compared to an average length of 11.4 inches for age III rain- bows in 1973 (Table 14) . Growth rates have continually increased tor age l and age II rainbow trout from 1970 through 1977 (Table 14). In 1978 growth rates had slowed for all three age classes. This may be a reflection of higher densities of trout and whitefish in the river. Growth rates also slowed in the 1974-75 growing season, when growth of age II and age III fish slowed consider- ably. The growth increment for age II fish decreased by 40 percent from the 1973-74 to 1974-75 growing season, but increased by 97 percent in 1975-76 (Table 15) . This decrease in growth was attributed to high flows and gas concentrations during 1974-75 (May and Huston 1975). Rainbow trout densities in the China Rapids to Kootenai Falls section were larger than for any section of the river previously censused (Table 16) . There were 228 (+33 percent) rainbow trout per 1000 ft of stream in this section, 97 percent~more than estimated for the Flower-Pipe section sampled in the spring (Table 13). This included one +12 pound and one +7 pound rainbow trout (Figure 22) . These estimates are undoubtedly low and are primarily useful in monitoring annual changes in relative abundance of rainbow trout. The total number of trout that would be expected in the 3.5 mile reach upstream from the falls using the 1978 estimate was 4,213 rainbow trout over 9.0 inches. A minimum total catch of rainbow trout was estimated to be 8,232 fish for the same stream reach (445/1000 ft) using the 1978 creel census data. The estimate illustrates the large number of rainbow trout that are presently supported in the Kootenai Falls section. The large difference between the fall estimate in the Kootenai Falls section and the spring estimate in the Flower-Pipe is due in part to absence of some of the mature rainbow trout in the spring estimate because they were still in the spawning tribu- taries. A second factor was the fact many age I fish were more susceptible to electrofishing in the fall because they were larger. This was countered in part because the fall estimate only included fish over 9.0 inches in length compared to a 7.0 inch minimum length in the spring estimate. Biomass estimates of rainbow trout in the Kootenai Falls section were 95 percent larger than in the Flower-Pipe section. Growth rates of rainbow between the two sections could only be compared for the 1976 year class because data were lacking in the Kootenai Falls section prior to 1978. Back calculated growth was 2.3 inches at age I and 9.8 inches at age II for a 7.5 inch increment of growth in the Kootenai Falls section. Back calculated growth was 2.8 inches at age I and 10.8 inches at age II for an 8.0 inch increment of growth in the Flower-Pipe section (Table 15) . Kootenai River rainbow trout generally rear one or more years in a tributary stream "migrate into the main stem of the Kootenai Appro xm lyJSJ percent of the rainbow trout that "smolf do so at age 1 ana at age 2. First year growth in the main river was "^"s^lfter rear?ng irsM r-vfr1: &9^nJ^«£££«£^ ~^:^l in tne main ixvcj., <-i 1Q7A aT1ri l 077 spawning runs into Libby in the spring. As determined from the 1976 and IS// spawning tT.10,000 cfs) and low flows (<10,000 cfs). Both high and low flow days occurred with relative frequency during these months. Fishing pressure was also large during July and August. Success was higher during low flows with one out of two fishermen catching fish during that period compared to one out of three fishermen catching fish under high flow conditions (Table 25). This difference was consistent during both months. 62 Table 23. Residence of anglers contacted in the Kootenai Falls angler survey in 1978. Season January - May June - November Total Lincoln County (%) 175 (75) 247 (57) 422 (63) Residence of Fishermen Out-of- County(%) 40 (17) 69 (16) 109 (16) Out-of- State(%) 18 ( 8) 117 (27) 135 (20) Table 24. Type of gear used by anglers in the Kootenai Falls angler survey in 1978. Type of Ge ar Season January - May June - November Natural (%) 162 (68) 218 (51) Lures (%) 7 ( 3) 69 (16) Flies (%) 35 (15) 68 (16) Combination (%) 33 (14) 75 (17) Total 380 (57) 76 (11) 103 (15) 108 (16) Table 25. Number of successful anglers contacted on the Kootenai River under high flow (>10,000 cfs) and low flow (<10,000) conditions in July and August, 1978. Month High Flow Low Flow Number of Anglers Number Successful (%) Number of Anglers Number Successful ("") 63 LITERATURE CITED Adair, W. D. and J. J. Hains . 1974. Saturation values of dissolved gases associated with the occurrence of gas-bubble disease in fish in a heated effluent. Proc. Symp. Augusta, Ga. May 3-5, 1973. P59. Conf-730505, U.S. Dept. of Commerce, NTIS, Springfield, Va. Applegate, V. 1971. The white sturgeon - a case for regulation. Mimeo rept on file at Montana Fish and Game field station, Libby, Mt. 8 pp. Bonde T. J. H. and R. M. Bush. 1975. Kootenai River water quality investigations - Libby Dam pre impoundment study. 1967-1972. Seattle District, Army Corps of Engineers. 124 pp. Bouck C R et al. 1976. Mortality, Saltwater Adaption, and Reproduction of Fish During Gas Supers aturation. EPA 600/3- 76-050, U.S. EPA., Duluth, Minn. Coon, J. C, R. R. Ringe and T. C. Bjornn. 1977. Abundance, growth, distribution 'and movements of white sturgeon in the mid-Snake River. Idaho Water Resources Research Institute. Proj . B-026-IDA. 63pp. Cordone, A. J. and D. W. Kelley. 1961. The influences of inorganic sediment on the aquatic life of streams. Calif. Fish and Game 47(2) :189-228. Davies, R. W. and G. W. Thompson. 1976. Movements of mountain whitefish (Prosopium williamsoni) in the Sheep River watershed, Alberta. J. Fish. Res. Board, Canada. 33(11) : 2395-2401 . Dawley, E. M. and W. J. Ebel. 1975. Effects of various concentrations of dissolved atmospheric gas on juvenile chinook salmon and steelhead trout. Fish. Bull., 73-787. Egloff, D. A. and W. H. Brakel. 1973. Stream pollution and a simplified diversity index. J. Water Pollut. Contr. Fed. 45:2269-2275. Fickeisen, D. H. and J. C. Montgomery. 1978. Tolerances of fishes to dissolved gas supersaturation in deep tank bioassays. Trans. Amer. Fish. Soc. 107 (2) :376-381. undated. Dissolved gas saturation: bioassays of Kootenai River organisms. Battelle, Pacific Northwest Laboratories, Richland, Wa. Fickeisen, D. H., M. J. Schneider and J. C. Montgomery. 1975. A comparative evaluation of the Weiss saturometer. Trans. Amer. Fish. Soc. 104(4): 816-820. Fisher, S. G. and A. LaVoy. 1972. Differences in littoral fauna due to fluctuating water levels below a hydroelectric dam. J. Fish. Res. Board, Canada 29(10) :1472-1476. Haynes, J. M. , R. H. Gray and J. C. Montgomery. 1978. Seasonal movements of white sturgeon [Acipensev transmontanus ) in the mid-Columbia River. Trans. Amer. Fish. Soc. 107(2) :275-280. 64 Hynes, H. B. N. 1970. The ecology of running waters. Univ. of Toronto Press. Toronto. 555 pp. Kaesler, R. L. and E. E. Herricks. 1977. Analysis of data from biological surveys of streams: diversity and sample size. Water Resources Bulletin. Vol. 13(1). Krebbs, C. J. 1972. Ecology: the experimental analysis of distribution and abundance. Harper and Row, N.Y. 696 pp. Lehmkuhl, D. M. 1972. Change in thermal regime as a cause of reduction of benthic fauna downstream of a reservoir. J. Fish. Res. Board Can. 29(9): 1329-1332. May, B. and J. E. Huston. 1977. Kootenai River fisheries investigation - March 1, 1976 through April 30, 1977. Annual prog, rept., Montana Dept. of Fish and Game. 14 pp. 1975. Status of fish populations in the Kootenai River below Libby Dam following regulation of the river. Final job rept. contract no. DACW 67-73-C-003. Mont. Dept. of Fish and Game. 28 pp. . 1974. Status of fish population in Kootenai River below Libby Dam following initial regulation of the river. Job prog. rept. Contract no, DACW 67-73-C-0003. 19 pp. . 1973. Status of fish populations in Kootenai River below Libby Dam following initial regulation of the river. Job prog, rept., Contract no. DACW 67-73-C-0003. 29 pp. Neuhold, J. M. and K. H. Lu. 1957. Creel census method. Utah State Dept. of Fish and Game, Pub. No. 8. Newell, R. L. 1976. Yellowstone River study. Mont. Dept. of Fish and Game and Intake Water Co., Final rept. 259 pp. Orr, H. , J. C. Marshall, T. L. Isenhour, and P. C. Jurs. 1973. Introduction to computer programming for biological sciences. Allyn and Bacon, Inc. Boston. 396 pp. Peterson, N. W. 1973. Inventory of waters of the project area. Job prog, rept., federal aid in fish and wildlife restoration acts. Mont. Proj . F-9-R-20, Job lb, 11 pp. Pettit, S. W. and R. J. Wallace. 1975. Age, growth and movement of mountain whitefish (Prosopium williamsoni) (Givard) in the North Fork Clearwater River, Idaho. Trans. Amer. Fish. Soc. 104(1) :68-76. Philipson, G. N. 1954. The effect of water flow and oxygen concentration on six species of caddisfly (Trichoptera) larvae. Proc. Zool. Sci. London 124:547-564. Pielou, E. C. 1977. Mathematical ecology. John Wiley and Sons, N.Y. 384 pp. 65 Rabeni, C. F. and K. E. Gibbs. 1978. Comparison of two methods used by divers for sampling benthic invertebrates in deep rivers. J. Fish Res. Board Canada 35 (3): 332-336. Semakula, S. N. and P. A. Larkin. 1968. Age, growth, food, and yield of the white sturgeon (Aaipenser transmontanus ) of the Fraser River, British Columbia, J. Fish. Res. Board Canada 25(12) : 2589-2602. Spence, J. A. and H.B.N. Hynes. 1971. Differences in benthos upstream and downstream of an impoundment. J. Fish. Res. Board Can. 28:35-43. Vincent, R. 1971. Electrofishing and fish population estimates. The Progressive Fish Culturist. 33(3) : 163-169. Ward, J. V. 1976. Comparative limnology of differentially regulated sections 'of a Colorado mountain river. Arch. Hydrobiol. 78(3) :319-342. Wilhm, J. L. and T. C. Dorris. 1968. Biological parameters for water quality criteria. Bioscience 18:477-481. Workman, D. L. 1976. Inventory of wafers of the project area. Job prog. rept. Fed. aid in fish and wildlife restoration acts. Mont, proj . F-9-R-24, Job I-c. 22 pp. 66 Appendix A-l Species Diversity Analysis Square-foot bottom sampler 67 MONTANA DEPARTMENT OF FISH AND GAMb SPECIES DIVERSITY ANALYSIS STATION: R- 1 AND 2 NUMBER OF SAMPLERS: 2 SAMPLING PERIOD: APRIL 13, 1978 RANK ABUNDANCE PERCENT CF TOTAL 1 2 3 4 5 6 7 a <3 10 11 1 2 1 3 935 I2e 32 30 1 8 17 6 77.4 10.6 2.7 2.6 2.5 1 .5 1 .4 0.5 0.2 0.2 0.2 0.2 0.1 TOTAL 12 08 100.0 SHANNON BRILLCUIN DIVERSITY MAXIMUM DIVERSITY MINIMUM DIVERSITY REDUNDANCY EVENNESS EQUITABILITY SPECIES RICHNESS 1.33 2.70 3.12 0.66 o . 3 e 0.13 1 .20 1 .30 3.66 0.10 0.66 0.36 0.15 1.15 68 MONTANA DEPARTMENT GF FISH AND GAME SPECIES DIVERSITY ANALYSIS SiVeZ, STATION: R-.3 AND 4 NUMBER OF SAMPLERS: 2 SAMPLING PERIOD: APRIL 13. 1978 RANK I 2 3 4 5 6 7 8 9 10 11 12 13 14 ABUNDANCE 21 1 189 144 133 15 12 9 5 5 5 3 I I 1 PERCENT OF TOTAL 28. 7 25. 7 19, 6 18. 1 2. 3 1 c .6 1. 2 0- .7 0. 7 0.7 0. 4 0. 1 0.1 0. I TOTAL 7 34 100.0 SHANNON BRILLOUIN DIVERSITY MAXIMUM DIVERSITY VI NI MUM DIVER5I TY REDUNDANCY EVENNESS EQUITABIL1TY SPECIES RICHNESS 2.44 3 .81 0 .19 0.38 0.64 0.26 2.18 2.39 3.74 0. 17 0 .38 0.6 4 0.30 2.09 69 MONTANA DEPARTMENT OF FISH AND GAVE SPECIES DIVERSITY ANALYSIS staticn: R-5 AND 6 NUMBER OF SAMPLERS: 2 SAMPLING PERIOD: APRIL 14, 1978 RANK ABUNDANCE 1 137 2 4 3 1 4 1 5 1 6 1 TOTAL 145 100.0 MINIMUM DIVERSITY 0.30 0.25 REDUNDANCY 0.95 0.95 EVENNESS 0.16 0.15 EQUITABILITY 0.06 0.06 SPECIES RICHNESS 0.36 0.30 SHANNON 0 .42 2 .58 0 .30 3 .95 3 .16 0 .06 0 .36 PE RC! ENT OF TOTAL 94 o5 2 o 3 0 .7 0 .7 0 .7 0 o7 BRILLCUIN DIVERSITY 0.42 0.36 MAXIMUM DIVERSITY 2.53 2.47 70 MONTANA DEPARTMENT OF FISH AND GAME SPECIES DIVERSITY ANALYSIS s;Wl station: r-7 and a NUMBER OF SAMPLERS: 2 SAMPLING PERIOD: APRIL 14, 1978 RANK I 2 3 4 5 6 7 a 9 10 111 12 13 14 15 16 17 a a 19 20 21 22 23 ABUNDANC 1832 148 66 32 28 27 1 3 13 1 1 7 4 3 2 2 2 1 1 PERCENT OF TOTAL 83.3 e.7 3.0 1 .5 1.3 1 .2 0.6 0.6 0.5 0.3 0.2 0.1 0.1 0,1 0.1 0.0 0.0 0.0 0.0 0.3 0.0 0.0 0.0 TOTAL 2198 100.0 SHANNON DIVERSITY 1.13 MAXIMUM DIVERSITY 4.52 MINIMUM DIVERSITY 0.13 REDUNDANCY 0.77 EVENNESS 0 .25 EQUITABILITY 0 .10 SPECIES RICHNESS 1 .03 BRILLOUIN 1 .11 4,48 0. 1 1 0.77 0. 25 0. 1 1 0 .99 71 MONTANA DEPARTMENT OF FISH AND GAME SPECIES DIVERSITY ANALYSIS s;-k I station: R- I AND ? NUMBER CF SAMPLERS: 2 SAMPLING PERIOD: AUGUST 1, 1978 PERCENT RANK ABUNDANCE OF TOTAL 608 5 2.2 321 27.6 55 4.7 29 2.5 22 1 .9 21 1.8 19 1.6 16 1.4 16 1.4 10 0.9 10 0.9 9 0.8 e 0.7 5 0.4 4 0.3 4 0.3 2 0.2 2 0.2 1 0.1 1 0.1 1 0.1. 1164 10 0.0 I 2 3 4 S 6 7 S 9 10 11 12 13 14 15 16 17 i e 19 20 21 TOTAL DIVERSI TY VAX IMUM DIVERSI TY MINIMUM DIVERSITY REDUNDANCY EVENNESS EGUITABILI TY SPECIES RICHNESS SHANNON RRILLCUIN 2.19 2. 14 4.39 4.32 0.20 0.17 0 .52 0.53 0.5 3 0.50 0.22 0.24 1 .38 1.90 72 MONTANA DEPARTMENT OF FISH AND GAMF SPECIES DIVERSITY ANALYSIS S.--U.Z. station: R-3 AND 4 NUMBER OF SAMPLERS: 2 SAMPLING PERIOD: AUGUST 1. 1978 RANK ABUNDANCE PERCENT OF TOTAL I 2 4 5 6 7 S 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 20? 133 78 53 40 34 33 33 17 17 I 6 12 8 5 5 2 I ! 1 26.9 23.8 10*1 6.9 5.2 4.4 4.3 4.3 2.2 2.2 2. 1 1 .6 1.3 1.0 1.1 0.7 O.? 0.5 0*3 0.1 0.1 0.1 0.1 TOTAL 769 100.0 SHANNON DI VERSI TY 3.29 MAXIMUM DIVERSITY 4.52 MINIMUM DIVERSITY 0 . 31 REOUNCANCY 0.29 EVENNESS 0.73 EQUITABILITY 0. 34 SPECIES RICHNESS 2.95 PRILLGLIN 3,21 4.42 C.27 0.29 0.73 0 .3 9 2.81 73 HUNT /SNA DEPARTMENT OF FISH AND SPEC-IE S DIVERSITY ANALYSIS GAVE s.4x2 3 o STATION: K-5 NUMBER OF SAMPLERS: 1 SAMPLING PERIOD: AUG 2, 1978 RANK 1 I 3 4 5 ABUNCANCE 6 2 2 1 1 PERCENT CF TOTAL 5C >C 16. ,7 16, ,7 8, .3 8. 3 TOTAL 12 100.0 JI VERS I TY MAXIMUM DIVERSITY MINIMUM DIVER SI Tf REDUNDANCY EVENNESS E0U1TABILI FY SPECIES RICHNESS HANNQN BPILLCUIN 1.96 1.45 2.32 1.72 1. 53 1. 13 0.49 C.47 0.84 0.84 0.5 5 C.60 1.41 C.64 74 1GN1 ANA DEPARTMENT Of FISH AND SPECIES DIVERSITY ANALYSIS GAME Sik3 STATION: R-6 NUMBER OF SAMPLERS: 1 SAMPLING PERIOD: AUG. 1978 RANK 1 2 3 4 5 6 7 a 9 10 11 12 13 TUTAL ABUNCANCE 39 23 6 5 4 3 2 2 I 1 1 I S2 PERCENT CF TCTAL 42. 4 €.5 5.4 4.3 4.3 3.3 1.1 1.1 10C.C Ul VER SI TY MAXIMUM DIVERSITY MINIMUM UI VERSITY REDUNDANCE EVENNESS EQUITAB1LI TV- SPECIES RICHNESS SHANNON PPILLCUIN 2.59 2.32 3.70 3.36 1.C3 0.84 a. 42 C.41 0.70 C.69 C.40 C.45 2. 19 1.87 75 MONTANA DEPARTMENT OF FISH AND GAME SPECIES DIVERSITY ANALYSIS S ;^e 4 station: R-7 anc 8 NUMBER OF SAMPLERS: 2 SAMPLING PERIOC: AUGUST 2, 1978 PERCENT RANK ABUNDANCE OF TOTAL 1434 76.8 158 8.5 se 3.0 27 1 .4 18 1.0 ie 0.9 15 0.8 14 0.8 14 0.8 14 0.8 13 0.7 13 0.7 11 0.6 11 0.6 11 0.6 10 0*5 8 0.4 6 0.3 6 0.3 3 0.2 2 0.1 2 0.1 1 0.1 1 0.1 1 0.1 1 0. 1 1866 100.0 1 2 3 4 5 6 7 a 9 10 11 12 1 3 14 15 16 17 13 19 2) 21 22 23 24 25 26 TCTAL ERILLOUIN DIVERSITY 1.59 1.55 MAXIMUM DIVERSITY 4.TQ 4.64 MINIMUM DIVERSITY 0.16 0.15 REDUNDANCY 0.69 0.69 EVENNESS 0.34 0.33 EOUITAHILITY 0.15 0.16 SPECIES RICHNESS 1.44 1.39 SHANNON J . 59 4 .70 3 .1 6 3 .69 0 .34 0 .15 I .44 76 Appendix A- 2 Species Diversity Analysis Small- substrate basket sampler 77 MUNTANA DEPARTMENT CF FISH AND SPECIES DIVERSITY ANALYSIS GA^E STATION: SB-1 NUMBER OF SAMPLERS: 1 SAMPLING PERIOD: APRIL L3- MAY 30, 197 8 RANK 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 TOTAL ABUNDANCE 49 3 469 121 63 £3 18 17 7 7 5 \ 2 2 t 1 12 73 PERCENT CF TCTAl 38. 7 36, 8 9. 5 4. ,9 4. .9 1 ,4 1 = 3 C = 5 c ,5 c ,4 0 ,3 0 = 2 G = 2 0 .1 c ,1 100. 0 01 VtRSITY MAXIMUM DIVERSITY MINIMUM DIVERSITY REDUNDANCY EVENNESS EQUIT ABILITY SPECIES RICHNESS SHANNON PRtLLCUIN 2. 17 2.14 3.91 3.86 C.13 0.11 0.46 G.46 0.55 0.55 0.21 0.24 1.96 1.89 78 MONTANA CEPAPTMENT OF FISH ANC SPECIES DIVERSITY ANALYSIS GAME STATION: SB-2 NUMSER OF SAMPLERS: 1 SAMPL ING PERIOD: APRIL L3 - MAY 3C, 1978 RANK I 2 3 4 3 6 7 8 9 10 TOTAL ABUNCANCE 374 356 242 124 56 28 4 2 2 12C2 PERCENT CF TCTAL 31.1 29.6 20.1 10.3 4.7 3.2 0.3 C.3 0.2 0.2 1GC.G J1VERSI TY MAXIMUM DIVERSITY MINIMUM DIVERSITY REDUNDANCE EVENNESS EQUITAB1LI TY SPtClES RICHNESS HANNON 8PILLCUIN 2.30 2.27 3.32 3.29 0.C9 0.C8 0.32 C.32 0.69 C.69 C.22 0.26 2.07 2.01 79 MONTANA' DEPARTMENT GF FISH AND GAI"F SPECIES DIVERSITY ANALYSIS ST ATI UN: SB-3 DUMBER OF SAMPLERS: 1 SAMPLING PERIOD: APRIL |4 - MAY 3C, 1978 RANK 1 2 3 4 5 6 7 8 . 9 10 11 TOTAL ABUNDANCE HO 57 22 12 7 4 4 2 1 1 251 PERCENT CF TOTAL 55, ,B 22, ,7 8, .8 4, , e. 2. ,8 1. ,6 1, .6 0. = 8 0, .4 0, ,4 0 c4 1CC.C litVER SI TY MAXIMUM DIVERSITY MI NIMUM J I VERSITY RE iXJNOANC.Y EVENNESS EQUITABILI TY SPECIES RICHNESS SHANNON OPILLCUIN 1.96 1.86 3.46 3.32 0.3 7 0.32 C.49 C.49 0.57 0.56 C.25 C.28 1.71 1.58 80 ? "f i 4 Appendix A- 3 Species Diversity Analysis Large-substrate basket sampler 81 MONTANA DEPARTMENT OF SPEC IES DIVERSITY FISH ANE GAME ANALYSIS STATION: L13-L NUMBER UF SAMPLERS: 1 SAMPLING PERIOD: APKIL 13 - MAY 3C, 1978 RANK ABUNDANCE PERCENT CF TCTAL 1 2 3 4 5 6 7 8 9 10 11 12 13 4C9 35£ 271 4 7 29 27 12 6 4 4 ? 2 1 35. C 30.4 2 C 23, 4, 2.5 2.3 1.0 0.5 C.3 C.3 0.2 0.2 C.l TOTAL 117C 100.0 JI VERS1 TY MAXIMUM DIVERSITY MINIMUM DI y/ERSITY REDUNDANCY EVENNESS LQUI TABILl TY SPECIES RICHNESS HANNON RRILLOUIN ?. 19 2.16 3.70 3.66 G.12 CIO C.42 C.42 C.59 C.59 0,21 0.25 1.97 1.91 82 MONTANA DEPARTMENT CF FISH AND CANE SPECIES DIVERSITY ANALYSIS STATION: NUMBER UF SAMPL ING LB-2 SAMPLERS: 1 PERIOD: APRIL 13 - MAY 3; 19 7 R RANK 1 2 3 4 5 6 8 9 10 11 12 TOTAL A BUN CAN IE 628 34 8 256 6 5 56 24 6 3 3 2 1 1 1393 PERCENT rF TOTAL 45 .1 25 ■ G 18 = 4 4 = 7 4 .0 1 = 7 C .4 c .2 0 ,2 c = 1 c .1 0 .1 IGG.O 01 VfcRSl TV MAXIMUM DIVERSITY MINIMUM 01 VERS1TY REDUNDANCY Ev/ENNESS EQUITABILI TY SPECIES RICHNESS SHANNON 2. C6 3, 58 Cc 09 44 Cc 58 0. 20 1 = £6 BPILLCUIN 2.04 3.55 C.C8 0.44 G.57 C.23 1-81 83 MONTANA DEPARTMENT CF FISH AND GAFF SPECIES DIVERSITY ANALYSIS STATION: LB- 3 JUM8ER OF SAMPLERS: 1 SAMPL ING PERIOD: APRIL 14 - MAY 3d 19 78 RANK ABUNDANCE PERCENT CF TCTAL 1 2 3 4 5 6 7 8 9 10 83 51 47 36 3 2 2 I 1 1 36.6 22.5 2C.7 15.9 1.3 0.9 C.9 C.4 G.4 C.4 TO TAL 227 100.0 01 VERSITY MAXIMUM DIVERSITY MINIMUM DI VERSITY REDUNDANCY EVENNESS EQUITAB1LI TY SPECIES RICHNESS SHANNON 2.21 3.32 0.27 0.38 0.6 7 0.28 1.93 3RC1LOUIN 2 ,12 1 .19 0. .31 0, .37 c. .66 0, 33 1, 79 84 ■,7f ?