NC0024392_Regional Office Historical File Pre 2018 (11)

OW-0 NATURAL REISOURCA 6,
LE REGIONAL
w ter �.
k
LAKE NORMAN
MAINTENANCE MONITORING PROGRAM*
2001 SUMMARY
McGuire Nuclear Station: NPDES No NCO024392
Duke Power A Duke Energy Company
January 2003

TABLE OF CONTENTS
Page
EXECUTIVE SUMMARY
i
LIST OF TABLES
v
LIST OF FIGURES
v '
CHAPTER I: McGUIRE NUCLEAR STATION OPERATION
I -I
Introduction
1-1
Operational data. for 2001
1-1
CHAPTER 2. WATER CHEMISTRY
2-1
Introduction
2-1
Methods and Materials
2-1
Results and Discussion
2-2
Future Studies
2-
Su
2_
Literature Cited
2-
CH TER. : PHYTOPLA KTt N
3_1
Introduction `
.1
Methods and Materials
-1
Results and Discussion
-2
Future Phytolankton Studies
3-9
Summary
-
Literature Cited
3-I1
CHAPTER 4: ZOOPLANI TON
4-1
Introduction
4-1
Methods and Materials
4-1
Results and. Discussion
4-2
Future Zooplankton Studies
4-6
Summary
4-
Literature Cited
4-7
CHAPTER S: FISHERIES
5-1
Introduction
-1
Methods and Materials.
-1
Results and Discussion
-2
Future Fisheries Studies;
-
Summary
-
Attachment l : Ilydroacoustic and Purse Seine Data.
A-1

EXECUTIVE SUMMARY
As required by the National Pollutant Discharge Elimination System (NPDES) pen -nit
number NCO024392 for McGuire Nuclear Station (MNS), the following annual report has
been prepared. This report summarizes environmental monitoring of Lake Norman
conducted during 2001.
McGUIRE NUCLEAR STATION OPERATION
The monthly average capacity factor for MNS was 96.8 %, 101.3 %, and 102.0 % during
July, August, and September of 2001, respectively (Table 1-1). These are the months when
conservation of cool water and discharge temperatures are most critical and the thermal limit
for MNS increases from a monthly average of 95.0°F (35.0'C) to 99.0'F (37.2'C). The
average monthly discharge temperature was 96.2°F (35.7°C) for July, 98.0°F (36.7°C) for
August, and 94.7'F (34.8°C) for September 2001. The volume of cool water in Lake
Norman was tracked throughout the year to ensure that an adequate volume was available to
comply with both the Nuclear Regulatory Commission Technical Specification requirements
and the NPDES discharge water temperature limits.
WATER CHEMISTRY
Temporal and spatial trends in water temperature and DO data collected in 2001 were similar
to those observed historically. Temperature and DO data collected in 2001 were within the
range of previously measured values.
Reservoir -wide 'isotherm and isopleth information for 2001, coupled with beat content and
hypolinmetie oxygen data, illustrated that Lake Norman exhibited thermal and oxygen
dynamics characteristic of historical conditions and similar to other Southeastern reservoirs
of comparable size, depth, flow conditions, and trophic status.
Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 2001 was
generally similar to historical conditions. All chemical parameters measured in 2001 were
within the concentration ranges previously reported for the lake during both MNS
preoperational and operational years. As has been observed historically, manganese
concentrations in the bottom waters in the summer and fall of 2001 often exceeded the NC
i

water quality standard. This is characteristic of waterbodies that experience hypolinmetic
deoxygenation during the summer.
PHYTOPLANKTON
Lake Norman continues to support highly variable and diverse phytoplankton communities.
No obvious short term or long term impacts of station operations were observed.
In 2001 lake -wide mean chlorophyll a concentrations were all within ranges of those
us years o
-d on long
,-tions of ash -free dry weights to dry )A
anual index for 2001 was lower than that of 2000, and was at the very low en
iediate range.
idication of "balanced indigenous populations" in a reservoir is the diversity, or
.a observed over time. Nine classes comprising 64 genera and 118 species, N
Maintenance Monitoring Program were identified during 2001.
ZOOPLANKTON
Lake Norman continues to support a highly diverse and viable zooplankton community.
Long term and seasonal changes observed over the course of the study, as well seasonal and
spatial variability observed during 2001, were likely due to environmental factors and appear
not to be related to plant operations.

Epilimnetic zooplankton densities during all but May of 2001 were within ranges of those
observed in previous years. The epilimnetic density at Location 15.9 in May 2001 was the '
highest recorded during the Program, and may have represented an ongoing lag response to
comparatively high phytoplankton standing crops uplake at that time.
One hundred and eight zooplankton taxa have been recorded from Lake Norman since the
Program began in 1987 (forty-six were identified during 2001). No previously unreported
taxa were identified during 2001.
FISHERIES
In accordance with the Lake Norman Maintenance Monitoring Program for the NPDES
permit for MNS, specific fish 'monitoring programs were coordinated with the NCWRC and
continued during 2001. General monitoring of Lake Norman and specific monitoring of the
NINS mixing zone for striped bass mortalities during the summer of 2001, yielded nine
mortalities within the mixing zone ` and nine mortalities in the main channel outside the
mixing zone.
Spring shoreline electrofishing of Lake Norman yielded variable catches for the three areas
sampled, the MNS mixing zone area, a mid -lake reference area, and the MSS nixing zone
area. The total number of taxa collected was the same for the MSS and MNS mixing zone
areas and slightly lower for the mid -lake reference area.
September 2001 forage fish densities ranged from a low of 3,173 fish/ha (Zane 6) to a high of
11,513 fish/ha (Zone 2). The estimated forage population was approximately 78 million fish.
Purse seine sampling indicated that these fish were 76.47% threadfin shad, 23.52% alewives,
and 0.01%;gizzard shad.
During December 2001, forage fish densities in the six zones of Lake Norman ranged from
1,451 to 8,647 fish/ha There appeared to be fewer fish in the downlake zones. The
estimated forage population was approximately 47 million fish. Purse seine sampling
indicated that these fish were 82.66% threadfin shad, 16.46% alewives and 0.88% gizzard
shad.

Fisheries data to date indicate that the Lake Norman fisher)
status and productivity of the reservoir. However, one aspe
that warrants close monitoring in the future is the compositi
� Lake Norman
introduction of alewives by fishermen over the past several years could have a dramatic
impact on lake -wide forage populations and game species.
iv

LIST OF TAB:
Table 1-1 Average monthly capacity factors for
ES
Page
Table -1
Water chemistry program for McGuire Nuclear Station
2-13
Table 2-2
Water chemistry methods and analyte detection. limits
2-14
Table 2-3
Heat content calculations for Lake Norman in 2000 and 2001
2-15
Table 2-4
Comparison of Lake Norman with TVA reservoirs
2-16
Table 2-5
Lake Norman water chemistry data in 18 and 1999
-17
Table 3-1
Mean chlorophyll a concentrations in Lake Norman
3-13
Table 3-2
Duncan's multiple range test for Chlorophyll a
3-1
Table 3-3
Total phtoplankton densities from Lake Norman
3-15
Table 3-4 '
Duncan's multiple range test for phytopinkton densities
3-16
Table 3-5
Duncan's multiple range test for dry and ash free dry weights
-17
Table 3-6
Phytopinkton taxa identified in Lake Norman from 1988-2001
3-18
Table 3-7
Dominate classes and species of Pytopl ton
3-28
Table 4-1
Total zooplankton densities and composition
4-10
- Table 4-2
Duncan's multiple range test for zooplankton densities
4-12
Table 4-3
Zooplankton taxa identified in Lake Norman from 1988-2001
4-13
Table 4-4
Dominant taxa and percent composition of selected zooplankton
4-17
Table 5-1
Electrofishing catches in the mixing zone of McGuire
-8
Table 5-2
Electrofishing catches in the mid -lake reference zone
-9
Table 5-3
Electrofishing catches in the mixing zone of Marshall
5-10`
u

LIST OF FIGURES
Page
Figure -1
Map of sampling locations on Lake Norman
2-20
Figure 2-2
Monthly precipitation near McGuire Nuclear Station
2-21
Figure -3
Monthly mean temperature profiles in background zone
2-22
Figure 2-4
Monthly mean temperature profiles in mixing zone
2-24
Figure 2-5
Monthly temperature and dissolved oxygen data
-26
Figure 2-6
Monthly mean dissolved oxygen profiles in background zone
2-27
Figure 2-7
Monthly mean dissolved oxygen profiles in mixing zone '
2-2
Figure 2-8
Monthly isotherms for Lake Norman
2-31
Figure 2-9
Monthly dissolved oxygen isopleths for Lake Norman
2-34
Figure 2-10a
Heat content of Lake Norman
2-7
Figure 2-10b
Dissolved oxygen content of Lake Norman
2-37
Figure 2-11
Striped bass habitat in Lake Norman
2-38
Figure -1
Chlorophyll a measurements of Lake Norman
3-2
Figure 3-2
Mean chlorophyll a concentrations by year
-30
Figure 3-3
Chlorophyll a concentrations by location
3-31
Figure 3-4
Class composition of phytoplankton at Locations 2.0
-33
Figure 3-5
Class composition of phytoplankton at Locations 5.0
3-34
Figure 3-6
Class composition of phytoplankton at Location 9.
3-35
Figure -7
Class composition of phytoplankton at Location 11.0
3-36
Figure -8
Class composition of phytoplankton at Location 15.9
3-37
Figure 3-9
Annual lake -wide Myxophycean index from 1988-2001
3-8
Figure 4-1
Zooplankton density by sample location in Lake Norman
4-19
Figure 4-2
Zooplankton densities among years during February and May
4-20
Figure 4-3
Zooplankton densities among years during August and November
4-21
Figure 4-4
Lake Norman zooplankton composition in 2001
4-22
Figure 4--5
Quarterly zooplankton composition from 1990 through 2001
4-23
4-6
Annual lake -wide zooplankton composition,'1988 through 2001:
4-4
Figure 4-7
Lake Norman zooplankton composition (mixing zone locations)
4-25
Figure 4-8
Lake Norman zooplankton composition (background locations)
4-26
Figure -1
Lake Norman creel zones
5-11
Figure 5-2
Striped bass weight vs length for Winter 2001 samples
5-12
Figure 5-3
Striped bass weight vs length for Fall 2001 samples
5-13
V

CHAPTER 1
WGUIRE NUCLEAR STATION OPERATION
INTRODUCTION
As required by the National Pollutant Discha
number NC002492 for McGuire Nuclear Stat
Denartment of Environment and Natural R sourc
® ® ♦. a. A.. ♦. 6. ®.:
and the NPiES discharge water temperature limits.
l-1

Table 1-1.
Average monthly capacity factors (%)
calculated from daily unit capacity factors
[Net Generation (Mwe per unit day)
x 100 / 24 h per day x 1129 raw per unit]
and monthly average discharge water temperatures
for McGuire Nuclear Station
during 2001.
NPDES DISCHARGE
CAPACITY FACTOR
TEMPERATURE
Month
Unit I
Station
Monthly Average
Unit
Average
Average
Average
OF OC
January
63.7 17.6
83.9
104.5
94.2
February
103.7
105.1
104A
67.9 19.9
March
26.7
104.7
65.7
70.8 21.6
April
41.8
104.5
73.2
72.3 22.4
May
104.3
104.0
104.2
83.7 28.7
June
102.8
102.7
102.8
91.9 33.3
July
101.7
92.0
96.8
96.2 35.7
August
101.4
101.1
101.3
98.0 36.7
September
102.4
101.6
102.0
94.7 34.8
October
104.0
103.4
103.7
85.3 29.6
November
104.6
104.0
104.3
79.5 26.4
December
105.0
102.7
103.8
76.3 24.6
1-2

CHAPTER
WATER CHEMISTRY
INTRODUCTION
The objectives of the water chemistry portion of the McGuire Nuclear Station ( S)
NPDES Maintenance Monitoring Program are to;
1. maintain continuity in Lake Norman's chemical data base so as to allow detection
of any significant station -induced and/or natural change in the physicochemical
structure of the lake; and
2. compare, where appropriate, these physicochemical data to similar data in other
hydropower reservoirs and cooling impoundments in the Southeast.
This year's report focuses primarily on 2000 and 2001. Where appropriate, reference to
pre-2000 data will be made by citing reports previously submitted to the North Carolina
Department of Environment, Health, and Natural Resources (NCDE . R).
METHODS AND MATERIALS
The complete water, chemistry monitoring program for 2001, including specific variables,
locations, depths, and frequencies is outlined in :Table2-1. Sampling locations are
identified in Figure 24, whereas specific chemical methodologies, along with the
appropriate references are presented. in Table 2-2.` Data were analyzed using two ap-
proaches, both of which were consistent with earlier studies (DPC 1985, 1987, 1988a,
1989, 1990, 1991, ;1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000, 2001). The
first method involved partitioning the reservoir into mixing, background, and discharge
vanes, and making comparisons among zones and years. In this report, the discharge
includes only Location 4; the mixing zone encompasses Locations 1 and ; the
background zone includes Locations 8, 11, and 15. The second approach emphasized a
much broader lake -wide investigation and encompassed the plotting of monthly isotherms'
and isopleths and summer -time striped bass habitat. Several quantitative calculations
were also performed; these included the calculation of the areal hypolimnetic oxygen
deficit (AI OD), maximum whole -water column and hypolimnion oxygen content,
2-1

maximum whole -water column and hypolimnion heat content, mean epilinionand
hypolimnion heating rates over the stratified period, and the Birgean heat budget.
Heat (Kcal/cmm z ) and oxygen content (ing/cm2) and mean concentration (mg/L) of the
reservoir were calculated according to Hutchinson (1957), using the following equation:
Lt = Aoa 1 * TO • Az + d
where,
Lt! = reservoir heat (Kcal/cm2) or oxygen (mg/cm2 content
Ao = surface area of reservoir (cm2)
TO = mean temperature (° C) or oxygen content of layer
Az area (cm) at depth z
dz = depth interval (cm)
zo = surface
zm = maximum depth
RESULTS AND DISCUSSION
Precipitation Amount
Total annual precipitation in the vicinity of MNS in 2001 totaled 32.71 inches (Figure 2-
2); this was similar to that observed in 2000 (33.68 inches), but appreciably less than the
long -terra precipitation average for this area (46.3 inches). The highest total monthly
rainfall in 2001 occurred in March with a value of 6.14 inches,
Temperature and Dissolved {oxygen
Water temperatures measured in 2001 illustrated similar temporal and spatial trends in
the background and mixing zones (Figures 2-3, 2-4). This similarity in temperature
patterns between zones has been a dominant feature of the thermal regime in Labe
Norman since MNS began operations in 1983. Water temperatures in the winter of 2001
were generally similar to corresponding measurements in 2000 except in early January
-2

when year 2001 temperatures ranged from 2 to 6 C cooler throughout the entire water
column in both zones than observed in 2000 (Figure 2-3, -4). Interannual variability in
water temperatures during the spring, summer, and tall months was observed in bath the
mixing and background zones, but these conditions were well within the observed
historical variability and were not considered of biological significance (DPC 1985, 1989,
1991, 1993. 1994, 1995, 1996, 1997, 1998, 1999, 2000). The major temperature
differences between year 2000 and 2001 were observed in early winter (December) when
year 2001 temperatures ranged from 2.5 to 6.2 C warmer than measured in 2000. These
differences can be traced to the cooler than average meteorological conditions observed
during the winter of 000/201.
Temperature data at the discharge location in 2001 were generally similar to 2000 (Figure
2-5) and historically (DPC 1985, 1987, 1988a, 1989, 1990, 1991, 1992, 1993, 1994,
1995, 1996, 1997, 1998, 1999, 2000, 2001). The warmest discharge temperature of 2001
occurred in September and measured 35.8'C, or 2.58 °C cooler than measured' in August,
1999 (DPC 2000).
Seasonal and spatial patterns of DO in 2001 were reflective of the patterns exhibited for
temperature, i. ,e., generally similar in both the mixing and background zones (Figures 2-6
and 2-7) Winter and early -spring DO values in 2001 were generally equal to or higher
than measured in 2000, and appeared to be related predominantly to the cooler water
column temperatures measured in 2001 versus 2000. The cooler water would be
expected to exhibit a higher oxygen content because of the direct effect of temperature on
oxygen solubility, which is an inverse relationship, and indirectly via an enhanced
convective nixing regime which would promote reaeration.
Spring and summer DO values in 2001 were highly variable throughout the water column
in both the mixing and background zones ranging from highs; of 6 to 8 mg/L in the
surface waters to lows of 0 to 2mg/L in the bottom waters. This pattern is similar to that
measured in 200 and earlier years (DPC 1985, 1987, 1988a, 1989, 1990, 1991, 1992
1993, 1994, 1995, 1996, 1998, 1999, 2000, 2001). Hypolimnetic DO values during the
spring and summer of 2001 generally ranged from 0.1 mg/L - 2.0 mg/L greater than
measured in 2000; the lone exception to this was observed in September when DO values
were considerably lower (by as much as 6.0 mg/L) than measured in 2000. All dissolved
oxygen values recorded in 2001 were well within the historical range (DPC 1985, 1987
1988a, 1989, 1990, 1991, 1992, 1993, 1994, 1995, 16, 1997, 1998, 199, 2000, 2001).
-

Considerable differences were observed between 2001 and 2000 fall and early -winter DO
values in both; the mixing and background zones, especially in the .metalimnion and
hypohmnion during November (Figures 2-6 and -7). These interannual differences in
fall DO levels are common in Catawba River reservoirs and can be explained by the
effects of variable weather` patterns on water column cooling and mixing. Warmer air
temperatures would delay water column cooling (Figure 2-3, -4) which, in turn, would
delay the onset of convective mixing of the water column and the resultant reaeration of
the metalimmon and ;hypol mmmn. Conversely, cooler air temperatures would promote
the rate and magnitude of this process resulting in higher ISO values sooner in the year.
Interannual differences in DO are common in Southeastern reservoirs, particularly during;
the stratified period, and can reflect yearly differences in hydrological, meteorological,'
and limnological forcing variables (Cole and Hannon 1985 Petts; 1984).`
The seasonal pattern of DO in 2001 at the discharge location was similar to that measured
historically, with the highest values observed during the winter and lowest observed in
the summer and early -fall ;(Figure 2-5). The lowest DO concentration measured at the
discharge location in 2001 (5.5 mgfL) occurred in August, and was similar to DO levels
measured in August 2000 (5.4 mg/L). Low DO values measured at the discharge location
during the summer and early fall occurred concurrently with hypolimnetic water usage at
M S for condenser cooling` water needs.
Reservoir -wide Temperature and Dissolved Oxygen
The monthly reservoir -wide temperature and dissolved oxygen data for 2001; are
presented in Figures'' 2-8 and 2-9. These data are similar to that observed in previous
years and are characteristic of cooling impoundments and hydropower reservoirs in the
Southeast (Cole and Hannon, 1985, Hannon et. al., 1979; Petts 1984). For a detailed
discussion on the seasonal and spatial dynamics of temperature and dissolved oxygen
during both the cooling and heating periods in Lake Norman, the reader is referred to
earlier reports (DPC 1992, 1993, 1994, 1995, 1996).
The seasonal heat content of both the entire water column and the hypolimnion for Lake
Norman; in 2001 are presented in Figure 2-10a; additional information on the thermal
regime in the reservoir for the years 2000 and 2001 are found in Table -3. Annual
minimum heat content for the entire water column in 2001 (7.45 Kcallcm2; 7. °C)

occurred in early January, whereas the maximum heat content (27.96 Kcal/c 2 27.57 OC)
occurred in mid -August. Heat content of the hypolimnion exhibited a somewhat different
temporal trend as that observed for the entire water column. Annual minimum
hypolimnetic heat content occurred in early January and measured 4.4 Kcal/cm2 (6.98
IC), whereas the maximum occurred in early September and measured 15.17 Kcal/cm2
(23.48 IC). Heating of both the entire water column and the hypolimnion occurred at
approximately a linear rate from minimum to maximum heat content. The mean heating
rate of the entire water column equalled 0.090 Kcal/cm 2/day versus 0.043 Kcal/cm2/day
for the hypolimmon The 2001 heat content and heating rate data were slightly lower
than measured in 1999 and 2000, but similar to earlier years (DPC 1992, 1993, 1994,
199, 1996, 1997, 1998, 1999, 2000).
The seasonal oxygen content and percent saturation of the whole water column, and the
hypolimnion, are depicted for 2001 in Figure 2-10b. Additional oxygen data can be
found in Table 2-4which presents the 2000 AHOD for Lake Norman and similar
estimates for 18 TVA reservoirs. Reservoir oxygen content was greatest in mid -winter
when DO content measured 10.6 mg/L for both the whole water and the hypolimion.
Percent saturation values at this time approached 945 % for the entire water column and
90% for the hypolimnion. Beginning in early spring, oxygen content began to decline
precipitously in both the whole water column and the hypolimnion, and continued to do
so in a linear ;fashion until reaching a minimum in mid -summer. Minimum summer
volume -weighted DO values for the entire water column measured 4.33 mg/L (7 % i
saturation), whereas the minimum for the hypolimnion was 0.33 mg/L (3.9 % saturation).
The mean rate of DO decline in the hypolimnion over the stratified period, i.e., the
AHOD, was 0.030 Mg/cm7/day (0.047 'mg/L/day) (Figure -10b), and is similar to that
measured in 2000 (DPC 2001).
Hutchinson (1938, 1957) proposed that the decrease' of dissolved oxygen in the
hypolimnion of a waterbody should be related to the productivity of the trophpgenic zone.
Mortimer (1941) adopted a similar perspective and proposed the following
criteria for AHOD associated with various trophic states; oligotrophic - < 0.025
m /em2 /day, mesotrophic - 0.026 mg/ m2/day to 0.054 mg/cm2/day, and eutrophic - ?
0.055 mg/cm 2/day. Employing these limits, Lake Norman should be classified as
mesotrophic based on the calculated AHOD value of 0.030 mg/cm 2/day for 2001. The
oxygen based mesotrophic classification agrees well with the mesotrophic classification
based on chlorophyll a levels (Chapter ). The 2001 AHOD value is also similar to that
-5

found in other Southeastern reservoirs of comparable depth, chlorophyll a status, and
secchi depth (Table 2-4).
Striped fuss Habitat
Suitable pelagic habitat for adult striped bass, defined as that layer of water with
temperatures :!� 26 °C and DO levels > 2.0 mglL, was found lake -wide from October 2000
through mid -June 2001. Beginning in late -June 2001, habitat reduction proceeded rapidly
throughout the reservoir both as a result of deepening of the 26 °C isotherm and
mtalimnetic and hypolimnetic deoxygenation (Figure 2-11). Habitat reduction was most
severe from mid July through early September when no suitable habitat was observed in
the reservoir except for a small zone of refuge in the upper, riverine portion of the
reservoir, near the confluence of Lyles Creek with Lake Norman. Habitat measured in
the upper reaches of the reservoir at this time appeared to be influenced by both inflow
from Lyles Creek and discharges from Lookout Shoals Hydroelectric facility, which were
somewhat cooler than ambient conditions in Lake Norman. Upon entering Lake Norman,
this water apparently mixes and then proceeds as a subsurface underfloor (Ford 1985) as it
migrates downriver.
Physicochemical habitat was observed to have expanded appreciably by mid -September,
primarily as a result of eplimnion cooling and deepening, and in response to changing
meteorological conditions. The temporal and spatial pattern of striped bass habitat
expansion and reduction observed in 2001 was similar to that previously reported in Lake
Norman and many other Southeastern reservoirs (Coutant 198 , Matthews 1985, D 'C
1 92, 1 93, 1994, 1 95, 1996, 1997, 1 9 , 1999, 2000, 2 01).
Turbidity and Specific Conductance
Surface turbidity values were generally low at the MNS discharge, mixing zone, and mid -
lake background locations during 2001, ranging from 1.04 to 2.3 NTUs (Table 2-5).
Bottom turbidity values were also relatively low over the study period, ranging from 1.22
to 12.5 NTUs (Table 2-5). These values were similar to those measured in 2000 ('Table
2-5), and well within the historic range (DPC 1989, 1990 1991, 1992,' 1993, 1994, 1995,
1 96, 1997, 1998, 1 9 , 2000, 2001).
2.6

trom 48.9 to I UZ5 umho/cm, and
istorically (DPC 1989, 1992, 1993,
Specific conductance values in
ughout the year except during the
ses, in bottom conductance values
le iron and manganese from the
s phenomenon is common in both
utic oxygen depletion (Hutchinson
pH and Alkalinity
During 2000, pH and alkalinity values were similar among MNS discharge, mixing and
background zones (Table 2-5); they were also similar to values measured in 2000 (Table
2-5) and historically (DPC 1989, 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000,
2001). Individual pH values in 2001 ranged from 6.3 to 8.1, whereas alkalinity ranged
from 14.0 to 35.0 mg/L of CaCO3.
Major Cations and Anions
The concentrations (mg/L) of major ionic species in the MNS discharge, mixing, and
mid -lake background zones are provided in Table 2-5. The overall ionic composition of
Lake Non-nan during 2001 was similar to that reported for 1999 (Table 2-5) and
previously (DPC 1989, 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000, 2001).
Lake -wide, the major cations were sodium, calcium, magnesium, and potassium, whereas
the major anions were bicarbonate, sulfate, and chloride.
Nutrients
Nutrient concentrations in the discharge, mixing, and mid -lake background zones of Lake
Norman for 2000 and 2001 are provided in Table 2-5. Overall, nitrogen and phosphorus
levels in 2001 were similar to those measured in 2000 and historically (DPC 1989, 1990,
1991, 1992, 1993, 1994, 1995, 1996, 1997, 1998, t999, 2000, 2001). Total phosphorus
concentrations in 2001, however, averaged about one-third to one-half of the values
measured in 2000 for each of the zones investigated, but were well within the historical
2-7

range (DPC 1989, 1990, 1991, 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000,
2001) (Table 2-5).
Metals
Metal concentrations in the discharge, mixing, and mid -lake background zones of Lake
Norman for 2001 were similar to that measured in 2000 (Table 2- ) and historically (DPC
1989, 1990, 1991, 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000, 2001). ;Iron
concentrations near the surface were generally law (:5: 0.1 mg/L) during 2001, whereas
iron levels near the bottom were slightly higher during the stratified period Similarly,
manganese concentrations in the surface and bottom waters were generally low (:5 0.1
mg/L) in bath 2000 and 2001, except during the summer and fall when bottom waters
were anoxic (Table 2-). This phenomenon, i.e., the release of iron and manganese from
bottom sediments because of increased solubility induced by low redox conditions (low `
oxygen levels), is common in stratified waterbodies (Wetzel 1975). Manganese
concentrations near the bottom rose above the NC water quality standard (0.5 mg/L) at
various locations throughout the lake in summer and fall of both years, and is
characteristic of historical conditions (DPC 1989, 1990, 1991, 1992, 1993, 1994, 1995,
1996, 1997, 1998, 1999, 2000, 2001). Heavy metal concentrations in Lake Norman clever
approached NC water quality standards, and there were no :appreciable differences
between 2000 and 2001.
FUTURE STUDIES
No changes are planned for the Water Chemistry portion of the Lake Norman
maintenance monitoring program during 2002.
SUMMARY
Temporal and spatial trends in water temperature and DO data collected in 2001 were
similar to those observed historically. Temperature and DO data collected in 2001 were
within the range of previously measured values.
2-

Reservoir -wide isotherm and isopleth information for 2001, coupled with heat content
and hypolimnetic oxygen data, illustrated that Lake Norman exhibited thermal and
oxygen dynamics characteristic of historical conditions and similar to ether Southeaster
reservoirs of comparable size, depth, flow conditions, and trophic status.
Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 2001 was
generally similar to historical conditions. All chemical parameters measured in 2001
were within the concentration ranges previously reported for the lake during both MNS
preoperational and operational years. As has been observed historically, manganese
concentrations in the bottom waters in the summer and fall of 2001 often exceeded the
C water quality standard. This is characteristic of waterbodies that experience
hypolinmetic deoxygenation during the summer.
LITERATURE CITED
Coutant, C. C. 1985. Striped bass, temperature, and dissolved oxygen: a speculative
hypothesis for enviromnental risk. Trans. Amer. Fisher. Soc. 114:31-61.
Cole, T. M. and H. H. Hannon. 1985. Dissolved oxygen dynamics. In: Reservoir
Limnology: Ecological Perspectives. 1 . W. Thornton, E. L. Kimmel and F. E.
Payne editors. John Wiley & Sons. NY.
Duke Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke
Power Company, Charlotte, NC.°
Duke Power Company. 1987. Lake Norman maintenance monitoring; program.. 1986
summary:
Duke Power Company. 1988a. Lake 'Norman maintenance monitoring program. 1987
summary.
Duke Power Company. 1988b. Mathematical modeling; of McGuire Nuclear Station
thermal discharges. Duke Power Company, Charlotte, NC.
Duke Power Company. 1989. Luke Norman maintenance monitoring; program: 1988
summary.
2-9

Duke Power Company.
1990. Lake Norman maintenance monitoring
program: 198E
summary.
Duke Power Company.
1991.
Lake Norman maintenances monitoring program:
1990
summary.
Duke Power Company.
1992.
Lake Normanmaintenance monitoring program:
1991
summary.
Duke Power Company,
1993.
Lake Norman maintenance monitoring program:
1992
summary.
Duke Power Company.
1994,
Lake Norman maintenance monitoring program:
1993
summary.
Duke Power Company.
1995.
Lake Norman maintenance monitoring program:
1994
summary.
Duke Power Company.
1996.
Lake Norman maintenance monitoring' program.
1995
summary.
Duke Power Company.
1997.
Lake Norman maintenance monitoring program.
1996
Summary.
Duke Power Company.
1998.
Lake Norman maintenance monitoring program.
1997
Summary.
Duke Power Company.
1999.
Lake Norman maintenance monitoring program:
1998
Summary.
Duke Power Company.
2000.
Lake Norman maintenance monitoring program:
1999
Summary.
Duke Power Company.
2001.
Lake Norman maintenance monitoring program:
2000
Summary.
Ford, D. E. 1985. Reservoir transport processes. In: Reservoir inmology: Ecological
Perspectives. K. W. "Thornton,
B. L. Kimmel and F. E. Payne editors. Jahn
Miley
& Sons. NY.
2-10

Hannan, H. H., 1. R. Fuchs and D. C. Whittenburg. 1979 Spatial and temporal patterns of
temperature, alkalinity, dissolved oxygen and conductivity in an ofigo-
mesotrophic, deep -storage reservoir ini Central Texas. Hydrobilologia, 51 (30);
209-221.
Higgins, J. M. and B. R. Kim. 1981. Phosphorus retention models for Tennessee Valley
Authority reservoirs. Water Resour. Res., 17:571-576.
Higgins, J. M., W. L. Poppe, and M. L. lwanski. 1981. Eutrophication analysis of TVA
reservoirs. In: Surface Water Impoundments. H. G. Stefan, Ed. Am. Soc. Civ.
Eng., NY, pp.404-412.
Hutchinson, G. E. 1938. Chemical stratification and lake morphometry. Proc. Nat. Acad.
Sci., 2463-69.
Hutchinson, G. E. 1957. A Treatise on Limnology, Volume 1. Geography, Physics and
Chemistry. John Wiley & Sons, NY.
Hydrolab Corporation. 1986. Instructions for operating the Hydrolab Surveyor Datasonde.
Austin, TX. 105p.
Matthews, W. J., L. G. Hill, D. R. Edds, and F. P. Gelwick. 1980. Influence of water
quality and season on habitat use by striped bass in a large southwestern reservoir.
Transactions of the American Fisheries Society 118: 243-250.
Mortimer, C. H. 1941. The exchange of dissolved substances between mud and water in
lakes (Parts I and 11). J. Ecol., 29:280-329.
Petts G. E., 1984. Inipounded Rivers: Perspectives For Ecological Management. John
Wiley and Sons, New York. 326pp.
Ryan, P. J. and D. F. R. Harleman. 1973. Analytical and experimental study of transient
cooling pond behavior. Report No. 161. Ralph M. Parsons Lab for Water
Resources and Hydrodynamics, Massachusetts Institute of Technology,
Cambridge, MA.
Stumm, w. and J. J. Morgan. 1970. Aquatic chemistry: an introduction emphasizing
chemical equilibria in natural waters. Wiley and Sons, Inc. New York, NY 583p.
2-11

Wetzel, R. G. 1975. Limnolagy. W. B. Saunders Company, Philadelphia, Pennsylvania,
743pp.
2-12

Table 2- 1, Water chemistry program for the McGuire Nuclear station PDES long-term monitoring on Lake Norman.
2002 McGUIRE NPDES SAMPLING PROGRAM
PARAMETERS
LOCATIONS
Lo
2.0 4.0
5,0
8,0 9.5 1 Lo
0A
14,0 15,0
15.9 610
69.0 72,0
Wo Wo
DEPTH (in)
33
33 5
20
32 23 27
21
10 23
23 15
7 5
4 3
SAM CODE
IN -SITU ANALYSIS
Temperature
Dissolved Oxygen
Hydrolab
Hydrolab
In -situ measurements are collected monthly at the above locations at I m intervals from 0.3m to I above bottom,
PH
Hydrolab
Measurements are taken weekly from July -August for striped bass habitat.
Conductivity
Hydrolab
NUTRIENT ANALYSES
Ammonia
AA -Nut
Q/T,B
Q/T,B Q/T
Q/T,B
QIT,B Q/T,B QMB
Q/T'8
Q/T
QIT'B
Q/T,B
Q(T'B
QtT,B
SIT
SrT
Nitratc+Niolte
AA -Nut
Q/T,B
Q/T,B Q/T
QIT'B
Q/T,B
Q/ r,g Q/TjJ Qrr,B
Q/T,B Qtr'B Qfr,B
Q/T,B
Q/T,B
Q/T
QIT
Q/T,B
Q/T,B
SIT
Orthophosphate
Total Phosphorus
AA -Nut
AA-TP,DG-P
QIT,B
Q/T,B
Qrr,B Q/T
Q/T,B Q/T
Q/T,B
Q/T,B Q/T,8 Q/T,B
Q/T,B
Q/T
Q/T,B
Q/T,B
S/T
S/T
Silica
AA -Nut
Q/TB
Q/T,B Q/T
Qrr,B
Qrr,B Q/T,B Q/T,B
Q/T,B
Q/T
Q/T,B
Qrr,8
Q/T'8
Q/T,B
SIT
Cl
AA -Nut
Q/T,B
Q/T,B; Q/T
Q/T,B
Q/T,B Q/T,B Q/T,B
Q/T,B
Q/T
Qrr,B
Q/T,B
TKN
AA-TKN
Q/T,B
ELEMENTAL ANALYSES
Aluminum
ICP-24
Q/T,B
S/T,B S/T
Q/T,B
Q/TB Qrr,B Q/T,B
Q/T,B
Q/T
Qfr,a
Q1T'8
Q/T,B
Qfr,B
S/T
S/T
Calcium
ICP-24
Q)TB
Q/T,B
QiTB Q/T
Q/T,B Q/T
Qrr,B
Qrr'8
Q/T,B Q/T,B Q/T,B
Q/T,B Qrr,B Q/TIB
Q/T,B
Qrr,B
Q/T
Q/T
Q/T,B
Qrr,B
S/T
Iron
Magnesium
ICP-24
ICP-24
Q/Tj3
Q/T,B Q/T
Q/T,B
Q/T,B Q/T,B Q/T,B
QIT,B
Q/T
Q/T,B
Qrr,B
Q/T,B
SIT
SIT
Manganese
ICP-24
Q/T,B
QITB Q/T
Q/T,B"
Q/T'a Q/T,B Q/Tj3
Q/T'8
Q/T,B
Q/T,B
off
Q/T
Q/T,B
Q/T'B
Q/T,B
SIT
Potassium
306-K
ICP-24
Q/T,B
Q/T'a
Q/T,B Q/T
Q/T,B Q/T
Q/T,B
QjT'B
Q/T,B' Q/T,B
Q/T,B Q/T,B Q/TB
Q/T,B
Q/T
Q/T,B
Q/T,B
SIT
Sodium
Zinc
ICP-24
Q/T,B
Q/T,B Q/r
Q/T,B'
Q/T,B"Q/T,B' Q/T,B
Q/T,B
QIT
Q/T,B
Qrr,B
SIT
Cadminum
HGA-CD
S/T,B S/T
S/T,B S/T,B
SIT
S/T
S/T,B
Str'B
S/T
S/T
Copper
HOA-CU
S/T,B S/T
S/T,B S/T
S/T,B S/T,B
S/T,B S/T,B
S/T
SIT'n
SIT
Lead
HGA-PB
ADDITIONAL ANALYSES
Alkalinity
T-ALKT
Q/T,B
Qrr,B Q/T
Q/T,B
Q/T,B Q/TB Q/T,B
Qrr,B
Q/T
Q/T
Q/T,B
Q/T,B
Q/T,B
Q/T,B
S/T
S/T
Turbidity
F-TURB
Qrr,B
Q/T,B Q/T
Q/T,B
Q/T,B Q/T,B Q/Tj3
Q/T,B
S/T
S/T,B
S/T
Sulfate
UV_SO4
S/T,B SIT
S/T,B S/T
S/T,B
StTB
S/T
SfT,B
S/T
Total Solids S-TSE
Total Suspended Solid! S-TSSE
SrrB SIT
S/T,B
S/T
S/T,B
S/T
CODES: Frequency Q - Quarterly (Feb, May, Aug, Nov)
S - Semi-annually (Fcb,Aug)
T - Top (0.3m) B = Bottom (I m above bottom)

Table 2-2.
Water chemistry methods and, analyte detection limits for the McGuire Nuclear Station NPDES long-
term maintenance program for Lake Norman.
yXiati.t:1
Alkalinity, total
Method
Electrometria titration to a pH of 5.12
F1=111101
40C
lmg-CaCO3-1*1
0.3 T1
Aluminum
Atomic emission/ICPdirect injecition
O5% HNC,
mg
0,050
Ammonium
Cadmium
Automated phonate'
Atomic absorption/graphite fumace-direct injection
40C
O5% HNOs
mg.1.1
0,1 µg,l"
Calcium
Atomic emissionACP-direct injecition2
0,5% HNO3
0.04 mg
1,0 T,
Chloride
Conductance; specific
Automated fmicyanidel
Temperature compensated nickel electrode'
411C
In -situ
mg
Igmho,cm*l
Copper
Atomic absorption/graphite furnace -direct injection
0.5% HNO,
0.5 PgTl
0,10 -r,
Fluoride
Iron
Potentiometricl I
Atomic emission/ICP.direct injection
40C
O�5% HNO3
mg
O� I mg T,
Lead
Atomic absorption/graphite fumace-direct injection 2
0,5% HNO,
2,0 pgT1
0,001 .1,
Magnesium
Atomic emission/ICP-direct injection'
0,5% HNO,
HNO,
mg
0,003 mg T1
Manganese
'Witrite-Nitrate
Atomic emission/1CP-direct injection'
Automated reduction'
0.5%
40C
0.050 mg T"
Orthophosphate
cadmium
Automated ascorbic acid reduction'
40C
0.005 mg T,
Oxygen, dissolved
Temperature compensated polarographic cell'
In -situ
0,1 mg T,
pH
Temperature compensated glass electrode'
In -situ
0A std. units*
Phosphorus, total
Persulfate digestion followed by automated ascorbic acid
40C
0,005 mg °.1 #*
reduction'
0.015 mg T,
Potassium
Atomic absorption/graphite furnace -direct injeotion2
0.5% HNO,
O. I mg `1*1
Silica
Automated molydosilicatel
40C
0.5 mg T,
Sodium
Atomic emission/ICP.direct injection'i
0.5% HNO,
0,3 mg T1
-1*1
Sulfate
Turbidimetric, using a spectrophotometerl
4°C
I .O mg
Temperature
Thermistor/thermometerl
In -situ
0AOC*
Turbidity
Nephelometrio turbidity'
40C
I NTU*
Zinc
Atomic em issior,/ICP- direct injection
0,5% HNO3
4 ligTl
'United States Environmental
Protection Agency 1979. Methods for chemical analysis of
water and wastes,
Environmental Monitoring and Support Laboratory, Cincinnati, OH.
'USEPA. 1982
'USEPA. 1984
*Instrument sensitivity
used instead of detection limit.
*Detection limit changed doting 1989.

Table -3. Heat content calculations for the thermal regime in Lake Norman
for 2000 and 2001.
2001
2000
Maximum areal heat content (g cal/cm }
27,964
27,44
Minimum areal heat content (g cal/cm2)
7451
806
Maximum hypolimnetic (below 11.5 )
15,173
15,459
areal heat content (g cal/cm )
Birgean heat budget (g cal/cm 2}
20,513`
19,368
Epilimnron (above 11.5 m) heating
0.094
0.106
rate ('C /clay)
Hypolimnion (below 11.5 m) heating
0.062
0.082
rate (°C /clay)
2-1

Table 2-4. A comparison of areal hypolimnetic oxygen deficits (AHOD),
summer
chlorophyll
a (chl a); secchi depth (SD), and mean depth of Lake Norman
and 18 TVA reservoirs.
AHOD
Summer Chl a
Sec hi Depth
Mean Depth
Reservoir
(mg/cm2/day)
(ug/L,)
(m)
(m)
Lake Norman (2001)
0.030
5.9
2.03
10.3
TVA
Mainstem
Kentucky
0.012
9.1
1.0
5.0
Pickwick
0.010
3.9
0.9
6.
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
Nickajack
0.16
2.8
1.1
6.8
Chickamauga
0.008
3.0
1.1
5.0
Watts Bar
0.012
6.2
1.0
7.
Fort London
0.023
59
0.9
7.
Tributary
Ch tuge
0.041
5.5
2.7
9.
Cherokee
0.078
109
1.7
139
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
Norris
0.058
2.1
3.9
16.3
South Holston
0.070
6.5
2.6
23.4
Tis Ford
0.059
6.`1
2.4
149
Watauga
0.066
2.9
2.7
24.5
a Data from Higgins et al. (1980), and Higgins and Kim ( 1981)
-16

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Table 2-5. (Continued)
Mixing Zone
Mixing Zone
MNS Discharge
Mixing Zone
Background
Background
LOCATION
Surface
1.0
Bottom
Surface
2
Bottom
4.0
Surface
Surface
5.0
Bottom
Surface
8.0
Bottom
Surface
11.0
Bottom
05PTH:
PARAMETERS YEAR;
2000
2001
2000
2001
2000:
2001
2000
2001
2000
2001
2000
2001
2000
2001
2000
2001
2000
2001
2000
2001
2000
2001
Zinc (ugdl)
5
5
8
5
6
5
5
5
5
5
5
5
5
5
5
5
3
5
5
5
6
5
Feb
May
5
6
6
5
5
6
5
5
6
5
9
5
5
5
5
6
6
Aug
5
5
12
9
5
5
6
6
5
5
5
5
5
5
5
5
5
5
5
5
5
5
Nov
5
6
7
5
5
5
6
5
5
�5
6
5
5
5
5
5
5
5
5
5
5
Annual Mean
50
53
.9
8.5
6.5
5.0
5.0
5.0
6.3
6,0
5.0
5.0
5.0
5.0
5,0
5:0
5.0
5.0
5.0 -
5.3
5.0
5.0 5.0
Nfltale (ug/l)
Feb
100
110
100
120
100
120
100
120
100
110
100
110
100
120
100
110
90
110
160
150
/50
160
May
160
130
240
150
160;
130
240
150
160
140
160
130
220
150
160
130
220
170
190
640
260
140
Aug
20
30
290
260
20
30
240
270
60
30
40
30
30
170
30
30
ISO
1460
20
20
140
260
Nov
70
590
20
710
70
820
20
50
70
20
80
50
180
50
60
40
20
100
120
90
210
100'
Annual Mean
87.5
240:0
162.5
310.0
$7,5
275.0
15{},0
147,5
97.5
75.0
95.0
80.0
132.5
122,5
875
77.5
1275
d60.0
122.5
2 5.0
19t7.0
165,0
Ammonia (ugtl)
Feb
20
20
20
40
20
20
20
30
20
20
20
20
20
30
20
20
20
20
40
30
40
40
May
20
20
20
60
20
20
20
50
20
30
20
20
20
50
20
20
20
60
20
20
20
90
Aug
20
20
20
70
20
20
50
50
20
20
20
10
180
60
20
20
60
20
20
20
100
20
Nov
20
30
560
600
20
20
730
90
20
20
20
20
20
70
20
30
610
80
70
120
80
210
Annual Mean
200
225
155.0
i926
00.0
00 :
2b5.0
55.0
202O
22.5
20.0
i7.5
60.0
52.5
Z00
22.5
177.5
46.0
37.5
47.5 :
60.0.
9p.0
Total Phosphorous (ug/1)
6
4
17
63
7
4
9
7.
7
8
Feb
7
4
7
6
6
4
8
5
26
4
5
31
8
4
7
8
6
7
7
7
5
10
8
10
6
May
Aug
9
23
6
10
11
16
5
10
7
18
16
10
6
9'
8
10
6
26
10
10
10
20
10
10
10
11
10
18
10
29
17
Nov
13
10
14
10
8
10
14
10
9
10
159
10
11
10
10
10
24
18
17
11
26
11
Annual Mean
i3:0
7.5
12.0
7:5
98
i0.0
9,3 '
8.3
16.8
7.3
52,0
7.8
11.3
7.5
11.0
22:5
12.3
9,3
13.5
9.0
18,0
10.5
onnopmospnate (ug/1)
2
5
2
5
2
5
2
5
2
B
2
5
2
5
2
Feb
5
5
2
2
5
5
2
2
6
5
2
2
6
6
2
5
2
6
2
6
2
14
2
6
2
5-
2
6
2"
May
Aug
5
5
5
8
6
5
6"
5
5
5
5
7
5
7
5
5
5
Nov
5
5
5
6
5
5
5
5
E
5
5
6
5
5
5
5
5
5
5
5
5
Annual Mean
50
3.5
-5.0
4,3
5,0
3.5
�.6
5.3
4
6.0
4
5.3
4
5.3
d
7.3
4
5.0
4
5.0
4.0
5.3
4
S4,ca (mg/I)
Feb
3:3
2.9
3.2
30
3.2
310
3.3
3.0
3.2
3.0
3.2
2.9
3.2
3.0
3.3
2.9
3,1
2.9
4.1
3.6
4.0
17
May
3A
2.0
4.0
3 2
3,5
2:9
4;0
3A
3.6
2.9
3.5
2.9
3.9
3.2
3.5
3.0
3:9
3.3
3.4
2.9
4,3
3.5
Aug
2.0
2A
4S
4,0
2,0
2.7
4;6
4A
2:2
2.7
2.1
2.7
4,2
41
2.0
2,6
4.2
4.0
2A
V
4.6
4.2
Nov
2.7
3.4
5.3
4.7
2,7:
9.2
6:6
3.4
2.7
3.2
2.7
3.3
3.2
3.4
2,6
3.1
5.1
4:3
3.3
3:5
4.4
4.5
Annual Mean
2.9
2.9
4.3
3 7
2.9:
3.0
a.A
3.4
2.9
3.0
2.9
3.0
. 3.6
3A
2.9
2:9
4.,
16
32
3,2.
4,3
4.0
NS . Not Sampled

8
N
LC
5.
m
15
18
.
c�
2
Figure 2-1. Water quality sampling locations for Lake Norman.
-20

JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC
Month
10 2000 W 2001
Figure 2-2. Monthly precipitation in the vicinity of McGuire Nuclear Station.
2-21

Temperature (C)
Temperature (C)
Temperature (C)
0
5 10 15 20 25 30 35
0
5 10
15 20 25 30 35
0
5 10
15 20 25 30 35
5
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x
35-
35
35
APR
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JUNE
Temperature (C)
Temperature (C)
Temperature (C)
0
5 10 15 20 25 30 35
0
5 10
15 20 2530 35
0
5 10
15 20 25 30 : 35
0
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OCT
NOV
DEC
Temperature (C)
Temperature (C)
Temperature (C)
0
5 10 15 20 25 30 35
0
5 10 15 20 25 30 35
0
5 10 15 20
25 30 35
0
�. , _,
0
0
x
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5
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to
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20.00
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u
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F-
10.00
5.0
0.00
Jan Feb Mar Apr May Jun Jul Aug Sep tact
Nov
Dec
Month
12.00
10.00
tTs
E
0
8.00
W
6.00
0"
4
a
C? 4.00
cn
c
0
2.00
0.00
—,
Jan Fete Mar Apr May Jun Jul Aug Sep Oct
Nov
Dec
Month
Figure -5. Monthly surface (0.3m) temperature and dissolved oxygen data at
the
discharge location (loc. 4.0) in 200 (0) and 2001 (■)
2-26

JAN
FEB
MAR
Dissolved Oxygen (mg/L)
dissolved Oxygen (mg/L)
Dissolved Oxygen (mg/L)'
0 2
4 6 8 10 12
0
2 4 6; 8
10 12
0
2 4 6 8
10 12
0`
0
0
._,.
x
x
x
5
z
5
z
x
5
x
x
x
x
Xx
x
x
14
10
z ;
10
xx ,
x
_
E 15
x15
i
E 15
x
20
x
xX
..
-20
X'
.5
Cu
0 20
25x
zx
25
x
25
x
x
x
X
30
30
30
x
35
35
35
APRIL
MAY
JUNE
Dissolved Oxygen (mg/L)
Dissolved Oxygen (mg/)
Dissolved Oxygen (mg/L)
0 2
4 6 8 10 12
0
2 4 6 8
10 12
0
2 4 6 8
10 12
0
-~—
0
a
0
x
X
x
x
5
x
%
5
x
x
5
Xf
10
x
xx
10
I x
X
10
,
15
z
x
x15
le
x
v
,..
115
kx
x
20
x
X
%
.c
2t1
x
x
x.
x
25
x
25
z
25-:x
x'x
x
,%..
X.
30'
30'
30
35 `
35
35
N
kJ
Figure 2-6.
Monthly mean dissolved oxygen profiles for the McGuire Nuclear Station background zone in 2000 (xx) and 2001 (♦ �

8z-
Depth (m)
Depth (vn)
i�
:.
# K+
to..:
cx
ns
O
�
Gri
G.J C.
C} GT1
Depth (m) _
N ..
CS:; Gh C} GT
C? '.
O
Depth (m)
C.? Ld IV AV
Lri C? GT O {,y�
_
{}
C. Ci
C?
s
X
4']
t33
GJ''
Depth (m)
.v
Ci Un
Depth (m)
CS {%# 8 .r
GS
%i
i
:%

JAN
FEB
MAR
Dissolved Oxygen (mg/L)
Dissolved Oxygen (mg/L)
Dissolved Oxygen (mg/L)
0 2
4 6 8
10 12
0
2 4 6 6 10 12
0
2 4 6` 8 10 12
0
0
x
x
' `X
x
5
*
5-
10
*
14
t0
z
x,
x
z
�15
�
�15
W15
o 20
X
20
. x
e*)20
x
25
x
x
25
x
25
X
30
x
#
x
30
30
35
x
35
35
APR
MAY
JUNE
Dissolved Oxygen (mg/L)
Dissolved Oxygen (mglL)
Dissolved Oxygen (mg/L)
0 2
4 6 8
10 12
0
2 4 6 8 10 - 12
0
2 4 6 8" 10 12
0
��
0
y
0
5
x
X
x
5
X
X
x
Xx
x'
10
10
XX
10
;
15`
X'
X15
X
x,
zx15
X
X
xx
c
20
X
X
-20
x
X
x
C:S
. x
+'
x
X
X
X
X
25
z
25
z
25
X
30
x
x
X
30
X
X,
X
30
X
X
X
z
35
x
x
35
35
e
t�J
V. ,, ri n '7
R,s-4,1<} —�. A;ov^1irpA ,,vm vAn „rr%filoc frNr flip Mt -(I rp N„ Apnr Crar,nn m,xtncr 7nna ,n g.flon t ) and 2001 � ♦ a ):

Qc`
Depth (m)
Depth (m)
tea'+ Jry
Cl
xNY4NNN NNN�
�
�
:
e X
•x>C X
N:x X X
e
LL
C
kf
C>
t?}
x KN.....X%%NN5tX��XNN
�
'tx
N
x
cu
-WIP
Depth (m)
b ZA O tx'i
N
b
tae 0.. JY
N
tas "O
Depth (m)
teal V+ O
•}tX XKX.
}€
X f %xNXx
Xx
... �Cx xx
G1.C>O„
C>
C%9 50
hl
N
Depth (m)
Depth (m) 8
cs
':
x
icl
.A
a
m
.X
r>2<1
.xNNXNxN
XX
w
—`�
SOU
kl x
to
XNNMN%........NNNNNN...NYC
xyl}r.NNNNN

240-
Sampling Locations
Sampling Locations
235- 1.0 8.0 1110 Me 1s'0 16.9 62,0 $9.0 72.0 80.0
235- 8.0 MO 13.0 Me 1&0 $2.0 69.0 72.0 MO
C� P�
230;
22
22 a 71*5
E
nr
> 20-
220: 2
E 215:
cc 21
21 C;
LU 21
205-
20 -
Temperature (deg C) 200: Temperature (deg C)
20C�
Feb 6, 2001
Jan 3, 2001 1
0
195� 'T -50 25 3 S 40 45 so 55
15
0 5 10 1'5 .... jo .... jS dO 35 ZO 45 so 55 0 5 ... 10 .... i's... L
Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)
240-
240- -
- Sampling Locations Sampling Locations
235 ic sc 13.0 MO MO 62.0 69.0 72.0 80.0 235-1,0 8.0 11'0 110 Mo 1&9 SZO 69.0 72.0 soc
230-
230;
225-
225'
> 220:
220- 2 -
E 215
21
E-D
21
21
205-
205-
Temperature (deg C)
Temperature (deg C) 200:
200
Mar 8,2001 Apr 2,2001
I T-T-T--,,-T--- ' I I .... I
19
0 5 10 iIs 's io 2t 30 35 40 45 so 55 0 5 10 20 25 30 35 40 45 50 55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
Figure 2-8. Monthly reservoir -wide temperature isotherms for Lake Norman in 2001.

24
Sampling Locations
23 1.0 8.0 MO 13.0: 15.0 M9 "62.0 Me 72.0 80.0
23 `2 ✓`24x y"a c
22
22
0 22
^
Ki
v
1.
.2.: 21
21
14 75,
w 21
73a
21
...��
2a
20
Temperature (deg C)
2a
Temperature (deg C)
20
Apr 30, 2001
Jun 4, 2001
19
a 5 1a
15 2a 25 30 35 4a 45 60 55
,9
0
5 1Ct 15 2a 25 3a 35 40 45 50 55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
24
24
Sampling Locations
Sampling locations
23
i.0 8.0
11.0 :13.0 15.0 MO" 62.0 69.0 Me' 80.0
23511.0
L
8.0 11,0 13.0 Me i6.9 62.0 69.0 72.0 80.0
L L 1 L 1 1 L L 1
L L
d d i 1 1 1 1 L
23
Z`�o>
�3
22
w
22
2J/
m
22
26
24,
22
21,
0 21
\
21
a
20
1
20
Temperature (deg C)
20
Temperature (deg C)
20
Jul 9, 2001
Aug 6, 2001
19
19
0
5 10 15: 20 25 30 35 40 45 50 55
0 5 10
i5 20 25 30 35 40 45 50 55
}
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
Figure -8.
Continued.

205-
200,
Distance from Cowans Ford Dam (kM)
P40-�-
24:1--
10
23 so 7
1
230�
Sampling Locations I

ua 210.
2o5-
200-
195
240
235
230
225
220
E
215
m
eu
210
205
200
Distance from Cowans Ford Dam (km
L✓'IOOvawcu vnyy�,a+ ktllyj y
Feb 6, 2001
15 20 25 30 35 40 45 50 55
Distance from Cowans Ford Dam (km)

22 22 4 W
' 21
21
uD 1
21
205 0 20
Dissolved Oxygen (mg/1) 20 Dissolved Oxygen (mall)
20
Apr CI, t}C}1 Jun 4, 2001
19
i45 50 55 0 5
Q iQ i5 20 25 30 35 40 10 15 20 25 30 35 40 45 50 55
DDistance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km}
24 24
Sampling Locations Sampling Locations
23 t„0 5.t7 St;Q i3,0 TS.t} #5.9' 62.0 69.0 72.4. 80.0 23 4.0 e.0 Mo 130 15.0 15.9 62.0 6010 "72.0 80.0
23 c} A, lea >r 4 3 r' 0 qs
22
j 22``�
2204 2_ 22 A o
7 21 �0"k
21
21 � 21
1
20 2fi3
. ) Dissolved Oxygen (mg/1) 20Dissolved sc lve Oxygen (mall)
20
Jul 9, 2001 Aug 6, 2001
1 i9
y 0 5 i 0 i 5 20 25 3035 40 45 50 5 0 5 10 i 5 20 25 30 35
40 4 0 55
" Distance from Cowans Ford Dam (km) Distance from Cowans Ford Darn (km)
Figure -, Continued.

222255:
22,C 220-
E
21 215'
10 21 .- 210
01
2020/7
A.
Dissolved Oxygen (mg/1) 200: C> Dissolved Oxygen (mg/1)
20 Sep 5, 2001 Oct 1, 2001
T_r_r
19 ­T-T_ -IT- ' 'T 'T 1 11 30 3_5 40
0 5 10
15 20 25 30 35 40 45 50 55 0 5 10 15 20 25 45 so 55
Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)
240- 240
Sampling Locations Sampling Locations
235 0 e.o 1110 134 164 15.9 62.0 6910 72,0 $0.0 51355,1,0 8.0 1110 13:0 16,0 15,9 62,0 69"0 72.0 80.0
1 4 1
23
225: 225-
220- 220-
S
21.5 215-
cu -
210:6.210:
20 s: co 20
20 Dissolved Oxygen (mg/1) 20c; Dissolved Oxygen (mg/1)
Dec3,2001
Nov 5, 2001
—T T I 1 4 1 5 5 1 0 5 , 5
35 40 0 5 10 15 20 25 30 35 40
15
0 5 10 1 W_ ' '2'0 .... 2V '3'0" 4'5... 50 55 Distance from Cowan$ Ford Dam (km)
Distance from Cowans Ford Dam (km)
Fizure 2-9. Continne-d.

30
a
0
1
ttS o a
1
J _-0-
0
0 50 100 150 200 250 300 350
Julian Cate
re 2-10a. Meat content of the entire water column (13) and the hypolimnion (Q)
in Lake Norman in'2001
`I2 100
C `3fl
0 4-3
6
0` <
4 v
0
2 20 CL
Q Q
0 50 100 150 200 250 300 350
Julian Date
ire -10b. Dissolved oxygen content (—) and percent saturation (--- of the entire
water column (®) and the hypol mnion (Q) of Lake Norman in 2001.
2-37

r"`w •,,�« a }. F.SIas � },,. k." '•,? a«+. 4a ««4 � ....
f!i 22 a a� a 2 wat Ckk a{a? x U �&
{ a s •r± c* a; '; '.�w `t�•.+ s. �"'^ y 6 t a. «av •,,.•a, E
}afi a hrat� E 2 a k ex
`E 22 a1 'i a k 4 'va+. a t "} ycF;:'• 4 l...w' }
21 art {�§ 4'+,:f �,, �.`"•� �,kaa�"d• t, 21
r aaaa t hrta{y a >
21 C�
y'#}�'«a
205—
a a r as 20
t is
20 4. Jurt 11, flfl1 20 a Jun 27, 2001
19 19
0 5 10 15 20 25 30 35 40 45 50 55 0 5 10 15 20 25 30 35 40 45 50 55
Distance from CowanCowans Ford Dam (km) Distance from Cowans Ford Cram (km)
24 24
LAKE NORMAN STRIPED BASS HABITAT LAKE NORMAN STRIPED BASS HABITAT
23 .0 8.0 11.0 13.0 15,015.9 62.0 69.0 72.0 80.0 23 .0 8.0 11.0 13.0 15.015.9 62.0 69,0 72.0 80.0
1 d 1 1 ! 1 1 1 1 1 a 1 1 1 1 1 1 1 1 l
23 23 "
E E
22yt:.:; ::.....:.: 22
21 a ^t 21
03
r } a• tSS
21a 3 i. W 21
20 20
k
20 a h. Jul 9, 2Q(?1 20 Jul 24, 2001
19
1950 5 10 15 20 25 30 35 40 45 50 55 0 5 10 15 20 25 30 35 40 45 50 55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Clam km

2
22 2
22 22�
2121
its �
21 W 21
205 0
200 Aug 6, 2001 20 Aug 20, 2001
19 19
0 5 10 15 20 25 30 35 40 45 50 55 0 5 10 15 20 25 30 35 40 45 50, 55
Distance from Cowans Ford clam (km) Distance from Cowans Ford Dam (km)
24 24
LAKE NORMAN STRIPED BASS HABITAT LAKE N RMAN STRIPED BASS HABITAT
2 3541 0 E3.0 11.0 13.0 15.015.9 62.0 59.0 72.0 80,0 .0 8.0 11.0 1 .0 M015.9 '62.0 69.0 72.0 80.0
22
ryr� ry�y +,• "� ;,"��fi tkw. � �" ,t S�w'f �+ s w �w fi *, h kt
22 o{.,.,•' {jj k $ kfi wk v1• s";"' ti
w,�fiw1 w*£i k ,.rk
s i .
E
6 E�'-"'' 22 •`•. k{ b,..3•,. $c ^y ,Y fib " .'hk "' ; Y
r 6
.ply k S5. r'sv?ti fi} d''.{ •7k f•..
21 :r' 21'' +.: fiw w,''*'fi'+..�, *.w2•+rw'wk,t wW„ "''"fi w...•
21
21
205 20
20 Sep 10, 2001 0 Sep 25, 2001
1J 1
40 4
0 5 10 i5 20 5 30 35 40 45 0 55 0 5 10 15 20 25 30 35 50 55
Distance from owan Ford Dam (km) Distance c from Co�nrans fiord Liam (km)
Figure -11. Continued,

CHAPTER 3
FHYTO PLANKTO
INTRODUCTION
Phytoplankton standing crop parameters were monitored in 2001 in accordance with the
DES permit for McGuire Nuclear Station ( S). 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,
November 2001) with historical data collected in other years during these months.
In previous studies on Lake Norman considerable spatial and temporal variability in
phytoplankton standing crops and taxonomic composition have been reported (Duke Power
Company 1976, 1985; Menhinick and Jensen 1974; Rodriguez 1982). Rodriguez (1 82)
classified the lake as oli o-mesotrophic based on phytoplankton abundance, distribution, and
taxonomic composition. Past Maintenance Monitoring Program studies have tended to
confirm this classification.
METHODS AND MATERIALS
Quarterly sampling was conducted at Locations 2.0, 5.0 (Mixing Zone), 8.0, 9.5, 11.0, 13.0,
15.9, and 69.0 in Lake Norman (see map of locations in Chapter 2, Figure 2-1). Duplicate
grabs from. 0.3, 4.0, and 8.0 m (i.e., the estimated ephotc zone) were taken and then
composited at all but Location 69.0, where grabs were taken at 0.3, 3.0, and 6.0 m due to the
shallow depth. Sampling was conducted on 9 February, 1 May, 6 August, and 5 November
2001. Phytoplankton density, biovolume and taxonomic composition were determined for
samples collected at Locations 2.0, 5.0, 9.5, 11.0, and 15.9, chlorophyll a concentrations and
seston dry and ash -free dry weights were determined for samples from all locations.
Chlorophyll' a and total phytoplankton densities and biovolumes were used in determining
phytoplankton standing crop. Field sampling and laboratory methods used for chlorophyll a,
sexton dry weights and population identification and enumeration were identical to those
3-1

used by Rodriguez (1982). Data collected in 2001 were compared with corresponding data
from quarterly monitoring beginning in August 1987.
A one way ANOVA was performed on chlorophyll a concentrations, phytoplankton densities
and seston dry and ash free dry weights by quarter. This was followed by a Duncan's
Multiple Range Test to determine which location means were significantly different.
RESULTS AND DISCUSSION
Standing Crop
Chlorophyll a
Chlorophyll a concentrations (mean of two replicate composites) ranged from a low of 1.42
ug/l at Location 2.0 in February, to a high of 32.57 ug/l at Location 69.0 in August (Table -
1, Figure -1). All values were below the North Carolina water quality standard. of 40 ug/l
(NCDEHNR 1991). Lake -wide mean chlorophyllconcentrations were within ranges of those
recorded in previous years (Figure 3-2). The seasonal trend in 2001 of minimum, values in
February, increasing slightly in May, achieving maximum values in August, then declining to
the second highest levels in November, has never been observed during the course of the
Lake Norman Maintenance Monitoring Study. Based on quarterly mean chlorophyll
concentrations, Lake Norman was in the mesotrohic range during 2001, although a number
of individual values were less than 4 ug/l (oligotrophic) and greater than 12 ug/l ;(eutrophic).
Lake -wide quarterly mean concentrations of below 4 ug/l have been recorded on 'eight
previous occasions, while concentrations of greater than 12 ug/l were only recorded during
May 1997, and May 2000.
During 2001 chlorophyll a concentrations showed somewhat less spatial variability than. in
2000. Maximum concentrations were observed at Location 69.0 during all quarters, while
minimum concentrations occurred at Location 2.0 in all but August (Table -2). The trend of
increasing chlorophyll concentrations from down -take to up -lake, which had been observed
during most quarters of 2000, was apparent in varying degrees during all quarters of 2001
(Table 3-1,` Figure 3-1). Locations 15.9 (uptake, above Plant Marshall) and 69.0 (the
uppermost riverine locations) had significantly higher chlorophyll values than Mixing Zone
locations during all sample periods (Table 3-). Flow in the riverine zone of a reservoir is
subject to wide fluctuations depending, ultimately, on meteorological conditions (Thornton,
3-

et al. 1990), although influences maybe moderated due to upstream dams. During periods of
high flow, algal production and standing crop would be depressed., due in great part, to
washout. Conversely, production and standing crop would increase during periods of low'
flow and high retention time, Over long periods of low flow, production and standing crop
wouldgradually decline once more. These conditions result in the high variability in
chlorophyll concentrations observed between Locations 1.9 and 69.0 throughout the year, as
apposed to Locations 2.0 and 50 which were very similar during each sampling period.
Average quarterly chlorophyll concentrations during the period of record: (August 1987
November 2001) have varied considerably. During February 2001, Locations 2.0 through
13.0 had chlorophyll concentrations in the low range, and the :value at Location 5.0 was the
lowest yet recorded for February (Figure -3). The chlorophyll concentration at Location
15.9 was in the intermediate range, while the value at Location 69.0 was the highest February
chlorophyll yet observed. Long term February peaks at locations 2.0 through 9.5 occurred in,
1996; while long term February peaks at Locations 11.0 through 15.9 were observed in 1991.
As stated above, the highest February value at location 69.0 occurred in 2001. Locations 2.0
through 9.5 had lower chlorophyll concentrations in February 2001 than in February 2000,
while concentrations at Locations 11.0 through 69.0 were higher than in February 2000.
During May 2001 chlorophyll concentrations at Locations 2.0 through 11.0 were in the low
range, in fact the concentrations at Locations 5.0 through 11.0 were the lowest recorded. for
May. Location 1 .0 was in the intermediate range for May, while the value at 15.9 was i
the high range. Once again, Location 69.0 demonstrated a record high value for May (Figure
3-3). Long term May peaks at Locations 2.0 and 9.5 occurred in 1992; at location 5.0 in
1991; at Locations 8.0, 11.0, and 13.0 in 1997 and at Location 69.0 in 2001. All but
Locations 69.0 had lower chlorophyll concentrations in May 2001 than daring this period in
2000.
August 2001 chlorophyll concentrations at most locations were in the intermediate range.
The concentration at Location 69.0 was the highest August concentration yet observed at this
location (Figure -3). Long term. August peaks in the Mixing Zone' were observed in 199
while year-to-year maxima at Locations 8.0 and 9.5 occurred in 1993. Long term August
peaks at Locations 11.0 and 13.0 were observed in 1991 and 1993, respectively. The highest
August chlorophyll concentration from Location 15.9 was observed in 1998, while Location:
69.0 experienced its long terrn August peak in 2001. Locations 2.0 through 13.0, and 69.0
3-3

I higher August concentrations in 2001 than in 2000, while concentrations at all ott
ations were lower than the previous year.
November 2001, chlorophyll concentrations were in the low range at Locations
au 9.5. At Locations I LO through 69.0, November 2001 chlorophyll concentratio
re in the intermediate range (Figure 3-3). Long term November peaks at Locations 5
and 11.0 through 15.9 occurred in 1996; while November maxima at Locations 2.0 a
were observed in 1997. The highest November chlorophyll concentration at location 6�
,erred in 1991. All but Location 15.9 had higher November values in 2001 than in 2000
tal Abundance
nsity and biovolurne are measurements of pbytoplankton abundance. The lowest dens
ring 2001 occurred at Location 2.0 in February (669 units/ml), and the lowest biovolul
)8 mm3/m3) occurred at Location 5.0 during May (Table 3-3, Figure 3-1). The maximA
isity (6,430 units/ml) and biovolume (4,468 mm3/m3) were observed at Location 15.9
ty. Phytoplankton standing crops during February and November 2001 were genera
rher than those of February and November 2000, while May 2001 standing crops wi
ver than in May 2000 (Duke Power Company 2001). August 2001 densities wi
aerally higher than those of August 2000, while biovolumes during August 2001 w,
)st often lower than those of August 2000. Pbytoplankton densities and biovolumes dur�
01 never exceeded the NC guidelines 10,000 units/ml density, and 5,000 mm3/,
volume (NCDEH.NR 1991). Densities and biovolumes in excess of NC guidelines w,
-orded in 1987, 1989, 1997, 1998; and 2000 (Duke Power Company 1988, 1990, 191,
99,2001).
ital densities at locations in the Mixing Zone during 2001 were within the same statisti
iges, during all sampling periods but February (Table 3-4). In all sampling periods exe
igust, Location 15.9 had significantly higher densities than both Mixing Zone locatio
tring August, Location 9.5 had the maximum density, and was in the same statistical, rat
Location 15.9 and Mixing Zone locations. During all but August, phytoplankton densil
owed a spatial trend similar to that of chlorophyll, that is lower values at down-],,
rations versus up -lake locations.

Seston
, 0dry ; + r rAOA"f ergQ"ii�r't
I VII ash -free weights a �F;n mnt
inding crops. In some cases, this relationship held t
W, which had the highest ash -free dry weights, as
tring all quarters of 2001 (Tables 3-1, 3-2, and
,mparatively high ash -free dry weights in February,
aximurn density values during these periods (Table
-riods, the only significant statistical difference was
np-e than other locations. The proportions of ash fr(
2001 were slightly lower than in 2000, and similar to those of 1999, indicating very
change in inorganic inputs during those three years. Between 1994 and 1997 a tre,
declining or ratios was observed (Duke Power Company 1995, 1996,
1998, 2001).
Secehi Depths
Secchi depth is a measure of light penetration. Secchi depths were often the invej
S,tjq,n(-.ndt-.d -,odiment keston dry wei0it). with the shallowest denths at Locations
through 69.0 and deepest ftom Locations 9.5 through 2.0 down -lake. Depths ranged tr
1.10 rn at Location 69.0 in May, to 3.50 rn at Location 11.0, also in May (Table 3-1). 1
take -wide mean secchi depth during 2001 was the second highest recorded sir
measurements were first reported in 1992. The highest lake -wide mean secehi depth N
recorded for 1999 (Duke Power Company 1993, 1994, 1995, 1996, 1997, 1998, 1999, 20
2001). Again, high secchi depths were likely due to low rainfall over the past few years.

Community Composition
One indication of "balanced indigenous populations" in a reservoir is the diversity, or
number of taxa observed over time. Lake Norman typically supports a rich community of
phytoplankton species, this was also true in 2001. Nine classes comprising 64 genera and
118 species, varieties, and forins of phytoplankton were identified in samples collected
during 2001, as compared to 81 genera and 172 lower taxa identified in 2000 (Table 3-6).
The 2001 total represented an average number of individual taxa based on monitoring since
1987. Two taxa previously unrecorded during the Maintenance Monitoring Program were
identified during 2001.
Species Composition and Seasonal Succession
The phytoplankton community in Lake Norman varies both seasonally and spatially within
the reservoir. In addition, considerable variation occurs between years for the same months
sampled.
Diatoms (Bacillariophyceae) dominated densities at all locations in February 2001 (Table 3-
7, Figures 3-4 through 3-8). In May, cryptophytes (Cryptophyceae) were dominant at all but
Location 15.9, where diatoms were predominant. During most previous years, cryptophytes,
and occasionally diatoms, dominated February phytoplankton samples in Lake Norman.
Diatoms have typically been the predominant forms in May samples of previous years;
however, cryptophytes dominated May samples in 1988, and were co -dominants with
diatoms in May 1990, 1992, 1993, and 1994 (Duke power Company 1989, 1990, 1991, 1992,
1993, 1994, 1995, 1996, 1997, 1998, 1999, 2000, 2001). The most abundant diatoms during
February were Tabellaria fenestrata (Locations 2.0 through 11.0), and Melosira distans
(Location 15.9). During May, the most abundant cryptophyte was the small flagellate,
Rhodoinonas minuta, which was dominant at all but Location 15.9, where the diatom
Fragillaria crotonensis was most abundant (Table 3-7). All of these species have been
common and abundant at various times throughout the course of the Program. Rhodomonas
minuta has been one of the most common and abundant fonns observed in Lake Norman
samples since monitoring began in 1987. Cryptophytes are characterized as light limited,
often found deeper in the water column, or near surface under low light conditions, which are
common during winter (Lee 1989). In addition, R. ininuta's small size and high surface to
3-6

volume ratio would allow for more efficient nutrient uptake during periods of limited nutrient
availability (Harris 1978)
During August 2001 diatoms dominated densities at all but Location 15.9, where ,green algae,
primarily the small des id Cosmar um asphearosporum var. strigvsum, were dominant
(Figures -4 through -). The most abundant diatom in August was the small pennate,
Anvm eoneis vitrea (Table 3-7). This same pattern was observed in .August 1999 and
August 2000. During August periods of the Lake Norman study prior to 1999, green algae
(Chlorophyceaea), ` with blue-green algae (Myxophyceae) as occasional dominants or co -
dominants, were the primary constituents of summer phytoplankton assemblages. This
pattern of diatom dominance in August periods of 1999 through 2001 was generally lake -
wide. A. vitrea was described as a major contributor to periphyton communities on natural
substrates during studies conducted from 1974 through'' 1977 (Derwort 1982). The possible
causes of this significant shift in summer taxonomic composition were discussed in the 1999
report, and included deeper light penetration (the three deepest lake -wide secchi depths were
recorded from 1999 through. 2001), extended periods of low water due to draw -down, shifts
in nutrient inputs and concentrations, and macrophyte control procedures upstream (Duke
Power Company 000) Whatever the cause, the phenomenon was lake -wide, and not
localized near MNS or Marshall Steam Station (MSS), therefore, it was most likely due to a
combination of environmental factors; and not station operations.
During November 2001, densities at all but Location 2.0 were dominated by diatoms, while
cryptophytes were most abundant at Location 2.0 (Figures 3-4 through 3-8). The dominant
species at Locations 5.0, 11.0, and 159 was T fenestrate. The dominant taxa at Locations 2.0
and 9.5 were the cryptophyte R. min ata, and the centrate diatom Cy lotell c cointa (Table -
7). During previous years diatoms have been dominant on most occasions, with occasional
dominance by cryptophytes.
Blue-green algae (yxophycee), which are often implicated in nuisance blooms, were never
abundant in 2001 samples. Their overall contribution to phytoplankton densities was lower
in 2001 than in 2000 and 1999. Densities of blue -greens seldom exceeded 2% of totals. The
highest percent composition of My ophyceae (2.5%) during all sampling periods in 2001
occurred at Location 15.9 in August: Prior to 1991, blue-green algae were often dominant at
up -lake locations during the summer (Duke Power Company 1988, 1989, 1990, 1991, 1992).

Phytoplankton index
Phytoplankton indexes have been used with varying degrees of success ever since the
concept was formalized by Kolkwitz and Marsson in 1902 : (Hutchinson 1967). Nygaard
(1949) proposed a series of indexes based on the number of species in certain taxonomic
categories (.Divisions, Classes, and Orders) The Myxophycean index was selected to help
determine long term changes in the trophic status of Labe Norman. This index is a ratio of
the number of blue-green algae taxa to desmid taxa, and was designed to reflect the
"potential" trophic status as opposed to chlorophyll, which gives an "instantaneous" view of
phytoplankton concentrations. The index was calculated on an annual basis for the entire
lake, for each sampling period, and for each location during 201 (Figure 3-9).
For the most part, the long term annual Myxophycean index values confirmed that Lake
Norman has been in the oligo-mesotrephic (low to intermediate) range since 1988 (Figure 3-
9). 'Values were in the high, or eutrophic, range in 1989, 1990 and 1992; in the intermediate,
or msotrophic, range in 1991, 1993, 1994, 1996, 1998, and 2000; and in the low, or
oligotrophic, range in 1988, 1995, 1997, and 1999. The index for 2001 was lower than that
of 2000, and fell in the very low mesotrophic range.
The highest index value among sample periods of 2001 was observed in November, and the
lowest index value occurred in February (Figure 3-9). The highest lake -wide chlorophyll
was in August, with the minimum in February, therefore, the index did not completely reflect
chlorophyll concentrations observed throughout the lake during 2001. The index values for
locations during 2001 showed low values at Locations 2.0 through 9.5, with values in the
high range at Locations 11.0 and 15.. This tended to reflect the pattern of increasing algae
concentrations from down -lake to up -lake locations observed during most quarters of 2001.
During 2000, this pattern of increasing trophic state from clown -lake to up -lake locations was
also observed during most sampling periods (Duke Power Company 001).
3-8

FUTURE STUDIES
No changes are planned for the phytoplankton portion of the Lake Norman Maintenance
Monitoring program during 2002.
SUMMARY
In 2001 lake -wide mean chlorophyll a concentrations were all within ranges of those
observed during previous years of the Program. Lake Norman continues to be classified as
oligo-mesotrophic based on long term, annual mean chlorophyll concentrations. The lake_
wide mean chlorophyll in February represented the annual minimum. The take -wide mean
increased slightly during May, then increased to the annual maximum in August. The lake -
wide mean declined to the second highest value in November. This seasonal pattern had
never been recorded during the Maintenance Monitoring Study. Some spatial variability was
observed in 2001; however, maximum chlorophyll concentrations were most often observed
up -lake, while comparatively low chlorophyll concentrations were recorded from Mixing
Zone locations. Location 69.0, the furthest upstream location, demonstrated long term
maximum chlorophyll concentrations in February, May, and August of 2001. The highest
chlorophyll value recorded in 2001, 32.57 ug/l, was below the NC State Water Quality
standard of 40 ug/l.
In most cases, total phytoplankton densities and biovolumes observed in 2001 were lower
than those observed during 2000, and standing crops were within ranges established over
previous years. Phytoplankton densities and biovolumes during 2001 never exceeded the NC
guidelines for algae blooms. Standing crop values in excess of bloom guidelines have been
recorded during five previous years of the program. As in past years, high standing crops
were usually observed at up -lake locations; while comparatively low values were noted
down -lake.
Seston dry and ash free dry weights were generally lower in 2001 than in 2000, and down -
lake to up -lake differences were apparent most of the time. Maximum dry and ash -free dry
weights were most often observed at Location 69.0, while low values were most often. noted
at Locations 2.0 through 11.0. The proportions of ash -free dry weights to dry weights in
2001 were slightly lower than those of 2000, indicating little change in organic/inorganic
inputs into Lake Nonnan.
3-9

Secchi depths reflected suspended solids, with shallow depths related to high dry weight
The lake -wide mean secchi depth in 2001 was the second deepest recorded sin(
measurements were first reported in 1992. The greatest annual mean lake -wide secchi dep`
was recorded for 1999. High secchi depths over the last few years= were likely due to to
rainfall.
Diversity, or numbers of taxa, of phytoplankton had decreased since 2000, and the tot
s years. Diat,
to
4es were i
in August I
often dominant. A shift i,
mblages at Lake Norman lot
:)f 2000 and 2001. During n
August periods, green algae (and occasionally blue-green algae) dominate(
phytoplankton. This shift was likely the result of a variety of environmental factors, ai
related to station operations. Blue-green algae were less abundant during 2001 than
2000, and their contribution to total densities seldom exceeded 2%.
The most abundant alga, on an annual basis, was the cryptophyte Rhodomonas ff,
Common and abundant diatoms were Tabellariafenestrata in February and Novembe
Anomoeneis vitrea during August. Other diatoms, Melosira ditans, Fragillaria crotot
and Cyclotella conita; as well as small desmids, were occasionally dominant. All of
taxa, except A. vitrea, have been common and abundant throughout the Maintc
Monitoring Program. A. vitrea was found to be a major contributor to perif
communities on natural substrates during studies conducted from 1974 through 1977.
The phytoplankton index (Myxophycean) tended to confirm the characterization of
Norman as oligo-mesotrophic, The annual index for 2001 was lower than that of 200
was at the very low end of the intermediate range. Quarterly index values increase(
February to May, declined in August, then increased in November. Quarterly values (
completely reflect seasonal changes in phytoplankton standing crops. Location values I
to reflect increases in phytoplankton standing crops from down -lake to up -lake.
Lake Norman continues to support highly variable and diverse phytoplankton comma
No obvious short term or long term impacts of station operations were observed.
from
lid not
,ended

ERATURE CITED
xort, J. E. 1982. Periphyton, p 279-314
In J. E. Hogan and W. D. Adair (ed.). Lake
02. Duke Power Company, Production Support Department, Producti(
Envirom-nental Services, Huntersville, NC.
Duke
Power Company. 1976. McGuire Nuclear Station, Units 1 and 2, Environment
Report, Operating License Stage. 6th rev. Volume
2. Duke Power Compan
Charlotte, C.
Duke
Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke Pow
Company, Charlotte, NC.
Duke
Power Company. 1988. Lake Norman Maintenance
monitoring program: 19f
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1989. Lake Norman Maintenance
monitoring program: 19l
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1990. Lake Norman Maintenance
monitoring program: 19f
Surarnary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1991, Lake Norman Maintenance
monitoring program: 19<
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1992. Lake Norman Maintenance
monitoring program: 19�
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1993. Lake Norman Maintenance
monitoring program: 19#
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1994. Lake Norman Maintenance
monitoring program: 191
Summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1995. Lake Norman maintenance
monitoring program: 191
summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1996. Lake Norman maintenance
monitoring program: 191.
summary. Duke Power Company, Charlotte, NC.
Duke
Power Company. 1997. Lake Norman maintenance
monitoring program- 191
summary. Duke Power Company, Charlotte, NC.
3-

Duke Power Company. 1998. Lake Norman maintenance monitoring program: 1997
summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1999. Lake Norman maintenance monitoring program: 1998
summary. Duke Power Company, Charlotte, N.
Duke Power Company. 2000. Lake Norman maintenance monitoring program: 1999
summary. Duke Power Company, Charlotte, NC.
Duke Power Company, 2001. Lake Norman maintenance monitoring program: 2000
summary. Duke Power Company, Charlotte, N.
Harris, G. P. 1978. Photosynthesis, productivity and growth: the physiological ecology of
phytoplankton. Arch. Hydrobiol. Beih. Ergeb. Linmol. 10: 1-171.
Hutchinson, G. E. 1967. A Treatise on Linmology, Vol. 11. Introduction to the
limonplankton. John Wiley and Sons, New York, NY.
Lee, R. E. 1989. Phycology (2nd. Ed.). Cambridge University Press. 40 West 20th. St., New
York, NY.
Menhinick, E. F. and L. D. Jensen. 1974. Plankton populations, p. 120-138 In, L. D. Jensen
(ed.). Environmental responses to thermal discharges from Marshall Steam Station,
Lake Norman, C. Electric Power Research Institute, Cooling Water Discharge
Project (RP-49) Report No. 11. Johns Hopkins Univ., Baltimore MD.
North Carolina Department of Environment, Health and Natural Resources, Division of
hnvironmentai ivianagement tl)hm), W ater yuainy Section. i yy t. i Y!)u Aigai imoom
Report.
Nygaard, G. 1949. Hydrological studies of some Danish pond and lakes 11. K. danske
Vilensk. Selsk. Biol. Skr.
Rodriguez, M. S. 1982. Phytoplankton, p. 154-260 In J. E. Hogan and W. D. Adair (eds.).
Lake Norman summary. Technical Report DUKEPWR/82-02 Duke Power Company,
Charlotte, NC.
Thornton, K. W., B. L. Kimmel, F. E. Payne. 1990. Reservoir Limnology. John Wiley and
Sons, Inc. N. Y.
3-12

CD
�.
t h w —+ 1�7 00 C.h
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$
C C> C t h C C> G
C }( Ca LO 6 6 C
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-- C% -P t71
'
CJ C?C C> t dt C
i CYJ hJ GYJ N 7 to
r-+ r-i +^-+. tiJ %.i , taJ
-P C�'1 t—+r �—* tw++ �-+ h•+
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C t 4- C> '-«I P w VI
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t11 Ch `CJ CT � R
thCCtra;*-+{uj
LA "a Caw C> 0 N C?
P 0 hN)
40
t
tr.3

Table -2.
Duncan's multiple Range 'Test on chlorophyll a concentrations in Lake
Norman, NC, during 2001.
February
Location
2.0
5.0
8.0
9.5
11.0
13.0
15.9
69.0
Mean.
1.85
2.27
2.29
2.62
3.78
5.42
7.08
12.47
May
Location
2.0
9.5
5.0
8.0
11.0
13.0
15.9
69.0
Mean
1.42
1.44
1.53
1.70
1.98
6.80
12.82
14.15
August
Location
10
11.0
2.0
5.0
8.0
9
15.9
6.0
Mean
5.69
6.00
6.40
6.73
7.37
7.66
8.30
32.57
November
Location
2.0
5.0
9.5
8.0
13.0
15.9
11.0
69.0
Mean
3.34
3.46
4.47
4.71
5.72
8.10
8.21
9.54
3-14

Fable -3. Total mean phytoplankton densities and biovolumes from samples collected in
Labe Norman, NC, during ;2001.
Density (units/ml
Locations
Month 2.0
5.0
9.5
11.0
15.9
Mean
FEB
669
962
1106
1262
3275
1455
MAY
877
929
1202
1450
6430
2178
AUG
2957
3059
3221
2764
3155
3031
NOV 1286
1422
1611
2494
2873
1937
Biovolume (mrn3/m3)
Locations
Month 2.0
5.0
9.5
11.0
15.9
Mean
FEB
484
868
1258
1104
2786
1300
MAY
310
208
270
277
4468
1107
AUG
1474
1649
1706
1278
2975
1816 "
NOV 964
1180
1514
2680
2730
1814
3-15

rman
NC, during 2001.
February
Location
2.0
5.0
9.5
11.0
159
Mean
669
962
1106 '
1262
3275
May
Location
2.0
5.0
9.5
11.0
15.9
Mean
877
929
1202
1450
640
August
Location
11.0
2.0
5.0
15.9
9.5
Mean
2764
297
3059
3155
321
November
Location
2.0
5.0
9.5
11.0
1.9
Mean
126
1422
1611
2494
2873
3-16

Table 3-5.
Duncan's multiple Range Test on dry and ash free dry weights (mg/1) in
Lake Norman, NC during 2001.'
DRY WEIGHT
February
Location
5.0
11.0
2.0
8.0
9.5
13.0
15.9
69.0
Mean
0.50
0.92
0.98
1.12
1.18
1.6
2.75
7.1
May ',
Location
8.0
9.5
11.0
5.0
2.0
13.0
15.9
69.0
Mean
0.58
0.78
0.78
0.87
" 0.90
1.96
2.52
5.53
August
Location
11.0
13.0
2.0
9.5
8.0
5.0
15.9
69.0
Mean
1.45
1.67
2.04
2.07
2.18
2.32
2.39
7.43
November
Location
8.0
9.5
2.0
15.9
11.0
5.0
1.0
69.0
Mean
1.39
1.58
1.60
1.93
2.36
2.87
2.96
7.20
ASH FREE DRY WEIGHT
February
Location
5.0
8.0
9.5
11.0
13.0
2
15.9
69.0
Mean
0.8
0.59
0.63
0.70
0.85
0.93
1.09
198
May
Location
9.5
2.0
8.0
11.0
5.0
13.0
15.9
69.0
Mean
0.49
0.53
0.55
0.78
0.82
0.96
1.11
2.10
August
Location
1.0
11.0
15.9
8.0
2.0
5.0
9.5
69.0
Mean
0.88
1.06
1.31
1,56
1.58
1.67
1.80
3.11
November
Location
8.0
9.5
13.0
2.0
11.0
1.9
50
69.0
Mean
0.82
0.86
0.87
0.88
0.91
1.00
L 17
1.74
3-17

Table -6. Phytoplankton taxa identified in quarterly samples collected in Lake Norman
from February 1988 to November 2001.
i�
t
••a
an
?4m
am
I ii....
mm
Ow
no
an
k
i
MIN
w
hfifi
mom
-18

- ntinued e 2 of 1
m
Inow
jmmomk1k
am
1
NINON
+.
i
m
Munn
mm
a •,
j9
I,
1
i
r
e
1a
Ins
an
a
i
•
MINI

Table 3-6 (continued) pa e cif 10
a G. S. West
M
a
an
'j
0
MMIM
m
0
a
mmm
in
mum
a
IM
nano
an
man
Mom
mum
noun
NOMM
mom
on
0
m
mm
jmwest&Wt
a
mm
a
--min
M
on
am
Nam
mm
3-20

'rnlAl.- I-f, trnnflmjt-.dl
Daize 4 of 10
=Iwo=
M
mum
mm
mmmmm
mmmm
w -alum ON
mummmmmN
m
11022MOM
mumm
mum
mmml�
ism=,•
Manama
a
man
mmumma
man
mmmmm
m
=
mmmmu-m
a
mmmmmmmmm
mmmman
an
on 77777
mmmmmm
on
m
mmmmm
no
m
mmm
m
ma
Emmaunmmmm
mmmm
mm
IN
Munum
m
M
amm
m
m
mm
m
mm
EM
m
m
a
mm
um
1.
M
ma
MOM!
m
mm
m
mmmmmmm
Munn
mm
Om
M
m
mm
m
mm
mm
mu
mm
m
a
um
M
ihorprescott
N�q�Y.mj
m
mm
um
am
m
T411��nsgirg
U Prescott

INtr. I -A it-Antitilit-ail
Dap-e 5 of 10
Sil
mmmmmmummmm
mmmmmmmmumn
st
mmmmummmmmm
mmunnummmmmm
mmmmmmmmmumm
ammmmmmmmmms
mummummunum
mmmummmum
m
a
mummmm
No
mmomm
0-m-mom
amomm
mommumn
0
mmon
momm
womm
No
0
IBM
0
mmm
on
mom
mmma
won
mmmmmmmmmm
mumumunmu
mom
wommoulam
No
mum
MEMO
m
man
a
ON
0
15
no
No
no
on
ON
0
m
mmmmmm
Rell m.
muummu
IN
W,r cleve
3-2

'r�W.- I -A tnlN"t;tljlpA)
nap-e 6 of 10
0
M
Oman
ammulussm
OUR
n
mmusla
MMM
0
MMMMM
min
MOMM
On
a
a
Oman
a
a
a
M
amism
0
an
0
MMMM
a
MUM
a
min
0
MWOM
M
No
0
i
M
No
on
MMMM
MM
ON
ONO
0
c
an
UUMMOMM
M
MMMUMUM
a
a
On
ism
t.
am
MM
MM
MM
a
a
i.
ON
on
an
7t�l L
No
on
WON
•
MMM
ON
tZi
No
sGr4riow
ow
M
—77771
an
0

� i s
I
i !
J
i
ffi
a
l
�I
00
ice

I'l- I -A il,.v"flnll,-Al naae 10 of I
- -----------
MMMMMM
No
WWWOM
Olt
M
Woman
Is
noun
an
a
a
Oman
M
M
Noun
ON
a
NOON
an
an
an
an
an
Now
0
No
No
mom
M
0
0
M
0
M

at Lake Nonnan locations during each sampling period of 2001.
#
•
AAClLLAA7I11V-?'PVT I UhAh
a

DEN
7000
000
BI®Ut3LUME tmm3tm31
FEB MAY AUG NOV
--lr- - X--
Figure 3-1. Phytoplankton chlorophyll a, densities, and biovolumes, and s ston weights<
at locations is Lake Norman, NC, in February, May, August, and November'
2001.

14<
12 ._ ___-_ ._r---_ _. -._.__ - -__--_ _ -_-- _ _--w ____ _--r ____ __ __-_
10 ------- ______ ____ _.- - --- __- ___ __. --__ __-____
s
0
0
a 6 -
to
4 __ - - -' �- ---- _-_ ----_ _ ._
0
FEB MAY AUG NOV
MONTH
--*-987 -a-188 A- 1989 - x -198 -ar -1 91
- 4-•-199 1---1 93 5 1994 - e -1995--o--1996
--- `1997 ---1 98 6--1999 - - 2000 --o -26i11
Figure 3-2. Phytolankton chlorophyll a annual lake means from all locations in Lake
Norman, NC, for each quarter since August 1987.
-3

CHLOROPHYLL a (ugli)
FEBRUARY MAY
—ah- 2.0 --s-- 5.0 2.0 " &0
12 12 WONG ZONE
10 111X1NGZflNE _ _ __ _ __ ---_ 10 _---____. -: __ -. __. _ --_ --__
8 ____ ---- -- ----- --------- --- 8 - _ --- --_- -__-_-
6 _____-. _ _____ _ ._. ---------- g _-___ --------- _' ___ _ __ :_ - -----
4 '__ __- _ -.m_ _ _ _.. _ _ _
4 - - ----
2 __— --_._ ._ ____-----_ _ ------ ----- 2 _- ,___ _ -- _. ---------- ------
0 0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
—i— 8.0 --s — 9.5 - ;-- 8.0 --a— 9.5
20---�--- ---�- 12
10
15------ _-------------------- __. _ _--- 8
10 6 . - - - _.
5 _ __ _ 2 -----------
0 0 A+--+--r ----
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
11.0 - a— 13.0 13.0
16 30
14 _ __- -. _ ---__ - 25
12 _ ---- --------------- ---------
10-
20 - ._ . --- -
8 - 15
6 - 10
4 -
2 5 -. -- _ .. _
0 0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
{ --r-- 15.9 - -- 99.0 �- a� —15:9 —a— 69.0
16 35
14- - --- 25
jj
1g 0
A. -MI -- / 15
12 _
0W h t t h i 0
87 88 89 90 91 92 93 94 95 96 97 98" 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
YEARS YEARS
Figure 3-3. Phytoplankton chlorophyll a concentrations by location for samples collected
in Lake Norman, NC, from August 1987 through November 2001.

CHLOROPHYLL a (ug/1)
AUGUST
NOVEMBER
F-4::7-2,0
12-
12 -
10-
MIXING ZONE
-- MIXING �9 -_ ZONE ------------- ---- ----
10,
--.MIXING-Z0NE--
a -----------------
...... ... . -----------------
8-
----------- I ---------
61:
---- -- -------- ---- --
6 -
-------------- ---- -- -------- --- --------
41
---- --------------- ----- ---- - ------
4
-- --- ----- ---------
2 -
------------------------------------------- --
2
-------------- ---------- -------
0
0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
E�E- -9.5
L-t:!-10---*--9-5j
16-
—
14
14 -
------------------- --------------------------
12 -
----------------------------- -------------
12 -
---------------- ----------
10 -
--------------- ------------ ---- ------------
10 -
-------- --- - ----- -------------- - -----
8
8 -------------
-------- --- - - ------ ---
6 -
--- ------ --------------- ------ -- ---- - --
6
- ----- I'.---- ---- -- -------- ------
41
----- --- ---------- ------------
4 -
-- ---- ------------------------- ----
2 -
--- --- ------- ------------------------- -----
2
-------- --- ----- ------------------ ----------
0
0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
E4�::, —o-�-*-1 3 0
L:tjjL0 --*_- 13 0]
14-
14-
12 -
-- --------- --- ---- ------------------ ----
12 -
Al-
------- -- - - --------- ---- -- - ----- -
10 -
-- -- - ----- --- ---
-- ----- -- - -- ----------- --- --- -- --
10 -
-------- ---- ------
-
-------------- --- - --- 11 ------ --- - ---
6i---
---
6 -
--- - ----- ----- --- ----- -----
41
--- ---
41
- ------- ---- - -----
2-
--- - -- -----
2-
--------
0
0
-
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
F--4:Z1519 -4-6910
35--
25- —
30 - ---
-- ------
20-
- -- -------------- ---- ------------ ---
25-
- - -- ----- -------------------- -
20-
- -- - --------
15
5 ----
-
101
- - ---- ---- -------
10
0
0
-
87
88 89 90 91 92 93 94 95 96 97 98 99 00 01
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
YEARS
YEARS

LOC. ZO

LOC. 9.5

Lod. 15.9
8000
7000
6000
E 5000
.w
4000
W-
tt9
w 3000
Cf
2000
1000'
n:
t/
tttlttitti_illt
titlltiliiiti�
0
FEB MAY AUG NOV
ur -8. Mass composition (density and biovolume) of phytoplankton from euphotic''
zone samples collected at Location. 15.9 in Lake Norman, NC, during 2001.
3-7

MYXOPHYCEAN INDEX. LAKE NORMAN
2,O
t9
HIGH
1.5 --
1i - INTERMEDIATE
_ __.
1A
0,9
u.T
9.2
0.1
0,0
2 5 9.5 11 15.9
LOCATIONS
figure 3-9. Myxophycean index values by year (top), each season in 2000 (mid), and each
location in Labe Norman, NC, during 2001 .
3-38

CHAPTER
ZOOPLANKTON
INTRODUCTION
The objectives of the Lake Norman Maintenance Monitoring Program for zooplankton are to:
1. Describe and characterize quarterly patterns of zooplankton standing crops at selected
locations on lake Norman; and
2. compare and evaluate zooplankton data collected during this study (February, May,
August, and November 2001) with h'.
2000.
Previous studies of Lake Norman zooplank
seasonal distribution with highest values
:)n populations have demonstrated a I
nounced fall peak. Considerable spatial and year-to-year variability has been obsei
)plankton abundance in Lake Norman (Duke power Company 1976, 1985; Harnmc
nhinick and Jensen 1974).
"THODS AND MATERIALS
5.9 are defined as Background Locations. Field and laboratory methods for zooplan
anding crop analysis were the same as those reported in Hamme (1982). Zooplan
anding crop data from 2001 were compared with corresponding data from quay
.onitoring begun in August 1987.
one way ANOVA was performed on epilinmetic total zooplankton densities by qua
his was followed by a Duncan's Multiple Range Test to detennine which location m
ere significantly different.

RESULTS AND DISCUSSION
v
Y98 ul Tower CompAny I VVIV1,17, I,•
��066,2001).
4-2

watiolls than a the
(Thornton, et al. 1990). A similar trend was observed in the phytoplankton communit
(Chapter 3).
Epilinmetic zooplankton densities during all but May of 2001 were within the seaso
ranges of those observed during previous years of the Program. The mean epilimn(
zooplankton density at Location 15.9 in May 2001 was the highest value yet observed
this, or any location, during any previous quarter, This high epilinmetic zooplank
concentration, may have been a response to comparatively high phytoplankton concentratii
in this part of the take during May 2001 (Chapter 3). Although phytoplankton chloropI
and density values were not the highest ever observed; phytoplankton have typic,
displayed very high densities at this location during May. At the time of sampli
zooplankton had likely reached their peak after grazing on tile algae, which could well h,
been in decline by that time.
The highest February densities recorded during the Program at Locations 5.0 and
occurred in 1995, and in 1996 at Locations 2.0 and 11.0 (Figure 4-2). The long t(
February maximum at Location 15.9 was observed in 1992, Long term maximum densi
for May occurred at Locations 2.0, 5.0, and 9.5 in 2000, at Location 11.0 in 1995, an(
Location 15.9 in 2001. Long term August maxima occurred in 1988 at all but Location I �
which had its highest August value in 1996 (Figure 4-3). November long term maxirn�
Locations 2.0 through 9.5 occurred in 1988, and at Locations 11.0 and 15.9 in Novem
1999. Since 1990, the densities at Mixing Zone Locations in May, August, and Noverr
have not fluctuated much between years; while year-to-year fluctuations in densities dul
February have occasionally been quite substantial, particularly between 1991 and 1997. '
Background Locations continue to exhibit considerable year-to-year variability in all seas

Community Composition
4-4

Cladoera
Bvsmina was the most abundant cladoceran observed i
in most previous studies (Duke Power Company 20
comprised greater than 5% of the total zooplankton d
column samples, and was the dominant zooplankter i
Mixing Zone samples in November. Daphnia and Bo
ladocerans (Table 4-4. During May, Daphnia d
Locations 2.0, 5.0,and 95. Bosminvpsis dominated cl
(epilimnion) 11.0 and 15.9 in August. Bosminopsis
August 2001 as compared to August 2000. Diapl
cladoceran in May 2000 was never dominant among
similar patterns of Daphnia-Bosminopsis dominance h�
)gram (Duke Power Company 2001).
rig -term seasonal trends of cladoceran densities were variable: From 190 to 1993,
isities occurred in February, while in 1994 and 1995, maxima were recorded inf
gur 4-5). During 1996, peak cladoceran densities occurred. in May in the Mixing
1 in August among Background Locations. During 1997, cladoceran densities
eked in May. Maximum cladoceran densities in 1998 occurred in August. During
ximum densities in the Mixing Zone were observed in May; while Background Loco
)wed peaks in August. During 2000, peak cladoceran densities were again obsery
ry. In 2001, maximum cladoceran densities in the Mixing Zone occurred in Febt
.ile Background locations showed peaks in November. Spatially, cladocerans'were'
portant at Mixing Zone Locations than at other locations (Table 4-1, Figure 4-4).
tifera
ratlla was the most, abundant rotifer in 2001 samples. This taxon dominated r
pultions at Locations 2.0 5.0 ;(whole column), 11.0 (whole column), and 15
bruary. Kratella also dominated rotifer populations at Location '15.9 in August, at
t Location 2.0 in November (Table 4-4). P€alyarthra was dominant in most May sail
well as at Location 11.0 (eilimnion) in February, and Locations 2.0 and 5.0 in At
,nochilus dominated rotifer populations at Location 9.5 in February, Location 11.0 (N
lumn) in May, and Location 2.0 in November. Asplanchta was the dominant roti.
nples from Locations 9.5 and 11.0 in August, while Svnchaeta was the dominant roti

Location 5.0 (epilimnion) in February. All of these taxa have been identified as impol
constituents of rotifer populations, as well as zooplankton communities, in previous stu
(Duke power Company 200 1; Harnme 1982).
Long term tracking of rotifer populations indicated high year-to-year seasonal variab
Peak densities have most often occurred in February and May, with an occasional pea
August (Figure 4-5, Duke Power Company 1989, 2001). During 2001, peak densities at i
locations were observed in May.
No changes are planned for the zooplankton portion of the Lake Norman Mainte
Monitoring Program in 2002 and 2003.
SUMMARY
Maximum epilimnetic zooplankton densities most often occurred in May, while min
values were recorded in February (Locations 2.0, 5.0, and 15.9), and August (Locatio:
and 11.0). In most whole column samples, maximum densities occurred in May (Lo
15.9), August (Locations 2.0 and 5.0), and November (Locations 9.5 and 11.0). Min
values were most often observed in February. As in past years, epilimnetic densities
higher than whole column densities. Mean zooplankton densities tended to be higher a
values from downlake to uplake was observed. In add
Wc�
ilimnetic zooplankton densities during all but May of 2001 were within ranges of tj
3erved in previous years. The epilinmetic density at Location 15.9 in May 2001 was
,hest recorded during the Program, and may have represented an ongoing lag respons
,uparatively high phytoplankton standing crops uplake at that time.
Le hundred and eight zooplankton taxa have been recorded from Lake Nonnan since
)grarn began in 1987 (forty-six were identified during 2001). No previously unrepc
a were identified during 2001 �

ist often during 2001. Ov(
ghtly since 2000. Clado,
-mber, while rotifers were
.1 ol er quarters. Overall,
abundance of rotifers had increased since 2000. Historically, copepods and rotifers
shown annual peaks in May; while cladocerans, continued to demonstrate year-tc
variability.
Ik
Dt to be related to plant operations.
ITERATURE CITED
luke Power Company. 1976. McGuire Nuclear Station, Units I and 2, Environtnel
Report, Operating License Stage. 6th rev. Volume 2. Duke Power Compa
Charlotte, NC.
luke Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke Po,
Company, Charlotte, NC.
Wke Power Company. 1988. Lake Nonnan Maintenance monitoring program: 11,
Summary. Duke Power Company, Charlotte, NC.
)uke Power Company. 1989. Lake Norman Maintenance monitoring program: 11.
Summary. Duke Power Company, Charlotte, NC.
�ukc Power Company. 1990. Lake Nonnan Maintenance monitoring program: 11
Summary. Duke Power Company, Charlotte, NC.

Duke Power Company. 1991. Labe Norman Maintenance monitoring program: 1990
Summary. Duke Power Company, Charlotte, NC.
Duke Power Company:; 1992. Lake Norman Maintenance monitoring program: 1991
Summary. Duke :Power Company, Charlotte, NC. `
Duke Power Company. 1993. Lake Norman :Maintenance monitoring program: 199
Sununary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1994. Lake Norman Maintenance monitoring, program: 1993
Summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1995. Lake Norman Maintenance monitoring program: 1994
Summary. Duke Power Company, Charlotte, NC
Duke Power Company. 1996. Lake Norman Maintenance monitoring program: 199
Summary. ]Duke Power Company, Charlotte, NC.
Duke Power Company. 1997. Lake Norman Maintenance monitoring program: 196
Summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1998. Lake Norman Maintenance monitoring program: 1997 "
Summary. Duke Power Company, Charlotte, NC
Duke Power Company. 1999. Lake Norman Maintenance monitoring program: 199
Summary. Duke Power Company, Charlotte, NC
Duke Power Company. 2000. Lake Norman Maintenance monitoring program: 1999
Summary. Duke Power Company, Charlotte, NC'
Duke Power Company. 2001. Lake Norman Maintenance monitoring program: 2000
Summary. Duke Power Company, Charlotte, NC.
Hamme, R. E. 1982. Zooplankton, In J. E. Hogan and W. D. Adair (eds.). Lake Norman
Summary,Technical Report D PWRT82-02. p. 32-353, Duke Power Company,
Charlotte, NC. 40 p.
Hutchinson, G. E. 1967 A Treatise on Limnology. Vol. 1I. h troduction to Lake Biology
and the Limnoplankton. John Wiley and Sons, Inc. N. Y. 1115 pp.
Menhinick, E. F. and L. D. Jensen. 1974. Plankton populations. In L. D. Jensen (ed.).
Environmental responses to thermal discharges from Marshall Steam Station, ;Lake
Norman, North Carolina. Electric Power Research Institute, Cooling Water Discharge
Research Project (RP-49) Report No. l I., p. 120-138, Johns Hopkins University,
Baltimore, MD 235 p.
4-8

Thornton, K. W., B. L. Kimmel, F. P. Payne. 1990. Reservoir Linmology. Jahn Wiley and
Sons, Inc. New York, NY.
-

Table 4-1. Total zooplankton densities (no. X I 000/m3), densities of major zooplankton
taxonomic groups, and percent composition (in parentheses) of major taxa in
I Om to surface (I O-S) and bottom to surface (B-S) net tow samples collected
from Lake Norman in February,
May, August, and November 2001.
Sample
Locations
Date IYW
Taxon
2.0
5.0
9.5
11.0
15.9
2/9/01 10-S
COPEPODA
10.6
5.0
28.3
24.6
16.3
(24.6)
(17.4)
(46.7)
(40.2)
(63.0)
CLADOCERA
17.6
8.4
24�8
36.0
9.5
(41.0)
(29.3)
(40�9)
(58.7)
(36.7)
ROTIFERA
14.8
15.2
7.5
0.7
7.6
(34.4)
(53.3)
(12.4)
(1. 1)
(29.4)
TOTAL
43.0
28.6
60.5
61.3
33.4
B-S
depth (m)
of tow
COPEPODA
4.4
4.2
17.4
22.8
7.8
for each
(14.3)
(19-9)
(48.7)
(39.0)
(36.1)
Location
CLADOCERA
13.6
8.2
10.8
27.6
4.5
2.0=30
(43.7)
(38.8)
(30.2)
(47A)
(20.7)
5.0=18
ROTIFERA
13.1
8.7
7.5
8.0
9.3
9.5=20
(42.1)
(41.3)
(21.1)
(13.6)
(43.1)
1 1.0=25
15.9=21
TOTAL
31.1
21.0
35.7
58.3
21.7
5/1/01 10-S
COPEPODA
41.9
42.2
15.9
66.3
1013
(46�6)
(42.5)
(14.0)
(39.9)
(22.6)
CLADOCERA
7.7
9�6
9.6
27.0
M6
(8.5)
(10.3)
(8.4)
(15.9)
(2.3)
ROTIFERA
40.4
47.4
92.2
76�8
338.0
(44.9)
(47.8)
(81.5)
(45.2)
(75.1)
TOTAL
90.0
99.2
117.7
170.1
450.3
B-S
depth (m)
of tow
COPEPODA
21 �7
24.8
26.3
34.5
53.0
for each
(53.2)
(42.5)
(61.4)
(42.8)
(22.4)
Location
CLADOCERA
16
5.3
8.3
8.8
5�8
10=30
(8.9)
(9.2)
(19,4)
(10.9)
(2.4)
5.0=20
ROTIFERA
15.5
28.2
8.2
37A
183.0
9.5=20
(38.0)
(483)
(192)
(46.4)
(77.4)
1 1.0=24
15.9=20
TOTAL
40.8
58.4
42.9
80.7
241.7
4-10

11 "� 00 �
4tz
cv ',
' yr
Ca
r. ^ ... � .�, n v to �—• '"` .-. c N e � � c
09 W
c
t1a W
' C> W tQ00 LA0t,)1.0
y —+ Gar .A y to CJ 00 W P to 6 C?
P W txs w 00 (A t1i
i N G �' � Ch C> CJ � 4G iG 00
r+ .
cn-
loo
W kOtnN *3 cx�t> A GG ooC>C>C>W A R vlcn�ata3
ON CJ tA t-J IN u Ch cl, Ch C? OC 'Fs C CN
vx W wW- 1 can J tin vi tir Vi cA
. . a

Table 4-2. Duncan's Multiple Range Test on epilinmetic zooplankton densities (no. X
1 000/m3) in Lake Norman, NC during 200 1.
February Location
5.0
15.9
2.0
9.5
11.0
Mean
28.6
33.4
43.0
60.5
61.3
May Location
2.0
5.0
9.5
11.0
15.9
Mean
90.0
99.2
117.7
170.1
450.3
August Location
9.5
2.0
11.0
5.0
15.9
Mean
50.0
53.2
54.8
68.3
108.6
November Location
5.0
2.0
11.0
15.9
9.5
Mean
42.9
48.4
87.2
127.2
1,32.8
4-12

Table 4-3. Zooplankton to identifii
from 1988 through 2001.
J from samples collected quarterly on Lake Normal
Min-
Ir
ftes
c )e as
1 99
. . . ... .....
ir e
e
4

'r,qklA A-1
na2e 2 of 4
rIT
7777 77
an
77-7
KIM
•

Tn'hlf� A-1 (enntimind)
MOMMER-EW "Na
ww
tip
mmm
m
UUM
num
mmm
mill
F6
-9se
F64
NMI
4-15

Tnlylcs tl_2 fnnnfinrrrar�
na2c 4 of
fY t f
® . ,- •
4-16

Table 4-4. Dominant taxa, among copepods (adults), cladocerans, and rotifers, and their
percent composition (in parentheses) of copepod, cladoceran and rotifer
densities in Lake Norman samples during 2001.
FEBRUARY
MAY
AUGUST
NOVEMBER
COPEPODA
EPILIMNION
2.0
Epischura (6.0)
Epischura (4.7)
Tropocyclops (4.4)*
Tropocyclops (8.9)*
5.0
Tropocyclops (4.4)
Epischura (7.4)
Tropocyclops (6.7)*
Tropocyclops (8.5)
9.5
Epischura (19.8)
Epischura (6.6)
Tropocyclops (6.8)
Epischura (5.4)
11.0
Cyclops (1.6)*
Epishura (8.0)
Tropocyclops (4.3)
Tropocyclops (7.6)
15.9
Epischura (1.2)*
Epischura (3.3)
Tropocyclops (53)*
Ljrrpocydops (2.5)*
COPEPODA
LE COLUMN
2,0
Epischura (10.9)
Epischura (5.0)
Tropocyclops (4.3)
Epischura (6.8)
5.0
Mesocyclops (4.8)
Epischura (3.5)
Tropocyclops (4.9)
Tropocyclops (4.4)
9.5
Epischuria (8.6)
Epischura (4.1)
Tropocyclops (3.9)
Tropocyclops 01.3)
11.0
Epischuria (2.5)
Epischra (7.0)
Tropocyclops (5.6)
Diaptomus (9.0)
15.9
Cyclops (7.4)
Epischras (2*3)
Tropocyclops (4.0)
Tropocyclops (3.9)
CLADOCERA
EPILIMNION
2,0
Bosmina (100.0)
Daphnia (53.2)
Bosmina (78.0)
Bosmina (94.2)
5.0
Bosmina (100.0)
Daphnia (36.8)
Bosmina (64.8)
Bosmina (98.4)
9.5
Bosmina (100.0)
Daphnia (58.1)
Bosminopsis (55.7)
Bosmina (100.0)
11.0
Bosmina (95.2)
Bosmina (36.9)
Bosminopsis (63.9)
Bosmina (85.9)
15,9
Bosmina (93.9)
Bosmina (70.3)
Bosminopsis (72.4)
Bosmina (94.9)
CLADOCERA
Wfi LE COLUMN
2.0
Bosmina (98.4)
baphnia (48.3)
Bosmina (83.3)
Bosmina (85.2)
5.O
Bosinina (97.5)
Daphnia (43.6)
Bosmina (54.8)
Bosinina (93.2)
9.5
Bosmina (100.0)
Daphnia (61.7)
Bosmina (48.4)
Bosinina (98.5)
11.0
Bosmina (95.4)
Bostnina (41.4)
Bosminopsis (62.7)
Bosmina (63.1)
15.9
Bosmina (93.6)
Bosmina (68.3)
Bosminopsis (57.1)
Bosinina (86.0)
4-17

.inued)
FEBRUARY MAY
AUGUST
NOVEMBER
ROTIFERA EPILIMNION
2.0
Keratella (27.8)
Polyarthra (57.8)
Polyarthra (100.0)
Conochilus (44.1)
5.0
Synchaeta (33.6)
Plyarthra (56.2)
Polyarthra (98.5)
Keratella (63.5)
9.5
Conochilus (44.9)
Polyarthra (49.7)
Asplanchna (75.2)
Keratella (59.6)
11.0
Polyarthra (45.3)
Polyarthra (51.6)
Asplanchna (26.3)
Keratella (64.7)
15.9
Keratella (28.1)
Polyarthra (52.7)
Keratella (66.7)
Keratella (55.1)
ROTIFERA WHOLE COLUMN
2.0
Keratella (63 . 1)
Polyarthra (53.8)
Polyarthra (67.9)
Conochilus (44.4)
5.0
Keratella (37.5)
Polyarthra (56.5)
Polyarthra (98.5)
Keratella (33.7)
9.5
Conochilus (34.7)
Polyarthra (46.3)
Asplanchna (57.7)
Keratella (56.6)
11.0
Keratella (49.3)
Conochilus (43.8)
Asplanchna (26.6)
Keratella (65.0)
15.9
Keratella (45.7)
Polyarthra (5 1. 1)
Keratella (52. 1) -
Keratella (48.9)
Only adults present in samples.
4-18

10m TO SURFACE TOWS
500-
450 -
------------- ----------
---------------- --------------------------------------------------------- - -------------- -
400 -
----------------------
------------ I ------ ---------------------- --- -------------------------------------------- ----
350 -
-----------------------
------ - ----------------------------- --------------------- ------------- ------ ---------
E300 -
-- ---- - ----------
----------- ------------------------------------------------------ -------------- ---------------
!9 250 -
------ -----------
------------------------------ ------ - ------------------ --------------
x
,6 200 -
-------------- ---- ---
---------- ----------------------------------------- -------------------------
z
150 -
--------- -- -------------
---------- ----- ------------------------------ I -------- ---------- --- -------
100
-----
----------- --- ------ ------- ---- ------- -
50
---- ------------
0
ZO
5.0 9.5 11.0 15.9
BOTTOM TO SURFACE TOWS
E--*7FEB 7! 7MAY --*-AUG -4(tNO �V:]
240-
220-
--------------- --- - --- ---- -- --- - ---------- -- --- -- ---- - ------
200-
-- - -- ---
- ------- -- -------- ------- - -- -- ------ ----- - ------- -----
180 A
---- -- - --- --- --------
- -- - ---------- - -- ------------- -- -- -- - ---- - - ------ ----------
160 -
----- - - - -- ---
------ --- --------- - --- -- --------------- ------
E 140-
----- - ------- - -- -----
120
-- ----
X
,5 100-
-----------------
z
80-
----------- -- --- --
60,
--- ------------
- -------- -------
401
-------
20 ----- --
- ----- ------------- - --- - - - --- ----- -- --- ------
0
i
2.0
5,0 9.5 11.0 15.9
LOCATIONS
Figure 4- 1. Total zooplankton density by location for samples collected in Lake Non-nan,
NC, in 2001.
4-19

FEBRUARY
250
225
-----i-2.0 -iF-5.0 ___-_.. -------------
200
--- -.___ _ . _ --_ --___ .- --
-'175
- :-: -- _ :- --------- -------- ---- -_._--
0
'-150
---------- ----------- .------------ _-._. _ -- _._ ..
x
0 125
_.---------------------- .:__ _ -:
,100
---------- ----------- __,_ _ ._
w
----
50
--
0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
250 hAAY
225 - -. -- - _ -
200 ------------ -: _ _ _.-.:-___-. _ --- _-_ _ .. __-:_ ._
17 -- ---- - -- ------ --- ----------
150 _ _-_-------_-- -- __.-_ -- ___.____- _
125 _-._. - -
100 ----------------- _
75 --- -
50 - -_-_;. -_-_.-_-_ _--_-- .__ ------ _- -- - -_--
25 -
0
87 88 ' 89 90 91 92 93 94 95 96 97 98 99 00 01
ACKGOUND LOCATIONS
450 450
�11.0 - a— 55.9
400 400 .. - - - .
350 _ . 350
300 - 300 ----
0
-250 _- .- .. __.. 250
or
cs
200 - -- - 200.
w150 150
t�
100 100
50 50 _
0 0_
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
YEARS YEARS
Figure 4-. Total zooplankton densities by location for epilimnetic samples collected in
Lake Norman, NC, in February and May of 1988 through 2001.
4-20

MIXING ZONE
250 AUGUST 250 NOVEMBER
A._
225 ':__--2.0 -—5.0�_____________________ 225 . _ ----------- . r __. - ----- _
200 - ._ 200 ._ -- ._ _- --; . -- . -- -. -- _---
175 -- .__. 175 ___ __ _____ __ _ ____ __ -
x
0 125 -. _ - .- _ .., , _ 125- -------- ------- -- - --- ___ ----
c
c�
75 �- - ...� - ------- --- ------- ---- -_ .__._-.
w 75
50 ..
25 ,r 25 ------
01 0
8788 89 90' 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
BACKGROUND LOCATIONS
400 400
l
350 - - 350
300 - 300
� 250 - - _ 250
x
0200 _ 200 . _. _ . __
it
150 150
m
Uj
100 100
50 50
0 0
87 88 89 90 91 92 93 94 95 96 97 98 99 00 01 87 88 89 90 91 92 93 94 95 96 97 98 99 00 01
YEARS YEARS
Figure 4-3. 'Total zooplankton densities by location for epilmmetic samples collected in
Lake Norman, NC, in August and November of 1987 through 2001
4-21

70
500
MAY
450
60
400
r, 50
E
350
ca
40
30a
X
0
250
t
2aa
(4
z
� 2a
150
10a
1a
50
a
a
2.a 5.0 9.5 11.0 15.9 2.0
5.0 9.5 11.0 15.9
120
AUGUST 140
NOVEMBER
100
120
n;
100
E 80
S
C
80`
x
6 60
c
y
60'
z 4fl
Lu
CS
40
2fl
20
a
a
2.0 5.0 9.5 1t.0 15.9 2.0
5L 9.5 11.0 15.9
LOCATIONS
E==COPEPODS CLADOCERANS
R0TIFERS
Figure 4-4.
Zoopiankton community composition by month
for epilimnetic samples
collected in Lake Norman, NC, in 2001.
4-22

COPEPODS
120
100 _
-------
_ -----------___--___
60 --w _
.___._
_---_ -- -. _ ------
-------------
_._
___ _ __ : ____
20
--___ -_
_-=_-
0
.®p
1
i

\
:
\
U-0

0

I I I I I ICI I
I
�I
lal

CHAPTER.
FISHERIES
INTRODUCTION
In accordance with the NPDES permit for McGuire Nuclear Station (), monitoring of
specific fish population parameters was continued during 2001. The components of the 2001
fish monitoring program for Lake Norman were to:
1. Continue striped bass mortality monitoring throughout the summer;
. Continue acooperative striped bass study with NCWRC to evaluate striped lass
growth and condition as a function of stocking rates, forage availability, and summer
striped base habitat in Lake Norman;
3. Continue annual, fall hydroacousticlpurse seine forage population assessments;
4. Continue to support the bioenergetcs study on Lake Norman, to include spring,
summer and fall hydroacoustic and purse seine samples and -fall gill net samples to
enumerate and describe species composition of the lake's shad and herring
populations;
5. Revise annual, spring shoreline electrofishing program to be conducted every 2 years,
beginning spring 1999, with next sample scheduled for spring 001;
6. Continue to cooperate with NCWRC on a shoreline plantings demonstration project
on Lake Norrnan
7. Continue Duke participation on the Lake Norman Advisory Committee and assist the
NCRC in accessing and interpreting relevant Duke data, relative to Committee
activities.
METHODS AND MATERIALS
The spring shoreline electrofishing portion of the MNS maintenance monitoring program was
conducted on March 4 (MNS mixing zone), April 5 (Marshall Steam Station mixing zone)
and April 16 (mid -lake reference area). The locations sampled were the same locations
sampled during 1999; "Ten 300-m transects were sampled in each of three areas of Lake
Norman (MNS mixing zone, mid -lake reference area, and Marshall Stearn Station mixing
zone), for a total of 30 transects. The MNS mixing zone transacts were located within the
area between Ramsey Creek and Channel Marker l A. The mid -lake reference transacts were
located in the area between Channel Marker i and Channel Marker 9, while the Marshall
-1

Steam Station (MSS) mixing zone transectf
Marker 14 and the NC Highway 150 Bridge
include the various habitat types that exist ii
sampled. The only areas excluded were shal
area within 3-4 m of the shoreline. All saml
water temperatures generally ranged from 15
ere located in the area between Channel
All transects were subjectively selected to
ake Norman and that could be effectively
r flats where the boat could not access the
g was conducted during daylight and when
collected.
The mixing zone was monitored for striped bass mortalities during all summer sampling trips
on the lake. Additionally, from July 5 through September 14, weekly surveys were
conducted specifically to search for dead or dying striped bass in the main channel areas of
the entire lake from Cowan's Ford Dam to uplake of NC Highway 150.
During 2001, gill net sampling for striped bass condition was conducted during the winter
(January 30 - February 1) and fall (November 6 - 9). These data were collected as part of the
cooperative biocnergetics study being conducted by the NCWRC, North Carolina State
University and Duke. Due to the collection of sufficient striped bass data during sampling
for the bioenergetics study, no additional data were collected from the December striped bass
tournament.
The materials and methods for the purse seine and hydroacoustics sampling on Lake Norman
during 2001 are presented in a separate report included as Attachment 1.
During 2001, the gill netting for shad and alewives was conducted by the NCWRC to
evaluate the taxa composition and size distribution of Lake Norman forage species. As in
previous years, netting was conducted in creel zones 3, 4, and 5 (Figure 5-1). Since the
sampling was conducted by the NCWRC, the results of that sampling are not presented in
this report.
RESULTS AND DISCUSSION
As in previous years, spring shoreline electrofishing, of Lake Norman yielded variable catches
among the three areas sampled (Tables 5-1 through 5-3). In the MNS mixing zone area, a
total of 923 fish were collected, weighing a total of 62.60 kg and representing 19 taxa (Table
5-2

5-1). Although the total number of fish collected during 2001 (923 fish) was less than half
the number collected during 2000 (2,175 fish), the total biomass during 2001 (62.60 kg)a was
more than 1.5 times higher than during 2000 (38.t3 kg). The total number of taxa collected
during 2001 (19 taxa) was slightly higher than during 2000 (17 taxa). In addition to the
typical historical species collected from the MNS mixing zone area, one bowfin, one walleye
and six spotted bass were collected during 2001. Spotted bass were introduced into the
reservoir by fishermen and were collected for the first time during 2001. The abundance and
distribution of spotted bass is apparently increasing, as evidenced by the collection of this
species from three of the ten sample transects.
The substantially lower total number of fish collected from the MNS mixing zone area during
2001 is primarily attributable to lower catches of redbreast sunfish and bluegill. These lower
catches may be reflective of increased predation on these species due to the increasing
abundance of blue and flathead catfish in lower Lake Norman. The higher biomass during
2001 is primarily attributable to higher largemouth bass biomass and to the collection of 14
common carp, a species not collected during 2000. Individual transect catches ranged from a
low of 13 fish to a high of 156 fish.
The total catch from the reference area was 1,951 fish, weighing 81.07 kg and representing
17 taxa (Table 5-2). During 2001, the total number of taxa was only slightly higher than
during 2000 (16 taxa). The total number offish collected during 2001 was about 48 % higher
than the number collected during 2000 (1,314 fish), however, the biomass of fish collected
during 2001 was slightly lower than during 2000 (89.28 kg). Individual transect catches
ranged from 84 to 339 fish.
The total catch from the MSS mixing zone area was 1,946 fish, weighing 118.85 kg and
representing 19 taxa (Table 5-3). Unlike the previous two years, during 2001, the MSS
mixing zone area did not yield the highest number of fish, although the catch was only
slightly less than that for the highest area, the reference area (1,951 fish). The total biomass
from this area was substantially higher than that for the MN S mixing zone area (62.60 kg)
and the reference area (81.07 kg).
Compared to the 2000 sample, the total number of fish collected from the MSS mixing zone
area during 2001 was about 28 % lower than during 2000 (2,496 fish), however, the total
biomass was about 40 % higher than during 2000 (84.93 kg). The number of taxa collected
during 2001 (19 taxa) was slightly higher than during 2000 (17 taxa). Individual transect
5-3

catches ranged from 79 fish to 329 fish. Similar to the 2000 sample, the 2001 sample
included the collection of a single rainbow trout.
The condition of Lake Norman striped bass, as indicated by relative weight (Wr), varied by
season. During the winter, 96'% of the 107 striped bass collected had Wr values of ;�:.80,
and 4 % had Wr values >_.90 (Figure -2). The lowest Wr recorded during the winterwas
.76. Three fish had Wr values > 1.00, with the highest Wr value being 1.03.
The Wr values for striped bass collected during the fall indicated substantially poorer body
condition than was present during the winter (Figure 5-). During the fall, only 38 %p of the
82 striped bass collected had Wr values >_.80, and only 6 % had Wr values >.90. The lowest
Wr value during the fall was .63, while the highest Wr was .9. The poorer body condition
during the fall is consistent with striped bass condition decreases noted during previous years,
however, the fall 2001 sample indicates that the degree of body condition decrease during
2001 was more dramatic than in previous years.. The poorer condition of Labe Norman
striped bass during the fall 2001 is probably related to the additional summer stress resulting
from the extended drought. Additionally, forage availability may also be a factor in the
poorer condition, as increasing populations of blue and flathead catfish over the past several
years may be resulting in increased competition for forage.
General monitoring of Lake Norman and specific monitoring of the MNS mixing zone for
striped bass mortalities during the summer of 2001, yielded nine mortalities within the
mixing zone and nine mortalities in the main channel outside the mixing zone. The 18
observed mortalities ranged in -size from 455 mm to 670 mm. Specific observations by date
were:
5-4

DATE LOCATIONLENGTH m!nNUMBER
july 5 Vicinity f MNS Intake 491 1
Vicini of Channel Marker 21 522 1
August 3 Vicinity f MNS Intake 653 1
August 8 Vicinft of Channel Marker 6 510 1
Vicinity of Channel Marker D 5 535 1
Vicinity of Channel Marker D 8 534 1
August 17' Vicinity of MNS Intake 534 1
Vicini!j of Cowans Ford Dam 485
521
Vicinityof Channel Marker 1 489 3
491
526
August 22 Vicinity of Channel Marker D 1 553
54
August 27 Vicinity of C ow*ans Ford Dam 670 1
Vicinity of Channel Marker D 2 476 1
Vicinft of Channel Marker D 7 1 455 1 1
Vicinity of Channel Marker 14 530 1
"Results of the purse seine and hydroacoustics sampling on bake Norman during 2001 are
presented in a separate report included as Attachment 1.
FUTURE 1 FISH STUDIES
• Continue striped bass mortality monitoring throughout the summer.
• Continue a cooperative striped bass study with NC I C to evaluate striped bass growth
and condition as a function of stacking rates, forage availability, and summer striped bass
habitat in Lake Norman.
• Continue the annual, fall hydroacoustic/purse seine forage population assessment.
• Continue spring electrofishing program on a two-year frequency, with the next sample
scheduled for the spring 2003.
-5

Continue the late summer purse seine same
monitor changes in Lake Norman forage popu
• Cover December Striper Swipers tournament I
Su ort coo erative NCSU bioenervetics stu
e and fall small mesh gill net sample
3tion.
obtain striped bass body condition data.
FF
in the collection of striped bass, forage, and summer habitat data for Lake Norman, as
requested by the NCWRC.
• Assist and support the NCWRC in the evaluation of a shoreline plantings demonstration
project begun by the NCWRC and a local fishing club during 2000 in the vicinity of Duke
Power State Park.
The future studies/activities outlined above are subject to revision, based on an annual review
of the data submitted to date and a re-evaluation of the McGuire Maintenance Monitoring
program by the NCWRC.
SUMMARY
In accordance with the Lake Norman Maintenance Monitoring Program for the NPDES
permit for MNS, specific fish monitoring programs were coordinated with the NCWRC and
continued during 2001. General monitoring of Lake Norman and specific monitoring of the
MNS mixing zone for striped bass mortalities during the summer of 2001, yielded nine
mortalities within the mixing zone and nine mortalities in the main channel outside the
mixing zone.
Spring shoreline electrofishing of Lake Norman yielded variable catches for the three areas
sampled; the MNS mixing zone area, a mid -lake reference area, and the MSS mixing zone
area. The highest total catch numerically was from the mid -lake reference area, followed by
the MSS mixing zone, and MNS mixing zone areas, respectively. The highest total catch
gravimetrically was from the MSS mixing zone area, followed by the mid -lake reference and
MNS mixing zone areas, respectively. The total number of taxa collected was the same for
the MSS and MNS mixing zone areas and slightly lower for the mid -lake reference area.
The condition of Lake Non'nan striped bass, as indicated by relative weight (Wr), varied by
season. Striped bass condition was substantially better during the winter than during the fall.
During the winter, 96 % of the striped bass collected had Wr values -:�!.80, while only 38 % of
the fall striped bass had Wr values >.80. The poorer body condition during the fall is
consistent with striped bass condition decreases noted during previous years, however, the
5-6

degree of body condition decrease during 201 was more dramatic than in previous years and
is probably related to the extended drought.
During June 2001, forage fish densities in the six zones of Labe Norman ranged from 2,401
to 9,841 fish/ha. No trend in forage fish abundance was evident. The estimated population
was approximately 74 million fish. Purse seine sampling indicated that these fish were
17.97% threadfin shad, 81.92% alewives, and 0.11% gizzard shad.
September 2001 forage fish densities rangedfrom a low of 3,173 fish/ha (Zone 6) to a high of
11,513 fish/ha (Zone 2). The estimated forage population was approximately 78 million fish.
Purse seine sampling indicated that these fish were 76.47% threadfin shad, 23.52% alewives,
and 0.01 % gizzard shad.
During December 2001, 'forage fish densities in the six zones of Labe Norman ranged from
1,451 to 8,647 fish/ha. There appeared to be fewer fish in the downlake zones. The
estimated forage population was approximately 47 million fish. Purse seine sampling
indicated that these fish were 82.66% threadfin shad, 16,46% alewives and 0.8 % gizzard
shad,'
Through consultation with the NCWRC, the Lake Norman fisheries program continues to be
reviewed and modified annually to address fishery issues. Fisheries data continue to be
collected through cooperative monitoring programs with the NCRC, to allow the
Commission's assessment and management of Lake Norman fish populations. Fisheries data
to date indicate that the Lake Norman fishery is consistent with the trophic status and
productivity of the reservoir. However, one aspect of the Lake Norman fishery that continues
to warrant close monitoring in the future is the composition of forage populations. The
introduction: of alewives by fishermen over the past several years appears to be resulting in
the establishment of a substantial alewife population and could have a dramatic impact on
lake -wide forage populations and game species.
5-7

during March 2001
Transect
1
2
3
4
5
6
7
8
9
10
ALL
Species
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
Longnose gar
1
2165
1
2,165
Bowfin
1
1.697
1
1.697
Gizzard shad
2
1.183
9
3.420
2
1.085
3
1.065
1
0M5
17
7.288
Threadfin shad
5
0.011
5
0.011
Greenfin shiner
2
0.003
2
U05
1
0.001
2
0M4
6
0M9
13
0M2
Whitefin shiner
12
0.035
4
0.005
33
0.082
4
0.010
42
0,042
57
0.048
4
0.011
1
0.004
64
0A18
48
0.123
269
0478
Common carp
4
4.892
1
1.012
1
2250
1
2.180
1
2,365
3
4,685
3
1780
14
21.164
Spottail shiner
1
0.004
2
0M2
1
0.006
1
0.004
1
0.006
21
0.101
27
0.133
Channel catfish
1
0.640
1
OA30
2
0.510
4
IMO
White bass
2
0.614
2
0.614
Redbreast sunfish
25
0337
23
0,281
4
0.033
6
0.104
2
0M5
3
0.055
8
0185
1
0.033
2
0M4
74
1.057
Green sunfish
7
0.009
7
0.009
Warmouth
5
0.090
1
0,005
3
0.011
9
0.106
Bluel
71
0,519
49
0.545
53
0.395
69
0.540
4
0.023
1
0.006
3
0M9
5
0.039
16
0.125
4
0.017
275
1238
Redearsunfish
18
0.662
18
0.516
33
0.565
21
0A55
6
0337
1
0.002
1
0,016
10
0.310
2
0.016
7
1.020
117
1899
Hybrid sunfish
3
0M9
8
0.165
6
0.100
3
0M8
1
0.007
5
0.125
1
0.007
27
0,491
Spotted bass
1
0.171
2
0A35
3
1345
6
1.651
Largemouth bass
16
1920
13
5M0
6
1.466
6
1.402
1
1.175
5
1.057
3
U13
4
1.005
54
16.668
Walleye
1
1330
1
1.330
All
156
13,452
127
11.909
146
1833
115
7.854
61
1.034
70
0.517
13
1466
38
4.629
95
5.811
102
10.096
923
62,601
00

Table 5-2. Numbers and biomass of fish collected from electrofishing ten 300-m transects in the mid -lake reference area of Lake
Norman during April 2001.
Transect
1
2
3
4
5
6
7
8
9
10
ALL
Species
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
Gizzard shad
1
0.541
1
0.381
21
8.279
1
0.474
24
9,675
Greenfin shiner
2
U08
3
0.006
1
0.003
3
0M8
1
0M2
1
OMI
3
0.005
7
0.011
2
0M3
23
0.047
Whilefin shiner
138
0.341
43
0A34
82
0.249
71
0,160
21
0M2
114
0.322
1
0.004
73
0200
86
0.145
41
0A29
670
1Y36
Common carp
1
1.580
1
1M6
3
4.904
1
1.572
2
5.603
3
5,107
1
1.214
12
21.906
Spottail shiner
22
0084
7
0.029
27
0Al2
1
0.003
115
0.555
1
0=7
39
0.156
4
0.014
216
0.960
Channel catfish
1
0.420
2
0.433
1
0,577
1
0.265
2
0.444
1
0.414
1
0.202
1
0.202
10
2.957
Flathead catfish
2
2.413
2
2.413
White bass
1
0.310
1
0.310
Redbreast sunfish
12
0.216
9
0.157
29
0.680
14
0,467
29
0.357
7
0.102
5
0.209
16
0M7
13
0.580
9
0.240
143
1365
Warmouth
6
0.058
3
0.153
2
0.021
1
0.001
7
0.400
1
0.006
5
0.038
1
0.011
3
0.011
29
0.699
Bluegill
114
0.648
57
0.343
50
0.643
14
0.076
80
0.624
17
0A45
43
0A75
122
0108
59
0.602
15
0,084
571
4.348
Redear sunfish
27
0.761
7
0A00
4
0212
10
0.638
18
0298
2
0.513
26
0.661
13
0.447
4
0.094
2
0.028
113
3.752
Hybrid sunfish
2
0.016
1
0.008
2
0.063
2
0.095
9
0.238
1
0.044
2
0229
6
0,286
8
0.220
2
0.071
35
1.270
Largemouth bass
13
4239
7
1.472
18
4.946
8
2.852
18
4.392
3
0.120
18
7.020
5
0.590
4
0338
1
0.541
95
26.510
Black crappie,
1
0,311
1
0.259
2
0.540
4
1,110
Tessellated darter
I
0.001
1
0.001
2
0.002
Yellow perch
1
0M9
1
0.009
All
339
8.803
132
4.719
203
14.977
173
14.837
187
12.234
263
2.252
102
14.388
246
2.841
222
2.359
84
3.659
1,951
81.069

tubers and biomass of fish collected from electrofishing ten 300-m transects in the Marshall Steam Station mixing zone
a of Lake Norman during April 2001.
Transact
1
2
3
4
5
6
7
8
9
10
ALL
Species
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
N
KG
Gizzard shad
1
0.311
1
0311
Threadfin shad
5
0.015
46
0.226
51
0.241
Greenfin shiner
5
0.014
5
0.014
Whitefin shiner
57
0.168
48
0.167
68
0235
31
0A59
8
0.033
48
0183
71
0.252
49
0177
20
0.055
95
0.245
495
1,674
Common carp
1
1.170
3
4.730
2
3.910
9
15.270
1
IMO
7
13.350
3
5.705
26
45.985
Spottail shiner
21
0.097
43
0.201
12
0M4
1
0.004
23
0.122
7
0.036
22
0.138
57
0.260
186
0,922
Shorthead redhorse
1
0.345
1
0,345
Channel catfish
3
OMO
2
0.975
1
0.268
2
OM9
1
1A00
2
0,830
11
4.742
Flathead catfish
1
0,675
1
OMO
2
1.535
Rainbow trout
1
0M8
1
0.028
White perch
1
0A54
1
0A54
Striped bass
1
0M5
1
0M5
Redbreast sunfish
1
0.036
3
0.144
11
0.258
27
0.377
4
0.010
1
0M2
45
0340
57
0.770
9
0A83
5
0265
163
2185
Warmouth
1
0.015
3
0.019
1
0.001
3
0M5
1
0.014
1
0.007
10
0,081
Bluegill
26
0.260
11
0.208
53
0.570
144
1.007
152
0.800
4
0.081
96
0.730
190
1.346
21
0A60
4
16.000
701
21,162
Redear sunfish
8
0365
18
0.780
15
0.725
8
0254
24
0.397
6
0.290
37
1.100
7
0245
4
0.149
7
0.330
134
4.635
Hybrid sunfish
1
0M2
8
0.087
6
0.068
1
0,085
6
0.175
5
0A47
4
0.171
31
0J45
Largemouth bass
10
2.597
8
2.920
22
7.661
8
1385
11
4.925
7
2.159
15
1.570
13
2.488
18
3.669
13
1151
125
32.525
Tessellated darter
1
0,001
1
0.001
All
128
6.328
136
9A96
187
14.425
235
3.307
259
7.053
79
1&833
299
8.524
329
5.223
106
17.882
188
27.779
1,946
118.850

,,ZONE 4
ZONE 2
ZONE,3
ZONE "I
Figure 5-1. Sampling zones on Lake Norman, North Carolina.
5.11

Figure -2.Labe Nonnan striped bass relative weight ("fir) at total length ( ) for the Winter 2001 'sample.
January/February 2001 Striped Bass Relative Weights
110
N1 07
19
99
:
+
8
7
89
00 300 400 500 899 799
Total Length (mm

Figure -3. Lake Norman striped lass relative weight (V r) at fatal length (mm) for the Fall 2001 sample.
November 2001 Striped Fuss Relative Weights
110
N=82
100
90
970
•
+►
60
299 300 499 500 599 700
Total Length mm

Attachment 1:
Lake Norman Hydr€aacoustic and Purse Seine Data. 2001
INTRODUCTION
In accordance with the NPDES permit for McGuire Nuclear Station S), monitoring
of forage fish population parameters was conducted. in 2001. This monitoring included
mobile hydroacoustic survey to estimate forage fish density and population size. Purse
seine sampling was also employed to determine species composition and size distribution
for target strength evaluation. A. joint Duke Power / NC` C / NCSU study to evaluate
striped bass bioenergetics in Lakes Norman and Badin necessitated two additional
hydroacoustic assessments and purse seine samples in 2001.
METHODS AND MATERIALS
-tic axis. The lake was divided into six zones due to its largesize, spatial
ogeneit, and multiple power generation facilities.
seine samples were collected on June 12, September 10, and December 3, 2001
the lower (main channel near ,Marker 1), mid (mouth of Davidson Creek), and
.c (just ;downtake of Lake Norman (Duke Power) State Park) areas of the reservoir.
nurse seine measured 118 x 9 m (400 x 30 ft) with a mesh size of4.8-mra (3/16 in).
ibsample of forage fish collected from each area was used to determine taxa
)osition and size distribution.
CULTS AND DISCUSSION
e fish densities in the six zones of Lake Norman ranged from 2401 to 9,841 fish/ha
ne 200 (Table 1). No trend in forage fish abundance (e.g., higher densities uplake
mpared to downlake) were evident. The estimated population was approximately 74
on fish.' Purse seine; sampling indicated that these fish were 17.97% threadf n shad,
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ength frequency distribution indicated
forage fish under 80 mm (Figure 1).
a low of 3,173 (Zone 6) to a high of
a was approximately 78 million fish.
�V' bG'tnv' aauyinlr' ttttttvccty u-J."L utl%'Ov XIOXI VVvAv I W.- /V --AAA
vives, and 0.01% gizzard shad. The length frequency distribution indicated th
Forage fish densities in the six zones of Lake Norman ranged from 1,451 to 8,647 fish/ha
in December 2001. There appeared to be fewer fish in the do lake zones. The
estimated forage population was approximately 47 million fish. Purse seine sampling
indicated that these fish were 82.66% threadfin shad, 16,46% alewives, and 0.88%
gizzard shad. The length frequency distribution indicated that threadfin shad dominated a
single large size class of forage fish with a modal length of approximately 65 mm while
alewives occupied a higher size class with a modal length of approximately 90 min
(Figure 3).
The 2001 population estimates demonstrated some interesting results with the highest
estimate occurring in September. The 2000 population estimates demonstrated a steady
decline from the first sample (July) through the last (December) in contrast to the trend
seen in 2001. Our initial fears about conducting a June population estimate, and missing
a large portion of the threadfin shad population that may have been spawning in near -
shore locations, appears to have been well founded. This supposition is supported by the
low percentage and extremely small size of threadfin shad in the June 2001 purse seine
hauls as compared to the dominating percentages and much larger sizes on the two
subsequent purse dates. Despite the bitterly cold winter of 2000 — 2001, past data has
consistently shown that large numbers of threadfin shad survive in the heated waters near
the Marshall Steam Station and the McGuire Nuclear Station and would have been
available during June 2001. Therefore we can only surmise that a large percentage of the
threadfin shad population was inaccessible to the purse seine and hydroacoustic gear by
occupying near -shore areas and that the June 2001 population is all underestimate of the
true forage fish population size in Lake Norman. If we assume that the June estimate
should be higher, it still appears that the numbers of forage fish decline steadily
throughout the year. Undoubtedly, natural mortality from disease, starvation, and
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predation from Lake
represented a smallproportion of the total mortality for forage fish. Population estimates
in 2001 are in line with values measured. from 1997 to 2000 but are lower than the
estimates from 1993 to 1996.
FUTLM FISH Sj IDS
Continue the annual fall hydroacousticlpurse seine forme population assessment.
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estimates and 95% confidence limits from three hydroacoustic samples in 2001.
Density (no/hectare) _ Ponulation Estima
Zone
June
September
Dec -ember
June
Se tember
December
1
6,596
4,752
1,451
15,045,476
10,839,312
3,309,731
2
4,720
4,264
2,695
14,547,512
13,142,074
8,306,260
3
4,636
6,241
1,999
16 019,791
21, 65,900
6,9 7,584
4;
5,261
5,236
5,325
6,476,291
6,445,516
6,5 5,075
5 `
9,841
11,513
8,647
20,725,146
24,246,378
22,343,848
6*
2,401
3,173
1,147,678
1,516,694
Total
73,961,894
77,755,875
47,422,498
95% LCL
69,832,155
69,997,022
41,611,019
95% LTCL
78 (J91 6 3
85 14 728
53 243 977'
* Less than one
report (density estimate) was collected in Zone 6 due to low water levels. Zones 5
and 6 were combined for one density and one population estimate.
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Figure 1. Lake Norman (combined) forage fish — June 2001.
300 -
250 -
200 -
T Shad
E 150
G Shad
z
Alewi
00 )yi �es
1
50
o
20 35 50 65 80 95 110 125 140 155 170 185 200 215 230 245
Length Group (mm)
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Figure 2. Lake Nonnan (combined) forage fish — September 2001.
160
140
120
%100
E 80- T Shad
z 60 G Shad
i it Alewives
40 '1
20 -
20 35 50 65
30 95 110 125 140 155 170 185 200 215 230 245
Length Group (mm)
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Figure 3. Lake Norman. (combined) forage fish — December 2001.
200
180
160
140
120
00 EIT Shad
E 180 G Shad
60 Alewives
40
20
0
50 65 80 95 110`125 140 155 170 185 200 215 230 245
Length Group (mm)
-