ML113260356

Environ Monitoring & Ecological Studies Program for Monticello Nuclear Generating Plant,1980 Annual Rept.

ML113260356
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Issue date:	07/30/1981
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ENVIRONMENTAL MONITORING AND ECOLOGICAL STUDIES PROGRAM for the MONTICELLO NUCLEAR GENERATING PLANT K Monticello, Minnesota 198O ANNUAL REPORT I I I 81 A 05000263 PDR

CONTENTS INTRODUCTION.

WATER MONITORING STUDIES Water Monitoring Summary (Physical Parameters)....... 1.1-1 Water Monitoring Summary (Chemical Parameters)...... 1.2-1 ECOLOGICAL STUDIES Electrofishing Survey......................................2.1-1 Fish Seining Study............................. ........ 2. 2-1 Fish Y(ear-Class Strength .................................. 2.3-1

INTRODUCTION Two areas of ecological monitoring were conducted in 1980:

Water Quality and Fishery Studies. The objectives of the water quality study were to determine if plant operation was altering certain chemical parameters within the river and to determine if these changes (if any) had any effect on the fishery. Because the Mississippi River near Monticello.is a large, turbulent stream with a boulder substrate, many conventional fish sampling methods are impractical. Two techniques that have worked well for capturing specimens are electrofishing and seining. Large fishes are efficiently sampled by electrofishing, and small species and young fishes are captured by seining. The objective of the electrofishing and seining studies was to assess the rela tive abundance and seasonal distribution of fish in response to the plant discharge plume. A paper assessing the influence of several parameters on fish year-class strength is also presented.

This is the thirteenth consecutive report (tenth opera tional) summarizing environmental monitoring activities for the Monticello Nuclear Generating Plant (MNGP).

Science Services Section Environmental and Regulatory Activities Department Northern States Power Company (NSP)

July 15, 1981

MONTICELLO NUCLEAR GENERATING PLANT ENVIRONMENTAL MONITORING PROGRAM 1980 ANNUAL REPORT WATER MONITORING

SUMMARY

(1.1)

(Physical Parameters)

Prepared for Northern States Power Company Minneapolis, Minnesota by Science Services Section Environmental and Regulatory Activities Department Northern States Power Company 1.1-1

1.1 1980-MONTICELLO WATER MONITORING

SUMMARY

(PHYSICAL PARAMETERS)

The Monticello Nuclear Generating Plant (MNGP) had four outages during 1980 (Table 1.1-1). These outages accumu lated to slightly more thah 75 days. The outage of greatest duration began on February 23 and terminated on April 5.

MNGP's on-line performance for 1980 was 79 percent.

Data are collected hourly by the plant computer on the circulating water system at MNGP. These data were trans formed into weekly averages and are listed in Table 1.1-2.

Total precipitation in 1980 for central Minnesota (St. Cloud Weather Bureau data) was very close to the 40-year average (26.48 inches). However, April, May, July, October, and November were exceptionally dry months, which resulted in below average river discharge (4,400 cfs) for much of the year (Table 1.1-3). Maximum river discharge occurred in mid-April during a moderate spring run-off (Figure 1.1-1).

Minimum river discharge occurred in July and August, just prior to periods of extensive precipitation during August and September.

The rate of water withdrawal from the Mississippi River by MNGP was quite consistent and generally ranged between 500 and 600 cfs (Figure 1.1-2). The only deviations from this pumping rate occurred during plant outages and intake icing conditions.

Ambient river water temperatures are illustrated in Figure 1.1-3. Winter temperatures were consistently at 32*F; warming did not begin until early April. Maximum weekly mean temperature of 81"F occurred in mid-July during the low water period. Temperatures gradually declined in the fall, reaching 320 F in early December.

1.1-3'

Winter discharge canal water temperatures generally ranged between 650F and 750F (Figure 1.1-4). . Maximum discharge canal temperatures, slightly exceeding 92*F, occurred in late-May and mid-July. Discharge temperatures throughout the summer were generally near 850F, due to "helper mode" plant operation (once-through cooling tower operation) from late-May to September.

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Table 1.1-1 1980 MONTICELLO OFF-LINE TIME Date Off Date On Outage Time (Hrs) 2/23 (1800 hrs) 4/5 (2000 hrs) 1010 4/19 (2000 hrs) 4/28 (1400 hrs) 210 4/29 (0200 hrs) 5/15 (1100 hrs) 393 11/5 (2200 hrs) 11/14 (0300 hrs) 197 Total 1810 hrs (75.4 Day) 1.1-5

Table 1.1-2 I 1980 MONTICELLO WATER SYSTEM SUMMARIES River Plant Ambient River Discharge Canal I

Week Of 1/4/80 Discharge 4167 Intake (cfs) 543 Temp OF 32.0 Temp OF 65.1 I

1/11 3604 543 32.0 64.4 1/18 1/25 4049 4979 658 431 32.0 32.0 63.8 68.0 I 2/1 2/8 2/15 5879 4960 5082 277 215 432 32.4 32.5 32.1 79.3 64.2 63.5 I

2/22 4583 411 2/29 4782 7 32.3 32.1 56.6 36.9 I 3/7 4645 9 32.1 34.4 3/14 3/21 3/28 4569 4212 4683 6

5 5

32.1 32.5 32.7 34.3 34.9 34.4 I

4/4 4/11 7189 11571 39 520 33.0 37.0 35.0 63.1 I

4/18 10844 536 42.3 72.2 4/25 5/2 7645 6044 181 131 55.4 61.0 5

59.1 62.9 5/9 5/16 5/23 4758 3550 3083 57 259 574 61.5 57.9 64.5 64.3 64.8 92.3 I

5/30 6/6 2458 3076 550 557 71.7 69.9 87.8 84.8 I

6/13 4053 549 69.0 83.4 6/20 4201 545 70.8 84.2 6/27 3582 549 74.2 88.4 7/4 7/11 7/18 2582 2013 1772 539 545 541 72.1 78.3 80.7 85.8 91.5 92.5 I

7/25 2211 8/1 1848 541 537 76.3 76.7 88.9 85.7 I

8/8 1696 565 75.1 75.2 8/15 8/22 8/29 2008 2045 2342 560 558 568 73.5 70.7 71.9 73.5 70.7 72.7 I

9/5 9/12 2666 3382 552 562 69.1 69.0 80.3 86.4 I

9/19 5408 569 60.9 88.6 9/26 4471 573 56.7 85.7 I

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I Table 1.1-2 (Continued)

River Plant Ambient River Discharge Canal Week Of Discharge Intake (cfs) Temp OF Temp OF 10/3/80 4001 584 55.0 85.1 10/10 3317 578 59.5 85.1 10/17 3185 552 48.0 78.8 10/24 3427 550 45.1 77.2 10/31 3922 545 39.8 73.1 11/7 4004 442 40.8 64.2 11/14 3950 194 39.4 45.4 11/21 3683 418 35.7 64.7 11/28 3384 446 33.4 68.4 12/5 2693 474 32.7 74.0 12/12 3132 440 32.4 76.9 12/19 3399 481 32.7 76.3 12/26 2836 470 32.3 75.6 12/31 3352 522 32.1 75.2 1.1-7

Table 1.1-3 MISSISSIPPI RIVER AT MONTICELLO, MINNESOTA Monthly Average River Discharge (cfs) 1973 1974 1975 1976 1977 1978 1979 1980 January 3755 3787 6908 3459 1295 5800 4830 4557 February 3644 3875 6297 3763 1754 4800 5469 4856 March 11132 3796 5620 7796 3341 7500 6352 4653 April 6361 11513 18122 11700 3350 10500 17161 9138 May 6678 16387 26355 3815 2202 7000 17550 3611 June 4038 12370 9323 1903 2475 6500 9028 3698 July 2189 3918 12137 1852 2323 5500 9313 2008 August 4340 3458 3654 1203 1275 6000 4818 2036 September 2771 1616 3325 1052 3420 6500 3919 4105 October 12289 1719 3133 1151 5617 4700 2967 3522 November 7418 4171 3625 1331 6783 3996 6974 3755 December 4723 2572 3340 1286 6046 3376 4228 3080 Average 5778 5765 8395 3359 3323 6014 7717 4085 I

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mm mm m m rm m m-mma Figure 1.1-1. Monticello 1980 12000- Weekly Average River -12000 Discharge (CFS).

10000- -10000 Co, LL 8000- -8000 Co) w

< 6000- 6000 Co) 0 m 4000- -4000 2000- -2000 0 0 J F M A M J J A S 0 N D MONTH

-j

Figure 1.1-2. Monticello 1980 Weekly Average Plant Intake Withdrawal Rate (CFS)

CI)

H H W H

0 z

I-z

-j a.

MONTH m - m ~ ~ . -

m we Mmm -eeMMMMMM Figure 1.1-3. Monticello Weekly Average River Temperature (*F).

80 L 7 0

Z 70 1 5 60 I 50 CL w 40 MONTH

Figure 1.1-4. Monticello 1980 Weekly Average Discharge Canal Water Temperature (*F).

1 00 L.

H w M

H Z-H MONTH m - m - ~ -

MONTICELLO NUCLEAR GENERATING PLANT ENVIRONMENTAL MONITORING PROGRAM 1980 ANNUAL REPORT WATER MONITORING

SUMMARY

(1.2)

(Chemical Parameters)

Prepared for Northern States.Power Company Minneapolis, Minnesota by Sciences Services Section Environmental and Regulatory Activities Department Northern States Power Company 1.2-1

1.2 MISSISSIPPI RIVER WATER MONITORING SAMPLE ,

1.2.1

SUMMARY

The 1980 Mississippi River water monitoring program was identical to the programs of 1972 through 1.979. Three sampling sites were used in the acquisition of water quality data used in assessing the impact of the discharge from the Monticello Plant on the river.

The three sampling sites used were the discharge outfall, 1,000 feet upstream of the outfall, and 1,000 feet down stream of the outfall. Samples were taken during the last week of the month from January through December. Sample collection analyses were done by NSP personnel. The NSP Chestnut Street Testing Laboratory was used for the analyses. Procedures for collection and analyses were as outlined in US EPA Manual of Methods for Chemical Analyses of Water Wastes and APHA-AWWA-WPCF Standard Methods for the Examination of Water and Wastewater (14 Editions 1975).

Results of the analyses are presented in Table 1.2-1. A comparison of the discharge outfall and downstream transect values showed a significant difference only in the tempera ture values. This variation was apparent both on a monthly and an annual average comparison. The most significant variation for an extended portion of the year occurred during the months of September through January. Differences in temperature during this period ranged from 8.0*C in September to 220C in January.

1.2-3

I As in past years of monitoring, impact exerted by plant effluent discharge is observed on the significant elevation of the physical water quality temperature. This impact is, as expected, most evident at the discharge outfall. How ever, any attempt to extrapolate concern for the river system, based on the impact seen at the outfall, should dissipate when consideration is given to the impact of downstream transect, which is 1,000 feet from the discharge outfall.

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Monticello Environmental Monitoring Table 1.2-1 Mississippi River Water Dissolved Oxygen Specific Conductance Temp 0 C 0 mg/i1 02 pmhos/cm 25 C 1980 Upstream Downstream Discharge Upstream Downstream Discharge Upstream Downstream Discharge January 0 4 22 11.8 10.2 8.4 248 250 282 February 0 0 0 12.9 12.5 12.5 231 225 221 March 0 0 0 12.0 13.0 11.8 232 262 268 April 14 16 24 10.3 10.0 9.6 237 230 230 May 26 28 35.5 10.1 9.2 7.5 325 380 425 June 24 27 31 10.4 11.0 7.9 350 350 360 July 23.5 25.5 27.5 8.4 7.8 7.4 340 340 340 August* 19 24 25 8.0 8.4 7.6 350 360 360 September 12 16.5 20 10.6 9.3 9.6 240 280 280 October 9 12 18 12.8. 11.8 12.5 250 255 320 November 0 4 17 13.5 12.1 12.4 250 250 255 December 0 5 19 13.0 12.0 10.2 220 220 355 Average 10.6 13.5 19.9 11 11 10 273 306 305 Total Dissolved Solids Sulfate pH mg / 1 mg/i SO4 Upstream Downstream Discharge Upst ream Downstream Dis charge Upstream Downstream Discharge January 7.3 7.4 7.4 210 210 220 9 10 9 February 7.7 7.6 7.7 220 220 220 11 10 7 March 7.7 7.9 7.7 210 210 210 8 8 9 April 8.1 8.0 8.2 150 150 150 8 8 8 May 7.9 7.8 7.4 190 180 170 9 10 8 June 8.4 8.4 8.4 200 210 200 8 9 9 July 8.6 8.6 8.7 210 200 210 August 8.6 8.6 8.7 200 220 190 September 8.5 8.5 8.4 200 200 200 13 13 12 October 7.9 7.9 8.0 180 180 210 13 13 12 November 8.0 7.9 7.8 200 200 190 12 12 12 December 8.5 8.5 8.4 250 240 240 15 14 15 Average 8.1 8.1 8.1 202 202 201 11 10 10 P Alkalinity M Alkalinity Ammonia Nitrogen mf/l CaCo 3 mg/i CaCO mg/1 Upstream_ Downstream Discharge Upstream Downstream3 Discharge Upstrean Downstream Discharge January 0 0 0 174 177 173 .09 .08 .12 February 0 0 0 176 176 175 .11 .13 .14 March 0 0 0 168 169 170 .34 .28 .22 April 0 0 0 133 133 133 .01 .01 .01 May 6 6 5 157 157 158 .01 .01 .01 June 6 8 7 169 170 172 .04 .01 .01 July 5. 5 7 161 164 164 .04 .09 .05 August 5 6 6 159 163 162 .14 .08 .11 September 4 4 3 154 153 154 .04 .06 .03 October 6 6 5 159 161 160 .03 .02 .02 November 4 3 4 156 163 157 .01 .01 .01 December 0 0 0 180 188 185 .06 .08 .12 Average 3 3 3 162 165 164 .08 .07 .07

- = Sample lost

Table 1.2-1 (Continued)

Monticello Environmental Monitoring Nitrate Nitrogen Nitrite Nitrogen Total Dissolved Phosphorus mg/i N mg/i N mg/i P 1980 Upstream Downstream Discharge Upstream Downstream Discharge Upstream Downstream Discharge

.45 .48 .43 .008 .010 .010 .05 .03 .04 January February .54 .47 .43 .010 .007 .006 .02 .01 .05

.65 .60 .66 .010 .010 .013 .14 .08 .09 March

.10 .05 .03 .005 .006 .005 .02 .09 .03 April .06 May .17 .11 .11 .008 .007 .008 .02 .03

.11 .01 .01 .004 .005 .005 .06 .04 .05 June .13 July .01 .03 .03 .003 .003 - .003 .09 .09

.16 .09 .09 .007 .006 .007 .06 .06 .06 August .03 September .21 .19 .20 .004 .007 .008 .03 .03

.09 .08 .06 .007 .008 .007 .02 .02 .01 October

.10 .09 .10 .007 .005 .006 .01 .02 .02 November .02

.50 .42 .42 .010 .009 .013 .03 .02 December Average .26 .22 .21 .007 .007 .008 .05 .04 .05 Bio6hemical Oxygen Demand Chloride

.mg/1 mg/1 Cl Upstream Downstream Discharge Upstream Downstream Discharge January .9 1.0 1.3 10 11 11 February .9 1.0 1.0 5 5 5 March 3.0 2.1 2.7 8 7 8 April 4.4 4.0 4.4 5 6 5 May 3.1 3.0 2.8 6 6 7 June 4.0 2.9 3.4 8 7 .8 July 3.6 3.6 3.6 8 9 8 August 10 14 10 September 2.0 2.0 2.0 19 15 16 October 2.1 1.9 2.0 9 11 12 November 1.0 1.8 1.9 11 11 10 December 3.7 1.4 1.3 8 6 7 Average 2.4 2.1 2.2 8.9 9 8.9

- = Sample lost

~ m m - - m m m - m

MONTICELLO NUCLEAR GENERATING PLANT ENVIRONMENTAL MONITORING PROGRAM 1980 ANNUAL REPORT A

SUMMARY

OF THE 1980 MONTICELLO ELECTROFISHING SURVEY (2.1)

Prepared for Northern States Power Company Minneapolis, Minnesota by G. D. Heberling and J. W. Weinhold Environmental and Regulatory Activities Department Northern States Power Company 2.1-1

2.1 A

SUMMARY

OF THE 1980 MONTICELLO ELECTROFISHING SURVEY 2.

1.1 INTRODUCTION

Electrofishing studies were conducted in 1980 to assess relative abundance and seasonal distribution of fish in response to the Monticello Nuclear Generating Plant's (MNGP) thermal plume. Study areas (Figure 2.1-1) were sampled eight times between April 11 and October 24. Sector A encompasses an area of 21.6 ha and extends from the discharge canal outlet upstream 1.7 km to the top of Cedar Island. Sector B extends 1.5 km downstream from the dis charge- canal to the bottom of Boy Scout Rapids and includes an area of 27.1 ha. The thermal plume covered less than one-half the area of Sector B throughout most of the sam pling season.

Although total annual precipitation for central Minnesota was near the forty-year average, dry weather throughout much of the summer resulted in below average river discharge for most of the sampling season (see Section 1.1). River discharges near 2,000 cfs in July and August had a tendency to concentrate fish closer to the main river channel.

Percentage composition, catch per unit effort, condition factors, and length-weight relationships were determined for predominant species in each sector. Comparisons with 1968-1979 data were also made.

2.1.2 MATERIALS AND METHODS Equipment, sampling frequency, technique, and data computa tion were the same as the 1976-1979 studies. Sampling was conducted with pulsed direct-current electrofishing equip ment (Figure 2.1-2). A five-meter, flat bottom boat equipp ed with a railing, one anode, and ten cathodes was utilized.

2.1-3

I The power source was a 230-volt revolving field portable alternator. Current was maintained at five amperes at a rate of 60 pulses/second with a commercial transforming unit.

Paired shocking runs were conducted along opposing shore lines, as described in the 1975 report. Stunned fish were captured with one-inch mesh landing nets equipped with eight-foot insulated handles and placed in holding basins until completion of each sampling run. Elapsed shocking time was recorded for each run by a clock, which only tallied the seconds that the electrical field was energized.

Fish were measured to the nearest millimeter and weighed to the nearest 10 grams. Scales were collected from key scale areas from specimens over the entire length range for future age and rate of .growth analysis.

Species catch per unit effort (cpe) was computed for both sectors on each sample date. Cpe's were determined for number (fish/hr.) and weight (kg/hr.) by dividing the total number and weight of fish collected per area by the elapsed shocking time for that area.

Fish were grouped into twenty-millimeter intervals, and mean total lengths and weights were computed for each group.

Using these averages, condition factors were computed for the most abundant species with the formula:

K W x 105 L3 where K is the condition factor, W is weight in grams, and L is total length in millimeters.

I 2.1-43

Individual fish measurements were used to compute length weight relationships for the five dominant species. Data from both sectors were combined in this analysis. As with condition factors, all data were grouped and not segregated by sex. Metric measurements were transformed into loga rithms, and simple linear regressions were computed.

Length-weight formulas used to describe the data are pre sented in the following form:

log W log a + b log L, where W is the weight in grams, L is the total length in millimeters, a is the W axis intercept, and b is the slope of the length-weight regression line.

2.1.3 RESULTS A total of 3,154 fish was collected in the 1980 survey, 1,307 from Sector A and 1,847 from Sector B. Seventeen species from eight families were identified. Most of these species have been common components of previous electrofish ing surveys (Table 2.1-1).

Percentage contribution to the total catch by number was computed for each species from 1968 through 1980 (Table 2.1-2 and Figures 2.1-2 through 2.1-5). Monthly catch per unit effort statistics were computed by number (fish/hr.)

and weight (kg/hr.) for each species (Tables 2.1-3 and 2.1-4). Seasonal abundance patterns for the prominent species are presented in Figures 2.1-6 through 2.1-10.

Comparisons of annual cpe ,are presented as fish/hr. and kg/hr..in Tables 2.1-5 and 2.1-6.

Length frequency distributions are presented at twenty millimeter intervals in Figures 2.1-11 through 2.1-15.

Condition factors were determined using these twenty millimeter interval statistics for the five predominant 2.1-5

species (Table 2.1-7). A comparison of mean annual fish condition is presented in Table 2.1-8. Length-weight relationships were also computed for these species and are presented in Table 2.1-9.

2.1.4 DISCUSSION I

Stream conditions throughout much of the 1980 sampling season were low, which tended to concentrate fish toward the center of the river. This concentrating factor. may have contributed to high 1980 catch statistics.

Carp, shorthead redhorse, silver redhorse, white sucker, and smallmouth bass collectively comprised 96 percent of the total catch. Bowfin, green sunfish, and pumpkinseed were new additions to the species list since 1976.

Sector A had the following fish dominance ranking: short head redhorse, silver redhorse, carp, white sucker, and smallmouth bass. In Sector B the dominance ranking was shorthead redhorse, silver redhorse, carp, smallmouth bass, and white sucker.

Carp Carp constituted 11.4 percent of the total catch by number I

in Sector A and 8.7 percent in Sector B. Mean annual abundance for carp was 38.0 fish/hr. in Sector A and 49.4 fish/hr. in Sector B (Table 2.1-5). These averages are extremely close to the 1979 figures, which were the lowest I recorded during the five-year study period. Figure 2.1-6 illustrates that carp were attracted to the heated area of Sector B only during July. Catch rates for the two sectors were similar for the remainder of the year.

2.1-6

Mean condition factors for Sectors A and B fish were 1.25 and 1.36, respectively. Condition for this species was greater during 1976 through 1978. Competition from the increasingly abundant catostomid groups may-be stressing the carp population and contributing to their abundance and condition decline.

The length-weight relationship for carp was:

log W = -4.282 + 2.769 log L.

This formula compares well with other North American studies cited in Carlander (1969), -where similar regressions ranged from:

log W = -3.982 + 2.664 log L to log W - -6.226 + 3.477 log L.

Shorthead redhorse Shorthead redhorse composed 51.0 percent of the catch by number in Sector A and 50.8 percent in Sector B. This species was more abundant in 1980 than in previous studies (Table 2.1-5). Mean annual abundance for shorthead redhorse was 168.7 fish/hr. for Sector A and 293.2 fish/hr. for Sector B. The strong 1976 year class, which contributed to the high cpe's in 1977 through 1979, was the major component in the 1979 catch. Fish from this year class had a length range of 350 to 400 mm (Figure 2.1-12). This cohort exhib ited considerable growth since 1979, with anaverage length of 325 to 350 mm.

Shorthead redhorse were attracted to the thermally influenc ed area during April, May, and October (Figure 2.1-4).

Catch rates for both sectors were similar throughout the summer months.

2.1-7

I Average condition factors for shorthead redhorse were 1.11 for Sector A and 1.12 for Sector B. These means are higher than those computed for 1978 and 1979, but similar to 1976 and 1977 data.

The following length-weight relationship was developed for shorthead redhorse:

log W = -4.545 + 2.836 log L.

This regression compares well with those cited in Carlander (1969), which range from:

log W - -3.20 + 2.83 log L to log W = -4.042 + 3.021 log L.

Silver redhorse Silver redhorse constituted 26.2 percent of the catch by number in Sector A and 29.2 percent in Sector B. These figures are similar to 1978 and 1979 data, but are several times greater than previous studies (Table 2.1-2).

Fish were collected at the rate of 84.0 fish/hr. in Sector A and 164.5 fish/hr. in Sector B. Figure 2.1-8 reveals that catch rates in Sector B were substantially higher than those in Sector A during all months except May and late July.

Increased cpe's in 1978, 1979, and 1980 are attributed to the 1976 year class, which comprised a majority of the silver redhorse catch.

Condition factors for Sector A and Sector B fish compared well. Mean condition factors for Sector A and B fish were 1.14 and 1.15, respectively. These means are higher than those computed in 1978 and 1979.

I 2.1-8U

Silver redhorse had a length-weight relationship:

log W = -4.634 + 2.878 log L.

This regression closely approximates the formula reported in Carlander (1969), which was:

log W = -4.263 + 3.124 log L.

White sucker White sucker comprised 4.8 percent of the catch by number in Sector A and 2.9 percent in Sector B (Table 2.1-2). Catch per unit effort statistics (Table 2.1-5) have been quite stable since 1978. White sucker was collected at the rate of 16.1 fish/hr. in Sector A and 15.5 fish per hour in Sector B. The 1976 year class comprised a majority of the white sucker catch. Figure 2.1-9 indicates that white sucker had a preference for warm water in April and May, but avoided this area in August, September, and October.

Mean condition factors for Sector A and Sector B were'1.15 and 1.18, respectively. These indicies are similar to those computed since 1977. They do, however, show some increase over 1978 data but not nearly as high as 1976. As with other catostomid members, white sucker had excellent repro ductive success in 1976 and subsequent, high survival rates, which have imposed slight limitations on the popula tion through competition for food and habitat.

White sucker had a length-weight relationship of:

log W = -5.012 + 3.034 log L.

2.1-9

I This regression compares well with the range reported in I Carlander (1969) of:

log W = -2.822 + 2.2303 log L to log W = -5.395 + 3.223 log L.

Smallmouth bass Smallmouth bass composed 1.6 percent of the total catch by number in Sector A and 4.8 percent in Sector B (Table 2.1-2). Annual cpe data (Table 2.1-5) indicate a substan tial abundance decrease in the upstream sector. Fish were collected at a rate of 5.3 fish/hr. in Sector A and 29.4 fish/hr. in Sector B. Natural attrition and increased avoidance to the electrofishing equipment (due to age) by the strong 1976 year class fish are believed to be respon sible for the abundance decline of this species. Catch rates for this species now approximate those of 1976, prior to recruitment of the dominant 1976 year class.

Seasonal abundance, illustrated in Figure 2.1-10, reveals a preference for the warm water of Sector B in May, June, September,and October. During the remainder of the study similar catch rates were obtained in both sectors.

The mean condition factor for smallmouth bass was 1.48 for Sector A and 1.43 for Sector B. Average condition of these fish was higher than those of 1978 .and 1979. However, these fish were leaner for a given length than those col lected during 1976 and 1977.'

The length-weight relationship for smallmouth bass was:

log W = -5.005 + 3.069 log L.

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This formula compares well with the range of regressions reported in Carlander (1977):

log W = -4.177 + 2.701 log L to log W = -5.841 + 3.372 log L.

Walleye As in most years, walleye comprised a very small portion of the 1980 catch. Their percentage contribution by number was 0.6 percent in Sector A and 0.3 percent in Sector B.

Catch per unit effort for walleye was 2.3 fish/hr. in Sector A and 2.1 fish/hr. in Sector B (Table 2.1-5). This species' preference for deeper water, which is not efficiently electrofished, contributes to the paucity of walleye in this and previous studies. Insufficient numbers of walleye were collected in 1980 to warrant computation of condition factors or length-weight regressions.

Miscellaneous Species Miscellaneous species comprised 4.4 Percent of the total catch in Sector A and 3.3 percent in Sector B (Table 2.1-2).

Their mean annual catch rate was 14.8 fish/hr. in Sector A and 23.7 .fish/hr. in Sector.B (Table 2.1-5). The numerical dominance ranking for the miscellaneous catch in Sector A was: northern Pike, northern hogsucker, black crappie, rock bass, greater redhorse, burbot, and black bullhead. Sector B had the following dominance ranking: northern hogsucker, rock bass, black bullhead, black crappie, northern pike, greater redhorse, largemouth bass, bowfin, pumpkinseed, and green sunfish. As in earlier studies, the warm water of Sector B attracted uncommon species, especially centrachids and ictalurids.

2.1-11

I 2.1.5

SUMMARY

1. The 1980 electrofishing study was conducted with a pulsed DC unit at four-week intervals from April through October.

2. A total of 3,154 fish were collected from 17 species and 8 families.

3. Sector A had the following dominance ranking: shorthead redhorse, silver redhorse, carp, white sucker, and smallmouth bass. In Sector B the dominance ranking was:

shorthead redhorse, silver redhorse, carp, smallmouth bass, and white sucker.

4. Catch per unit effort was high-similar to 1978 and 1979.

Abundance for all major species, except shorthead redhorse, has declined since 1978. These reductions are primarily a result of the natural attrition of the exceptionally strong 1976 year classes.

5. Catch rates (cpe) were generally higher for the dominant species in Sector B. This condition also occurred in 1976 through 1979, suggesting a preference for warmer water by most species. This would be expected, because throughout most of the year, ambient temperatures are below the optimum or desired temperature range of most area species.

6. Condition factors were 'computed for the five dominant species. These indices indicate that:

a. In general, 1980 fish in both sectors have the same weight for a given length.

I 2.1-123

b. All species showed improved physical condition over 1979.

7. Length-weight relationships computed for the five dominant species compared well with regressions reported by Carlander (1969 and 1977).

2.1-13

I 2.1.6 LITERATURE CITED Carlander, K.D. 1969. Handbook of Freshwater Fishery Biology, Volume I, 752 pp. The Iowa State University

'Press, Ames, Iowa.

Carlander, K.D. 1977. Handbook of Freshwater Fishery Biology, Volume II, 421 pp. The Iowa State University Press, Ames, Iowa.

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Figure 2.1-1. 1980 Monticello Electrofishing Areas.

CEI LEGEND Sector A Sector B ISLAND PLANT SITE COOLING TOWERS DISCHARGE CANAL 0 0.5 1.0 I I OXBOW Scale - Kilometers ISLAND BOAT LANDING--IJ STORAGE BUILDING PLUME MONTISIPPI PARK 2.1-15

Figure 2.1-2 ELECTROFISHING BOAT ( 5m.)

GENERATOR 01' UNIT CATHODE ANODE

- m m - m

- - - ~ - - -

Figure 2.1-3 OVERALL FISH CATCH SHORTHEAD REDHORSE 1602 50.9%

S H

H

-J SMALLMOUTH BASS

/ 109 3.5%

MISCELLANEOUS 133 WHITE SUCKER 116 3.7%

Figure 2.1-4 SECTOR 1 FISH CATCH SHORTHEAD REDHORSE 665 51.0%

Ho 00 SMALLMOUTH BASS a-21 1.6%

MISCELLANEOUS 5.0%

WHITE SUCKER 63 4.8%

m ~ -mq m ~ d m " m MU N m mn

mf~mm ltm~fw - m m Figure 2.1-5 SECTOR 2 FISH CATCH SHORTHEAD REDHORSE 937 50.8%

N)

H H

'.0 SMALLMOUTH BASS 88 4.8%

MISCELLANEOUS

' 68 3.6%

WHITE SUCKER 53 2.9%

1980 MONTICELLO ELECTROFISHING CPE (fish/hr) CARP 100 t%3 04 H

0

'10 APR/11 MAY/8 JUNE/5 JULY/2 JULY/31 AUG/28 SEPT/25 OCT/23 DATE ma ma -m A m e s we am

-a -0 4w 4 m w M we 1980 MONTICELLO ELECTROFISHING CPE (fish/hr) SHORTHEAD REDHORSE 700 Figure 2.1-7 600- Legend A SECTOR 1 X SECTOR_2 500-0 H 400 ti H

F- 300.

200 100 o

APR/11 MAY/8 JUNE/5 JULY/2 JULY/31 AUG/28 SEPT/25 OCT/23 DATE

1980 MONTICELLO ELECTROFISHING CPE (fish/hr) SILVER REDHORSE S

H I'

I..,

t,3 APR/11 MAY/8 JUNE/5 JULY/2 JULY/31 AUG/28 SEPT/25 OCT/23 DATE m-2 m 4m on 4" 8ma mA w os omn -ws

M M 4W 6N" 0 04 I'N M,0mM W - M -I 1980 MONTICELLO ELECTROFISHING CPE (fish/hr) WHITE SUCKER I'3 I-I t'3.

0 -

APR/11 MAY/8 JUNE/5 JULY/2 JULY/31 AUG/28 SEPT/25 OCT/23 DATE

1980 MONTICELLO ELECTROFISHING CPE (fish/hr)

SMALLMOUTH BASS 140 1 Figure 2.1-10 120 Legend 2

L SECTOR 1

/

100- X SECTOR 2 /

/

/

80

/

I-1~ /

60- /

7<

/

40- /

/

20-A -........ . .

L-19A iA -  :

UT 9 APR/11 MAY/8 JUNE/5 JULY/2 JULY/31 AUG/28 SEPT/25 OCT/23 DATE im ON -

OW 4 - ml --- o m- W m

• t" -W 4M W ON , M M- M M 0 1980 MONTICELLO ELECTROFISHING LENGTH FREQUENCY CARP 35 Figure 2.1-11 o

so1 Legend E SECTOR1 WI SECTOR2 25 C2 U20 nE H

U15 cyI 400 450 mm LENGTH

1980 MONTICELLO ELECTROFISHING LENGTH FREQUENCY SHORTHEAD REDHORSE 250 -1 Figure 2.1-12 co Legend EZi SECTOR 1 2001 - SECTOR 2 0t

>- 150 U

t'3 z i-a t%) 0) 0~t 0

-4 F100

-4 Go

'0 50 -4 0-1\2 -

I cv C~2

-q C'2 -4

~

I 14 I

I co

= K - 14 V n ,

NoF I l I

100 I - 150 G&W= 200 250 Wom 300 I 350 400 450 500 550 mm LENGTH

-m m -- 4w 4m m m

m m ca /w a - - on m o Aft 1980 MONTICELLO ELECTROFISHING LENGTH FREQUENCY SILVER REDHORSE 120 -F Figure 2.1-13 0

100 Legend EZJ SECTOR 1

- SECTOR 2 80-C,,

C,-

N) is co 0

H z N)

D 60-40 7 CQ Li 20 cc p4

-4 c'l 0

-4 t co 0- 4C'.2 cc VI 200 250 300 350 400 450 500 550 600 mm LENGTH

1980 MONTICELLO ELECTROFISHING LENGTH FREQUENCY WHITE SUCKER 14-Figure 2.1-14

• 12 Legend Zi SECTOR 1 -I

-4

- SECTOR 2 10-C) 8 z

co I

S6-hfo to "4.

4 2

I LI-0- i i r~ -

100 150 200 250 300 350 400 450 500 mm LENGTH amw - m w /a m

1980 MONTICELLO ELECTROFISHING LENGTH FREQUENCY SMALLMOUTH BASS 12 -I.

Figure 2.1-15 o0 a 24 Legend 10 EZI SECTOR 1 M. SECTOR 2 8

N, 0

H UD N,

'~0 zr 6-Lz) ko Lo ko 4

I 2-U 50 100

-4 HQ 150 20 0 250 300 a- - - - - -

350 F

400 450 mm LENGTH I -J

Table 2.1-1. Monticello Electrofishing Species List.

Species 1976 1977 .1978 1979 1980 Bowfin x (amia calva)

Cisco x (Coregonus artedi)

Northern pike x x x x x (Esox lucius)

Muskellunge x (Esox masquinongy)

Shorthead redhorse x x x x x (Moxostoma macrolepidotum)

Silver redhorse x x x x x (Moxostoma anisurum)

Greater redhorse x x x (Moxostoma valenciennesi)

White sucker x x x x x (Catostomus commersoni)

Bigmouth buffalo x x (Ictiobus cyprinellus)

Northern hogsucker x x x x x (Hypentelium nigricans)

Carp x x x x x (Cyprinus carpio)

Black bullhead x x x x x (Ictalurus melas)

Yellow bullhead x x x x (Ictalurus natalis)

Brown bullhead x (Ictalurus nebulosus)

Burbot x x (Lota lota)

Smallmouth bass x x x x x (Micropterus dolomieui)

Largemouth bass x x x (Micropterus salmoides)

Rock bass x x x x x (Ambloplites rupestris)

Bluegill x x x (Lepomis macrochirus)

Black crappie x x x x x (Pomoxis nigromaculatus)

White crappie x (Pomoxis annularis)

Pumpkinseed x (Lepomis gibbosus)

Green sunfish x (Lepomis cyanellus)

Walleye x x x x x (Stizostedium vitreum)

Yellow perch x (Perca flavescens) 2.1-31

Table 2.1-2. 1968-1980 Monticello Electrofishing Percent of Total Catch by Number.

Shorthead Silver White Smallmouth Carp redhorse redhorse sucker bass Walleye Misc Sector A 1968 50.7 34.5 4.4 2.7 1.5 4.8 1.4 1969 29.4 48.6 7.4 4.5 1.8 2.0 6.3 1971 25.3 36.9 9.1 13.1 7.6 7.1 0.9 1972 45.1 26.1 9.1 4.1 7.0 1.1 7.5 1973 39.9 34.8 13.0 4.9 2.0 0.7 4.7 1974 44.3 20.3 16.7 9.2 1.5 0.1 7.9 1975 53.5 27.0 9.3 3.7 0.9 0.5 5.1 1976 41.0 36.4 12.3 3.5 3.4 1.4 2.0 1977 19.6 40.3 12.7 3.4 20.4 0.8 2.8 1978 15.4 32.2 26.4 5.0 15.4 0.5 5.1 t.3 1979 15.2 43.4 29.5 5.5 4.3 0.2 2.1 1980 11.4 51.0 26.2 4.8 1.6 0.6 4.4 H

(,J Sector B 1968 34.3 58.9 2.9 3.0 0.4 0.3 0.3 1969 17.3 65.1 9.6 4.8 2.0 1.2 0.4 1971 27.2 35.9 7.8 6.3 12.6 6.8 3.4 1972 38.4 33.4 8.2 3.3 5.9 2.0 8.8 1973 31.2 41.3 11.5 4.0 2.9 1.2 7.9 1974 47.0 22.6 15.2 6.4 0.9 0.6 6.4 1975 40.8 37.6 10.8 1.9 3.8 1.3 3.8 1976 32.4 40.1 12.6 1.6 9.3 1.5 2.5 1977 21.2 33.1 15.3 2.1 22.8 1.0 4.6 1978 11.3 30.3 31.3 3.8 16.5 0.6 6.2 1979 9.4 49.7 26.9 4.0 5.3 0.3 4.5 1980 8.7 50.8 29.2 2.9 4.8 0.3 3.3 m - - - \~ I (~ ~ -

Table 2.1-3 1980 Monticello Electrofishing Catch per Unit Effort by Number (fish/hr).

Shorthead Silver White Smallmouth Black Carp redhorse redhorse sucker bass Walleye Misc Total crappie Sector A 4/11 51.7 63.7 41.8 2.0 0 0 8.0 13.9 181.1 5/8 34.5 122.7 124.6 11.5 5.8 0 0 7.6 306.7 6/5 19.5. 195.5 161.7 19.5 5.3 0 0 9.0 410.5 7/2 29.3 227.3 82.5 14.7 5.5 1.8 7.3 23.7 392.1 7/31 48.1 138.3 100.2 18.0 4.0 2.0 4.0 8.0 322.6 8/25 35.0 192.4 67.5 25.0 7.5 10.0 5.0 12.5 354.9 t.J 9/25 49.6 259.4 81.2 13.5 4.5 4.5 0 15.8 428.5 H

(-Ii 10/24 36.5 150.1 12.2 24.3 10.1 0 0 4.2 237.4 LA)

Mean 38.0 168.7 84.0 16.1 5.3 2.3 3.0 11.8 .329.2 Sector B 4/11 60.4 430.0 190.6 25.6 0 S 0 0 0 706.6 5/8 20.7 203.3 101.7 31.1 20.8 0 0 6.2 383.8 6/5 31.6 166.9 223.3 13.5 13.5 2.3 9.0 4.5 465.3 7/2 91.2 283.2 136.8 14.4 7.2 0 0 9.6 542.4 7/31 78.0 231.2 94.1 18.8 5.4 0 0 18.8 446.3 8/25 20.4 179.1 179.1 6.8 4.5 0 0 15.9 405.8 9/25 58.0 176.7 129.2 10 .5 60.7 0 2.6 55.4 493.1 10/24 35.2 674.8 261.1 2.9 123.2 14.7 0 67.5 1179.4 Mean 49.4 293.2 164.5 15.5 29.4 -2.1 1.5 22.2 577.8

Table 2.1-4 1980 Monticello Electrofishing Catch per Unit Effort by Weight (Kg/hr).

Shorthead Silver White Smallmouth Black Carp redhorse redhorse sucker bass Walleye crappie Misc Total Sector A 4/11 73.6 43.1 22.2 0.8 0 0 0.7 7.4 147.8 5/8 49.1 76.8 106.2 7.8 1.4 0 0 2.8 244.2 6/5 30.5 115.7 104.8 11.4 0.9 0 0 3.7 267.0 7/2 45.0 139.3 54.5 8.0 1.6 0.5 1.0 6.4 256.3 7/31 66.0 97.3 49.3 11.4 1.4. 0.1 1.3 3.8 230.7 8/25 52.8 142.0 50.9 14.9 1.1 2.1 1.0 6.5 271.3 9/25 70.5 194.7 75.5 8..1 1.6 0.4 0 1.6 352.5 10/24 68.7 109.3 6.7 11.6 6.3 0 0 3.3 205.9 t.3 H

Mean 57.0 114.8 58.8 9.3 1.8 0.4 0.5 4.4 247.0 Sector B 4/11 80.5 252.5 58.3 15.1 0 0 0 0 406.4 5/8 23.9 124.4 53.8 18.2 6.5 0 0 9.1 235.9 6/5 37.8 101.7 101.0 9.2 3.8 0.5 1.7 0 255.7 7/2 66.1 164.2 70.8 8.5 2.4 0 0 0 312.0 7/31 64.7 152.6 41.6 10.9 0.1 0. 0 2.6 272.5 8/25 18.6 137.4 96.2 4.1 1.7 0 4.6 262.7 9/25 66.8 122.3 83.6 6.2 10.6 0 0.3 12.0 301.8 10/24 34.1 520 .3 136.4 1.5 52.0 6.3 0 19.0 769.6 Mean 49.1 196.9 80.2 9.2 9.6 0.9 0.3 5.9 352.1 O

~ ~ ONo

~ aso,4 u 40 an " mme ,=a

Table 2.1-5 1976-1980 Monticello Electrofishing Catch per Unit Effort by Number (fish/hr).

Shorthead Silver White Smallmouth Carp redhorse redhorse sucker bass Walleye Misc Total Sector A 1976 67.4 59..9 20.3 5.8 5.7 2.3 3.2 164.6 1977 61.3 126.1 39.7 10.5 63.7 2.4 8.9 312.6 1978 51.6 108.1 88.5 16.6 51.7 1.7 17.2 335.5 1979 49.3 140.9 95.8 17.9 13.9 0.5 6.7 325.0 1980 38.0 168.7 84.0 16.1 5.3 2.3 14.8 329.2 1

Sector B 1976 77.0 95.2. 29.9 3.8 22.2 3.5 6.0 231.6 1977 79.3 123.8 57.2 7.8 85.2 3.8 17.3 374.4 1978 67.7 181.7 187.6 23.0 99.0 3.3 37.3 599.7 1979 43.0 226.8 122.6 18.3 24.3 1.3 20.3 456.6 1980 49.4 293..2 164.5 15.5 29.4 2.1 23.7 577.8 5 yr. x 58.4 152.4 89.0 13.5 40.0 2.3 15.5 370.7 For both sectors combined.

Table 2.1-6. 1976-1980 Monticello Electrofishing Catch per Unit Effort by Weight (kg/hr).

Shorthead Silver White Smallmouth Carp redhorse redhorse sucker bass Walleye Misc Total Sector A 1976 97.5 46.1 23.3 4.2 1.6 0.6 1.7 185.0 1977 103.6. 109.4 64.4 5.7 13.0 1.1 4.6 301.8 1978 74.8 70.2 47.2 6.0 9.2 0.3 3.9 211.6 1979 66.3 91.8 57.1. 8.1 3.2 0.4 5.6 232.5 1980 57.0 114.8 58.8 9..3 1.8 0.4 4.9 247.0 Sector B S

H 75.2 89.0 34.4 2.9. 4.5 1.4 1.4 209.3 1976 Lii 0~t 1977 99.7 85.7 61.9 11.7 15.6 2.1 2.5 279.2 1978 86.0. 106.2 60.4 7.0 17.4 2.6 6.0 285.5 1979 53.1 145.5 69.8 .7.9 6.0 0.6 7.6 290.5 1980 49.1 196.9 80.2 9.2 9.6 0.9 6.2 352.1 5 yr. x 76.2 105.6 55.8 7.2 8.2 1.0 4.4 258.4 For both sectors combined.

- -- -- - - a mI

m m a m m-w as Table 2.1-7 1980 Condition Factor for Sector A and B.

Shorthead Silver White Smallmouth Carp redhorse redhorse sucker bass Length A B A B A B A B A B 100 1.32 1.19 1.71 1.40 120 .1.24 1.28 1.08 1.22 1.39 140 1.16 1.23 1.09 1.41 1.37 160 1.21 180 1.51 1.31 1.23 200 1.91 1.00 1.28 1.25 220 1.71 1.16 1.20 1.29 1.49 240 1.19 1.18 1.18 1.25 1.48 1.33 260 1.46 1.19 1.27 1.16 1.23 1.28 1.48 280 1.45 1.07 1.17 1.17 1.19 1.32 1.57 300 1.40 1.15 1.20 1.16 1.17 1.17 1.21 1.35 1.45 320 1.37 1.09 1.06 1.14 1.12 1.19 1.32 1.79 1.48

!0 340 1.29 1.08 1.07 1.11' 1.11 1.21 1.19 1.55 1.60 360 1.27 1.10 1.09 1.11 1.08 1.22 1.24 1.58 380 1.18 1.19 1.08 1.09 1.10 1.07 1.15 1.26 1.53 1.61 400 1.30 1.31 1.07 1.08 1.14 1.08 1.14 1.17 1.66 420 1.26 1.27 1.05 1.06 1.14 1.20 1.13 0.97 440 1.29 1.25 1.03 1.02 1.19 1.17 1.13 460 1.30 1.23 1.02 1.02 1.14 1.15 480 1.27 1.24 1.00 1.01 1.12 1.14 1.04 500 1.27 1.25 0.95 1.06 1.14 1.09 520 1.23 1.22 0.95 1.08. 1.05 540 1.16 1.30 1.11 1.06 560 1.31 1.36 1.05 1.13 580 1.23 1.33 1.17 1.06 600 1.19 620 640 1.20 660 Mean 1.25 1.36 1.11 1.12 1.14 1.15 1.15 1.18 1.48 1.43

-J

Table 2.1-8 Annual Average Condition Factor for 1976-1980 Monticello Electrofishing.

Shorthead Silver White Smallmouth Carp redhorse redhorse sucker bass A. B A B A B A B A B 1976 1.31 1.37 1.10 1.04 1.18 1.18 1.30 1.15 1.47 1.59 1977 1.35 1.35 1.14 1.15 1.19 1.20 1.17 1.14 1.55 1.43 V

w 1978 1.35 1.33 1.00 0.99 1.10 1.09 1.14 1.08 1.31 1.31

• 0 1979 1.27 1.28 0.99 0.97 1.04 1.05 1.12 1.19 1.39 1.29 1980 1.25 1.36 1.11 1.12 1.14 1.15 1.15 1.18 1.48 1.43

- - -~ m ~ -I

- = M as ana -M im as So ,* on v M M M Na Table 2.1-9 1980 Length-Weight Relationships for Fish Collected via Monticello Electrofishing (Length in Millimeters and Weight in Grams).

Species Log Formula Arithmetic Formula Length Range (mm)

Carp log W = -4.282 + 2.769 log L W = (5.22 x 10-5 )L2.769 180 - 660 Shorthead redhorse log W = -4.545 + 2.836 log L W = (2.85 xl10 -5 )L 2.836 120 - 520 Silver redhorse log W = -4.634 + 2.878 log L W = (2.32 x 10 -5 )L2.878 220 - 580 x1 6 3.034 White sucker log W = -5.012 + 3.034 log L W = (9.73 120 - 480 Smallmouth bass - 6 3 069 log W = -5.005 + 3.069 log L W = (9.88 x 10 )L '. 80 - 420 I

MONTICELLO NUCLEAR GENERATING PLANT ENVIRONMENTAL MONITORING PROGRAM 1980 ANNUAL REPORT SEINING STUDY (2.2)

Prepared for Northern States Power Company Minneapolis, Minnesota by J. W. Weinhold Environmental and Regulatory Activities Department Northern States Power Company 2.2-1

2.2 1980 MONTICELLO SEINING STUDY 2.

2.1 INTRODUCTION

During 1980, seining studies were conducted on the Missis sippi River near the Monticello Nuclear Generating Plant (MNGP). Locations within a kilometer, upstream and down stream from the MNGP site, were sampled to ascertain small fish populations. The objectives of this study were to determine relative abundance and species composition of the small fish community, with possible.observations on the effect of the MNGP's thermal discharge.

Seining was conducted once every two weeks between May 16 and September 22, 1980. The study area included 1.6 km of river extending 0.8 km upstream and 0.8 km downstream from the MNGP discharge structure. Two upstream stations and two downstream stations were utilized (Figure 2.2-1).

Station M-1 was located in a small channel between Beaver and Cedar Island. The bottom structure consisted of a sand-gravel mixture. Current was approximately one meter per second, with an average depth of 0.75 meter. No aquatic vegetation was present at this location.

Station M-2 was located in a small channel between two islands approximately 0.4 km upstream of Station M-1.

Current of 0.75 meter per second over a sand-gravel bottom' and a depth of one meter depict the characteristics of this seining station.

Station M-3 was located within the plant's thermal plume 0.3 km downstream from the MNGP discharge structure. This site had a current velocity of 0.75 meter per second, a gravel substrate, and an average depth of one meter.

2.2-3

I Station M-4, which was also within the thermal plume, was located 0.8 km downstream from the MNGP discharge structure.

Gravel bottom, current velocity of 0.4 meter per second, and an average depth of one meter depict the characteristics of this seining station.

2.2.2 MATERIALS AND METHODS A 15-foot seine with 1/8" mesh was used for sampling. Hauls were directed downstream with the current. The distance of each seining haul was determined and recorded. Captured fish were immediately placed in a water-filled basin, identified, tabulated, and released. Voucher specimens were preserved in a 10 percent formalin solution. Freshwater Fishes of Canada (Scott and Crossman 1973), Northern Fishes (Eddy and Underhill 1976), The Fishes of Missouri (Pflieger 1975), and Illustrated Key to the Minnows of Wisconsin (Becker and Johnson 1970) were used to identify specimens.

Computation of the area sampled was accomplished by multi plying the length of the haul by the width of the seine.

Species abundance indices, or catch per effort (cpe), were computed by expanding the number of fish captured per area seined to the number of fish that would have been captured in a hectare. Abundance indices were utilized to calculate percentage composition of each species in the total catch.

2.2.3 RESULTS A total of 4,246 fish was collected during the 1980 study.

Of these, 25 species were identified (Table 2.2-1). Mimic shiner, carp, blacknose dace, rockbass, brook stickleback, and logperch were collected during the 1980 study, but were not found in 1979. Creek chubriver shiner, brassy minnow, golden shiner, northern redbelly dace, black bullhead, brook silverside, white crappie, walleye, and yellow perch were collected in previous years but not in 1980.

2.2-4

Twenty-two species were found in each sector. Mimic shiner, blacknose dace, black bullhead, and trout perch were found exclusively in the upstream area during 1980. Common shiner, bluegill, rock bass, and brook stickleback were found only in the downstream sector.

Species abundance indicies (fish/ha) are presented for both sectors in Table 2.2-2. Species percentage contribu tions to the total catch for both sectors are presented in Table 2.2-3. Species percentage contributions to total catch since 1970 are listed. in Table 2.2-4. Seasonal abundance of individual species, as actual fish captured, for each seining station is presented in Tables 2.2-5 through 2.2-8. Abundance indicies for young-of-the-year of selected species (smallmouth bass, white sucker, and the Moxostoma species) are presented in ,Table 2.2-9. These indicies are reviewed annually for an indication of repro ductive. success for these dominant "large fish" species. A species list with both common and Latin: names of fish discussed in this text is compiled in Table 2.2-10.

2.2.4 DISCUSSION A total of 35 species has been identified during the seven years that seining studies were conducted (Table 2.2-4).

Brook stickleback was the only new species added to this species list in 1980. The brook stickleback's preferred habitat is small, cool-water streams. Its presence in the effluent section of the study area (Table 2.2-2) is believed to arise from accidental introductions by the Monticello Environmental Protection Agency (EPA) field station. The EPA outfall structure is located approximately 400 meters downstream from the MNGP discharge. Canals used by the EPA for toxicology studies were stocked with fathead minnows.

Brook sticklebacks are commonly found in stocks of fathead minnows supplied to the EPA field station by local bait distributors, and it is quite possible that some of these individuals have escaped to the Mississippi River.

2.2-5

I Creek chub, brassy minnnow, river shiner, golden shiner, northern redbelly dace, brook silverside, white crappie, yellow perch, and walleye are incidental species found in previous studies and not in 1980.

Mature northern hogsuckers have been observed since 1976 in Monticello electrofishing surveys (see Section 2.1).

This species first appeared as young-of-the-year in 1979 seining surveys. Its abundance also increased in 1980 (Table 2.2-4). Seining data and visual observation while electrofishing indicate an excellent 1980 year class of this species. Northern hogsuckers generally prefer clear and productive river systems for their habitats.' Its appearance and reproductive success is, therefore, believed to arise from substantial improvement in water clarity and quality, beginning with the 1975 to 1977 drought.

Species which dominated the 1980 upstream sector collections were: white sucker, sand shiner, Johnny darter, spotfin shiner, bigmouth shiner, and Moxostoma spp. (unidentified juvenile silver and shorthead redhorse). Major components g in the downstream sector were: white sucker, spotfin shiner, smallmouth bass, spottail shiner, and bluntnose minnow (Table 2.2-3). A preference for warm water was demonstrated by smallmouth bass, spottail shiner, bluntnose minnow, carp, largemouth bass, black crappie, and northern hogsucker, and is reflected by their greater abundance in Sector B (Table 2.2-2).

2.2-6

The species dominance ranking for 1976-1980 studies is as follows:

1976 1977 Bigmouth & sand shiner Bigmouth and sand shiner Bluntnose minnow Bluntnose minnow Spotfin shiner Spotfin shiner Moxostoma spp. White sucker White sucker Johnny darter 1978 1979 Bluntnose minnow Bigmouth and sand shiner Bigmouth and sand shinner Spotfin shiner Spotfin shiner Bluntnose minnow White sucker Moxostoma spp.

Johnny darter White sucker 1980 White sucker Spotfin shiner Johnny darter Sand shiner Moxostoma spp.

The taxon Moxostoma spp. was utilized in this text due to the difficulty of field separating early juvenile stages of silver and shorthead redhorse.

Bluntnose minnow, sand shiner, and bigmouth shiner were not as abundant in 1980 as they have been in previous studies.

Conversely, white sucker, smallmouth bass, Johnny darter, logperch, and northern hogsucker had increased abundance in 1980 (Table 2.2-4).

2.2-7

Seasonal abundance (Tables 2.2-5 through 2.2-8) of juvenile white sucker and smallmouth bass indicates that spawning occurred in late May through natural attrition, increased sampling gear avoidance, and shifts in preferred habitat; the juvenile abundance of these species decreased after midsummer.

Collections of spotfin shiner, sand shiner, and bluntnose minnow increased after midsummer. The seasonal abundance pulse for these species is attributable to their young-of the-year attaining a recruitable size for the seining gear.

Table 2.2-9 illustrates the average abundance (fish/ha) of smallmouth bass, white suckerland Moxostoma spp. (silver and shorthead redhorse) since 1973. This table reveals that young-of-the-year abundance for 1980 year classes of small mouth bass and white sucker were the highest recorded over the seven-year period. Although Moxostoma spp. did not reach record abundance, it joined smallmouth bass and white sucker by showing tremendous increases over 1978 and 1979 averages.

2.2.5

SUMMARY

1) A total of 4,246 fish was collected by seining in the Mississippi River near MNGP in 1980. Twenty-five species were identified in 1980, 35 species have been identified during the seven years studied. The one new species identified in 1980 was the brook stickleback.

2) Dominant species occurring in 1980 were; white sucker, spotfin shiner, Johnny darter, sand shiner, and Moxos toma spp.

I 2.2-83

3) Smallmouth bass, spottail shiner, bluntnose minnow, carp, largemouth bass, black crappie, and northern hog sucker showed a marked preferrence for the MNGP heated effluent.

4) Decreased abundance of bluntnose minnow, bigmouth shiner, sand shiner, and spotfin shiner was observed in 1980.

5) Increased abundance for young-of-the-year smallmouth bass, white sucker, and Moxostoma spp. indicates a strong 1980 year class for these major large fish species.

2.2-9

I 2.2.6 ACKNOWLEDGEMENTS A special thanks is given to Dr. J. C. Underhill and his University of Minnesota staff for verifying the identifica tion of certain specimens.

2.2.7 LITERATURE CITED Becker, G.C.and T,RJohnson. 1970. Illustrated Key to the Minnows of Wisconsin. Wisc.State University. Stevens Point, Biol.Dept. 45 pp.

Eddy, S.and J.C.Underhill. 1976. Northern Fishes. Univ of Minnesota Press, Mpls. 414 pp.

Pflieger, W L. 1975. The Fishes of Missouri. Missouri Dept.

of Cons. Publ. 343 pp.

Scott, W. B. and E. J. Crossman.. 1973. Freshwater Fishes of Canada. Bull. 184. Fisheries Research Board of Canada, Ottawa. 966 pp.

I I

I I

I 2.2-10U

1-2 PLANT SITE COOLING TOWERS<

DI C,

M-3 0 0.5 OXBOW Scale-Kilometers ISLAND BOAT LANDING STORAGE/>

BUILDING THERMAL PLUME MONTISIPPI PARK Figure 2.2-1. 1980 Monticello Seining Station Locations.

2.2-11

Table 2.2-1 1980 Monticello Seining Study - Species Lists for 1970, 1973, 1976, 1977, 1978, 1979, and 1980.

Species 1970 1973 1976 1977 1978 1979 1980 Hornyhead chub x x x x x. X x Creek chub x x x Fathead minnow x x x x x Bluntnose minnow x x x x x x Brassy minnow x Spotfin shiner x x x x x x Bigmouth shiner x x x x x x Sand shiner x x x x x x River shiner x x Spottail shiner x x x x x Common shiner x x x x x x Golden shiner x Mimic shiner x x Carp x x x Longnose dace x x x x x x Blacknose dace x x x x x Northern redbelly dace x Silver redhorse x x x x x x Shorthead redhorse x x x x x x White sucker x x x x x x Northern hogsucker x x Black bullhead x Trout perch x x x x x Brook stickleback x Brook silverside x x Smallmouth bass x x x x x x x Largemouth bass x x x Black crappie x x x x White crappie x Rock bass x x x Bluegill x x x x x Logperch x x x x x Johnny darter x x x x x x x Walleye x Yellow perch x x X - Denotes presence 2.2-13

Table 2.2-2 1980 Monticello Seining Study - Fish per Hectare for Sampling Stations Upstream and Downstream of the Monticello Plant Discharge.

Upstream Downstream Over all 1- 2 Ave 3 4 Avg Avg Hornyhead chub 82 120 101 146 18 82 92 Fathead minnow 22 94 58 15 9 12 35 Bluntnose minnow 560 436 498 584 145 364 431 Spotfin shiner 1396 769 1082 1693 300 996 1040 Sand shiner 1515 1282 1398 102 64 83 741 Bigmouth shiner 888 1113 1030 73 0 36 523 Spottail shiner 45 0 22 620 155 388 205 Common shiner 0 0 0 22 0 11 6 Mimic shiner 0 26 13 0 0 0 6 Carp 0 9 4 102 9 56 30 Longnose dace 866 214 540 88 36 62 301 Blacknose dace 0 26 13 0 0 0 6 Shorthead redhorse 119 137 128 117 64 90 109 Silver redhorse 157 154 156 36 9 22 89 White sucker 2724 3940 3332 1861 2045 1953 2642 Northern hogsucker 82 60 71 533 73 303 187 Black bullhead 0 9 4 0 0 0 2 Trout perch 7 0 4 0 0 0 2 Smallmouth bass 231 179 205 599 1200 900 552 Largemouth bass 37 0 18 15 100 58 38 Black crappie 0 9 4 7 36 22 13 Bluegill 0 0 0 80 0 40 20 Rock bass 0 0 0 0 9 4 2 Johnny darter 1522 1222 1372 109 282 196 784 Logperch 455 299 377 482 91 286 332 Brook stickleback 0 0 0 0 9 4 2 Shiner spp. 15 103 59 0 0 0 30 Moxostoma spp. 851 829 840 51 509 280 560 me m -M a M Wm m m M

Table 2.2-3 1980 Monticello Seining Study - Species Percentage Contribution to Total Catch by Number for Upstream and Downstream Areas.

Upstream Downstream White sucker 29.4% White sucker 31.3%

Sand shiner 12.3 Spotfin shiner 15.9 Johnny darter 12.1 Smallmouth bass 14.4 Spotfin shiner 9.6 Spottail shiner 6.2 Bigmouth shiner 9.1 Bluntnose minnow 5.8 Moxostoma spp. 7.4 Northern hogsucker 4.9 Longnose dace 4.8 Logperch 4.6 Bluntnose minnow 4.4 Moxostoma spp. 4.5 Logperch 3.3 Johnny darter 3.1 Smallmouth bass 1.8 Shorthead redhorse 1.4 Silver redhorse 1.4 Sand shiner 1.3 Shorthead redhorse 1.1 Hornyhead chub 1.3 Hornyhead chub 0.9 Longnose dace 1.0 Northern hogsucker 0.6 Largemouth bass 0.9 Shiner spp. 0.5 Carp 0.9 Fathead minnow 0.5 Bluegill 0.6 Spottail shiner 0.2 Bigmouth shiner 0.6 Largemouth bass 0.2 Silver redhorse 0.4 Mimic shiner 0.1 Black crappie 0.4 Blacknose dace 0.1 Fathead minnow 0.2 Carp 0.1 Common shiner 0.2 Black crappie 0.1 Rock bass 0.1 Black bullhead 0.1 Brook stickleback 0.1 Trout perch 0.1 2.2-15

U I

Table 2.2-4 1980 Monticello Seining Study - Species Percentage Contribution to the Total Catch 1970 Through 1980.

I I

Species 1970 1973 1976 1977 1978 1979 1980 Hornyhead chub Creek chub 3.1 0.3 1.7 0.1 0.1 3.0 0.2 0.1 1.0 1.1 I Fathead minnow Bluntnose minnow Brassy minnow 12.7 0.9 16.2 0.3 0.6 23.4 0.2 17.3 0.5 40.2 0.1 6.8 0.4 4.9 I 21.1 23.5 23.4 16.8 21.9 14.0 11.9 Spotfin shiner Bigmouth shiner Sand shiner 27.3 18.4 21.8 21.6 12.4 15.3 30.8 6.2 29.0 57.6 0.5 6.0 8.4 I River shiner Spottail shiner Common shiner Golden shiner 1.0 2.9 0.1 0.8 3.4 0.2 1.2 1.1 0.2 0.8 1.0 0.3 2.3 0.1 I 0.1 0.1 Mimic shiner Carp Longnose dace 3.1 0.7 0.5 2.0 0.1 1.1 0.1 2.5 0.3 3.4 I

Blacknose dace 0.4 0.3 0.1 0.1 Northern redbelly dace Silver redhorse 0.1 1.2 0.9 0.1 1.0 3

Shorthead redhorse White sucker Northern hogsucker 2.5 3.9 2.5 0.8 7.4 0.1 1.4 0.2 4.4 0.3 1.2 30.1 2.1 I

0.1 Black bullhead Trout perch Brook silverside 0.1 0.4 0.1 0.1 0.9 0.1 0.1 0.1 I Smallmouth bass 1.7 1.0 0.4 0.3 1.2 3.5 6.3 Largemouth bass Black crappie White crappie 0.1 0.1 0.6 0.1 0.1 0.1 0.4 0.2 I Rock bass Bluegill Yellow perch 0.1 0.2 0.1 3.8 0.1 0.1 0.3 0.1 0.1 0.2 I Logperch. 0.2 0.3 0.1 3.8 Johnny darter Walleye 5.0 2.6 1.3 6.8 1.3 1.4 0.4 8.9 0.1 1

Brook stickleback Shiner spp.

Moxostoma spp. 0.3 0.6 0.3 16.9 1.0 0.6 0.1 0.5 0.6 5.1 0.3 6.4 I I

I 2.2-16 I

Table 2.2-5 1980 Monticello Seining Study - Station 1 Actual Number of Specimens Collected Species 5/16 5/28 6/19 6/23 7/7 7/21 8/6 8/18 9/8 9/22 Total Hornyhead chub 6 5 '11 Fathead minnow 3 3 Bluntnose minnow 20 19 2 13 13 1 7 75 Spotfin shiner 33 47 3 13 61 4 26 187 Sand shiner 32 50 88 21 4 8 203 Bigmouth shiner 4 52 47 16 119 Spottail shiner 6 6 Common shiner Mimic shiner Carp S

Longnose dace 4 21 11 33 42 5 116 t%3 Blacknose dace I-a Shorthead redhorse 7 9 16

-.1 Silver redhorse 2 19 21 White sucker 127 96 25 20 60 21 5 11 365 Northern hogsucker 1 10 11 Black bullhead Trout perch Smallmouth bass 5 3 10 9 1 3 31 Largemouth bass 5 5 Black crappie Bluegill Rock bass Johnny darter 5 15 9 70 92 8 3 2 204 Logperch 2 20 35 1 3 61 Brook stickleback Shiner spp.

Moxostoma spp.

Haul lengths (ft) 80 80 40 50 60 90 60 70 90 100 720

Table 2.2-6 1980 Monticello Seining Study - Station 2 Actual Number of Specimens Collected Species 5/16 5/18 6/19 6/23 7/7 7/21 8/6 8/18 9/8 9/22 Total Hornyhead chub 1 3 9 14 Fathead minnow 1 5 5 11 Bluntnose minnow 5 2 1 11 1 24 16 51 Spotfin shiner 23 12 16 9 15 8 7 90 Sand shiner 18 34 2 21 17 29 12 17 150 Bigmouth shiner 51 7 18 3 79 Spottail shiner Common shiner Mimic shiner 3 3 Carp 1 1 Longnose dace 5 10 7 1 2 25 Blacknose dace 3 3 Shorthead redhorse 13 3 16 00 Silver redhorse 8 8 2 18 White sucker 207 131 15 20 23 3 54 8 461 Northern hogsucker 4 1. 2 7 Black bullhead 1 1 Trout perch Smallmouth bass 2 5 14 21 Largemouth bass Black crappie. 1 1 Bluegill Rock .bass Johnny darter 19 10 47 28 3 23 13 143 Logperch 7 20 4 4 35 Brook stickleback Shiner spp. 12 12 Moxostoma spp. 27 15 12 43 97 Haul Lengths (ft) 100 60 40 50 40 60 50 60 70 100 630 m M M M W W O mm m MM u m

mam M M m m mm m m m mM Table 2.2-7 1980 Monticello Seining Study - Station 3 Actual Number of Specimens Collected Species 5/16 5/28 6/19 6/23 7/7 7/21 8/6 8/18 9/8 9/22 Total Hornyhead chub 2 3 7 8 20 Fathead minnow 2 2 Bluntnose minnow 5 12 20 1 34 3 5 80 Spotfin shiner 5 11 46 54 57 35 4 20 232 Sand shiner . 5 1 2 4 14 Bigmouth shiner 8 2 10 Spottail shiner 1 84 85 Common shiner 2 1 3 Mimic shiner r.3 Carp 4 10 14 Longnose dace 2 8 1 1 12 H

Blacknose dace Shorthead redhorse 9 7 16 Silver redhorse 2 3 5 White sucker 167 16 59 12 1 255 Northern hogsucker 1 2 7 18 3 20 22 83 Black bullhead Trout perch Smallmouth bass 2 11 19 13 13 6 3 15 82 Largemouth bass 1 1 2 Black crappie 1 Bluegill 1 11 11 Rock bass Johnny darter 5 3 7 15 Logperch 11 48 4 3 66 Brook stickleback Shiner spp.

Moxostoma spp. 7 7 Haul Lengths (ft) 70 70 40 70 60 90 90 70 60 115 735

Table 2.2-8 1980 Monticello Seining Study - Station 4 Actual Number of Specimens Collected Species 5/16 5/28 6/19 6/23 7/7 7/21 8/6 8/18 9/8 9/22 Total Hornyhead chub 1 1 2 Fathead minnow 1 1 Bluntnose minnow 2 1 1 2 10 16 Spotfin shiner 6 5 10 12 33 Sand shiner Bigmouth shiner 7 7 Spottail shiner 17 27 Common shiner Mimic shiner Carp 1 1 Longnose dace 3 4

• 0 Blacknose dace Shorthead redhorse 6 1 7 Silver redhorse 1 1 White sucker 217 3 3 1 1 225 Northern hogsucker 1 4 2 8 Black bullhead Trout perch Smallmouth bass 9 12 32 38 13 8 14 6 132 Largemouth bass 7 2 11 Black crappie 2 2 4 Bluegill Rock bass Johnny darter 21 10 31 Logperch 2 7 1 10 Brook stickleback 1 1 Shiner spp.

Moxostoma spp. 56 56 Haul Length (ft) 50 40 40 40 40 80 60 80 90 70 590 mM = M M M M - m = m M M =

Table 2.2-9 1980 Monticello Seining.Study Average number of smallmouth bass, white sucker, and Moxostoma sp. collected per hectare in upstream and downstream areas in 1973, 1974, 1976*, 1977, 1978, 1979,and 1980.

Smallmouth bass Upstream Downstream Fish/ha Fish/ha Average 1973 256 92 174 1974 380 152 266 1976 135 1977 101 12 56 1978 101 167 134 1979 9 465. 237 1980 205 552 378 White sucker 1973 1881 1416 1648 1974 250 78 164 1976 1501 1977 2401 157 1279 1978 240 65 152 1979 364 236 300 1980 3332 2642 2987 Moxostoma species 1973 989 1140 1064 1974 841 797 819 1976 9823 1977 405 494 450 1978 201 125 163 1979 103 179 141 1980 1124 758 941

• 1976 data from NUS Monticello 316 a & b NPDES demonstration.

2.2-21

I Table 2.2-10 1980 Mo nticello Seining Study I

Species List of Fish Discussed in This Text U

Common Name Scientific Name U Hornyhead chub Nocomis biguttatus Creek chub Semotilus atromaculatus Fathead minnow Pimephales promelas Bluntnose minnow Pimephales notatus Brassy minnow Hybognathus hankinsoni Spotfin shiner Notropis spilopterus Bigmouth shiner Notropis dorsalis Sand shiner Notropis stramineus River shiner Notropis blennius Spottail shiner Notropis hudsonius Common shiner Notropis cornutus Golden shiner Notemigonus crysoleucas Mimic shiner Notropis volucellus Carp Cyrpinus carpio Longnose dace Rhinichthys cataractae Blacknose dace Rhinichthys atratulus Northern redbelly dace Chrosomus eos Silver redhorse Moxostoma anisurum Shorthead redhorse Moxostoma macrolepidotum White sucker Catostomus commersoni Northern hogsucker Hypentelium nigricans Black bullhead Ictalurus melas Trout perch Percopsis omiscomaycus Brook silverside Labidesthes sicculus Smallmouth bass Micropterus dolomieui Largemouth bass Micropterus salmoides Black crappie. Pomoxis nigromaculatus White crappie Pomoxis annularis Rock bass Ambloplites rupestris Bluegill Lepomis macrochirus Yellow perch Perca flavescens Logperch Percina caprodes Johnny darter Etheostoma nigrum Walleye Stizostedion vitreum Brook stickleback Culaea inconstans I

U U

2.2-22 I

MONTICELLO NUCLEAR GENERATING PLANT ENVIRONMENTAL MONITORING PROGRAM 1980 ANNUAL REPORT DEVELOPMENT OF A MODEL FOR PREDICTING YEAR-CLASS STRENGTH OF FISH IN THE UPPER MISSISSIPPI RIVER (2.3)

Prepared for Northern States Power Company Minneapolis, Minnesota by Dr. W. A. Swenson Superior, Wisconsin 2.3-1

2.3 DEVELOPMENT.OF A MODEL FOR PREDICTING YEAR-CLASS STRENGTH OF FISH IN THE UPPER MISSISSIPPI RIVER 2.3.1, INTRODUCTION Understanding of the relationship between stream stage, other physical conditions, reproductive success (year-class strength), and fish abundance could be useful in managing stream use by the electric power industry in a manner which promotes fish production and efficient power production.

As part of monitoring requirements, Northern States Power Company has been collecting information on physical condi tions and fish populations in the Mississippi River between their plants at Becker and Monticello, Minnesota since 1973.

During this study, literature review and analysis of physi cal data were used to develop and test a basic model useful in predicting year-class strength of important Mississippi River fish populations. Literature review was used to identify the mechanisms which influence year-class strength and abundance of fish in streams and formed the basis for development of the model. The model and information on temperature, discharge, and turbidity were used to predict relative strength of 1973-1980 smallmouth bass (Micropterus dolomieu) year-classes in the study area. Application of the model in predicting year-class strength was useful in identifying the area where data are needed to improve the predictive capacity of -the model. Estimates of year class strength based on the model will be compared with those based on analysis of age class structure of smallmouth bass populations in the study area to.validate the assump tions upon which the model is based.

2.3-3

I Fishing pressure is substantial .in the stream section between Becker and Monticello and has increased from 2,600 hours0.00694 days <br />0.167 hours <br />9.920635e-4 weeks <br />2.283e-4 months <br /> in 1973 to 20,000 hours0 days <br />0 hours <br />0 weeks <br />0 months <br /> in 1979. During the period, total catch increased from 173 kg to 2,644 kg (Heberling and Weinhold 1979). Most of the pressure is directed at small mouth bass (Micropterus dolomieu), the dominant game fish in the area. Black crappie (Pomoxis nigromaclatus), .walleye (Stizostedion vitreum vitreum), and northern pike (Esox lucius) are important in the catch. Rockbass (Ambloplites rupestris), black bullhead (Ictalurus melas), carp (Cyprinus carpio), shorthead redhorse (Moxostoma macrolepidotum),

silver redhorse (M. anisurum), white sucker (Catostomus commersoni), bigmouth buffalo (Ictiobus cyprinellus), and musky (Esox mascuinongy) are taken in limited numbers.

Although shorthead and silver redhorse are of limited importance to the fishery, they are the dominant species in the area.

2.3.2 LITERATURE REVIEW Smallmouth bass The influence of stage and related habitat conditions on the reproductive success of smallmouth bass has been studied extensively. There appears to be general agreement that catastrophic flow (flood stage) conditions during the reproductive period result in weak year classes and reduced abundance of smallmouth (Brown 1960; Cleary 1956; Funk and Fleener 1974; Reynolds 1965). Timing appears to be criti cal, however, as Funk and Pflieger (1975) found catastrophic flow prior to spawning may serve to improve spawning areas and subsequent spawning success. They also suggest that the influx of allochthanous material and subsequent increases in invertebrate production may have a positive influence.

I 2.3-43

Temperature variations which may accompany changes in stage have been associated in several ways to year-class success and smallmouth bass abundance. Delays in nesting behavior (Pflieger 1975; Shuter et al. 1980) and nest abandonment by spawning males (Cleary 1956; Henderson.and Foster 1956; Latta 1963; Marz 1964) occur when temperatures during the spawning and nesting period fall below approximately 15 0C. Spawning to hatch time and the period between hatch and the rising of fry in the nest are dependent on temperature (Webster 1948; Kerr 1968; Shuter et al. 1980). Early development time increases from approximately 8 days at 20*C to 14 days at 170 C. Although slower development within the nest does not result in direct mortality, it increases the probability of mortality from predation, siltation, or temperature declines below 150 C. Larimore and Suever (1968) and Coutant (1975) showed swimming of fry was slowed under reduced temperatures, increasing their susceptibility to current and predators. Under optimum feeding conditions, growth of young-of-the-year smallmouth increases from approximately 0.2 mm/day at 160 C to 1 mm/day at 220 C (Rowan 1962; Peak 1965; Shuter et al. 1980).

Oliver et al. (1979) and Shuter et al. (1980) provide evidence that young smallmouth stop feeding when temperatures drop below 7-10 0 C in the autumn, and that smaller individ uals do not possess the essential energy reserves to live through extended winters. Based on the energy reserves and energy requirements of young-of-the-year smallmouth bass, Shuter et al. (1980) accurately predicted changes in size structure of over-wintering young smallmouth for a natural system. They concluded that the controlling influ ence of temperature on reproductive success and growth are the primary mechanisms controlling survival during the first year of life and subsequent year-class strength in lacustrine systems. The mechanisms through which tempera ture influences first year survival are identified by a 2.3-5

I conceptual model (Figure 2.3-1). Shuter et al. (1980) demonstrated that the geographic range and year-class strength of lacustrine populations of smallmouth bass could be predicted from information on temperature variation during the spawning period and from average July air temper atures.

Although temperature represents the primary controller of I

smallmouth bass abundance in lacustrine systems, flow appears to be extremely important to survival and abundance of populations in riverine habitats. Smallmouth require quiet waters for nesting behavior to occur, and high flow rates have been found to delay nest construction to restrict the availability of spawning habitat (Pflieger 1975) and to result in nest abandonment by males. While few studies provide information on flow rates critical to nesting, Weinmeller (Personal Communication)1 observed 100 percent nest abandonment occurred at flows exceeding 55 mm/sec. (near the bottom) in Indian Creek, Ohio. It was not clear whether nest abandonment occurred due to the direct effects of current or as a result of cover loss associated with higher stage and flow conditions. Wein meller observed that all nesting was associated with cover, and that cover was destroyed under high flow conditions.

Flow has been shown to have direct effects on smallmouth fry I

survival. Surber (1939) and Webster (1954) found smallmouth fry are extremely sensitive to currents and are displaced from their nests under high stage conditions. In laboratory flumes, Larimore (1975) observed that the capacity of young smallmouth bass (22-25 mm total length) to maintain position was related to visual and tactile orientation, which was I

1 Kirk Weinmeller, Dept of Zoology, Miami University, Oxford, Ohio.

2.3-6

reduced under darkness, turbidity, or turbulence. Most young smallmouth could maintain position for short periods (15 minutes) under flows of 170 mm/sec. in lighted condi tions, but were displaced at flows of 100 mm/sec..under darkness or turbid conditions. Larimore (1975) showed that darkness and turbidity resulted in loss of visual orienta tion, which promoted displacement, and that rapid changes in flow rates had similar effects due to loss of tactile orientation. He concluded that high flow, turbulence, and turbidity associated with high stage conditions promote year-class failure in smallmouth bass due to loss of orien tation and related displacement of young bass. Another form of displacement is suggested by Munther (1970), who observed that smallmouth bass concentrate in the lee of currents or quiet areas. These observations suggest that during high flow periods, young smallmouth bass are displaced or active ly seek out quiet water areas of reduced current, reducing the total habitat available to the population. The concen trating effects associated with this response to flow can be expected to promote intraspecific and interspecific preda tion and competition (Eipper 1975). Although not measured in smallmouth, observations on other species (Symon 1976) suggest that energy directed at coping with flow can be expected to reduce energy available for growth.

Increased turbidity and sedimentation generally occur under high stage conditions in low flow areas of streams where smallmouth nest. High sedimentation rates and turbidity levels have been found to cause spawning failure and slow growth of smallmouth fry 'in ponds (Swingler .1949; Buck 1956).

2.3-7

Other Species Information on factors which control abundance of other dominant species in the study area are limited. Larimore et al. (1952) and Funk (1975) found abundance and weight distribution of smallmouth bass to be correlated with those of several catostomid species, suggesting that factors which control year-class success are similar. Large, slow-moving, warm water streams of moderate depth and with a mixed substrate are identified as optimum walleye habitat by Ketchill et al. (1977). Substrate requirements and spawning behavior of walleye and the redhorse sucker group are well adapted to riverine conditions. Walleye and the suckers spawn in riffle areas. Walleye spawning generally occurs between temperatures of 6-10*C (Smith and Koenst 1975). Shorthead redhorse spawn earlier and at lower temperature (12*C) than silver redhorse (16*C) (Meyer 1962).

After hatching and early development in the spawning areas, walleye and sucker fry drift passively downstream in near surface waters. Drifting occurs primarily at night (Gale and Mohr 1978). Priegel (1970) found walleye fry are unable to feed during the drifting period, even under moderate current conditions, and must reach quiet waters where feeding can take place within 3-5 days to avoid starvation.

He also found that highly turbulent water results in signif icant walleye fry mortality. Houde (1969) showed walleye fry less than 9.3 mm could not maintain their positions in current velocities of 30 mm/sec., and only 50 percent of fry 10-16 mm could maintain position at flows from 30-50 mm/sec.

Although information on the biology of redhorse suckers is limited, Gale and Mohr (1978) found larger fry occur in shallow, quiet water near the stream margin, suggesting a 2.3-8

I preference for low-current velocities exists and low veloc ities are critical to survival and growth. Meyer (1962) found that although adult redhorse may enter areas of high current velocities, the young inhabit slow water over muck bottoms, often under banks.

Susceptibility to current is increased at reduced tempera tures, which slow growth. Walburg (1972) found much of the variation in sauger (Stizostedion canadense) year-class strength is associated with early summer temperatures and flow in Lewis and Clark Lake, and impoundment of the Missouri River. Slow growth and greater displacement of young saugers occurred during summers, where temperatures fell below 210 C and water retention in the reservoir dropped below five days. Smith and Koenst (1975) showed fast growth and high survival of walleye after yolk sac absorption requires temperatures of 21-22*C.

2.3.3 A CONCEPTUAL MODEL OF YEAR-CLASS FORMATION Information on the factors which control year-class strength in smallmouth bass indicates that reproductive behavior and' development are controlled through several mechanisms, acting on different phases of the reproductive and develop mental processes. The available data suggest that year class success and fish abundance are the products of the combined success of all phases of the reproductive and early development processes. Measurement of year-class success and the factors which control it may, therefore, best be approached through a modelwhich considers the success of each phase of the reproductive and early development pro cesses.

In smallmouth bass, nest construction, spawning, nest guarding, embryo development, fry development, growth of young, and overwinter survival represent phases in the 2.3-9

reproductive and development processes which control strength of year-classes and abundance. These phases may be viewed as a series of compartments through which percentages of the adult population (reproductive compartments) or young (development compartments) pass (Figure 2.3-2). Year-class strength may be viewed as the outcome of the number of young created within the reproductive compartments and their survival through the developmental compartments.

Under conditions where early summer temperatures are not favorable to spawning or current, turbidity, sedimentation, and cover conditions prohibit nest building, spawning, or nest guarding, reproduction does not occur and the species is absent from the system. Where temperature, current, and related conditions retard spawning, large numbers of young may be produced, but the probability of survival through the developmental compartments is generally low because of the demonstrated influence of small size on the capacity of young to cope with current, predation, and winter energy demands. Therefore, in situations where spawning is delay ed, year-class strength can be expected to be comparitively low. Early spawning may also lead to year-class failure, because temperature instability early in the year promotes high embryo-and fry mortality (Shuter et al. 1980).

By considering the temperature critical to embryo survival and time required to accumulate the energy required to overwinter, Shuter et al. (1980) predicted that the largest year-classes of smallmouth bass occurred in the Baie du Dove', Lake Huron, population when spawning occurred between June 10-20. In stream populations, several studies have shown that flow, turbidity, and sedimentation can have similar effects on spawning and embryo survival. Generally, strong year-classes should be promoted in stream habitats when temperatures are maintained above 150C by mid-June and flow, turbidity, and sedimentation remain low. If tempera 2.3-10

tures remain below 15*C after mid-June and flow, turbidity, and sedimentation are high, or if temperatures and other conditions are appropriate for reproduction prior to mid June but subsequently are altered in a manner which reduces fry survival (low temperature; high flow, turbidity, and sedimentation), poor year-classes should result. Among the variables important to year-class strength in stream habi tats, flow during the fry development stage appears to be most critical.

Beyond the fry stage, temperature and flow appear to be primary controllers of the amounts of energy accumulated in the young through the growth process. Because size attained through growth is important in coping with current and predators, survival during summer should be promoted by higher temperatures and reduced current conditions. Years of low summer temperatures and increased flow should result in reduced summer and overwinter survival, resulting in weaker year-classes. Overwinter survival is also influenced by winter severity, which determines the energy expenditure required to survive.

If temperature, current, turbidity, and sedimentation are determined to a large degree by stage, the existing data suggest that stage is the ultimate determiner of year-class strength and abundance of fish in riverine habitats. The existing data also make it clear that defining the influence of stage on year-class strength will require identifying the relationships between stage temperature, current, turbidity, and sedimentatioh levels. Data collected by NSP were analyzed to define relationships between stage and the other important physical stream parameters.

2.3-11

I 2.3.4 PHYSICAL CONDITIONS IN THE MISSISSIPPI Discharge, Temperature, and Turbidity Relationships Stage, discharge, temperature, and turbidity measurements taken at the NSP Monticello facility from 1973 to present were analyzed to determine their relationships and potential influence on fish abundance. Discharge was estimated from stage and represent a good indicator of stage and current conditions.

Daily discharge and temperature observations were averaged for 15-day periods, starting January .1, for all years of record. The 15-day averages were plotted to define normal trends for the eight-year period (Figure 2.3-3). The records show that discharge starts to increase from a winter average of approximately 4,000 CFS during March and reaches a peak of 14,000 CFS in late April. Discharge declines from early May through July. An average discharge of 3,700 CFS occurred during August and September. Temperatures increas ed with discharge in early March and continued to rise until late July. Temperature declines slowly from July through early December.

Temperatures appeared to vary independent of discharge except during the May-early June period. During May and early June it was apparent from the records that short term increases in flow resulted in lower temperatures. Regres sion analysis was used to define the relationship between 15-day average temperatures and discharge for the years 1973-1980. The analysis showed that temperature decreased at a rate of 0.4aC per 1,000 CFS increase in discharge, within a range of 1,000-16,500 CFS, during May and the first 14 days of June (Figure 2.3-4). Late June temperatures did not appear to be influenced significantly by variations in discharge.

2.3-12

Turbidity (NTU) and total suspended solids (mg/1) were measured on a weekly basis. General analysis indicated turbidity and suspended solids increased considerably during periods of high discharge and remained high .during periods of reduced discharge which followed. Turbidity and suspend ed solid measurements were higher during spring and summer months than during winter (Table 2.3-1). The difference appeared related to the fact that both measurements are influenced by plankton abundance as well as sediment load.

Suspended solid values averaged four and one half times the winter NTU values and six times the summer NTU values, indicating they were most responsive to changes in plankton abundance. The limited number of measurements, delayed response of turbidity and suspended solid measurements to changes in discharge, and the influences of plankton abund ance on these measurements made it impractical to precisely define the influence of discharge on turbidity or sedimenta tion. However, mean NTU and suspended solid measurements during the reproductive-early development and growth periods of smallmouth bass were useful indicators of relative sedimentation rates and food availability.

2.3.5 PREDICTING YEAR-CLASS STRENGTH Approach The conceptual model (Figure 2.3-2) is based on the assump tion that flow and temperature are primary controllers of smallmouth bass year-class strength in the study area. The model, information from the' literature, and information on physical conditions in the study area were applied in estimating relative strength of smallmouth bass year-classes during the period 1973-1980. This application of available ihformation was used to test the validity of the assumptions upon which the model is based, and to identify areas where additional quantitive information is needed to convert the 2.3-13

1 conceptual model into a more useful predictive tool.

Predictions based on the model will be tested against estimates based on population age structure. The relative probability of successful completion of nesting, spawning, nest guarding, embryo, and fry development phases was estimated on the basis of physical conditions during May and June. The relative probability of overwinter survival was based primarily on summer temperatures and length of the growing season.

Two-day average temperature and discharge during May and June of each year were plotted against the eight-year averages to determine if conditions were above or below average. Time of major nest construction was predicted to occur when two-day average temperatures reached 150 C and discharge was not high enough to cause turbulence in protected areas. Because field data are lacking, 12,000 CFS was selected somewhat arbitrarily as the level of discharge above which all spawning would be inhibited. This discharge represents three times the normal summer, autumn, and winter average. During periods when discharge fell below 12,000 CFS, peak spawning was predicted to occur using the formula of Shuter et al. (1980).

D = 8.0 - 0.55d Where:

D = days after nest construction d = number of degree days above 10*C accumulated prior to the date nest construction began Time from spawning to hatch and hatch to rise were predicted from regression relationships between temperature and time (days) developed by. Webster (1948) and Kerr (1968) and presented graphically by Shuter et al. (1980).

I 2.3-143

Relative survival during the time from spawning to hatch, hatch to rise, and the first five days after larvae rise in the nest was ranked as either excellent, good, average, below average, or poor on the basis of temperature, dis charge, or turbidity observations. Although quantitive observations are needed, for the purposes of this test of the model, survival during the critical early development period was generally classified as follows:

1) Excellent - Temperature remains above 16*C and increasing; discharge less than 4,000 CFS; turbidity, below average.

2) Good - Temperature above 15*C remains stable or increases; discharge less than 6,000 CFS and declining; turbidity average or below.

3) Average - Temperature above 15*C and remains stable; discharge above 8,000 CFS and fluctuating; turbidity average or below.

4) Below Average- Temperature remains at about 150C; discharge between 6-12,000 CFS; turbidity above average.

5) Poor - Discharge above 12,000 CFS; turbid ity above average.

Initiation of active summer growth was considered to occur five-days after larvae were predicted to rise in the nest.

Active growth was considered to end when temperatures dropped below 10*C in the autumn.

Applying data summarized by Shuter et al. (1980), growth was estimated to occur at the following rates:

2.3-15

II 0.14 cm/day at temperatures between 25-36 0 C 0.10 cm/day at temperatures between 20-24*C 0.06 cm/day at temperatures between 18-19*C 0.02 cm/day at temperatures between 15-17C 0.01 cm/day at temperatures between 10-14'C3 Quantitative information relating discharge and turbidity to growth is lacking. However, evidence is available that turbulence and reduced visibility have a negative influence on growth. Therefore, discharges above 12,000 CFS were considered to have a negative influence on growth. For the purpose of this analysis, growth was estimated to be reduced by 50 percent during periods when discharge approached or exceeded 12,000 CFS. Survival during summer and over winter was considered to be positively correlated with size at the end of the growing season. Size at the end of the growing season was estimated as length accrued during the period of active growth and length before growth started (15 mm).

Estimated Spawning and Early Development Success During 1973 temperatures, discharge, and turbidity were generally below average during May and June (Figure 2.3-5).

Temperatures promoting nest construction were reached on May

19. Peak spawning was estimated to occur on May 25, when discharge had declined to a low for the period of 5,600 CFS (Figure 2.3-5; Table 2.3-2). Discharge, however, started to increase on May 27 and reached a peak of 8,008 CFS about May 30.

I During this period turbidity reached 17 NTU and temperatures remained at approximately 14.8*C. The reduced temperature, increased current, and high turbidity probably promoted nest abandonment and poor embryo survival. Dis charge and turbidity declined after May 28, and tempera tures rose to 20'C by June 8, which probably stimulated a second nesting and good survival of any fry that survived the. incubation period from the first spawning. Conditions 2.3-16

remained good after June 8 for survival of embryo and fry phases. Temperatures during the summer of 1973 were about normal during June-September, but never reached into the optimum growth range. Discharge exceeded 12,000 CFS after October 12, when temperatures reached 13*C and growth was considered to have ceased. The period of growth was esti mated at 133 days (June 10-October 12) for the first spawn ing and 121 days (June 22-October 12) for fish from the second spawning.

During 1974 discharge remained above 12,000 CFS until June 1, when it dipped to an average of 11,700 CFS for 6-7 days.

Nest construction in protected areas was estimated to occur at this time, with a spawning peak occurring approximately June 5. Discharge began to rise on June 7 and reached 16,221 CFS by June 12. Discharge declined slowly from that date and fell below 12,000 CFS by June 22. The high dis charges are predicted to have resulted in below average survival of embryo and fry in the nest and poor survival of the black fry stage. A second nesting period is predicted to have begun on June 22. Although discharge was high at this time, it declined and subsequent temperatures were in the range which promoted rapid incubation and fry develop ment. The delay spawning and low October temperatures (100C on October 1) would. have resulted in a short growing season and poor survival during later development stages, even though July temperatures fell in the optimum growth range.

Discharge on May 1, 1975 was 40,668 CFS and did not drop below 12,000 CFS until Junle 1 when nest construction was considered to have begun in protected areas. Temperatures were above 20 0 C at this time, and peak spawning is expected to have occurred around June 3. Discharge continued to decline from June 3 through June 11 when it reached 6,094 CFS. However, temperatures declined below average to 170C prolonging the incubation and nest fry stages. The black 2.3-17

I fry stage is predicted to begin around June 14, when dis charge began to rise to a peak-of 11,405 CFS which occurred June 24. Turbidity was above average (10-12 NTU) during the predicted black fry stage. The high discharge and turbidity is predicted to have promoted displacement and below average survival during the black fry stage. Discharge remained above 12,000 CFS through July 16, and is predicted to have slowed growth during the period by 50 percent. Temperatures were above average and within the optimum growth range through early August and remained above average during early September. Temperatures fell below 10*C on October 16..1 Conditions were optimum for reproduction and early develop ment during 1976 (Figure 2.3-6). Temperatures reached 150 C by May 9 when discharge was 2,500 CFS and falling. Based on the thermal conditions prior to that date, the spawning peak is predicted to have occurred on May 14. Temperatures during and following spawning were above normal and averaged 18.5 0 C. This would have resulted in a four-day incubation period and a seven-day early fry development stage. Through out the incubation and early fry development period, temper atures continued to rise, discharge declined to an average of 1,700 CFS, and turbidity remained below normal (3.8 NTU),

indicating survival was excellent. Temperatures were above average or average through late September and remained above 100C until October 10.

Conditions at the beginning of May, 1977 were very similar to 1976, with discharge below 4,000 CFS and temperatures above average. Based on thermal history, spawning can be predicted to have occurred May 5. Average discharge remained low through the early development stages, however, starting on about May 17 and continuing through June, discharge and temperature began to fluctuate in response to rain events. Although discharge never exceeded 4,000 CFS 2.3-18

and temperatures did not drop below average, turbidity was abnormally high and reached 25 NTU. This turbidity may have resulted in considerable fry displacement. Temperature and discharge remained in the optimum range for growth through most of July, but temperatures were below normal during August and September. Temperatures dropped below 10*C after October 10.

Temperatures reached 150C on May 14, 1978 when discharge was 6,366 and dropping. Peak spawning was predicted to occur May 19. Conditions continued to be excellent into the black fry stage, when discharge increased rapidly to 9,670 CFS during the period May 29-June 4. Turbidity increased (7.4 NTU) and temperatures fell below average during the period suggesting considerable fry displacement occurred. Dis charge fluctuated and declined toward the average in late June, but climbed above 12,000 CFS in early July when temperatures were well below normal. Temperatures were also below normal during August and discharge remained above normal (6,000-9,000 CFS).

During 1979 discharge did not drop below 12,000 CFS until May 27, which was also the approximate date that tempera tures surpassed 15*C. Based on the thermal history, spawn ing was estimated. to occur 6 days later. Temperatures ranged between 17-19*C during the period following spawning, and incubation and early fry development were estimated to require 5 and 7 days, respectively (Table 2.3-2). Tempera tures fluctuated but remained below normal while discharge declined toward the normal' level during the early develop ment period. However, on June 17, discharge began a steady increase and reached 12,117 CFS by June 25. Turbid ity was measured at 23 NTU on June 29, and the combined effects of turbidity and discharge are predicted to have induced considerable fry displacement. Temperatures were below normal during July and August and dropped below 10*C October 8.

2.3-19

I Temperatures reached the lower end of the preferred spawning range by April 28, 1980 when discharge was 5,993 CFS and declining. Based on thermal history, spawning was predicted to peak seven days later. However, temperatures dropped below 15"C May 4 and did not exceed that temperature again until May 15. The reduced temperatures expanded the period of development, and were predicted to cause nest abandonment and poor survival. Based on temperature, a second spawning could be expected to have occurred May 22. Discharge during the period was below 3,000 CFS, and temperatures were above normal promoting rapid incubation'and early fry development.

Discharge began to increase May 28 and reached 4,730 CFS by June 8. This rise resulted in a temperature decline to the eight years norm but turbidity remained below normal. The rise in discharge is expected to have caused some displacement of fry. Discharge remained low throughout the major growth period, and temperatures were average or above through early September when discharge rose above 7,000 CFS. Temperatures remained below 10*C after October 10.

Estimated Overwinter Survival and Year-Class Strengths I

Estimates of total length and the end of the growing season I

were based on laboratory data developed under conditions of a continuous food. supply. It is probable, however, that the small size of young spawned at later dates limited the range of forage sizes available to them restricting their food consumption and growth. If food availability was lower for smaller fish it is likely that real size differences would be greater than indicated by the estimates given in Table 2.3-2. Because both spawnings in 1973 occurred fairly early,.growth was good and winter (period below 10*C) was not extended (189 days); survival was expected to be average or above and year-class strength was ranked as good. Winter length was extended (200 days) in 1974, and survival and 2.3-20

growth during the summer was not good; therefore, year-class strength was ranked as weak. The year-class produced during 1975 was also ranked weak due to poor survival during early development and poor growth during the summer, al though winter length was short (178 days). The combination of successful spawning, early development, rapid summer growth, and a short winter (176 days) during ,1976 should have.promoted development of a dominant year-class. A good year-class should have developed during 1977 as a result of the early spawning, although summer temperatures were not excellent for growth and the winter period was long (197 days). High water, poor growth, and extended winters during 1978 (213 days) and 1979 (191 days) were predicted to result in weak year classes. The 1980 year-class was ranked as strong as a result of the expected excellent. survival and good growth, although winter length is yet to be determined.

2.3-21

1 2.3.6 BIBLIOGRAPHY I

Brown, E.H. Jr. 1960. Little Miami River headwater stream investigations. Ohio Dept. Nat. Res., 143pp.

Buck, D.H. 1956. Effects of turbidity on fish and fishing.

Trans. N.Am. Wildl. Conf. 21:249-261.

Cleary, R.E. 1956. Observations on factors affecting smallmouth bass reproduction in Iowa. J. Wildl. Mgmt.

20(4) :353-359.

Coutant, C.C. 1975. Responses of bass to natural and artifical temperature regimes. pp 272-285. In:

Stroud, R.H. and H. Clepper, eds. National Symposium on the Biology and Management of the Centrarchid Bass, Sport Fishing Institute. Washington, D.C.

Eipper, A.W. 1975. Environmental influences on the mortal ity of bass embryos and larvae. pp. 295-305. In:

Stroud, R.H. and H. Clepper, eds. National Symposium on the Biology and Management of Centrarchid Basses.

Sport Fishery Institute, Washington, D.C.

Funk, J.L. 1975. Evaluation of the smallmouth bass popula tion and fishery in Courtois Creek. pp 257-269. In:

Stroud, R.H. and H. Clepper, eds. National Symposium on the Biology and Management of Centrarchid Basses.

Sport Fishing Institute, Washington, D.C.

Funk, J.L. and G.G. Fleener. 1974. The fishery of a Missouri Ozark stream Big Piney River and the effects of stocking fingerling smallmouth bass. Trans. Am.

Fish. Soc. 103(4)757-771.

Gale, W.F. and H.W..Mohr, Jr. 1978. Larval fish drift in a large river with a comparison of sampling methods.

Trans. Am. Fish. Soc. 107:46-55.

Heberling, G.D. and J.W. Weinhold. 1979. A summary of the 1979 Monticello-SHERCO creel survey. In: Monticello Nuclear Generating Plant Environmental Monitoring Program 1979 Annual Report. Northern States Power Company, Mpls, MN.

Henderson, C. and R.F. Foster. 1956. Studies of smallmouth black bass (Micropterus dolomieu) in the Columbia River near Richland, Washington. Trans. Am. Fish. Soc.

86:112-127.

Houde, E.D. 1969. Sustained swimming ability of walleye (Stizostedion vitreum vitreum) and yellow perch (Perca flavescens). J. Fish. Res. Bd. Can. 26:1647-1659.

2.3-22

2.3.6 BIBLIOGRAPHY (Continued)

Kerr, S.R. 1966. Thermal relations of young smallmouth bass, Micropterus dolomieui Lacipbde. M.S. Thesis, Queens Univ., Kingston, Ontario. 67pp.

Kitchill, J.F., M.G. Johnson, C.K. Minns, K.H. Loftus, L.

Grieg, and C.H. Olver. 1977. Percid habitat; the river analogy. J. Fish. Res. Bd. Can. 34:1936-1940.

Larimore, R.W. 1975. Visual and tactile orientation of smallmouth bass fry under floodwater conditions. pp 323-332. In: Stroud, R.H. and H. Clepper, eds.

National Symposium on the Biology and Management of Centrarchid Basses. Sport Fishing Institute, Washington, D.C.

Larimore, R.W. and N.J. Duever. 1968. Effects of tempera ture acclimation on the swimming ability of smallmouth bass fry. Trans. Am. Fish. Soc. 97(2):175-184.

Larimore,. R.W., G.H. Pickering, and L. Durham. 1952. An inventory of the fishes of Jordon Creek, Vermillion C.

Illinois. Ill. Nat. Hist. Survey Biol. Note 29, 26pp.

Latta, W.C. 1963. The life history of the smallmouth bass, Micropterus dolomieu, at Waugoshance Point, Lake Michigan. Mich. Dept. Conserv. Inst. Fish. Res. Bull.

5. 56pp.

Meyer, W.H. 1962. Life history of three species of red horse (Moxostoma) in the Des Moines River, Iowa.

Trans. Am. Fish. Soc. 91:412-419.

Marz, D. 1964. Observations on large and smallmouth bass nesting and early life history. Wisc. Conserv. Dept.

Res. Rep. 11 (Fish). 13 pp.

Munther, G.L. 1970. Movement and distribution of small mouth bass in the Middle Snake River. Trans. Am. Fish.

Soc. 99(1):44-53.

Oliver, J.D., G.F. Holeton, and K.E. Chua. 1979. Over winter mortality of fingerling smallmouth bass in relation to their size, percent storage materials and environmental temperature. Trans. Am. Fish. Soc.

108:130-136.

Peek, F.W. 1965. Growth studies of laboratory and wild population sample of smallmouth bass (Micropterus dolomieui Lecipbde) with applications to mass marking of fish. Master's thesis. University of Arkansas, Little Rock, Arkansas, USA.

2.3-23

I 2.3.6 BIBLIOGRAPHY (Continued)

I Pflieger, W.L. 1975. Reproduction and survival of the smallmouth bass in Courtois Creek. pp231-239. In:

Stroud, R.H. and H. Clepper, eds. National Symposium on the Biology and Management of Centrarchid Basses.

Sport Fishing Institute, Washington, D.C.

Priegel, G.R. 1970. Reproduction and early life history of the walleye in the Lake Winnebago region. Wisc. Dept.

Nat. Res. Tech. Bull. 45. 105pp.

Reynolds, J.B. 1965. The life history of smallmouth bass Micropterus dolomieu Lacipede, in the Des Moines River, Boone County, Iowa. Iowa State J. Sci. 39(4) 417-436.

Rowan, M.I. 1962. Effects of temperature on the growth of young-of-the-year smallmouth black bass. Master's Thesis. University of Toronto, Toronto, Canada.

Shuter, B.J., J.A. MacLean, F.E.J. Fry and H.A. Regier.

1980. Stochastic simulation of temperature effects on first-year survival of smallmouth bass. Trans.Am.

Fish. Soc. 109:1-34.

Smith, L.L., Jr. and W.M. Koenst. 1975. Temperature effects on eggs and fry of percoid fishes. U.S. EPA Ecol. Res. Series Publ. EPA 660/3 75-017.

Surber, E. 1939. A comparison of four eastern smallmouth bass streams. Trans. Am. Fish. Soc. 68(1938):322-333.

Swingler, H.S. 1949. Some recent developments in pond management. Trans. North Am. Wildl. Conf. 14. 295-312.

Symon, P.E.K. 1976. Behavior and growth of juvenile Atlantic salmon (Salmo solar) and three competitors at three stream velocities. J. Fish. Res. Board Can.

33:2766-2773.

Walburg, C.H. 1972. Some factors associated with fluctua tions in year-class strength of saugers in Lewis and Clarke Lake, South Dakota. Trans. Am. Fish. Soc.

101:311-316.

Webster, D.A. 1954. Smallmouth bass, Micropterus dolomieui 327. 39pp.

in Cayuga Lake. Cornell Univ. Agric. Exp. Sta. Memoir 2.3-24

SURVIVAL OVER FIRST YEAR OF LIFE A

SURVIVAL SURVIVAL ON 'NESTS OVER-MINTER TIMING OF DEVELOPMENT WINTER

!0 W SPAWNING TIM ON TESTS STARVATION I)

U.'  ::: V ANNUAL WATER TaMPERATURE REGIME Figure 2.3-1. Schematic outline of the model of the influence of the annual water temperature regime on first-year survival of smallmouth bass (Shuter et al. 1980).

Nest L Nest L-&ab ryo -J ry Growth of i- Overwinter Construction ________ Guarding __fDevelopment -Development -Young - Survival Temperature 44 Stable and Above 15 0 C by mid-June - - *-Above -- -Short Periods 2100 Below 80 C Current Low (Less than 55mm/see over nests +--cc Low.

-p Turbidity Low Sedimentation_ Low IA Figure 2.3-2. Schematic diagram of the reproductive and developmental phases (compartments) important to year-class survival in smallmouth bass with habitat conditions suggested by the literature to promote strong year-classes.

m m m m mmMMM me M

Figure 2.3-3. Average discharge (CPS) and temperature (oC) in the Mississippi 30- River near Monticello, Minnesota for the period 1973-1980.

-30

• Q 0

20 0 -0 I g* 10 0 rz 4

Lai 1

10-I

Figure 2.3-4. Relationship between average discharge and temperature during May and June.

May 1-15 T mp 17156 -.00047 7 *FS 1973 6929 12.2 20- r,=3. 741$ 1974 16425 11.1 r,=63t1.3 05 1975 32579 11.1 P 0.8 - 1976 3067 13.8

- - N*7 1977 2512 18.3 10 - 1978 6712 13.9 1979 19849 6.7 1980 4448 15.5 0- May 16-30 T m0-1988 -. 0002511 *CS 1973 6515 15.6 20 ir57)9.87;64 1974 16334 13.9 21 8 1975 16592 18.9

• 1976 1482 18.3 N-8 1977 1868 23-3 10-- -1978 4865 19.4 C.)

0 1979 5706 15.5

0. 0-1980 2706 20.0 May 31-June 14 1973 5586 21.1 IW (L

• 1974 11361 18.8 1975 8624 18.8 I- 1976 1478 23.9 Temp= 3.4196 .00 482 25* CFS 1977 2750 21.6 1=1 646 399 3 1978 7974 19.4

=3 54. )679 1979 7886 19.4

=0. 24- 1980 3647 21.1 I =8 0 June 15-29

• 0------ - 1 1973 2821 22.2 20t 1974 11627 21.1 1975 9500 21.6 emp = 2.696 00 095722 *CFS 1976 1625 22.2

=0 712903424 1977 2157 23.3

=3110.18951 1978 6416 21.1

=0. 6- 1979 9333 22.7 T=8 1980 3730 22.2 I I d 8 12 16 20 24 DISCHARGE CFS x 1000 m mmmminminminm~~m

Figure 2.3-5. Relationship between normal and 1973 temperature and discharge.

30

-30 40

.0 $4

• 1 020 0. 10 Q 0

$4 C1) 10-It K

Jan Feb Nov Dec

Figure 2.3-6. Relationship between normal and 1976 temperature and discharge.

0 4-)

54 0

o2 o20 4)

E-1 4

W 10 AC Jan Feb m m m m - m m m - - m - - m m

Table 2.3-1.

Mean Turbidity (NTU) and suspended solids (mg/1) in the Mississippi during; winter (December-Februar) and during the reproductive (May-June) and growth periods (July- September) of smallmouth bass.

Year Period Winter Reproduction Growth NTU mg/1i NTU mg/1i NT mg/1i 1973 2.5 9.5 8.9 47 4.2 29 1974 1.6 18.0 13.3 41 not available 1975 1.6 9.9 5.5 26 7.0 69 1976 3.8 8.7 3.6 71 6.0 39 1977 2.1 5.5 13.5 45 7.4 39 1978 3.3 16.5 8.4 46 11.1 37 1979 2.1 11.1 14.8 99 9.6 54 1980 3.4 12.5 5.2 21 not available Mean 2.6 11.5 9.2 50 7.6 45 2.3-31

Table 2.3-2.

Predicted ronroductive develop-ment and survival success of sm-1lmouth bass in the Missi-sip based on the stae effects.

Nesting Spawning Incubation Fry in Nest 3Blck Fry Growth Summer-inter Year-Class Peak (date) Period Success Period Survival Survival Period Size Su-rvival Rank (date) (days) (rank) (days) (rank) rank (days) (mm) rank 1973 First 5/19 5/24 6 eo 6 Good Good 133 112 Good Good Avernage Second 6/08 6/10 3 Good 4 Good Good .112 100 Average 19t~74 Fr 6/6/3 Below Below Poor 103 107 Averae 4First 60 /0 3 Average Average Weak Second 6/21 6/25 3 Average 4 Avern e Average 79 83 Poor W 1975 First 6/01 6/0446/16/4Ave Average 7 Average rage 118 97 v I..e Av,,;r ~ a NA) 1 First V76 / 5/14 4 Excellent 7 Excellent E'xcellent 132 1' Excellent Dominant 1977 First 5/06 5/11 3 Excellent 6 2xcollont Averaje 138 113 ood Good 1978 First 5/14 5/19 4 Exce1lent 6 Excellent Beo 133 96 Beow Weak Averag~e .Avera ge 1979 First 5/27 6/2 5 Average 7 Good 141 92 B Average Weak Avera4e 1980 First 4/28 5/05 7 Poor 10 Poor Excellent 143 138 Excellent Strong Second 5/15 5/22 3 Excellent r,xcellent Average 126 121 Good m m m m m m m m - - - m

I I

I I

I I

I PfEWL TO IRECTIO14& WIORCEMWg FIf5S