ML20079N189

Lake Norman:1989 Summary - Maint Monitoring Program,Mcguire Nuclear Station:Npdes NC0024392

ML20079N189
Person / Time
Site:	Mcguire, McGuire
Issue date:	12/31/1989
From:	Buetow D, Degan D, Foris W DUKE POWER CO.
To:
References
RTR-NUREG-1437 AR, PES-90-04, PES-90-4, NUDOCS 9111110103
Download: ML20079N189 (122)

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l l TITLE: Lake Norman: 1989 Summary---Maintenan' Monitoring Program l McGuire Nuclear Station: NPDES No. NC0024392 l .

Buetow, D. H., Degan, D. J., Foris, W. J , horton, W. 1.

AUTHOR (S): Lewis, R. E.

18 April, 1990 DATE:

AVAILABLE FROM:

DUKE POWER COMPANY PRODUCTION ENVIRONMENTAL SERVICES 13339 HAGERS FERRY RD.

91122:0103 o,2231 HUNTERSVILLE, NC 28078 SS$7 E" ena (704) 875-5400

L u s 1.AKE NORMAN: 1989

SUMMARY

MAINTENANCE MONITORING PROGRAM McGUIRE NUCt. EAR STATION: NPDES No. NC0024392 DUKE POWER COMPANY Production Environmental Services, TTC/ASC 13339 Hagers Ferry Road Huntersville, North Carolina 28078 e

s MAY, 1990 I

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'd 1.tKE NORMAN: 1989

SUMMARY

Page EXECUTIVE

SUMMARY

i MNS OPERATIONAL DATA Operational Characteristics - 1989 .................. 1 New McGuire NPDE S Permit Thermal Limit . . . . . . . . . . . . . . 2 WATER CHEMISTRY Introduction ........................................ 5 Method s and Ma te ri al s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 Re sul t s and Di sc u s si on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7 future Studies ...................................... 19 Summary ............................................. 19 Literature Cited .................................... 22 Ta bl e s a nd F i g ur e s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24 PHYTOPLANKTON Introduction ......................................., 57 Me thod s and Ma ter i al s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 57 Re sul t s and Di scus si on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 58 Summary ............................................. 63 Literature Cited .................................... 65 Ta bl e s a nd F i g ur e s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 67 200Pl.ANKTON Introduction ........................................ 82 Me thod s a n d Ma te r i a l s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 82 Re sul t s and Di sc us si on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 83 Summary ............................................. 86 Literature Cited .................................... 87 Tables and Figures .................................. 89 FISHERIES Introduction ........................................ 96-Meth od s an d Ma te r i a l s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 97 Re sult s and Di scus si on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 99 Future Studies ...................................... 103 Summary ..................................-.......... 105 Literature Cited .................................... 107 T a bl e s a nd F i g u r e s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 108

o EXECUTIVE SUPMARY This report sumarizes the 1989 results of the Lake Noman aquatic environment maintenance monitoring program, as required by NPDES Pemit No.

NC0024302, for McGuire Nuclear Station (MNS). The overall capacity factor for McGuire during 1989 was 77.1%, in contrast to 77.9% in 1988. Reduced operation of Unit 2 during July, August, and September, plus periodic low-level intake pumping, tended to maintain the monthly average discharge +

tenperature_ well below the 35 C (95 F) NPDES Pemit limit.

Temperature.and dissolved-oxygen data from 1989 were generally within the historic ranges of these variables, in both the mixing and background zones. Specific conductanca and chloride concentrations continued a multi-year trend of increasing values, as in other Catawba River reservoirs.. iron and manganese concentrations were elevated in the sumer anoxic bottom waters. Concentrations of most other chemical parameters (major ions, nutrients, and metals) were within previously reported ranges.

Chlorophyll a and phytoplankton densities and biovolumes often tended to increase from downlake to uplake locations, as in the past, and were usually within the historically documented ranges. Seasonal trends in zooplankton were generally similar to previous years, as were the species ,

composition and relative dominance of both phytoplankton and zooplankton. ,

No measurable changes hne occurred in the Lake Noman fish comunity since McGuire Nuclear Station became operational.. Fisheries ctive rotenone data (species compo*.ition and total standing stock) were similar to results of previous years. Gizzard shad populations have continued to decline at l

Location 4.0 since 1978. Ten striped bass mortalities occurred in late

[ July near the MNS intake, and were likely attributable to the observed l' decline of habitat and the operation of the lower level intake pumps by MNS in late July. Annual ' measures of largemouth bass abundance continue to remain stable, with higher catch rates uplake, as with nutrientr, phytoplankton, and threadfin shad, i

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OPERATIONAL CHARACTERISTICS--1989 The 1989 annual mean capacity factor (CF) for McGuire Nuclear Station (MNS) was 77.1% (Table 1). The yearly mean capacity factor for MNS Unit 1-was 79.11 and for MNS Unit 2 was 75.2%. Most noteworthy was the reduced CF for Unit 2 in July, August, and September. Because of the reduced operation of Unit 2 during these months, the running monthly average discharge temperature was well below

. the.350C (950F) McGuire NPDES thermal limit (Figure 1).

Intermittent withdrawal of cocl water via the MNS low level intake also contributed to reduction of the MNS discharge water temperature. Use of low level intake water for three days of July was associated with a peak demand for electricity, Use of this cool water improved efficiency and;hklped generate additional electrir.ity. Withdrawal of low levei intake water to inprove efficiency of MNS is usually postponed-until late summer or fall, as observed in August and September 1989 (Figure 1). The volume of cool water in Lake Norman is tracked throughout the year to ensure that an adequate volume of cool water is available to comply with both the NRC Technical Specification requirements and the NPDES monthly discharge water temperature limit.

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1-NEW McGUIRE NPDES THERMAL LIMIT ,

The alteration of the MNS themal-limit froin a monthly average distran e water 0 0 temperature of 350 C (950 F) to 37.2 0 (99 F) during July. August, and September of each year was approved in the new NPDES pemit, effective february 1,1990.-

This change will require less use of low level intake water for compliance with the-new thermal limit and : help conserve habitat for cool water fish in Lake No man. - As required by the new NPDES permit for MNS, usage of the MNS mixing zone by striped. bass, a cool water fish, is to be addressed as part of the 316(a) variance for MNS.

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Table 1. Monthly capacity factors (11-for McGuire Nuclear-Station during 1969. Average capacity factors--

were calculated from daily unit capacity factors 4 (Net Generation x-100 / 24 h per day x 1120 mw per unit)-

Month Unit 1 Unit 2 Station

-Average Average Average

January 89.3 99.7 94.5 February 101.9 ,

102.3 s 10'.1 March 22.2 89.6 55.9 April 0,0 79.3 39.3-May 64.3 90.6 77.4 June 97.1 97.8 97.5 July 90.0 10.8 50.4 August 87.4 0.0 43.3_

= September 95.6 28.1 61.8

' october 99.5 100.9 100.2-November 100.4 102.3 101.3 December. 101.0- 75.2 77.1 Annuwl-Average 79.1 75.2 77.1' s

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YeGuire Nuclear Station Discharge Temp and LLI Pump Flow

-300 99- L L

-250 I 97 i

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1. 1 -200 F

E 95 "

M h 0 P 93- " " " -150 W D

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• on 85- i.........,.........,.........i.-,.......i.........i 08/26/89 09/15/89 '0/05/89 06/27/89 07/17/89 08/0b/89 DATE Figure 1. The monthly running and daily average condenser cooling water discharge level intake flow for McGuire Nuclear Station.

temperature and the igw McGuire therinal discharge limit.

• represents daily Horizontal line is 95 F discharge temperature, diamond represents low-level intake flow, and bold lines represent running monthly at . rage discharge temperature.

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LAKE NORMAN WATER CHEMISTRY INT RODL'CTION This chapter of the report describes the water chemistry of Lake Norman during 1989. The objactives of the Water . Chemistry portion of the McGuire Nuclear Station NPDE5 Long-term Maintenance Program for Lake Norman are to:

1) maintain continuity with Lake Norman's historic water chemistry data base at " critical" locations;

2) detect any significant impacts from Duke's operatf ors:

3) document any long-term natural changes in tne chemistry of the lake, which might af fect plant operations;

4) characterire the reservoir-wide thermal and dissolvad orygon regimes of the lake; and

5) compare, where appropriate, these data to other impoundments in the Southeast.

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9 METHODS AND MATERIALS

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The complete water chemistry monitoring program, including specific variables, locations, depths, and frequencies, is outlined in Table 1. r ., N SamplinglocationsareidentifiedinFigureIbT5especificchemical i A _Ry) a methodologies for 1989, along with the appropriate references, are presented in Table 2.

Data were analyzed using two approaches. The first was similsr to that used in the 316(a) report. The sampling locations weie either discussed individually, or the reservoir was partitioned into mixing, background, and discharge zones, and comparisons were made among preoperational and operational years. The discharge is location 4,0; the mixing zone includes locations 1.0, 2.0, 5.0; the backgrnund zone includes locations 8.0, 11,0, 15.0. The preoperational period in this report extends f ro3 j' 1977 through 1981, The operational years include:

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a) the first full year of 2-unit operations at MNS, September 1983 thrcugh August 1984, and a

b) all of 1989.

The second approach, used principally for temperature and dissolved

' oxygen data, emphasized a much broader lake-wide investigation for 1989 and encompassed the plotting of monthly isotherms and isopleths, the determination of the hypolimnetic exygen deficit, and the calculation of specific ' quantitative' thermal parameters such as the maximum heat content and the Birgean heat bucget.

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RESULTS AND DISCUS $10N lemnerature and Dissolved Oxvoen Historic Comparisons Temperature and dissolved. oxygen datt collected in 1989 were generally at or within the historic ranges observed .r each of the specified zones in Lake Norman (Figure's 2, 3, 4, 5, 6). Temperatures greater than historic values (preoperational period through first year operational period, September 1983 - August 1984) were observed in both the mixing zone and the background zones somewhere in the water column in every month except December (Figure 7). Generally, these increase s over historic-values occurred in both :ones and measured s2 *C. Exceptions to this were observed during the fall and winter conling. periods (September, October, January and February) when temperatures exceeded historic values by as much as 5.7 *C, These larger differencas can ce attributed to an earlier fall " turnover" in 1989 and an unusually warm vinter which reduced the rate of water column cooling. Overall, 1989 temperatures in the mixing and background zonas were similar to temperatures rneasured during the previous operational years (DPC 1987, 1988, 1989).

Temperatu a fata at the discharge location in 1989 were within or at the upper end or the historic range for all months except February and August when 1989 values were 4.2 *C and 2.1 *C, respectively, warmer than tne maximum historic temperatures for those months. The warmest I

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discharge temperature of the year occurred in August and measured 32.7 "C. This was slightly warmer (2.1 C) than observed during the first year operational period but well within the range observed during subsequent operatienal years (DPC 1987,1988,1989)

Seasonal and spatial patterns of dissolved oxygen (00) in 1989 were similar to historic patterns in both the mixing and background zones (Figures 5 and 6). In the mixing zone, D0 values were within the historic range for all mont' pt February, April, June, July, October and November (Figur' : *nerally, DO values during these months were only slightly lower (51.0 mg/1) than historic values.

Exceptions to this occurred in July when 1989 values were s1.4 mg/l of the historic minimum, and February when D0 values were s1.7 mg/l of the historic rainimum. D0 values in 1989 were slightly higher (by 1 to 4 mg/1) than the historic maximum in the lower hypolimnion of the mixing zone in October and November (Figure 5).

DO concentrations in the bsckground zone in 1989 t.tre within the historic range for all months except Fd ruary, April, June and July

= (Figure 6). Generally, DO values during these months were no more than 1.0 mg/l lower than observed during the preoperational and first year operationa'l periods. The lone exception to this occurred in February when D0 values were as much as 2.3 rng/l lower than historic minimum. DO concentrations in 1989 for both the mixing and background zones were i similar to values measured during previous operational years (DPC 1987, 1988, 1989) l l

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e DO concentrations in 1989 et the discharge location were generally slightly lower than historic values (Figure 4) but similar to values ebserved in previous operr.tional years (DFC 1987, 1988, 1989). The lowest D0 concentration measured ac the discharge location in 1989 (4.5 mg/1) occurred in July. This was 1.0 mg/l less than the minimum D0 value maasured in the first year operational period but similar to the historic low measurad in 1988 (4.9 mg/1).

Reservoir-Wfd9 Comparisons lhe monthly reservoir-wide temperature and dissolved oxygen data for 1989 are presented in figures 7 and 8. For the most part, the temporal and spatial distributional patterns of both temperature and dissolved cxygen are similar to other cooling impoundments and hydropower reservoirs in the Southeast. Curing the wintor cooling and mixing a terind, vertical rather than horizont al homogencity in temperature predominated, with the shallower eplake ' riverine' rone exhibitina slightly coolet t9mperatures than the deeper downlake ' lacustrine' zn'e (Figure 7). These longitudinal differences in temperatures were clearly illustrated in January and February. The principal factors influent:ing this gradient in Lake Norman are thermal discharges from MSS and MNS, morphometric (depth) differences within the reservoir,and surfar.e water inputs from the upper reaches of the reservoir.

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The beginning of the heating period in Lake Norman generally begins in March, as more heat is gained at the waters surface than is lost at night. During the initial stages of the heating period, buoyancy forces

" smooth out" the horizontal differences in temperature thereby reducing temperature differences between up-reservoir and down-reservoir locations. Due to the vertical instabi'ity of the water column during this period, temperature increases are observed at all depths. These points are illustrated by contrasting the January and February temperature data with the March and April data (Figure 7). As solar radiation and air temperatures increase, heating occurs at a greater rate in the upper waters than the mid and bottom waters. Eventually, differential heating at the surface leads to the formation of the classical epilimnion, meta'imnion, and hypolimnion zones. These zones (strata) are claarly depicted in the July, 1989 data (figure 7).

In contrast to most natural lakes, but not unlike many reservoirs in the Southeast, a distinct thermocline within the metalimnion was not observed in Lake Norman in 1989. Rather, the matalimnion was more or y- less continuous with respect to vertical density differences within the lower water column. and even showed signs of merging with the hypolimnion, as illustrated in the August data (Figure 7).

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Cooling of the water column began in early September as illustrated by decreases in surface temperatures compared to August data. Concurrent with decreases in surface te.1peratures were an increase in the depth of the epilimnion (caused by convective mixing) and a disruption of tha horizontal homogeneity in epilimnion temperatures (caused by reservoir-wide differential heating and cooling, and advective inputs from upstream). Continuation of these differential vertical and horizontal processes led to even more pronounced thermal differences within the reservoir. For example, by October the uplake riveriae zone had already

' turned over' while the downlake lacustrine zone was still strongly stratified. Not until early November was Lake Norman completely mixed vertically throughout the reservoir.

Distributional patterns of dissolved oxygen in 1989 were similar to but not identical to temperature (Figure 8). Gererally, dissolved oxygen concentrations were greatest during the winter cooling and mixing period when biological respiration was at a minimum and atmospheric reaeration was at a maximum. The highest reservoir vide mean concentration of dissolved oxygen (10.8 mg/1) occurred in March when the reservoir

- exhibited a mean temperature of 8.6 C (Figure 7). Unlike the thermal regime, no major longitudinal differences existed in dissolved oxygen within the reservoir during the winter. Not until the lake became I stratified, thereby isolating the metalimnion and hypolimnion from atmospheric reaeration, were uplake-to-downlake gradients in dissolved oxygen observed. Longitudinal gradients in metalimnetic and hypolim-netic dissolved oxygen in 1989 were first observed in May. Differential li

dissolved oxygen depletion and eventual anoxia were first observed in the transitional zone (Locations 15 through 62) where hypolimnetic volume is small, water column and sediment organic matter high, and advective mixing minimal. By August, the complete hypolimnion throughout the reservoir below elevation 217 m was anoxic. This represents approximately 18% of the entire volume of the lake at full pond.

Reaeration of the water column started in September concomitantly with the cooling and mixing of the reservoir. Decreasing air temperatures cooled the surface waters resulting in a convective deepening, aided by wind-induced mixing, of the epilimnion. As the oxygenated epilimnion eroded-progressively deeper into the water column, the width of the anoxic zone decreased. Longitudinal differences in reaeration were also observed and apparently were reisted to differential mixing caused by McGuire Nuclear Station (MNS) and Marshall Steam Station (MSS), upstream advective inputs, and horizontal gradients in photosynthesis (Table 1 Plankton section). Reaeration of the reservoir was essentially complete by early November, except for the bottom waters in the downlake "lacus' rine" zone.

Heat and Dissolved Oxygen Calculations Table 3 pr 3nts some common quantitative limnological calculations for the thermal environment in Lake Norman. Few comparable calculations exist in the literature for reservoirs, but these data are generally within the 'ballpark' of those prasented by Hutchinson (1957) for natural lakes at similar latitudes throughout the world.

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Table 4 presents the 1989 areal hypolimnetic oxygen deficit (AH00) for Lake Norman compared to similar estimates for 18 TVA reservoirs. The data illustrate that Lake Norman exhibits an AH00 that is similar to other Southeastern reservoirs of comparable depth, chlorphyll a status, and secchi depth.

Prectoitation Annual precipitation for the period 1975 through 1989 is shown in Figure

- 9. Precipitation data from MNS (courtesy of PES / Environmental Systems subunit) indicated that the area received about fifty-twa inthes of rain -

during 1989, about 29 % more than during 1988. The precipitation amount during 1989 was relatively high for the fourteen-year period.

Precipitation during 1988 was moderately low for the same period, but rot as low as rainfall during the 1981, 1984, and 1986 droughts.

Turbidity and Soecific Comincians Despite 29 % more rainfall in 1989 than 1988, quarterly turbidity values

" measured at the surface (0.3 m) remained relatively-low (2 to 8 NTU) across Lake Norman during 1989 (Table 5). These levels were similar to Surface turbidity was those reported during 1988 (Duke Power Co._1989).

slightly higher at up-lake Locations 13.0, 14.0, and 69.0 than levels measured in the main-lakt. Bottom (bottom minus ont meter) turbidity levels ranged from 2 to 21 NTU. A trend of increasing turbidity from down-lake to up-lake was also observed in the near-battom samples.

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Specific conductance in Lake Norman during 1989 ranged from a low of 48 umho/cm in August at Location 69.0 to a high of 95 umho/cm in February, also at location 69.0 (Table 5), The annual means of each location were similar; surf ace annual means varied within 4 umho/cm and bottom annual means varied within 7 umhos/cm (Table 5). Quarterly values representing the Cowans Ford Hydro tailrace (16.0), MNS discharge (4 0), lower-lake area (mean of 1.0, 2.0, 5.0), mid-lake area (8.0, 11.0), and area north of Marshall . Steam Station (mean of 15.9. 69.0) generally fell within a range of 60 to 80 umhos/cm, regardless of depth (Figure 10). This range was slightly higher than the range of 50 to 70 umbo /cm observed in 1988 (Ocke Power Co.1989). Specific conductance in surf ace and bottom waters was similar except during the summer ( August), when bottom values averaged about 20 umhos/cm higher than surface values. August was a period of bottom anoxia for locations within and outside the MNS mixing zone in Lake Norman (see Temperature and Dissolved Oxygen section, this chapter). The metals, iron and manganese,were likely released from lake bottem sediment to bottom waters during the summer (Tab'e 5).

Specific conductance contTnued to increase throughout the lake during 1989, as observed in most of the reservoirs in the Catawba River Basin This tr end is most probably re,ated to (Clawson et al. 1984).

l population growth in the watersheds encompassing Lakes No. man, Rhodhiss, i

l and Hickory.

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4 pH and Alkalinity The pH of water in Lake Norman ranged from 6.0 (Location 14,0, surf ace) in August to 8.1 (Location 15.9, surface) in May of 1989 (Table 5),

lhis range was witnin the range reported during 1988 (Duke Power Co.

1989), Bottom pH's averaged 0.4 units lower than surface values. The greatest differences in pH between top and bottom waters, which often exceeded I unit, were observed during the thermally stratified period, May through November, when respired CO 2 was confined to the hypolimnion.

Surface pH's generally increased in an uplake direction except in the Marshall Steam Station (MSS) discharge (14.0) and at location 13.0. The skimmer wall at MSS allows the plant to intake and discharge bottom, hypolimnetic water, and the pH of these waters more closely resembles that of bottom waters in the area.

Alkalinity in Lake Norman ranged f rom 10 mg-CACO 3

/1 (L cati n 69.0, surf ace) in November to 23 mg-Ca r 3

O /1 (L cui n 15.9 bottom) in August during 1989. Alkalinity in bottom waters at det.9 locations (i.e. those greater than 20 m wM ch develop a hypolimnion) increased by 3 to 12

, mg-CACO /1 during August. Such occurrences are well decumented for deep 3

lake systems (Faust and Aly 1981; Stumm and Morgan 1970). Respired CO 2

in the bottom waters decreases pH, which a'ters carbonate-bicarbonate equilibrium reactions to create alkalinity. Surface and bottom annual mean alkalinities were similar among locations throughout the lake (13 to 16 mg-CACO 3

/1), and were similar to the values reported during 1988 (Duke Power Co. 1989).

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Metals Total iron concentrations in the lake ranged from 50.1 mg/l to 2.1 mg/l during 1989 (Table 5). Iron concentrations were usually low (i.e.,50.4 mg/1) in surf ace and bottom waters throughout the lake during the winter, spring, and fall. One exception was a concentration of 2.1 mg/l in bottom water from location 15.9 during November. However, in August iron levels in bottom, of ten anoxic hypolimnetic waters at several locations throughout the lake (locations 2.0, 8.0, 9.5, 11.0, 13.0, 15.9) rose to co.icentrations of 0.7 to 1.8 mg/1, levels in excess of 1 mg/l exceed the currert North Carolina water quality standard for iron (NCONR&CD 1989). Iron levels were within the range of levels histori-cally reported for the lake, including the MNS preoperational period.

Total manganese levels in Lake Norman during the winter, spring, and fall of 1989 usually ranged from 0.01 to 0.2 mg/1, with bottom waters rarely exceeding about 0.5 mg/1. One exceptier was a manganese concentration of 0.86 mg/l'in the bottom water at location 1.0 in November. During August, manganese levels in the bottom, often anoxic hypolimnetic waters throughout the lake (Locations 1.0, 2.0, 5.0, 8.0, 11.0, 13.0, 14.0, 15.9) rose to levels of 0.78 to 2.05 mg/1. Manganese levels observed in the lake during 1989 were within the ranges historically reported.

Aluminum, cadmium, copper, lead, and zinc leve's were monitored semi-annually at selected locations, and their concentrations are given in Table 5. Total aluminum levels remained at er below the ICP 18

IhllIltAll Nutrient levels in Lake Norn 1988 (Duke Power Co.1989).

remained low and were charat status (Rodriguez 1982), N-less than the detection lim-8.0, 9.5, and 15.9, to 382 i 69.0 (Table 5). Quarterly I locations (Figure 12).

Ammonia levels in Lake Norm.

detection limit of 50 ug/l ug/l (Location 15.9) during similar to levels previousi percent of the observations values, were either at or b Total phosphorus concentrat values usually did not exte analytical detection limit 1989, no consistent differe between top and bottom dept from s5 to 19 ug/1. with vt

+

analytical detection Itmit of 0.3 mg/1. Cadmium remained at or below its detection limit of 0.1 ug/l during 1989. Lead levels remained below 2.0 ug/1, the detection limit. Copper levels ranged from 0.8 to 1.6 ug/. .vithin most of the lake (Table 5), with no clear differences among those locations. Copper levels were elevated at location 14.0, the Marshall Steam Station discharge cove (2.8 ug/1), compared to the other locations, but well under the current (15 ug/1) and proposed (7 ug/1) water quality standard for copper (NCDNR&CD 1989). Zinc levels were low throughout ths lake (54 to 8 ug/1), well belcw the State's water quality standard for zinc (50 ug/1).

EDTURE STQQlES No changes are planned for the Water Chemistry portion of the Lake Norman maintenance monitoring program during 1990, 1L. @3 R_Y, Temperature and dissolved oxygen data collected in 1989 were similar throughout the lake to data collected during the preoperational and first through sixth year operational periods of MNS. Temperatures warmer than measured during the preoperational and first year operational periods were observed in both the mixing and ba-kground zones in 1989 but generally were s2 C of the monthly maxima.

Exceptions to this occurred in the fall and winter cooling period when 19

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temperatures exceeded first-year operational maxima by as much as-5,7

'C. These differences were attributed'to an earlierLfall " turnover" in

-1989'and an unusally warm winter-which delayed reservoir cooling.

Overall... temperatures measured in 1989 in the mixing and background zones were within the monthly ranges observed during the second through sixth year operational period. The greatest increase in temperature over that measured during the preoperational through first year.

operational period (4.2 'C) occurred-in February at the discharge l oc a t i on.- The highest = temperature measured in 1989 occurred at the.

discharge location in August and measured.32.7 *C. This was 2.1 'C warmer than measured during the preoperational through first year

-operational period but lower than the operational period high of_ 34.3 'C-

-measured-in 1988. ,

D0 values measured-in 1989 in both the mixing and background zones were i generally s1.0 mg/l of preoperational and first year operational values.

Exceptions to this occurred in July and February when DO values were c

$2.3 mg/l of- the preoperational through first year operational minima; -

however, both July and February values were similar to those measured in-

. 'recent operational years. 00 values-in the hypolimnion of the mixing zone in the fall of.'1989 were 1 to 4.mg/l higher than the preoperational through.fiYst year operational monthly maxima but similar to values measured during the-second through sixth-year operational period. 00

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concentrations in 1989 at'the discharge. location were generally slightly

' lower than measured during the preoperational and first-year operational-period but similar to values measured over the second through sixth year 20

operational period. Reservoir-wide isotherm and isopleth information for 1989, coupled with heat content and hypolimnetic oxygen depletion data, illustrated that Lake Norman exhibited thermal and oxygen dynamics similar to other Southeastern reservoirs of comparable size an ' trophic status.

Most chemical parameters were within the concentration ranges previously reported for the lake during both MNS preoperational and operational years. $pecific conductance, largely due to chloride, continued to a increase lake-wide in 1989. This trend is most likely attributed to population increases and development in the watersheds of lakes Norman, Hickory and Rhodhiss. Iron and manganese concentrations in bottom waters within and outside the MN5 mixing zone were elevated during the summer anoxic period. Bnttom levels for iron during the summer exceeded the NC water quality standard at several locations.

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LITERATURE CITED Clawson, P. A., C. W. Harden, R. N. Keener, and T. J. Bowling. 1986.

Evaluation of historical data on 12 reservoirs in the Piedmont Carolinas with respect to acid rain considerations. PES /84-21.

Duke Power Company, NC.

Duke Power Company. 1987. Lake Norman maintenance monitoring program:

1986 summary. Water chemistry chapter.

Duke Power Company. 1988. Lake No man maintenance monitoring program:

1987 summary. Water chemistry chapter Duke Power Company. 1989. Lake Norman maintenance monitoring program:

1988 summary. Water chemistry chapter.

Faust, S. D. and O. M. Aly. 1981. Chemistry of natural waters waters.

Ann Arbor Science Publishers, Inc. Ann Arbor, MI. 400 p.

Hem, J. D. 1970. Study and interpretation of the chemical C

characteristics of natural water. Second ed tion. U. S.

Geological Survey water-supply paper 1473. U. S. Printing Office.

Washington, DC. 363 p.

Higgins, J. M. and B. R. Kim. 1981. Phosphorus retention models for Tennessee Valley Authority reservoirs. Water Resour. Res.,

17:571-576.

22

Higgins, J. M., W. L. poppe, and M. L. lwanski. 1981 Eutrophication analysis of IVA reservoirs. In: $urface Water Impoundments. H.

G. Stefan Ed. Am. Soc. Civ. Eng., NY, pp. 404-412.

Hutchinson, G. E. 1957. A Treatise on Limnology, Volume 1. Geography, Physics and Chemistry. John Wiley & Sons, NY.

Rodriguez, H. 5. 1982. Reletionships tatween phytoplankton growth rates andnutrient dynamics in Lake Norman, itC. Duke Power to DUKEpWR/82-01. Huntersv111 c. 39 p.

Stumm, ti. and J. J. Morcan. 1970. At.uatic chemistry, an introduction emphasi;ing chemical equilibria in natural waters. W1!ty and Sons, Irc. New York, NY. 583 p.

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1 24

Table 2.

Water chemistry methods and analyte detection litetts for the McCoire Nuclear Station NITE 5 long-ters maintenance monitoring program for I.ake Norman, 1988 and 1989.

Ve e_is*1ta__ Pit ttW Prutnethre Detettfea Ltatt Atlettetty teteI [letteemetetg titeetten te e pH ef S I' e*C I*g* CACO I **

Atwataw' Ateetc cetsston/ICP-direct tajectiea' O.51 58u0, 0 1 og I '

As=nalem Avtemeled cheaste' e*C 0 0$0 e gi *

(ehtee Ateetc abseTttea/geophite fuenece-dietti tejectie=' O 5% Seu0, 0 1 og i

• Ca tc N= Ateetc *=tssion/tCP-dient tajntlea' O 5% toun, 0 0= m -I '

thteefd* A=temeted ferettyeelde' e*t 1.0 og 1

• Coadarteace. spec t f ec Tempeestwee es=pe : ted mittel electeede' la-sttw I w=he-t= '*

torpee Atomic abseert %a/yeechtte fernece-dient tajectiea' 0,5% $880, 0 $ em I '

Ftwee'de hteattemetetJ e*t 0.10m 1

• y I ea Atcmic e=es tea /*CP-dtent tsjett f ea' O 5% lese, 0.3 og 1

• teed Ate =tc abseert sea 9eachtte fweasce-dieert tajntec a' O 51 sese, 2.0 og I-'

Megaes%= Ate =ic cot sstem'ICP-d6ent taject taa' O.51 pese, 0 001 og 1 '

me ageaese Atcott emisstem/ICP-dirert tajectlea' O.52 tou0, 0.003 og 1 '

Witette

• allteate Aetemeted coe'ta= eedvettoa* et 0.050 mg I

• Orthephosphate Aete=eted escorbec add eeductee=, e*C 0.005 og I-*

On gea. dessolved Te=ecestree co=yeauted pek.eegeophic cell' la-stto 0.1 og I **

p89 Te=ecestv e ce=censated elets etntrede' fa-stt, 0.1 std watts

• Phospheevs. total Peeswifate digesttea fellW t- estemeted asce tric acid e*C 0 005 og 1 '**

eedvetten' O 0:5 9 ,3 '**

Petesstwo Ateetc est 5 stoa /ICP-dt**c t lejec tio*' O.5%$80, Sittee 0.6 og I .

Aetemeted molydesttecete* e*C 0.5 og 1.

Sodtw Auste eet ssten/ICP-dient t=Jnttea' O 5% $8'0, 03=11*

$wifete Twebidtertetc. witag a specteephete=et,,' e*C 1.0 mg 1-'

Tempeeatwee 7feeceI stee/t heceemstee* Ia-s1tv 9.1*C*

Iw4totty IIephelemetett svebidttyt 4*C 1 GETts*

lenc _e .*

Ateetc e=tsslee/ICP-dtecct tajn ttea' O 51 seue. % ,9-3 70 eg.I .eg1'.

't899ted States E==teoamratal Pretnt sen Aeeacy 1979. leethods fee cha=# col oestysts of water sad westes.

lavtreamretel ptonttertag and Support lebeestery. Clacteasti. R

'If5fPA. 1982.

• tf5tPA. 1994

• f asteweeat*....

..*........ seasttlet'y s.. used tasteed.of

. deseet ten llett.

_ _ . . _ _ _ . _ - . - . . _ ~~ . _ -_ _ . ___ _ _ _ . _ _ . _ _ _ _ . __ _ __ _._ _ __..._ _ ._

i Table 3. Heat content calculations for the thermal regime in Lake Norman in 1989.

h Maximum areal heat content 27,155 g cal cm-2 Maximum hypolimnetic 13,819 g cal cm'2 [

(below 11.5m) areal heat content  !

Birgean heat budget 18,166 g cal cm"2 Epilimnion (above 11.5m) beating rete 0.137'C day ~I 0.085'C day ~l Hypolimnion (below 11.5m) heating rate t

i 4

e 26

, . . . . , . . , ,-w . _ , _ . - . , , .

.c .- .4 ..< , ,. . . . , , , . , -.-,,, .-.,,..n_,.,.,, . - . . . , , . _ , , _ , ...,.._,,,,.,.,-+.l' ,

Table 4 A comparison of areal hypolimnetic oxygen deficits (AH00), summer chlorophyll a (chi a), secchi depth (SD), and mean depths of Lake Norman and 18 TVA '

rese rvoi rs.

4 AH00 Summer Chl'a Secchi Depth Mean Reservoir (mg-cm~ -day ~ ) (vg-L'I) (m) De h (m)

Lake Norman 0.050 5.0 3.0 10.25 TVA* l Mainstem '

Kentucky 0.012 9.1 1.0 5.0 Pickwick 0.010 3.9 0.9 6.5 Wilson 0.028 5.9 1.4 12.3 Wheelee 0.012 4.4 --

5.3 Guntersville 0.007 4.8 1.1 5.3 03 Nickajack 0.016 2.8 1.1 6.8 Chickamauga 0.008 3.0 1.1 5.0 Watts Bar 0.012 6.2 1.0 73

! Fort London 0.023 5.9 0.9 7.3

Tributary Chatuge 0.041 5.5 2.7 9.5 '

Cherokee 0.078 10.9 1.7 13.9 l Douglas 0.046 6.3 1.6 10.7  !

Fontana 0.113 4.1 2.6 37.8  :

Hiwassee 0.061 5.0 2.4 20.2 j Norris 0.058 2.1 3.9 16.3 i South Holston 0.070 6.5 2.6 23.4 Ties Ford 0.059 6.1 2.4 14.9  !

Watauga 0.066 2.9 2.7 24.5 r

• Data taken from Higgins et al. (1980), and Higgins and Kim (1981) l i

r

1 s

Page I of 4 i

Table 5. . . Quarterly near-surf ace (0.3 m) and .near-bottom (bottom minus I m') water chemistry for the Cowans. Ford Ilydro tailrace and Lake Norman locations during 1989. .The syStbolo " < " ,

indicates a value'less than the analytical detection limit.

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32

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Figure 2. Maximum (right solid line) and minimum (left solid line) monthly neon temperature profiles in the McGuire mixing zone (locations 3.0, 2.0, 3.0, 4.5, 5.0, 6.0, 7.5) ob-erved daring the preoperational period 1977-1981. Also depicted are the swan ptofiles for the period September 1983-August 1984 (*;

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56  ;

PHY10PLANKTQS INTRODUCTION Phytoplankton population parameters were monitored in 1989 in accor-dant.e with the NPDES permit fo. McGuire Nuclear Station.

The objectives of the phytoplankton section for the Lake Norman Maintenance Monitoring program are to:

1. Describe quarterly patterns of phytoplankton standing crop and species composition throughout Lake Norman, and

2. Compare phytoplankton data collected during this study (February, May, August, Nove:uber 1989) with historical data collected du-ing these months.

Previous studies on Lake Norman have reported considerable spatial and tempora'. variability in phytoplankton standing crops and taxonomic compt -ition (Duke Power Company 1976, 1985; Menhinick and Jensen 1974; Rodriguez Rodriguez (1982) classified the lake as 1982).

oligo-mesotrophic based on phytoplankton abundance, distribution, and taxonomic composition.

METHODS ASO MATERIALS Quarterly phytoplankton sampling was conducted at Locations 2.0, 5.0,

8. 0, 9. 5, 11. 0, 13. 0, " ^ and C5.0 (Chemistry, Figure 1). Duplicate composite grabs f rom .4, 4.0, and 8.0 m (i.e., the euphotic zone) were taken at all l oc a t i or. s . Sampling was conducted on 27 February, 57

23 May, 23 August, and 10 and 28 November 1989. Standing crop (densi-ty and blovolume) and taxonomic composition were determined for samples collected at Locations 2.0, 5.0, 9.5,11.0, and 15.9; chloro-phyll A concentrations were oetermined for samples from all locations.

Field sampling methods, and laboratory methods used for chlorophyll, standing ciop, and taxonomic composition determinations were identical to those used by Rodriguez (1982).

Chlorophyll A data for February, May, August, .nd November 1989 were compared with historical data beginning in 1975. Density and biovolume data for 1989 were compared to data collected beginning in 1978.

RESULTS AND DISCUSSION 11andina Cr.gp Phytoplankton chlorophyll A values in 1989 ranged from a low of 1.82 3 3 mg/m at Locaticn 15.9 in February to a high of 13.98 mg/m at Loca-tion 69.0 in August (Table 1). The yearly lows for both total densi-ties and biovolumes occu. red at location 2.0 in February (397 units /ml and 261 mm j,3 3

, respectively). The yearly highs for both total densities and biovolumes were observed at Location 15.9 but on differ-ent months; ln August (10,247 units /ml) for densities and in February (5,300 mm 3 /m 3 ) for biovolumes (Tables 2 through 5).

Chlorophyll A values demonstrated a trend of increasing-concentrations from downlake to uplake locations during August and November and total 58 e a

densities and biovolumes showed this trend in February and August (Figure 1). Similar trends of increasing standing crop values from downlake to uplake locations in Lake Norman have been observed in previous Duke Power studies (Duke Power Company 1976, 1985; Rodriguez 1982). However, there were also exceptions to this trend in 1989.

Chloroptyll A values at Location 69.0, the furt hest uplake location, were lower than midlake locations during May and November, probably due to the more riverine character of this location. In February, chlorophyll a values were generally lower uplake than downlake. This trend was opposite of that observed for total densities and 3 3 biovolumes, where the biovolume estimate of 5300 mm /m at Location 15.9 was over three times that for any location during the year. The only parameter which consistently showed an increase f rom downlake to uplake each month was seston dry weights (Figure 1).

Phytoplankton standing crop values during 1989 in general were similar to those observed during the same months of the preoperational and operational periods (Figures 3 ind 4). ChloropFyll a values during February 1989 at uplake locations were slightly lower than previous years while values at downlake locations during May were slightly higher. Total densities and biovolumes, due to high populations of Melosira ambioua, at Location 15.9 in February were higher than previously recorded. This may be dt.e, in part, to warmer temperatures observed in February 1989 es cenpared with past years (Chapter 1) which could trigger an earlier onset of the spring diatom pulse. High populations of Melosira uplake in Lake Norman during earl.v yring are V

not unusual. With the exception of Location 15.9, total biovolumes 59

decreased slightly overall at most locations during all periods of 1989 compared with 1988. lotal densities also generally decreased in February and August compared with 1988 Pnd were mixed in May and Hovember. No consistent trends of densities. or biovolumes were identified at any location throughout the study period possibly due to the variability of standing crop parmeters recorded during previous years and the lack of historical data from Locations 9.5 and 69.0.

Community Comoosition Ten classes comprising 90 genera and 226 taxa of phytoplankton have been identified from samples collected o r, Lake Norman since the Maintenance Monitoring Program was initiated in August 1987. The distribution of species within classes was as follows: Chloroph) aae, 113; Bacillariophyceae, 45; Chrysophyceae, 20; Haptophyceae and Xanthophyceae, 1 each; Cryptophyceae, 7; Myxophyceae, 26 Euglenophyceae, 6; Dinophyceae, 9; and Chloromonadophyceae, 3 and 1 Unidentified taxon (Table 6). Thirty-five taxa have been identified during the Maintenance Monitoring Program which were not recorded during previous studies (Duke Power Company 1976, 1985; Menhinick and Jensen 1974, Rodriguez 1982).

The seasonal ' succession . of phytoplankton in Lake Norman in 1989 is presented in Figure 2. Lower lake lucations (Locations 2.0, 5.0 and 9.5) were combined as their composition was very similar. The major classes cu ing February, in terms of density, were the Bac111ariophyceae (diatoms), followed by Chlorophyceae (green algae) and Cryptophyceae - (cryptophytes). During May, the chrysophytes were 60

most important at downlake locations (Loc. 2.0, _ 'd.0 and 9. 5), while cryptophytes were dominant midlake at Location 11.0 and codominant with blue green algae uplake at Location 15.9. Diatoms and green algae were also important numerically at all locations in May. In August, the green algae were the most abundant class a+ all locations followed closely by chrysophytes at downlake locations and blue green algae at Location 15.9. Diatoms and cryptophytes were also important.

In November, green algae, diatoms and chrysophytes were almost equally abundant at all locations. Cryptophytes were also important at Location 2.0 in November. Over111, the seasonal composition of the phytoplankton community in Lake Norman during 1989 was very similar to previous years.

In terms of biovolume, the diatoms dominated samples during all periods except August, when the Dinophyceae (dinotlagellates) d:minat-ed phytoplankton biovolumes at downlake locations. This is similar to the taxonomic composition observed during February, May, August, and November of the pre. operational and operetional periods and in 1988.

High densities and blevolumes of blue green algae were observed bt

~

Location 15.9 in 1980 as in 1988. Blue green algae comprised more than 20% of the total density and blevolume at Location 15.9 during both May and August whil.: not comprising more than 16t, of the density or biovolume at any other location during the year.

i' Major species of phytoplankton (>5% of the to;al density or biovolume) observed during 1989 are presented 50 Tables 7 and 8. Species compo-sition among phytoplankton samples collected during 1989 was generally f

61 i

\

I similar to that observed for samples collected during 1988 and the preoperational and operational periods. Melo11a anbigua, a centrate diatom, was an important constituent of phytoplankton assemblag3s during all sample periods especially during February and November.

During February, it comprised mors than SCt of the biovolume at all locations except 11.0. Cyclotella comta, a diatom species prtviously unreported from Lake Norman, was dominant in the biovolume at downlake locations during May (Figurt 5). This taxa was checked with a second analyst and a specimen has been sent to our diatom consul' ant, Dr.

Charles Reimer, for confirmation, it is also possibi that this species has been previously observed in Lake Norman but o..ly identi-fled to genus (J. Derwort, pers. comm.). Cyclotella cata is a common component of plankton in lakes throughout the world (Sin-Hole it al.

1985; Koussouris 1978; Maruyama 1988; Munawar et al. 1988). Van Donk et al, (1988) f ound that C2G10Rlla rampif, became dominant in late spring (May-June) when contentrations of phosphorus were decreasing.

BhodagnL5 minuta, a smail cryptophyte, was again a numerically abundant taxe observed at locations on Iake Normar. throughout the 1939

= .

n.onitoring study although it never comprised a large portion of the biovolume, Several dif f erent corysophyte tara were important in 1989 compared with previous years. Taphrion spp. was the dominant taxa at downlake location., in May, unidentified chrysophytes were important at all locations in August, and, in November, Qchromonas spp. was impor-tant numerically and lynEA uvelle was an important part of the biovoume at most locations. G re e n a l g a l t a x a , A n k i .s.tI_Q.dnttui 151LitR$

v. tniabilis, Ant. spiralis , Cosmarium spp. and coccold greens were i

62 I

l

numerically import &nt components of phytoplankton assemblages during all periods. AnkistrodeJmg3 soiralis was the numerical dominant at Lccation 15.9 in August with 26.8% of the total density. Blue green algal taxa were important at Location 15.9 with Oscillatoria - spp,

. comprising mote than 30% of the total density in May and Raphidionib gyryala accounting for over 15% of the phytoplankton density in August. Dinoflagellate taxa, primarily several species of Peridinium.

were important components of the biovolume at downlake locations during al1 periods except November. As mentioned last year, Melosira figlirJL and M italica v. tennuissima are now being recceted as titlosira AthlauA accordiog to Dr Charles. W. Reimer of the Philadelphia Academy of Scier.ce, t

10MMARY Phytoplankton sampling was conducted at locations 2.0, 5.0, 8.0, 9.5, 11.0, 13.0, 15.9, and 69.0 on Lake Norman in February, May, August, and November 1989. Chlorophyll A analyses were performed at all loca-tions, while standing crops and taxonomic composition were determined at Locations 2.0, 5.0, 9.5, 11.0, and 15.9.

Phytoplankton stcnding crop values (chlorophyll A, total densities and biovolumes) during '1939 were usually withia the ranges of those observed during the same months of previous w ars. Exceptions includ-ed higher thto usual densities and biovclumes at location 15.9 in February 1989, which coulo be due to warmer temperatores than in previous years bringing about an earlier onset of the typical spring 63

• - ~- , r- + + ,

. (

numerically importa rJ. components of phytoplankton assemblages durir.g all periods. Ankistrodeimus soiralij was the numerical dominant at Location 15.9 ia August with 26.8% of- the total dens, ./. Blue green algal taxa were important at Location 15.9 with OscillatorJa spp.

comprising more than 30% of the total density in May and hphtdigntis curvata accounting for over 15% of the phytoplankton density in August. Dinoflagellate taxa, primarily several species of Peridinium, were important components of the biovolume at downlake locations duritc all periods except November. As mentioned last year, Melosira italica and M. jtallca v. tennuissima are now being reported as klosira ambiava according to Dr Charles W. Reimer of the Philadelphia Academy of Science.

SUMMARY

I phytoplarikton sampling was conc'.-ted at Locations 2.0, 5.0, 8.0, 9.5, 11,0, 13.0, 15.9, and 69.0 on Lake Norman in February, May, August, and November 1989. Chlorophyll A analyses were_ performed at all loca-tions, wl.ile standing crops and taxonomic composition were determined at Lo.ations 2.0, 5.0, 9.5, 11.0, and 15.9.

Phytoplankton standing crop values (chlorophyll 3, total densities and biavolumes) during 1989 were usually within the ranges of those observed during the same months of previous years. Exceptions includ-ed higher than usual densities and biovolumes at Location 15.9 in February 1989, which could be due to warmer temperatures than in previous years bringing about an earlier onset of the typical spring 63

-~ - - - _ . - . .. .- -

pulse of diatoms. Phytoplankton stancing crops generally showed a trend of increasing values f rom downlake to uplake locations during most months except May due mainly to large populations observed at Location 15.9. This trend was also observed during previous stuoles on Lake Norman.

Phytoplankton taxonomic composition during c,onths sampled in 1989 was generally similar to that observed during these same months of previ-ous studies, with diatoms. cryptophytes, chrysophytes and green algae the most abundant forms. Blue green algae were not an inportant part <

of the phytoplankton community except uplake (Location 11.0 and 15.9) during Mt4y and August. Olatoms (primarily tielosira ambigua) dominated phytoplankton biovolume in all months but August, when dineflagellates (mostly Peridinium species) were dominant. Major species observed during 1989 were similar to those observed during previous studies.

Cvelotella getA, a planktonic diatom species previously unreported from Lake Norman, dominated the biovolume at downlake locations in May. This species is a common component of plankton assemblages throughout the world and may havo been previously only identified to genus in Lake Normen.

64

, _ ~ . _ . . _ . __ . . - . _ _ _ _ _. _ .. _ _ __. . _ _ . -.. -. _ . .

LITERATURE. CITED

Bin-Hole, R. , Pont, D. 'and A.' Vaquer.1986. Spatial distribution of phytoplankton in the Sainte-Croix _Reservior, France. Sci. Eau. J.

Wate r Sci . , Vol . 5, No. 1, pp. 101-115. ' .

~ Duke Power Company. McGuire Nuclear Station, Units 1 and 2. Environ-mental Report, Operating -License Stage. 6th rev Volume 2. Duke - ,

Power Company, Charlotte, NC. 1976.

Duke Power _ Company. McGuire Nuclear Station, 316(a) Demonstration.

Dtke Power Company, Charlotte, NC. 1985.

Koussouris, T. S.-1978. Plankton observations in three lakes of western Greece. Thalassographica, Vol. 2, _ No.1, pp.115-123.

- - Maruyama, K.1983. Spatial differences in Cvelotella conta populations in the Nishina-Sanko Lakes,.Nagano Trefecture, Japan. Jpn. J.

Phycol. Vol. 36,-No. 2, pp. 154-165.

Menhirick, E. F. and L. D. Jensen. Plankton populations, p. 12J-138 In.

- L. D. Jensen-(ed. ). : Environmental- responses to thermal- discharges from Marshall Steam Station,-Lake Norman,1Noth Carolina. Electric L 1 Power Research Institute, Cool _ing Water Discharge Project (RP-49)-

=-

L Report No. 11. ' Johns Hopkins Uni,ersity, Baltimore, MD, 235 p. ,

E 1974.

Munawar, M. et al. 1988. Phycological studlei in the North Channel,.

Lake Huron, Canada. Hydrobiologia, Vol .163, No. O, pp.119-134.

' Rodriguez, M.' S. Phytoplankton, p. 154-260 in J. E. Hogan and W. _ D.

-Adair (eds.). Lake Norman summary; Technical Report DUKEPWR/82-02 t

Duke Power Company, Charlotte, NC. 460 p., 1982. ,

(

65 L

L h

.a. Y- _ - , , . - . . . . . - , , . . - , - _ . ~ , - . . . . .,. , , - - ~ a.- n- ..n

Van Donk, E., Veen,_A. and J. Ringelberg. 1989. Natural community ,

bioassays to determine the abiotic factors that control phytoplankton growth and succession. Freshwater Biol. Vol. 20, No. 2. pp. 199-210.

e M

66

+fd Table 3. op Phyg/m}anktentotaldensity(units (mm ), as well as major class densities /ml),andblevolume ard biovolumes, and percent composition (in parenthesis) at each location for samples collected on 23 May 1989.

Locations Parameter _2 d_ _LQ_. _LL ILQ_ IL1, Total density 1,492 2,05C 1,a74 1,936 2,898 Chlorophyceae 193 214 255 317 362 (12.9) (10.4) (17.3) (16.4) (12.5)

Bac111ario- 354 366 338 299 305 phyceae (23.7) (17.8) (22.9) ( 15. 4 ) (10.5)

Chrysophyceae 678 1,160 460 205 173 (45 4) (56.4) (31.2) ( 10. 6) (6.0)

Cryptophyceae 222 189 297 697 927 (14.9) (9.2) (20.1) (36.0) (32.0)

Myxophyceae 8 8 17 340 955 (0.5) (0.4) (1.2) (17.6) (33.0)

Others

• 37 119 107 78 176 (2.5) (5.8) (7.3) (4.0) (6.1)

Totsl biovolume 797 822 759 972 1,037 Chlorophyceae 20 36 43 38 37 (2.6) (4.3) (5.6) (3.9) (3.6)

Bacillario- 497 435 438 592 423 phyceae (62.4) (52.9) (57.7) (60.9) (40.7)

Chrysophyceae 159 217 79 42 70 (20.0) (26.4) (10.4) (4.3) (6.8)

Cryptop'hyceae 79 55 76 180 161 (9.9) (6.7) (10.1) (18.5) (15.5)

Myxophyceae 7 4 22 106 228 (0.9) (0.5) (2.9) (10.9) (22.0)

Others 33 75 101 14 118 (4.2) (9.1) (13.3) (1.5) (11.3)

• = Haptophyceae at all locations; Dinophyceae at all locations except Location 11.0; unidendified taxa at Locations 11.0 & 15.9 69

Table 2. op Phy}/m}anktontotaldensity(units (mm

/ml),andbiovolume

), as well .5 major clahs densities and biovel;mes, and percent composition (in parenthesis) at each location for temples collected on 27 February 1989.

Locations Parametu . 2. 0 i q. 9.5 11.0 15.9 Total density 397 413 546 1,012 4,809 Chlorophyceae 116 160 232 392 501 (29.2) (38.7) (42.5) (38.7) (10.4)

Becillario- 179 178 205 303 3,121 phyceae (45.1) (43.1) (37.5) (29.9) (64.9)

Chrysophyceae 15 21 34 66 186 (3.8) (5.1) (6.2) (6.5) (3.9)

Cryptophyceae 62 35 42 148 815 (15.6) (8.5) (7.7) (14.6) (16.9)

Myxophyceae 16 2 2 33 37 (4.0) (0.5) (0.4) (3.3) (0.8)

Others

• 9 17 31 70 149 (2.3) (4.1) (5.7) (6.9) (3.1)

Total biovolume 261 292 355 528 5,300 Chlorophyceae 10 10 15 25 37 (3.8) (3.4) (4.3) (4.6) (0./)

Baci11ario- 173 223 251 24d 4,102 phyceae (66.2) (76.3) (70.5) (46.2) (77.4)

Chrysophyceae 7 5 6 13 55 (2.7) (1.7) (1.8) (, 4) (1.0)

Cryptophyceae 45 9 11 63 617 (17.3) (3.2) (3.1) (12.0) (11.6)

Myxophyceae 6 4 1 2 1 (2.5) (1.2) (0.1) (0.4) (0.0)

./ Others 20 41 72 181 (88

"' (14.1) (20.2) (34.3) (9.2)

(7.6)

• = Includes primp.ily the Dinophyceae, which were found at all locations; and the Euglenophyceae, which were found at Lucation 5.0.

68

a Table 5. Phy}cp}ankton total density (units /ml), and biovolume (mm /m ), as well as major class densities and biovolumes, and percent composition (in parenthesis) at each location for samples collected on 10 and 28 November 1989.

LKILt10A1 brneler _LO_ _5JL .JLL LIL EL

, Total 1,893 2,575 density 1,385 1,720 2,162 690 649 743 789 Chlorophyceae 250 (18.1) (40.1) (30.0) (39.2) (30.6) 329 595 329 626 Bacillario- 483 phyceae (34.9) (19.1) (27.5) (17.4) (24.3) 175 551 448 580 Chrysophyceae 300 (21.7) (16.0) (25.5) (23.6) (22.5) 295 135 99 229 354 Cryptophyceae (21.3) (7.8) (4.6) (12.6) (13.7) 45 267 230 70 115 Myxophyceae (3.2) (15.$) (10.6) (3.7) (4.5) 38 66 111 Others

• 12 24 (0.9) (1.4) (1.8) (3.5) (4.3)

Total 1,029 662 402 811 752 biovolume 42 39 63 74 Chlorophyceae 16 (2.4) (10,5) (4.8) (G.3) (7.2) 494 219 490 230 473 Batt11ario- (i;6. 0) phyceae (74.6) (54.6) (60.4) (30.6) 48 116 216 201

• ysophyceae 60 (9.0) (11.8) (14.3) (28.7) (19.5) 23 18 71 83 Cryptophyceae 67 (9.6) (5.8) (2.3) (9.5) (8.0) ,

54 51 2 12 Myxophyceae 19 (2.9) (13.5) (6.2) (0.3) (1.2) 16 98 170 186 Othars 3 (0.4) (3.9) (12.0) (22.5) (18.1)

• = HP_otephyceae at al' locations; Dinophyceae at all but locations 2.0 and 5.0; Euglenophyceae at locations 5.0,11.0 and 15.9.

71

Table 4. Phyt3 0p}anktontotal_ density (units /ml),andbiovolume

(%m /m ), e well as ma.jor class densities and biovolumes, and percer., ..omposition (in parenthesis) at each location for samples collected on 23 August 1989.

Locations 11.0. 15., 9 ..

Parameter 2.0 5.0 SJi.

Total 2,168 10,247 density 1,139 1,327 1,995 532 654 679 3,885 Chlorophyceae 386 (33.9) (40.1) (32.8) (31.3) (37.9) 239 308 427- 691 Baci11arlo- 287 phyceae (25.2) (18.0) (15.4) (19.7) (6.7) 300 245 635 486 1,663 Chrysophyceae (26.3) (18.5) (31.8) (22.4) (16.2) 200 181 288 1,131 C ryptophycSae 91 (8.0) (15.1) (9.1) (13.3) (11.0) 55 127 189 2,798 Myxophyceae 21

( 1. 8.1 (4.1) (6.4) (8.7) (27.3) 56 90 99 79 Others

• 54 (4.7) (4.2) (4.5) (4.6) (0.8)

Total 1,486 732 885 497 973 biovolume 103 96 64 291 Chlorophyceae 129 (17.6) (11.5) (19.3) (8.6) '.19. 6 )

204 162 218 276 Baci11ario- 202

. phyceae (27.6) (22.9) (32.6) (22.4) (18.6) 67 82 76 219 Chr>sophyceae 111 (15.2) (7.6) (16.6) (7.8) (14.8)

S4 37 48 212 Cryptophyceae 36 (4.9) (10.6) (7.4) (4.9) (14.3) 30 43 51 353 Myxophyceae 2 (0.2) (3.4) (8.5) (5.2) (23.7) 253 390 78 497 135 Others (34.6) (43.9) (15.6) (51.0) (9.1)

• = Dinophyceae and Unidentified at all locations; Euglenophyceae at location 15.9.

70

-. _, . _ .._. _ - . _ _ _ - > .. -. .~ . _.. _ __ _~ - - .

j Table 6.- (cont.)

NYuoPHYCIAt feetla gaingirigDR,fJ (Cabejssetourw) toerror f raatlaria erotarensis Kitten AnnanelM =* hist 4tatJa treMesan Annamena wisc.enalmeng Prescott

• frustutte 1_ .!R.1 (threrters) Detont 8. app. Bory

• Mientra amt pm (Gristou) 0, so.itter 6teerstis tverte brouet ard Deity 8, distans (threrters) Kuetal;g 8 1DERI13 Drouet ord Deity

3. gjg gg v. alaiunna Gr eow 6. app.Meneghtml

. g warylata (threreorg) talfs ' threncaccus tianaticus Lesmennen

3. ararwtata v. annusticates steelle-

• G. 3M EC tuottiry

3. igligg (thre w arg) Eustrinp #segeti

8. app. Agordh

• E'm'8Pa Ge pandaaria iacuntrie Chodet mayfcule app. h ep. Agert!h attzachie ac1 cuter {s (Kuet ing) W. taith

t. m a iita L anclia austedt + glitasy.alla man afnana t wt:Ing g, helAa1113 watedt Onchtatarla meninata Neneghini P. 3133 (Kuetting) W. Smith *

• g. atelinearia Nuotedt 9. itenstica Leonorman

9. app. Vmacher

3. esp. Norsett Phorsidium answtisslaus Rhlzmastarda app. Ihrertorg R. tpp. Ewiting

8. gfjjggj" N. L. Smith Ranbidionais curvata Fritsch I klch Italatansas acteqas (Wher) Nesle Steeanadtscus sp. Ehrertorg Unidentf fled htw. green filements h ,3 gng Eusttirg (WGLENOPM C AE

1. gigt.1. antes thr**ers inaltos e m threremrg

1. D e sua sustaltw . -

• Lagdglig app. Perty

3. m v. fraattLeiolden Grunow flatWe laring (Lema.) Skvorttow

1. m v. scotica Grwtow

• Trachettmanas acanthostems (Stokes) Def terdre

}._ girg (ultisch) threreorg 1. mulcherrima Playfetr 3 30. A 1.velvocinathrereorg

~3. epp. threreorg. .

iabetteriaigrggtg313(Lyrgby)Kueting DlWW#fMAt

1. flocculcan (Roth) Kuetting Egfat!)g birweilnetla (Weller) Schrer*

..Unidenttfled centrate dietens

• Gtenacinfo batsai (Lemerman schitter G. g!!!D911013e Perord '

CHRYS&WYGAt themmatins app, tiermouski G. gg 1 1tg hchittfrg Dinabryon havarie w feeof Pericinie acicut iform Launennen

~

t.1DESCVdShag Lessorann R. df wrmens 1. aus!'.tw (Pemord) Lemieriaan g, aartut erla threreerg 2 3.tagjegit M g Eddy R. app, threreorg f,,. e;p. thrercerg

• greligig s h oicitinte Skuja L. en.

Kanhvrim rtbi ktaus11,1 tenrod CMLOR3eCNAD & MYCtat

.* Gorivostimp eenres#w (tedert;cene) Lammerman E. app. Pes,cher s ggl,t M M Lg Iwenoff

• G. 13163 1wano#f

9. sw. Deleine L smedacoronate Prescott L tartyrsta lelling Unidentified fleg6er.es

3. app. Perty -

Octim1, opp. WenotIki +* het recorded f rom previos studies, tatt blores have been -

• thhechrvain opp. Pascher e- observed uplete outs'Je annitored erees.

Statenanones dichottena lectey Jggg teinona Korshikov

1. wette threreorg a uroatenmais enseicme (Cetk) tesourman Unidumtifled enryeopmytes i ' NAPTOPHYCEM. .

I ChrvanchreamJtIna ggtyg Lockey RANTNWHYCEAt pichotomacoccus sm. Korshitov CeYPTOPHYCEAt ggr%'M RI2Sg th.*ertorg

• E. marsontt Staje i

G. gyls throwert G. gtgg.gg.igt Skuja E. rettw e Stufe G. em. threreers Rhocknenes 31rW13 Skujo t'

73

~ . . - .

Phytoplankton taxa identified from Lake horman samples Table 6. . collected in August and November 1987 and Februarys May.

- August and November 1988 and 1989 (*ataxm not recorded in previous Lake Norman studies). l I

l CMLOROPWY2At Actinastra tiarmachil tagerheim - . shtun e Lucks.

. Igigg (Ihrerterg) eetfa Ansiatranansa 13153343 (Corien) eetfs ..Jgitas v. tetranen (Cords) Retts

6. falcatus v. airantita (Cords) telfs . lartteessinata antatimas G. N. Smith A. falcate v. 1 3133 (West & West) 6. A. West hagrigdg tacustria (Chocht) C. M. Smith g flaitomia Core aerou KerW4er he'iemmina gm (Elechner) Chodet

' 6. astratta (fumer) Louimerson ), gDwglang v, anymantrica (Shroeder) G. M. $sith Arthrmanaeus 1 3 3 (Greb.) Nesse((

• 1. stuulans v. brevicasta G. M. tmith

• Cartaria f rinachH 18kede 1. acminatus (Legereets) Chodet

' g. app. Diesirig 3.g[Mhgv.bisptus(G64tlettPrinta)Chodet Charactus opp. 1. glhas (Turpin, Legerheim Chtammamaansa om. (hrertiers - 1. glyg vi gligygg (Reinsch) Werngirg Chlor mant s a m . threnberg 1. tamtteutstum Legeehele Clestteieenia itriniasima 3. giggghg (Turpin) Kuetting 512sterialsta friettaiPing. ffwica West & West 1. R giasautatus Closter' s incurv e Brettesen 1. m adricauda (Turpin) Grebissen clostect s apo. Nittsch IggDessga ear.

Cagtestem canaricw Archer naianantnr3 quinute (meeeeti) Cottlns

• Cassierte arsiutama vi concirne (naher*orst) West & West 1. genil G. m. smith G. anaheare m or e v. atrines e norsteet igespracratin assireeteri Choset

• g, contract e strchner screarozoama tranulata soy & stiss

• G. antynore (knogell) Archer flavr.salta ausricarse (West & Wst) C. M. tutth

• g.1stna Archer 1. anicytste treetss vi

• g. th cts Lurusett i

• 1. brevisoirun Brebissers

[. opp. Coren

1. curvets v. sleimate G. M. Smith trucimenta cruelfera (Wolle) Collins

• 3. gunotdatum BreDteson E teraeutere Wttle 1. testects erobisson C. tetraments (Kirchner) Wet & West

• 1. gislan v. rhanhof dre West and Wst D!ctroamegr.tm ehrenharnia'w Neogeti E. Editt.l.Lg Wood L. am* etatil v. ftwinanne Schm acher itakatstheta antatinost Witte 1 arascant'ne Lu:'iestl tauastre spp. thromerg 1,neramme

• hasortna ajammu thromere 1. naraansi.sn v. cirMw West & West I. naraanne v. gary m W. West f rarrete droescheri (Leseneren) G. M. Setth

• 1. suncruciate Coose & Wille

1. gy,3111 (f rance) Lennerson I, tetraterm notfs Glee 0CYstin Dt arttonica (West & West) lanternen

• 1, lwrggggggg Denot

g. ainap (Kuetting) Lagerheim Stauraast a sp .

G. sep. meegeti

• IA11gggf,gD gr,1.h,.rodameHorne v. contorta Wotostynske GotenLinia anziscina West & Weat 14 33 331 3 (Corde) Hanseirg G. Lag!A1.3 (Choest) Witte . . . catalate v. lonalamirun Lennernen

$g],13 acciale (Dujer.) Warm. .

. Pinuse (A. Braun) Mansf ir0 -

Kirchnertella ggtetta ($cheWej 8.tilin

• 1. mJtic@ (A. Brem) Wensgirg

1. Imarts (Kirchner) Nomb. Dentaedric e West and West

1. m (W. West) Schnidte .. . reauta*e

. L Shgastitseia G 5. West . tenutare v. 1De n falling

5. 'sp. Ich*'8'8 I. s m . Kustning

• Lamerhella til.f au. (tsperhete) Chodet Trueberte setine7 ( Archer) G. m. Smith L. Laratang (w-weruan) Printa Westetia linearjn G. M. Smith L. madette's (Loes.) A M. salth Coccotd greens L. 3g313 Lommereen ngsentiana yig13 Leutertiorn - 5ACILLAnlW M MAE Bigfactinis matite f resenius Achnenthes microcambala (Kuetting) Grmow B9c( aaftidim snailhan Print 8. epp. Sory ,

thauotta alarmate (Agerc81) Wittract Annnesonia yj,ttag (Gemow) noss E. opp. (agerdi) Wittrock Astertorwlla forgest Nessett tembrogvti m anartigge anageli Attweva tachariasi J. Brm i

• 3. iisiett; g (G. m. smith) 5. W. Smith Coccorv!s etscentute thromerg .

• Dotystta tMyntIca W. West

• Custotet to gEr42 (Ehr.) Kutt.

g. (acus c Chosest g4 lumrenMntare Kustning g , gry.g West & West' g4 neemstet t teera Mustedt

~

g. aus*tta Monnaire g. 13.elliners (Cleve) van Nuerck Parerina charkowiersit torshikov L s m . Eutt.

E. Ette (Nuott.) scry i n g dj thralda Gregory Pediastry biratiate 16eyen E. amtes meyan

s. sm.- Asere 72

l Table 8. Biovolumes (nn)/m2) and, in parentheses, percent composition of-major taxa (>5%) of phytoplankton collected at locations in 1.ake Norman, NC during February, May, August and Ncvember 1989, mejor f ame

• Slovotees Locrtions 2.0 5.0 9.5 11.0 15.9 fame s4/%3 1 mg/m3 1 mg/m3 1 se/m3 1 se/m3 1

-esseeeeeeeeeeeeeeeeeeeeeeeeeeeee............................ .eeeeeeeeeesseessessesseessneesesse ......e February motostre selgue 132.4 (50.7) 196.5 (67.3) 218.2 :61.4) 163.3 (31.0) 3926.2 (74.1) met. distens v. atpleena 16.2 (5.8)

Cryptomanos reftene 32.4 (12.4)

.. Cryptomones erose 43.6 (8.3) 292.1 (5.5)

Peridinfue inconspicaan 27.0 (9.2) 27.4 (7.7) 85.9 (16.3)

P. pasit tun 44.3 (12.5) 70.7 (13.4)

,,y ..............................................................................

Attheye techerieel 55.4 (7.0) 56.3 (6.9) 316.9 (32.6) 57.0 45.5)

Cyclotelle compte 216.6 (27.2) 188.8 (23.0) 300.3 (39.6) 131.6 (13.5) metostre aelawa 144.2 (18.1) 256.7 (24.8)

Synedre app. 41.4 -(5.2) 41.6 (5.1) 20.5 (7.2) febetterte fenestrate 54.2 (6.6)

Dinobryon divergens 64.1 (8,0) tephrion app. 66.8 (6.4) 160.4 (19.5: 54.2 ( 7.1 )

Cryptomones.orose 43.3 (5.3) 59.1 (7.8) 55.3 (5.7) 97.5 (9.4)

Cryptomones rettese 41.3 (5.2) 84.4 (8.7)

Anebeena spp. 50.4 (5.2) 57.7 (5.6) oscillatoria spp. 53.2 (5.5) 164.2 (15.8)

Peridinion inconspicum 43.1 (5.3) 74.8 (9.9)

Augus t " * " * " " - " " * " ' " " " " " " " * * " " * " * " " * " " ' ' * " " " " " " " " "

• Ar*. spirells 123.9 (8.3)

Coetastrue caerican 34.0 (6.8) 82.2 (5.5)

Staurastrun peradoxun 59.5 (8.1)

Attheye nocherlesi 62.9 (6.4) melostra aelgua 86.9 (11.9) 100.5 (11.3) ahinosolenia eriensis 38.7 (5.3)

Synedre sp. A 35,7 (7.1) synedre spp. 47.7 (9.5) 90.5 (6.2) 110.8 (7.4)

Tabetterte fenestrata 45.3 (9.1) mattomonas caudatus 52.3 (6.1)

Unidentified chrysopnytes 27.4 (5.5) 89.8 =(6.0)

Cryptomanas erose 83.8 (9.4) 76.9 (5.1)

Rhaphidiopsis curvete 243.6 (16.3)

Carat tunfirmdinet ta 66.9 (6.8) l- Glenodinlun yprediniun 46.6 (5.3)

(,

Pe!dinfue esp. 213.9 (29.2) 311.5 (35.1) 53.6 (10.7) 374.8 (38.5)

Woaaamher ************************ *****************************************************

Attheye ancheriest 54.5 (13.6)

Melostra amipus 425.5 (64.2) 87.5 (21.8) 353.3 (43.6)- 1N.9 (17.3) 293.9 (28.6)

I thinosolenis artensis 32.0 (8.0) ochromones spp. 28.9 (7.1) synure wella 34.8 (5.2) 43.7 (6.9) 183.4 (24.4) 108.7 (10.6) tryptomanas erose 45.7 (6.9)

Ansoeena spp. 45.6 (11.3)

Ceratium hirmdinet t e - 66.9 (8.3) 66.9 (8.9) 66 9 (5.6) l Phacus tortus 58.9 ( 7.8) 5 7.', (5.6) i-l 75

I

-Table 7. Total densities (units /ml) and in parentkses percent composition of major taxa (>5%) of pnytoplankton collected at locations in I.ake Norman, NC during '2ebruary, May, August and November 1989, i kejor tone De mities Locations 2.0 5.0 9.5 11.0 15.9 f 1

Tsaa unite /at F units /el 1 mite /st % unitt/al I mits/mL j Fetruary Ank. feltetus v. etrabille 25 ( A.3) 50 (12.0) 33 (6.1) 90 (8.9) ,

Ank. spirelle 48 (11.5) 29 (5.3) 125 (12.2) coccold greene so (15.1) 56 (13.6) 136 (24.9) 123 (12.1) feetcairs eselgue 87 (22.0) 130 (31.4) 144 (26.3) 1C0. (10.6) 25o0 (53.6) met. distens v.-alpigene 121 (11.9) 438 (9.1)

Cryptomanos erose 305 (6.3)

Rhodomones elftJte 46 (11.4) 27 (6.5) 31 (5.7) 90 (8.8) ney ..............................................................................

Ank. falcatus v. atrabills 119 (6.1) coccold greens 74 (5.0)

Cyclotette cosepte 95 (6.3) 131 (8.9) metostre meisue 95 (6.3) 169 (5.8) synedre app. 87 (5.9)

Dinotryon divereens 156 (10.4) rephrlon sm. 415 (27.8) 996 (48.4) 337 (22.8) nhadomones miraate 218 (14.8) 606 (31.3) 821 (28.3) ocelltatoria spp. 291 (15.0) 898 (30.9)

August * - -

Ank. spiretis 2752 (26.8)

Cosmerlun spp. 74 (6.4) 131 (9.8) coccold greens 119 (10.4) 180 (13.5) 210 (t0,5) 226 (10.4) metostre aseleva 57 (5.0)

Rhltosolenia eriensis 58 (5.0)

Synedre spp. 115 (5.2)

Ochromones spp. 181 (9.0) 227 (10.4) unidentified chrysophytes . 214 ( i.7) 1?e (10.2) 360 (18.0) 222 (10.2) 1i81 (11.5)

= -Cryptomones erose 87 (6.5)

Rhodomones minut0 89 (6.6) 211 (9.7) 574 (5.6) thephidiopsis curvete 1668 (16.2)

- + - -

November Ank. falcatus v. e "obills 111 (6.4) 144 (6.6)

Ank. spirelle 143 (8.3) 144 (6.6) -189 (9.9) 152 (5.9)

Scenedeemus Sandricaude 107 (5.6) 140 (5.4)

Coccold greens 78 (5.6) 131 (7.6) 131 (6.0) 111 (5.8) 140 (5. a Melostre estigue 281 (20.2) 233 (10.7) 194 ( 7.5 )

ochromones spp. 206 (14.8) 242 (14.0) 292 (13.5) 205 (10.8) 337 (13.0)

Synure uvette 173 (9.1)

Unidentified chrysconytes 201 (9.3)

Cryptcmones eross til (8.2) thodemones minute 135 (9.7) 189 (7.3)

Gesiphonemo tecustris 217 (12.6) 177 (8.1) ,

74

e i

Osovolume j ia f

,e .,.j [ ) ta<

//6 '

on.

U:

1, Downlake locabons ce< '

j cs,

10. EO & E5 5

t

((o4,

, 08- ,

ts.

e e

rig my AuG e l FEB mV AUG

, l ff- _

t< _.._ ...

a'< , _ . _ j

{,*<

14< ""' n Location 11.0 "

't.w ' 'U ,

i t;Wg3<

ghg g,

e C

" e Fts my A.;G e fte mv A.JG

~~

so.-

.. O Blueveens O Cryptophytes s

/ N -

[53 Crvysophytes

- C""3 Goon Algas

f. EER Diatoms

' i *-

? .(

s-

= Lo abor 3 0 {

. .m ,

3 ,

h , M 8

W/R EEE ,:A&

8 .

=

- @ are 3 o-rce i

lB,E m

6 K i u;G e i

rte w;m eac e Figure 2. Total class densities and biovolumes for downlake locations (Locations 2.0, 5.0 and 9.5), midlake Location 11.0 and uplake tc.Stion 15.9 from Lake Norman, NC during 1989.

77

14 14 '

Chlorophyl Data g3 Seston Ash Free Dry Weights 13' 12-12< 11- <

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Figure 1. Chlorophyll a, seston dry weights, total densities and total biovolumes for locations in Lake Norman, NC-during February, May, August'and November 1989, 76

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to .e n u a se n = se NOVEMBER gar AUGUST FEBRUAay figure 4. Phytoplankton densities and biolumes from euphotic zone composite samples collected at locations in Lake Norman in february, May, August and November of each year from 1975 10.1989.

+

o

~

s 100 PLANKTON 1NTRODUCTLQN The objectives of the Lake Norman Maintenance Monitoring Program for zooplankton are to:

1. Describe quarterly patterns of zooplankton standing crops at selected locations on Lake Norman, and

2. Compare zooplankton data collected during this study

( February, May, August , and November 1989) with historical data collected during these months.

A Previous studies on Lake Norman zooplankton populations have demon-strated a bimodal seasonal distribution with peaks occurring in spring and fall. Considerable spatial and year to year variability has also been observed (Duke Power Company 1976, 1985; Hamme 1982; Menhinick and Jensen 1974).

METHODS AND MATERIALS Quarterly zooplankton samples were collected at Locations 2.0, 5.0, 9.5, 11.0, and 15.9 (Chemistry, Figure 1). Duplicate 10 m to surface and bottom to surf ace net tows were taken at these locations on 27 Feoruary, 23 May, 23 August, and 10 and 28 November 1989. Field and 82

laboratory methods for zooplankton standing c%p at:61ysis were report-ed in Hamme (1982). Zooplankton standing crop data f rom February, May, August, and November 1989 were compared with historical data from these months collected since 1978.

BESULTS AND DISCUSSION Sttndina Crom Except for Locations 11.0 and 15.9 in Febrt,a ry and Location 5.0 in May, zooplankton densities in 1989 were higher among 10 m to surf ace samples than among bottom to surf ace samples (Table 1; Figure 1).

This . was also found in previous years. Zooplankton in 1989 also exhibited a trend of increasing densities from downlake to uplake, with the exception that minimum values were often observed at Location 9.5. Total zooplankton densities from 10m to surface tows ranged from 3 3 20,800/m at Location 9.5 in November to 165,000/m at location 15- 9 .

in February. Zooplankton densities from bottom to surface tows ranged 3

= from 17,500/m 3 at Location 11.0 in August to 189,600/m at Location 15.9 in February.

Zooplankton standing crops for the year were highest in May at all locations with the exception of location 11.0 in the 10m to surf ace tows -and at Location 15.9, where they were highest in February (Fig. . ,

ures 1 and 2). Minimum values were observed in November at all locations except Location 2.0 in the bottom to surface tow and 83

4 Locatio!< 11.0 which had minima in August. Hamme (1982) noted that the primary peak in zooplankton densities usually occurred during the spring, while minimum zooplankton standing crops were typically observed during the winter.

Zooplankton densities during February, May, August, and Noven.ber 1989 were generally within the range of ttiose observed during these months of previous years (Figure 3). ' Exceptions were mid and uplake ,Loca-tions 11.0 and 15.9 in May, which exhibited lower densities than in previous years, and Location 15.9 in february, which was somewhat higher than in February of previous years.

Community Composition Fifty-three zooplankton taxa have been identified in samples collected since the Lake Norman Maintenance Monitoring program was initiated in August 1987 (Table 2). W new zooplankton taxa were identified in samples collected in 1989.

Rotifers generally dominated zooplankton assemblages at all locations during 1989 f,ollowed in importance by copepods and cladocerans Cladocerans dominated the zooplankton at Loca-(Table 1- Figure 1).

tion 2.0 in February 1989 and copepods dominated at times at downlake locations during all inonths except February. The highest percent composition of rotifers was recorded uplake at Location 15.9, where rotifers accounted for more than 70't of the total densities in 10m to surface tows each month. Hamme (1982) also found that highest rotifer 84

~. . . . - . - _ .____ -

densities generally occurred at uplate locations. While rotifers were the dominant taxonomic group each month the overall percent compost-tion in 1989 was lower than in previous years (Table 3). 4 During February 1989 EtrJLitlla was the most abundant rotifer at Locations 2.0 and 5.0 and the 10m to surf ace tows at Location 9.5, whereas polvarthra was usually dominant at locations further uplate.

Polvarthra and lynghttig were codominant in rotifer populations at Locations 2.0 and 5.0 in May with iynchaett becoming more important at Locations 9.5 and 11.0 and Keratella dominating at Location 15.9.

Conochilus was the dominant rotifer at all locations in August, with Asolanc5na also being important at Location 9.5. During November 1989, the major rotifer taxon at most locations was Etratella, with

[.gl!.pchilus al so being important at downlake locations. These taxa vere among the most abundant rotifers observed during 1988 and in previous years (Hamme 1982).

Copepods were generally most abundant during May at downlake locations and during February at Location 15.9. Lowest copepod densities were observed in February at Locations 2.0 and 5.0, in August at Locations 9.5 and 11.0 and in November at Location 15.9. No distinct seasonal trend in copepod abundance was detected for samples collected in 1989.

The overa,ll percent composition of copepods was close to that observed during the preoperational and operational periods (Table 3). As in previous years, copepods were dominated by immature forms during all sampling periods of 1989, with adults seldom accounting for more than 10% of the total copepod densities.

85

4.

Cladocerans were generally more abundant at downlake locations than uplake locations in 1989. Cladoceran densities we re generally higher in August and lowest in November. In February, cladocerans comprised over 45% of the density at Location 2.0 for both 10 to surf ace and bottom to surface tows. During August they comprised over 20% of the densities at all locations except Location 15.9. Cladocerans com-prisei less than 10% of the total zooplankton at Location 15.9 for all months in both 10m to surface and bottom to surface samples. Percent _

composition values for cladocerans at Lake Norman locations in 1989 were generally higher than in previous years (Table 3). Bosmina was the most hbundant cladoceran observed in samples collected in 1989, as in previous years (Hamme 1982). During August, Bosminoosis was also an important constituent of cladoceran populations at downlake loca-tions.

SUMMARY

Zooplankton densities were generally higher among 10 m to surface samples than among bottom to surface samples in 1989, as in previous

= years. Total zooplankton standing crops for bottom to surf ace tows were-highest in May at downlake Locations 2.0, 5.0 and 9.5 and highest in February for uplake Locations 11.0 and 15.9. Lowest standing crop values were seen in November at all locations except Location 11.0 which had lows in August. These seasonal trends are similar to past studies where zooplankton peaks were of ten observed in the spring, with minima occurring in winter and summer months. Zooplankton 86

densities during 1989 were generally within ranges observed during previous years.

Rotifers dominated zooplankton standing crops throughout 1989, as they have done in past years, followed in importance by copepods and c'adocerans. Major rotifer taxa observed in 1989 were Erntella, Polvarthra, Synchaeta, and Conochilus. Copepud populations were i

dominated by immature forms, Cladoceran relative abundance was 4

highest at downlake locations and lowest at Location 15.9 where they l did not comprise more than 10% of the density at any time in 1989. l As in previous years, Besmina was the most abundant cladoceran taxa observed, with Eosmincesis also becoming abundant downlake in August.

Most of the majnr genera identified during 1989 were also listed as among the most abundant taxa during previous years. Rotifer persent

, composition by month in 1989 was slighly lower than in past years, cladocerans were higher and copepods were about the same.

LITERATURE CITED

" Duke Power Company. 1976. McGuire Nuclear Station, Units 1 and 2, Environmental Report, Operating License Stage. 6th rey. Volume 2.

Duke Power Company, Charlotte , NC.

Duke Power Company. 1985. McGuire Nuclear Station, 316(a)

Demonstration. Duke Power Company, Charlotte, NC.

Hamme, R. E.1982. Zooplankton, in J. E. Hogan and W. D. Adair (edt.).

87 a

_ ,-, , .,, .mm

n

.r . .

4 1

9-Lake Norman summary, Technical Report DUKEPWR/82-02. p. 323-353, Duke Power Company, Charlotte, NC. 460 p.

Menhinick, E. F. and L. D. Jensen. 1974. Plankten populations.

In L. D. Jensen (ed.). Environmental responses to thermal dis-charges from Marshall Steam Station, Lake Norman, North Carolina.

Electric Power Research Institute, Cooling Water Discharge Re- ,

. search Project (RP-49) Report No. 11., p. 120-138, Johns Hopkins University, Baltimore, MD, 235 p.

Ruttner-Kolisco. 1974 Plankton rotifers: biology and taxonomy. Die Binnengewasser. 24(1) supplement. 146 p.

e W

88

~ ' ' ' ' +P"r .

r , y.. ,__

-0 Page 1 of 2 .

3 Table 1.

Total rooplankton deatities (no.*1000/m ), densities of '

major zoopler kton taxonomic groups, and percynt composition

'(in parenthesis) of major taxa in 10 m to surf ace (10-5) and bottom to surf ace (B-5) net tow samples collected on Lake

-Norman in February, May, August, and November 1989.

Sample Locations I.yne Taxon _2.0 - 5.0 .__9.5 _ _11.0 15.9 DA.Le 02/27/89 10-5 COPEP00A 6.4 5.1 11.2 13.3 36.8 (14.0) (11.8) (33.2) (24.4) (22.3)

CLA00CERA 21.6 5.4 9.4 4.4 9.9 (47.1) (12.8) (27.9) (8.1) (6.0)

ROT 1FERA 17.8 32.3 13.1 36.8 118.3 QB.ll (75.4) QiL1) (67.5) 54.6 (71.7) 165.0 TOTAL 45.9 42.8 33.6 B-5 COPEPODA 4.2 4.4 7.0 23.6 35.3 l (depth [m] (12.8) (13.1) (31.6) (24.8) (18.6) i

]

of tow for each CLADOCERA 16.1 -6.2 6.5 4,9 3.2 location: (49.7) (18.5) (29.5) (5.1) (1.7) 2.0231 5.0=19 ROTIFERA 12.1 22.7 8.6 66.7 151.0 9.5=22 (37.5) (68.3) Old) (70.1) Gil) 11.0=28 101AL 32.4 33.2 22.1 95,2 189.6 15.9=21)

~~

-05/23/89 '0-5 COPEPODA 20.9 13.7 17.8 18.5 32.5 (38.7) (31.7) (46.9) (20.4) (20.7)

CLA00CERA 9.B 18.6 5.5 4.0 7.9 (18.2) (18,6) (14.5) (4.4) (5.0)

ROTIFERA 23.1 21.5 14.7 68.3 116.6 (43.0) L41,_D (38.6) ULD (74.3)

TOTAL 53.8 43.2 37.9 90.8 157.0 B-5 COPEPODA 16.4 24.1 19.7 20.0 37.9 (depth [m] (47.6) (42.1) (52.0) (30.9) (31.4)

- of tow for each CLA00CERA 3.5 4.7 3.0 3.5 11.4 location: (10.3) (8.2) (7.9) (5.4) (9.5) 2,0=31 5.0=20 ROTIFERA 14.5 28,5 15.2 41.2 71.1 9.5=21 (42.11 (49.8) (40.1) ( 6 3. 7.) (59.1) 11.0=26 TOTAL 34.3 57.3 37.8 64.6 120.4 15.9=21) 89

l .

Table 1 (continued) Page 2 of 2 Sample Locations Dng _Lyp_e_ __IngL 2.0 5.0 9 . 5__ 11.0 _15.J_

08/23/89 10-5 COPEP00A 9.9 11.6 6.5 5.6 18.0 (22.1) (34.0) (22.1) (18.3) (15,7)

CLAD 0CERA 17.1 9.6 8.1 7.9 7.9 (33.2) (28.0) (27.6) (25.8) (6.9)

ROTIFERA 17.7 13.0 14.8 17.0 88.7 (39.7) (38.0) (50.2) (55.9) (77.4)

TOTAL 44.7 34.2 29.5 30.5 114.6 B-5 COPEPODA 7.6 10.5 6.3 5.7 14.1 (depth [m] (35.0) (41.3) (28.0) (32.5) (23.2) of tow for each CLADOCERA 7.3 5.4 6.2 3.7 5.6 location: (33.5) (21.0) (27,5) (21,1) (9.3) 2.0=31 5.0=20 ROTIFERA 6.9 9.6 10.0 8.1 41.1 9.5=21 (31.6) (37.7) (44.5) (46.3) (67.5) 11.0=26 15.9=21) INSECTA 0.1 0.0 0.2 0.0 0.0 LQJD LO.J) (1J1) LQJD L(L 0)

TOTAL 21.9 25.5 22.6 17.5 60.9 11/10 & In-S COPEPODA 13.6 11.5 10.1 12.5 10.1 28/89 (41.4) (47.3) (48.4) (22.7) (14.2)

CLADOCERA 4.8 2.6 0.5 4.3 1.3 (14.5) (10.5) (2.4) (7.8) (1.9)

ROTIFERA 14.6 10.2 10.2 39.2 60.0 (44.1) L4LZ) (49,2) (69.51 (84 0) 10.AL 33.0 24.3 20.8 55.0 71.5

~

B-S COPEP00A 12.8 12.1 10.5 13.5 9.6 (depth [m] (47.2) (53.6) (58.0) (30.1) (15.8) of tow for each CLAD 0CERA 3.2 4.8 0.5 7.0 1.5 location: (11.7) (21.2) (2.6) (15.5) (2.5) 2.0=28 5.0=19 ROTIFERA 11.2 5.7 7.1 24.5 49.8 9.5=18 (41,1) (25.2) (39.4) (54.5) ( BL.7 )

11.0=24 TOTAL 27.2 22.5 18.1 45.0 61.0 15.9=21) 90

_- _ _ _ _ . _ . - -. _ _ _ _ _ _ _ . . m _ . _ _ . _ . _. . _ .

Table 2. Zooplankton taxa identified from samples collected in Lake Norman on August and November 1987 and February, May, August and November 1988 and 1989. (*etaxon not recorded in previous Lake Norman studies).

GIEL!ste twtons ghwnesi (l. A. Fortes) Mac.t@estwg esp. Perty Monastyta stenroosi (heissener)

G. app. (O. F. Aller)

3. esp. Ehrertorg 9J321954 ht'.Sil M*rsh -

g. einsissinoistuis norsh Ploeosans trwtate (Leverufer)

. R. settidus perick 2. app Herrick R. app marsh Potvoe tbra arveteen (Weirteljski) meerveloqa ggs (S. A. Fortars) 2. wtaarfs Carlin

-5. esp. Eers 2. opp.thrertorg f renoevetens prest'ss (fischer) Ptrairp sp. Ihrerters Sv@aeta sp. Ehrortierg 1.em.Kiefer Trichoceen gaawcine (Welreijski) talanoid copepodites Cyttopold c w Mtes 1.evtiretta(tahof) kauptli. 1. opp. Lenorck Unimentlfted boetloidea tt.AD0tf G.A IW11CtA Beagine imairesteit (O. F. Ntter) theatsorus sp. Lichterstein

8. esp. Seird tossinoosis deiteesi Richard Ceriodee nte spp. Dane Ege,,ait eminus $courfield R. ns*Wt e Fort?rce R. app. N(ter Dietarcome spp. Fischer

• Netanadium amazonic e Stingetin

3. app Zeddech Leptodo's !J.n,,(111 (Focke) f tvoervetus soeditAss (Lieven)

@ crystet tina 0. F. Alter 2011Fien Arurseccais spp. Lovterborn asetarchne sm. Goose

- Seachlorus caudete sorrois and Dadey R. haveneensis Roussetet

8. natulus 0. F. Etter Chramonaster app. Leutertsoen teltotbece sm. Herring Conochiloides spp. Nieve Cunochi.l g Wicoenis (Rousselet)

{ spp. Wieve Castranus spp. laesef Mene*thre opp. $ctimorde Kelticott e bestoneasis (Ecusselet) 1, app. Ahlstrarn Kerstet t e spp. Bory de St. Vircert Las. ant spp. Nitzsch l

91

Table 3. A comparison of the density percent composition of major taxonomic groups during certain years of the preoperatior.al peried (1978-1931), the operational period (1982-1984), and the t.ake Norman Maintenance Monitoring Study (1988 and 1989).

May Ft h.rgry 16-al 82-84 ISE 1919 78-81 M-M 12B 12 %

33.2 28.7 23.1 20.7 33.9 18.2 10.2 36.3 COPEP00A 6.8 4.5 7.9 20.7 5.1 3.9 6.9 10.2 CLAD 0CERA 66.8 69.0 59.6 61.0 78.2 82.9 53.6 ROT 1FERA 60.0 0.0 0.0 0.0 0.0 0.0 0.0 0,0 0.0 INSE CT A A.us.V 5 t __ _

.__Roymber ZS-El M-BA ltS8 1939 71-81 E2.-!L4 L9M 1912 22.1 7.7 27.2 19.7 26.6 97 37.9 COPEPCOA 27.4 g

12.3 3.7 23.9 3.2 6.4 2.5 9.1 CLADOCERA S.0 65.4 88.6 48.9 77.1 67.1 87.8 53.1 R011FFRA 64.0 G.0 0.2 <01 c0.1 0.0 0.0 0.0 0.0 1NSECTA M

N

=

F 9

+

92

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Zooplankton Donettles 170 '

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f 140 - s --e Feb 4 130 - <7 4--+ May i;

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9.5 11.0 159 20 50 Locatxis 3 3 Figure 1. Zooplankton densities (unitsx10 /m ) by location for samp'es collected in Lake Norman, NC in 1989.

93

10m to Surisco Bottom to Surfsee Downlake locabons (20. 50 & Q 5) ,,

Downlake locahons (20. 50 & 9.N Aug Nov

- Feb May Aug Nov feb Mary Locahon 11.0 Location 11.0 so < so e< m m- m n

so < gV

+' .

, - y.1 m r_ ,

2 May Aug Nov Feb May Aug Nov Feb Locabon 159 Locahon 15 9 , , .

_ ,m O ciadocerans

'S @ Copepods E Rotfors O

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so E, m

May Aug Nov io May Aug Nov Feb Figure 2. ?ooplankton densities (unitsx103jg3) by group for downlake ,

(l.oc. 2.0, 5.0 and 9.5), midlake (l.oc.11.0) and uplake (l.oc.15.9) locations in t.ake Norman, NC in 1989.

9

~~ 10m TO SURrACE LOCAtl0N 2o

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t **t n a en u u u n no a u u n n se n u u a n u n u u u NOVEMBER MAY AUGUST FEBRUARY 3 3 Figure 3. Total zooplankton densities (unitsx10 /m ) from 10m to surface and bottom to surf ace samples collected at locations in Lake Norman, NC in February, May, August and November of each year from 1978 through 198-9.

95 l

. ~. .. .

6 EISHERIES INTRODUCTION In accordance with the NPDES permit for McGuire Nuclear Station, monitoring of specific fish population parameters was continued during 1989. The objectives of the fish monitoring program for Lake Norman during 1989 were to:

1. Determine taxonomic composition, standing stock, and density of fish at McGuire Nuclear Station (MNS) discharge and a reference location from cove rotenone samples.

2. Determine density and distribution of fish in the MNS mixing zone during summer.

3. Investigate the applicability of bioenergetics models for assessing predator-prey relationships in Lake Norman.

4. Determine striped bass habitat lake-wide and note

~ any occurrence of fish mortalities.

5. Survey numbers and size distribution of striped

' bass caught in tournaments and conduct angter diary surveys of selected striped bass anglers.

6. Determine age and growth of striped bass collected from Lake Norman.

7. Determine an index of largemouth bass abundance in Lake Norman.

8. Determine age and growth of largemouth bass collected from Lake Norman.

96

c__- - - _ __ __ __ _ _

MATERIALS AND METHODS fish Community Samelina Taxonomic composition, standing stock, (kg ha'I) and density (number ha-1) of fish were determined with cove rotenone samples during August 1989 at MNS discharge Location 4.0 and midlake location 19.0, as in 1988 (Duke Power Company, 1989) (Figure 1). A 1.2-ba ares was sampled at each rotenone location as described in Siler et al. (1982),

Density of fish in the limnetic areas of the MNS mixing zone was determined with 420 KHz hydroacoustic gear similar to sepling in 1988 (DPC,1989) on 22 June and 30 August 1989 af ter sunset (Figurc 2).

Bioenercetics Modelina a Bioenergetics modeling for threadfin shad and striped bass in Lake Norman was conducted in 1989. However, the model did not produce viable results, possibly due to the lir.ited knc,,tledge of appropriate inputs for these species.

Striped Bass Samolina The availability of suitable adult striped bass habitat in Lake Norman was determined f rom water temperature and dissolved oxygen concentration profiles taken lake wide during 1989 97

-- ~ _ -

(Chemistry Chapter). Water with a temperature 526'C and a dissolved oxygen concentration 22 mg l'I was considered -

suitable habitat for adult striped bass in Lake Norman. The main channel of Lake Norman was searched for dead and moribund fish in conjunction with physitochemical samples during June, July, August, and September. Additional searches for stressed and dead fish were also conducted in the MNS mixing zone 27 - 31 July. Dead and moribund fish were identified, and striped bass were measured (nearest mm total length). Scales and otoliths were removed for age and growth analyses of striped bass.

Data collected from striped bass fishing tournaments conducted on Lake Norman on 12 February, 4 March, 29 April, and 30 August 1989 provided information on size and age structure, spatial distribution, and food ha)its of striped bass. Data were analyzed as in 1988 (Duke Power Co.,

1989), although ages were not determined for striped bass collected in 1989, A striped bass angler diary program was initiated in 1989 to provide seasonal distribution of striped bass in Lake Norman, catch rates and harvest, and size distribution of angler.

caught striped bass. Angler cooperators were provided with diaries and asked to record the length of the fishing trip, number-of anglers in the party, zone where any striped bass were caught, length and weight of fish, and whether a fish was kept or released. The diary program will be ongoing for 98 l

. - - - - ~ _ _. ,, .. ._ ._ .

(

l three years and end in P%'

Langnnouth Bass Samolina largemouth bass were collected at night from Lake Norman

- f ror. 9 - 20 April 1989 with boat-mounted electrofishers by Duke Power Company (DPC) and North Carolina Wildlife Resources Commission (NCWRC), using techniques similar to 1988 (DPC, 1989), although sampling was conducted lakewide rather than in Zones 1 and 2. Age of largemouth bass collected in 1989 was determined using the computer program MIX (MacDonald and Green, 1988) to assign mean lengths at age and proportion in each age group using length frequency distributions from each zone and lakewide.

RESULTS AND DISCUSSION Fish Community The fish community, as determined by cove rotenone sampling, at Locations 4.0 and 19.0, was similar to 1989 (Duke Power Co. , 1989). A total of 26 fish species was collected at location 4.0 (MNS discharge) (24 species) and 19.0 (mid-lake) (24 species) in 1989 (Table 1). The fish community at the MNS discharge in 1989 remained similar in species composition and total standing stock to previous years (Table 2). A decline in gizzard shad standing stock since 1978 at Location 4.0 is apparent (Table 2). There is no way 99

? :o

'9 to ascertain the cause for this decline, but it may be due to overwintering survival or concentration of threadfin shad or other species in the MNS discharge.

Response of the fish community to the MNS discharge during the summer months was dif ferent in 1989 than in 1988, On June 22, 1989, fish densities, estimated with hydroacoustics, were highest in areas adjacent to the MNS discharge (Figure 3), but not in the discharge. By August 30, 1989, fish densities were highest in the immediate discharge area (Figure 4). This dif fered from 1988, when fish densities were highest in the discharge in June and September, and lowest in July and August, This change may be explained by the outage at MNS during July, August, and part of September 1989, resulting in discharge temperatures well below the 35'C thermal limit for MNS (MNS Operational Data Chapter).

9 StriDed Bass During 1989, adult striped bass habitat was acequate throughour Lake Norman, except during late July and early August'(Figure 5), Previous years have exhibited similar ,

/

habitat depletion patterns, Ten striped bass mortalities i associated with decreases in suitable habitat occurred between July 27 and 29,1989, These fish ranged in length from 581 to 705 mm. These fish were primarily collected in the MNS mixing tone, near the MNS intake.

100

l Tournament catches of striped bass monitored during 1989 The produced 57 fish ranging from 395 to 830 mm (Table 3).

majority (82%) of these fish were caught in April, and most '

(53%) fish were caught in Zone 5. No striped bass catches were reported f rom Zone 1 (MNS mixing zone) or the MNS

- discharge.

Detailed analyses of striped bass gut contents were not conducted in 1989; however, cursory examination revealed feeding patterns similar to those observ'ed in 1988, with Ages were gizzard shad and threadfin shad the major forage.

determined for striped bass otoliths collected during tournaments, and for dead fish from the summer period; however, fe # fish were collected and age growth information f rom these few fish would not accurately reflect growth rates nor year class strength.

Data from striped bass angler diaries were compiled for spring and summer 1989. Angler diary reports (Table 4) indicated that 45% of the fish were caught in zone 5, with 25%

and 20% caught in zones 3 and 4, respectively. Striped bass anglers harvested 71% of their catch. Although 80% of the striped bass were caught in the spring, angler success was higher in the ammer (7.6 hours6.944444e-5 days <br />0.00167 hours <br />9.920635e-6 weeks <br />2.283e-6 months <br /> / fish in the spring and 4.8 hours9.259259e-5 days <br />0.00222 hours <br />1.322751e-5 weeks <br />3.044e-6 months <br /> / fish in the summer).

101 l

l 1

Larcemouth Bass Le.rgemouth bass abundance, as indicated by electrofishing  ;

catch rates, have remained stable for the years sampled (Table 5). Highest catch rates are in the upper lake Zones (3, 4, and 5), and lowest in Davidson Creek (Zone 2) and ,

I the MNS mixing :ene (Zone 1). This gradient is similar to gradients in phytoplankton, nutrients, and threadfin shad in Lake Norman (Siler, et al,1986), and does not reflect MNS operation.

Ages for largemouth bass collected in 1989 were assigned by length frequency analysis using the MIX program. The program was used to assign mean length and proportion in each age class for data collected from 1982, 1983, 1984, 1988, and 1989. Because this program was able to accurately predict mean lengths and proportions for ages I through Ill in 1982, 1983,- 1984, and 1988, as compared to aging with

-- scales, this program was used to assign ages to fish collected in 1989 without aging scales (Table 6).- Ages of largemouth bass collicted in Lake Norman have been predominately I and 1

i

-11 (Figure 6). During 1988 and 1989, length frequency distributions indicated that ages I through Ill were dominant (Figure 7). This increase in the relative abundance of age 111 largemouth bass may be due to a large 1986 year-class, or the higher size limit (356 mm increased from 305 mm) imposed in 1982. The mean length of age ill largemouth bass has 102

varied from 318 to 342 mm during the study years, and increasing the size limit in 1982 has removed a portion of this age group from the harvest.

Zonal differences in length f requency distributions were

- - similar to previous years, with zones 4 and 5 producing more and longer fish (Figure 8). However, sampling occurred over a two-week period when water temperatures increased from .

12.5 to 18.5'C while we sampled progressively from Zone 1 through Zone 5. This may have resulted in dif ferential electroffshing efficiency for young and older fish from lower lake zones to upper lake zones.

FUTURE STUDIES

1. Fish community

• Cove rotenone sampling at Location 4.0 during May and August 1990 to evaluate the fish community in the-discharge 1rea at water temperatures of 30*C and 37*C.

.

• Fish distribution and density in the MNS mixing zone in 1990 using hydroacoustics and purse seine when water temperatures approximats 32, 35, 37 and 32'C to evaluate the change in the discharge temperature limit from 35 to 37.2*C.

• Plan a lakewide creel survey for 1992 in cooperation with NCWRC 103 yw w' - a-r u--

2. Striped Bass

' Continue habitat monitoring throughout the summer.

' Continue monitoring tournament catches in 1990, but discontinue in 1991 if not useful for NCWRC or DPC.

' Continue angler diary program to provide distribution

- and hirvest information through 1992,

3. Largemouth Bass

• hepeat Zone 1 and 2 study in 1992 or 1993.

- 104 a

iW.41Y Several sampling techniques were employed to monitor the fish ,

I community in,the MNS mining zone and takewide in 1989, and no measurab's changes occurred since MN$ has been operational. Species composition in cove rotenone sarpilng has consistently been dominated by gizzard shad, common carp, and bluegill; however, girrard shad are declining in

%ndance at location 4.0.

Hydroacoustic sampling in 1989 did not show changes in fish distribution in and near the MNS discharge as it had in 1988, because Unit 2 was shut down through most of the summer and fish did ncit avoid the discharge plume as they did in 1988. ,

1en striped bass mortalities were documented in 1989, and this was most likely due to the ob'erved decline in habitat in late July, and the operation of the lower level intake pumps by MNS. The lower level intake pumps were operated to increase performance during late July when additional generating capacity was needed. Use of the lower level pumps prior to September speeds the decline in striped bass habitat in the lower reservoir. The NPOES permit was chnged in 1990 to allow higher discharge temperatures, and ,

significantly reduce the need for using lower level pumps during June, July, and August each year. ,

105

t i

Tournament catches of striped bass and angler diaries l indicated the majority of striped bass were caught in Zone 5. l 4 Striped bass fishermen fished 7,6 hours6.944444e-5 days <br />0.00167 hours <br />9.920635e-6 weeks <br />2.283e-6 months <br />'to catch a striped  !

bass in spring and 4.8 hours9.259259e-5 days <br />0.00222 hours <br />1.322751e-5 weeks <br />3.044e-6 months <br /> in summer, Largemouth bass growth rates and electrof f shing catch rates f have remained stable Since our first sampling program in 1982, but age distribution has changed. An increase in the proportion of age 111 largemouth bass is occurring in Lake i

Norman, ,

k f

r I

e 106

L11f3A10BLt11LD Ouke Ecypr Company. Eake Norman: 1988 maintainance mor,itering program, McGuire Nuclear Station. 1989.

- MacDonald, P.O.M. and Green, P.E.J. MIX an interactive program for fitting mixtures of distributions. Release 2.3. Ichthus Data systems, Hamilton, Ontario, Canada.

1988.

Siler, J.R.; lewis, R.E.; Baker, B.K.; Vaughan, G.E.;

Hansen, R.A. hapter 10. Fish. In Hogan, J.E. and W.D. Adair (eds. ). Lake Norman Summary. Duke Po ir Technical Report No. DUKE PWR/82-02. Duke Power Company, Charlotte, NC. 460 p. plus appendices. 1982.

Siler , J.R.; Fori s, W.J. ; McInerny, M.C. $patial beterogeneity in fish populations within a reservoir.

Pages 122-136 in G.E. Hall and Van Den Avyle, M.J.,

- editors. Reservoir fisheries management: Strategies for *be 80's. Reservoir Committee, Southern Division American Fisheries Society, Bethesda, Maryland. 1986, 107

Table 1. Standing stock (Lilograms/ hectare) an : deM '.)

(number / hectare) of fish collected in cove rotenone $8rrples in Lake Normari in 1989.

LtcAtita 6.0 tocatsom 19.0 tons ippe , rerbe terho re/he L opt ece t eve osseus 0.76 1 2.19 2 Dorosome cepedisrun 19.25 64 10.86 3a 9.6 74a3 0 0 porceone seienense Cyprirus corpio 24.4% 27 22.63 18

1. stenitorus cryseleixes 0 0 0 i 0.02 18 0.19 iTT e betrcels chloristlub 0.05 21 0.o9 45 Retrcole hudsonius metropis nivevs 0.48 444 0.55 496 0 1.9 3 Carplodes typrirus 0 0.16 41 0.29 23 Icteturue cetus Ictelurus furcetus 0 0 0.69 2 leteturus platytecestus 0.07 3 0 0 1.64 33 4.44 $4 Ictaturus sancta vs PLrudi tie elIworis 0 0 0.04 11 0.01 14 Gereusie affinie 0 1 horone chrysocs 0.26 2 0.32 i Lecomis euritus 3.83 620 2.3 35%

Lepamis siteosus 0 0 34.32 4934 Locomis putosus 0.52 90 0.36 40 Lepcsiis macrochirus 13.99 2260 14.18 5389 Lepanis eterotc5Aus 0.95 46 0.17 i Locamis hytg id 0.51 34 0.28 8 2.48 130 6.P9 87 Mitracterus selecides 2.23 30 0.47 41 Pcmeals nigromecutetus 0 1 0 2 Itheostome fustforow (theostome olmatodt 0 1 0.32 54

• Perce fievescens 0.66 141 0.54 trf 81.89 11491 103.85 11975

$4L 108 l

l Table 2. Standing stock (611ograms/ hectare) for those taxa susceptible to cove rotenone sampling at location s

i 4.0 and 19.0 from 1978 through 1989. Totals Qw reflect all taxa captured.

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Table 3. Catches of striped bass in tournaments held on Lake Norman in 1989. Numbers in parentheses arelength ranges (mm). NR = none reported.

Dete me r. 04 Apr 29 Aug.30 tone t et>.12 0 0 0 1 0 2 0 0 F (580 T33) 0 0 0 8 (395 T54) 1 (580) 3 4 0 0 8 (555 830) 0 4 (545 672)  ; (TSO + T81) 13 (425 762) 1 (643) 5 0 0 1 (190) 0 6

0 0 0 be 2 (593

• ort) 2 47 2 totAt 6 Table 4. Angler harvest of striped bass for spring and summer 1989 from angler diaries.

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Table 5. Catch rates (number / kilometer) for largemouth bass collected with electrofishing gear in spring during 1982, 1983, 1984, 1988, and'1969.

Fws trat i 2 3 4 5 6 9 1952 21.9 19.5 16.1 52.s 60.6 mA nA 1953 28.2 29.8 16.9 30.8 37.6 118.5 15.0 1964 35.7 46.5 41.5 41.0 46.9 56.1 h6 1968 17.5 12.8 ha kA hA kA hA 1999 22.1 16.9 37.2 55.3 61.2 70.7 $3.0 110

lable 6. Mean lengths and proportion by age group using the scale aging technique and MIX program for largemouth bass collected with electrofishing gear in spring 1982. 1983. 1984, 1988, and 1989.

ng Scote estrq pla program lecqth 1 t w esition t oeg th 1982 1 composit te

$5.2 162 $6.? 163 I

259 30.4 267 Il 27.8 305 10.6 327 Ill 10.1 349 1.6 190 IV 4.2 Iv+ 2.6 0.8 19E3 161 31.9 161 3 3D.9 4.? . 7 256 II 40.1 251 302 21.5 323 til 22.7 360 3.1 393 IV 4.1 iv+ 2.1 0.8 1964 172 16.8 171 1 16.2 11 60.0 267 40.6 265 323 21.5 323 til 21.0 398 2.4 189 IV 2.1 0.7 0.7 iv+

19M 16.? ita 14.4 ill i 265 41.3 260 42.3 II 142 12.4 335 18.7 las 8.2 162 0.6 IV Iv+ 1.5 ,

1989 35.0 150 4

31.4 251 11

• 33.0 318 III 2.7 390 IV Iv+

111

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8 McGUIRE HUCLEAR STATIDH Figure 2. Hydroacoustic sampling transects in the mixing zone of McGuire Nuclear Station, 113 i..

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