NC0024392_Regional Office Historical File Pre 2018 (14)

K DEPTOF ENVIRONMENT
AND N'A{TURAL ti20 m
LLE
"RE
Duke ,, %1 Duke Power
McGuire Nuclear Station
Iftopower.. I2700 Haters Ferry Read.
r4 Dukr Enero Company Huntersville, NC 28078
s. r
Sullins, ivision
Water Quality
North Carolina Department of Environment
and Natural Resources ..€i
1617 Mail Service tenter
Raleigh, NC 27699-1617 WATCzpN U4
Subject: McGuire Nuclear Station
Lake Norman Environmental Monitoring Program; 2001 Summary Report
Certified. 7001 2510 0003 4218 1925
Dear Ms. Sullins:
Enclosed are three copies of the annual Lake Norman Environmental Monitoring Program: 2001
Summary m Report, as required by the NPDES permit NCO024392 for McGuire Nuclear Station.
Fishery studies continue to be coordinated with the Division of Inland Fisheries of the North
Carolina Wildlife Resource Commission to address Lake Norman fishery management concerns.
Results of the 2001 data were comparable with that of previous; years.
If you have any questions concerning this report,; please contact either, John Williamson (704)
75-5 94, or Robert W. Caccia [phone].
Sincerely,
lhiaa .amil
McGuire Site Vice President
c. Mr. Scott 'fan Hom North Carolina Wildlife Resource Commission

^:
Michael F. Easley
Governor
William G. Ross, Jr., Secretary
y � Department of Environment and Natural Resources
Kerr T. Stevens, Director
Division of Water Ouality
January 29, 2001
Mr. Michael A. Ruhe C E "I V t
Manager, Water Compliance
Duke Power'
M 0 A
13339 Hagers Ferry React
Hunt rsville, N C 28076-7929 (Lt 4Ej)i hA� x
AND
�: �,aa�
`ie"`A P,"r, w`'H 4m4„ t4ui,.�,':�Mea, .
Dear Mr. Ruhe:
We have received the McGuire Nuclear Station, Lake Norman: 1999 Summary Report, Environmental Monitoring
Program as required by NPD S permit, and the Belews Creek Steam Station, 1999 Dan River Summary Report as
required by NPDES permit. We have no comments on the Lake Norman report as conditions appear similar to prior
yearn:
In the Belews Creek report, Gave L.enat comments that the between -year changes in benthfc macroinvertebrate data
should be interpreted in relation to flow. Much of the variation can probably be explained in this way, otherwise the low
number of BPT taxa collected at both locations is alarming.
Concern is also raised by the higher selenium values found in the tissue of sunfish at locations 720 and 736 downstream
of the plant, and by the continued increase of these values since 1997, regardless of the fact that they are below the
1evels found during the failure of the fishery in Belews Lake in the 1970s. The same increasing trend is not found at
location 710 above the plant. Our concern is further intensified by a similar pattern in selenium concentrations of the
ertebrate , where the difference in upstreamand downstream concentrations s much greater than had been found
iously. As noted in your report, such concentrations have been reported by some in the scientific literature as cause
for concern.
DWO would recommend a meeting between DWO and your staff to discuss possible reasons for the downstream
increase, unless the 2000 data is available and it does not show the same increasing trend. Please contact Bark Hale
(919-733-6946) to set up a meeting or to provide him the 2000 fish tissue and invertebrate data.
Please also note that pages -1 through 3-6 of the Belews Creek report were duplicated in all three copies.
Please contact Jimmie Overton (919-733-9960) if you have other questions about these comments or would like to
discuss further the need to meet about the Belews Creek Steam Station discharge to the lean Diver.
Sincerely,
Coleen Sullins
Water Quality Section Chief
Mark Hale
Jimmie Overton
Larry Coble, WSRt -Clan River rpt
ll
WN
Customer Service Division of Water Quality 1617 Mail Service Center Raleigh, NG 276 1617 (19) 3-7015
1 800 623-7741

cfq /
LAKE NORMAN: 1999 SUMMARY
MAINTENANCE MONITORING PROGRAM
McGUIRE NUCLEAR STATION: NPDES o. NCO024392
RECEINI'D
NC DEPT. OF EWROWENT
AND NATURAL RESCURMS
MOOREMLLE REGIONAL OFFICE
DUKEPOWER
A COMPANY OF DUKEENERGY
C

TABLE OF CONTENTS
Page
EXECUTIVE SUMMARY
i
LIST OF TABLES
iv
LIST OF FIGURES
v
CHAPTER 1: McGUIRE NUCLEAR STATION OPERATIONAL DATA
1-1
Introduction
1-1
Operational data for 1999
1-1
CHAPTER 2: LAKE NORMAN WATER CHEMISTRY
2-1
Introduction
2-1
Methods and Materials
2-1
Results and Discussion
2-2
Future Water Chemistry Studies
2-8
Summary
2-8
Literature Cited
2-9
CHAPTER 3: PHYTOPLANKTON
3-1
Introduction
3-1
Methods and Materials
3-1
Results and Discussion
3-2
Future Phytoplankton Studies
3-
Su ary
3-9
Literature Cited
3-11
CHAPTER 4: ZOOPLANKTON
4-1
Introduction
4-1
Methods and Materials
4-1
Results and Discussion
4-2
Future Zooplankton Studies
4-6
Summary
4-6
Literature Cited
4-8
CHAPTER 5: FISHERIES
5-1
Introduction
5-1
Methods and Materials
5-1
Results and Discussion
5-
Future Fisheries Studies
5-4
Summary
5-5
Attachment 1: Hydroacoustic and Purse Seine Data
5-13

EXECUTIVE SUMMARY
As required by the National Pollutant Discharge Elimination System (NP DES) permit
number NCO024392 for McGuire Nuclear Station ( S), the following annual report has
been prepared. This report summarizes environmental monitoring of Lake Norman
conducted during 1999.
OPERATIONAL DATA
The monthly average capacity factor for MNS was 99. %, 101 % , and 79. %i during Jul
August, and September of 1999, respectively, 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,OOF (35.00C) to 99.00F ,(3.20C). The average:
monthly discharge temperature was 93.90 " (34.40C) for July, 9 .20F (6.80 ) for August,
d 91.00F (32, C) for September 1999.Two of three low-level intake water pumps of
Unit l were operated to provide additional cooling for I I days in August.: Three pumps were
operated for 10 days and two pumps for 5 days in September. "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 NP ES discharge water temperature limits.
WATER CHEMISTRY DATA
All chemical parameters measured in 1999 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 1999 often exceeded. the NC water quality standard. This is characteristic of waterbodies
that experience by ohmnetic deoxygenation during the summer.
Temporal and spatial trends in water temperature and dissolved oxygen concentration (IBC))
data collected in 1999 were similar to those observed historically. The summer pelagic
habitat for adult striped bass in Lake Neuman in 1999 was generally similar to historic
conditions.. Reservoir -wide isotherm and isopleth information for 1999, coupled with heat
content and hypolimnetic oxygen data, illustrated that Lake Dorman exhibited thermal and
oxygen dynamics characteristic of historic conditions that are also similar to other South-
eastern reservoirs of comparable size, depth, flaw conditions, and trophic status,.
i

PH TCIPLANKTON DATA
Lake Norman continues to support highly variable and diverse phytoplankton communities.
No obvious short term or long-term impacts of station operations were observed. Lake -wide
can chlorophyll a concentrations in February and May were the lowest observed for these
months since the program began. Low chlorophyll a concentrations may have been due to
very low rainfall during seasons prior to sampling
The phytopkankton index (Myxophycean) tended to confirm the characterization of Lake
Norman as oligo-mesotrophic Quarterly index values were in the low -intermediate range,
and tended to reflect seasonal changes in phytoplankton standing crops in 1999. Ten classes
comprising 76 genera and 135 species, varieties, and forms ofphytoplankton were identified
in samples collected during the year, as compared to 86 genera and 168 lower taxa identified
in 1998. The 1999 total was the fifth highest number of individual taxa recorded since
monitoring began in 19 T Live taxa previously unrecorded during the Maintenance
Monitoring Program were identified during; 1999
ZOOPLANKTON DATA
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 as seasonal
and spatial variability observed during 1999, were likely due to environmental factors and
appear not to be related to plant operations. Epilimnetic zoolankton densities during May
d .August of 19 were within ranges of those observed in previous years. The February
density do lake at Location 2.0 was the lowest recorded from this location for this month,
while densities at midlake Location 11.0 and at uptake Location 15.9 in November were the
highest ever observed at these locations for November, > One Hundred and eight zooplankton
taxa Have been recorded from Lake Norman since the Program began in 1987 (fifty-two were
identified during 199). Four taxa previously unreported during the Program were, identified
during 1999.
FISHERIES DATA
Continuation of specific fish monitoring programs was coordinated with the NRC" during
1999 General monitoring of Lake Norman and specific monitoring of the MN S mixing zone
for striped bass mortalities during the summer of 1999 yielded one mortality within the
mixing zone and five mortalities in the main channel outside the mixing zone. Striped bass
body ` condition data were collected from 73 fish caught during a one -day striped 'bass
tournament held on Lake Norman in December 1999. Striped bass ranged in size from 510
11

mm to 719 mm. Individual fish weights ranged from 1,202 g to 3,575 g. All data were
submitted to the NCWRC for detailed analyses of striped bass growth and condition.
Spring shoreline electrofishing of Lake Norman yielded variable catches for the three areas
sampled; 1) the downlake MNS mixing zone area, 2) the mid lake reference area, and 3) the
uplake Marshall Steam Station (MSS) mixing zone area. The highest total catch numerically,
gravimetrically, and in taxa composition was from the MSS mixing zone area. Catches from
the MNS mixing zone area were the next highest numerically, but were slightly lower than
the reference area in both total biomass and taxa composition.
Purse seine sampling conducted during August 1999 to monitor possible changes in the
species composition and size distribution of Lake Norman forage fish yielded gizzard shad,
threadfin shad, gizzard/threadfin hybrids, and alewives. Catches from all three areas of the
reservoir were dominated by threadfin shad.
The hydroacoustic/purse seine sampling for estimation of Lake Norman forage fish
populations continued in 1999. The September 1999 purse seine was dominated by threadfin
shad with minor contributions from gizzard shad and alewives; comprising 99.26%, 0.26%,
and 0.48% of the catch, respectively. Analyses of forage fish population data for 1998 and
1999 were completed, and a summary report was prepared (Attachment 1).
Fall gill netting for shad and alewives yielded< total of 376 fish from 24 net nights of
sampling in three zones of Lake Norman. All three forage fish species (gizzard shad,
threadfin shad, and alewives) were collected from Zones 3 and 5, while only gizzard shad and
threadfin shad were collected from Zone 4.
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 NCWRC to support 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.
zap

LIST OF TABLES
Page
Table 1-1
Average monthly capacity factors for McGuire Nuclear Station
1-2
Table 2-1
Water chemistry program for McGuire Nuclear Station
2-12
Table 2-2
Water chemistry methods and analyte detection limits
2-13
Table 2-3
Heat content calculations for Lake Norman in 1998 and 1999
2-14
Table 2-4
Comparison of Lake Norman with TVA reservoirs
2-15
Table 2-5
Lake Norman water chemistry data in 1998 and 1999
2-16
Table 3-1
Mean chlorophyll a concentrations in Lake Norman
33 - 14
Table 3-2
Duncan's multiple range test for Chlorophyll a
3-15
Table 3-3
Total phytoplankton densities from Lake Nonnan
3-16
Table 3-4
Duncan's multiple range test for phytoplankton densities
3-17
Table 3-5
Duncan's multiple range test for dry and ash free dry weights
3-18
Table 3-6
Phyroplankton taxa identified in Lake Norman from 1987-1999
3-19
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 1988-1999
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
5-7
Table 5-2
Electrofishing catches in the mid -lake reference zone
5-8
Table 5-3
Electrofishing catches in the mixing zone of Marshall
5-9
Table 5-4
Purse seine catches from Lake Norman in 1999
5-10
Table 5-5
Gillnetting catches from Lake Nonnan in 1999
5-11
iv

LIST OF FIGURES
Page
Figure 2-1
Map of sampling locations on Lake Norman
2-19
Figure 2-2
Monthly precipitation near McGuire Nuclear Station
-20
Figure -3
Monthly mean temperature profiles in background zone
-1
Figure 2-4
Monthly mean temperature profiles in mixing zone
2-23
Figure 2-5
Monthly temperature and dissolved oxygen data
2-25
Figure 2-6
Monthly mean dissolved oxygen profiles in background zone
2-26
Figure -7
Monthly mean dissolved oxygen profiles in mixing zone
2-28
Figure -8
Monthly isotherms for Lake Norman
2-30
Figure 2-9
Monthly dissolved oxygen i opleths for Lake Norman
2-33
Figure 2-1 a
Heat content of Lake Norman
2-3
Figure 2-10b
Dissolved oxygen content of Lake Norman
2- 6
Figure 2-11
Striped bass habitat in Lake Norman
2-7
Figure 3-1
Chlorophyll a measurements of Lake Norman
3-28
Figure 3-2 `
Mean chlorophyll a concentrations by year
3-29
-3
Chlorophyll a concentrations by location
3-30
Figure 3-4
Class composition of phytoplankton at Locations 2.0 and 5.0
3-32
Figure -5
Class composition of phytoplankton at Location 9.5
3-33
Figure 3-6
Class composition of phytoplankton at Location 11.0
3-34
Figure 3-7 '
Class composition of phytoplankton at Location 15.9
3-5
Figure 3-8 ;
Annual lake -wide Myxophyean index from 1988-19
3-6
Figure 4-1
Zooplankton density by sample location in Lake Norman
4-19
Figure 4-2
Zoplankton densities among years during February and May
4-0
Figure -3
Zooplankton densities among years during August and November -
4- 1
Figure 4-4
Lake Norman zooplankton composition in 1999
-22
Figure 4-5
Quarterly zooplankton composition from 1990 through 199
4-23
Figure 4-6
Annual lake -wide zooplankton composition (1998 through 1999)
4- 4
Figure 4-7
Lake Norman zooplankton composition (nixing zone locations)
4-25
Figure 4-8
Lake Norman zooplankton composition (background locations)
4-26
Figure -1 '
Lake Norman creel zones
5-12
v,

CHAPTERI
McGUIRE NUCLEAR STATION
OPERATIONALA A
INTRODUCTION
As required by theNational Pollutant discharge Elimination System (NPDES) permit
number NCO024 92 for McGuire Nuclear Station ( S) issued by the North Carolina
Department of Environment and Natural Resources (NCTDENR), the following annual report
has been prepared. This report summarizes environmental monitoring of Lake Norman
conducted during 1999
OPERATIONAL DATA FOR 1999
The monthly average capacity factor for MNS was 99.7 %, 101.4 %, and 79.8 % during July,
August, and September of 1999, 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.OoF` (35.tloC) to 99.0F (37.20C), The
average monthly discharge temperature was 93.9 F (34.40C) for July, 9 ,2oF 36,80C) for
August, and 91.0F (3.80C) for September 1999. Two of three low level intake water
pumps of Unit 1 were operated to provide additional cooling for 11 days in August and
during September three pumps were operated for 1 clays and pumps for 5 days, 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.
1-1
1-

Table 1-1.
average monthly capacity facture %) calculated from unit capacity
factors [Net Generation (; we per unit ay) x 1
/ 24
It per ; ay x 1129
mw per unit] and
monthly
average discharge
water
temperatures for
McGuire char Station urin 1999.
NPDES DISCHARGE
CAPACITY FACTOR
(° a)
TEMPERATURE
Month
Unit I
Station
Monthly Average
Unit 2
Average
Average
Average
OF
oC
January
105.4
105
105.2
69.3
21.0
February
1053
100.9
10.1
70.5
21.
March
105.2
32.6
68.9
9.9
21.1
April
104.9
47.5
76.2
73.7
23.2
May
104.4
1 4.8
104.E
32.1
27.
June
103.1
1015
103.3
90.9
32.7
July
102.1
97.3
9.7
93.9
34.4
August
101.4
1 1 A
101 A
982
36.
September
57.1
1 2.5
79.8
91
32.3
October
November
0
80.8
1 3.7
90.6
5.6
65.7
33.3
77.5
28.5
25.3
December
101.8
61.4
91.6
72
22.2
1-2

CHAPTER2
LAKE NORMAN WATER CHEMISTRY
INTRODUCTION
The objectives of the water chemistry portion of the McGuire Nuclear Station (MNS)
NPDES Maintenance Monitoring Program are to:
I . maintain continuity in Lake Norman's chemical database so as to allow detection of
any significant station -induced and/or natural change in the physicochemical structure
of the lake; and
1 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 1998 and 1999. Where appropriate, reference to pre-
1998 data will be made by citing reports previously submitted to the North Carolina
Department of Environment and Natural Resources (NCDENR).
METHODS AND MATERIALS
The complete water chemistry monitoring program, including specific variables, locations,
depths, and frequencies is outlined in Table 2-1. Sampling locations are identified in Figure
2-1, whereas specific chemical methodologies, along with the appropriate references are
presented in Table 2-2. Data were analyzed using two approaches, both of which were
consistent with earlier studies (Duke Power Company 1985, 1987, 1988a, 1989, 1990, 1991,
1992, 1993, 1994, 19951, 1996, 1997.1 1998, 1999). The first method involved partitioning the
reservoir into mixing, background, and discharge zones, and making comparisons among
zones and years. In this report, the discharge includes only Location 4; the mixing zone
encompasses Locations I and 5; 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
hypolinmetic oxygen deficit (AHOD), maximum whole -water column and hypolimnion
oxygen content, maximum whole -water column and hypolimnion heat content, mean
epilimnion and hypolimnion heating rates over the stratified period, and the Birgean heat
budget,
2-1

Heat (Kcal/cm) and oxygen (Ing/CM2 or mg/L) content of the reservoir were calculated
according to Hutchinson (1957), using the following equation:
Zo
Lt = Ao- I * Z111 f TO # Az dz
where;
Lt = reservoir heat (Kcal/Cm) or oxygen (Mg/CM2) content
An = surface area of reservoir (cm2 )
TO = mean temperature (' Q or oxygen content of layer z
Az = area (cm2) 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 1999 totaled 35.21 inches; this was
similar to that observed in 1998 (33.5 inches), but appreciably less than measured in the 1997
(48.0 inches) (Figure 2-2). The highest total monthly rainfall in 1999 occurred in September
with a value of 4.88 inches.
Temperature and Dissolved Oxygen
Water temperatures measured in 1999 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 Lake Norman since
MNS began operations in 1983. Water temperatures in the winter of 1999 were slightly
warmer throughout the entire water column in both zones than observed in 1998 (Figure 2-3,
2-4). Minimum metalimnion and hypolimnion winter temperatures in 1999 measured 9 to 10
OC, were slightly warmer than measured in 1998, but noticeably warmer than the 5 to 6 OC
corresponding temperatures measured in 1996 (Duke Power Company 1997). Interannual
2-2

variability in water temperatures during the spring and summer months was observed in both
the mixing and background zones„ but these conditions were well within the observed`
historical variability and were not considered of biological significance (Duke Power
Company 1985, 1989, 1991, 1993. 1994, 1995, 1996, 1997, 1998, 1999).
Temperatures in the fall of 1999 (October through December) were noticeably cooler in both
the mixing -and background zones than measured at similar times in 199 (Figure 2-3 2-),
and similar to that measured in 1997 (Duke Power Company 1998). These inter -year
differences can be explained by the effect of El Nino on local meteorological conditions and
the corresponding water: column response;, a warmer air temperature would result in delayed
cooling of the water column, as measured in 1998
Temperature data at the discharge location in 1999 were generally similar to 1998 (Figure 2-
5) and historically (Duke Power Company 1985, 1987, 1988a, 1989, 1990 1991, 1992, 1993,
1994 1995, 1996, 1997 1998, 1999). The warmest discharge temperature of 1999 occurred
in August and measured 38.4 °C>, or 1.7 °C" warmer than measured In August, 1998 (Duke
Power Company 1999).
Seasonal and spatial patterns of DO in 1999 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 spring DJ values in 1999 were generally lower than measured in 1998,
and appeared to be related predominantly to the warmer water column temperatures
measured in 1999 versus 1998 The wanner water temperatures would be expected to exhibit
a lower oxygen content because of the direct effect of temperature on oxygen solubility, and
indirectly via a reduced convective nixing regime which would inhibit reaeration. Summer
DO values in 1999 were highly variable throughout the water column in both the Mixing and
background zones ranging from highs of 6 to 8 mg11. in the surface waters to lows of 0 to 2
mglL in the bottom waters, this pattern is similar to that measured in 1998 and earlier years
(Duke Power Company 1985, 1987, 1988a, 1989, 1990, 1991, 1992, 1993,1994, 1995, 1996,
1998, 199)• All dissolved oxygen values recorded in 1999 were well within the historic
range (Duke Power Company 1985, 1987, 1988a; 1989, 1990, 1991, 1992, 1993,199 , 1995,
196, 1997; 1998, 1999).
Considerable differences were observed between 1998 and 1999 fall and early -winter DO
values in both the mixing and background zones, especially in the metalimnion and
hypolt neon (Figures 2-6 and 2_7). Dissolved oxygen values in 198 were appreciably lower
2-3

than measured in 1999, and these differences appear to be related to the effect of El Nino on
water column cooling and reaeration. A similar phenomenon was observed in fall DO values
for the years 1997 versos 1998, and. was attributed to the effects of El Nino (Duke Power
Company 199). Warmer air temperatures would delays water column. cooling (Figure 2-3,
-4) which in turn, would delay the onset of convective mixing ofthe water column and the
resultant reaeration of the metalimnion and hypolimnion. Conversely, cooler air
temperatures would promote the rate and magnitude of this process resulting in higher DO
values sooner in the year. Intera nual differences in DO are common in Southeastern
reservoirs, particularly during the stratified period, and can reflect yearly differences in
hydrological, meteorological, and l mnolo ical forcing variables (Cole and Hannon 19 5;
Petts 194).
The seasonal pattern of DO in 1999 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 LAC) concentration measured at the discharge
location in 1999 (5,4 nag/L,) occurred in September, concurrent with hpoli 'netic water
usage at MNS for condenser cooling water needs.
Reservoir -wide Temperature and Dissolved Oxygen
The monthly reservoir -wide temperature and dissolved oxygen data for 1999 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 Fannon, 19 5; 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 sake Norman, the reader is referred to earlier reports (Duke Power
Company 1992, 1993, 1994, 1995, 1996).
The seasonal heat content of both the entire water column and the hypoli nic n for Lake
Norman in 1999 are presented in Figure 2-1 Oa; additional information on the thermal regime
in the reservoir for the years 1998 and 1999 are found in "Table 2-3. Annual minimum heat
content for the entire water column in 19 (10.29 local/CM2; 10.4 °C) occurred in early
March, whereas the maximum heat content (28.37 Kcal/cm='; 30.0 ' ) occurred in mid July.
Heat content of the hypolimnion exhibited a somewhat different temporal trend as that
observed for the entire water column. Annual minimum hypolimmtic heat content occurred
in early March and measured 5.8 Kcal/cM2 (9.2 "C), whereas the maximum occurred in
2-

September and measured 15.65 Kcal/cm' (24.4 'C). Cleating 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 0.132 Deal/c 2/day
versus 0.055 Kcal/cm'/clay for the hypolimnion. The 1999 heat content -data were slightly
elevated compared to previous years and appeared to be primarily related to the effects of El
Nino (Duke Power Company 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999).
The seasonal oxygen content and percent saturation of the whole water column and the
hypolimnion for 1999 are depicted in Figure 2-10b. Additional oxygen data can be found in
'Fable 2-4 which presents the 1999 AHOD for Lake Norman and similar estimates for 1
TVA reservoirs. Reservoir oxygen content was greatest in mid -winter when DO content
measured 10.1 ng/L, for the whole water and 10.2 g/L for the hypolimnion. Percent
saturation values at this time approached 5% for the entire water column and 90% for the
hypolimnion. Beginning in early -spring, oxygen content began by 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 id -summer. Minimum summer DO values for the entire
water column measured 4.6 g/L (62% saturation), whereas the minimum for the
hypolimnion was 0.2 mg/L (2. % saturation). The mean rate of DO decline in the
hypolimnion over the 'stratified period., i.e., the AHOD, was 0.040 glc zlday (.064
mg/L /day) (Figure 2-10b), and is similar to that measured in 199 (Duke Power Company
1999).
Hutchinson (1938, 1957) proposed that the decrease of dissolved oxygen in the hypolimnion
of a waterbody should be related to the productivity of the trophogenic zone. Mortimer
(1941) adopted a similar perspective and proposed the following criteria for AHOD
associated with various tro pic states; oligotrophic - :5 0.025 mg/cm' /day, mesotro hic
0.06 mg/' '/day to 0054 glc 2/day, and eutrophic - > 0.055 g/can`/day. Employing
these limits, Lake Norman should be classified as mesotrophic based on the calculated
AHOD value of 0.040 mg/cm'/day for 1999. The oxygen bared mesotro hic classification
agrees well with the mesotrophic classification based on chlorophyll a levels (Chapter 3).
The -1999 AHOD value is also similar to that found in other Southeastern reservoirs of
comparable depth, chlorophyll a status, and secc.hi depth (Table -4).
25

�itripect t3ass tlaoitat
Suitable pelagic habitat for adult striped bass, defined as that layer of water with
temperatures <_ 2 °C and DO levels ? 2.0 mgll,, was found lake -wide from October 199
through June 1999. Beginning in pithy 1999, habitat reduction proceeded rapidly throughout
the reservoir both as a result of deepening of the 2 °C: isotherni and metalimnetic and
hypolimnetic deoxygenation (Figure 2-11). Habitat reduction was most severe from early
August through early September when no suitable habitat was observed in the reservoir
except for a small refugium in the upper, riverine portion of the reservoir, near the confluence
of Lyles Creek with Labe Norman. Habitat pleasured in the ripper reaches of the reservoir at
this time anneared to be influenced by bath inflow from Lvles Creek and discharge- from
Lookout Shoals Hydroelectric facility, w.
in Lake Norman. Upon entering Lak,
proceeds as a subsurface: underfloor (Ford
Physicochemical- habitat was observed
primarily as a result of epilimnion coo
meteorological conditions. The temporal
and reduction observed in 199 was Simi
any other Southeastern reservoirs (CYou
1 95, 1 19 7 199 , 1999).
Turbidity and Specific Conductance
Surface turbidity values were generally low at the NINS discharge, nixing zone, and mid -
lake background locations during 1999, ranging from 1.5 to 2.9 N TUs (Table 2-5). Bottom
turbidity values were also relatively low over the study period, ranging from 2.6 to 12.5
NTDs (Table 2-5). These values were similar to those pleasured in 199 (Table -5), and
well within the historic range (Duke Power Company 1989. "1990, 199L 1992. 1993, 199
1995, 199 ,1997, 1998, 1999).
Specific conductance in Lake Norman in 199 ranged from 51 to 105 umholcm, and was
similar to that observed in 19 (Table -5) and historically (Duke Power Company 1989,
0 1992, 1991, 1994, 1995, 1996, 1997, 1998, 1999). Specific conductance values in surface
and bottom waters were generally similar throughout the year except during the period of
intense thermal stratification, These increases in bottom conductance values appeared to be
2-6

related primarily to the release of soluble iron and manganese from the lake bottom under
anoxic conditions (Table 2-5). This phenomenon is common in both natural lakes and
reservoirs that exhibit hypolimuctic oxygen depletion (Hutchinson 1957, Wetzel 1975).
pH and Alkalinity
During 1999, PH and alkalinity values were similar among MN S discharge, mixing and
background zones (Table 2-5); they were also similar to values measured in 1998 (Table 2-5)
Zn
and historically (Duke Power Company 1989,1992, 1993, 1994,' 1995, 1996, 1997, 1998,
1999). Individual PH values in 1999 ranged from 6. 1 to 7,91, whereas alkalinity ranged from
12.5 to 17.5 mg/L of CaCO,.
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 'Fable 2-5. The overall ionic composition of Lake
Norman during 1999 was similar to that reported for 1998 (Table 2-5) and previously (Duke
Power Company 1989,1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999). Lak-e-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 are provided in Table 2-5. Overall, nitrogen and phosphorus levels in 1999 were
similar to those measured in 1998 and historically (Duke Power Company 1989, 1990, 1991,
1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999); they were also characteristic of the lake's
oligo-mesotrophic status. Ammonia nitrogen concentrations increased appreciably in the
bottom waters at the background location. concurrent with the development of anoxic
conditions. This pattern is similar to that observed in previous years, 'Total and soluble
phosphorus concentrations in 1999 ranged from < 5 ug/L to 26 ug/L and were similar to
values recorded in 1998, and historically (Duke Power Company 1989, 1990, 1991, 1992,
1993, 1994, 1995, 1996, 1997, 1998, 1999) (Table 2-5).
2-7

Metals
Metal concentrations in the discharge, mixing, and maid -lake background zones of Lake
Norman for 1999 were similar to that measured in 18 (Table 2-5) and historically (Duke
Power Company 1989, 1990, 1991, 1992, 1993, 1994, 1995, 1996, 1997, 1998, 1999). Iron
concentrations near the surface were generally low (:!�- 0.1 mg1L) during 1998 and 1999,
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 (
0.1 mg/L) in both 1998 and 1999, except during the summer and fall when bottom waters
were anoxic (Table 2-5). 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 197). 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 historic conditions (Duke Power Company 1989, 1990, 1991, 1992, 1993, 1994, 1995,
1996, 1997, 1998, 1999). Heavy metal concentrations in Lake Norman never approached NC'
water quality standards, and there were no consistent appreciable differences between 1998
and 1999.
FUTURE STUDIES
No changes are planned for the Water Chemistry portion of the Lake Norman maintenance
monitoring program during 2000 or 2001.
SUMMARY
Temporal and spatial trends in water temperature and DO data collected in 1999 were similar
to those observed historically. Temperature and DO data collected in 1999 were: within the
rangeof previously measured values.
Reservoir -wide isotherm and isopleth information for 1999, coupled with heat content and
hypoli netc oxygen data, illustrated that Lake Norman exhibited thermal and oxygen
dynamics characteristic ofhistoric conditions and similar to other Southeastern reservoirs of
comparable size, depth, flow conditions, and trophic status:
-8

Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 1999 was
generally similar to historic conditions. All chemical parameters measured in 1999 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 full of 1999 often exceeded the N(
water quality standard. This is characteristic of waterbodies that experience hypolimnetic
deoxyenation during the summer.
LITERATURE CITED ,
Courant, C. C. 1985. Striped bass, temperature, and dissolved oxygen: a speculative
hypothesis for environmental risk. Trans. Amer. Fisher. Soc. 114:31-61'a
Cole; T. M. and 1-I. H. Hannon. 1985. Dissolved oxygen dynamics. In: Reservoir
Limnolo y : Ecological Perspectives. K. W. Thornton, B. L. Kimmel and F. E. Payne
editors. John Ailey & Sons. N.
Duke Power Company. 1985. McGuire Nuclear Station, 16(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. dike Power Company, Charlotte, NC:
Duke Power Company. 1989. Lake o air maintenance monitoring program: 1988
summary.
Duke Dower Company. 1990. Lake Norman maintenance monitoring program: 1989
summary,
Duke Power Company. 1991. Lake Norman maintenance monitoring program: 1990
summary,
Duke Power Company. 1992. Lake Norman maintenance monitoring program: 1991
summary.
2-9

Duke Power Company. 1993. Lake Norman maintenance monitoring program: 1992
summary.
Duke Power Company, 1994, Lake Norman maintenance monitoring program; 1993
summary.
Doke 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: 199
Summary.
Ford, D. E. 1985. Reservoir transport processes. In: Reservoir Limnology: Ecological
Perspectives. K. W. Thornton, B. L. Kimmel and P. P. ;Payne editors. John Wiley
Sons, NY.
Hannan, H. H., 1. R. Fuchs and D. C. Whittenburg. 1979 Spatial and temporal patterms, of
temperature, alkalinity, dissolved oxygen and conductivity in an oligo-mesotrophic,
deep -storage reservoir in Central Texas. I-Iy robilologia 51 (30);209-22 1.
Higgins, J. M. and B. R. Kim. 19 1. Phosphorus retention models for Tennessee Malley
Authority reservoirs. Water Resour. Res., 17:571-57 .
Higgins, J. M., W. L. Poppe, and M. L. lwanski. 198 1. Eutrophication analysis of TVA
reservoirs. In: Surface Water Impoundments. H. G. Stefan, Ed. Am. Soc. Civ. Eng.,,
N, .404-41.
Hutchinson, G. E. 1938, Chemical ical stratification and lake morphometry. Proc. Nat. Acad,
Sci., 24:6 3-69.
Hutchinson, G. E. 1957. A Treatise on Limnology, Volume 1. Geography, Physics and
Chemistry. John Wiley & Sons, NY.
Hydrolab Corporations 1986. Instructions for operating the H drolab Surveyor 1.):iat sol de,
Austin, T . 105p,
2-10

Matthews, W. J., L G. Hill, D. R. Edds® and F. P. Gelwic . 1980. Influence of water quality
and season on habitat use by striped Kass in a lame southwestern reservoir.
Transactions of the American Fisheries Society 118: 243-250
Mortimer, C. H. 1 41. The exchange of dissolved: substances between mud and water in
lakes (Parts I and II). J. Ecol., 9-280-32 .
Petts G. E., 1984. Impounded Rivers: Perspectives For Ecological Management. John
Wiley and Sons. New York. 32 pp.
Ryan, P. J. and D. F. R. Harle an. 1973. Analytical and experimental study of transient
cooling pond behavior. Report No 161. Ralph M. Parsons Lab for Water Resources
and Hydrodynamics, ics, Massachusetts Institute of Technology, Cambridge, MA.
Stun m, w. and J. J. Morgan. 1970. Aquatic chemistry: an introduction emphasizing
chemical equilibria in natural waters. Wiley and Sons, Inc. New York, NY 583p.
Wetzel, R. G. 1975. Linmolo y. W. B. Saunders Company, Philadelaphis, Pennsylvania,.
743 ppY
2-11

0
0
0
`Fable 2-1 . Water
chemistry
program for the McGuire Nuclear station NPDES long-term monitoring on Lake Norman.
199GUIRE NPDES SAMPLING
PROGRAM
PARAMUERS,
LOCATIONS
1.0
2,0
4,0
5e
8,0
9.5 11'0 13,0
14,0
Is 0 15 9 62,0
69O 720 800
16,0
DEPTH (m)
33
33
5
20
32
23 27 21
W
23 23 15
7 5 4
3
SAM CODE
IN -SITU ANALYSIS
Temperature
Hydrolab
t3nscofyed Oxygen
Hydrolab
In -situ measurements
are collected monthly at the above locations at Int intervals
front
03m w I mabove boriom
lA4
Plydrolim
Measurements
are taken weekly
from July -August
for striped bass habitat,
Conduciivity
Hydrolab
NUTRIENT ANALYSES
Arnmonia
AA -Nut
Q/T,B
QtT,B
Q/T
QfLB
QIT,B
Q/T,B Q/T,B QtT,B
QIT
QIT, B
QrLn
sn'
Nitrate+Nitrite
AA-NatQfl',B
Q/T,B
Qfr
Q/T,B
Q/T,B
Q/T,B Q/T,B Q/T,B
Q/T
QfT,B
Qrr,B
SIT
Orthophosphate
AA -Nut
Qfr,B
QIT,B
QfT
Q/7,B
Qfr,B
Qrr,B Q/T,B QIT,B
Q(r
Qfr,B
QIT,B
SfT
Total Phosphorus
AA-TP,DG-P
Qrr,B
Q/T,B
Q/T
QrLB
Q/T,B
Qrr,B Qrr,B Qrr,B
Qrr
Qrr,B
Q/-r,B
SIT
Silica
AA -Nut
Qrr,B
Qrr,B
Q/T
Qrr,B
Qrr,B
Qrr,B Q/-r,B Qrr,B
Q/T
OrT,B
Q/-r,B
SIrr
cl
AA -Nut
Qfr,B
Qn-,B
Q/T
Qrr,B
Qfr,B
Oru QrLB QIT,B
Qrr
Qrr,B
Qrr,B
Srr
TKN
AA-TKN
Qrr' B
Qtr,B
QfT,B
ELEMENTAL ANALYSES
Aluminum
ICP-24
Qrr,B
Srr,B
SIT
Q/T,B
Qfl',B
QIT,B QIT,B QIT,B
Q/T
Qrr,B
QfLB
S/T
cliciurn
ICP-24
Qfr,B
QrLB
Q/T
Q/T,B
Qrr.B
Q/T,B Qfr,B Qf U
Qrr
Qf u
Qrr,B
srr
iron
lCP-24
Qrr,B
Qrr,B
oil'
Qfr,B
Qrr,B
Q/T,B QrLB Q/-r,B
Q/T
Qrr,B
Q/-r,B
S/T
Magnesium
ICIP-224
Qrr,B
Qrr,B
Q/T
Qrr,B
Qrr,B
Qrr,B Qtr,B QrT,B
Qtr
Qrr'B
Qrr,B
SIT
Manganese
ICP-24
QN-,B
Qfr,B
Qfr
Q/T,B
Qrr,B
Qfr,B Qrr,B Qrr,B
Qrr
of r, 1,
QfLB
SIT
Potassium
306-K
Qrf,B
QIT,B
Qrr
QfLB
QrT,B
Q/T,B Qrr,B Qrrdt
Qir
QfI'L
Q/T,S
Sri,
Sodium
ICP-24
Qrr,B
Q/T,B
Q/T
Qrr,B
Qfr,B
Q/T,B Qfr,B Q(T,B
Qfr
Qrr,B
QrLB
S/T
Zinc
ICP-24
Qrr,B
Qrr,B
Qfr
Q/-r,B
Qrr,B
Q(F,s Ql-r,B QIT,ll
Qrr
Qq-,B
Q/T,13
sIrr
Cadminum
HGA-CD
srr,B
sn'
SfT,B
SfT,B
SIT
S/T,B
Srr
Copp vr
HGA-CU
S/T,B
str
SrLB
sfr,B
SIT
Sfl',B
S/T
Lead
HGA-PB
Srr,B
Sit'
S/T,B
SfU
SfT
Sfr,B
S/T
ADDITIONAL ANALYSES
Alkalinity
T-ALKT
QIT,B
Q/T,B
oft
Q/T,B
Q/1',13
Q/T,B Q/T,B Q/T,B
Q(r
Q/T,B
Q/T,B
SIT
Turbidity
F-TURFS
Qfr,B
Qrr,B
Q/T
Q/­LB
QIT,B
Qfr,B Qfr,B Qrr,B
Qrr
Qr1',8
QIT,B
S/T
Sulfate
UV—SO4
Sfr,B
S/T
srr,u
SIT
sfr,B
Srr
Total Solids
S-TSE
S/T,B
Srr
Srr.B
Srr
S1rLB
SIT
Torsi Suspended Sc
SJSSE
sfr,B
S/T
Srr,B
Sir
S/T,B
S/T
CODES Frequency Q =
Quarterly (Feb, May, Aug, Nov)
S = Scmi-annually
(Feh,Aug)
T = Top (03in)
B = rottom (t m above bouotn�

0
0
Table 2-2.
Water chemistry methods and analyte detection limits for the
McGuire Nuclear Station NPDES long-
term maintenance program for Lake Norman,
Yardah195.
E=Yalhal
D=dOldmil
Alkalinity, total
Electrometric titration to a pH of 5,12
40C
lmg-CaCO3T1
Aluminum
Atomic emission/ICP-direct injecition2
O5% HNO,
03 mg T1
Ammonium
Automated phenatel
40C
0.050 mg,l"
Cadmium
Atomic absorption/graphite farnace-direct injc�tion2
0,5% HNO,
0A �gTl
Calcium
Atomic emission/ICP-direct injecition2
0.5% HNO3
0.04 mg -1"
Chloride
Automated ferricyanidei
40C
1.0 rag Ti
Conductance, specific
Temperature compensated nickel electrode'
In -situ
I Pmhwcm*1
Copper
Atomic absorption/graphite fornace-direct injection2
0.5% HNO3
0.5 PgT1
Fluoride
Potentiometric2
40C
0.10 Mg .1"
Iron
Atomic err is injection 2
0-5% HNO3
0A mg T,
Lead
Atomic absorption/graphite fumace-direct injection2
015% HNO3
2.0 Itg•l'i
Magnesium
Atomic emission/ICP-direct injection2
015%HNO3
0.001 mg T,
Manganese
Atomic emission/ICP-direct injection2
0.5% HNO3
0,003 mg T1
Nitrite -Nitrate
Automated cadmium reduction'
40C
O,050 mg T,
Orthophosphate
Automated ascorbic acid reduction'
40C
0.005 mg T,
Oxygen, dissolved
Temperature compensated polarographic cell'
In -situ
O. I mg T,
pH
Temperature compensated glass electrode'
In -situ
0.1 std. units*
Phosphorus, total
Persulfate digestion followed by automated ascorbic acid
41C
0.00 mg Ti
reduction'
0.015 mgT1
Potassium
Atomic absorption/graphite furnace -direct injection2
0,5% HNO3
01 mg,P1
Silica
Automated molydosilicatel
40C
T
0.5 mg '
Sodium
Atomic ernission/ICP-direct injection2
0.5% HNO,
0.3 mg,I .1
Sulfate
Turbidimetric, using a spectrophotometer3
40C
1,0 mg T,
Temperature
Thermistor/thermometer'
In -situ
0.1 OC*
Turbidity
Nephelometric turbidity'
40C
I NTU*
Zinc
Atomic emission/ICP-direct injection'
O.5% HNO,
4 µg-l"
'United States Environmental
Protection Agency 1979. Methods for chemical analysis of water and wastes,
Environmental Monitoring and Support Laboratory. Cincinnati, OR
'USEPA. 1982
3 USEPA. 1984
Instrument sensitivity used instead of detection limit.
*Detection limit changed during 1989.

Table 2-3. Heat content calculations for the thermal
for 1998 and 1999.
are in Lake Norman
199
199
Maximum areal heat content (g cal/c )
28,371
28,432
Minimum areal heat content (g cal/cm--)
10,293
8,970
Maximum hypolimnetic;(below 11.5 in)
15,649
15„917
areal heat content (g cal/cM2)
Birge n het budget (g cal/c 2)
181,079
19,462
Epilimnion (above 11.5 rn) heating
0.094
0.084
rate (°C /day)
Hyp li nion (below 11.5 ) heating
0.085
0.07
rate (°C /clay)
2-1

0
Table 2-4. A comparison of areal hypoli
netic oxygen deficits ( HOD),
summer
chlorophyll a (chl ), secchi depth (SIB), and mean depth of Lake Norman
and 18 TVA reservoirs. "
AHOD
Summer Chl a
Secchi Depth
Meaty Depth
Reservoir
(mg/crn2/day) `
(g/L)
( )
(in)
Lake Dorian
0040
5.5
2.03
10.3
TVA a
Mainstern
Kentucky
0.012
9,1
1.0
5.0
Pickwick
0.010
3.9
0.9
6.5
Wilson
0 028
5.9
1.4
12.
Wheel e
0.012
4.4
5.3
Guntersville
0.007
4.8
l :l
5.3
Nickajack
0.016
2.8
L l
6.8
Chickamauga
0.008
3w0
1.1
5.0
Watts Bar
0:012
6.2
1.0
7.3
Fart London _
0.023
5.9
0 9
7.3
Tributary
Chatuge
0:41
5.5
2.7
9.5
Cherokee
0.078
10.9
1.7
13,9
Douglas
0.046
6.3
L6
10.7
Fontana
0.113
4.1
16
3 .8
Hi assee
0.061
, .0
2.4
20.2
Norris
0058
2. l
3.9
16.3
South Holston
0: 70
6.5
2.6
2.4
Tines Ford
0.059
6.1
2,4
14.9
Watauga
0.066
2.9
23
24.5
a Data from Higgins
et al. (1980), and Higgins
and Kim (1981 )
-1

0
0
0
Table 2-5. Quarterly surface
(0.3
m) and bottom
(bottom
minus
I m) water chemistry for the
MNS discharge, mixing zone, and background locations on Lake
Norman during
1998 and 1999.
Values less than
detection were assumed to be the
detection limit for
calculating
a mean,
MixIng Zone
MIxing Zone
MNS Discharge
Mixing Zone
Background
Background
LOCATION:
1.0
2-0
4.0
5a
8.0
lic
DEPTH
Surface
Bottom
Surface
Bottom
Surface
Surface
Bottom
Surface
Bottom
Surface
Bottom
PARAMETERS YEAR,
98
99
98
99
98
99
98
99
98 99
98
99
98
99
98
99
98
99
98
99
98
99
Turbld,ty turn)
Feb
2.8
1.87
4.5
U
5,4
is
U
8.2
41 1.8
3
1,8
NS
4.3
92
1,6
42
7.7
21
1,7
31
122
May
2,7
1,77
6A
12.5
2,15
2,0
71
2.9
3.1 2,6
2.7
2.3
$A
13
1,78
2,2
7.1
3.2
2,3
2.9
8A
13
Aug
1,7
1 .71
2,9
5:2
1.52
21
3S
22
IAB i's
1,76
1.5
C84
21
1,65
1,6
&05
2B
105
2a
IT6
2.6
Nov
2.2
1.9
7.6
3a
2.0
2:0
3.7
sa
2.0 2,7
2.1
22
8,5
4,3
2,5
21
4.7
4:3
3:9
2.2
3.2
12.0
Annual Mean
235
1,80
534
619
2,84
is
5,60
4.9
2.83 2.1
2.40
2c
3,6
179
1.9
6.01
4.6
T56
22
14,98
T5
7Spectttc Conductance (urnholcm)
_6.91
Feb
S8
52
60
68
58
51
60
61
60 53
59
52
58
53
62
51
58
67
58
53
53
66
May
42
60
38
95
46
60
38
59
40 60
40
60
45
59
40
60
38
59
35
60
37
66
Aug
54
60
66
66
55
60
61
64
55 60
56
60
65
63
55
60
63
63
55
61
64
61
Nov
55
64
— 58
105
64
79
56 64
55
64
—5970
55
—75-8
63
55
63
57
63
58
64
57
65
Annual Mean
523
59,0
55-5
8-35
53.0
5-88
5-30
6-58
5-28 5-93
5-25
—595
­o3 0
78-5
54b
610
51,5
59,5
62.8
64,5
pH (units)
Feb
6A
6,3
6a
6,3
6s
6.6
6,6
6.3
6A 6,6
6S
6,7
6.6
6.4
6,5
6.7
6,6
6.5
6,6
6.7
6A
6.5
May
6,6
6 3
5,9
6,2
6s
6'5
6.0
6.5
6.3 6,5
6.4
8.6
6,0
6,7
6,7
63
6c
6,5
6.9
61
5.9
6.4
Aug
7,6
7.1
6A
U
7A
7.2
63
6.2
7A 6,8
Ta
7,0
6A
61
8,0
7.9
6.3
6,2
71
8.0
6,3
62
Nov
7.0
6.6
6A
6.6
—
6.8
—
6.5
6.9 6.8
72
6.9
6,8
6.7
71
7.0
63
6.8
7.3
7,0
6.7
6'5
Annual Mean
688
6.55
638
6.32
6,83
6,75
6.30
6,38
6.68 6,68
—
6�93
679
6AS
6A7
T08
7�07
—
6,40
—
6.48
—
6aty
—
711
—
U3
—
6.39
Alkalinity (mg CaCO3/1)
Feb
13,5
130
13.0
13,0
12.5
13a
110
115
115 13a
11.5
110
NS
115
12,0
12,5
12.0
13.5
12.0
115
145
12.5
May
11.0
14.5
it's
14,0
11,0
14,0
11.5
14,0
11.0 14 a
12.0
115
it's
14,O
11:5
115
10,5
14.0
11.0
13,5
10'5
14,0.
Aug
13.0
15.0
15.5
17.6
110
14.5
15.5
14,5
13,0 14.5
i10
14,5
18,5
15.5
13.0
14,5
l7c
17,0
115
14o
16,5
16,0
Nov
14,0
16:0
—14
17.5
16.5
14.0
16,0
14.0
16.0
14,0 16.0
13,5
16.0
1445
16.0
14.0
i5.5
144
15'5
115
15.5
14S
15'5
Annual Mean
12.88
64
7-4-25
1526
12,63
14.39
1150
14,51
1288 14,39
12,00
14.26
14,83
1416
12,63
14,01
13,38
15,0,
12450
14�14
388
4,5,
5—ilonde (mg/1)
Feb
se
4,9
5,9
5,2
ss
51
5.9
545
5.6 4,9
5A
4,8
NS
5.0
61
4,8
51
5,8
5.9
4,9
51
6,3
May
4,3
51
44
5.2
43
5,0
44
5.1
4A 51
42
51
4.5
5,1
4A
5.1
42
512
3.8
5,2
4A
5a
Aug
4.1
5,0
4,5
4.8
4,3
4,9
4,3
4.9
4A 4,9
4,2
4,9
42
4.9
4,5
4S
4,2
43
41
4,9
42
4-8
Nov
42
5.0
4,8
5.0
44
5.0
4,5
se
4A 5.0
4,3
4:9
4.4
4,9
4a
&0
4,3
5,0
4,7
5,0
4.7
5,4
Annual Mean
'�—ultate
455
500
490
5o5
4,63
5.00
4.78
5.13
4.63 4.98
4_ 53
4 91
437
4 911
4110
495
460
5 18
j.63
500
453
5,18
(mgA)
Feb
NS
NS
NS
NS
4,9
4,5
6.5
so
5,8 44
NS
NS
NS
NIS
8A
4,3
8.4
5.3
INS
NS
NS
NS
May
NS
INS
NS
NS
NS
8.7
NS
8.2
NS 8.2
NS
NS
NS
NS
NS
91
NS
U
NS
NS
NS
NS
Aug
NS
RE
NS
INS
52
6S
4.6
NS
SA 86
NS
NS
NS
NS
5.0
9.6
1,6
NS
NS
RE
NS
NS
Nov
NS
NS
NS
NS
4e
7,7
5,3
82
3,7 68
NS
NS
...DNS
NS
3:8
7;5
18
7,2
RE
NS
NS
NS
Annual Mean
-Ea—lctum
—
4,70
6.85
5A7
T13
4.97 700
523
7,63
460
683
(rngA)
Feb
2,58
2,71
2,62
2,67
2.58
2.75
2,64
2,72
2.64 2,72
2,67
2,73
NS
2,69
210
2,75
2,62
2.70
NS
2:76
2A2
2,84
May
2,76
2:86
2,82
2,95
2:70
2,87
2,83
2,92
2,76 2,88
2,60
2.87
239
2,86
2;73
2,89
2.85
2,97
2.73
310
2,90
3.04
Aug
2:88
3.01
3,14
3,33
2,87
102
313
121
2,86 2,99
2.77
3,00
3,22
3.15
2.90
2,99
3,27
3.29
2,98
105
3.22
3,26
Nov
2,86
—
3,11
—
283
_T8_5
3.17
2.91
--'�
3.13
—T
2,92
—�-88—
315
2.91 3,12
—'�
2,89
—17-3
3,17
290
314
2,89
3,14
2.86
116
2:68
2.97
2,70
2.68
Annual Mean
217
2�92
3-03
7-6
9-4
3-00
7-9 2-93
=94
9-7
—296
8-0
2-94
—T9-0
3-03
7-9
7—
97
—T _9
—F 9-5
Magnesium (mg/1)
Feb
1.34
1.33
1S3
1:32
1.33
1.35
1,33
1,36
1.35 1.33
1.36
1,33
NS
1,33
1,32
1,35
1,34
1.33
NS
1.34
1 25
35
11,41
may
1.23
1.38
1,23
IA2
1.19
128
1.25
1,39
1.21 1,38
1,21
1:38
1,24
1.38
1.21
1:38
123
1.41
1,14
1,40
1.23
Aug
1,29
1.45
1;36
1.55
1,31
1,44
1:36
1.50
1,29 1,42
1,31
1:44
1,38
1 As
1,30
1A4
1.40
1-52
1,33
1,46
1,39
1.50
Nov
1.34
1,53
1 .40
1,55
1.37
1.52
1.37
1,52
1,36 1,53
1,37
1,55
1.35
1.53
1„35
1,53
1,36
1,56
1,35
1,52
1 ,
Annual Mean
1 30
42
33
1-46
1-30
142
1.33
---- =Z-
127
—
1,43
_L37
1,31
L49
1,44
NS . Not Sampled

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Figure 1 Water quality sampling locations for Lake Norman.
2-1

McGuire Rainfall
C3
J;AN FEB
MAR APR MAY JUN JUL AUGEP OCT NOV DEC
Month
Figure 2-2,
Monthly precipitation in the vicinity of McGuire Nuclear Station.
2-2

JAN
FEB
MAR
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
s 1,.,.1
0
,,,
0-
10-
10-,10
E 15
15
15
20
�20
20
25
25
25
30-
30
30
35
35
35
APR
MAY
JUN
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
10
10
10
E 15
u
� 15
15
7
20
p2020
c2
25 "
25
25
30
30
30-
35
35
3
Figure
-3. Monthly mean temperature profiles for the McGuire
Nuclear Station background zone
1n 1998 and 1999 ( i.
P�J

JUL0
AUG
SEP
Temperature (C)
Temperature (C)
Temperature (0)
0 5
p-
10 15 20 25 30 35
0
5 10 15 20 25 30 35
0
5 10 15 20 25
30 35
5
5
5
10
14
10
o20
p20
20
25-
25-
25
30
30
30
35 -
35
35
OCT
NOVDEC
Temperature (C)
Temperature (C)
Temperature (C)
0 5
0
10 15 20 25 30 35
0
5 10 15 20 "25 30 35
0
5 10 15 20 25
30 35
0
0
5
5
5
10
10
10
�15
FT
�15
�15
cr 20
c, 20
20
25
25
25
30"
30
30
35'
35
35
Figure 2-3. (can't).
N
H

JAN FEB MAR
Temperature (0) Temperature (0) 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 4--L-
5-
10- 10- 10
15
15
IL
20 50 20
25- 25- 25-
30- 30 30
35-, - 35L 35LF-
APR MAY JUN
Temperature (C) Temperature (C) Temperature (0)
0 5 10 15 20 25 30 35 0 5 10 15 20 25 30 35 0 5 10 15 20 25 30 35
04 ---- A- — 0-- -- 0
5 5- 5
101 10-, 10
15- 15 - 5
20- 20- 20
4 26 25
: 5 030 T 30
Figure 2-4. Monthly mean temperature profiles for the McGuire Nuclear Station mixing zone in 1998 and 1999

0
0
JUL
AUG
SE-P
Tomperature (c)
Temperature (c}
Temperature (C)
0
0
5 10 15 20 25 30 35
0 5 10 15 20 25 30 35
0 -
0 5 10 15 20 '2 5 30 35
0
10
10
10
20
8) 2 o
L
20
25-
25
25
30
30-
035. 3
35
35
OCT
NOV
ose
Temperature (C)
Temperature (C)
Temperature (C)
0
5 10 119 20 25 30 35
0
5 10 15 20 25 30 35
0
5 10 15 20 25 30 35
5f
5
5-
f
10
t 0
10-
15
20
20
020-
25
25
25
30
30
30
35
Figure 2-4. (con't),

40
35
ff ,
r
30
25
�
20
l
°a
d..
CL
1
F- 0
Jan Feb Mar Apr May Jun Jul Aug Sop Oct Nov Dec
Month
1
10
t
..
Jan Feb Mar Apr May Jun Jul Aug SepOct Nov Dec
Month
1
Figure 2-5,
Monthly surface (0. m) temperature and dissolved oxygen data at the discharge
location (lac. 4,0) in 1 ( ) and 1 (11),
2-25

0
0
0
JAN
FEB
MAR
Dissolved Oxygen (mgJL)
Dissolved Oxygen (mgfL)
Dissolved Oxygen (mgQ
0
2 4 6 8 10 12
0
2 4 6 8 10 12
0
2 4 6 8 10
12
0
1010
15C)
I10
2020
-
20
Fj
25
25
25
3o3o335-30
L---
35
APR
MAY
JUN
0
Dissolved Oxygen (mgfL)
2
Dissolved Oxygen (mgfL)
Dissolved Oxygen (mgA-)
0
4 6 8 10 12
0
0
2 4 6 a 10 12
0
2 4 6 8 10
12
0
5
5-,
5
10
10--
10
20-
-
020
20
25
25
25-
30,
30
30-�
35
35
Figure 2-6.
Month1v mean dissolved oxygen
profiles for the
McGuire Nucleir Station background zone in 1998 and
1999

0
0
0
JUL.
AUGP
Dissolved Oxygen (mg/L.)
Dissolved Oxygen ( gfQ
Dissolved Oxygen (Mg1L.)
0 2 4 6 8 10 12
0
2 4 6 8 1012
0
2 4 6 8 10
12
0
5
0
taw
0
10
10
10
T
L
5
15
�15
2q
q 0
t 0
25-
25
25
30
30
30
35tL
35
_
35 "
7
NOVDEC
Dissolved Oxygen (mgrL)
Dissolved Oxygen (mg1L3
Dissolved oxygen (mgdL)
0 2 4 k 8 10 12
0
2 4 6 8 10 12
0
2 4 6 8 10
12
3 w
t
(}
0
i
10
10
10'
15
15
15
20 A
0
20
25
25
25
30
30
30
3
5
35
Figure -6. (con't).
c,;
cw:a

0
JAN
FEB
MAR
Dissolved Oxygen (mgfL)
Dissolved ox)egen (mgjL)
Dissolved Oxygen (MgfL)
0
2 4 6 8 10 12
0
2 4 6 8 10 12
0 2 4 6 8 10 12
10
10
10-,
15-
20
L
cj20'
020-
25
25
25-
30
30
30
35-
35
APR
MAY
JUN
Dissolved O�cygen (mgfL)
Dissolved Ox),gen (rngfi-)
DissoNed Oxygen (MgfL)
0
0
2 4 6 B 10 12
0
2 4 6 8 10 12
0 2 4 6 a 10 12
20
5
5
10
10-,
10
15
15
—15
20
j 20
020
25
25
25
30
30
30
35
36
35
Figure 2-7.
Monthly
mean dissolved oxygen profiles for the
McGuire Nuclear Station mixing zone in 1998 and 1999

JUL
AUG
SEP
Dissolved Oxygen (M91L)
n- Is solved Oxygen (;,ngIL)
Dissolved Oxygen (mg/Q
o 2 4 6 8 10 12
0
2 4 6 8 10 12
0
2 4 6 8 10
12
0- 1
0
0
5
6
5
10
10
10
15
15
15
20
c a 20
20-
25-
26
25
30-
30
30
35--
35
35
OCT
NOV
DEC
Dissolved Oxygen (mgfL)
Dissolved OXYgPll (t-ngft-)
Dissolved Oxygen (mgfL)
0 2 4 6 a 10 12
0
2 4 6 8 10 12
0
2 4 6 a 10
12
0
0
0
5 f
5'
10
10
10
E 15_
2 15
15
20
20
M.
20
25
25
25
30
30
30
35 -
35
35
Figure 2-7, (con't),

24
Sampling Locations
Sampling Locations
23
jo 8,0 11,0
130 15,0 15'9 62,0 69.0 720 800
23
1.0 80 11.0
13,0 15,0 15,9 620 690 7210 80,0
------
---- ---
23
✓23
------
14
22
22
E
E
22
i
22w.
E
E
21
21
u' 21
uj 21
20
20
20
Temperature (deg C)
20
Temperature (deg C)
Jan 4, 1999
Feb 10, 1999
10 15
20 25 30 35 40 45 50 55
10 15
20 25 30 35 40 45 50 55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
240
-
240
Sampling Locations
Sampling Locations
23
1,0 e.o 11,0
13,0 15O 15,9 62.0 69,0 72,0 80,0
235
In 80
1,0 8,0 11,0
13,0 150 15,9 62,0 690 720 80,0
-720 800
23
230
22
225
Z�
16
14
22
220
C 21
0
215F
/I
ul 21
210.Z
20
205:
20
Temperature (deg C)
200
Temperature (deg C)
p
kilar 18,1999
��101�520�25
Apr9
r : 7,199 9
19
195
1 15
20 25 30 3 40 4
�30 35 05
44 5_0 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 1999,

Sampling Locations 240 Sampling Locations
23 'a 8,0 Ito 13,0 15,0 15,9 6240 69,0 710 800 235 10
80 11.0 13.0 15.0 15,9 62,0 69,0 73.0 180.0
23
20 230
18 Li
22 27
22
E V) 25
9� 6 24
22
220 ZZ2
21 14
21
J� ------- u' 210
f Nlti M 210
20
20
20 Temperature (deg C)
200 Temperature (deg C)
19 icy5, 1999 Jun 10, 1999
10 15 20 25 30 35 40 45 50 55 19 'JU" 'U'
--T�l 0 5 �2O 2 �5 3 '3d3 �54 O� Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (krn) 45 �50 �55
240
Sampling Locations 2 4 0
Sampling Locations
23 10 8.0 11.0 13,0 15.0 15,9 62.0 69c 72,0 80,0 23 1,0
80 110 13,0 15,0 15,9 62-0 690 72,0 80.0
23
30,' sa, 23 Is
30
225
E 29
R
220 :IZ:7
E
21 E
21
210
w 21
IIL�-4
20
V
20
20 Temperature (deg C) 200 Temperature (deg C)
Jul 7,1999
19 1C7 15 2Q 25 30 35 40 45 5Q 55 195 10 15 20 25 Aug9,1999
Distance from Cowans Ford Dam (km}3 35 4 4 5 55
Distance Prom Cowans Ford Dam (km)
Figure, 2-8. Continued.

Sampling Locations
240-
Sampling Locations
23
1 1 0 810 11.0 13,0 15a 15.9 62.0 69.0 72,0 80,0
235:
10 8,0
110 13.0 1SO 1S.9 62,0 690 720 80o
23
27' 26
2304
22
22
220
0
E
22
21
2f,
IS 21
21
uj 21
20
20
200
Temperature (deg C)
20
Temperature (deg C)
19
Sep 7, 1999
Od 11, 1999
1 15 2025 30 35 40 45 50 55
19
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
240
—
24
Sampling Locations
Sampling Locations
23
10 8o 11'0 130 1SO 15,9 620 69,0 72,0 MO
23
10 80
11,0 130 15.0 15,9 620 690 720 800
23
23
— ------- — -----
22
22
E
E
> 22
22
E
21
21
210t
21
1
205
20
--------
20
Temperature ((deg C)
20
Temperature (deg C)
Nov 1, 1999
Dec 8,1999
19
1 15 2 �O2 5�3 C, 35 4O �5O5�5
19
23
10 15 0 27305 4 -"---7-50,1 �45 �5�55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
Figure 2-8. Continued.

---1 240-
Sampling Locations - Sampling Locations
235,: 10 8.0 11.0 13,0 15.0 1&9 62.0 69.0 72,0 80.0 235--1c 80 Ito 13,0 15.0 15.9 62,0 69:0 72,0 80,0
230: 230-
225 225
220- 220
E
215' 215
0
M 210-- Ao-, to 210
205,: 205 10
C>
200 Dissolved Oxygen (mg/1) 200 Dissolved Oxygen (mg/1)
Jan 4, 1
9
5 0
45�50 55 10 15 20 2 3 35 40 45 50 55
Jan 4, 1999 Feb 10, 19-9-9-
195 0 15 2 25 �30 3 40 19,
Mstance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)
240- 240-
Sampling Locations Sampling Locations
235, 1.0 8.0 110 110 15.0 15,9 62,0 69,0 7207180.0 235-:1 0 80 11.0 13,0 15.0 15,9 620 690 720 800
23C�:
r 10
225-
225:
r
FF E
220 1 0 220:
E
cc 215 215-
0 210-- M 210:
C> -
205-: 205:
20 Dissolved Oxygen (mg/1) DiSSOIVZd oxygen (mg/1)
0 20 Dissolved Oxygen (mg/1)
Nbr 18,1999 9
19 _�----- — Apr7,1999
1 19 0 15 20 �2 5 30 35 40 45 50 55
Distance from Cowans Ford Dam (krm Distance from Cowans Ford Dam (km)
Figure 2-9. Monthly reservoir -wide dissolved oxygen isopleths for Lake Norman in 1999.

Sampling Locations Sampling Locations
23 107 so 11 0 13o 1510 15.9 6210 Mo 72Z 8010 I'0 8'0 9 i.0 13.0 95o 15,9 62,0 69.0 720 80o
23
23
Cb �b
22 Q-
2251
E
E
220- 220'
0
9 1 . —
cc 215.:
16 rf'CO 215'
N
210--
210-
2054
205-
Di 'Solv%d oxygen (mg/1)
20 Dissolved Oxygen (mg/1)
5 1999
200 Dissolved Oxygen (mg/1)
19 NbY 5, 1999 Jun 10, 1999
4' 0 �5O� 0 0 45 50 55 195
1 1 2 25 30 35 4YO 4 50 55
10
Distance from Cowans Ford Dam (km) t4 50 55
Distance from Cowans Ford Dam (km)
240 240-
Sampling Locations
Sampling Locations
235 10 B'o 110 130 150 15,9 62L 69,0 710 80,0 235-1,0 80 11.0 13,0 15Z 15.9 62,0 69.0 720 800
23 230*--------"--(------4—"-------'----l-'-------'----"--"---
mot,I\ af,
5 0 0
C,
225
225-
E
E
220 5 -Z
220-
E
21 0
215-
210-
210-
--N
205:
205-
200 Dissolved Oxygen (mg/1)
200 Dissolved Oxygen (mg/1)
19 19 15 -- Jul 7,1999 19 'SS Aug 9,1999
0 5
1 15 250�25 �30 �35 �40�455O�55 10 15 20 25 3 35 40 ' 1994 50 55
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
Figure 2-9. Continued,

Sampling Locations —0 Sampling Locations 0-
23 10 &0 110 13,0 1&0 15,9 62.0 69.0 710 800 23 1,0 8,0 11.0 13,0 15,0 15,9 620 69,0 720 80,0
23
225-
6
0-
22 22
7
21
5
J
21
20
20
200 Dissolved Oxygen (mg/1)
20
Dissolved Oxygen (mg/1)
19 Sep 7, 1999 19 w 11, 1999
0
15' 20' 25 30�3 5 40 �46 �50 55 10 15 20 25 30 35 40 45 so 55
Distance from Cowans Ford Dam (km} Distance from Cowans Ford Dam (km)
240
240-
Sampling Locations
SaMPling Locations
23 F110 &0 130 15,0 159 62.0 690 72.0 800 2310 &0Mo13,0 15.0 1&9 62,0 690 720 80,0
22
22 6.
E
220-
220
21 ✓ 215-
M
21 a
u-' 210-'
0
"N4
220�<
20 Dissolved Oxygen (mg/1)
200 Dissolved Oxygen (mg/1)
Nov 1, 1999
9 is 20 25 3 3 4 45 50 5 19 ... Dec 8,1999
1
A . . . . i6`7�530�35 �40 �45 59 �55
Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)
Figure 2-9. Continued.

�
30 �w
25
Cr
15
10
,
...........
99000 99050 99100 99150 99200 99250 99300 99350
Julian Date
Figure 2-1 u. Heat content of the entire water column () and the hypolimnion ()
in Lake Nu an in 1999.
1080
-. Ca'-
CM IN
CU
40
X 4
CL
99000 99050 99100 99150 99200 99250 99300 99350
Julian Date
Figure 2-1b. e
Dissolved oxygen content (-) and percent saturation ( --- ) cat the entire
water column () and the by olimnion (: ) of Lake Norman in 1999.

H
Distance from Cowans Ford Dam (km)
Distance from Cown s Ford Dam (km) vw
240-
LAKE NORMAN STRIPED BASS HABITAT
-
LAKE NORMAN STRIPED BASS HABITAT
'0 8,0 11,0 13,O 15,015,9 62.O 69.O 72,0 MO
23
8,0 11,0 13.0 15,015.9 6ZO 69,0 72.0 80,0
---- --- ---
- ------
22
E
E
220
.2
215
>
210
NN
110- Jul 27, 1999 20 Aug 2, 1999
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 Dam (km) Distance from Cowans Ford Dam (krn)
Figure 2-11 . Striped Bass habitat (temperatures 26 deg C and dissolved oxygen 2 ug/1) in Lake Norman in June, July, August,
September, and October 1999,

240
LAKE NORMAN STRIPED SASS HABITAT
LADE NC RMAN STRIPED SASS HABITAT
2
0 8:0 i to 13.0 15.015.9 62.0 69,0 72.0 80,0
2 5
.0 8.0 11.0 13,t 15.015.9 62,0 69.0 72.0 80,0
230-
230
_
225
-
5
�f
215-
ram"
21 V pp�y
rr{{
^,�..
„g p�
2
r.
LU
6 V
r
'
py
205
205
00
Aug 16, 1999
2�10
*
Sep 1, 1999
i.7
95
0 5 10 15 20 25 30 35 40 45 50 55
0 5 10 15 20 25 3C} 35 40 45 50 5
Distance from Cowans Ford Dam (km)
Distance from Cowans Ford Dam (km)
240
240.
IMF NORMAN STRIPE SASS HABITAT
LAKE NCJRMAN STRIPED SASS HABITAT
235
•0 8.0 11'0 13.O 15.015.9 62.0 69.0 72.0 80,0
23
.0 8,0 11.0 13.O 15.015.9 6ZO 69�0 7ZO 80.0
w
w.._
230
__ _... _ ,_u.
��ryy
230--
225-
c
225
22
E
2217
15
.:
215
210'
21200
4{
Sep , 1 9
_. w........--'
zoo
..,.....'. Oct11, 1999
1
15
y
0 5 10 15 20 25 30 35 40 45 50 55
0 5 '1015 20 25 30 5 40 45 50 5
r
Distance from CowansFire! Dam (
Distance from Cowans Ford Dam (
Figure
-11, (con't).

CHAPTER3
PHYTOPLANKTON
INTRODUCTION
Phytoplankton standing crop parameters were monitored in 1999 in accordance with the
NPDES permit for McGuire Nuclear Station (). The objectives of the phytoplankton
section for the Lake Norman Maintenance Monitoring Program are to:
1. Describe, quarterly patterns of phytoplankton standing crop and species
composition throughout Lake Norman; and
2. Compare phytoplankton data collected during this study (February, May,
August, November 1999) 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, 19 5; "Menhinick and Jensen 1974; Rodriguez 1982). Rodriguez (19 2)
classified the lake as oligo-meotrophic 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, &0, 9.5, 11,0. 13.0a 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 in (i.e., the estimated euphotic zone) were taken and then composited at all but
Location 69.0, where grabs were taken at 0.3, 3.0, and 6.0 in due to the shallow depth.
Sampling was conducted on 4 February, 3 May, 25 August, and 12 November 1999.
Phytoplankton density,_biovolume and taxonomic composition were determined for samples
collected at Locations 2.0, 540, 9.5, 11.0, and 1 .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 biovolume's were used in determining phytoplankton
standing crop. Field sampling methods, 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 1999 were compared with corresponding data
from quarterly monitoring beginning in August 1987.
A cane-wayANOVA was performed on chlorophyll a concentrations, phytoplank'ton densities
and sexton dry and ash free dry weights by quarter. This was followed by a Duncan's
Multiple Range Zest to determine which location means were; significantly different.
RESULTS AND DISCUSSION
Standing Crop
Chlorophyll c
Chlorophyll a concentrations mean of two replicate composites) ranged from a low of` 1.21'
ug/l at Location 2.0 in May, to a high of 14.42 ug/l at Location 69.0 in August (Table 3-1
Figure 3-1. .All values were well below the Forth Carolina water quality standard of 40 ug/l
(NCDEHNR 1991). Lake --wide mean chlorophyll concentrations in February and May of
1999 were the lowest yet observed for these periods since the study began (Figure 3-2). The
annual lake -wide mean chlorophyll concentration. in August was it the high range for this
month, whereas the mean for November was in the mid range. The annual trench in 199 of
maximum values in August, with minimum values in May has newer been observed during
the course ofthe Lake Norman Maintenance Monitoring Study, According to Water Quality
Criteria (1972) which Leases trophic status on overall chlorophyll concentrations, value; of 4;
ugfl or less are considered oligotrophic. Although Lake Norman continues to be primarily in
the naesotrophic range (>4 ug/l to 1.2 ug/1), lake -wide means in February and May were well
below the level of oligotrophy. Lake -wide quarterly mean concentrations below 4 ug/l have
been recorded on six previous occasions. record low chlorophyll concentrations in February
and May 1999 may have been due, in part; to very low rainfall during the seasons prior to
sampling. The cumulative rainfall total during the fall of 199 (October through December)
was among the lowest fall totals observed since sampling began. The total accumulated
rainfall during the winter of 1999 (January through March) was the _lowest winter total ever
observed during this monitoring steady (McGuire Nuclear Station, monthly rainfall totals
1-1999). Very low cumulative rainfall totals during the seasons preceding Februaryand
May 1988 were also followed by the second lowest` lake -wide chlorophyll means ever
recorded (Figure -). Low rainfall, and lack of inputs from runoff would tend to reduce'
nutrient availability throughout the lake.
3-2

�
During 1999, chlorophyll a concentrations showed considerable spatial variability.
Maximum concentrations were observed at Location 15.9 during May and November, and at
Location 69.0 in February and August (Table -2). Minimum concentrations occurred at
Location 2.0 during all but august, when the, minimum was observed at Location 13.0. The
trend of increasing chlorophyll concentrations from down -lake to up -lake, which had been
observed in 1994 (Duke Power Company 1995), was not as apparent during 1999.
Increasing; values from down -lake to up -lake were observed to some extent in November
when chlorophyll concentrations increased from the Mixing Zone locations (2,0 and 5.0) to
15.9, then declined at Location 69.0 (Table 3-1, Figure 3-1)._ In tact, a consistent pattern of
increasing values from down. -lake to up -lake has not been observed since 1994. Location
15.9 (uptake, above Plant Marshall) had significantly higher chlorophyll values than Mixing
Zone locations during all sample periods, and Locution 69.0 (the uppermost, riverine
location) had significantly higher values than Mixing Zone locutions in February and August
(Table 3-2), Flow to the riverine zone of a reservoir is subject to wide fluctuations
depending, ultimately, ; on meteorological conditions" (Thornton, of al. 1990), although
influences may be moderated due to upstream dams. Luring 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 would gradually decline
once more. These conditions result in the high variability in chlorophyll concentrations
observed between Locations 15.9 and 69.0 throughout the year. as apposed to Locations 2.0
d 5.0 which were very similar during each sampling period,
Average quarterly chlorophyll concentrations during the period of record. (August 1987 -
November 1999) have varied considerably (Figure 3-3,). Luring February 1999, Locations
5,0, 8.0, and 11.0 hard the lowest February chlorophyll concentrations on record, while
Locations 2.0, 9. , and 13.0 had the next to lowest concentrations yet observed. (Figure 3-3).
Chlorophyll concentrations at Locations 15.9 and 69.0during February were in the low to
mid range. 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. The
highest February value at location 69.0 occurred to 19 7. During May 1999, chlorophyll
concentrations at all locations were the lowest yet observed for this sampling period. Long-
term: May peaks at Locations 2.0 and 9.5 occurred to 1992„ at location 5.0 to 1991, at
Locations 8,0 and 11.0 through 15,9 in 1997, and at Location 69.0 to 1996.
3-3

Chlorophyll concentrations at Locations 2.0 through 9,5 in east 1999 were in the high
range. At Locations 11.0 through 69,0, August 1999 chlorophyll values were in the
intermediate to upper ranges, Long -tents August peaks in the Mixing Zone were observed in
1998, while year-to-year maxima at Locations 8.0 and 9.5 occurred in _1993. Long-terni
August peaks at Locations 11.0 and 13.0 were observed in 1991 and 1993, respectively. The.
highest August chlorophyll concentration 1rorn Location 15.9 was observed in 1998, while
Location 69.0 experienced its long term August peak in 1993.
In November, chlorophyll concentrations were in the low range at Locations 2.0 through 9.5.
At Locations I1.0 and 13.0 November 1999 chlorophyll concentrations were in the
intermediate to high ranges, while November concentrations at Locations 15.9 and 69.0 were
in the mid range. Long-term. November peaks at Locations 5.0, .0, and 11.0 through 15.9
occurred in 1996 while November maxima at Locations 2.0 and 9.5 were, observed in 1997.
The highest November chlorophyll concentration at location 69.0 occurred in 1991 . All
locations had higher November values in 1999 than in 1998,
Total Abundance'
Density and biovolume are measurements of phytoplankton abundance. Phytoplankton
standing crops during 1999 were generally lower than these of previous years; especially
during February and May (Duke power Company 1999). The lowest density during 1999
occurred at Location 11.0 in :February (530 unitstml), and the lowest biovolume ( 1
mm31m') occurred at Location 2.0 during; May; ("fable 3-3 Figure 3-1). The maximum
density occurred at Location 9.5 in August (6,495 units/ l), while the highest biovolume was
observed at Location 1`5.9 in November (3,660 11IM /ni'). Phytoplankton densities and
biovolumes during 1999 never exceeded NC state guidelines for algae blooms of 10.000
unit lml density, and 5,000 mm3t"m3 biovolume (N L EFIN1 1991). Densities and
biovolumes in excess of NC guidelines were recorded in 1998 and 1997 (Duke Power
Company 1,999):
Total densities at locations in the Mixing Zone (2.0 and 5.0) during 1999 were within the
same statistical ranges during all sampling periods but February (Table 3- ). In May,
August, and November Location 15.9 had significantly higher densities than Mixing Zone
locations. During February Location 2.0 had the maximum density, and was to the same
statistical range as Location 15.9. In August, Location 9.5 had the highest density, which
was significantly higher than densities at other Locations. In November, phytoplankton
-

densities showed a spatial trend, similar to that of chlorophyll, of lower values at down -lake
locations versusup-lake locations. During February, May, and August, no consistent "
distribution patterns were observed.
Seston
Seston dry weights represent a combination of algal muter., and other organic and inorganic
material. Location 69.0 the uppermost riverine location, had the highest sexton dry weights
during all sample periods except May, when the maximum dry weight was observed at
Location 15.9 (Table 3-5). No consistent spatial trends of dry weights were observed In 1999
(Figure 3-1). Statistically, Location 69.0 had significantly higher values than other locations
in February, August, and November, During May, no statistical differences were observed.
From 1995 through 1997 seston dry weights had been on the increase (Duke Power Company `
1998). Values since 1,998 represented a reversal of this trend, and were in the low range at
most locations during 19 (the exception was the very high dry weight at location 69.0 in
August):
Seston ash -free dry weights represent organic material and may reflect trends of algal
standing crops. In most cases, relationships between ash -free dry weights and chlorophyll
concentrations and standing craps were not very apparent. In some eases, a relationship was
observed, most notably at Locations 15.9 and 69,0, which had the highest ash -free dry
weights, as well as maximum chlorophyll values during 1999 (Tables 3-1, -2, and 3-5).
Location 15.9, which had comparatively high ash -free -dry -weights in May, august, and
November also had high density values during these periods (Fables 3-4 and -5). In terms
of statistical significance, Location 69.0 had significantly higher values than other locations
in August (Table -5). During the other throe sampling periods, little or no statistical
differences were observed. The ratios of ash -free dry weights to dry weights during 1999
-were slightly higher than in 1998, indicating a very small increase in inorganic inputs during
1999. Between 1994 and 1997, a trend of declining organic/inorganic ratios was observed
(Duke Power Company 1995, 1996, 1997, 1998).
Secchi Depths
Secchi depth is a measure of light penetration. Secchi depths were often the inverse of
suspended sediment (se ton dry weight), with the lowest secchi values at Locations 13.0
through 69.0 and the highest values reported from Locations 9.5 through 2.0, Secchi depths
-

ranged from 0.77 in at Location 69.0 in May, to 3.81 in at Location 2.0 in February (Table -
1 ). The lake -wide mean secchi depth during 1999 was the deepest recorded since
measurements were first reported in 1992 (Duke Power Company 1993, 1994, 1995,1996,
1997, 199 1999).
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
hytoplankton species, this was also true in 1999. Ten classes comprising 76 genera and 135
species, varieties, and forms ofphytoplankton were identified in samples collected during the
year, as compared to 86 genera and 168 lower taxa identified in 1998 (Table 3-6), The 1999
total was the fifth highest number of individual taxa recorded since monitoring began in
1987,`Five taxa Previously unrecorded during the Maintenance Monitoring program were
identified during 1999.
Species Composition and Seasonal Succession
The phytoplankton community to Lake Norman varies both seasonally and spatially within
the reservoir. In addition., considerable variation may also be observed between years for the
same months sampled.
Cryptophytes (Cryptophyceae) dominated densities at all but Location 15.9 in February
1999 and were also the most abundant forms at all locations in May 1999 (;Figures 3-4'
through 3-7). Diatoms (primarily small I elosira sty.) were dominant at Location 15,9 in
February. During most previous years, cryptophyt s, and occasionally diatoms„ dominated
February phytoplankton samples in Lake Norman. Diatoms have typically been the
predominant forms in May samples of previous years. However, cr ptoph tcs dominated
May samples in 1988, and were co -dominants with diatoms in May 1990, and from May,
periods of 1992 through 1994 (Luke power Company 1989, 1990, 1991, 1992, 1993, 1994,;
1995, 1996, 1997, 1998, 1999). The most abundant crypophyte was the small flagellate,.
R otio onars minumi. This species has been one of the most common and abundant forms
observed in February samples since monitoring began in 1987. Cryptophytes are
characterized as light limited, and often found deeper to the water column, or near surface
under low light conditions, which are common during winter (Lee` 1989. In addition, this
36

taxon"s small size and high surface -to -volume ratio would allow for more efficient nutrient
uptake during periods of limited nutrient availability (Harris 197).
During August 1999, diatoms dominated densities at all but Location 5.0, where green algae
(C'hlorophyceae) were most abundant. The most abundant diatom in August was the small
pennate, Anc tnoeonei.s vitrea. This was unusual since it represented the first time diatoms
had ever dominated most summer samples. During all past August periods of the Fake
Norman study, green algae, with blue-green algae (Myxophyceae) as occasional dominants
or co -dominants, were the primary constituents of'surnmer phytoplankton assemblages. This
pattern of diatom dominace in August was lake -wide, and not associated specifically with
locations in the vicinity ofMNS or Marshall Steam Station (MSS).
A. vitrea, has been described as ubiquitous, and found under a wide range of ecological
conditions (Patrick and Riemer 1966). A. 1,11rea has also been found in abundance in low to
circumneutral pH water of low conductivity (Lowe 1974, Round, et al. 1990). Arcane}orreis
spp, were listed in a trophic index as having a tolerance for moderate to high nutrient
concentrations (Kelly 199). This diatom was found in phytoplanton samples during six
previous years of the Lake Norman Maintenance Monitoring Study, but was never observed
in great abundance. In other Lake Norman studies, A. vitrea was not observed from
phyroplankton samples, but had always been a common and abundant form among artificial -
substrate periphyton samples collected in Lake Norman between 1974 and 1984 (Rodriguez
1982, Duke Power Company 1985). It was also described as one of the most abundant
periphytic diatoms on natural substrates (near -shore bottom sediments) in Lake Dorman
(Derwort 1982). Its high densities among summer p ytopl nkton assemblages cannot be
readily explained. Basel on past reports, the mean lake:-widesecchi depth during; 1999 was
the highest since 1992, when measurements were first reported. A. vitrecf has been
characterized as an epipellic form (living in and on sediments). Therefore, if water levels
were low for an extended period, and nutrient inputs were lower than normal due to low
rainfall, deep light penetration may have triggered a response that caused these diatoms to
migrate into the water column as a result of nutrient depletion in the: sediments. In addition,
there were periods of high winds reported during August. Subsequent wave action could
have dislodged mats or clumps of these diatoms. Another theory is that macrophyte control
procedures up -river (in Lookout Shoals) could have introduced large numbers of A. vitrea
into and throughout Lake Norman. Weed control treatments were done in Lookout Shoals on
1 - 0 August 1999 (sampling was conducted on 25 August). A. vitrea has also been reported
as epiphytic (attached to plants) on a variety of aquatic macrophyte (Schram 2000, unpubl.).
7

0
Whatever the cause, the phenomenon was lake -wide, and not localized near MNS or MSS.
Therefore, it was most likely due to a combination of unusual environmental factors, and not
station operations.
Luring November 1999, densities at all locations were dominated by diatoms, as has been the
case in most previous years of this study. The large centrate diatom, Melosira arr bigua, was
the most abundant diatom at lower lake locations (2.0 through 9.5), While the per ate,
Tabellarru ferre.srrata, dominated diatom assemblages at Locations 11.0 and 15.9. Both of
these diatoms have been described as common and abundant among Lake Norman
phytoplankton in past years of the study.
Blue-green algae (Myxophyceae), Which are often implicated in nuisance blooms, were never
abundant in 1999 samples, and their overall contribution to phytoplankton densities was
lower than in 1998. Densities of blue greens seldom exceeded 3% of totals. The highest
percent composition of Myxophyceae< (3.3%) during all sampling periods in 1999 occurred at
Location 15.9. 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). In 1949,
Nygaard (1949) proposed a series of indexes based on the number of species in certain
taxonomic categories (Divisions, Classes, and Orders). The M xoph cean index Was
selected to help determine long-term changes in the trophic statics of Lake Norman. This
index is a ratio of the number of blue greets algal taxa to desmid taxa, and was designed to
reflect the "potentials' tro hic status as opposed to chlorophyll, which gives an estimate of
instantaneous phytoplankton biomass. The index was calculated can an annual basis for the
entire lake, for each sampling period of 1999, and for each location during 1999 (Figure 3-8).
For the most part, the long term annual Myxophycean index values confirmed that Lake
Norman has been in the oligo- lesotrophic (low to intermediate) range since 198 (Figure 3a
8). 'Values were in the high or cutro hic range in 1989, 1990,and 1992, in the intermediate
or mesotrophic range in 1991, 1993, 1994, 1996, and 1998, and in the low or oligotrophic
range in 1988, 1995, and 1997 The index for 199 was lower than that of 1998 and fell in
the low ranged
3-8

The highest index value among sample periods in 1999 was observed in November, and the
lowest index value occurred in May. This tended to reflect record -low chlorophyll
concentrations observed throughout the lake during May 1999. The index values for
locations during 1999 showed comparatively low values at Locations 2.0 through 9.5, with
the value at Location 15.9 in the intermediate range. Last year, a clear pattern of increasing
trophic state front down -lake to up -lake locations was observed (Duke Power Company
1999).
FUTURE STUDIES
No changes are planned for the phytoplankton portion of the Lake Norman Maintenance
Monitoring program during 2000.
SUMMARY
In 1999 lake -wide mean chlorophyll a concentrations aduring February and May were the
lowest observed for these periods since the program began. During May, record low
chlorophyll concentrations were observed at all locations. Lake -wide mean chlorophyll
concentrations in August and November were within ranges previously reported for these
months. Record low chlorophyll concentrations in February and May could have been due to
very low rainfall totals recorded during the fall of 1998 and the winter of 1999, Lake
Norman continues to be classified as oligo-mesotrophic based on annual mean chlorophyll
concentrations. Lake -wide chlorophyll means declined from February to May, increased to
the lake -wide maximum in August, then declined in November. This seasonal pattern has
never been recorded during the Maintenance Monitoring Study. Considerable spatial
variability was observed in 1999, However, maximum chlorophyll concentrations were most
often observed tip -lake, while comparatively low chlorophyll concentrations were recorded
from Mixing Zone locations. The 1999 maximum chlorophyll value of 14.42 ug/I was well
below the NC State Water Quality standard of 40 ug/l.
In many cases, total phyroplankton densities and biovolumes observed in 1999 were lower
than those observed during 1998, especially in February and May when they were lower than
normal. During August and November, standing crops were within ranges established over
previous years. The maximum density and biovolume recorded during 1999 were well below
3-9

NC guidelines for algae blooms. As in past years, high standing crops were usually observed
at up -lake locations, while low values were noted down -lake.
Seston dry weights were generally lower in 1999 than in 1998, and down -lake to up -lake
differences, while still apparent, were less dramatic than in some previous years. Maximum
dry and ash -free dry weights were most often observed at the riverine location (69.0), while
minima were most often noted at Locations 2.0 and 9.5. The ratios of ash -free dry weights to
dry weights in 1999 were slightly higher than those of 1998, indicating little change in
organic/inorganic-inputs into Lake Norman,
Secchi depths reflected suspended solids, with shallow depths related to high dry weights.
The lake -wide mean sechhi depth in 1999 was the deepest recorded since measurements were
first reported in 1992.
Diversity, or numbers of taxa, of phytoplankton had decreased since 1998, but the overall
number of individual taxa was still high compared to most previous years. The taxonomic
composition of phytoplankton communities during February, May, and November were
similar to those of previous years. Cryptophytes were dominant at most locations in
February and May, while diatoms were the principal contributors in November. A
significant shift in community composition was observed in August 1999 when diatoms,
primarily the periphytic form Anomoeonies vitrea, dominated phytoplankton assemblages at
most locations. During most previous August periods, green algae (and occasionally blue-
green algae) dominated the phytoplankton. This shift was likely the result of a variety of
unusual environmental factors, and not related to station operations. Blue-green algae were
less a4indant during 1999 than 1998, and their contribution to total standing crops seldom
exceeded 3%.
The most abundant alga, on an annual basis, was the cryptophyte Rhoclonionas initnact.
Common and abundant diatoms were Anomoeneis vilrea during August, and 1VIelosira
ambigua and Tabellaria fenestrala in November. All of these taxa, except A. vitrea, have
been common and abundant throughout the Maintenance Monitoring Program. A, vitrea was
found to be a major contributor to periphyton communities on natural substrates during
studies conducted from 1974 through 1977.
The phytopkankton index (Myxophycean) tended to confirm the characterization of Lake
Norman as oligo-i-nesotrophic. Quarterly index values were in the low -intermediate range,
3-10

and tended to reflect seasonal changes in phytoplankton standing crops, whale most location
values were in the low range;
Lake Norman continues to support highly, variable and diverse phytoplankton communities:
No obvious short term or long term impacts of station operations were observed.
LITERATURE URE CITED
Derwort, J. E. 1982. Periphyton, p 279-314. In J. E. Hogan and W. D. Adair (ed.). Lake
Norman Summary, vol. 11. Duke power Company, Technical hnical Report DUKE
PWR/82-02. Duke Power Company, Production Support Department, Production
Environmental services, Huntersville, NC.
Duke Power Company. 1976. McGuire Nuclear Station, Units I and 2, Environ-
mental Report, Operating License Stage. 6th rev. Volume 2. Duke Power
Company, Charlotte, NC.
Duke Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration.
Duke Power Company, Charlotte, N.C.
Duke Power Company. 1988 Lake Norman Maintenance monitoring program: 1987
Summary. Duke Power Company, pany, Charlotte, NC.
Duke Power Company. 1989. Fake Norman Maintenance monitoring program: 1988
Summary. Duke Power Company, Charlotte, NC'.
Duke Power Company. 1999. Lake Norman Maintenance monitoring program: 198
Summary, Duke Power Company, Charlotte, NC.
Duke: Power Company. 1991, Lake 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, Fake Norman Maintenance monitoring program; 1992
Summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1994. Lake Norman Maintenance: monitoring program. 1993
Summary. Drake Power Company, Charlotte, NC.
Duke Power Company, 1995. Lake Norman maintenance monitoring program:
1994 summary. Duke Power Company, Charlotte, NC,
3-11

Duke Power Company. 1996. Lake Norman maintenance monitoring program.
1995 summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1997. Lake Norman maintenance monitoring program:
1996 summary. Duke Dower Company, Charlotte, NC.
.Duke Power Company. "1998. Lake Norman maintenance monitoring program:
197 summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1999. Lake Norman maintenance monitoring program:
1998 summary. Duke Power Company, Charlotte, NC.
Harris, Cl. P. 1978. Photosynthesis, productivity and growth: the physiological ecology of
phytoplankton. Arch. Hydrobiol. Beih. Er eb. Limnol. l 0; 1-171.
Hutchinson, G. E. 1967. A Treatise can Limnology, Vol, 11. Introduction to the
limonplarjkton. John Wiley and Sons, New York, NY
Kelly, M. G. 1998. Use of the Trophic Diatom Index to Monitor Eutrophication in Rivers.
Wat. Res. Vol. 32, pp 236-241
Lee, R. E. ' 1989. Phy ology (2"d. Ed.). Cambridge University Press. 40 Nest 201n. St.,
New York, NY.
Lowe, R. L. 1974, Environmental requirements and pollution tolerance of freshwater
diatoms. United States Environmental Protection Agency, Cincinnati, Ohio.
Water Quality Criteria, '1972. A report of the Committee on Water Quality. Criteria,
Environmental Studies Board; Nat. Acad. Sci.,1 Nit Acad. Engineer,, Washington:,
DC
Menhinick, E. F. and L. D. Jensen. 1974. Plankton populations; p. 120-138 In
L. 1 . Jensen (ed.). Environmental responses to thermal discharges from Marshall
Steam Station, Lake Norman, NC. Electric Power Research Institute, Coaling Water
Discharge Project (RP-9) Report No. 11. ,Johns Hopkins Univ., Baltimore MD.'
North Carolina Department of Environment, Health and Natural Resources, Division of
Environmental Management DEM), Water Quality Section. 1991; 1990 Algal Bloom
Report.
Nygaard, G. 1949. Hydrological studies of some Danish pond and lakes 11. K. danske
Vilensk. Selsk, Biol. Skr.
Patrick, R. and C. W. Reimer. 966. The diatoms of the United States, Vol 11, Part 1.
Acad, Nat, Sci, Philadelphia, Monograph 13.213 pp.
3-1

Rodriguez,-M. S. 1982, Phytoplankton, p. 154-260 In J. E. Hogan and W, D. Adair (eds.).
Lake Norman summary. Technical Report DUKEP RJ 2-02 Duke Power Company
Charlotte, NC.
Round, F. E., R. M. Crawford, and D. G. Mann. 1990. The Diatoms. Cambridge University
Press, New York, NY,
Schr nz, C. 2000e Epiphytische Diato en auf Phra rnit s australis (Cay.) Trin. Ex Steudel
uas Seen untersehiedlicher Trophie. (unpubl.). http://w-"rw,limno.biologie.tu-
muenchen.de/Forscung_und-LehrelZus_C<'.htn�
Thornton, I . ., B. L. Kimmel, F. E. Payne. 199 . Reservoir Linmology. John Wiley and
Sons, Inc. N. Y.
3-13

90 U"
00
ITI
Ln
t1i
00 UJ
CA
00
Z cn
z
4-
4-- t-J 00 4- t-A
00 --j of Cw Ic
U4 (.A Lh

Table 3-2.
Duncan's multiple Mange Test can chlorophyll a concentrations to Lame
Norman, NC, during 1999.
February
Location
2.0
9.5
8.0
11.05.0
13.0
15.9
69.
Mean
110
2.14
2.20
2.30
141
2.44
3.17
3.36
May
Location
2.0
69.0
95
5.0
13.0
8.0
11.0
15.
Mean
1.21
1.7
1.56
1.64
1.71
1.91
2.08
2.71
August
Location
13.0
5.0
2.0
11.0
8.0
15.9
9.5 '
69.
Mean
3.58
7.16
7.63
825
9.89
10,68
12.01
14.42
November
Location
2.0
5.0
69.0
9.5
8.0
11.0
13.0
15. `
Mean
2,58
2.71
2.87
3.42
3.74
3.92
, 6.02
6.93
-1

aa
r- qr T—
C43 t -
00 It
It C14
as
V-
T-
---
u�a
rra
c0 V*
cs
oi
ca
to
*`
!
cv
N c
a
�-
"'t
't
ev tom-
t
co
0

Table 3-4.
Duncan°s multiple Range Test on phytoplankton densities In Lake Norlxlan,
NC, during 1999.
February'
Location
11.0
9.5
5.0
15.9
2.
Mean
530
681
901
1064
1=110
May
Location
2.0
9.5
5.0
11.0 ,
15.9
Mean
955
976
1018
1932
2242
August
Location
11.0
5.0
2.0
15.9
9.5
Mean
210
3356
342
5060
6495
November
Location
2.0
5.0
9.5
11.0
15.9
Mean
1161
1558
2061
2269
397
3-1

Table 3-5.
;Duncan"s multiple Range Test on dry and ash -free dry weights (nig/1)
in
Lake Norman,
NC during 1999.
DRY WEIGHT
February
Location
11.0
5.0
8.0
2.0
13.0
15.9
9.5
69.0
Mean:
U8
0.67
0.74
0.95
1.21
1.23
1.47
4.79
May
Location
9.5
2.0
5.0
11.0
69.0
8.0
13.0
15.9
Mead,
0,55
0.58
0.65
' 0.65 `
0.73
U7
1,00
1.66
August
Location
2.0
5.0
15.9
9.5
11.
13.0
6.
Mean
109
1.78
1.81
1.82
2.18
2.19
2.49
24,23
November
Location
9.5
2.0
11.0
8.0
5.0
15.9
13.0
69.
Mean
1. 3
1 A7
1 84
1.93
2.01
2 52
3:04
5.06
ASH FREE
DRYS WEIGHT
February
Location
8.0
11.0
5.0
13.0
15.9
9.5
2.0
69.0
Mean
0.46
U l
0.67
0.69
0.75
037
O.94
L59
May
Location
9.5
2.0
5.0
11.0
69.0
8.0
13.0
15.9
Mean
0.55
U8
0.65
0.65'
0.72
0,87
1.00
1,28
August
Location
2.0
5.0
9.5
8.0
13
1 .9
11.0
69.
Mean
0.85
1:02
1.16
1.33
L56
164
131
14A
November
Location
8.0
9.511.0
2.0
5
13.0
15.9
69.0
Mean
1.30
0.68
0.79
0. 2
1.23
1.48
151
1
.53
3-1

Table 3 )-6. Phytoplankton taxa identified in quarterly samples collected in Lake Norman
0 from August 1987 to November 1999.
0
w
TAXON
87
8
4
7-1
3
IT
95
77677M78--9—o
CLASS, CHLOROPHYCEAE
A canthospaera Zcichariasi Lermn
x
x
x
clidesmium hookeri Reinsch
x
Actinastrion hantichii Laaerheim
-X1-x
-YT
-x
Ankistro4lesnws braunii (Naeg) Brunn
I
x
x
x
x
x
A, falcatus (Corda) Ralfs
X
X
-x
x
x
I x
A,fiusaforntis Corda sense Korsch.
x
x
x
x
x
x
A. spiralis (Turner) Lemm.
Jx
x
x
x
x
x
Aspp, Corda
x
x
Arthrodesinus convetgens Ehrenberg
x
A. ineus (Breb.) Hassall
x
x
X-
x
A, subulatits Kutzin-
x
x
x
A. spp, Ehrenberg
x
x
AsIvrococcus limneticus G. M, Smith
x
J
7
x
x
Boltyococcus braunii Kutzing
x
x
Carteriaftr:schii,rakeda
x
C spp. Diesing
x
x
x
x
Characium spp. Braun
x
Chlamydomonas spp. Ehrenberg
R,
x
x
x
x
x
21�
x
Chlore&7 vulgaris Beyerink
x
Chlorogonium euchlorian Ehrenberg
x
C. —Spirale Scherffel & Pascher
x
Closteriopsis longissima West & West
x
x
x
X
—x
x
x
x
x
Clostet-hint cornit EhrenbemT
x
C gracile Brebisson
x
C incia-vum Brebisson
x
x
-x
C spp. Nitzsch
x
x
x,
5z
Cocconiontis orbicularis Stein
x
Coelastrunicambricuin Archer
—,x
—x
x
C. inkropm-um Nageli
x
x
x
Ix
reticulatum (Dang.) Sinn.
x
Csphuericutn Nageli
x
x
x
x
C. proboschlewn Bohlin
x
C spp. Nageli
x
x
Costnarhan anulosuni v. concinnum (Rab) W&T—
X
* asphaerosporum v. strigosum Nord.
x
-4-
x
x
x
x
x
x
x
x
x
x
x
x
C. contractum Kirchner
x
C'. pokornycinum (Grun.) W. & G.S. West
x
C polygonum (Nag.) Archer
x
tjx
:sj
X
x
�
x
Ix

Am Table 3 )-6 (continued) page 2 of 9
* phaseolus f. minor Boldt.
* regnellii Wille
C.regnesi Schmidle
C. tenue Archer
C. rinctum Ralfs
C tinctures v. tumidum Bore.
X
—0-
7-0
1 —1
x
7-21
x
-7, --
x
x
1-4
X—
=)5
x
7-6
x
i#xx
-7-7
x
x
x
7 n-
x
x
x
­w
x
x
C. spp. Corda
X1
Crucigenia crucifera (Wolle) Collins
X
X
x
x
x
x
x
x
Xx
(',fienestrala Schmidle
C. irregularis Wille
x
x
C. rectangularis (A. Braun) Gay
x
* letrapedia (Kirsh.) West & West
—X—x
-x
-x
-x
x
-x
Dictyospaerhan ehrenbergianum Nageli
D. pulchellum Wood
x
x
x
Ditnorphococcus spp. Braun
Elakatothrix gelatinosa Wille
T
7T
-T
x
x
x
x
-x
x
Euastrum denticulatum (Kirsh.) Gay
x
i
X
x
x
E. spp. Ehrenberg
x
T
Eudorina elegivis Ehrenbe—rg
x
Franceia droescheri (Lemur,) G. M. Smith
X
x
x
x
x
F. ovalis (France) Lemur.
x
X.-----
Gloeocystis botryoides (Kurz,) Nageli
-x
Cr. giAgas Kutzing
x
x
x
G. major Gerneck ex, Lemmermann
x
G, planktonica (West & West) Lemm.
x
x
x
x
x,
X
X
s
X
x
7-, ­l—'esciculosa Naegeli
x
G. spp. Naggeli
x
x
x
x
x
x
x
X—
Golenkinict paucispina West & West
G. radiala Chodat
-Ix
x
x
Z
K
-K
R
K
Goniumpectorale Mueller
Cr". sociale (Dqj.) Warming
x
x
x
—T7Tchracrac? coniorta (Schnnidle) Bohlin
x
x
X
X
X
x
K. hinaris (Kirsh.) Mobius
x
T--x
#X#
K, lunaris v. dkinae Bohlin
x
K, obesa W, West
x
x
—X—
X
-T
-T
-T
K. subsolituria G. S. West
X
X-T
-x
x
K spp. Schmidle
x
x
T
x
x
Lagerheinfia ciflata (Lag.) Chodat
x
L. citriformis (Snow) G. M, Smith
x
L. longisela (Lernmennarm) Print
L. quadriseta (Leman.} G. M. Smith
x
x
x
" vex
3-20

Table 3-6 (continued)
Page 3 of
lei
9
(ttl
91
92
93
94
95
96
97
uh,sala Lernmerman
xx
x).s
tigma viride Latlterborne
kAles1li"e?(actintunm
pusillum l"resen,
lA
11
o
9
k
1k
r�
Atonora rhillium c•omortum Thuret
x
x
x`
x
Af pusillum Print
r
x
x
qq,rr
Iota g itia elegantula Whittrocic
x
Af Sp a. A g rdh
Nephrocytium agat,41hianum Naigeli
NN, lirnneticum (G.M. Smith) G.M. Smith
Oocyvi'.s Inc>rglr Snow
0. eltvptica W. West
0, lacti.stris Chodat
0. pativ West & West
x
x
x
x
x
x
x
x
x
0. pusilla L ansgirg
0, jayrtfornis Prescott
Pandorina charkowiensis Kprshikov
;,
P. morum Rory
x
f ediastrum bi'radiatam Meyen
P, duplex Meyen
e
P, duplex v.'gracillirnum West and West
P. tetras v. tetroadon (Corda) Rab nhorst
`<
P, sp. Meyen
£ hinhlosph aer•ia , elatinosa G. M, Smith
Qu adris uhi closterioidcs (F ohlin) Print
Q. laacirstris (Chodat) G, M Smith
Scci edesmus abun 'ans (Kirchner) Chodat
S. abunclans v. asynetrica (Schr,) G, Sm,
X
}
,
S, albiindans v, brevicumb G. M. Smith
x
S. actaninatacs (Lagerheim)'Chociat
S. armatus v. bicautfatris (Guw.-Prin,)Chocl
,
S. bi uga (Tarp.) Lawgerheinax
x
x
x
x
x
x
x
x
"
S. 17tftii;Ca v. LiltE;rYdYi.4' (l*einsch) Hansg.
x
S. brasilicnsis 1 ohlin
x
x
S", Caentic ulatus Lagerheaas
x
T
x
S. climornhus (Turp.) K tzing
S. incrassulattrs G. M. Smith
S. quactricauda (Tarp.) E rebisson
S. smithn Teilin
S. spp. Meyer
x
x
Schi ochlarnys compacta Prescott
3— 1

Fable 3-6 (continued)
page 4 of 9
87
88
89
go
91
75-2719­94
7T
56
7
7k
9
icr;S'Ii Frei (sliri cl.) I eTltTi.
5
um gracile Reins h
x
in (Nageld) Collins
N,S�.'westfl
x
x
x
M. Sm tli
'
u�rr(rerr`C1eyr5ryi�zr/m (B li>ylyttn) Schmzdl
'
L $aJdda.#.�4MR&,kS.IE•1& i..48R4 4.
�p
th
CA.
Sphcaerozosnrcagran arlcrttrrn Roy & BIiss
x
Stczzravtruin rameric antrrn (—W& ) G.
S. capic ulcatum T rebtsson
S. brcachialum Ralfs
x
x
S. brevispinum Brcbtsscsn
x
S. c caetcdcer°teas (Schoed.) G. M. Smith
S°, curvation W. '4sr'est
x
S. c u phicdtum Brebtsson
e
S c1qjectzarPt'Brebis on
x
x
:r
x
x
S. dicken v, wtvinnon West & West
S. glcaclrtrsum Turner
S. leptcrciczdunt v, sinuatunt Wolle
x
S, manfltltza v.flunatnense Schumacher
i{
S. me rcr anthum Lundell
s
S. carlttculcare Ralfs
aS. pcarcacltrxum Meyen
xx
x
r1.
x
x
x
x
S. pctr°Cat oxian v, cYr 4,?2 him West & West
y
S. paraado.rum v. pxt-wim W. West
S. subcwrucialunt Cook & Wille
S, tcetr=cacetwin Ralis
xi
x
-,
_
S, tur escens de Not,
'
S. spp, Meyen
Tetr< e d'ron bifurctltterrr v, minor Prescott
x
T. caud atum (Gorda) Hans; tr4.?
,'
"
T, linineticttnt Borf;e
1 lobulaatunt v. crcassunt Prescott
:4�
�S
r
T: mitinnerrt (Braun) ! tans�girg,
�i
�i
x
x
p muticum (Braun) Hansairg
T. cdliesum (W & W,) Wille ew Brunnthaler:
T plcanktonicum G. M. Smith
;
p pentcaeclricum West & West
x
T: i-eg cicare Kut in
T. regulcare_v. irifur°ccatum Wille
T: regultire v. incus T'etltng
xS�
T traaararrr (Nac h) Hansdrl;
3_2

Yabl -6 (continued)
�
page of
87
g �
fly
90
91
92
9 7
4
99S
cj
c)7
9
_ 99
T tl"t°�'onzim v. gracile (Reim+") DeToni
T spp. Kutzing
Tetrospora spp. Link
r*
x
Tetrastrian %etc>rractint u (Nordst.) hod
Trzuboriii setigerum (Archer) G. M. Smith
'
C
Westellci bot roicles (West : West) Wilde.
PV, liiiwris• G. M. Smith
Xanthiclium spp. Ehrenberg
�S. BACIC.�L✓f iliA l�C i$�t l.. A...�L
LAchnnuithes
micTroc ephcila Ut to<r
A, spp. Bury
x
x
x
x
Anomoeon is vitreu (Grunow) Ross
A, spp. Pfitzer
Jst rrcxrar>ll .jbrrr osa H ssall
S
C
5
Atthczi°cr zachariasi J. Brun
1
occc, neis plac enti&7 Ehrenberg
x
x
C'. spp. Ehrenberw
Ctrclotelhi eointci (Ehrenberg) Kutzing
* glomerata Bachmann
x
x
x
x
C. rri neghiniana Kutzing
x
x
x
x
C. laseudostclligera Hustedt
C. stedligcra Cleve & Grunow
x
Ix
x
x
x
x
x
x
x
h
C. spp. Kutzing
C y iarc llca firaiairtcr (Biiesch & Itabri.) fteiiri.
', rumicici (Bret.) van Fluerck
x`
C. ti rgscici (Gregory) Cleve`
C", spp, Agardh
Denticula therinalis Kuetzing
Diploneis spp. Ehrenberg
t.un thi:asulnirte sis (Cab,) Koerner
x
xx
x
xT
x'
x
1'rcigiltai ki crotonensiS Kitton
x
x
1
Y1
1'rustulia rh(3tT7bohles (Ehr.) deToni
i
Goniphf.7t"PGina spp. Agardlt
'
Atelosirir canthiguu (Gran.) Q. Muller
Af. clistcans (Ehr.) Kutzing
i
{
(Ehr.) ali`
x
v. ungrrrtisst'rrici C}. Muller
r.) Kutzing
PIspR.R
s
13
Al,g rdh.
Agardh
x
-23

Table 3-6 (continued)
®page
of 9
.._
7
�.:
IF
9
I
92
9 s
9
95
96
7
98
99 e
Alt7vte rrlcr c tj ptr', cephcrlcr Kutzincy
N. exi rtcr (Gregory) 0. Muller
x
N. e;xigua v. ccrpitcrlct Patrick
tV subtilissinut Cleve
N. spp, Bory
x
x
x
X
,
Nit :S hicl twiculor°is W. Smith
N. agnitet H rstedt
i
,�;
r1
r
t1
�r
ra
N, holsatiC'a Huste t
t
�y
)
x
fix,*
x
N. rrlt-w (Kutzing) W, Smith
N. ssubline?cir is E lustedt
S
1
N. spp, EEnssall
;
1'rrzr ular ki -spp, Ehrenberg
;
Rhizosolentcr spp, Ehrenberg
x
x
x
.`
x
Skeletone rrrcx p tc>mos (Weber) Elrlse
Sta;phanodi.scus spp. Ehrenberg
Surirellcr linear°is v. constrryicrto (Ehr.) Grun,
: ync'clw trctinastroide's Lernnierman
SG7eus Kutzin-
K7
1
x
1
S. defic rtissirnu Lewis
S. frliiforrrris v. e ilt's Cleve-E.uler
AS. plcinktoniccr Ehrenberg
?
x
S. rumpens Kutzing
x
x
x
x
S. rumpens v. frt7gilw-ioides Grunocv
f, ruinpens v. scotica Grunow
'
S. rtltta (Islrt sch) Ehrenberg
x
x
S. spp. Ehrenberg
"K
T
1x
T'ab lleirdci ft-n strata (lamyngb) Kutzing
x
x
x
r
x
x
x
fltrCc uloscr (Roth,) K tzin ?
S
5
CIsASS. CEI YSOPHYCEwEAE
S'IC'f7ccapetiolutrtm (Stien)Prtngshern7
max`'
:.
C alciccrrr onas perscheri (Van Boor) Lund
C hrorrartlina spp, Chien.
C.'larysosphaer"e*llcr solitarict Lawerb.
x <
x
X,x
CL)Clt7rvronus CXrlr uhito Lacked'
xx
Dinohr~ on havwricum Imhof
x
x
x
x
x
x
x
x
x
x
x
x
D. c°yftndric°um Inihol
A divergens Imhof
x
A ser"iidarici Ehrenberg:U
L7. spp. Ehrenberg
?C

Table 3- (continued)
page i cif
7
8
99
90
9I
9'
9
94t
95
96
97
9
99
L?crm atc>rnococ'eus eylinclricum Lackey
x
Erkinica subezerluieilliata Skuja
%eplavrtvn ltttorcale Lund
. r ubi-claustri Conrad
K. ska�ae Ertl
K. spp. Pascher
x
, allonaaanas aearoicles Perry
hfl, akrarkcarnras (Naumann) krXeer'
AI alpina Pascher
x,
R c°auciata C onrad
x
x
M. globos'ca Schiller
tll. pserac ocoroncata Prescott
x
x
x
X
Al.. tonsurczta Teiling
_
Af. spp. Perry
x
x
Oc• ronrcrnas granularis Doflein
x
;
0, spp. Wyss
pseudokepkvrion schiller"i Conrad
A tintinabulrtrn Conrad
x
Rhizoehrisis polyinorpha Naumann
x
R. SI}p. Pascher
x
x
Salpingoecaftequentissima (Zachary) Lerr m.
Stelexomonas clichotonra Lackey
Stokesiella epipywis Pascher
rrc"'a korschikov°
hrenbergenberg
ff-P
x
x
xsis
americcana (Caulk.) Lemrn.
X
x
CLASS: HAPTOPHYC'EAE
C'hij,sochroinulina parva Lackey
x
x
x
x
x
x
x
x
CLASS: XANTLIOPHYCEAE
C"lacdrexc ila'rs crrrhlea Iascherx
x
x
Dichott?rnG7coccus curiwei Korschikov
()phivcytharr c°aoitcrtum v. l anl;isp. (M) Lem
x
x
CLASS: CR: PTOPHYCEAE
Cryptomonas eresa Ehrenberg
X
C. erc sa v. reflexa Marsson
C. mar scami Skuja
C. ovala Ehrenberg,
-`? ,

Table 3)-6 (continued)
-.
page 8 of 9
'. llrcxsec�lac;s Sl uj
xxx
C". r°Hera Sluja
X
X
C". spp. Ehrenberg
x
X
h'lacrrlrarr oncr�s rrrinuta Sku a
r
i
�i
CLAMS: MYXOPi-i k:AE
A,gnzenellwn qu acLriclrrpliccztauin BrebPsson
x
x
x
x
x
X
X
An ab aena czaterttalca (Kutzing) Born.
A, wheremetievi Elenl:Pn
X
X
,4, wi'sconsitrc?nsw Prescott
i
4
A, spp. Bory
,
Arrcr . stis incerta (Letrun) Cruet & Daily
A. spp. Men MhPnP
X
ChrE3t)€ o cus dispersus (Ketssl) l,emm.
X
C'. limn ticus Lernmermann
X
X
X
C'. minor Kutzing
C. turgicltrs (Kutz) Lemniermann
C. spp, Nag li
X;
X
Coelosphcieriza n kuet int ran a Nageli
L)ogvlococ co psis irr•e ulcar is Hans Pr
X
1). smithii Chodat and Choclat
Clomphospuer is lcacustris Choclat
x
x
X
I )'i?€*bya cantor to LenliYPennarm
x
L. linuietic a Lent erntann
x
x
x
x
x
x
L. suhtilis W. West
x
X
X ;
X
L, spp. Apron
x
x
x
X
T
x
'x
x
x
x
Xfel rlvngpecli a lenuissrrraca LePn Hermann
X
Microceyvtrs cwr a inosca Kutz. emend Elen.
i
x
X
x
x
x
X
x
X
Oscillwori gL'17?inata Meneghlni
xx
xx
0. llrninettctl LemmernPann
x
Ix
x
0, splendid Greville
X
X
X
0. spp. Vaucher
IT
X
Phor miclrum tarigrustissdrirron West & West
x
X
X
X
P. spp. Kutzing
x
x
x
eiphiclir�psis c'ift"1atu Fritsch & Rich
t�
�
�
�
R. mecliter°ranea Skuja
Rh alaticrclerm a srgrntl rclea S hrn, & L utrb.
ynec ococcus linear° (Sch. & Laut.) Korn,
�x
x
x
'.
x
X
X
CLASS. EUGLENOPIIYCEAE
Ettglena cacus Ehrenberg
X
X
-?

Table 3-6 (ontirrued)
page 9 of
7
88
89
90
91
92
93
94
95
96 µ97
98
9
E. minut a Prescott
x
E. po4,,morphca Dangearci
spp. Ehrenber<g
Lepocinchcs spp. P rty
Pheacus orhicularis Hubner
P. tortus (I. mm.) Skvortzow
4'
P. spp, Duj rdin
Trcachedo onaas cacranthosd<>m a (St k.) l }efl.
T hisdricdca (Perty) Stein
x
T pulche>rrim a Playfair
T volvcacin a Ehrenberg
T spp. Ehrenberg
CLASS: ASS: D11` C?f'H YC EA
Cercatium hirundin llca (CJFM) Schrank
`—x
x
x
x
ti
,'
Cilenocdinium hor ci (Lena i.) Schiller
{
G. k:1, rnocdinium Penard
G. pulustre (Lemur..) Schiller
G. penurcd bme (linde.) Schiller
G. cluadridens (Stein) Schiller
x
:?
G. spp, ( hrenber`w) Stein
Cdy°rrarrocdinnarra caeruginosum Stern
iymnCrdinium spp, (Stern) Kofcrrd c . Swezy
x
x
x
x
x
x
Peridinium acicaalij&ru),n L nimerinann
i
P. incons icuum Lentnrerntann
'
P. it?ft'1"ii?G'dt"um Playfnir"
R pusr"llum (Lenard) Lernmerntanrt
P. um oncatum Stein
x
x
x
P. 14'7,SL"CJr7tiir7C'a1.Sk I dtlt
i
K
sr
5 i
,r
Jz
P. spp. Ehrenberg
CLASS: Cl-ILCrl2C} ONADOPI'iYCEAF
t.r'otFy<?sac3mum tde'd7i't.'sseum Lauterborne
G, semen (E renber#�) I iSt Sl[l
G, spp. Diesing
x
x
.x
-2

CHLOROPHYLL a (ugd9) DENSITY (unit /mI)
16 ��.,
v....._ _..w._wr ..._.ate. 7000 .... ... ........... .....::.... .....: ..._.�
14
6000
1
5000
10
4000
..
3000
6
r
2000
4
1000 "
' 0 __:... .... ._,....
2.0
2.0 5,0 9.5 11.0 15.9
5.O 13.0 9.5 11.0 13.0 15.9 69.0
EE TON DRY WEIGHT (mg/1) EIOVOLla E (mm3lm3)
30
- _. �.�. _�. _._ � 4000
25
300
3000
20
_
i 2500
15
2000
q �(�yy
i0
? 100 Y
1000
5
i
Soo
2.0
5.0 60 9.5 11.0 130 15.9 69:0 2.0 5.0 9.5 11.0 15.9
LOCATIONS LOCATIONS
:N V
Figure
-L Phytoplankton chlorophyll a, densities, and blovolum s, and sexton weights
at locations in Lake l orrnan, NC, in February, May, August, and November
1999.
3-2

14
12
10
8
0
X
4
2
ggi
0
FEB
MAY AUG NOV
MONTH
--*--1987 --w-1988 1989 --,X- 1990 199 1
--41�-1992 ---j-1993 ---6-1994 --j4-1995 -.o-1996
-1991998 1999
Figure 3-2.
Phytoplankton chlorophyll a annual lake means from all locations in Lake
Norman, NC, for each quarter since August 1987.
3-29

CHLOROPHYLL a {ri ll}
FEBRU ARY MAY
12 12 ,.'MIXNG 2CNS
10 MIXfNG ZONE10
2
87 88 89 90 91 92 93 94 95 "96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98 99'
8,0 9.5 8,0 9,5
20 . _ 12
10
1
8
10 6
4 ;
5 2
0 :w _ W._ _. _. w _ t
87 88 89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98 99
III O 1 .9 11,0 110
14 25
12
10 20
g 15
6 10
4 5
2
a
87 88 89 90 91 92 93 94 95 96 97 98 99 87 °88 89 90 91 92 93 94 95 96 97 98 99
15.9 69,0 15.9 63.0
1 N,., :.. �..... 30 �. ....... ...... .w .
14 25
12 ..,. w.
SO 20
8 1
6 10
4
2 5
_. p _.
87 88 89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98 99
YEARSYEARS
Figure 3-3. Phyt lan tun chlorophyll a concentrations by location for samples collected
in .aloe Norman, NC„ from August 1987 through November 1999.
-3

CHLOROPHYLL a (ug/i)

LOC. ZO & 5.0 _
'000
6500
_..
IgCHRYSOPHYCEAE
M CRYPTOPHYCEAE
6000
IM MYXOPHYCEAED
I OP YC A
5500
OTHERS
5000
4500
._
s
4000 f
3500
`3000
2500
2000
1500
_.

7500
I , ' HYC EA
7000
gOTHERS
6500
6000
550
5000
v,
4500
4000
3500
00
250
2000
1500
1000
50
FEB N44Y
AUG V
4000
3500
�
300
2500
1
ZUUU
E
1500
i
1000
Cif?
z
FEB MAY
AUG NOV
Figure
3-1..
Class composition (mean density and iovolume) of phytoplankton from
euphotic zone samples collected at Location
9.5 inLake Norman, NC,
during 1999.
3-33

~a0
J CHL t R1PHYCEAE
SAC>6LLARIOPHY ;EAE
6500
s
C;H Y OPHYC EAE
® TOPHYC EA
O o
MMYXOPHYCEAE
M l INOPHYCA
5500
OTHERS
5000
y
4500
4000
_ {
3500
3000
2500
2000
i,
1500
1000
�
f
500.:.
_.
FEB
AUG wv
4000
.... .:..._
500
3000
2500
E"
w
2000
>
0
1500
��
1000
i
500
0
FEB MA Y
AUG NOV
Figure -1.
Class composition mean density and biuvolume) of phytoplankton from
euph tic zone samples collected at Location 11.0 in Lake No ian, NCB,
during 1999.
- +4

L . 15.9
7000 ] CHLOROPHYCEAE g BACILLARIOPHYCEAE
5500 gg CHRYSOPHYCEAE M CRYPTOPHYCEAE
sago OPHYC� N P IYC
OTN P
5500 r _ _. _....._ ._ ... _ _._ ..--- ..__.._........__.
5000
4500
4000
Z 3500
3000
2500
2000 f µ
1500
1tlt 0
500
t.._
FEBY AUGNOV
4000
3500
3000
2500
_.�.`
to 2000 w
1000
500
o L
FEB M61Y AUGNOV
Figure 1-1, glass composition (density and biovolunle) of phytoplankton from euphotic
cane samples collected at Location 15.9 in Labe Norman, TIC, during 1999,
.-3 5

0,50
O) 25
02 ur
2 5 9.5 11 15.9
LOCATIONS
Figure 3- . Myxophycean index values by year (top), each season in 1 (raid), and each
location in Lace Norn'ian NC, during 1999.
3-36

CHAPTER
ZOOPLANKTON
INTRODUCTION
The objectives of the Lake Norman Maintenance Monitoring Program for zooplanktonare to:
1. Describe and characterize quarterly patterns of zooplankton standing craps at
selected locations on Lake Norman, and
Compare and evaluate zooplankton data collected during this study (February,
May, August, and November 1999) with historical data collected during the
period 197-199.
Previous studies of Lake Norman zooplankton populations have demonstrated, a bimodal
seasonal distribution with highest -values generally occurring to the spring, and a less
pronounced fall peak.. Considerable spatial and year-to-year variability has been observed to
zooplankton abundance to Lake Norman (.Duke power Company 1976, 19 5; ffarnme 19 „
feninick and Jensen 1974).
METHODS AND MATERIALS
Duplicate 10 in to surface and bottom to surface net tows were taken at Locations 7.0, 5.0,
9. , 11.0, and 15.9 to Lake Norman (Chapter 2, Figure ` -1) on 4 February, 3 May, 25
August, and 12 November, 1999. (Note. due to loss of mooring buoys and high winds, 10 ni
to surface samples were not collected at Location 5.0 in August and November, and bottom
to surface net samples were not collected at Location 5.0 in May, August, and November,
and Location 15.9in November). For discussion purposes the 10 in to surface tow samples
are called e ilinmetic samples: and the bottom to surface net tow samples are called whole
column samples. Locations 2.0 and < .0 are defined as the Mixing gone and Locations 9.5,
11.0 and 15.9 are defined as Background Locations. Field and laboratory methods for
zooplankton standing crop analysis, were the same as those reported to 1lamme (1982),
'ooplankton standing crop data from 1999 were compared with corresponding; data from
quarterly monitoring begun to August 1987,
A one-way ANOVA was performed on eptl€mnetxc total zooplankton densities by quarter.
This was followed by a Duncan"s Multiple Range Test to determine which location means
were significantly different,
4-1

0 RESULTS AND DISCUSSION
Total Abundance
Lack of data from Location 5.0 in August and November 1999 make it impossible to
determine overall seasonal patternsat this location (epilimnetic samples were collected in
February and May, whole column samples were only collected in February): Epilimnetic
densities at this location were higher in May than in February.
During 1999, considerable seasonal variability was observed in epilimnetic samples. Total
zooplankton densities in epilimnetic samples at Location 2.0 were highest in August, while
maximum densities at Location 9.5 occurred in May. The highest epilimnetic densities at
Locations 11.0 and 15.9 occurred in November (Table 4-1, Figure 4-1). The lowest
epili netic densities at Location 2.0 occurred in November, while annual minimum densities
at Locations 9.5 and 11.0 were observed it August. The lowest mean epilimnetic density at
Location 15.9 occurred in February. Epilimnetic densities ranged from a low of 1 ,200/m') at
Location 9.5 in August, to a high of 401,400/m3 at Location 1.9 in November. In the whole
column samples (with the exceptions of Locations 5.0 and 15.9), maximum densities were
observed in November. Minimum densities were observed in February at Location 2. , and
in August at Locations 9.5 and 11.0. Whole column densities ranged from l ,400/m3 at
Location 11.0 in August, to 110,400/ 3 at Location 11.0 in November.
Historically, maximum epili netic zooplankton- densities at Lake "Norman locations have
most often been observed in May, with annual peaks observed in February about' 25% of the
time. Annual maxima have, only occasionally been recorded for August and November.
Total zooplankton densities were most often higher in epilimnetic samples than in whole
column samples during 1999, ;as has been the case in previous years (Duke Power Company
1999). This is related to the ability of zooplankton to orient vertically in the water column in
response to physical and chemical gradients and the distribution of food sources, primarily
phytoplanklon, which are generally most abundant in the euphotic zone (Hutchinson 1967).
Considerable spatial variability in epilimnetic zooplankton densities was observed during
each sampling period. The results of the Duncan's multiple range test revealed several
statistically significant differences duringeach season (Table 4-2). In February, the mean
density at Location 11.0 was significantly higher than at other locations, while the density at
.2

location 2.0 was significantly lower. During May the higher population densities at
Locations 11.0 and 15.9 were statistically different from Locations 2.0 through 9.5. During
August, the density at Location 9.5 was significantly lower than other locations. Location
15,9 had a significantly higher mean density than other locations in November. Mean
zooplankton densities in the Mixing Zone were lower than mean densities from Background
Locations during all but August, when Location 2.0 had a higher mean density than
Locations 9.5 and I 1,0: In most previous years of the Program, Background Locations had
higher mean densities than Mixing Zone locations (Duke Power Company 1988, 1989, 1990,
1991,1992,1993,1994,1995,1996,19971,1998,1999).
Historically, both seasonal and spatial variability among epilimnetic zooplankton densities
had been much higher among Background Locations than among Mixing Zone locations. The
uppermost location, 15.9, showed the greatest range of densities during 1999 (Table 4-1,
Figures 4-2 and 4-3). Apparently epifirmietic zooplankton communities are more greatly
influenced by environmental conditions at the uplake locations than at downlake locations.
Location 15.9 represents the transition zone between river and reservoir where populations
would be expected to fluctuate due to the dynamic nature of this region of Lake Norman. At
the locations nearest the dam (Locations 2.0 and 5.0), seasonal variations are dampened and
the overall production would be lower due to the relative stability of this area (Thormon, et
al. 1990). A similar trend was observed among phytoplankton communities (Chapter 3).
Epilinmetic zooplankton densities during May and August of 1999 were within the seasonal
ranges of those observed during previous years, The mean epilimnetic zooplankton density
at Location 2.0 in February was the lowest yet observed for February at this location. The
highest February densities recorded during the Program at Locations 5.0 and 9.5 occurred in
1995, and in 1996 at Locations 2.0 and 11.0 (Figure 4-2). The long-term February maximum
at Location 15.9 was observed in 1992, Long-term maximum densities for May occurred at
Location 2.0 in 1998, at Locations 5,0, and I LO in 1995. and at Locations 9.5 and 15.9 in
1988, Long-term August maxima occurred in 1988 at all but Location 15,9, which had its
highest August value in 1996 (Figure 4-3). November long-term maxima at Locations 2.0
through 9.5 occurred in 1988, and at Locations 11.0 and 15.9 in November 1999. Since
1990, the densities at Mixing Zone Locations in May, August, and November have not
fluctuated much between years, while year-to-year fluctuations in densities during February
have occasionally been quite substantial, particularly between 1991 and 1997. The
Background Locations continue to exhibit considerable year-to-year variability in all seasons
(Figures 4-2 and 4-3).
4-3

_
� .
�
�
~ ~'
.' .
. '
Community__Composition`_�-_
One hundred and eight zooplankton taxa have been identified since the Lake Norman
Maintenance Monitoring Program began in August 1987 (Table 4-3). Fifty-two taxa were
identified during 1999, as compared to fifty-nine taxa recorded during 1998 (Duke Power
Company 1999). Four taxa previously unreported during this Program were identified in
1999; however, three of these had been reported from Lake Norman in earlier studies
(Hamme 1982; Duke Power Company 1985). The one previously unreported taxon was the
Copepods were dominant most often during 1999 (Table 4-1, Figures 4-4 and 4-5). These
microcrustaceans were dominant at Location 15.9 in February, at all locations in May, at
Locations 9.5 and 15.9 (whole column) in August, and at Locations 2.0 (epilimnion) and 9,5
in November, Cladocerans were dominant at Locations 2.0, 1 1A and 15.9 (epilimnion) in
August, and at Location 2.0 (whole column) in November. Routers dominated zooplankton
at all but Location 15.9 in February, and tit Locations 11.0 and 15.9 in November. Record
high densities at Locations 11.0 ,aid 15.9 in November were due primarily to rotifers,
Although microcrustaceans remained dominant in 19991, both numbers and percent
composition of rotiters had increased since 1998, when the overall lakewide percent
composition of rotifers was the lowest observed (Figure 4-6). This represents a reversal of
the trend of increasing relative abundances of microcrustaceans and declining rotifer
abundances which started in 1995 (Figures 4-6 through 4-8). A similar trend was observed
between 1988 and 1993. From 1988 through 1991, the annual lake -wide percent composition
of microcrustaceans increased from 13% to approximately 52% in epilimnetie samples, and
showed an overall increase of from 20% to nearly 60% in whole column samples. By 1992,
lake -wide microcrustacean percent compositions had declined to 43% and 47% in epilimnetic
and whole column samples, respectively. Between 1995 and 1998 lake -wide percent
composition of microcrustaceans increased from approximately 40% to 63% in epilimnetic
samples, and increased from approximately 40% to 67% in whole column samples, This
trend was observed at all locations (Figures 4-7 and 4-8). The nature of both trends would
indicate some lake -wide natural cause at work, and not the impacts of station operations,
which would be reflected in localized areas. In addition, the annual zooplankton density
(based on quarterly data from the same months sampled during this Program) in the Mixing
Zone was dominated by microcrustaccans in 1979, several years prior to MNS station
operations (Duke Power Company 1985). During 1999, lake -wide percent compositions of
4-4

microcrustaceans'had declined to 50% and <65% in epilimnetic and whole column samples,
respectively.
Copepoda
Copepod populations were consistently dominated by immature forms (primarily nauplii) ,
during 1999, as has always been the case. Adult copepods seldom constituted more than %
of the total zooplankton density at any location during 1999. Tropocyc°lops, Mesocyclops,
and Cpischur°a were often important constituents of adult populations, while Diapton7us was
occasionally important ('Table 4-4.
Copepods were more abundant at Background Locations than at Mixing Zone Locations
during 1999, and their densities peaked in May at both Mixing Zone and Background
Locations (Table 4-1, Figure -5). Historically, maximum copepod densities were most often
observed in May.
Cladocera
osmina was the most abundant cladoceran observed in 1999 samples, as has been the case
in most previous studies (Duke Power Company 1999, Hamme 1982). Bosmina often
comprised greater than '5% of the total zo plankton densities in both epilimmtic and whole
column n samples. Bosminop.sis and Diapdranosoina were also important among cladocerans
(Table 4-4). During August, Bosininopsis dominated cladoceran Populations in all but the
whole column sample from Location 9.5. Diaph anoso a dominated cladoceran populations
in most May samples. This same pattern of cladoceran taxonomic ditribution was observed
in 199 (Duke Power Company 1999).
Long-term seasonal trends of cladoceran densities were variable; from 1990 to 1993, peak
densities occurred in February, while in 1994 and 1995, maxima were recorded in May
(Figure 4.5). During 1996, peak cladoceran densities occurred. in May in the Mixing ,done,
and. in August among Background Locations. During 1997, cladoceran densities again
peaked in May. Maximum cladoceran densities in 1998 occurred in August, Luring, 1999,
peak cladoceran densities occurred at location 2.0 in August; and in November at Locations
9.5 through 15.9. spatially, cladocerans were more abundant at Locations 11.0 and 15.9` than
at other locations (Table 4-1, Figure -4).
4'-5

Rotifera
Pob)arthru was the most abundant rotifer in 1999 samples, as was the case in 1998 (Duke
Power Company 1999), This taxon dominated rotifer populations at all locations in February
and May (Table 4-4). Polyarthra also dominated rotifer populations at Locations 2.0, 9.5
(whole column), and 11.0 (epilimnion) in August, and was the dominant rotifer at Location
15.9 (epilimmon) in November. Kerwella was dominant in most November samples.
Conochilus dominated rotifer populations at Location 15.9 (whole column) in August, and
Location 2.0 (epilimnion) in November, Ploesoma and Tricocerea were the dominant
rotifers among August samples frorn Locations I 1 .0 (whole column) and 15,9 (epilimnion),
respectively, All of these taxa have been identified as important constituents of rotifer
populations, as well as zooplankton communities, in previous studies (Duke power Company
1999; Hamme 1982).
Long-term tracking of rotifer populations indicated high year-to-year seasonal variability,
Peak densities have most often occurred in February and May, with an occasional peak in
August (Figure 4-5, Duke power Company 1989, 1990). During 1999, peak densities at
Mixing Zone locations were observed in February, while maximum densities at Background
locations occurred in November, The mean rotifer density from Background locations in
November 1999 was the highest yet observed.
FUTURE STUDIES
No changes are planned for the 7ooplankton portion of the Lake Norman Maintenance
Monitoring Program in 2000 and 2001
SUMMARY
Considerable seasonal variability was observed in Lake Norman zooplankton populations
during 1999: Maximum epilininetic densities occurred in May (Location 9.5), August
(Locations 2.0), and November (Locations 11.0 and 15.9), while minimum values were
recorded in February (Location 15.9), August (Locations 11.0 and 15.9), and November
(Location 2.0). In whole column samples, maximum densities occurred in November, with
minimum values most often observed in August. Mean zooplankton densities tended to be
higher among Background Locations than among Mixing Zone locations during most seasons
4-6

of 1999. In addition, long-term trends showed much higher year-to-year variability at
Background Locations than at Mixing Zone Locations.
Epilimnetic zooplankton densities during May and August of 1999 were within ranges of
those observed in, previous years, The February density at Location 2.0 was the lowest
recorded from this location for this month, while densities at Locations I 1 .0 and 15.9 in
November were the highest ever observed at these locations for November.
One hundred and eight zooplankton tax.a have been recorded from Lake Norman since the
Program began in 1987 (fifty-two were identified during 1999). Four taxa previously
unreported during the Program were identified during 1999.
Copepods dominated zooplankron standing crops through most of 1999. Overall relative
abundance of copepods in 1999 had declined since 1998, when their relative abundance was
the highest observed in recent years. This represented a reversal of the trend of increasing
microcrustation abundance observed between 1995 and 1998. Cladocerans dominated most
zooplankton densities in August, while rotifers were dominant at most locations in February.
Record high densities at Locations 11.0 and 15.9 in November were due primarily to high
numbers of rotifers in these samples. Overall, the relative abundance of rotifers had
increased since 1998. Historically, copepods and rotifers have shown annual peaks in May,
while cladocerans continued to demonstrate year-to-year variability,
Copepods were dominated by immature forms with adults seldom accounting for more than
8% of zooplankton densities. The most important adult copepods were Tropocyclops,
Afesocyclops, and Epischta-ci, as was the case in previous years. Bostnina was the
predominant cladoceran, as has also been the case in most previous years of the Program.
Bosminopsis dominated most cladoceran populations in August, while Diaphanosonla
dominated cladoceran populations at most locations in May, The most abundant rotifer
observed in 1999, as in previous years, was Polyarthra.
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 1999, were likely due to environmental factors and appear
not to be related to plant operations.
4-7

LITERATURE CITED
Duke Power Company. 1976. McGuire Nuclear Station, Units 1 and 2„ Environmental
Report, Operating License State. 6th rev, Volume 2. Duke Power Company,
Charlotte , NC.
Duke Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke
Power Company, Charlotte, NC.
Duke Power Company. ,1988. Lake Norman Maintenance monitoring program: 198'
Summary. DukePower Company, Charlotte, NC,
Duke Power Company. 1989. Lake Norman Maintenance monitoring program: 1988
Summary: Duke Power Company, Charlotte, NC.
Duke Power Company. 1990. Lake Norman Maintenance monitoring program: 1989
Summary, Duke Power Company, Charlotte, NC.
Duke Power Company. 1991. Lake 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. 1992
Summary. Duke Power Company, Charlotte, N.
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. 1995
Summary. Duke Power Company, Charlotte, NC.
Duke Power Company. 1992. Lake Norman Maintenance monitoring program: 1996
Summary. Duke Power Company, Charlotte, NCB.
Duke Power Company. ,1998. ,Lake Norman Maintenance monitoring program: 199
Summary, Duke Power Company, Charlotte, NC.
Duke Power Company. =1999. Lake Norman Maintenance monitoring program: 1998
Summary. Duke Power Company, Charlotte, NC.
1-8

I-1annme, R. E. 1982. Zooplankton, In J. E. Hogan and W. D. Adair (ids.). Lake Norman
Summary, Technical Report DUKEPWRJ82-02, p. 323-353, Duke Power Company,
Charlotte, NC. 460 p.
Hutchinson, G. E. 1967. A Treatise on Linmolog . Vol. 11. Introduction to Lake
Biology and the Limnoplankton. John Wiley and Sons, Inc. N. Y. 1115 pp.
Ienhinick; E. F. and L. I . 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 Prcjject (RP-49) Report No. I L, p. 1 -138, Johns Hopkins > University,
Baltimore, MD 235 p.
'rho ton, I .. W., 13. L. Kimmel, F. E. Payne. 1990. Reservoir Limnology. John Wiley
and Sons, Inc.. New Fork, NY.
4-

Table 4-1. Total zooplankton densities (no. X 1000/m3), densities of major zooplankton
taxonomic
groups, and percent composition (in parentheses) of major
to a in
10m to surface (10-S) and bottom to surface ( -S) net tow samples collected
from Lake Normanits February, May,
August, and November
1999.
Sample
Locations
Date .1. ' e
Ta on
2.0
0=
. 5
11.0
15.9
2/4/99 1 -S
COPE;P DA
7.2
11.0
14A
16.9
24.9
(2,1.1)
(23.3)
(27.9)
(26.5)
(50.0)
CLADOCERA
1.0
2.4
2A
8.0
6.6
(3.0)
(.1)
(4.6)
(12.6)
(13.1)
ROTIFERA
25.8
33.8
34.7
38.9
18.4
(75.8)
(71.6)
(67.5)
(60.9)
(X9)
TOTAL
34A
47.1
51 A
63.9
49„9
13-S
depth (in)
of tow
COPFPO A
T5
9.1
123
11 A
21.3
for each
(223)
(19.)
(26.2)
(27.7)
(51,8)
Location
C1.,ADOC1 RA
1.0
1.2
1.6
43
63
2.0=30
(3.0)
(2.5)
(3.5)
(10.4)
(15.4)'
5.0=17
ROTIFERA
25,1
36,9
33.1
25.6
13.5
9.5=21
(7.8)
(78.2)
(70.3)
(61.8)
(32.8)
11.0=25
15.9=20
TOTAL
33.6
47.2
47.0
41.3
41.1
5/3/99 10-S
COP PODA
34.1
33.3
45.7
73.9
60.
(60.8)
(9.5)
(67.9)
(61.6)
(60.8)
CLADOCFRA
14.
11.7
-1 1.8
22.5
16.8
(2,4)
(20.9)
(17.4)
(18.7)
(17.0)
ROT1F13RA
7.7
10.9`
9.9
23.6
211
(1 .8)
(19.6)
(14�7)
(I )
(22. )
TOTAL
56.1
55.9
67.4
120.0
99.2
_j
depth (in)
of tow
COPEPODA
27.8
36,9
46A
40.6
for each
(6T 1)
(70A)
(67.2)
(56.3)
Location
CLADOC ERA
T5
7.8
M7
15.0
10=30
(18.1)
(14.8)
(15.5)
( .7)'
5.0=NS
ROTA ERA :
6.1
7.8 ,
11.9
16.6
9.5=21
(14.8)
(14.8)
(17.2)
(23.0)
11.0=25
15.9=0
TOTAL
41.4
NS
52.4
69.0
72.2
a- 0

'Fable
4-1 (continued).
Sample
Locations
Date I:Ype
Taxon
2.0
5 0
9 5
11.0
15.9
/25/99 10-S
COPEPODA
11.7
7.8
1 A
24.5
(IT5)
(41.6)
(6.5)
(3.1
CLADOCERA
511
7.6
28.1
31.7
(79.7)
(4U)
(51A)
(41 )
ROTIF RA
L
3.3
111
1 .0
(1)
(17.4)
(22.2)
(24.2)
TOTAL
66.6
NS
M7
54.6
74<2
B-
depth (m)
of tow
COPEPODA
I L5
10.7
10.8
29.6
for each
(2.5)
(61.7) '
(31.6)
(4 3.6)
Location
CLADOCERA
27.6
5.5
17.5
20.6
10=3
(6 ,2)
(31.)
(51 A)
(30.3)
5.0=NS
Ro,rIF RA; _
13
L I
5.7
17.5
9.5=19
(3.3)
(6.5)
(16.7)
(25.8)
11.0=25
15.9=18
TOTAIL
40.4
NS
17.4
34.1
67.9"
11/12/99 10_S
COPEPODA
11.4
30.0
318
20.0
(35A)
(55.8) '
(18,8)
(5.0)
CLADOCERA
1'0.6
7,7
52,8
15.7
(33.0)
(14A)
(2 A)
(3.9)
ROTIFERA
10.2
16.0
93.1
365.7
(31.6)
(29,)
(51. )
(91.1)
TOTAL
32.2
NS
53.7
179.6
401A
B-
depth (xis)
of tow
COPEPODA
15.6
37.4
37.9
for each
(36.1)
(58.0)
(23.6)
Location
CLADOCERA
M8
6.Q
49.2
2.0=30
(43.6)
(9A)
(30.7)
5.O=NS
ROTIFERA
&8
21.0
733
.5=20
(20A)
(316)
(45.7)
1 1.0=2
15.9=NS
TOTAL
43.1
NS
64.5
160.4
N
Sample not collected due to high winds, or no
mooring buoy.
Chzroborus spp.,
Chcrobor us spp.,
<0. l /tn3, 0.2°r
0. /m), 0.3°
- I

�
Table 4-2.
uncan's Multiple Range Test can epil mnetic zooplanktc n densities (no.
1000/ 3) in Labe Nonnan, NC during ' 1999.
February
Location
2.0
5.0
15.9
9.5
11.
Mean
34.0
4T 1
49.9
51.4
63.8
May
Location
5.0
2.0
9.5
11.0
15.
Mean
55.9
56.1
67A
99.2
120.0
August
Location
.5
11.0
2.0
15.9
5.
Mean
18.7
54.6
66.6
74,2
ASS
November
Location
2.0
9.5
11.0
15.9
5.
Mean
32.2
53.7
179.6
401.4
NS
4-12

Table 4-3. oplank-ton taxa identified from samples collected quarterly oil Lake
Norrnai.r from 1988through 1999,
�l't� �iON
Q
r l
?
9 s
9
�?Ei
%
�7
C D—
_
QvIO s tlrc meisr Forbes
x
* vernalis Fischer
her
". spp. 0. F. Muller
l aptoinus liar , ll larsh
x
x
x
x
x
_v
D. missrssalrprensrs Marsh
x
, palla(lus Herack
, rerl lrcrr•clr Marsh
D. spp. Marsh
x
Y
—hj—)ishur_a lrrviati.sr.s Herrick
x
x
x
x
x
.'rcasclras spp-
ucyc clops, a rlrs° (Koch)
..._ _
;c�crc#t"c'Icr_s �cicrx ( . Fc�rl�s)
a
s,
_.
l2 spp. Sars
Tr°opocjvlo s Irr asznus (Fischer)
spp.
x
Cali c�zd c�pepcsrtes
_
_
x
Cyclopoid copepodztes
x
x
x
x
x
x
x
x
Harpactrccardea
_
aplix
l'arasrtrc cpepc�ds
-CLADOCERA
Alona spp,Barrd
,Tl-o aellca spp. {Birge)
Bosmrna lon, rrostr°rs (0, E i .)
x
x
x
13. spp, Baird
x
x
x
x
x
x
x
x
_
Bosrnrnol7sas clietersr Richard
x
x
x
x
_
ioc1gj,) Pntca Icac'arstr"r.s• Birge
t . spp. Darla
x
x
x
x
x
C. lawlorrrs spp. leach
x
I gphnrca ambigma Scourlreld
D. cccatcrwb a Coker
D, galeata Sars
D. la eves Rage
x
D. lon rr rrrtsr Sars
D. lumhol i Sars�
?
a D. mendol (Sacs) rrge
D. Ilcarl'1alCl Fordyce
x
�
x
x
x
s.
x
x
x
x
T .—pule (de Geer)
- l 3

Table 4-3 (c ntinued)
page
2 o'4
TAXON
8
89
0
91
9?
93
9
75
9
7
9
CL Cr A (continued)
D. puliccar i a Sars
D. retrocury a Forbes
X
D, .schodler i Sars
D. spp, Mullen
Dicrphanos m a brachyrerum (L evin)
D. spp. Fischer
5
J�-
E, ubosmin a Spp. (Baird)
a olopedium camazz t icum St nge.
.1L 9ibbcr m addach`
H spp. Stingelin
Ilya crypta s sorclidus (Lieven)
X
X
I. spinifer
I. spp. Sars
Lcatonca setiferca (O.F. Muller)
Le todora kincltii (Focke)
x
x
_
Leydi,gica spp. Freyber
to nca spp. Baird
xS`ida crystallinca 0. F. Muller
.Simoceph alas expinosus
Simocephalus spp. Sc odler
ROTIFERA
Anaaraeopsas spp. Laut rbo e
Asplcanchnca bi-ightsvelli Caosse
x
A. praodontca Crosse
A. spp. Gosse
x
X
Brcachionus ceaud atca Barr, & Daday
X
X
X
B. h av aiwensis Rousselet
X
B. pataalaa.s O� F. Muller
x
x
x_
x
B. spp. Pallas
x
x
C iromog,a.ster ov alr.s (Bergendel)
C , spp. Lauterborne
Collotheca bLalCatonacLa Harring
x
x
x
C . inutcabilis (Hudson)
• spp. 1`arrina'
r�l'
Colurellca spp. Bory de St. Vincent
Conochil ides d1 ssu arias Hudson
C ". spp. Hlava
Conochilus unicornis (Rousselet)
x
X
-14

Fable 34 (continued)
_
page of
TAXON
fit}
i 1
>
t
_ _ .,� .. -)-__ -
�'�
}q�t?I2�22'�ii
Hlava
ray
x
vy�{y
d�78.
^{}[y
1k
/Ta+Y.}(y.}gegp/y. `9y Cs# pp'y¢
8 4d ffid L6 + & ii i,.l G.. �4dA4
(�
,p'�,
—X—
Gcistwjwis slyll lc>r Irnho
G. spp, Imhof
?
excrrthrcc rrrrrcr Hudson
x
x
II spp. Sch ada
ellictrttt€t basin tienssrs (Roos let)
X
X
a
'rr
:. It ngisj)ina K llicott
K. spp. Rousselet
'e crt ll i coc hlerrr is
�. tcrrtroc epha-lcr Myers
, spp. Bory de St, Vincent
x
x
x
x
x
x
x
x
,ckcz ne spp. Nitzsch
x
x
x_
x
AllacrCichaelus sZ1b4jIGadr"c7t; Perty
Alf spp. Perty
jx
,Atonost lcr stem—ocrsi (Meissen r)
M. spp. Ehrenberg
�
x
x
?
_
-
crtlrlrrccr spp. Gosu
.Plcr crsrrma hudstrrrrr` Brauer _x
x
P. truncation (L.e vandq)
x
x
, spp. Herrick
Povelrthrc eu) y lera ( cirzeljski)
P. rr ijor l urckhart
x
x
P, vul oris Carlin
P. spp. Ehrenberg-
_
Pony7holyy spp. Gosse
Ptv,qur°cr libr a Meyers
P, spp. Ehrenberg
?s
x
x
,S*ync°haetu spp. Ehrenberg
I t ichocercei C'C7lm,cina (Weireijski)
x
x
x
x
x
x
x
T cylindrtca (Inihot)
Ix
—XI
.longis"ew chranK
T rrrrrltic rr"rzrs (Klhcc�tt)
'' x
T P rrcellus (Gasse) -
T pusilla ;lcnnin ;s
;
P sr'rrlrs Lamar
T spp. Larnarl.
?
r-tchotrrcr spp. Bory de St. Vii-nccnt
4-l5

Table3-4 (continued) page 4 of 4
TAXON 1 88 1 89 1 90 91 92 93 94 95 96 97 98 99
ROTIFERAcontinue
Unidentified Pdelloida x x x x x x x x
Unidentified lotifera
INSECTA
Ch aobort v spp. Lichtenstein
T A. (unidentified)! x
-16

Table 4-4. Dominant to a among copepods (adults), cladocerans, and routers, and their
percent composition
(in parentheses) of copepod, cladoceran
and rotifer
densities in Labe Norman samples during
1999.
FEBi2LTARY
MAY
AUGUST
NOVE1�IBER
COPEPODA
EPILI NION
2,0
Epischura (13.2)
Ueso(yclops (3<7)
Diaptoinus (2.7)*
Epischura (3.2)
5.0
Tr;opocyclons (12,9)
rl?esoqyclops (2.3)
NOT SAMPLED
NOT SAMPLE
9.5
Epischura (.)
Epischura (2.6)
Epischura (3.4)
Tropocyctlops (10A)
11.0
Tropo yclops (7.9)
Diaptornits (3:3)
Tropc cyclops (6.0)
Tr•opocyclops (1.9)
15,9
Epischura (3:2)
Epischura (3,0) ,
Tropa cyclop:s (I.5)
Tropocyclops (5,0)*
COPEPO A
! OLE COLtll' N
2.0
Tropocyclops (29.0)
hfesocyclops (1.7)
Alesocyclops (10.0)
Hesocyclops (4,6)
5.0
Tropocyclops (9.9)
NOT SAMPLED
NOT SAMPLED
NOT SAMPLED
9,5,
Tropocyxclops (7.)
htesocYclops (2.3)
Mesocyclops (5.5)
Epischura (13.0)
11,0 -
Tropocyc:lops (11.5)
Diaptonnis (2.)
AlesocyFclops (4.9)
IvIesoryclops (10 4)
15.9
Tropocy°clops (5.0)
Epischura (2.2)
Hesocyclops;(3.6)
NOT SAMPLED
CLADOCE A:
EPILI NION
2.0
Daphnia (50.8)
Holopecliurn (34:0)
Bostuanopsis (82.8)
Bosrni'na (98.4) ;
5.0 ,
Daphnia (4 .1)
Bosntin t (36.0)
NOT SAMPLED
NOT SAMPLED
9.5
Bosmina (45.8)
Dtaphanosorna (59.7)
Bosminopsis (52.9)
Bostnina (88,0)
11,0
Bostnina (45.1)
Daaphanosotna (51.4)
Bosrninopsis (84.2)
Bosrninca (98.9)
15.9
Bofinnna (58,5)
Diaphat o.soina (58,1)
Bosrtlanopsis (80.8)
Bosmina (90.8)
CL,A DOCERA
2.0
Bostnina (42.3)
Bosmina (50.0)
5.0
Bosmina (55.5)
NOT SAMPLED
.5
Daphnia (44,0)
Diaphanosorua (48.5)
11.0
Bosmina (38.9)
Diaphanosorna (36,5)
15.9
Bostnina (63.3)
Bosmina (36.0)
OLE COLD N
Bosrnin« psis (79.3) _ Bosmina (94.9)
NOTSAMPLED NOT SAMPLED
Bosmina (47.9) Bosmina (88.3)
Bosminopsis (81.8) Bosmina (87.0)
Bosrninopsis (71.9)
0 -
NOT SAMPLED
4-17

Table _4 (continued)
I l IRTAR.Y_ MAY
_ AlY7t�i.JS�
IvT(l T�11
O TIIa EI A
EPIL.IM I( N
2.0
Poy arthrca (68. 1 }
I'tal�rcarthrea (84.3)
Poly arthru (74.8)
C.'onochttacs (22 4)
5.O
Poi y trthra (81.6)
Pt 4yarthrca (82.9)
NOTSAMPLED
NOT SAMPLED
9.5
Poly zrthrer (74.5)
Ptrlyarthrcr (73.8)
Keratella (34.2)
Keratella ( 3.7);
1 1.0
Perlycarthrcr (73,8)
Polyarthra (94, I)
Pralvaarthra (62.3)
Kertatellcr (85,6)
15.9
Po4v arthrca (59.2)
I?o4y arthrea (941 5)
T`richvc� rcca (23,7)
Ptrlycarthrtr (52.8)
ROTIT R _
_ WI-OLIE+COLU VN
2
Pc 4yarthrca (45.7)
Ptrlt'crrtlrr"tr (83.6)
Ptrltwrthrca (58.7)
ereatellta (24.2) -
5,0
Pcrly rthrca (86.4)
NOT SAMPLER
NOT SAMPLED
NOT SAMPLER
9.5
Ptrly arthra (62.2)
Poly arthrca (82,1)
Pcrltwrthrca (60.5)
Kertafella (40.2)
11,0 ,
Praly arthru (59.8)
P lycarthrca (93.3)
Ploeoscrrrrea (54.4)
NOTSAMPLED
15.9"
Ptrlyzarthrta (54.7)
Polyarthra (92.0)
Conochilus (27.1)
14 rcatellta (77.2)
* = Only in
adults present
samples.
4-8

10m TO SURFACETOWS
450
400
350
300
250
200
150
100
50
a
2.0
5.0 9.5 11.0 15.
BOTTOM TO SURFACE TOWS
FEES Y A U G NOV
180 _.-d
-w -._.._w
la
140
120
f
100
80
60 {
40 O
20
a
2.a
5.0 9.5 11.a 15.9
LOCATIONS
Figure
4-1.
Total zooplankton densityqy> location tar samples collected in Take Norman
N, in 1999.
4-1

FRUAR A
300 30t1 .. _
..,-2.0 5.0
1
20 250
200 200
150 t 150
100 100
0 50
00_
87 88 89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 ' 95 96 97 98
99
BACKGOUND LOCATIONS
IO
00 ...... _ .. _.._.0 , . a , 00 _..
427,000
250 250
00 200
l
,6
150 150
100 100
0 � 50 {
{
87 88 89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98
99
YEARS YEARS
Figure 4-2. Total zooplankt n densities by location for epzlznnietie samples collected in
Lake Norman, NC, in February and May of 1988 through 1999,
4-2}

300
AUGUST NOVEMBER
300
250
250 _
200
200
x
>e
50
150
f
i
100
100
50
f
50
87 88
89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98 99
BACKGROUND O ATIO
...
300
450
9.5 11.0 15.9
400
250
7
350
l±
200
y
300
250
150
200
100
150
100
50 `
5�0y
pay
87 88
89 90 91 92 93 94 95 96 97 98 99 87 88 89 90 91 92 93 94 95 96 97 98 99
YEARS YEARS
Figure
-
. Total zooplankton densities by location for e ili netze samples collected in
Lae Norman, NC, in August and November of 1987 through 1999.
_2

COPEPODS
90
80
70
69
50
2
40
30
k
20
f
�
10
l
CLADOCERANS
60
---------
MING. ZONE BACKGROUND LOCATIONS
50
40
i
Cl
i
0
10
180
16(1
140
120
100
80
60
40
20
v"i
w� CV C5 M +d aP lit iat v7 «i5 A- t•-� 4? C9 4`r +»m
5T cri iT n"fl G'p➢. R'r O'+ «i'r C� t7+ Ls5 tT � tri tri iT � � ir+
U.
U. < U. < U. Q 7a:T U.
Figure -
.. Zooplankton composition by quarter for epim lmnetic samples collected in
Lake Norman, NC, from 1990 through 1999 (only Location 2.0 represents the
MIXING ZONE in August and November),
4-2

LAKE -WIDE- EPILIMNION
pCOPEPODS M CLADOCERANS ROTIFERS
100°la _. _.m. ..-._ ------ ___.. __. �'... .. M,..
90%
80%
70%
Q
60% _
50%
40%
30%
20%
10%
_
Qa/a
19881989 1990 1991 1992 1993 1994 1995 1996 1997 1998 1999
YEARS
wHoLE COLLM
(�cbpEpoDs cLADodmANs M ROWERS
100°fo
90%
80�%
p0%
cta
60%
50%
40%n
30%
20%
10%
0%
1988 1989 1990 1991 1992 1993 14 1995 1996 1997 1998 1999
YEARS
Figure 4-6.
Annual lake -wide percent composition of major zooplankton taxonomic
groups from 1988 through 1999.
4-24

41XING ZONE (LOCATIONS 2.0 + 5. ): EPILIM MON
0 COPEPODS 0 CLADOCERANS R01YERS
100%
m.. r ..... ........
90%
;
I
0%
d
70%
60%
50%
40%
30%
0%
10%
p
1988
199 1990 1991 1992 1993 1994 1995 1996 1997 1998 1999
YEAR
1 1 ZQ (LOCATIONS- 2.64 0): WHOLE 60LW
0 bbPEPoDs 0 CLADOCERANSROWERS
90%
80%
70%
k
.m
F.
60%
50%
}
40%
30%
20°la ,
10%
0%
1988
1989 1990 1991 1992 1993 1994 1995 1996 197 198 1999
YEAR
Figure 4-7.
annual percent composition of major zooplankton taxonomic groups t"rorn
Mixing Zone Locations: 1988 through 1999.
4-25

•
e9 a
IIR.
r
6M
dT
t
ii
e
CL
50%
fJ
49%
30%
ta.
20%
10%
0%
1988 1989 1990 1991 1992 1993 1994 1995 1996 1997 1998 199
YEAR
Figure -7. Annual percent composition of major zooplankton taxonomic groups from
Background locations: 1988 through 1999.
4-26

CHAPTER 5
FISHERIES
INTRODUCTION
In accordance with the NPDES permit for McGuire Nuclear Station (MNS), monitoring of
specific fish population parameters was continued during 1999. The components of the 1999
fish monitoring program for Lake Norman were to:
I. Continue striped bass mortality monitoring throughout the summer.
2. Continue a cooperative striped bass study with NCWRC to evaluate striped bass
growth and condition as a function of stocking rates, forage availability, and summer
Striped bass habitat in Lake Norman.
3. Continue annual, tall hydroacoustic/purse seine forme population assessments.
4. ,Assist the NCRC in shad netting collections to evaluate the tax, composition and
size distribution of Lake Norman forme species.
5'a Revise annual, spring shoreline electrofishing program to be conducted every
years, beginning Spring 1999.
6. Coordinate Spring 1999, shoreline electrofishing sampling with NCWRC;" personnel
to collect largemouth bass age/growth information.
7`. Summarize Lake Norman h droacoustics/pars 'seine -data. for 1998 and. t 99.
Continue Duke participation on the Lake Norman Advisory Committee and assist the
NC CRC in accessing and interpreting relevant Duke data, relative to Committee
activities.
METHODS AND MATERIALS
Spring shoreline electrofishing was conducted during April -. Ten 300-m transects Were
sampled in each of three areas of Lake Norman (MNS mixing zone, mid -lake reference area,
and Marshall Steam Station mixing zone), for a total of_30 transacts. The MNS ruing zone
5-1

transects were located within the area between Ramsey Creek and Channel Marker I A. The
mid -lake refcrence transects were located in the area between Channel Marker 7 and Channel
Marker 9, while the Marshall Steam Station (MSS) mixing zone transects were located in the
area between Channel Marker 14 and the NC Highway 150 Bridge. All transacts were
subjectively selected to include the various habitat types that exist in Lake Norman and that
could be effectively sampled. The only areas excluded were shallow flats where the boat
could not access the area within 3-4 m of the shoreline. All sampling was conducted during
daylight and when water temperatures generally ranged from 15 to 20 C. Except for
largernouth bass, all fish collected were identified to species., and total number and total
weight were obtained tior each species. Individual total lengths (mni) and weights (g) were
obtained for all largemouth bass collected.
The mixing zone was monitored for striped bass mortalities during all summer sampling trips
on the take. Additionally, from July I through August 24, 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 1,999, sampling for striped bass condition was restricted to data collected during the
winter Lake Norman striped bass tournament conducted on December 4. North Carolina
Wildlife Resources Commission and Duke personnel obtained individual total lengths (mm)
and weights (g) from striped bass caught during the tournament, These data were used by the
NCWRC to calculate early winter condition of Lake Norman striped bass,
Purse seine samples were collected on August 17 and 18 and September 23, from the lower
(main channel near Marker 1), mid (mouth, of Davidson Creek), and uplake Oust downlake of
Duke Power State Park) areas of the reservoir. The August purse seine sample was
conducted as an additional qualitative sample per a request from the NCWR,C. The sample
was intended to monitor possible changes in the species composition and size distribution of
Lake Norman forage, relative to the recent discovery of' alewives in the reservoir. 'rhe
September purse seine sample was the routine fall sample conducted in corijunction with the
fall hydroacoustic surveys. A subsample of' forage fish collected during this sample was used
to deterrnine taxa composition and size distribution of the lake -wide forage population,
Gill netting for shad and alewives was jointly conducted by the NCWRC and Duke during
September 20-23, to evaluate the taxa, composition and size distribution of Lake Norman
forage species. Netting was conducted at four locations, each, in creel zones 3, 4, and 5
(Figure 5-1). The sampling consisted of two overnight net sets at each location, one shallow
5-2

0
net and one deep net, for a total of eight net nights per zone, Collected fish were removed
from the nets, sorted by; species, and measured for individual total length (i rn). Netting data
were recorded separately for each net fished.
RESULTS ULTS AND DISCUSSION
Spring shoreline -'electrc flshia g of Labe Norman yielded variable catches among the three
areas Sampled (Tables 5-1 through -3). In the NINS mixing zone area., a total of 1,379 fish
were collected, weighing a total of 7 . 1 kg and representing 14 taxa (Table 5-1).. Individual
transect catches ranged from a low of 16 fish to a high of 07 fish. The total catch from tlae
reference area was 998 fish, weighing 80.45 kg and representing 16 taxa (Table 5-2).
Individual ;transect catches ranged from 16 to 311 fish. The highest total catch and taxa
composition was collected from the HISS mixing zone area (Table 5-3). The total catch was
1,421 fish, weighing 107.86 kg, and representing 20 taxa.
General monitoring of Lake Norman and specific monitoring of the SINS nixing zone for
striped bass mortalities duringthe sunimer of 1999, yielded one mortality within the mixing
zone and five mortalities in the main channel outside the mixing zone. The six observed
mortalities ranged in size from 471 rum to 670 ram. Specific observations by date were.
ATE
LOCATION LENGTH (nina): NUMBER
July 27
Vicinity of Channel Marker 18 530 1
,duly 29
Vicinity of Mountain Creek 471 1
Vicinity of Channel Marker 1A 601 1
August 3
Vicinity of Channel Marker 14 670
August 9
Vicinity of Channel Marker 19 550
August 24 Vicinity of Channel Marker 17 555 1
Catches from the December 4 Striped bass tournament yielded a total of 73 Striped bass.
Striped bass ranged in Size from 510 mm to 719 mm. Individual fish weights ranged from
1,202 g to 3,575 g. These data will be used by the NCWRC to determine early winter
condition of Lake Norman Striped bass.
5-3

Purse seine sampling during August to monitor possible changes in the species composition
and size distribution of Lake N arnian forage yielded gizzard shad, threadf n shad,
i : ard/threa fin hybrids, and alewives j ble 5- ). Of particular interest was the collection
of alewives (identification verified by Wayne Starnes, North Carolina State Museum). This
species had not been collected from lake Norman, prior to 1998. Catches from all three
areas of the reservoir were dominated by thregadfin shad. Numerically, thr adfin shad
comprised 97.5%, 96.7%, and 97.9 of the total catch from the lower lake, rnid lake, and
upper lake areas, respectively. Total catch ranged from 353 fish in the lover lake to 794 fish
in the mid lake. Alewives were collected from bath the mid lake and upper lake areas, with
catches of'5 fish and 9 fish., respectively.
Analyses of fall hydroiacoustics data collected during 1998 and 1999 to estimate Lake
Norman forage populations has been completed. A ` separate stzmmary report has been
prepared and is included as Attachment 1.
Gill netting for shad and alewives yielded a total of 37E fish ti°orn 34 net nights of sampling
in three zones of I: -cake Norman (Table 5.5). All three forage species (gizzard shad, threudfin
shad, and alewives) were collected from Zones 3 and 5, while only gizzard shad and thre dfin
shad were collect from Gone 4. Total net catches were highest in Zone 5 (2 n fish), followed
by Tones 3 1 7 fish). and 4 (13 fish).; respectively.
FUTURE FISH STUDIES
• Continue striped bass mortality monitoring throughout the summer.
• Continue a cooperative striped bass study with NCWRC to evaluate striped bass growth
and condition as a function of stocking rates, forage availability, and summer striped
bass habitat in Lake Norman.
• Continue the; aannual„ hall hydroacoustic/purse seine forage population assessment.
• Continue spring electrof shing program on two year frequency. with the next sample
scheduled for the Spring 001i
• Repeat late summer purse seine sample and fall small mesh krill net sample to monitor
changes in Lake Norman forage population.
• Cover December Striper Swipers tournament to obtain striped bass body- condition data.
• Support cooperative NCU bioener etics study on lakes I actin and Norm, an by
assisting in the collection of striped bass, forme, and summer habitat data for lake
Norman, as requested by the NCWRC.
5-4

0
Assist the NC CRC in the design, construction, and evaluation of a shoreline plantings
demonstration project can Lake Norman, per guidelines presented in the shoreline
plantings brochure being developed by Duke.
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 environmental maintenance monitoring program for the
NPDES permit for MNS, specific fish monitoring programs were coordinated with the
NC W C and continued during 1999. Generalmonitoring, of Lake Norman and specific
monitoring of the MNS mixing zone for striped bass mortalities during the summer of 1999,
yielded one mortality within the mixing zone and five mortalities in the main channel outside
the mixing zone.
Spring shoreline electrofishing of Lake Norman yielded variable catches for the three areas
sampled; the NINS mixing zone area, a mid lake reference area., and the MSS mixing zone
area. The highest total catch numerically, gravimetrically, and in taxa composition was from
the MSS mixing zone area. Catches from the MNS mixing zone area were the next highest
numerically, but were slightly lower than the reference area in both total biomass and tart
composition.
Striped bass body condition data were collected from 73 fish' caught during the December 4
striped bast; tournament. Striped bass ranged in size from 510 turn to 719 turn. Individual
fish weights ranged from 1,207 g to 3,575 g. All data were submitted to the NCWRC for ,
detailed analyses of striped bass growth and condition.
Purse Seine sampling during August to monitor possible changes in: the species composition
and size distribution of Lake Norman forage yielded gizzard shad, threadfin shad,
gizzard/threadfin hybrids, and alewives. Catches from all three areas of the reservoir were
dominated by threadfin shad.
Nall ;hydroacoustic/purse seine sampling for estimation of Lake Norman forage populations
continued in 1999. Analyses of forage, fish population data for 1998 and 1999 were
completed, and a summary report was prepared (Attachment 1).
5-5

Gill netting for shad and alewives yielded a total of 376 fish from 24 net nights of sampling
in three zones of Lake Norman. All three: forage species (giTzard shad, threadf n shad, and
alewives) were collected from Zones 3 and 5, while only gizzard shad and threadfin shad
were collect from Zone 4.
Through consultation with the NCWRC, the bake Norman fisheries program continues to be
reviewed and modified annually to address fishery issues. Fisheries data continue to be
collected through cooperative monitoring programswith the NCWR.C, to allow the
Commission's assessment and management of Lake Norman fish pOulatic ns. Fisheries data
to date indicate "that the Lake Norman fishery is consistent with the trophic status and
productivity of the reservoir.
-6

Table 5-1. Numbers and biomass of fish collected from electrofishin ten 300-m tr nsects in the MNS mixing zone of Lake Norman during April 1999,
Transdct
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
KC
N
KG
N
KG
N
KG
N
KG
{gizzard shad
1
0.385
3
0.79
4
1,175
Greenfin shiner
1
0.002
1
0.002
itefin shiner
5
0,011
13
0.048
6
0.007
33
0.108 ' 6 0,031
2
0.011
1
OM8
26
0,073
7
0,03
99
0,327
Common carp
1
1.52
4
7,265
3
4.94
3
5.86
1
1.125
2
Z555
14
23,265
Spo ail shiner
1
0,006 1 0.007"
7
0.032
2
0.007
11
0,052
tuillbak
2
3.125
1
0,895
3
4.02
Striped bass
1
0.86
1
0.865
Redbreast sunfish
85
1.165
32
0,31
9
0.111
2
0.022
1
OM7 3 0.029
72
1.25
46
0.815
2
0,79
7
0.21
259
4109
Warmouth
1
0,018
1
0,005
3
0 054
0,077
Bluegill
161
1,535
210
1345
14
0.166
32
0.331
34
0.125 5 0,021
91
0.65
111
0 805
28
0,141
14
0.156
700
5.675
Rede r sunfish
11
0.48
20
0,485
5
OA26
4
0.195
3
_0,225
2
0.315
7
O59
9
0,525
2
0.29
63
3.531
Hybrid sunfish
7
0:096
6
0.081
2
0,021
1
0.035
30
0,605
14
OA8
1
0.047
3
0.07
64
1.435
Largemouth bass
30
&562
25
4273
14
1,627
9
3,097
3
0.164 1 1.39
13
3,112
32
5098
9
1M1
16
3.081
152
25.435
Black crappie
1
0106
1
O.3
1
0,14
3
0.64E
All
302 10,593
307
7,327
51
1127
50
4.531
82
11.06 16 1,478
214 %888
218 14.605
35
4,066
54
6,539
1379
74,214
e

Table 5-2. Numbers and biomass of fish collected from electrofishing ten 300-m transacts in the mid -take reference area of Lake Norman during April 1999,
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
2
OM5
5
1,34
1
0.3
2
0,83
10
1275
Threadfin shad
238
1 �355
238
1,355
Whitefin shiner
25
0.094
2
O�012
1
OM6
7
OM4
19
0.054 1
O�004
6
0.017
28
0,028
89
0,249
Common carp
1
1 �75
3
4,62
4
5�275 1
1.945
3
4,075
2
2,725
14
20,39
Spottail shiner
6
0,027
1
0,005
7
0,032
Swallowtall shiner
1
0,002
1
0,002
Channel catfish
2
IM
1
OA4
2
0,72
5
1.97
Flathead catfish
1
017
1
0,17
White bass
1
OA9
1
OA9
Redbreast sunfish
2
OA25
6
0,17
1
OM3
3
0,056
11
0,3 52
1 A3
5
0,102
24
O�285
25
0,29
27
0.78
156
1571
Warmouth
1
0,058
2
0,024
3
O�075
2
U27
8
0,184
Bluegill
4
0,145
9
0,155
11
U75
18
0,425 84
1,36
12
0.44
19
0,345
42
0,315
30
0,395
229
3,955
Redearsunfish
5
OA8
6
0,51
9
1�015
4
0A
9
U9 1
0.004
1
0.004
2
O�31
1
0,135
38
1248
Hybrid sunfish
1
OA04
1
OA05
3
U1 12
0,28
1
0,004
1
OM1
11
OM
10
O�25
40
1.304
Largemouth bass
13
0.782
33
M63
3
0,932
6
IA7
20
4,189 19
1584
15
4,62
12
3,235
13
2,537
10
3,543
144
36222
Black crappie
6
1,39
2
OA25
1
016
1
0,41
3
071
4
0,935
17
4M
All
59
4312
311
22,782
16
2231
33
2755
87 11,273 173
9A35
38
9,403
68
5A71
127
4�595
86
839
998
80,447
00

0
Table 5-3. Numbers and biomass of fist
1
0 0
collected from electrofishing ten 300-m transepts it the Marshall Steam Station mixing zone area of Lake Norman during April 1999..
Transept
2 3 4 5 6 7 8 9 10 ALL
Gizzard shad
1
0.149
1
0.2
1
0,26
4
1.065
7
1,674
Threadfin shad
92
0,325
58
0.375
20
0.355
170
1,055
Whit fin shiner
14
0.067
5
0.029
7
0.04
6
0.056
11
0.057
16
0.101
59
0,35
Common carp
1
1.615
2
197
2
4,235
1
1:635
2
3,105
5
8.875
2
4.63
4
6,76
19
34.825"
Spottail shiner
2
0,0099
0.053
38
0.212
3
0,016
52
0.29
Swallowtail shiner
4
0,026
4
0.06
Shorthead re hor e
1
0,35
1
0,33
0.68
Channel catfish
1
0,46
1
0.575
2
1,035
Flathead catfish
1
0,7
1
0.7
White perch
8
0.248
8
0,248
Striped bass
1
1.56
1
1,56
Redbreast sunfish
29
0,432
6
0,137
8
0,177
4
0.092
47
1.045
4
0.165
17
0,43
26
" 0,65
41
0.935
14
0.725
196
4.788
Warmouth
3
0.04
1
0.013
3
0.1 6
1
0.008
4
0,035
12
0,222'
Bluegill
41
0.465
15
0,23
25
0,385
85
0,785
65
0.655
80
0:735
36
0.72
58
0,845
:82
0.805
36
0.745
523
6.37
Redear sunfish
1
0,2
4
0.432
6
0.225-
5
0,085
4
0.36
9
0.36
- 3
0.39
2
0.365
34
2,417
Hybrid sunfish
6
0.145
3
0,078
4
0,169
7,
0.175
5
0.215
2
0,12
17
;0.755
8
0,175
5
0.245
57
' 2.077
Largemouth bass
30
8.427
12
1.343
29
T388
7
1.113
54
8.772
21
1.595
28
3,882
21
4.545
26
2,428
39
8.637
267
48.13
White crappie
3
0.83
3
0.835
Black crappie
3
0.565
3
0.565
Yellow perch
1
0.009
1
0.009
All
127
11.55
52
5.84
68
8,779
203
3.487
256 17,248
136
4,785
94
8.903
144 16.669
217 10.376
124 20,219
1421
107,856
vr'

Table 5-4. Numbers and percent composition by location and taxa, for purse seine sampling on August 17 1999,
Lover Lake
Mid Lake
upper Lake
Taxa
No. %
No. %
No. %
Gizzard and shad
3 0.4
Threadfin shad
344 97.5
765 96.7
614 98.0
i' a /Threadfn hybrid
9 Z5
18 2.3
4 0.6
Alewife
5 0.6
9 1.4
"dotal
353 100.0
794 1000
67 100.0'

Table 5-5a Numbers and size ranges by taxa of catches from from gill net sampling during September 20-23, 1999.
Zone 3
Zone 4
Zone 5
axa No.
Length Range (mm)
No. Length Range (mm)
No.
Length RanFe (mm)
75izzard shad 44
84-5
5 29-356
31
183-332
Threadfin shad 60
62-161
8 68.151
219
64-166
Alewife 3
1 -118
6
110-19
Total 107
13
256

ONE
ONE . cy ti
t V
P
C�
ZONE ......:..... 0
Figure 1. Creel survey sampling zones can Lake Norman, North Carolina.
5-12

ATT CHMEN3' 1
-1

Lake Norman Hydroacoustic and Purse Seine Data: 1998 and 1999
INTRODUCTION
In accordance with the NPD S permit for McGuire Nuclear Station ( S), monitoring of
forme fish population parameters' was conducted in 1998 and 1999. This monitoring
included mobile hydroacoustic surveys 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.
METHODS AND MATERIALS
Mobile hydroacoustic surveys of the entire lake were conducted on November l I and 12,
t998 and September 20, 28, and 29, 1999 to estimate forme fish populations. Flydroacoustic
surveys employed multiplexing, side -scan and down -looking transducers to detect surface -
oriented fish and deeper fish (2.0 m to bottom), respectively. Froth transducers were capable
of determining target strength directly by measuring fish position relative to the acoustic axis.
The lake was divided into six zones due to its lame size, spatial heterogeneity„ and multiple
power generation facilities. ,
Purse seine samples were collected on November 2, 1998 and September 23, 1999 from the
lower (main channel near Marker 1). mid (mouth of Davidson Creek), and uplake Gust
downlake of Duke Power State Park) areas of the reservoir. The purse seine measured 118 x
9 m (400 x 30 ft) with a mesh size of 4.8-mm (3/16 in)._ A subsampie of forage fish collected
from each area was used to determine taxa composition and size distribution.
RESULTS AND DISCUSSION
Forage fish densities in the six zones of Lake Norman ranged from 925 to 9,815 fish/ha in
1998 and from 3,547 to 11,368 fish/ha in 1999 (Table 1). In November 1998 the highest fish
density was in Zone 3 (approximately midlake) while in September_1999 the highest density
was in Zone 5 (vicinity of Duke Power State Park.). The estimated forage population was
92,216,000 fish in 1998 and 75,062,000 in "1999, These values are higher than the
6,41,000 estimate in 1997 but lower than the estimates from 1993 to 1996.
With the exception of three gizzard shad (total lengths ranged from 87 rum to 91 mm,
99.95% of the catch in the November 1998 purse seine was comprised of threadfin shad with
an average length of 50 mrn (Figure 1). The September 1999 purse seine was dominated by
1

thrcadfin shad with minor contributions from gizzard shad and alewives; comprising
99.26%, 0.26%, and 0.4 %cif the catch, respectively (Figure 2) The average length of
threadfin shad in the 1999 purse seine sample was 46 mm. The gizzard shad lengths ranged
from 2 to 16 mm and alewife length ranged from 65 to 120 rum.
FUTURE E FISH STUDIES
Continue the annual fall hydroacusticlpurse seine forage population assessment.
2

'
Table 1,
Lake Norman forage fish densities and c� ulation estimates b zones, and lakewide population
lip y_ pp
estimates and 95% confidence limits as estimated by hydroacoustic sampling in 1998 and 1999.
Dens (no./hectare)
Zone
1998 1999
2
7,695 4,756
3
9,815 5,189
4
5,616 6,098
8
5,844 11,368
925 3,547
Population Estimate
Zone
1998 1999
1
1 a
2
23,717,000 14,658,000
3
33,916,000 17,931,000
4
6,913,000 7,507,000
12,307,000 23,941,000
6
442,000 1,695,000:
Total
9,216,000 75,062,000
95% Lower Limit
86,508,249 70,5 5,675
95% Upper Limit
97,922,990 79,547,451

0 0 0
Figure 1Lake Norman Forage Fish - 1998
250
200
150
104 T Shad
ING Shad
50
f
0' z
r c a cvN cv c`v
Length Croup ( M

Figure ` ,
160 Lake Norman Forage Fish - `1999
14 t
120 ,
100
80
EjT Shad
60 MG Shad
Alewives
I
40 .
}
20
i
i., tw tt t h i' ca !! {tit t11 }
tJ1