COPPER AND CADMIUM DYNAMICS IN A
HYPEREUTROPHIC POND

i Dissertation for the Degree of Ph. D.
MICHIGAN STATE UNIVERSITY

‘ JERRY BOYD LISIECKI

A 1977

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This is to certify that the .
thesis entitled
Copper and Cadmium Dynamics in a

Hypereutrophic Pond
presented by

Jerry Boyd Lisiecki

has been accepted towards fulfillment

of the requirements for
PhD d . Fisheries 8c Wildlife
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Major piofessorra

Date January 8, 1977

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ABSTRACT

COPPER AND CADMIUM DYNAMICS IN A
HYPEREUTROPHIC POND

By
Jerry Boyd Lisiecki

A record was developed of temperature, light, dissolved
okygen, Eh, pH, and sediment characteristics for a municipal waste
stabilization pond in Belding, Michigan in which the dynamics of
copper and cadmium were studied through the growing season, May 23
to September 27, 1973. The submersed vascular plants, geratgr

phyllum demersum L. and Potamogeton foliosus Raf., and the

 

epineustic Lemna minor L. formed the principal plant populations

 

in the pond. Their participation in the budgets of the metals is
described. Germination and growth of the plants occurred above
10°C. The pond had a median temperature of 23°C during the months
of June through September. Fifteen to 60% of the light incident
at the surface penetrated to a depth of 2 m during the time of
net biomass increase of the plants from early June to mid-August.
Thereafter light penetration diminished to the range of 2% to

10% through September 27. Dissolved oxygen measurements showed
the pond to be essentially aerobic throughout 24-hour cycles.
Vertical profiles of E7 yielded values generally between 0.2V to

0.6v. pH was in the range typical of photosynthetically active

Jerry Boyd Lisiecki

systems, 8.5 to l0.0. A floc with consistency and color character-
istics of ferric iron covered the sediments or the vegetation along
the bottom of the pond. Sediments beneath the floc and over the
clay seal of the pond were soft and unconsolidated, black, had
lower electrode potentials than the water, and were ca. l6% carbon.

Budgets for total copper and total cadmium were developed
for the pond at two or three week intervals from May through
September. For total copper, the efficiency of removal, grams in
influent - grams in effluent/grams in influent, as measured by
simultaneously sampling the influent and effluent, was l0% in June,
38% in July and was negative or copper release in August and
September. Over the entire study, 2% more copper left the pond
than entered in the influent. However, due to a decrease in the
copper held in the water of the pond (total capper concentration
in the water x pond volume) at the beginning and end of the study,
the sediments trapped 4 mg Cu/mz. This amounted to 15% of the
amount of copper influent to the system during the study. The
aquatic vascular plant community had a net uptake of copper during
June, but thereafter lost it to the environment. For the period
of study, the plants had a net loss equivalent to 2% of the copper
influent to the pond.

There was a net removal of cadmium by the pond for inter-
vals from the start of the study to mid-August. The efficiency
of removal averaged 26%. Thereafter through September, the effi-

ciency of removal was close to zero. During the study, the pond

Jerry Boyd Lisiecki

had an efficiency of removal of 17%. The sediments of the pond had
a net gain of 2.3 mg Cd/mz, an amount equivalent to 28% of the
amount in the influent over the study period. A portion of this
was deposited as the quantity of cadmium in the volume of water in
the pond declined between June and September. The aquatic plant
community showed a net gain in cadmium until mid-August, and a

net loss with senescence thereafter.

Zooplankton and benthic macroinvertebrates of the pond
showed net gains and losses that were a very small fraction of the
total budgets of the elements. Less than 5% of the quantity of
either element influent after the initiation of spring growth

could have been removed by a harvest of the aquatic plants.

COPPER AND CADMIUM DYNAMICS IN A
HYPEREUTROPHIC POND

By

Jerry Boyd Lisiecki

A DISSERTATION

Submitted to
Michigan State University
in partial fulfillment of the requirements
for the degree of

DOCTOR OF PHILOSOPHY

Department of Fisheries and Wildlife

1977

Copyright by
JERRY BOYD LISIECKI
1977

ACKNOWLEDGMENTS

I sincerely thank Dr. C. D. McNabb for his guidance and
assistance during his time as my major advisor.

My graduate committee, Professors R. C. Ball, N. H. Conley,
and B. D. Knezek, was valuable in planning and discussing my pro-
ject and reviewing this thesis.

The graduate students of this department were very helpful
in discussions. Special thanks go to Douglas Bulthuis, John Craig,
Robert Glandon, Louis Helfrich, Jane Kotenko, David Mahan, and
Frederick Payne for their assistance on the studies. Additional
gratitude is due John Craig for his ingenious sampling devices and
Jane Kotenko for her excellent work as a laboratory technician.

I appreciate most of all the efforts of my wife, Connie, to
make my degree effort pleasant and isolate me from outside irri-
tation. My son, Chad, was most understanding of my need for quiet
whenever I required it.

The research for this thesis was partially supported by
funds provided by U. S. Department of Interior, Office of Water
Research and Technology under Project No. A-O73-MICH of the Institute
of Water Research at Michigan State University and the Michigan

Agriculture Experiment Station under Project No. ll57.

ii

TABLE OF CONTENTS

Page
LIST OF TABLES . . . . . . . . . . . . . . . . . iv
LIST OF FIGURES . . . . . . . . . . . . . . . . vi

INTRODUCTION . . . . . . . . . . . . . . . . . l
METHODS . . . . . . . . . . . . . . . . . . . 3
RESULTS . . . . . . . . . . . . . . . . . . . 14
Features of the Environment . . . . . . . . . . 14
Copper and Cadmium Budgets . . . . . . 20
Biotic Interactions with Copper and Cadmium . . . . . 33
DISCUSSION . . . . . . . . . . . . . . . . . . 4O
LITERATURE CITED . . . . . . . . . . . . . . . . 52

APPENDIX . . .l . . . . . . . . . . . . . . . . 57

iii

LIST OF TABLES

Table Page

1. The schedule of sampling in Pond 4 at the Belding
wastewater system in l973 . . . . . . . . . 6

2. Mean dissolved oxygen concentrations (mg/l) observed at
0400 hours in Pond 4 at Belding, Michigan during the
growing season . . . . . . . . l6

3. The penetration of light in Pond 4 of the Belding waste-
water system in 1973.. . . . 18

4. Characteristics of the unconsolidated sediments of Pond 4
in the growing season of 1973 . . . . . . . . . . 21

5. Hydrologic data (values x 103 liters) for Pond 4 of the
Belding wastewater system during the growing season of
1973 . . . . . . . . . . . . . . . . . . 22

6. The partitioning of influent copper among functional
compartments in Pond 4 of the Belding, Michigan waSte
treatment system for intervals of the growing season,
1973 . . . . . . . . . . . . . . . . . . 23

7. Relationships between the total quantities of copper and
cadmium in the inflow and outflow of Pond 4 for the
24-hour period on the date given . . . . . . . . . 25

8. The partitioning of the net total copper that was pro-
cessed by the biota for intervals of the growing season . 26

9. Total grams of capper and cadmium in the pond volume,
the biota, and the vascular hydrophytes on each 24- hour
sampling date . . . . . . . . . . . . . . 27

10. The partitioning of influent cadmium among functional
compartments in Pond 4 of the Belding, Michigan waste
treatment system for intervals of the growing season,

1973 . . . . . . . . . . . . . . . . . . 31

iv

Tab1e
11.

12.

Page

The partitioning of the net total cadmium that was pro-
cessed by the biota among components of the biota for
intervals of the growing season . . . . . . . . . 32

Concentration ratios (ratios of concentrations of metal

pgm/gm of organisms to mg/l of water) for biological

components in Pond 4 of the Belding wastewater treatment
system, 1973 . . . . . . . . . . . . . . . 37

Figure

LIST OF FIGURES

The system of ponds that receives untreated wastewater
from the community of Belding, Michigan

Changes in the standing crop of aquatic plants (it) and

the quantities of copper (O) and cadmium (©) contained

in the crop over the growing season

Differences in tissue concentration of copper between
the floating plant, Lemna minor (CD), and the submersed
vascular plant, Ceratophyllum demersum (C), over the
growing season . . . . . . . . . .

vi

Page

34

35

INTRODUCTION

The need to protect bodies of water from the eutrophying
elements present in the effluent of municipal wastewater treatment
facilities has led in recent years to the use of stabilization ponds
and adjacent land sites for the disposal of finished water. The
ponds principally reduce the fecal bacterial abundance, chemical
oxygen demand and biological oxygen demand of the wastewater and

remove a portion of the eutrophying elements. The irrigated land
areas are intended to trap the remainder of these through the action
of soil and plants. Additionally they may trap toxic heavy metals.
These may represent a particular threat to the long-term optimum
operation of land disposal sites (Chaney, l973; Leeper, 1972; and
Chumbley, 1971).

Many stabilization pond systems in Michigan are designed so
that the series of ponds contains aerobic, facultative, and anaerobic
cells (King, 1967; Porges and MacKenthun, 1963; Fitzgerald and
Rohlich, 1958; and Towne, Bartsch, and Davis, 1957). During the
growing season, submersed vascular hydrophytes are a conspicuous
component of the biota of cells that appear to be aerobic in nature
(McNabb, 1976). These aquatic plants affect the dissolved gases, Eh,
and pH of such ponds (Wium-Andersen and Andersen, 1972; Armstrong,

1964; and Buscemi, 1958) and thus may influence the dynamics of metal

compounds and complexes. The quantity of metals reaching the spray
irrigation sites may be influenced by aquatic plant growth.

Bulthuis, Craig, and McNabb (1974) showed that eight micro-
nutrient and trace metals were in two general categories: those which -
were substantially reduced in concentration during passage through
stabilization ponds and those which were but little reduced. Copper,
of the former category, and cadmium, of the latter, were selected for
this study. Copper is an essential micronutrient for plants, but can
be toxic to both plants and animals at high concentrations (Scott,
1972). Cadmium has not been shown to be an essential inorganic
nutrient. Cadmium toxicity can occur in plants (Traynor, 1974) and
animals (Baes, 1973; Lagerwerff, 1972).

Except for the work of Bulthuis et a1. (1974), the seasonal
cycles of these elements have not been detailed in stabilization
ponds. Cowgill (1968) and Kimball (1973) have examined copper cycles
in natural lakes but did not examine the biota or sediments. In this
meager background, three objectives were formulated for this study.
The first was to obtain a detailed record of temperature, light,
dissolved oxygen, Eh, pH, and sediment characteristics under which
the Cu and Cd dynamics were studied and a submersed vascular plant
community completed its seasonal cycle of growth. The second was to
develop a growing season budget for Cu and Cd in a sewage lagoon with
a dense community of aquatic macrophytes. The third was to determine
the effects of the biota, principally vascular hydrophytes, on the
budgets during logarithmic growth, biomass peaks, and senescence of

populations. To compute the budgets, metal concentration, ash-free

dry weight, and mass were measured for water, sediments, plants,
and aquatic invertebrates at intervals through the growing season,

May 23 through September 27, 1973.

METHODS

The city of Belding, located in the southwest quadrant of the
lower peninsula of Michigan, has a stabilization pond system con-
sisting of a series of five cells (Figure 1). The ponds cover 23
hectares, have a maximum depth of 3 m and serve a population of
approximately 5,000. Untreated waste from the primarily residential
community enters cell 1 and flows by gravity through cells 2, 3, 4
and 5. The fifth cell serves as a seepage unit, discharging through
the sand and gravel materials on which it is perched (Bulthuis et_al.,
1974). The remaining effluent of pond 5 is used for spray irriga-
tion on adjacent land, or is periodically released to the Flat
River. The system began operations in 1966.

The fourth pond in the series was the site of this work. It
was 3.0 hectares in area, and averaged 1.8 m in depth during the
study. The pond was sampled regularly through the seasonal cycle of
growth and senescence of the vascular hydrophytes (May 23-September
27, 1973). The various categories of samples for each date are
shown in Table 1.

Temperature, dissolved oxygen, Eh and pH vertical profiles
of the pond were obtained at 4-hour intervals over 24-hour periods
during the growing season. Temperature and dissolved oxygen were
measured from the surface with a YSI Model 51 automatic compensating
probe. Eh was measured jn_situ with the calomel reference electrode

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floating at the surface of the pond while the platinum electrode
was lowered through the water column. These electrodes were used
in conjunction with a Beckman Model SBL meter. pH was measured
concurrently using a Beckman Model SBX meter. The calibrations of
these instruments were checked before each series of measurements.
The thermistor was checked against two mercury thermometers. The
dissolved oxygen probe was standardized against the azide modifica-
tion of the Ninkler method (American Public Health Association,
1971). The Eh system was standardized using quinhydrone after the
method of Effenberger (1967). The pH system was standardized

using pH 7.0 and pH 10.0 solutions.. Probes were recharged whenever
they could not be standardized. Eh was converted to E7 following
Mortimer (1941).

Percent transmittance of light was measured near mid-day at
weekly intervals with a submarine photometer connected to a low
resistance galvanometer (Fred Schueler, Haltham, Massachusetts).
Measurements were made at 0.25 m intervals through the depth of the
pond in two plant-free areas. These were expressed as a fraction of,
the incident light as measured at the surface with the same photocell.

Hydrologic characteristics of the pond were measured at two
or three week intervals in order to construct a water budget.
Estimates of volumes standing in the unit were obtained from a
surface-level gauge that was set to relate to a base mean depth.
Influent and effluent flow velocity was measured with a Gurley meter
centrally positioned in the fully submersed conduits at 4-hour

intervals over 24-hour cycles on the dates given in Table 1.

Volume of flow per day was obtained from the mean of these measure-
ments having negligible variance, and the cross-sectional area of
the round conduits. The estimates of total volume of influent and
effluent for the intervals between sampling dates were obtained
from these values by averaging consecutive daily measurements and
multiplying by the number of days in the interval. Evaporation and
rainfall were calculated from data of the weather station Operated
on the site. Water not otherwise accounted for in the budget was
consigned to evapotranspiration from floating and marginal vegeta-
tion and seepage loss.

Water samples for copper and cadmium analyses were taken in
three ways. Near-shore and off-shore locations were selected at
random from grid positions on the pond. Samples were taken there by
dipping an acid-washed 2-liter polyethylene bottle 0.25 m beneath
the water surface from a boat. Samples of the inflow and outflow
were taken in 2-liter polyethylene bottles from the bottom of the
standpipe structures between ponds. When a 24-hour cycle of
sampling was not done,a single bottle was filled. During twenty
four hour studies, 2-liter bottles were partially filled at four-hour
intervals, water being added in proportion to the flow-rate at each
sampling time. The bottles were refrigerated overnight. One liter
was filtered through the minimum possible number of 0.45 micron
hemiacetate millipore filters to remove particulate matter and the
associated metals. The filters were air-dried at ambient tempera-

ture. The remaining liter of each sample was treated by

freeze-drying in a Virtis apparatus. The residue was dissolved
with concentrated HNO3 and stored in polyethylene bottles.
Plant samples were collected in four ways. The hydrophyte

Lemna minor was collected quantitatively by moving through the

 

floating plants and placing a 25 cm square at random on the water.
All of the plants in the square were placed in a polyethylene bag.
Submersed species were quantitatively sampled either by randomly
dr0pping a weighted plastic cylinder (0.114 m2) and collecting the
hydrophytes originating within, or by raising an unweighted

cylinder (0.094 m2) from beneath the floating mats of Ceratophyllum
demersum and collecting the plants inside. The plants from each
quadrat were placed in individual polyethylene bags. Finally, to
obtain sufficient biomass for metal analyses, all species were sampled
wherever they occurred. The samples were returned to the laboratory
and refrigerated. The plants were washed and segregated by species,

except for the potamogetons which were a mixture of E, foliosus and

 

E, berchtoldii. In the absence of flowers or fruits these species
with similar vegetative parts were not distinguishable in material
brought to the laboratory. The plant samples were dried in a
forced draft oven at 80°C and weighed.

Benthic invertebrates were collected in two ways. Quantita-
tively, samples were taken using a 232.3 cm2 Ekman dredge and washed
in a three-step separator the same day. The invertebrates were
returned to the laboratory alive in polyethylene bottles with pond
water and refrigerated overnight. The organisms were picked from

the water and placed in acid-washed plastic petri dishes. To obtain

lO

adequate biomass for metal analysis, benthic macroinvertebrates
were picked from the wash-water of the aquatic plants and placed in
acid-washed plastic petri dishes. Organisms were dried in a forced
draft oven at 30°C and weighed. Because of small weight within
taxonomic groups, these invertebrates were composited for digestion.
The benthic fauna consisted of chironomids, snails, amphipods,
odonates, cladocerans, and notonectids.

Samples of the zooplankton were collected in two ways.
Quantitatively, the organisms were taken between 2000 and 2400 hours
with a 34.4 liter transparent plexiglass box-trap (Schlinder, 1969).
The contents of the trap were drained through a number 25-mesh (25
micron openings) nylon plankton net, placed in polyethylene bottles,
and refrigerated overnight. In the laboratory, the contents were
sieved through a number 25-mesh screen. The residue was washed from
the screen into acid-cleaned petri dishes using minimal double-
distilled water. The organisms were dried in a forced draft oven
at 30°C and weighed. The zooplankton was also sampled at two stations
between dusk (2000 hr.) and midnight (2400 hr.) using amber—bulb
light traps (Ervin and Haines, 1972). Four traps were evenly spaced
from the surface to the sediments and operated for one hour. The
contents of the four traps were pooled in a single polyethylene bag
for each station and refrigerated overnight. This material was
washed in the laboratory over a 30 mesh/inch screen. Fathead

minnows (Pimephales promelas) and sticklebacks (Eucalia inconstans)

 

 

were introduced to the Belding system in 1971 and 1972. Those taken

in the plankton traps were discarded. The zooplankton was transferred

11

to acid-washed glass beakers, dried in a forced draft oven at 30°C
and weighed. The relative proportions of cladocerans, insects, and
other groups were similar in box and light trap catches. The groups
of zoonlankton were digested in composite.

Sediments were collected by skimming a collapsed poly-
ethylene bag through the loose sediments. The mouth of the bag was
opened in the shape of a scoop with a finger in each corner. The
bag was guided just off the firm clay of the bottom. This procedure
filled the bag without inclusion of air or water from upper strata.
The bags were closed, allowed to stand overnight, and the excess
water above the settled sediments was removed by suction. The
sediments were then dried in a forced draft oven at 80°C and ground
with a wooden rolling pin to pass a 1 mm aperature stainless steel
sieve. Soil pH, percent total extractable cations, percent carbon,
and DTPA (diethylenetriaminepentaacetic acid) extractable (plant
available) metals were analyzed by the laboratory of the Michigan
State University Soil Science Department.

The general procedure for handling samples following drying,
was to grind to powder in a Wiley mill or with mortar and pestle.

A subsample was then incinerated at 500°C for 1 hour, and ash-free
dry weight was determined. A subsample was digested for total

metal content in a Bethge distillation apparatus using HNO3 and HC104.
When possible, 5.0 grams of dry material were used and taken to
50 ml final volume by addition of double-distilled water after

digestion. If less than 4.0 grams were used initially, the final

4‘

 

 

12

volume was 25 ml. The resulting solutions were analyzed for cadmium
and copper on a Perkin-Elmer 303 atomic absorption unit.

The raw data for replicate samples of water, biota, and
sediments were tested for homogeneity of variances using the F-max
test (Sokal and Rohlf, 1969), and those which did not meet this
test were converted to base-10 logarithms. After this transforma-
tion all data had homogeneous variances. Changes through time were
then tested in an analysis of variance with weeks corresponding to
treatments. Given significance, mean separations were accomplished
using Duncan's multiple range. Curve fits for all data for metal
concentration and mass for water, sediments, plants, and inverte-
brates were conducted using a polynomial regression program
available from the MSU statistical package and run on a CDC 6500
computer. The most simple curve which reflected the significant
relationships among means was selected. The curves were fitted to
remove the non-significant variability due to sampling and to pro-
duce a logical mathematical continuum between the weekly means.
Estimates for a parameter for each sampling date were taken from
the curves, and where necessary converted from the logarithmic mean
to the arithmetic mean by: arithmetic mean = antilog (log Y + EMS/2),
where EMS is the error mean square from the analysis of variance
associated with the curve fitted to the original data.' These means
were used to compute budgets for copper and cadmium in the pond
from June 6 to September 27. After accounting for gains and losses
of each metal in the functional components that were samples in the

pond system, the amounts sedimented were obtained by subtraction.

13

Finally, a set of 31 variables were compared using simple

correlation coefficients.

RESULTS

Features of the Environment

 

Sampling for this study began with visual confirmation of
germination of the vascular hydrophytes from over—wintering tissue.
This occurred in late May of 1973. Water temperatures for the
sampling period of May 23-September 27 are recorded in Tables Al
and A2 of the Appendix. On May 23, they were in the range of 15°C-
16.5°C. For the period of the study as a whole, the median
temperature at the surface of the pond was 23.8°C; the recorded
maximum was 28°C. The temperature at the sediment-water interface
reached a maximum of 27°C with a median of 22.8°C. Being well
exposed to the wind, the pond was generally homothermal. At the
close of sampling on September 27, water temperatures were in the
range 18.5°-21°C.

Measurements of the vertical dissolved oxygen profile
illustrate the aerobic nature of the pond (Appendix: Tables A3 and
A4). The upper l m of water was consistently well aerated. The
dissolved oxygen concentration in this layer averaged 9.9 mg/l
during the study. It was never less than 2.5 mg/l, and did not
fall below 5 mg/l for more than eight hours during any of the 24-
hour observation periods. In the layer from 1 m to the surface of
the sediments, concentrations of oxygen were less than in the water

above. At the sediments, 2 mg/l or less were most frequently

l4

15

observed. However, complete oxygen depletion did not occur for
longer than four hours during any sampling period, and concentrations
of less than 1 mg/l did not persist throughout any of the 24-hour
periods. Oxygen concentrations were transient and generally lowest
at the surface of the sediments during the period of maximum standing
crop of macrophytes. The aerobic regime of the pond is suggested in
Table 2 where the mean values for vertical oxygen profiles taken near
the end of the non-photosynthetic period (0400 hours) on each 24-
hour sampling date are presented.

During 24-hour cycles of measurement, the E7 of the surface
1 m of the pond was consistently in the range of 0.2v to 0.6v
(Appendix: Tables A5 and A6). Occasionally during early morning E7
in this layer ranged from 0.1v to 0.0v. Values in this range were
never found to exist for more than eight hours. Concurrent changes
in the temperature and dissolved oxygen profiles suggest that such
low redox conditions in the upper water were induced by wind-driven
mixing of the previous day that circulated reducing substances (e.g.,
organic acids of decomposition) from the bottom stratum. Potentials
from 1 m depth to the bottom of the pond were lower than in the
water above and were more variable with time. Values in the range
of 0.2v to 0.5V were most often observed, but measurements of 0.0v
to -0.1v were also found.

A record of pH was made while measuring electrode potentials
in order to correct the latter to a pH of 7 in the manner of
Mortimer (1941). The pH of the pond was within a range character-

istic of photosynthetically active systems (Appendix: Tables A7 and

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17

A8). Over the season of sampling 78 percent of the pH measurements
made at each of four depths in the upper 1.5 m of the pond were in
the range of 8.7 to 9.8. Values falling outside of this range were
predominately lower. Measurements made at the surface of the
sediments were more variable over time during the 24-hour studies
than in the water column. Forty-one percent of the measurements
made at the mud-water interface over the season were in the range
of 7.0 to 8.0. The range 8.0 to 9.0 was encountered in the same
percentage of cases. The remaining measurements were equally
divided in the < 7.0 and > 9.0 portions of the scale.

The light regimes in macrophyte-free portions of the pond
are shown in the data of Table 3. While penetration was somewhat
variable over time, a trend related to the time of vascular
hydrOphyte development and scenescence was present. The plants
began to grow from the bottom as light penetration improved in the
May 23-June 6 interval. During the time of rapid development of
the maximum standing crop (June 6-August 15), light penetration was
generally greatest; as the macrophytes senesced (August lS-September
26), it declined. Extinction coefficients (n2 = 1n Io - 1n 12
where z is depth and I is intensity) calculated for the pond can be
compared with the range of values observed for lakes. Very clear
lakes, such as Crater Lake, Oregon and Lake Tahoe, California have
extinction coefficients near 0.2 per meter; highly stained lakes or

those with dense phytoplankton blooms have values near 4.0 (Wetzel,

1975).

18

TABLE 3.--The penetration of light in Pond 4 of the Belding wastewater
system in l973.

 

 

 

Percent of Incident Light Remaining Extinction
Date Coefficient
0.25m 2.0m at 2.0 m
5/23 56 l 2.30
5/31 60 2 1.96
6/6 77 13 1.02
6/14 85 28 0.64
6/20 94 60 0.26
6/28 87 31 0.59
7/4 86 33 0.55
7/12 65 3 1.76
7/18 84 25 0.69
7/26 86 30 0.60
8/1 80 18 0.86
8/9 81 19 0.83
8/15 80 17 0.89
8/23 60 2 1.96
8/30 68 4 1.61
9/5 72 7 1.33
9/13 60 2 1.96
9/20 70 6 1.41
9/26 78 12 1.06

 

19

Unconsolidated sediments, ranging in thickness from 10 to
25 cm, were found to occur over the clay seal of the pond. The
physical appearance of the sediments changed over the growing
season. An orange-brown layer several millimeters thick existed
at the water interface when intensive sampling was begun in early
June. Going deeper, the color changed abruptly to black that con-
tinued to the clay. Although specific sediment element forms were
not determined, these visual differences were presumably due to the
presence of an oxidized microzone at the water interface colored by
a preponderance of ferric hydroxide, and beneath it, an anoxic
layer that owed its black color to an abundance of ferrous sulphide
(Wetzel, 1975; Ruttner, 1963; Mortimer, 1942). The discrete orange-
. brown boundary layer was disrupted and displaced during June by
development of a low shrubby layer of vegetation dominated by the
profusely branching vascular hydrophyte, Ceratophyllum demersum.
A presumed ferric iron floc occurred on the surfaces of the inter-
twined vegetation at that time. Simultaneously, the ferrous iron
layer was exposed to the water in the depressions of the lattice-
work formed by branches and leaves immediately adjacent to the soft
sediments. This heterogeneous pattern persisted in the vegetation
along the bottom of the pond through September 27. Placement of
the dissolved oxygen probe or the platinum Eh electrode when lowered
to the region of the oxidized-reduced microzones of the early season
sediments, or later, into the labyrinth of plant tissues along the
bottom was the cause of variability in the record of these measure-

ments at the sediment-water interface.

20

Table 4 shows copper and cadmium concentrations found in
the top 2-4 cm of pond sediments. While both of the metals showed
an increase in the sediments during the May 31-August 15 interval,
and a decrease from August 15 to September 26, the differences in

concentrations were not statistically significant.

Copper and Cadmium Budgets

 

Development of a water budget for the pond was essential to
describing the seasonal dynamics of copper and cadmium. The data
for such a budget are presented in Table 5. Using the tabled
estimates of volume of the pond and rates of flow, the unit had a
mean retention time of 32 days. Its volume was displaced approxi-
metely four times during the study. Over the season, inflow
slightly exceeded outflow, evaporation exceeded rainfall, and
seepage and transpiration were minimal.

Table 6 concerns the partitioning of copper in the pond's
influent among four functional components of the pond during
intervals of two or three weeks through the growing season. The
partitioning coefficients were calculated as the amount of metal
gained or lost by a compartment during the interval divided by the
amount of metal in the influent in the same period.

1he rate at which copper entered the pond decreased from an
early season high to a minimum in late July. It then increased
over the remainder of the season. The rate at which copper left the
pond followed a similar pattern. The concentration of copper

measured in the influent water was highest on June 6 (10.5 pgm/l),

21

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22

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mwo.um mp\w

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moo.m I mo~.N mum.P Pon.mm 0Nu.mm mm0 I
muo.mm m~\u

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Iooe>m

 

Eoumxm Lopezopmez mswu—om esp mo u usos sow Amsoump

.mump 0o someem mswzosm esp mswsou

m

o_ x Ae=_e>v eAeu oesoposussII.m momsh

23

TABLE 6.--The partitioning of influent cooper among functional
compartments in Pond 4 of the Belding, Michigan waste
treatment system for intervals of the growing season, 1973.

 

Coefficients of Partitioninga

 

 

Inflow
Interval gm/day Outflow Storageb Biota Sediments
6/6 - 6/20 18.7 0.90 -0.21 0.0 0.31
6/21- 7/4 11.1 0.90 -0.05 0.03 0.12
7/5 - 7/18 5.1 0.62 0.06 -0.05 0.37
7/19- 8/1 3.7 0.74 -0.14 -0.28 0.68
8/2 - 8/15 4.0 1.35 -0.31 -0.02 —0.02
8/16-9/5 4.3 1.39 -0.11 -0.08 -0.20
9/6 - 9/27 4.9 1.43 —0.24 0.02 -0.20
Season's
Values
(total gms) 790. 806 -119 -16 119

 

aThe fraction of the influent for the interval that was
accumulated or lost from a compartment.

bChange in cooper in the total volume of water in the pond.

24

declined to a minimum of 1.8 pgm/l in early August, then increased
to 2.7 ugm/l on September 27. The effluent concentrations were
9.4-9.9 pgm/l in June, reached a minimum of 1.3 pgm/l in mid-

July, and gradually increased to 4.6 ugm/l in late September
(Appendix: Tables A9 and A10). Total grams of copper entering and
leaving the pond on each 24-hour sampling date are given in Table
All of the Appendix. The efficiencies for the pond in reducing the
copper concentration in the water, as measured on dates of 24-hour
sampling, are shown in Table 7.

The volume of water in the pond and the concentration of
copper in the water decreased through the season (Appendix: Tables
A9 and A10). These factors in combination caused the fluctuations
in the coefficients of partitioning shown in Table 6 for copper
storage within the pond. On June 6 there were 174 gm of copper in
the water; 55 gm were present on September 27.

Table 6 demonstrates a low level of participation of the
biota in the net copper dynamics of the system, relative to the out-
flow, sedimentation and storage, except for the mid-season interval
of July l9-August 1. Copper loss from the aquatic plant community
during this interval was particularly high (Table 8). The biota
as a whole contained in the range of 45-50 gm of copper during the
first one-half of the season (Table 9). Its content then gradually
diminished to 26 gm on September 27. Table 6 shows that the net sedi-
mentationtyfcopper was positive for the first one-half of the season,
and negative thereafter. For the season as a whole, 118 gm of

copper were sedimented over 3.0 ha of pond. However, the pond

25

TABLE 7.--Re1ationships between the total quantities of copper
and cadmium in the inflow and outflow of Pond 4 for the
24-hour period on the date given.

 

(Inflow-Outflow/

 

 

 

gm Inflow-gm Outflow Inflow) x 100
Date
Cu Cd Cu Cd

6/6 2.1 1.4 10.3 38.9
6/20 1.6 1.0 9.4 33.3
7/4 1.0 0.3 15.9 16.8
7/18 2.1 0.8 58.3 42.1
8/1 -0.7 0.3 -1.9 13.0
8/15 -1.8 0.2 -45.0 11.8
9/5 -1.6 -0.2 -34.0 -10.0

9/26 -2.2 0.4 -46.8 15.4

 

26

 

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27

TABLE 9.--Tota1 grams of copper and cadmium in the pond volume, the
biota, and the vascular hydrophytes on each 24-hour
sampling date.

 

 

 

 

 

Vascular
Pond Volume Biota Hydrophytes

Date
Cu Cd Cu Cd Cu Cd
6/6 173.9 82.0 45.0 0.7 38.3 0.5
6/20 118.7 80.5 44.5 1.8 43.6 1.7
7/4 110.3 60.6 49.6 2.5 49.1 2.4
7/18 114.5 49.0 46.3 3.0 45.8 2.9
8/1 107.2 56.6 32.0 3.3 31.7 3.2
8/15 90.3 54.1 30.8 4.2 30.6 4.1
9/5 80.3 30.1 23.7 4.1 22.8 4.0
9/26 55.1 51.9 25.6 3.2 25.0 3.1

 

28

lost more copper in the effluent than it received in the influent
due to the decrease in the copper held in the pond volume.

In Table 8, the net amount of copper gained or lost by five
components of the existing aquatic community is partitioned for
intervals of the season. Among these, the population of the

vaScular hydrophyte Ceratophyllum demersum had the largest absolute

 

content of copper at all times of the season (Appendix: Tab1e A18).
The plants held 29 gm at the beginning of the study, increased to
38 gm during the first week of July, and declined to 25 gm at
termination of sampling. These changes in the content of copper
occurred across a fifteen-fold difference in the biomass of the
plants within the pond (362 to 5,101 kg), and a difference of
similar magnitude in the concentration of copper in the plants
during the season (4.87 to 79.81 mg/kg). During mid-season, there
was a consistent net loss of copper from the population of C,
demersum.

The potamogetons completed a cycle of vegetative growth,
seed setting, senescence, and disintegration by August 1. These
plants held a total of 9 gm of copper at the start of the study
(Appendix: Tab1e A18). For the purpose of this budget, that
quantity was returned to the abiotic environment with vegetative
collapse of the population. By August 1, the reproductive parts
of these species (seeds and stem fragments) had fallen to the sediments.
These parts were estimated to be 4-7% of the mass of the mature stand of
plants. It is of interest to note that the net effect of these

low-density species amounted to one-half of the total seasonal

29

participation of the biota in the copper dynamics of the system
(Table 8).

A population of the floating vascular plant, Lemna minor,

 

grew from scattered fronds to cover portions of the pond withdense
mats of vegetation in late July and early August. The population
then diminished to near a negligible biomass on September 5. The
copper that it extracted from the water during growth to mid-July
was returned to the abiotic pond components with disintegration of
the p0pulation over the latter one-half of the period of sampling.
The seasonal net effect of this plant in regard to copper was near
zero (Table 8).

The content of copper in the benthic macroinvertebrates and
the zooplankton was strongly tied to their respective biomass shifts
and late season concentration peaks. There were 5.60 gm in the
200plankton on June 6. This fell to an observed minimum of 0.01
gm in early August, and increased to 0.85 gm one month later
(Appendix: Tab1e A21). The late season increase was caused by a
rise from 48 to 597 ugm/gm ash-free dry weight in copper concentra-
tion of the animals, rather than by a dramatic change in their
abundance. There was 1.16 gm of total capper in the benthic macro-
invertebrates in early June. This gradually diminished to 0.06 gm
in early September, and rose by an order of magnitude (0.53 gm) on
September 27 (Appendix: Table A24). As with the zooplankton, an upturn
in the copper concentration in the animals was again noted on September 5.
These dramatic changes in concentration may be of considerable biological

interest, but had little influence on the budget of the pond.

30

The partitioning of the total cadmium inflow to the pond
among the four principal compartments measured is shown in Table 10.
Total grams of cadmium entering and leaving the pond on each 24-hour
sampling date are shown in Table All of the Appendix. Except from
June 6 to June 20, the rate of cadmium input was relatively con-
stant near 2 gm/day. The rate of output in the effluent declined
during the first three intervals of measurement (2.07 gm/day,
1.69 gm/day and 1.29 gm/day, respectively), then gradually increased

until September 27 (1.58, 1.74, 1.80 and 2.31 gm/day in sequence).

Changes in the daily efficiency of the pond in removing cadmium
were related to these relationships (Table 7). Similar to the
case for copper, the change in calculated storage of cadmium
within the pond was influenced by changes in concentration and
water volume. There were 82 gm of cadmium in the water of the
pond on June 6, in the range of 50 to 60 gm in mid-season, and
30 gm on September 5 (Table 9). The combined effect of the biota
and the sediments was to accumulate cadmium within the pond until
late in the growing season. For intervals of the season and for
the season as a whole, the sediments served as the principal trap
for cadmium. Eighty-three percent of the influent cadmium left the
pond in the effluent.

The rates of cadmium gain or loss by the biota are given in
Table 11. The most significant interaction in the biota with the
cadmium budget of the pond occurred in the population of the sub-

mersed plant, 9, demersum.

31

TABLE 10.--The partitioning of influent cadmium among functional
compartments in Pond 4 of the Belding, Michigan waste
treatment system for intervals of the growing season,

 

 

 

l973.

Inflow Coefficients of Partitioninga
Interval m/da

g y Outflow Storage Biota Sediments
6/6 - 6/20 3.29 0.63 -0.03 0.02 0.38
6/21- 7/4 2.29 0.74 -0.62 0.02 0.86
7/5 - 7/18 1.82 0.71 -0.46 0.02 0.73
7/19- 8/1 2.11 0.75 0.26 0.01 -0.02
8/2 - 8/15 2.02 0.86 -0.09 0.03 0.19
8/16- 9/5 1.86 0.97 -O.62 -0.00 0.65
9/6 - 9/27 2.16 1.07 0.48 -0.02 -0.54
Season's
Values
(total gms) 246 204.2 -29.5 2.4 68.9

 

aThe fraction of the influent for the interval that was

accumulated or lost from a compartment.

32

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musesoosoo 0soEe eposs esp As uommoooss me: uesp Eossueo seeop ems use so osssospsuseo ossII.__ msm<s

33

Biotic Interactions With
Copper and Cadmium

 

 

Figure 2 shows how the total macrophyte community behaved
for the growing season with respect to total kilograms of ash-free
dry weight in the pond and concentrations of copper and cadmium in
the tissues. The standing crop of aquatic plants increased until
August 15 and decreased thereafter. 9, demersum dominated the
general trend and magnitude of the biomass curve. Changes in the
biomass of L, miggr_and the potamogetons were relatively small and
did not disrupt the trend shown in the figure for the plant com-
munity as a whole. The total quantity of cadmium held by the macro-
phytes followed their biomass because of its relatively constant
concentration in the plant tissues. The rise in the total copper
content of the plants in the beginning of the growing season was
influenced by the high rate of biomass increase, rather than by the
significant decrease in copper concentration that was occurring simul-
tanesouly in the macrophyte tissue (Figure 3). After July 4, the
growth rate began to decrease and the tissue concentration continued
to fall rapidly; total amount of copper in the plant community
decreased. After September 5, an increase in the concentration in
the macrophytes resulted in a slight upturn of total copper content.

Figure 3 shows two types of copper concentration behavior
for the macrophytes. The submersed plants, 9, demersum and the

Potamogeton spp., began on June 6 with high copper concentrations

 

and decreased steadily during the period of growth and early

senescence. An upturn in metal concentration occurred in late

34

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35

 

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36

senescence of both taxa. The data point for C, demersum in

December (Figure 3), suggests that over-winter the capper concentra-
tion in the tissues would return to the high value of the previous
spring. For the submersed species, June and December values for
copper concentration were significantly different (p < 0.05) from
those of July, August and September (Appendix: Table A26).

L, nfinoE, a floating vascular plant, possessed increasing tissue
concentration of copper during the period of total biomass increase
and decreasing tissue concentration during biomass decrease after
7/18.

Copper and cadmium concentrations in the zooplankton and
benthic macroinvertebrates were very similar (Appendix: Tables A21
and A24). The copper concentration in both groups declined to a
minimum on August 1 (20.27 and 15.01 ugm/gm, respectively), increased
to a maximum on September 5 (597.10 and 19.20 ugm/gm, respectively),
and then decreased on September 27. The cadmium concentration in
benthic macroinvertebrates reached a maximum on August 16 (7.6 ugm/
gm) and declined to September 27. The zooplankton cadmium concentra-
tion also peaked on August 16 (1.74 ugm/gm) and decreased thereafter.

The metal concentration of the pond water divided into the
concentrations of the biotic components of the pond, are presentedirI
Table 12 as concentration factors. The table shows concentration
factors for the dates of each 24-hour study. These factors for
copper in C, demersum and the potamogetons decreased through time
with a slight upturn at the end of the season (September 27). The

copper concentration factor for L, minor doubled between June 6

37

 

 

 

 

 

 

 

 

 

 

 

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38

and July 4 and decreased thereafter to the end of sampling. The
cadmium concentration factors for species in the plant community
were less stable in trend, but tended to peak near September 5.
Copper concentration factors for invertebrates, both benthic macro-
invertebrates and 200plankton, peaked on June 20 and September 5.
Cadmium concentration factors for zooplankton peaked on September 5,
and for benthic macroinvertebrates on August 18.

Simple correlation coefficients between variables sug-
gest patterns but not cause and effect relationships between
variables. When macrophyte copper concentration was examined, it

was found that for C, demersum and Potamogeton spp., there were

 

simple correlation coefficients (r2) with the influent and effluent
copper concentrations which were significant at the 99% level.
Benthic macroinvertebrate copper concentrations also had a 99%
level of significance with the influent and effluent capper con-
centrations. The submersed macrophyte copper concentrations versus
the pond water copper concentrations were significant at the 99%
level.

For the plant community, the relationships between total
standing crops of two species would demonstrate species compati-
bility. The total kilograms of organic material in the pond for

the g, demersum and the Potamogeton spp. had a negative correlation

 

significant at the 95% level.
A Comparisons between the total biomass and metal concentra-
tions of the biotic compartments would reveal the link between

organic matter production and metal metabolism. The biomass and

39

copper concentration quantities for C, demersum were negatively
related at the 99% level. The same comparison for L, nflflg§_was
positively related at the 95% level.

Comparisons of the metal concentrations in biotic compart-
ments show whether the biotic groups behave similarly in regard to
a metal. The copper content of C, demersum and the Potamogeton spp.

were significantly positively related at the 99% level.

DISCUSSION

Environmental conditions in ponds receiving untreated
municipal wastes have been well described in the American literature
in the years since the pioneering work of MacKenthun and McNabb
(1961), Fitzgerald and Rohlich (1958), Bartsch and Allum (1957),
Caldwell (1946), and Gillespie (1944). Authors have dealt with
ponds heavily loaded with organic wastes. These are characterized
by high rates of algal photosynthesis and bacterial respiration,
high turbidity, poor light penetration, broad fluctuations in the
dial pH and dissolved oxygen profiles, periodically anaerobic water
columns, and anaerobic sediments with low (< 0.2V) redox potentials
at their surface. The environmental conditions in ponds of waste-
water systems where submersed vascular plants, rather than
planktonic algae, are the dominant primary producers in the
temperate growing season, have not been well described in the
literature. The fourth pond in the series of five serving Belding,
Michigan was such a pond at the time of this study. Data are pre—
sented to characterize it as a low turbidity pond with very good
light penetration over most of the season. Diel fluctuations in
the pH and dissolved oxygen profiles were moderate; the water
column was continually aerobic. The surface of the sediments

tended to have redox potentials in excess of 0.2V.

40

41

Net changes in capper and cadmium over two or three week
intervals were used to construct budgets for these elements.
Measurements were made of the amount of each element flowing in and
out of the pond, the gain or loss from the water of the pond, and
the gain or loss from the aquatic plants, 200plankton, and benthic
macroinvertebrates. An estimate of the interaction of the metals
with the sediments was made by bringing the sum of the above
changes to zero.

The quantities of copper and cadmium handled by the
invertebrate fauna of the pond were found to be insignificant
portions of the total budgets. The aquatic plants served as a trap
for copper for approximately one month following initiation of
growth in early June. Twenty-four hour measurements on the influent
and effluent at that time showed that the pond had a copper removing
efficiency, calculated as

Cu. - Cu

( Incu. OUt) X 100
1"

 

on the order of 10%. The plant community accumulated one-quarter
the amount of copper necessary to achieve this percentage reduction,
while the sediments accumulated eight times the amount taken up by
the plants. The copper over and above that in the influent that was
trapped by these processes was removed from the water of the pond.
The concentration in the water and the total quantity of copper

present in the pond dropped over this early seasonal interval.

42

In the month of July when the aquatic plants were growing
most rapidly, they lost copper from their tissues. By calculations
of the budget, this copper went into the sediments; the concentra-
tion of copper in the water of the pond did not increase during
this loss. Taken as a whole, the sediments trapped copper during
this time at a rate that was 50% of the rate at which the element
was entering the pond in the wastewater. The pond as a whole had
a measured removal efficiency of near 38%.

In early August, the efficiency of the pond for copper
removal fell to zero. Thereafter until the study was terminated in
late September, more copper left the pond in the effluent than
entered it; 4.4 gm/day influent, 6.1 gm/day effluent. Continued
loss of copper from the aquatic plants, now in senescence, and
ineffective sedimentation of copper are implicated in this loss.

For the season as a whole, the efficiency of the pond for
copper removal was close to zero (-2% removal). The plant community
showed a net loss equivalent to 2% of the total copper received by
the pond in the influent. The sediments trapped a quantity of
copper equivalent to the difference between the total quantity of
copper standing in the water of the pond at the beginning and the
end of the study. In this particular case, that amounted to 4 mg
of copper per square meter of pond bottom, or 15% of the amount
that flowed in to the pond during the growing season.

The seasonal pattern of cadmium accumulation and loss was
different from that for copper. The aquatic plant community and

the sediments trapped the element during the period of growth from

43

early June to mid-August. In that time, the rate of cadmium inflow
to the pond was relatively constant, averaging near 2 gm/day. The
concentration and the total amount of cadmium in the water of the
pond dropped as a result of cadmium deposit in the plants and
sediments. Together they accumulated an amount equivalent to 45%
of the amount in the influent. The major portion (94%) of this was
gained by the sediments. The efficiency of removal for the pond
during this interval averaged near 26%.

From mid-August through late September, the rate of cadmium
input to the pond remained at 2 gm/day, while the output increased
over the earlier period to reduce the pond's efficiency to zero.
During this time, the senescing plant community lost cadmium, while
the volume of water in the pond and the sediments together had no
net gain or loss.

For the June through September season, the pond had an
efficiency for cadmium removal of 17%. 0f the amount that was
trapped, the plant community held 6% in late September with the
remainder in the sediments. The sediments in addition received
the difference between the total quantity of cadmium in the water
standing in the pond at the beginning and the end of the study
(30 gm). For this particular case, the total accumulation in the
sediments amounted to 2.3 mg of cadmium per square meter of pond
bottom, or 28% of the amount in the influent over the period of
study.

Bulthuis gL_gl, (1974) showed that, for the season, copper

was trapped in this pond and cadmium was not. This study was

44

contradictory. However, major vegetational changes occurred
between the two studies. Bulthuis et a1. (1974) present data to

show that Potamogeton foliosus grew in beds that covered 57% of the

 

area of Pond 4 in the Belding treatment system in September of 1972.
Q, demersum existed over 39% of the pond in that year. The species
grew in mutually exclusive beds. McNabb (1976), from observations
of 30 systems of oxidation ponds in Michigan, concluded that

E, foliosus and E. berchtoldii are pioneer species of plants in

 

these ponds, and are displaced by 9, demersum or Elodea canadensis

 

as the ponds age. The study of this present paper was done in a
year in which such a displacement was in progress. Additionally,
the sampling intervals of the two studies were not identical.

Hence, apparent contradictions may be artifacts of biotic shifts

and sampling schedules. No other studies of seasonal metal balances
in sewage oxidation lagoons were available in the published litera—
ture for comparison.

In nature, copper and cadmium occur as divalent cations when
in solution. The effects of E7 and pH in water on copper and
cadmium dynamics are primarily on their associated anions, cations,
and form changes of these.

In pond 4, from June 6 to September 27, 16% of the total
copper in water samples passed through a 0.45 micron filter. This
fraction could have been dissolved, colloidal, or chelated. For
example, Stiff (1971) showed that as the pH and alkalinity of an
aerobic system increased, the percentage of total copper present as

cupric ion decreased. At pH 8.0 and bicarbonate alkalinity of 200

45

mg/l as CaC03, which are typical summer values for the Belding pond,
cupric ion was 1.2% of the total copper present. The remainder was
precipitated or colloidal CuCO3. Stiff then theorized that the
slower formation of malachite (Cu2(OH)2CO3), a more insoluble com-
plex, controls Cu+2 availability. Stumm and Morgan (1970) propose
that tenorite (CuO), rather than malachite, controls copper
solubility above pH 7. Another possible complex of cupric ion is
chelation by organic substances. Stiff (1971), working with copper-
dosed sewage found 20-25% of the dose complexed with organic com-
pounds, 1-2% was present as CuC03, and the remainder was insoluble
inorganic compounds (malachite, cupric sulphide, or cupric cyanide).
Cheam (l973) theorized that copper and other trace elements in
natural waters would be strongly complexed by fulvic acids.
Finally, Jenne (1968) suggested that hydrous iron and manganese
oxides dominate heavy metal dynamics through co—precipitation and
sorption.

From June 6 to September 27, 17% of the total cadmium passed
a 0.45 micron filter. Cadmium has the same charge and is nearly the
same size as calcium and can substitute for it in its compounds.
Hem (1972) showed that cadmium is very soluble at pH less than 8 and
above 10. Between pH 8.9 and 10.7, cadmium carbonate dominates and
is the most insoluble form. Cadmium is not well complexed with
organic ligands. It is subject to co-precipitation and sorption
with iron and manganese hydroxides.

These possible mechanisms can be used to discuss copper and

cadmium dynamics in the water column and at the mud-water interface.

46

In pond 4, the water mass was aerobic and oxidizing over sediments
which varied from oxidizing to reducing through the season. With
respect to the isovolt point of iron, Eh = 0.25v, the sediments were
always reducing through a 24-hour sampling period from June 6 to
July 4, and again on September 27. From July 18 to September 6 the
sediments varied from oxidizing to reducing during a day. The
strongest oxidizing conditions occurred on July 18, August 1, and
August 18.

According to the above discussion, from June 6 through
September 27, the precipitation of inorganic copper and cadmium
compounds and associated iron and manganese hydroxides from the
water mass would have been expected. Simultaneous solution of the
iron and manganese hydroxides at the sediments would have occurred
in the early summer and again in late September. However, during
mid-summer iron and manganese hydroxides would not have been sub-
jected to reducing conditions at the sediments for more than 12
hours per day. Therefore the precipitation rate could have exceeded
solution and reduced the water concentration of the metals with time,
if other conditions remained stable. In addition, the reduction of
wind-induced water circulation by macrophyte populations would have
favored particle settling.

The mechanisms controlling the copper and cadmium dynamics
in pond 4 are complex and interrelated. 0f the 16% of the total
copper and 17% of the total cadmium which passed through a 0.45
micron filter, the majority was probably chelated with organic

ligand, complexed as carbonates or hydroxides, or associated with

47

iron and manganese hydroxides. Less than 1% of the total copper or
cadmium content of the pond water would have been expected as the
free cation. The free cation is thought to be the biologically
available form (Eisler and Gardner, l973; Sandholm, Iksanen, and
Pesonen, 1973; Wilson, 1972; and Nielson and Wium-Andersen, 1970).

Over the interval June 6 to September 27, 28% of the amount
of the influent cadmium was retained by the sediments; for copper
15% of the influent metal was trapped by the sediments. Data on the
sediment copper and cadmium concentrations over the growing season
agree with the theory of the affect on metal dynamics of the oxidizing
and reducing nature of the mud-water interface. From May 31 to
August 18, there were increased sediment concentration of both metals.
This was a period when the sediments were either weakly reducing
(E7 near 0.2V) or alternated between oxidizing (E7 > 0.25v) and
reducing (E7 < 0.2V) in 24 hours. From August 18 to September 27
there were decreases in the sediment concentrations of both metals.
This was a period of weak to strong reducing conditions; oxidizing
conditions at the mud-water interface were not observed.

The influence of the biota as a mechanism for trapping
elements over the entire season was minor for both metals. Cadmium
was taken up by the biota at a seasonal rate of 1% of the influent
total; copper was released at 2% of the season's influent total.

The aquatic vascular plant community was the dominant biotic
component of the system in terms of quantity of metals processed.
The data show that the yield of copper by harvest of the aquatic
plants would have been highest in this system on July 18. An

48

August 15 harvest would have resulted in the maximum yield of cadmium.
However, harvest of the aquatic macrophytes at peak periods of metal
content would have removed less than 5% of the copper or cadmium
that had entered the pond from June 6 to July 18 (copper) or from
June 6 to August 15 (cadmium).

The data of this study reveal significant biotic relation-
ships with copper and cadmium not previously reported for the
aquatic environment. The large seasonal changes in the copper
concentrations in the submersed vascular plants are one example.

For C, demersum.over-wintering terminal stem-portions 5 to 10 cm in
length had approximately the same concentration of total copper as
the sediments on which they lay at the beginning of the growing
season (ca. 75 ugm/gm). As the stems elongated into the water of
the pond by growth, whole plant copper concentrations fell to
approximately 5 ugm/gm. The water in which the new stem and leaf
itissue developed contained ca. 2 pgm Cu/l; approximately 4 orders of
magnitude less than the sediments. With disintegration of the basal
stem and leaf tissue in the fall, the stem-tips settled into the
high-copper environment of the sediments. The concentration in
these over-wintering parts in December was ca. 45 ugm/gm. It would
appear that differences in the abundance of copper in portions of
(the environment in which the plants resided from seaSon to season
influenced the concentrations found in whole plant analyses of the
tissues. The statistically significant negative correlation found
between the biomass of C, demersum and the copper content of its

tissues over the interval of sampling was probably due to a change

49

in the supply of copper available to the absorbing tissues. The
supply changed in two ways; from origin in the sediments in pre-
season (and post-season) to origin in the water, and the supply in
the water decreased over the growing season.

The copper concentrations of C, demersum and the potamogetons
were significantly positively correlated at the 99% level during the
time they co-existed. Individuals of the species of potamogetons
were first collected as small shoots in the sediments. As they
grew, new stem and leaf tissue reached the surface of the pond.

With senescence, the population collapsed and individuals fragmented
into over-wintering parts at the sediment surface. Copper concen-
trations in these plants changed in the same manner as in

g, demersum (Figure 3). Presumably, the copper concentrations in
the over-wintering tissue of both submersed plant taxa would return
to the high early summer values observed in this study in the months
subsequent to the study. Reduced sediment conditions under ice
would cause solution of various precipitated and adsorped copper
complexes. Thus copper would be more available for uptake by the
plants at the sediment surface in winter.

In a mode consistent with that described for the submersed
plants, the population of the free-floating L, @1393, having access
only to the supply of copper in the water, showed a significant
positive correlation between the concentrations in the water and
tissue. Unlike the submersed plants, however, concentration in the
tissues and biomass showed a significant direct correlation. Also,

unlike the submersed plants, the corcentration factors for copper

50

presented in Table 12 for L, mjoog, changed over the growth cycle

in the same direction as biomass while the supply (water concentra-

tion) remained relatively constant. It appears that populations of

the submersed plants and floating plants employ different strategies
regarding copper uptake from the environment.

While cadmium was distributed in the environment in a manner
similar to copper (ca. 2.5 pgm/gm in sediments and 1.4 pgm/l in water),
measurements for the three plant groups were not related in the manner
described above for copper. Reasons for this difference are not
suggested in the data. Speculations for the causes of this differ-
ence would include differences that might exist in the biological
mechanisms for the uptake of an element essential for growth (copper)
and one that is not known to be essential (cadmium). The significant
correlations of the fauna with the concentrations of copper in the
water show that the ambient water was a more important source of
copper than the sediments for this group. Such a relationship for
cadmium did not exist.

The variability of the concentration factors for metals
reported here through the season is unusual. Dietz (1972) found
concentration factors in aquatic macrophytes for Pb, Cu, Ni, Zn, Fe,
Mn, and Hg to be relatively constant over a range of ambient con-
centrations. They varied by a factor of two at most. In this study,
the copper concentration factor varied by nine-fold in C, demersum,
six-fold in the potamogetons, and four-fold in L, mfloog, However,
the data reported by Dietz were from paired water and plant samples

taken at the end of the growing season in various locations, while

51

data reported here were from samples taken at various times through
the growing season in one location. The lack of paired water and
biotic samples prevent the computation of concentration factors in
studies reporting on heavy metals in zooplankton or benthic macro-
invertebrates (Copeland and Ayers, 1972; Bryan and Hummerstone,
1971).

While biotic interactions with copper and cadmium observed
in this study are of considerable interest, the information pre-
sented is most relevant to management of sewage stabilization pond
systems. Effluents from stabilization ponds in Michigan are being
more widely used to irrigate adjacent land sites in an effort to
meet water quality discharge standards. The danger that heavy
metals in the water may inactivate land disposal areas makes it
necessary to understand the cycling of heavy metals in the ponds.
The sediments were found to be the principal trap for copper and
cadmium in the pond that was studied. However, for the growing
season as a whole, neither element was efficiently trapped. Addi-
tional investigations of this sort would enhance the accuracy of
predications regarding the loading rates on sites irrigated with

municipal wastes.

LITERATURE CITED

52

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Armstrong, W. 1964. Oxygen diffusion from the roots of some
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Baes, C. F., Jr. 1973. The properties of cadmium. Pages 29-59
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Bartsch, A. F. and 1H. 0. Allum. 1957. Biological factors in
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Bryan, G. W. and L. G. Hummerstone. 1971. Adaptation of the
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Bulthuis, D. A., J. R. Craig and C. D. McNabb. 1974. Metal
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Buscemi, P. A. 1958. Littoral oxygen depletion produced by a
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Caldwell, D. H. 1946. Sewage oxidation ponds - performance,
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Chumbley, C. G. 1971. Permissible levels of toxic metals in

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54

Copeland, R. A. and J. C. Ayers. 1972. Trace element distribu-
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Kimball, K. D. 1973. Seasonal fluctuations of ionic copper in
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APPENDIX

57

58

TABLE A-1.--Vertical temperature profiles (C°) for an
inshore station over the 1973 growing season.

 

Bottom

 

 

Depth
Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
5/23 1200 16.0 16.0 15.9 - 15.9 1.4
1600 16.5 16.3 16.2 - 15.0 1.3
2000 16.1 16.1 16.2 16.2 16.1 2.1
5/24 2400 15.5 15.5 16.0 - 16.0 1.4
0400 15.0 15.0 15.0 15.0 15.0 1.9
0800 15.0 15.0 15.0 15.0 15.0 1.5
1200 17.0 16.0 16.0 16.0 15.5 1.6
5/31 1200 16.2 16.2 16.1 16.1 16.0 1.8
6/6 1200 22.1 22.0 22.0 21.0 21.0 1.5
1600 22.5 22.5 22.5 21.5 21.2 1.9
2000 22.5 22.5 22.5 22.2 21.5 1.8
6/7 2400 21.0 21.8 21.9 21.9 21.5 1.8
0400 21.0 21.0 21.2 21.2 20.9 1.6
0800 21.0 21.0 21.0 21.0 20.9 1.9
1200 22.1 22.1 22.0 21.5 21.5 1.5
6/14 1200 26.7 25.5 25.2 24.8 24.0 1.7
6/20 1200 25.2 25.0 24.9 - 24.6 1.4
1600 26.0 25.7 25.2 24.1 23.5 1.8
2000 24.9 24.9 24.9 24.3 23.8 1.8
6/21 2400 24.0 24.0 24.0 24.0 24.0 1.8
0400 23.5 23.5 23.5 23.5 23.5 1.6
0800 23.4 23.4 23.4 23.3 23.3 1.7
1200 24.0 24.0 23.8 23.4 23.4 1.8
6/28‘ 1200 23.0 22.9 23.0 23.0 22.9 1.6
7/4 1200 23.8 23.3 23.0 22.0 22.0 1.5
1600 25.0 25.0 25.0 23.5 23.5 1.5
2000 24.0 24.0 23.5 23.0 22.0 1.8
7/5 2400 23.0 23.0 23.0 23.0 22.0 1.8
0400 24.0 24.0 24.0 24.0 23.0 1.6
0800 23.0 23.0 23.0 22.4 22.4 1.7
1200 24.6 23.8 23.2 22.8 22.1 1.6
7/12 1200 23.0 23.2 23.2 23.2 23.0 1.7
7/18 1200 24.8 24.8 23.8 23.0 23.0 1.5
1600 26.5 25.0 24.0 23.2 23.0 1.8
2000 26.2 26.0 24.5 23.2 22.7 1.6
7/19 2400 24.5 25.0 23.9 23.2 22.5 1.6
0400 23.0 22.7 23.0 23.5 23.5 1.5
0800 24.1 24.5 24.2 23.0 23.0 1.6
1200 24.8 24.0 23.9 23.3 23.2 1.8

TABLE A-1.--Continued.

59

 

 

 

Depth Bottom

Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
7/26 1200 25.0 24.9 24.0 23.0 22.8 1.6
8/1 1200 24.5 23.5 23.0 23.0 23.0 1.5
1600 25.5 24.0 23.5 22.5 22.0 1.7
2000 24.5 24.5 23.5 22.5 22.5 1.5
8/2 2400 23.5 23.5 23.5 23.5 23.0 1.8
0400 22.5 23.0 23.0 23.0 23.0 1.6
0800 22.0 22.5 22.5 22.5 22.5 1.7
1200 23.5 23.0 23.0 22.7 22.7 1.5
8/9 1200 27.0 27.0 26.0 - 25.0 1.2
8/15 1200 25.0 25.0 24.5 24.0 24.0 1.5
1600 28.0 27.0 25.9 25.0 24.2 1.8
2000 28.0 27.5 25.5 - 24.5 1.4
8/16 2400 25.1 25.5 25.5 24.5 24.5 1.5
0400 23.9 24.0 24.1 24.5 24.5 1.5
0800 23.5 24.0 24.0 24.0 24.0 1.5
1200 25.5 25.2 25.0 24.5 24.5 1.5
8/23 1200 22.0 22.0 21.8 21.8 21.8 1.5
8/30 1200 26.0 25.5 25.5 25.0 25.0 1.5
9/5 1200 25.4 25.4 25.2 25.1 24.9 1.7
1600 26.5 26.2 26.1 25.3 25.3 1.5
2000 25.3 25.3 25.2 - 24.9 1.3
9/6 2400 25.1 25.1 25.1 25.1 25.1 1.9
0400 26.9 27.0 27.0 27.0 27.0 1.6
0800 23.1 23.2 23.3 - 23.5 1.4
1200 24.0 24.0 24.0 - 24.0 1.3
9/13 1200 19.2 19.2 19.0 - 18.9 1.3
9/20 1200 14.4 14.4 14.2 - 14.2 1.4
9/26 1200 20.0 19.9 19.5 - 18.0 1.3
1600 20.9 20.2 18.5 17.5 17.5 1.5
2000 22.3 22.4 20.5 - 19.1 1.3
9/27 2400 20.8 20.4 19.3 18.7 18.7 1.5
0400 21.0 21.0 20.7 19.1 19.1 1.5
0800 20.3 20.3 20.1 - 18.7 1.4
1200 20.2 20.1 19.9 19.0 18.5 1.6

 

60

TABLE A-2.--Vertica1 temperature profiles (C°) for an
offshore station over the 1973 growing season.

 

 

 

Depth Bottom
Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)

5/23 1200 16.0 16.0 16.0 16.0 15.0 2.1
1600 16.5 16.4 16.3 16.2 15.3 1.6

2000 16.2 16.2 16.2 16.2 16.0 2.0

5/24 2400 15.0 16.0 16.0 16.0 16.0 2.1
0400 15.0 15.0 15.5 15.5 15.5 1.6

0800 15.0 15.1 15.1 15.0 14.9 2.3

1200 17.5 17.0 17.0 17.0 15.0 1.8

5/31 1200 15.3 15.3 15.2 15.1 15.1 1.8
6/6 1200 22.0 22.0 22.0 22.0 22.0 1.7
1600 23.0 22.9 22.9 22.8 20.8 2.1

2000 22.5 22.5 22.5 22.0 21.0 2.0

6/7 2400 21.1 21.8 21.8 21.9 21.5 1.8
0400 21.0 21.0 21.2 21.2 18.6 2.5

0800 21.0 21.2 21.2 21.1 21.0 1.9

1200 22.1 22.0 22.0 22.0 22.0 2.0

6/14 1200 26.0 25.8 25.0 24.8 24.0 2.0
6/20 1200 24.9 24.8 24.8 24.2 23.2 2.4
1600 25.2 25.2 25.2 24.5 23.8 1.8

2000 25.0 24.9 24.9 24.9 23.2 2.1

6/21 2400 24.0 24.2 24.5 24.5 23.9 1.9
0400 23.0 23.5 23.5 23.5 23.0 2.0

0800 23.2 23.3 23.3 23.2 23.2 2.0

1200 24.0 24.0 24.0 23.8 23.8 1.9

6/28 1200 23.0 23.0 23.0 23.0 21.5 2.4
7/4 1200 24.0 23.5 23.2 22.0 21.0 1.9
1600 25.0 25.0 24.0 23.0 21.0 2.0

2000 24.0 24.0 23.5 23.0 22.9 2.0

7/5 2400 23.5 24.0 24.0 22.0 22.0 2.1
0400 24.0 24.0 24.0 24.0 21.0 2.1

0800 23.0 23.0 23.0 22.0 20.0 2.3

1200 24.5 24.0 23.0 22.7 20.4 2.3

7/12 1200 23.3 23.3 23.3 23.3 22.0 2.2
7/18 1200 25.0 24.8 24.0 23.8 22.8 1.9
1600 26.5 25.0 24.0 24.0 22.5 2.0

, 2000 26.5 26.5 24.5 23.5 23.0 1.7
7/19 2400 24.9 24.2 23.5 23.0 22.5 2.1
0400 23.6 24.0 24.0 24.0 23.0 1.8

0800 24.2 24.5 24.4 23.0 23.0 1.6

1200 25.0 24.8 24.8 24.2 21.2 2.4

TABLE A-2.--Continued.

6]

 

 

 

Depth Bottom
Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
7/26 1200 25.0 24.9 24.5 23.0 22.0 1.9
8/1 1200 25.0 24.0 23.5 23.0 22.5 1.7
1600 25.5 24.0 23.5 22.5 22.0 1.7
2000 24.5 24.0 23.5 22.0 22.0 1.5
8/2 2400 23.0 23.5 23.5 22.0 22.0 1.6
0400 23.0 23.0 23.0 22.5 22.0 1.7
0800 22.2 22.8 22.9 22.9 22.0 1.9
1200 23.5 23.0 23.0 22.5 22.0 1.9
8/9 1200 26.0 26.0 26.0 24.5 23.0 2.0
8/15 1200 26.0 25.0 24.5 24.2 24.0 1.9
1600 28.0 26.5 25.5 24.5 23.0 2.3
2000 27.2 27.2 26.0 24.5 24.5 1.6
8/16 2400 25.5 25.5 25.0 24.0 24.0 1.5
0400 24.0 24.1 24.2 24.2 24.2 1.8
0800 23.5 24.0 24.0 24.0 23.5 1.8
1200 26.0 25.0 24.8 24.2 24.0 1.8
8/23 1200 22.0 22.0 21.8 21.6 21.4 2.0
8/30 1200 26.0 25.0 26.0 26.0 23.0 2.5
9/5 1200 25.4 25.4 25.2 25.2 25.0 1.8
1600 26.5 26.0 26.0 25.0 25.0 1.8
2000 25.5 25.5 25.6 25.2 25.2 1.5
9/6 2400 25.0 25.2 25.2 25.2 25.2 1.8
0400 26.5 27.0 27.5 27.2 27.2 1.9
0800 23.4 23.9 23.9 23.9 23.9 1.8
1200 24.0 24.0 24.0 24.0 23.0 1.7
9/13 1200 19.2 19.0 19.0 19.0 19.0 1.9
9/20 1200 14.2 14.2 14.2 14.0 14.0 1.7
9/26 1200 20.0 19.5 19.0 17.5 17.0 2.0
1600 21.0 21.0 20.8 18.2 17.5 1.8
2000 23.1 23.1 21.2 18.1 18.1 1.5
9/27 2400 21.0 21.1 20.8 19.1 18.1 1.7
0400 20.9 20.8 20.5 18.9 17.7 2.0
0800 20.3 20.1 20.0 18.2 17.1 2.0
1200 20.1 20.1 19.8 19.5 16.5 2.1

 

62

TABLE A-3.--Vertica1 dissolved oxygen profiles (mg/L) for
an inshore station over the 1973 growing

 

 

 

season.
Depth Bottom

Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
5/23 1200 8.6 8.5 8.2 8.2 7.4 1.4
1600 10.1 9.9 9.8 - 8.2 1.3
2000 9.0 8.9 8.4 8.4 5.0 2.0
5/24 2400 7.6 7.5 7.5 - 5.4 1.4
0400 6.5 6.6 6.5 6.4 1.8 1.9
0800 7.2 7.0 7.0 5.0 5.0 1.5
1200 8.0 7.6 7.4 4.7 2.8 1.6
5/31 1200 6.4 6.4 6.1 6.1 5.8 1.8
6/6 1200 6.9 6.8 6.8 4 5 4.5 1.5
1600 7.8 7.7 7.6 8.8 2.4 1.9
2000 8.8 9.0 8.6 14.5 4.2 1.8
6/7 2400 7.6 7.5 7 5 7.3 1.3 1 8
0400 7.0 6.6 6.5 6.2 4.2 1.6
0800 6.8 6-8 6.6 6.6 5.4 1.9
1200 8.4 8.6 8.8 5.7 5.7 1.5
6/14 1200 11.8 12.1 12.2 8.6 4.0 1.7
6/20 1200 11.1 11.4 11.4 - 1.4
1600 11.8 11.8 12.1 11.9 5.3 1.8
2000 12.3 12.0 11.9 7.6 1.8 1.8
6/21 2400 10.0 9.8 9.8 3.7 2.7 1.8
0400 10.0 9.7 7.5 6.5 6.1 1.6
0800 10.0 10.0 10.1 6.6 8.7 1.7
1200 6.8 6.3 6.8 6.3 3.5 1.8
6/28 1200 10.0 10.4 11.0 9.0 5.0 1.6
7/4 1200 14.4 13.5 10.6 1.9 1.9 1.5
1600 16.5 16.5 17.2 7.5 7.5 1.6
2000 14.5 14.0 7.5 7.5 2.1 1.8
7/5 2400 12.5 12.5 12.5 9.8 2.5 1.8
0400 14.0 13.5 10.5 6.2 1.2 1.6
0800 10.8 11.2 8 6 2.4 2.0 1.7
1200 16.2 14.0 10.7 3.0 2.0 1.6
7/12 1200 10.4 10.0 10.2 9.8 8.5 1.7
7/18 1200 10.7 10.6 6.6 1.2 1.2 1.5
1600 13.6 14.2 12.8 7.6 6.4 1.8
2000 16.2 16.1 14.1 7.8 3.2 1.6
7/19 2400 12.8 12.2 11.6 8.2 4.8 1.6
0400 11.0 11.0 10.0 7.6 7.6 1.5
0800 11.4 12.2 11.8 1.6 1.2 1.6
1200 7.1 6.4 6.1 3.2 1.2 1.8

63

TABLE A-3.--Continued.

 

Bottom
Depth

Depth

 

Time

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

1.6

0.8

1200 10.

7/26
8/1
8/2

5758675

1111111

8212525

602621

8518435

602991

65nU.6rnwrnwz
8~/.—/.0.9n/.5

89576nU.5

O O O 0.
9120935
111

8508815

I O. O O O 0
8420937
111

1200
1600
2000
2400
0400
0800
1200

10 10.

1200

8/9

5845555

1111111...

2262876
. o o o o o 0
6020709
11.
26 2876
o o— o o o o
62 0709
l 1
2360032
1573091
11 ll 1
8088946
0 O O O O O 0
0523090
11111.1 1
0644718
0433090
11111 1
0000000
0000000
2604482
1122001
5 6
l l
/ /
8 8

1200 9.

8/23

11.0 10.9

1200 9.9

8/30

7639643

1111111

8000474..

012455r0.

4560222

0 I O 0
6299668
1

9520443

[209668
11

2420.3rnwdn

8200hrhw68
11

1200
1600
2000
2400
0400
0800
1200

9/5
9/6

10.2

9.0 9.0 10.6
8

1200

9/13

3.1

.4

1200

9/20

3535546

1111111

3686623

1451122

1229091
111 l 1
4386470
0. O C I. 0
1210091
11111 1
0000000
0000000
2604482
1122001
6 7

2 2

/ /

9 9

 

64

TABLE A—4.-—Vertical dissolved oxygen profiles (mg/L) for
an offshore station over the 1973 growing

 

 

 

season.
Depth Bottom
Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
5/23 1200 8.2 8.2 8.1 8.1 4.2 2.1
1600 8.9 8.8 8.6 8.0 2.8 1.6
2000 8.8 8.7 8.6 8.6 4.0 2.0
5/24 2400 7.5 7.5 7.4 7.4 5.8 2.1
0400 7.7 6.8 6.8 3.2 3.2 1.6
0800 7 6 7.2 6.6 6.6 3.2 2.3
1200 8.3 8.2 8.2 8.2 2.8 1.8
5/31 1200 7.8 6.0 5.9 5.9 2.0 1.8
6/6 1200 6.4 6.4 6.5 5.2 1.7
1600 8.2 8.0 7.9 8.1 2.6 2.1
2000 8.4 8 4 8.4 9.8 0.8 2.0
6/7 2400 7.8 7.6 7.4 7.4 3.3 1.8
0400 6.5 6.4 6.4 6.2 0.2 2.5
0800 6.8 6.8 6.6 6.6 5.4 1.9
1200 8.2 8.0 7.9 8.2 6.2 2.0
6/14 1200 11.5 11.4 13.0 12.7 4.8 2.0
6/20 1200 10.1 9.8 10.1 10.7 1.6 2.4
1600 11.2 11.2 11.4 15.8 9.8 1.8
2000 12.2 12.2 12.5 12.4 2.5 2.1
6/21 2400 10.4 10.2 10.3 10.2 2.6 1.9
0400 9.4 9.0 5.2 5.2 2.9 2.0
0800 8.6 8.5 8.4 8.4 3.6 2.0
1200 8.3 8.5 8.6 6.8 5.7 1.9
6/28 1200 9.8 9.7 9.7 7.5 0.4 2.4
7/4 1200 14.6 15.0 14.5 12.6 4.5 1.9
1600 15.0 15.5 15.0 10.0 2.2 2.0
2000 17.8 18.0 12.0 8.5 3.0 2.0
7/5 2400 14.0 14.0 15.0 10.0 2.2 2.1
0400 14.0 13.8 10.5 5.8 0.9 2.1
0800 12.4 12.4 11.9 11.0 0.0 2.3
1200 13.8 14.2 10.4 6.0 0.8 2.3
7/12 1200 8.9 8.8 8.8 8.2 0.7 2.2
7/18 1200 14.2 13.5 11.6 7.2 0.6 1.9
1600 13.4 13.2 11.5 11.6 5.0 2.0
2000 15.3 15.4 14.5 9.7 4.8 1.7
7/19 2400 11.2 10.8 11.4 5.8 1.2 2.1
0400 5.8 5.6 4.8 1.6 0.6 1.9
0800 12.0 12.2 12.4 1.0 0.6 1.6
1200 7.4 7.4 7.3 4.0 0.3 2.4

65

TABLE A-4.--Continued.

 

Bottom
Depth

Depth

Time

 

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

1.9

0.1

1200 9.2

7/26
8/1
8/2

7756799

1111111

5295858

1000000

5890824

100152.].

2526424

I. I O O I 0
8409964
1

5008888

0 O 0 O O 0 0
8330954
111

6502866
0 O I O O O 0

8430955
111

1200
1600
2000
2400
0400
0800
1200

1200 10.2 .

8/9

9365888

1211111

8285663

1011200

4425202
. C I O C O .
2321604
1
0064424
. C O C C .
8052109
11111
0244489
0 O O O O O 0
2443191
11111 1
0440288
0 . . O C C .
0423192
11111 1
0000000
0000000
2604482
1122001
5 6
l l
/ /
8 8

10.4 8.6

1200 10.0

8/23

9.8 9.6 .

1200

8/30

8858987

1111111

8582003

1018630

6486482

0 0
7118655

10.2

1200 8.2

9/13

1200 8.0

9/20

0857001

2111222

4868632

1541001

1
6nunu4239u3
O O I O O 0
lnzauoanZL
111111.1 1
248nu1f4042
O O 0 O O O O
0119T1nu011
11111111111
4Fo114nqdii
0119:1nu011
11111111111
OnUnuOnunuO
OnunuonunVO
2ron74na8q¢
1119:4nu011

9/26
9/27

 

TABLE A-5,--Vertical profiles of platinum electrode

66

potentials (E7 in mv) for an inshore station
over the 1973 growing season.

 

 

 

Depth Bottom

Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
5/23 1200 484 479 474 274 117 1.4
1600 388 266 250 - -72 1.3
2000 239 233 227 224 12 2.1
5/24 2400 67 61 61 - —25 1.4
0400 164 158 72 78 -20 1.9
0800 211 56 26 -96 -96 1.5
1200 323 312 179 76 -50 1.6
5/31 1200 397 386 91 96 -73 2.0
6/6 1200 351 342 338 118 118 1.5
1600 336 334 334 212 69 1.7
2000 260 253 253 198 -21 1.6
6/7 2400 220 202 116 101 10 1.7
0400 259 269 259 253 134 1.6
0800 197 46 46 1 1 1.5
6/14 1200 161 151 151 133 27 1.7
6/20 1200 320 320 318 - 269 1.4
1600 332 330 315 298 94 1.8
2000 135 183 151 149 —60 1.8
6/21 2400 94 98 89 61 -74 1.8
0400 262 217 281 289 83 1.6
0800 373 281 281 280 130 1.6
1200 245 239 239 239 163 1.8
6/28 1200 250 287 297 295 192 1.6
7/4 1200 340 348 337 140 140 1.5
1600 338 353 293 226 226 1.6
2000 210 215 178 178 70 1.8
7/5 2400 161 161 171 61 44 1.8
0400 129 130 160 2 -131 1.6
0800 102 76 101 49 -56 1.7
1200 203 230 210 187 40 1.6
7/12 1200 172 146 191 6 6 1.5
7/18 1200 633 603 566 342 342 1.5
1600 576 638 499 477 311 1.8
2000 440 375 357 151 151 1.5
7/19 2400 28 23 100 80 -166 1.6
0400 180 180 180 142 142 1.5
0800 291 306 306 243 145 1.6
1200 617 617 587 490 283 1.6

TABLE A-5.--Continued.

67

 

 

 

- Depth Bottom
Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
7/26 1200 387 377 342 203 93 1.6
8/1 1200 744 733 586 402 402 1.5
1600 602 598 567 451 337 1.7
2000 612 612 599 362 362 1.5
8/2 2400 659 485 609 578 412 1.8
0400 562 562 604 460 402 1.6
0800 514 463 463 460 367 1.7
1200 393 386 386 306 306 1.5
8/9 1200 271 292 163 - 129 1.2
8/15 1200 292 362 226 170 170 1.5
1600 460 435 342 156 76 1.8
2000 430 396 390 - 324 1.4
8/16 2400 98 79 34 -14 -14 1.5
0400 186 169 234 105 105 1.5
0800 259 250 290 5 5 1.5
1200 507 509 509 365 365 1.5
8/23 1200 224 209 198 188 188 1.5
8/30 1200 202 202 200 -164 -164 1.5
9/5 1200 366 396 320 299 194 1.7
1600 366 350 350 298 298 1.6
2000 207 210 204 - 36 1.3
9/6 2400 291 279 324 180 180 1.9
0400 234 158 232 237 164 1.6
0800 166 154 159 - 106 1.4
1200 361 373 233 - 151 1.3
9/13 1200 380 369 362 - 234 1.3
9/20 1200 405 379 392 - 249 1.4
9/26 1200 335 342 252 - 67 1.3~
1600 307 307 252 32 32 1.5
2000 331 330 192 - 105 1.3
9/27 2400 220 253 211 147 147 1.5
0400 152 142 152 56 56 1.5_
0800 159 169 113 - 82 1.4
1200 197 221 135 119 14 1.6

 

TABLE A-6.~~Vertica1 profiles of platinum electrode
in mv) for an offshore station

potentials (E7

68

over the 1973 growing season.

 

 

 

Depth Bottom

Date Time Depth
Surface 0.5m 1.0m .5m Bottom (m)
5/23 1200 139 127 117 106 ~71 1.9
1600 389 385 865 169 ~39 1.6
2000 289 267 257 257 126 1.8
5/24 2400 91 86 74 41 ~57 2.1
0400 171 170 70 52 ~62 1.6
0800 250 204 53 57 38 2.3
1200 354 353 67 67 ~74 1.8
5/31 1200 397 386 127 132 ~2 2.0
6/6 1200 371 371 371. 172 11 1.6
1600 235 235 165 165 19 2.1
2000 374 363 306 287 44 1.9
6/7 2400 374 374 409 413 256 1.8
0400 208 130 50 44 ~263 2.3
0800 41 41 75 51 51 1.9
1200 238 79 49 65 ~43 2.2
6/14 1200 209 193 193 189 29 2.0
6/20 1200 503 490 488 455 226 2.0
1600 307 307 297 310 208 1.8
2000 283 276 209 104 ~102 2.0
6/21 2400 134 48 63 93 ~100 1.9
0400 401 260 314 414 47 2.0
0800 428 396 280 280 149 1.8
1200 272 273 272 267 121 1.9
6/28 1200 150 132 107 96 ~79 2.4
7/4 1200 314 312 186 168 113 1.9
1600 347 321 346 322 199 2.0
2000 305 270 241 213 2 2.0
7/5 2400 266 267 212 181 ~112 2.0
0400 168 239 185 177 ~276 2.1
0800 163 167 86 44 ~175 2.3
1200 226 230 192 175 ~153 2.3
7/12 1200 572 552 486 426 164 2.2
7/18 1200 595 567 530 514 429 1.9
1600 674 658 497 491 284 2.0
2000 506 492 472 443 216 1.7
7/19 2400 202 257 280 246 196 2.0
0400 '326 227 271 254 132 1.9
0800 271 266 266 241 130 1.6
1200 514 474 498 481 224 2.4

TABLE A~6.~-Continued.

69

 

 

 

Depth Bottom

Date Time Depth
Surface 0.5m 1.0m 1.5m Bottom (m)
7/26 1200 329 181 297 268 202 1.9
8/1 1200 621 619 588 566 383 1.7
1600 668 602 567 548 411 1.7
2000 608 602 602 421 421 1.5
8/2 2400 577 566 566 559 445 1.6
0400 497 454 604 592 391 1.7
0800 552 553 553 553 467 1.9
1200 392 390 395 393 238 1.9
8/9 1200 146 143 153 133 21 2.0
8/15 1200 397 386 184 173 126 1.9
1600 307 294 292 279 155 2.3
2000 458 457 470 367 355 1.6
8/16 2400 119 111 127 ~137 ~137 1.5
0400 44 29 0 84 59 1.8
0800 283 294 290 296 157 1.8
1200 516 510 407 425 388 1.8
8/23 1200 329 319 304 242 9 2.0
8/30 1200 128 72 52 45 ~101 2.5
9/5 1200 371 365 309 289 254 1.8
1600 416 405 394 257 91 1.8
2000 227 226 221 137 ~27 1.6
9/6 2400 284 269 262 267 96 61.8
0400 259 244 243 254 62 1.9
0800 140 126 136 146 11 1.8
1200 294 304 218 223 210 1.7
9/13 1200 324 334 264 251 241 1.9
9/20 1200 438 429 409 366 366 1.5
9/26 1200 361 377 352 275 74 2.0
1600 260 253 253 240 2 1.8
2000 217 81 192 52 52 1.5
9/27 2400 205 209 203 192 159 1.7
0400 145 154 176 158 58 2.0
0800 145 29 79 51 ~37 2.0
1200 252 261 135 126 33 2.1

 

70

TABLE A—7.~-Vertica1 pH profiles for an inshore station

over the 1973 growing season.

 

Bottom
Depth

Depth

Time

 

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

4314956

11112.1111fl

1285986

9888778

982

879

4843823
0 O O O O O 0
9999899

A953924
9999899

4164035
0 O O O .0.
9099999
1...
0000000
0000000
2604482
1122001
3 4
2 2
/ /
5 S

1200 8.7

1200

5/31

4767675

111111.].

2185076

7767577

2441276

7888677

4.441381

8888678

A442380

8888678

4452582

8888678

1600
2000
2400
0400
0800
1200

6/6
6/7

1200 8.6

6/14

4888668

1111111

9234587

8888778

0452028

9999998

1.3—[.3128

9999998

1204240”

0 0 O O O 0

9909998
.1.

1200
1600
2000
2400
0400
0800
1200

6/20
6/21

6
l

1200 9.4

6/28
7/4
7/5

5688676

1111:111111

7871145

8988788

7898551

8988889
4782525
0 O O O O O 0
9989999
5752535
0 I O

O O O 0
9999999

5852848

9999899

1200
1600
2000
2400
0400
0800
1200

5
l

1200 9.1

7/12

5856566

1111111

4305292

97007978

4401290”

998998OJ.

6675561

9999999

7898762

9999999

7988773

9999999

1200
1600
2000
2400
0400
0800
1200

7/18
7/19

7]

TABLE A-7L--Continued.

 

Bottom
Depth

Depth

Time

 

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

1200 9.6

7/26

5758675

1111111

5655596

7777768

575356rnw

7879878

31556_/.3

99999—/.Q“

4375473

9999979

3575454
0 O I O O O 0
9999989

1200
1600
2000
2400
0400
0800
1200

8/1
8/2

1200 9.

8/9

5845555

1111111

6574210

8688857

9533753

8999899

0641852

9999899

0.851455

9999899

OnunuonunuO
Onunuonunuo
2ronv4.qnu2
lai952nunul
5 6
l l
// //
8 8

1200
1200

8/23

9.4

9.

8/30
9/5
9/6

7635643

1111111

2601390

9978879

3,0 1.5

O O
99 89

4952342
0 O O O I O 0
9989989

4963A43

9989989

A95556l

O O O O

$989989

1200
1600
2000
2400
0400
0800
1200

3
l

5
9

1200

9/13

1200 9.

9/20

3355546

1111111

0057563

8878888

332118flw

9999989

3333191

9999989

A444192

9999989

1200
1600
2000
2400
0400
0800
1200

9/26
9/27

 

72

TABLE A-8.--Vertical pH profiles for an offshore station

over the 1973 growing season.

 

Bottom
Depth

Depth

 

Time

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

9r0.8163

111212

002679

899778

36468nw

999889

4740..an

999999

4..rO.421-._nu.

999919

466331

a o o o o 0
999999

1200
1600
2000

5/23

2400

5/24

0400
0800
1200

5/31
6/6

6198392

1211212

2544776

8776677

2522976

8887678

25330.r0.5

8887~/._/.8

23440.75
8nd.B_/.—/.78

2544376
0 O... O 0
8887778

1200
1600
2000
2400
0400
0800
1200

6/7

1200 8.

6/14

0809089

2121211

5360938

8977687

9522901
8999899

1332901

9999899

8363nw12

8999999

9374222
8999999

1200
1600
2000
2400
0400
0800
1200

6/20
6/21

1200

6/28
7/4

9000133

1222222

6778283

8876677

”494111

9989999

3607934

9999899

3558845

9999899

4668456

9999799

1200
1600
2000
2400
0400
0800
1200

7/5

1200 9.2

7/12

9070964

1212112

0248782

9777877

4640720

9998899

57740.r0..l_

9998999

$895162

9998999

7891172

73

TABLE A-8.——Continucd.

 

Bottom
Depth

Depth

 

Time

Date

(In)

0.5m 1.0m 1.5m Bottom

Surface

 

. 1.9

. 9.1 .

1200 9.6

7/26

7756799

1111111

7220538

7888787

2921499

9889988

4173691

9999989

4.573691

9999989

5684792

9999989

1200
1600
2000
2400
0400
0800
1200

8/1
8/2

1200 9.6

8/9

9265888

1211111

0588842

9866876

3428464

9976996

4536352

9979897

5645845

9979897

5756245

9979897

OnunuOnUnuO
OnunuOnUnuO
2ronu4.qpu2
11L9g2nUnul
5 6
l l
/, //
8 .8

1200 8.

8/23

1200 9.6

8/30

7869987

1111111

2360468

9867767

2040542

9989989

3770443

9989989

4873544

9989989

4992664

9989989

1200
1600
2000
2400
0400
0800
1200

9/5
9/6

1200 9.6

9/13

1200 9.3

9/20

0857001

2111222

3419263

8788878

2213969

9989888

3313090

9999989

2324891

9999889

14358nuoz

9999899

1200
1600
2000
2400
0400
0800
1200

9/26
9/27

 

74

TABLE A-9. --Total copper and cadmium concentrations in the
water expressed as three-point means,a with
seasonal mean percentage in the suspended
fraction.

 

Copper - microgm/L Cadmium - microgm/L

 

 

 

Date ———

Inflowc OutflowC Pondd InflowC Outflowc Pondd
5/23 9.86 13.49 2.45 1.9 1.2 1.8
5/31 3.21 1.6
6/6 10.47 9.87 2.86 1.8 1.2
6/14 2.61
6/20 8.83 9.42 1.81 1.7 1.1
6/28 2.10
7/4 5.18 2.38 2.10 1.3 1.1 1.1
7/12 1.81 0.9
7/18 1.82 2.31 1.64 1.1 0.9 0.8
7/26 2.27 0.9
8/1 2.13 2.04 2.28 1.2 1.0
8/9 2.08 1.2
8/15 2.48 3.63 1.33 1.0 0.9
8/23 1.28 .
8/30 1.63
9/5 .53 1.70
9/13 1.62 .
9/20 1.12 .
9/26 2.74 4.53 1.11 1.2 1.4 1.0
Pemxmt‘
Suspended 80.9 86.1 84.2 88.9 77.5 84.1

 

aTabled values are means of samples taken on date
listed, preceeding date, and following date, except for the
first and last in the series (these are two-point means).
bBy membrane filtration
CFrom samples composited over 24 hr.

dFrom surface samples taken at an inshore and
offshore station at noon.

75

TABLE A-10.--Copper concentrations (microgm/L) in the water
as taken from curves fitted to the total copper
data of Table A-9.

 

 

Sample Date Total Suspended Dissolved
Inflow 6/6 10.45 8.45 2.00
6/20 8.96 7.25 1.71
7/4 7.87 3.94 0.93
7/18 2.23 1.80 0.43
8/1 1.83 1.48 0.35
8/15 2.58 2.09 0.49
9/5 2.76 2.23 0.53
9/26 2.74 2.22 0.52
Pond 6/6 2.97 2.48 0.49
6/20 2.05 1.71 0.34
7/4 1.91 1.60 0.31
7/18 2.08 1.74 0.34
8/1 1.97 1.65 0.32
8/15 1.67 1.39 0.28
9/5 1.52 1.27 0.25
9/26 1.04 0.87 0.17
Outflow 6/6 10.00 8.61 1.39
6/20 8.75 7.53 1.22
7/4 3.68 3.17 0.51
7/18 1.25 1.08 0.17
8/1 2.13 1.83 0.30
8/15 3.96 3.41 0.55
9/5 3.38 2.91 0.47

9/26

4.56

3.93

0.63

 

76

TABLE A-11.--Total quantities of c0pper and cadmium in the
flow of water entering and leaving Pond 4
during the 24-hour period on the dates listed.

 

 

 

 

 

Volume (106L) Gm Inflow Gm Outflow
Date

Inflow Outflow Cu Cd Cu Cd
6/6 1.9 1.8 20.3 ' 3.6 18.2 2.2
6/20 1.9 1.8 17.1 3.0 15.5 2.0
7/4 1.3 1.4 6.3 1.7 5.3 1.4
7/18 1.6 1.2 3.6 1.9 1.5 1.1
8/1 2.0 2.1 3.7 2.3 4.4 2.0
8/15 1.6 1.5 4.0 1.7 5.8 1.5
9/5 1.7 1.9 4.7 2.0 6.3 2.2
9/26 1.7 1.5 4.7 2.6 6.9 2.2

 

77

TABLE A-12.--Cadmium concentrations (microgm/L) in the water
as taken from curves fitted to the total cadmium
data of Table A-9.

 

 

Sample Date Total Suspended Dissolved
Inflow 6/6 1.87 1.66 0.21
6/20 1.55 1.38 0.17
7/4 1.32 1.17 0.15
7/18 1.19 1.06 0.13
8/1 1.13 1.00 0.13
8/15 1.12 0.99 0.13
9/5 1.17 1.04 0.13
9/26 1.24 1.10 0.14
Pond 6/6 1.40 1.18 0.22
6/20 1.39 1.17 0.22
7/4 1.05 0.88 0.17
7/18 0.89 0.75 0.14
8/1 1.04 0.87 0.17
8/15 1.00 0.84 0.16
9/5 0.57 0.48 0.09
9/26 0.98 0.82 0.16
Outflow 6/6 1.22 0.95 0.27
6/20 1.10 0.85 0.25
7/4 1.01 0.78 0.23
7/18 0.97 0.75 0.22
8/1 0.97 0.75 0.22
8/15 1.02 0.79 0.23
9/5 1.18 0.91 0.27

9/26

1.44

1.12

0.32

 

78

TABLE A-13.--Relationships between the concentrations
(microgm/L) of copper and cadmium in the
inflow and outflow of Pond 4 taken from the
raw data collected on the dates given.

 

Inflow - Outflow Outflow/Inflow x 100

 

 

 

Date

Cu Cd Cu Cd
6/6 0.45 0.65 95.7 65.2
6/20 0.21 0.45 97.7 71.0
7/4 1.11 0.31 75.6 76.5
7/18 0.10 0.22 56.1 81.5
8/1 -0.30 0.16 116.4 85.8
8/15 -1.38 0.10 153.5 91.1
9/5 -0.62 -0.01 122.5 100.9

9/26 -1.82 -O.20 166.4 116.1

 

79

TABLE A14.--Biomass of vascular hydrophytes.

 

Log10 Ash-Free Dry Weight in gm/samplera

 

 

 

 

 

Species _ 2
Date Mean (Y) s; s n
Ceratophyllum
demersum 5/23 .40416 .06845 .07964 17
6/6 .04170 .11761 .27663 20
6/20 .43109 .10455 .26235 24
7/4 .78111 .14809 .57021 26
7/18 1.02018 .13600 .07233 26
8/1 1.11225 .10582 .26876 24
8/15 .80866 .11183 .25010 20
9/5 1.01747 .08602 .12581 17
9/26 .98305 .06322 .06792 17
Potomageton spp.b 5/23 -.44242 .18550 .58500 17
6/6 -.29492 .16933 .57344 20
6/20 -.31931 .13470 .43547 24
7/4 .04937 .12124 .26456 18
7/18 -.18809 .24735 .61180 10
8/1 -.55380 .26820 .43159 6
Lemna minor 7/4 -.16272 .13355 .35670 20
7/18 -.02498 .11146 .24846 20
8/1 -.09828 .09168 .16812 20
8/15 .30618 .12060 .29087 20

 

aSampler for g. demersum and POtamogeton spp, had
area of 0.1135 m2; for 5*. minor, 0.0625 m4.

b

 

 

P. foliosus and g. berchtoldii combined.

TABLE A-15.--Percentage ash of dry-weight in the vascular

80

 

 

 

 

 

hydrophytes.
Species Date Mean(Y) s; 52 n
Ceratophyllum
demersum 5/23 17.43 .67 2.22 5
6/6 18.45 .34 .59 5
6/20 29.68 1.97 19.46 5
7/4 26.10 1.62 13.07 5
7/18 22.38 1.72 14.75 5
8/1 21.60 1.14 6.65 5
8/15 18.78 .73 2.64 5
9/5 20.46 2.66 35.27 5
9/26 20.85 1.31 8.62 5
12/13 21.71 1.72 14.83 5
Potamogeton spp.a 5/23 18.09 1.69 14.25 5
6/6 20.37 2.85 40.74 5
6/20 22.27 1.30 8.43 5
7/4 22.01 2.74 37.49 5
7/18 18.79 4.54 61.93 3
8/1 19.00 1.33 8.82 5
Lemna minor 5/23 13.84 - - 1
6/20 22.82 1.18 2.76 2
7/4 21.35 1.20 7.20 5
7/18 20.78 .83 3.48 5
8/1 19.09 .42 .87 5
8/15 20.43 .37 .67 5
9/5 19.44 .39 .76 5
9/26 19.87 .29 .42 5

 

a2. foliosus and P. berchtoldii combined.

 

81

TABLE A-16.—-Mean copper concentrations in vascular
hydrophytes expressed as loglo of microgm/gm
of ash-free dry weight.

 

 

 

 

 

Date Mean (Y) s; s n

Ceratophyllum
demersum 5/23 1.86543 .06228 .02715 7
6/6 1.77013 .08022 .04504 7
6/20 1.62546 .10487 .14298 13
7/4 1.25669 .06835 .07008 15
7/18 .89140 .04750 .03385 15
8/1 .79512 .02539 .00967 15
8/15 .68481 .04202 .01766 10
9/5 .76459 .02464 .00607 10
9/26 .80683 .03909 .01528 10
12/13 1.65299 .03608 .01302 10

Potamogeton

spp.a 5/23 1.86028 .06414 .02468 6
_—— 6/6 1.79282 .05899 .03132 9
6/20 1.60106 .07071 .04999 10
7/4 1.18166 .07370 .05431 10
7/18 .97643 .17419 .12136 4
8/1 1.08653 .11771 .06928 5
Lemna minor 5/23 1.46389 - - 1
6/20 1.35139 .11118 .04944 4
7/4 1.43407 .15096 .11394 5
7/18 1.59339 .08437 .03559 5
8/1 1.45216 .09878 .04878 5
8/15 1.44845 .12720 .08089 5
9/5 .76917 .02337 .00273 5
9/26 .76756 .01179 .00070 5

 

a

 

E. foliosus and P. berchtoldii combined.

82

TABLE A-17.--Mean cadmium concentrations in vascular
hydrophytes expressed as loglo of microgm/gm
of ash-free dry weight.

 

 

 

 

 

 

Date Mean (Y) s; 52 n

Ceratophyllum '
demersum 5/23 —.13571 .01296 .00118 7
6/6 -.06256 .07516 .03954 7
6/20 .09113 .02499 .00812 13
7/4 -.01679 .03086 .01333 14
7/18 -.16849 .02672 .01071 15
8/1 -.10620 .02176 .00711 15
8/15 —.18154 .04559 .02078 10
9/5 -.04999 .05548 .17543 10
9/26 -.04396 .02423 .00587 10
12/13 -.27630 .03597 .01294 10

Potamogeton
spp.a 5/23 -.45506 .11727 .08252 6
6/6 .09925 .01212 .00132 9
6/20 .26347 .04778 .02283 10
7/4 -.20255 .15736 .24762 10
7/18 -.05671 .09035 .03266 4
8/1 .24193 .06313 .01993 5
Lemna minor 5/23 -.04335 - - 1
6/20 -.26106 .03723 .00555 4
7/4 -.35986 .02577 .00332 5
7/18 -.26999 .04475 .01001 5
8/1 .17566 .01783 .00159 5
8/15 .01598 .02737 .00375 5
9/5 -.11259 .04141 .00857 5
9/26 -.O4425 .01814 .00165 5
a

P. foliosus and P. berchtoldii combined.

 

83

TABLE A-18.--Tota1 quantities of copper and cadmium in the
vascular hydrophytes of Pond 4 as derived from
curves fitted to the data for ash-free biomass
and tissue concentration (also given) for dates
of sampling in 1973.

 

 

 

 

 

D Pond Biomass Cu in Cu held Cd in Cd held
ate . . .

1n Kg mg/Kg 1n gm mg/Kg 1n gm
Ceratophyllum demersum
6/6 362 79.81 28.9 0.89 0.3
6/20 987 35.37 34.9 1.26 1.3
7/4 2164 17.69 38.3 0.98 2.1
7/18 3416 10.11 34.5 0.75 2.6
8/1 4336 6.70 29.1 0.70 3.0
8/15 5101 5.21 26.6 0.76 3.9
9/5 4577 4.87 22.3 0.88 4.0
9/26 3368 7.39 24.9 0.92 3.1

a

Potamogeton spp.
6/6 141 66.67 9.4 1.40 0.2
6/20 210 41.10 8.7 2.05 0.4
7/4 279 16.99 4.8 0.70 0.2
7/18 155 9.28 1.4 1.01 0.2
8/1 25 13.21 0.4 2.03 0.1
8/15 nil - - - -
Lemna minor
6/6 nil - - - -
6/20 1 20.91 nil 0.56 nil
7/4 159 37.84 6.0 0.42 0.1
7/18 238 41.82 9.9 0.61 0.1
8/1 81 27.30 2.2 0.96 0.1
8/15 194 20.40 4.0 1.13 0.2
9/5 49 9.26 0.5 0.76 nil
9/26 19 5.74 0.1 0.91 nil

 

I'U

foliosus and P. berchtoldii combined.

 

84

TABLE A-19.--Biomass of zooplankton.

 

Loglo Ash-Free Dry Weight gm + 1.0/samplera

 

 

Date

Mean (Y) s; s2 n
6/6 .03057 .00886 .00102 13
6/20 .01353 .00200 .00008 20
7/4 .00586t .00071 .00001 20
7/18 .00315 .00071 .00001 20
8/1 .00199 .00071 .00001 20
8/15 .00240 .00071 .00001 20
9/5 .00330 .00100 .00002 20
9/26 .00251 .00100 .00002 20

 

aSampler volume 34.3 L.

85

TABLE A-20.--Copper and cadmium concentrations and per-

centage ash in the zooplankton.a

 

 

 

 

Date Copper Cadmium % Ash of
microgm/gm microqm/gm Dry We1ght
Ash-Free DW Ash-Free DW
5/23 38.22 0.80 -
30.53 0.67
6/6 42.73 0.60 8.84
44.47 0.47
6/20 43.82 0.85 10.54
57.78 0.89
7/4 24.21 0.20 8.58
20.23 0.20
7/18 22.12 0.92 9.69
27.37 0.79
8/1 16.51 0.31 5.63
29.66 0.52
8/15 33.15 2.61 -
9/5 660.00 1.03 -
9/26 141.28 0.91 -

Mean 8.96

 

aSamples for a date combined to obtain sufficient

material for analyses; tabled values are for individual

analyses.

86

TABLE A-21.--Tota1 quantities of copper and cadmium in the
zooplankton of Pond 4 as derived from curves
fitted to the data for ash-free biomass and
tissue concentration (also given) for dates

of sampling in 1973.

 

 

Date Pond Biomass Cu in Cu held Cd in Cd held
1n Kg mg/Kg 1n gm mg/Kg 1n gm
6/6 119.8 46.49 5.6 0.62 0.1
6/20 5.9 42.55 0.3 0.77 nil
7/4 2.5' 31.78 0.1 0.40 nil
7/18 0.8 20.73 nil 0.41 nil
8/1 0.5 20.27 nil 0.86 nil
8/15 0.9 48.46 nil 1.74 nil
9/5 1.4 597.10 0.9 1.23 nil
9/26 0.8 147.45 0.1 0.99 nil

 

TABLE A-22.--Biomass of benthic macroinvertebrates.

87

 

 

 

Loglo Ash—Free Dry Weight gm + 1.0/samplera

Date
Mean (Y) s— 52 n
5/23 .04216 .00671 .00089 20
6/6 .01344 .00300 .00018 20
6/20 .00878 .00229 .00010 19
7/4 .00711 .00141 .00004 20
7/18 .00746 .00158 .00005 20
8/1 .00926 .00200 .00008 20
8/15 .00205 .00071 .00001 20
9/5 .00149 .00071 .00001 20
9/26 .00966 .00265 .00014 20

 

aSampler

2

area .023 m .

88

TABLE A-23.--Copper and cadmium concentrations in benthic
macroinvertebrates.a

 

 

 

 

Copper Cadmium

Date
nficnmegnAshdheeIMP ' nficfimegnlEhflhnelfiP

5/23 37.34 2.22

30.59 1.85

33.67 2.16

34.86 3.13
6/6 26.47 2.97
6/20 25-04 4.64
7/4 20.38 5.68
7/18 14.59 4.94
8/1c 14.05 5.37
8/15 18.94 9.69
9/5 18.73 1.73
9/26 16.92 1.59

 

aSamples for a date combined to obtain sufficient
material for analyses; tabled values are for individual
analyses.

bA11 samples combined for single determination of
percentage ash; this composite 12.15% ash.

CA second sample consisting of only dragonfly naiads
(Anax g2.) had 16.42 microgm/gm Cu and 0.02 microgm/gm Cd.

89

TABLE A-24.--Tota1 quantities of copper and cadmium in the

benthic macroinvertebrates of Pond 4 as

derived from curves fitted to the data for
ash-free biomass and tissue concentration
(also given) for dates of sampling in 1973.

 

 

Date Pond Biomass Cu in Cu held Cd in Cd held
1n Kg mg/Kg 1n gm mg/Kg 1n gm
6/6 44.0 26.25 1.2 2.94 0.1
6/20 25.9 26.49 0.7 5.62 0.1
7/2 25.4 18.75 0.5 4.60 0.1
7/18 26.3 15.01 0.4 5.15 0.1
8/1 23.5 15.21 0.4 7.43 0.2
8/15 12.7 17.57 0.2 7.60 0.1
9/5 3.3 19.20 0.1 1.93 nil
9/26 31.5 16.88 0.5 1.61 0.1

 

90

Hoooooo.l Noooo. mmooo.l mmvoo. NmNNo.I mmamo. AHmHQEmm
\H + .35 8.5:: 59
mmflfiqmmmoaflhmm amen

 

 

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mmflfifim
.5 “Sign 285
m 288. 88.8.- 88m. 2.88.- 259.8335 005.5.“ 89
mmgfifim.EfiHWE¥u
5288858 o as
m «88.- ~88. 880. cad 39: 35:88
5 5868 550585
N 880.- 88m. 88m.» :3 m}: 3%
5 .888 53588
N 388.- «SS. 8288 2.35 $9:
35588 5 55.08 58
m 82.- ~mc-.~ 352.: 1.3.6 m}:
mamandomfiauqu%Hvamfiau
A 5-38.8. 735. 880.- 808. 808.- M88. 088.- 880. 381 8383
88 5 5568 1.88.
p 8-35 735- 888. 808.- 8.80. 880.- 888. 858.- 38.5 8383
88 5 0088 58.
m 8888. 880. :89- 880. 38.5 85.2
3238 5 5588 58.
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3338 5 .688 38.
m 8088.- N88. 088.- 188. 38,5 8382
355 5 85888 58.
m 2888. 880.- 880. 388.. SEC. M88: 3815 8383
3035 5 8&8 138.
X X X X I
85:. 4. 8 mx 4x mx m ax 88.435 5

 

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newmmmummu Hmfifiocxaom wo mumzoauc ou manmfium>nx u0m mucofiowmwmoo cam ummonmucfllwll.mmn< wands

91

 

 

 

 

 

 

 

880. 38. >88. 898. u «2.85 889? 2.35 8812 963
c8388 5 5668 fig
288. ~88. 88o. 88~. 388. u ~88~ 3.3 85.5 $9:
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880. 3.8. 808. 83.. . 88¢.~ 885.? cad 855 $63
855m 5 .5868 35
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303 mQfiam 5 59900 363
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no.3: map-3 5.. .5868 303
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