Chlorine Toxicity Study
Mad River
Waterville Valley, N.H.
April, 1977
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U.S. Environmental Protection Agency
Region I
New England Regional Laboratory
Lexington, Massachusetts
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EPA Region I Mobile Toxicity Trailer
Modification of the Wuerthele and Riley proportional
diluter delivering a continuous flow of nine
different percent effluents to duplicate assay
chambers.
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Chlorine Toxicity Study
Mad River
Waterville Valley, New Hampshire
July 30 - August 8, 1976
by
Peter M. Nolan
Arthur F. Johnson
U.S. ENVIRONMENTAL PROTECTION AGENCY
REGION I
New England Regional Laboratory
Lexington, Massachusetts
April 1977
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Acknowledgement
This report was made possible with the close cooperation of
The Town of Waterville Valley, N. H., The N. H. Water Supply
and Pollution Control Commission, N. H. Fish and Game,
U. S. Fish and Wildlife Service and the U. S. Forest Service.
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Table of Contents
Page
List of Tables iii
List of Figures iv
Conclusions v
Recommendations vii
Introduction 1
Site Description 2
Waterville Valley WWTP 2
Mad River 5
Toxicity Study
Introduction 9
Procedures and Methods 10
Test Chambers 12
Toxicant 12
Experimental Design 15
Chemical Methods and Analysis 16
Biological Methods 17
Results and Discussion 17
lc50's 25
Linear Regression and 95% Confidence 30
Toxicity Curve 30
Instream Studies 38
Results 40
Chronic Toxicity and Chlorine Criteria 40
References 47
Appendices A-l to A-10
ii
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1
2
3
4
5
6
7
8
9
10
11
12
13
14
List of Tables
Description
Trout and Salmon Stocking Program
Mad River, Waterville Valley, N.H.
Flows, U.S. Forest Service Gaging
Station, Mad River at Shell Cascade
Seven-day Low Flow, Five Northern
New Hampshire Watersheds
Waterville Valley Chlorine Toxicity
Study - Phase I, 7/30-8/3/76
Waterville Valley Chlorine Toxicity
Study Replicate Tests
Phase I - 7/30-8/3/76
Waterville Valley Chlorine Toxicity
Study - Phase II 8/4-8/8/76
Waterville Valley Chlorine Toxicity
Study Replicate Tests -
Phase II, 8/4-8/8/76
Waterville Valley, N.H. Chlorine
Toxicity Study LC5Q,s
Total Residual Chlorine Values
in Mad River, Waterville Valley, N.H.
August 5, 1976
Seven-Bay Low Flows and Percent Effluent 36
in Mad River at Various Discharges
Mad River, Benthos and Live Cage 39
Fish Stations
Live Cage Fish Study, 3 meters 41
Salvelinus fontinalis
Live Cage Fish Study 42
Salvelinus fontinalis
Mad River, Waterville Valley New 43,44
Hampshire, Qualitative Benthos Study
of Chlorinated Effluent, August 1976
iii
Page
6
7
8
18
19,20
21
22,23
28
35
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List of Figures
Figure Description Page
1 Waterville Valley Sewage Chalet 4
2 Waterville Valley Chlorine Toxicity 26
Study - Phase II
24 Hour LC^q- Log Probability Analysis
3 Waterville Valley Chlorine Toxicity 27
Study - Phase II
96 Hour LCcjq - Log Probability
Analysis
4 Waterville Valley Chlorine 31
Toxicity Study - Phase II
Linear Regression Analysis
from Data in Table 7
5 Toxicity Curve from LC5Q, 32
Phase II S
Plate 1 Mad River Live Cage Study 47
lv
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Conclusions
1. Chlorine toxicity was exhibited over a range of concentrations
using Eastern Brook Trout, with the 96 hour LC^q determined
to be .135 mg/1 TRC. This is also the incipient lethal concen-
tration or threshold level.
2. The acute toxic effects of total residual chlorine are normally
manifested during the first 24 hours of exposure, the time
during which most mortalities occur.
3. A mean value of 0.21 mg/1 total residual chlorine killed 100%
of the fish at Station MR02 ( 3 meters downstream of discharge pipe)
in 64 hours. Caged fish stayed alive at all other stations.
4. Of the total taxa of benthos collected from all stations (41)
39% were obtained from the control area and 44% and 49% collected
at the 18 meter and 64 meter downstream stations. Fewer species
of mayflies, caddisflies and chironomids were present downstream
of the discharge pipe and comprised only 17% of the total taxa
collected.
5. An effluent plume or zone of influence determined with Rhodamine
b dye exists in the Mad River and extends approximately one-third
the distance across the river for at least 137 meters downstream of
the point of discharge.
v
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Conclusions (Con1t.)
6. Periods of low flow in the Mad River coupled with discharge of
chlorinated wastewater from the Town of Waterville Valley poses
the greatest potential risk to the salmonid fish and other
aquatic biota indigenous to the Mad River.
vi
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Recommendations
On the basis of the information contained in this report the
following recommendations are made:
1. A maximum Total Residual Chlorine Criteria of 0.13 mg/1 be
adopted for the Waterville Valley Waste Treatment Plant discharge.
3
2. During period of low flow of .48 m /sec. (17 CFS) or less,
discharge of chlorinated effluent should be curtailed, or
stopped by recycling in order to insure the protection of the
salmonid fishery and aquatic life in the Mad River.
3. In view of changing coliform bacteria standards, the need to
chlorinate at Waterville Valley should be reviewed in order
to weigh the environmental risks against the benefits achieved.
vii
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Waterville Valley, N. H. Chlorine
Toxicity Study
July 30 - August 8, 1976
Introduction
Chlorination of wastewater treatment plant effluents is the most
common procedure for disinfection and protection of public health.
There are, however, complications due to the acute and chronic
toxicity caused by total residual chlorine to important aquatic
species of which the salmonid fish appear to be the most sensitive.
Many studies have concluded that chlorine causes increased mucus
production and damage to respiratory epithelium of the gills leading
to death by asphyxiation.
Because of this, the future course of wastewater chlorination is
being influenced by recent proposed changes in the Environmental
Protection Agency's regulations on secondary treatment. The changes
intend that disinfection only be considered when public health
hazards need to be controlled, and that the exclusive use of chlorine
should not be considered where protection of aquatic life is of
primary consideration. Where these uses co-exist, alternate means of
disinfection are to be considered.
Recognizing the potential toxicity that total residual chlorine poses
to the many important species of fish and other aquatic life in the
Mad River, the New Hampshire Water Supply and Pollution Control
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Commission requested that the EPA, New England Regional Laboratory
conduct studies to assess what affect, if any, the chlorinated
effluent from Waterville Valley, N. H. Wastewater Treatment Plant
has on the biota of the Mad River, and to determine what concentra-
tions of total residual chlorine are toxic. Continuous flow on-line
toxicity studies, and instream live cage studies were used to deter-
mine the concentration of total residual chlorine that is lethal to
half of a selected fish population, Salvelinus fontinalis, in the
fixed period of time of 96 hours. Benthic invertebrate populations
were examined as part of the instream study.
New Hampshire Water Supply and Pollution Control Commission personnel
conducted a dye study to determine the zone of influence and concentra-
tion of the Waterville Valley waste discharge in downstream areas in
the Mad River.
Other interested agencies in addition to WS&PCC and EPA, Region I
that participated in the planning of the study include: The New
Hampshire Fish and Game Department, U. S. Forest Service, Town of
Waterville Valley, and the U. S. Fish and Wildlife Service.
Site Description
Waterville Valley WWTP
Advanced wastewater treatment is supplied to Waterville Valley's
fluctuating recreational population during the year - Alpine and
Nordic skiing during the winter, and tennis schools, fishing and
-2-
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hiking during the summer. Peak recreational population at present
is 3000-4000 people, and Waterville Valley's Sewage Treatment Facil-
ity is designed to treat the waste of up to 7000 people. Treated
waste is not discharged continuously as it can be pumped back to the
two aerated lagoons and recycled through the treatment plant during
dry periods.
Solids contact clarifiers, dual media sand filters and carbon adsorp-
tion columns polish the water for chlori-nation with sodium hypo-
chlorite (15% available chlorine) in the chlorine contact chamber for
a 15-20 minute detention time (Figure 1).
Plant operators try to maintain a total chlorine residual of 0.5 mg/1
in the chlorine contact chamber. It is then piped to the Mad River
at the rate of 681 liters per minute (180 gals, per minute) when dis-
charging. Total coliform bacteria counts averaged 2.9 colonies per
hundred milliliter before chlorination (Letter, Appendex). Total
coliforms allowed in the discharge permit is 240 per hundred
milliliters.
Ammonia removal reactors are not used at present because there is
less than 7 mg/1 of ammonia in the effluent. During the backwashing
of carbon filters total residual chlorine can increase to 2 mg/1 for
30-45 minutes and volume of discharge decreases to 416 liters per
minute (110 gals, per minute). Total suspended solids are approxi-
mately 5 milligrams per liter using two of the three carbon adsorption
columns.
1)
Waterville Valley Treatment Plant personal communication.
-3-
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WET WELL
COMMINUTER AND
BAR RACK
AERA1 ED L ^GOONS
MAIN SEWAGE PUMPS
SLUDGE
DISPOSAL
BEDS
SLUDGE HOLDING PONDS
CARBON ADSORPTION COLUMNS
AMMONIA REMOVAL REACTORS
IA
DUAL
SAND
FILTERS
PUMPS
J SOLIDS CONTACT CIARIFIERS
CHLORINE
CONTACT
TANK
ER SUMP
FILTERED WAT
EFFLUENT CONTROL VALVE (To Mad River)
WATERVILLE VALLEY SEWAGE CHALET
ADVANCED WASTEWATER TREATMENT FOR UP TO 7000 PEOPLE
BREAKPOINT CHLORINATION FOR AMMONIA REMOVAL
Figure 1
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Mad River
The Mad River in Northern New Hampshire's White Mountain National
Forest, is a fast-flowing, well-oxygenated boulder-strewn stream
supporting a salmonid population consisting of the heavily stocked
Eastern Brook Trout (Salvelinus fontinalis) and Rainbow Trout (Salmo
gairdnerii) for sport fishing, and the Atlantic Salmon (Salmo salar)
as part of the Merrimack River Atlantic Salmon Restoration Program
(Table 1).
An erosional riffle fauna of caddisflies, mayflies, stoneflies and
blackflies are the major forms of benthos and food source for the cold
water fish population.
During the instream study, August 4-8, 1976, the river mean flow volume
3
was 1.7 m /sec. (61.2 cu. ft/sec.) obtained at the U. S. Forest Service
Shell Cascade Gaging Station approximately 3.7 Km (two miles) down-
stream (Table 2). The dissolved oxygen content was 10-11 ppm, a
temperature range of 13-20° Centigrade, and a pH range of 6.7-7.6 and
a mean of 7.1.
Seven-day low flow volumes for the Mad River for different intervals
are estimated from U. S. Geological Survey data of runoff in cubic
meters per second per square kilometer for five Northern New Hampshire
Watersheds (Table 3). An annual seven-day low flow of 0.007/mVsec./
Km (0.71 cubic feet per second per square mile) runoff for the Mad
River Watershed (estimated) is the average of the five Northern New
Hampshire Watersheds and approximately equals the flow for the Pemi-
gawasset River at Lincoln, N.H. to which the Mad River is a tributary
(Appendix A). Approximately 62.2 km2 (twenty-four square miles)
of watershed contribute to the Mad River flow volume in the study area.
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TABLE 1
TROUT AND SALMON STOCKING PROGRAM*
Mad River, Waterville Valley, N.H.
Year Brook Trout Rainbow Trout Atlantic Salmon
1972 4800 3100
1973 7300 3000
1974 4700 4000
1975 4600 3100 36,000
1976 4875 2900 63,100
*New Hampshire Fish and Game Department
-6-
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TABLE 2
FLOWS
U. S. FOREST SERVICE GAGING STATION
MAD RIVER AT SHELL CASCADE
Water Depth
at Lead Pin in Ledge
(cm)
Flow
cu. m/s
CFS
16.7
.42
15.0
18.6
.56
20.0
20.1
.71
25.0
21.6
.85
30.0
22.9
.99
35.0
24.0
1.13
40.0
25.0
1.27
45.0
26.2
1.42
50.0
27.1
1.55
55.0
28.0
1.69
60.0
28.9
1.84
65.0
29.6
1.98
70.0
30.5
2.12
75.0
31.1
2.26
80.0
32.0
2.41
85.0
32.6
2.55
90.0
32.9
2.69
95.0
34.1
2.83
100.0
39.6
4.25
150.0
44.2
5.66
200.0
Source: Gordon Stuart, White Mountain National Forest, P.O. Box 638,
Laconia, N.H.
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TABLE 3
SEVEN-DAY LOW FLOW
FIVE NORTHERN NEW HAMPSHIRE WATERSHEDS
Cubic Meters per Second per Square Kilometer
Return Upper Ammonoosuc
Interval River at Groveton
Baker River at
Rumney
Saco River at
Conway
Ammonoosuc River
at Beth. Junction
Pemigewasset River
at Lincoln
Annual
6.34 0.58
4.92 0.45
9.84 0.90
9.84 0.90
7.76 0.71
2-Year
3.38 0.31
1.53 0.14
3.61 0.33
4.26 0.39
5.03 0.46
i
oo
10-Year
2.18 0.20
1.09 0.10
2.51 0.23
3.28 0.30
2.84 0.26
100-Year
1.53 0.14
0.98 0.09
2.07 0.19
2.84 0.26
1.42 0.13
1 O O
Data from U. S. Geological Survey - m /sec/km x 10 CFS/sq. mi.
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Toxicity Study
7/30 - 8/8, 1976
Introduction
In compliance with a request from the State of New Hampshire Water
Supply and Pollution Control Commission a Chlorine Toxicity study
was conducted on Waterville Valley treatment plant wastewater. The
study was performed in two successive phases. Phase I, 7/30-8/3/76,
the total residual chlorine concentration in the plant effluent was
elevated to a maximum mean TRC of 1.45 ppm. The effluent at this
concentration of chlorine was not discharged to the Mad River but
recirculated through holding lagoons at the head of the treatment
process. The total residual chlorine for Phase II, 8/4-8/8/76, was
maintained at a level not to exceed concentrations normally discharged
to the Mad River which is 0.5 ppm. The actual mean TRC for this
second phase of the study was 0.33 ppm and was discharged directly to
the Mad River. During this part of the study, live cages containing
brook trout were placed in the Mad River and monitored concurrently
with the operation of the on line continuous flow bioassay conducted
in the mobile laboratory. Of concern to all participating parties in
this study was the need to maintain the necessary safeguards to
protect the salmonid fishery and Atlantic Salmon restoration in the
Mad River.
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Procedures and Methods
The EPA mobile toxicity laboratory was moved from Lexington, Mass. and
located on site at the Waterville Valley WWTP the week of July 26, 1976.
Following its delivery, the laboratory was hooked up and all apparatus,
equipment, and instruments were readied for start-up on July 30.
The laboratory as designed is equipped for both static and continuous
flow bioassay. The unit has a separate fish keeping and acclimation
tank of approximately 378 liters (100 gallons), a 1703 liter (450 gallon)
dilution water tank and two 189 liter (50 gallon) effluent tanks. Each
of the above tanks are equipped with a combined aeration and temperature
control unit. Power vents are strategically located in the laboratory
to expel any contaminated air which could potentially cross contaminate
the dilution water or fish stock tanks.
Pumps are used to deliver dilution water continuously from the Mad
River to the dilution water tank and from this tank to the diluter.
Likewise, effluent is pumped continuously from the treatment plant to
effluent tanks to the diluter. Non contaminating tygon tubing is used
to transport fluids within the laboratory and good quality garden hose
is used to pump from the river and treatment plant. All water connec-
tions are made of inert plastic or stainless steel where possible to
avoid potential contamination.
Materials used for the construction of all tanks or chambers holding
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water or effluent are either fiberglass, lucite, plate glass or
Stainless steel. These materials minimize leaching, sorption and
and dissolution of unknown substances into the diluted effluent.
The effluent dilution apparatus used in these tests is a modification
of the Wuerthele and Riley proportional diluter (Riley, 1975). The
diluter has three sections, stacked in order from top to bottom they
are, a metered flow box, a mixing box, and a distribution box. The
diluter combines effluent and diluent flows of equal volume to give
nine separate effluent concentrations of the following proportions
based on percent volume, 100, 87.5, 75, 66.7, 50, 33.3, 25, 12.5,
and 0. These diluted effluents in their respective concentrations are
thoroughly mixed, split into equal flows and delivered to replicate
assay chambers. A series of tests to measure the diluters performance
were conducted at the New England Regional Laboratory using
hydrogen ion concentration and salt solutions. The results of these
tests demonstrated the diluters ability to perform well within the
five-percent maximum allowable diluter error, (i.e., actual dilution
vs. theoretical dilution).
Flows from the distribution box to the assay vessels are delivered
constantly at a mean rate of 343 ml/min. with a calculated error of
approximately 2%. A suggested maximum allowable flow difference
between replicate tanks is 10%. The flow of 343 ml/min., or
approximately 20 1/hr allows for a flow rate through each of the
assay vessels containing fish of about 24 volumes per day. The desired
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minimum flow rate for any toxicant delivery system is at least
10 volumes per 24 hours.
During operation at Waterville Valley the diluter system was maintained
as needed during operation to prevent clogging by debris.
Test Chambers
The assay chambers used were both welded stainless steel and window
glass glued with silicon adhesive. The chambers are provided with
an adjustable standpipe for continuous overflow from the tank. Water
depth within each of the tanks was adjusted to a depth of approximately
20 centimeters thus giving a volume of approximately 20 liters. Maximum
capacity of the stainless tanks is 38 liters and 28 liters for the
glass tank. As mentioned previously, the Wuerthele and Riley diluter
as modified to deliver 343 ml/min. can accommodate a maximum of 160
grams fish per unit based on Sprague's (1969) conservative flow to
fish weight ratio of 3 liters per gram fish per day. Using the less
stringent loading criteria recommended by the committee on Methods
for Toxicity Tests with Aquatic Organisms (1975), a total of up to
400 grams fish per unit is possible. That is, not more than 2 grams
of fish per liter of test solution passing through the vessel in
24 hours should be used and not greater than 20 grams/liter in the test
chamber at any time should be allowed. For our tests, the above stated
criteria were not exceeded as the average fish weight per unit was
approximately 120 grams.
Toxicant
The toxicant used for this study is the wastewater discharge from the
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Waterville Valley, N.H. waste treatment plant. The plant is of
modern design (See Fig. 1 ) with secondary and tertiary treatment
being provided. Since there are no industrial wastes being treated
the effluent discharged to the Mad River is essentially free from
complex chemical toxicants other than those added during the treatment
process and for which there is prior knowledge. The chemical of con-
cern and for which this toxicity study was designed is chlorine added
as hypochlorite for disinfection purposes. Chlorination is normally
used to effect a total residual of not greater than 0.5 ppm during
routine operation. During our study an elevated residual of 1.5 ppm
was used for Phase I, with 0.33 ppm used for Phase II. At times when
back flushing is required within the plant chlorine values at discharge
can be elevated 100% or more at a reduced discharge volume for short
periods of time. Effluent temperatures during the test period ranged
from 20-22°C. Ph's ranged from 6.5-7.2 and dissolved oxygen 6.8-7.2
mg/1. Chlorinated effluent is pumped directly from the contact chamber
into the continuous flow bioassay system located in the trailer.
The dilution water source for the study was pumped directly from the
Mad River upstream of the waste discharge and integrated into the
laboratory in the same manner as the effluent. Water temperatures
during the test period ranged from 12°C to 16°C. The normal summer
temperature range for the Mad River is 10°C-21°C (USFWS May, 1976).
Dissolved oxygen concentrations ranged from 8.0 to 9.5 mg/1 or
80-90% of total saturation. Ph values recorded for the Mad River ranged
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from 6.1 to 7.1 with the more acidic Ph being recorded during a period
of increased flow due to heavy rains. Conductivities are normally in
the range of 35 to 50 micromhos per cm at 25°C (USFWS, 1976). Mad
River water in addition to its use as diluent was used to acclimate
the test fish at 15°C.
Test Specie
Eastern Brook Trout, Salvelinus fontinalis were used as the test species.
The brook trout is an indigenous, sensitive, and recreationally im-
portant fish species of the Mad River and is regularly stocked by the
New Hampshire Fish and Game. The fish stocks used for the duration of
our tests were supplied by the N.H. Fish and Game via truck from the
New Hampton, N. H. fish rearing station. All fish arrived in apparently
healthy condition. During acclimation of the first shipment of fish
(appro*. 250) a 70% mortality occurred due to a faulty aerator in the
holding tank. The survivors of this group were stocked in the Mad
River. A second delivery of approximately 250 fish were successfully
acclimated at 15°C for 24 hours prior to use for bioassay Phase I.
For Phase II of the study and the live cage study, a third delivery of
180 fish was received. These fish also were acclimated at 15°C prior
to start-up. The Salvelinus fontinalis were all from the same year
size class. A representative lot of test fish (10 specimens) had a
mean body weight of 11.8 gm and a mean standard length measured from
the tip of the snout to the end of the caudal peduncal of 9.3 cm.
The uniformity of the test group is demonstrated by the fact that
only a 30% length difference existed between shortest and the longest
fish.
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Experimental Design
Beginning early the morning of July 30, 1976, chlorinated effluent
and dilution water from the Mad River were continuously pumped and
integrated into the continuous flow on line bioassay system set up
in the mobile laboratory. Each of the 18 test chambers receiving
nine treatments in replicate was allowed to fill and overflow its
entire volume prior to introducing the test animals and conducting
any physical and chemical analysis.
No water connections between replicate test chambers existed.
Randomized treatments for each effluent concentration were used by
random assignment of the test vessels in two rows. This was accomplished
by assigning the 18 total dilutions delivered by the diluter (9 rep-
licates) to cards numbered 1 through 18. These cards were mixed-up
in a hat, drawn and assigned to vessels from left to right for each of
the two rows. Brook trout introduced to the test chambers was done
impartially by placing the number of fish captured from the fish
holding tank with a small aquarium net into each of the random test
tanks. This was repeated until 10 fish total per tank was reached.
Normally, between one and four fish was introduced at one time. This
technique was both convenient and reduced stress on the trout due to
less handling.
Artificial lighting during the test was held at approximately 75 foot
candles with some natural lighting provided by six roof mounted sky-
lights .
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Chemical Methods and Analysis
Ph, temperature, dissolved oxygen and total residual chlorine were
routinely measured for the duration of the tests using recommended
procedures. (Standard Methods, 1975, EPA, 1974).
Ph was measured using a Corning Digital 109 general purpose Ph meter.
The meter was calibrated daily using buffer solutions of Ph 4, 7 and
9.
Dissolved oxygen was measured using an Orbisphere Model 2609 oxygen
meter. The meter was calibrated daily using water saturated air at
a known temperature and barometric pressure.
Temperature was measured using a mercury thermometer and the tempera-
ture indicator portion of the orbisphere meter.
Total residual chlorine was measured using the amperometric titration
method. A Wallace and Tiernan titrator was used. As a back up
procedure the DPD ferrous titrametric method was used. Reliable
measurements of .01 mg/1 TRC and above were achieved. Levels of
detection below .01 mg/1 were considered too inaccurate to quantitate.
Measurements for all of the above parameters were made each day at
the end of a specified exposure period (i.e. 8 hours). In addition,
other measurements were made periodically throughout the time, at
least one fish in a test tank remained alive.
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Biological Methods
The biological data resulting from both phases of the laboratory
study and the live cage study was developed from recommended acute
toxicity testing procedures (Standard Methods, 14th Ed, Committee
on Methods for Toxicity Tests....1975, EPA Biological Methods
(1973). Acute toxicity using death as the criteria was recorded
based on a lack of gill movement and a lack of response to prodding.
Dead fish were removed from the test chambers as soon as the mortality
was confirmed and then recorded in a log. Typically, the dead brook
trout would be found floating belly up with distended gills. With
the biological responses recorded, the concentration of TEC at which
50% of the fish survive for 2 hours, 4 hr, 6 hr, 8 hr, 24 hr, 48 hr,
72 hr, and 96 hr is determined.
Results and Discussion
The results of the continuous flow bioassay tests for Phase I and
Phase II with maximum mean residual chlorine concentrations of
1.45 mg/1 and 0.33 mg/1 respectively are presented in Tables 4 to
7 . The data is arranged showing the results for each replicate
analysis using ten fish, as well as the combined results for each
dilution using 20 fish. Included also, is the data for the mean
values for Dh, temperature, dissolved oxygen and total residual chlorine.
The test species, the number of each exposed to each test concentration
and the number of mortalities at the end of a specified time interval
is also listed.
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96
20
20
20
20
20
20
20
1
0
Table 4
Waterville Valley Chlorine Toxicity Study - Phase I, 7/30-8/3/76
Mean Mean Mean Mean No. Test
Residual Test Dissolved pH Organisms
Chlorine Temp Oxygen Salvelinus
ppm ^C ppm fontinalis
1.45 22.0 7.4 6.5 20
1.20 21.0 7.4 6.5 20
1.0 21.0 7.7 6.5 20
0.95 19.0 7.6 6.5 20
0.68 18.0 7.6 6.6 20
0.51 17.0 7.5 6.6 20
0.37 17.0 7.2 6.6 20 •
No. Salvelinus fontinalis Dead At
2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr
20
(. 5hr) 20 20 20 20 20 20
20
(.5hr) 20 20 20 20 20 20
20
(l.Ohr)20 20 20 20 20 20
20
(l.Ohr) 20 20 20 20 20 20
20
(l.Ohr)20 20 20 20 20 20
4 20 20 20 20 20 20
0 4 15 20 20 20 20
0.11 15.5 8.1 6.5 20 OQOOl 11
0 14.6 8.4 6.6 20 0Q000 00
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Table 5
Waterville Valley Chlorine Toxicity Study Replicate Tests - Phase I, 7/30-8/3/76
Effluent Mean Mean Mean Mean No. Test
Concentra- Residual Test Dissolved pH Organisms No. Salvelinus fontinalis Dead At
tion Percent Chlorine Temp Oxygen Salvelinus
Volume ppm °C ppm fontinalis 2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr 96 hr
—
100 Ri 1.4 22 7.5 6.4 10 (.5hr) 10 10 10 10 10 10 10
10
100 R2 1.5 22 7.4 6.4 10 (.5hr) 10 10 10 10 10 10 10
97.5
R1
1.2
21
7.4
6.5
10
10
(. 5hr)
10
10
10
10
10
10
10
87.5
r2
1.2
21
7.3
6.5
10
10
(-5hr)
10
10
10
10
10
10
10
75
R1
1.0
21
7.7
6.5
10
10
(l.Ohr)
10
10
10
10
10
10
10
75
r2
1.0
21
7.7
6.5
10
10
(l.Ohr)
10
10
10
10
10
10
10
66.7
%
1.0
18.5
7.5
6.5
10
10
(l.Ohr)
10
10
10
10
10
10
10
66.7
r2
0.9
19
7.6
6.5
10
10
(l.Ohr)
10
10
10
10
10
10
10
50
R1
0.7
18
7.5
6.6
10
10
(l.Ohr)
10
10
10
10
10
10
10
10
6,6 10 (l.Ohr) 10 10 10 10 10 10 10
-------
Table 5 (Cont'd)
Waterville Valley Chlorine Toxicity Study Replicate - Phase I, 7/30-8/3/76 (Cont'd)
Effluent Mean Mean Mean Mean No. Test
Concentra- Residual Test Dissolved pH Organisms No. Salvelinus fontinalis Dead At
tion Percent Chlorine Temp Oxygen Salvelinus
Volume ppm °C ppm fontinalis 2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr 96 hr
33.3 Rl 0.52 17 7.4 6.6 10 2 10 10 10 10 10 10 10
33.3 R2 0.50 17 7.6 6.6 10 2 10 10 10 10 10 10 10
25 Ri
0.36
17
7.3
6.6
10
0
3
8
10
10
10
10
10
25 R2
0.37
17.5
7.2
6.6
10
0
1
7
10
10
10
10
10
12.5 Ri
0.11
15.9
8.0
6.5
10
0
0
0
0
1
1
1
1
12.5 R2
0.11
15.7
8.1
6.5
10
0
0
0
0
0
0
0
0
0
Control R^
0.0
14.6
8.4
6.6
10
0
0
0
0
0
0
0
0
0
Control R2 0.0 14.6 8.5 6.6 10 0 0 0 0 0 0 0 0
-------
Table 6
Waterville Valley Chlorine Toxicity Study - Phase II, 8/4-8/8/76
Effluent
Concentra-
tion Percent
Volume
0
Control
Mean Mean Mean Mean No. Test
Residual Test Dissolved pH Organisms No. Salvelinus fontinalis Dead At
Chlorine Temp Oxygen Salvelinus
ppm °C ppm fontinalis 2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr 96 hr
1PP
0.33
18.0
7.0
7.3
20
0
3
11
19
20
20
20
20
87.5
0.28
17.7
8.1
7.1
20
0
0
0
12
17
20
20
20
75
0.22
17.3
7.6
7.1
20
0
0
0
8
15
19
20
20
66.7
0.17
16.4
7.8
7.1
20
0
0
0
1
14
16
16
17
50
0.12
16.4
7.8
7.1
20
0
0
0
0
2
3
5
5
33.3
.08
15.2
8.0
7.1
20
0
0
0
0
0
0
1
1
25
.05
15.2
8.2
7.0
20
0
0
0
0
0
0
1
1
12.5
^ .01
15.0
8.3
7.1
20
0
0
0
0
0
0
0
0
0.0
14.2 8.8
7.1
20
2*
2* 2*
* 1 mortality due to fish jumping out of tank
-------
96 1
10
10
10
10
10
10
10
8
2
3
Table 7
Waterville Valley Chlorine Toxicity Study Replicate Tests - Phase II, 8/4-8/8/76
Mean Mean Mean Mean No. Test
Residual Test Dissolved pH Organisms
Chlorine Temp Oxygen Salvelinus
ppm oc ppm fontinalis
0.32 18 6.8 7.4 10
0.34 18 7.1 7.2 10
0.29 18 7.3 7.0 10
0.28 17.5 8.5 6.9 10
No. Salvelinus fontinalis Dead At
2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr
0 1 6 9 10 10 10
0 2 5 10 10 10 10
0 0 0 9 10 10 10
0 0 0 3 10 10 10
0.23 17.3 7.9 7.1 10 0 0 0 5 7 9 10
0.22 17.2 8.0 7.0 10 0 0 0 3 8 10 10
0.17 16.0 7.9 7.1 10 0 0 0 0 8 10 10
0.17 16.8 7.8 7.1 10 0 0 0 1 6 7 7
0.12 16.7 7.8 7.1 10 0 0 0 0 1 1 2
0.12 16.2 7.8 7.1 10 0 0 0 0 1 2 3
-------
Table 7 (Cont1d)
Waterville Valley Chlorine Toxicity Study Replicate Tests - Phase II, 8/4-8/8/76 (Cont'd)
Effluent Mean Mean Mean Mean No. Test
Concentra- Residual Test Dissolved pH Organisms No. Salvelinus fontinalis Dead At
tion Percent Chlorine Temp Oxygen Salvelinus
Volume ppm ppm fontinalis 2 hr 4 hr 6 hr 8 hr 24 hr 48 hr 72 hr 96 hr
33.3 0.08 15.3 8.0 7.1 10 0 0 0 0 0 0 0 0
33.3 R2 0.07 15.2 7.9 7.0 10 0 0 0 0 0 0 1 1
25 Rx .04 15.2 8.2 7.0 10 0 0 0 0 0 0 0 0
25 R2 .05 15.2 8.1 7.1 10 0 0 0 0 0 0 1 1
12.5 Rx ^.01 14.8 8.2 7.1 10 0 0 0 0 0 0 0 0
12.5 R2 ^.01 15.1 8.4 7.1 10 0 0 0 0 0 0 0 0
0
Control
R1
0.0
14.1
8.8
7.1
10
0
0
0
0
0
2*
2*
2*
0
Control
R2
0.0
14.2
8.8
7.0
10
0
0
0
0
0
0
0
0
* 1 mortality due to fish jumping out of tank
-------
During Phase I at concentrations of 1.45 and 1.2 mg/1 total residual
chlorine mortalities started initially within 10 minutes of the fish
being introduced. At the end of one-half hour all fish were dead.
By the end of one hour 100% kills occurred at 1.0, 0.9, and 0.68 mg/1
TRC. At a concentration of 0.51 mg/1, 100% of the fish died at the
end of four hours and within 8 hours all fish died at a concentration
of 0.37 ppm. Only one mortality was recorded at 0.11 ppm TEC for
96 hours. This occurred during the first 24 hours of exposure. The
control fish all survived the 96 hours during Phase I.
At the completion of Phase I, all surviving fish were released to the
Mad River. It is noteworthy that the group exposed to the chlorine
showed a distinct loss of vigor and an inability to orient to the
stream flow. These fish were easily recaptured by hand 45 minutes
after release. In contrast the control fish released, seem to adjust
very rapidly to their new environment by swimming into the deeper,
swifter portions of the river. Sight of this group was soon lost.
For Phase II, no mortalities occurred at any concentration during
the first 2 hours. At the end of 4 hours, three mortalities were
recorded at a TRC of 0.33 mg/1. By the end of 24 hours all fish had
died. At 0.28 mg/1 greater than 50% died within 8 hours with a
complete mortality recorded at the end of 48 hours. At TRC concentra-
tions of 0.22 and 0.17 mg/1 greater than 50% of the brook trout died
during the first 24 hours with 0.22 mg/1 killing all fish by the end
of 72 hours. At 72 and'96 hours .17 mg/1 TRC killed 80% and 85% of
-24-
-------
the fish respectively. A 10% mortality occurred within 24 hours at
.12 mg/1 and a 25% mortality was recorded at the end of the experiment.
One death each was recorded at concentrations of .08 and .05 mg/1 TRC
at the end of 72 hours. No deaths were recorded at TRC's of _<_ .01 mg/1
and below. Two deaths in the controls occurred during the first 48
hours. One of these mortalities was due to the fact that one fish
jumped from its test tank and was replaced in a stressed condition. The
other mortality was a natural death. All surviving fish in this phase
of the study were apparently healthy when released to the Mad River.
They also seemed to adjust well to the environment although they
appeared somewhat sluggish at first.
LC 50's
LC 50's were determined for each data set in the preceding tables.
This data was plotted on logarithmic probability paper with percentage
dead (mortality) on the probability scale and effluent concentration
(TRC mg/1) on the logarithmic scale. For each LC5Q calculated, one
or more chlorine concentrations at which greater than 50% of the brook
trout survived and less than 50% of the fish survived is plotted. The
point at which the curve connecting two or more of these points crosses
the 50% survival line is the LC^q. The curve is drawn on a best fit
basis. Representative plots, using probit analysis (Litchfield,
Wilcoxon, 1949) to determine the 24 hour and 96 hour LC^q's for Phase II
are presented in Figures 2 and 3 * Table 8 gives the complete LC^q
data for both Phase I and Phase II of the on-line bioassay and the
estimated 24 and 96 hour for the live cage river study.
-25-
-------
FIGURE 2
WATERVILLE VALLEY CHLORINE TOXICITY STUDY - PHASE II
24 Hour LC^® - Log - Probability Analysis
LC
Residual Chlorine
Parts per Million x 10"^
-26-
-------
FIGURE 3
WATERVILLE VALLEY CHLORINE TOXICITY SUTDY - PHASE II
96 Hour LC50 - Log - Probability Analysis
o
LC
Residual Chlorine
Parts per Million x 10
-27
-------
TABLE 8
WATERVILLE VALLEY, N.H. CHLORINE TOXICITY STUDY
1
Time
Hours Days
2
4
6
8
LC
50's
Phase I
7/30-8/3/76
TRC2
0.58
0.39
0,28
0.20
Phase II
8/4-8/8/76
TRC
0.33
0,24
Live Cage
in Stream
8/4-8/8/76
TRC3
24
48
72
96
1
2
3
4
0.16
0.16
0.16
0.16
0,17
0,15
0.14
0.135
.15
.15
.15
.15
20 Test Animals
'Total Residual Chlorine ppm
Estimated
-28-
-------
By review of this data for the LC^q, some differences are noted to
exist between Phase I and Phase II for specific time intervals.
This can be explained mostly due to the extremely toxic nature of
the TRC concentrations used during Phase I. These doses in most
cases either killed all the fish or none of the fish within the
specified time. The LC^q's determined on the basis of this although
valid are not as accurate as might be expected if more partial
mortalities occurred at TRC concentrations where at least one of the
responses was in the range of 16% to 84%. As can be seen, the Phase I
LC_ 's are the same for 24 to 96 hours. This is because no dilutions
oO
were accomplished between 0.37 and 0.11 mg/1. A similar situation
exists for the live cage study, where various dilutions or TRC con-
centrations result from a combination of river flow and volume of
discharge.
The LC50 data for Phase II on the other hand can be considered to be
more accurate because partial mortalities occurred at TRC values
where at least one and usually more than one response was in the range
of 16 to 84%. The dilutions in Phase II also provide the necessary
information with which to calculate the LC^q's for the 24 to 96 hour
time periods.
Both the LC5q data and experimental data show that total residual
chlorine in toxic concentrations exhibits its major impact during
the first 24 hours of exposure. It is during this time that most
mortalities occur.
-29-
-------
Linear Regression and 95% Confidence
A statistical analysis of the replicate data for Phase II is performed
using linear regression. Linear regression is a useful statistical
tool, particularly when investigating relationships between variables
in biological systems. Dose effect response such as TRC concentra-
tion vs. mortality is suited to bivariant analyses. Figure 4 is a
graphic representation of the regression analysis together with the
95% confidence limits for the data in Table 7 . This graph with the
95% confidence bands about the mean tells us that at a mean TRC of
.135 mg/1 a mean of 50% of the brook trout will survive for 96 hours.
This confirms the log-probit analysis and also states that at .135 mg/1
TRC, 95 out of 100 times the survival will be between 40 and 60% at
this concentration. Also of value is the ability to predict expected
survival with 95% confidence between TRC concentrations of .05 to
.22 mg/1.
Toxicity Curve
Figure 5 shows a classical toxicity curve which was drawn from the
LC50's determined from experimental data. This curve shows the
progressive toxicity of chlorine versus time of exposure. From this
it is possible to determine when acute toxicity has stopped. In
Figure 5 the curve is very close to the asymptote with respect to
time at about 72 hours and appears to have nearly reached it at 96 hrs.
The LC^q which is located in the asymptotic part of the curve, is the
threshold concentration or incipient LC5q. The incipient of
.13 mg/1 TRC is the point in time (96 hours) at which acute
-30-
-------
FIGURE *
WATERVILLE VALLEY CHLORINE TOXICITY STUDY
PHASE II. LINEAR REGRESSION ANALYSIS
FROM DATA IN TABLE 7
V
Cnrvjilis EnvnonMonMl Resk,;
200 S.W 35th Str-ot
Corvallis, Or«n< r; 0
O
o
o
00
cd
>
•H
>
M
3
C/i
4J
0
-------
FIGURE 5
TOXICITY CURVE FROM LC , PHASE II
50 s
Incipient LC
50
rn—r"tri
.15 .2 .3 .A .5 .6
MEAN RESIDUAL CHLORINE - ppm
-32-
-------
toxicity has ceased or the point at which 50% of the fish can survive
indefinitely. This information is important for prediction of in-
stream toxicity, particularly, when distinguishing acute and subacute
responses.
Brungs (1973) in a summary of several studies, indicates the acute
and chronic effects of residual chlorine on a range of aquatic life.
In Quality Criteria for Water (1976) the adverse effects of chlorine
are also cited. Although there is a range of TRC concentrations over
which various authors demonstrate acute toxicity for a given species,
there is a general agreement in the literature to the effect that the
salmonids are among the most sensitive group to chlorine. Since the
Mad River is significant to New Hampshire as a leading sport fishing
stream and is also being studied for Atlantic Salmon production potential,
it is necessary to evaluate the effects of chlorine in the Mad River so
that intelligent decisions can be made to protect the aquatic life
and its most important uses, fish preservation and enhancement.
Our studies, both instream and on-line continuous flow bioassay
demonstrate chlorine toxicity over a range of concentrations using
Eastern Brook Trout (Salvelinus fontinalis). The incipient lethal dose
or threshold level of approximately .13 mg/1 TRC appears to be a valid
discharge criteria for the Waterville Valley Waste Treatment Plant.
This level as determined is non-acutely toxic and with dilution and
dissipation should reach the 2 ug/1 safe concentration (EPA 1976)
within an acceptable distance downstream of the discharge.
-33-
-------
Using the results of a rhodamine b dye study (Appendix C, D) conducted
by the New Hampshire Division of Pollution Control and Water Supply
as part of the overall study, a zone of influence or effluent plume
is established. This zone at a flow of .85 mVsec. (30 CFS) , extends
approximately one-third the distance across the Mad River and at least
137 meters (450 feet) downstream. A general assessment of this data
shows that an initial outfall dye concentration of 35 ppb is diluted
approximately 10 times at 13 meters (45 feet) downstream of the out-
fall, approximately 25 x at 30 meters (100 feet), 65 x at 61 meters
(200 feet). From the 61 meter (200 foot) mark downstream to the 137
meter (450 foot) mark, the dilution factor increases to approximately
100 x. Most lateral mixing appears to take place during the first
61 meters (200 feet) with less farther downstream. The above estimates
for dilution are based on the maximum observed dye concentration at a
specified distance downstream. Applying the dye data to our recommended
effluent concentration of .13 ppm TRC, the EPA safe concentration
(2 ppb) could be realized approximately 61 meters (200 feet)downstream
of the discharge.
Table 9, gives an impression of actual chlorine concentrations measured
quantitatively in the Mad River at specific distance downstream of the
discharge. At 18 meters (60 feet) no total residual chlorine was
detected keeping in mind the minimum detection limits we established
was .01 ppm. The flow during this period of time was approximately
1.7 m3/sec. (61 CFS) or about twice the flow recorded during the dye
s tudy.
-34-
-------
TABLE 9
Total Residual Chlorine Values in Mad River
Waterville Valley, N.H.
August 5, 1976
Total Residual
Station Chlorine (mg/1)
Discharge Pipe 0.43
3 Meters (10 Ft.) Downstream 0.23
3.5 Meters (11.6 Ft.) Downstream 0.21
7.01 Meters (23 Ft.) Downstream 0.02
11.6 Meters (38 Ft.) Downstream * 0.01
18 Meters (60 Ft.) Downstream No Detection
-35-
-------
TABLE 10
SEVEN-DAY LOW FLOWS* AND PERCENT EFFLUENT
IN MAD RIVER AT VARIOUS DISCHARGES
Estimated % Effluent by Volume in River at Discharge of
Return Flow 681 liters/min. 920 liters/min* 1442 liters/min.
Interval Cu. Meters/Sec. 180 Gals./Min.^" 243 Gals./Min. 381 Gals./Min.
Annual 0.48 (17.0 CFS) 2.4 3.2 5.00
2-Year 0.22 (7.8 CFS) 5.1 6.9 10.9
10-Year 0.15 (5.2 CFS) 7.7 10.4 16.4
100-Year 0.11 (3.9 CFS) 10.3 13.9 21.8
Aug. 4-8, 1976 1.73 (61*2 CFS) .65 .88 1.4
~Calculated from U. S. Geological Survey Data (Table 3) - Also see Appendix A
^"Present Discharge
2189 liters (50 Gals.) of Waste per Person/Day for 7000 People
^Plant Designed to Treat 2.1 x 10^ liters/day maximum (550,000 Gals./Day Maximum)
-36-
-------
Table 10 gives estimated seven day low flows for the Mad River and
the estimated percent effluent within the river at projected dis-
charge capacities, assuming total mixing. From this data a
reasonable concentration of TRC within the Mad River can be estimated,
provided the effluent concentration is known. Even a maximum effluent
concentration of .13 mg/1, at the annual low flow of .48 m /sec
(17 CFS) the 2 ppb safe concentration could be exceeded a sizeable
distance downstream. Intuitively it seems best to limit or curtail
dxscharge completely, or not chlorinate during low flows of .48 m /sec.
(17 CFS) or less. Both of the above alternatives are feasible and
reasonable due to the recycle capability at Waterville, and due to
the very low coliform counts before chlorination.
Periods of low flow are considered by us to be critical. With the
added natural stresses there is reduced dilution and more concen-
trations of fish to restricted areas such as small pools and rips
which receive flow. The net effect of which can be higher densities
of fish exposed to higher concentrations of chlorine with a corres-
ponding higher mortality risk.
-37-
-------
Instream Studies
The rhodamine b dye study conducted July 26-27, 1976 by the N. H.
Water Supply and Pollution Control Commission personnel served to
determine the location of the treatment chalet's discharge plume.
Stations MR02-MR04 were located in this plume for total residual
chlorine concentrations, qualitative benthos sampling, and the live
cage fish study. Station MR01, the control, was located 15 meters
(50 feet) upstream of the discharge pipe.
Fluorescein dye was also used to visually determine the discharge
plume for locating the fish cages in the effluent.
Duplicate 19 liter (5 gallon) plastic pails with 6.3 mm (1/4-inch)
holes drilled in sides, bottom and top, containing ten Eastern Brook
Trout (average length 9.3 cm) per pail were placed in the river at
Stations MR01-MR04 (Table 11). Three large stones in the bottom of
each pail held them in the river, and a hinged plexiglas door in the
top cover allowed for viewing the fish without disturbing them during
the four-day study.
Qualitative benthos sampling was performed to determine the presence
or absence of benthic invertebrates between the upstream control
station (MROl) and the downstream Stations (MR02-MR04) situated in the
chlorinated effluent plume. The inorganic substrate of the reach of
river in the study area consisted of rubble, 6.4 cm to 25.4 cm
(2 1/2 to 10 in. diameter), boulders, 25.4 cm (>10 in. diameter) and
solid bedrock. Accumulated organic materials were not noticeably
present in the substrate; current velocity and depth was similar for
-38-
-------
TABLE 11
MAD RIVER
Benthos and Live Cage Fish Stations
Waterville Valley Sewage Treatment Chalet
August 4-8, 1976
Station Location
MR01 15 Meters (50 Feet) Upstream of Discharge Pipe
MR02 3 Meters (10 Feet) Downstream of Discharge Pipe
MR03 18 Meters (60 Feet) Downstream of Discharge Pipe
MR04 64 Meters (210 Feet) Downstream of Discharge Pipe
-39-
-------
all stations. Intensive sampling was conducted at each station by
collecting the invertebrates from the rubble and boulders to determine
the variety of life living in the substrate.
Results
A mean value of 0.21 mg/1 total residual chlorine killed 100% of the
fish at Station MR02, 3 meters (10 feet) downstream of discharge pipe
in 64 hours at a temperature of 20°C (Table 12) . All of the Eastern
Brook Trout stayed alive during the 96-hour study at the 18 meters
(60 foot) and 64 meters (210 foot) downstream stations and the upstream
control station without any apparent ill affects (Table 13).
Of the total taxa of benthos collected from all stations (41) 39%
were obtained from the control area and 44% and 49% collected at the
18 meters (60 foot) and 64 meters (210 foot) downstream stations.
Fewer species of mayflies, caddisflies and chironomids were present
3 meters (10 feet) downstream of the discharge pipe and only 17% of
the total taxa collected (Table 14).
Chronic Toxicity and Chlorine Criteria
The focus of our studies conducted at Waterville Valley WWTP centered
on the acute toxic effects of chlorine. Considerable information and
data resulting from field and laboratory research also exist to indicate
that chlorination of wastewater can result in residual chlorine levels
which are chronically toxic in very low concentrations to aquatic life.
As a result, EPA supports a Total Residual Chlorine Criteria of 2 ug/1
for salmonid fish and 10 ug/1 for other freshwater and marine organisms
-40-
-------
TABLE 12
LIVE CAGE FISH STUDY, 3 meters
Salvelinus fontlnalis
Mad River, Waterville Valley, N.H.
August 4-8, 1976
Date
8/5/76
8/6/76
Time
8/4/76 1430
Station
3 Meters (10 Ft.) Down-
stream of Discharge Pipe*
Total
Residual
Chlorine (mg/1)
1640
0830
1000
1130
1330
1400
1530
0730
1050
1430
0.22
8/7/76 0630
0.22
0.23
0.22
0.23
0.16
0.21
Fish Survival
(Cages)
10
10
5
4
4
3
2
1
0
0
0
10
5
4
3
3
3
3
1
1
1
Mean total residual chlorine of 0.21 mg/1 at 20°C killed 100% of the fish
in 64 hours, 3 meters (10 feet) downstream of the discharge pipe.
*Chlorinated effluent discharge 681 liters (180 gals) per minute,
-41-
-------
TABLE 13
LIVE CAGE FISH STUDY
Salvelinus fontinalis
Mad River, Waterville Valley, N.H.
August 4-8, 1976
Fish
Mean Total
Survival
Residual
Cages
Temp.
Flow
Date
Time
Station
Chlorine (mg/1)
1
2
°C
CFS
8/4/76
1430
Control
0.00
10
10
16
70
Discharge Pipe*
0.23
-
-
-
3 Meter Cage
0.00
10
10
20
18 Meter Cage
0.00
10
10
17
64 Meter Cage
0.00
10
10
16
8/5/76
0830
Control
0.00
• 10
10
16
59
Discharge Pipe
0.40
-
-
-
3 Meter Cage
0.22
5
5
20
18 Meter Cage
0.00
10
10
17
64 Meter Cage
0.00
10
10
16
8/6/76
0730
Control
0.00
10
10
16
57
Discharge Pipe
0.37
-
-
-
3 Meter Cage
0.19
0
1
20
18 Meter Cage
0.00
10
10
17
64 Meter Cage
.0.00
10
10
16
8/7/76
0630
Control
0.00
10
10
13
59
Discharge Pipe
0.34
-
-
-
3 Meter Cage
0.21
0
0
18
18 Meter Cage
0.00
10
10
14
64 Meter Cage
0.00
10
10
13
8/8/76
0715
Control
0.00
10
10
13
Discharge Pipe
0.32
-
-
-
3 Meter Cage
0.20
0
0
17
18 Meter Cage
0.00
10
10
14
64 Meter Cage
0.00
10
10
13
Mean 61.2
^Chlorinated effluent discharge of 68 liters per minute (180 gals, per minute)
and mean total residual chlorine of 0.33 mg/1.
-42-
-------
TABLE 14
MAD RIVER
Waterville Valley, New Hampshire
Qualitative Benthos Study of Chlorinated Effluent
August-1976
Stations
Downstream of Effluent
Upstream 3 Meters 18 Meters 64 Meters
Organisms Control (10 Ft.) (60 Ft.) (210 Ft.)
MR 01 MR 02 MR 03 MR 04
Plecoptera (stoneflies)
Nemouridae
Leutra sp. x x
Chloroperlidae
Alloperla sp. x
Ephemeroptera (mayflies)
Baetidae
Ephemerella comuta x
Ephemerella margarita x
Ephemerella catawba x x
Ephemerella simplex x x
Ephemerella sp. x
Neocloen sp. x
Baetis vagans x
Baetls sp. x
Heptageniidae
Heptagenia julia x x
Heptagenla sp. x
Rhithrogena doddsi x
Trichoptera (caddisflies)
Limnephilidea
Limnephilus consocius x x x
Limnephilus submonilifer x
Pycnopsyche sp. x
Philopotamidae
Trentonius distinctus x x
Hydrop sychidae
Hydropsyche simulans x
Hydropsyche betteni x x
Hydropsyche sp. x
Arctopsyche sp. x x x
Leptoceridae
Oecetis cinerascens x x x
Rhyacophilidae
Rhyacophila glaberrima x
Glossoma sp. x x
Brachycentridae
Brachycentrus sp. x x
-43-
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TABLE 14 (Con't)
MAD RIVER
Waterville Valley, New Hampshire
Qualitative Benthos Study of Chlorinated Effluent
Stations
Downstream of Effluent
Upstream 3 Meters 18 Meters 64 Meters
Organisms Control (10 Ft.) (60 Ft.) (210 Ft.)
MR 01 MR 02 MR 03 MR 04
Psychomyiidae
Neurellipsis sp. x
Neuroptera (fishflies)
Sialidae
Sialis sp. x
Diptera (flies)
Chironomidae
Calopsectra polita
Diamesa sp.
Diplocladius sp.
Prodiamesa sp.
Psectrocladius sp.
Polypedilum sp.
Hydrobaenus sp.
Tanypus sp.
Simuliidae
Simulium sp.
Blepharoceridae
Agathon sp.
Tabanidae
Coleoptera (bettles)
Haliplidae
Haliplus sp.
Amphipoda (sucds)
Talitridae
Hyalella azteca x
Total taxa 41
Total taxa at each station 16 7 18 20
Percent of total taxa 39% 17% 44% 49%
x
x
x
X
X
X
X
X
X
X
X
-44-
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(EPA, 1976). Other potential dangers are associated with
chlorine use (EPA Task Force, 1975) such as, human health hazards
where disinfection of wastewater with chlorine can result in the
formation of halogenated organic compounds which have been identified
as potential carcinogens.
Accordingly, requirements for chlorine disinfection of wastewater
and limitations on fecal coliform bacteria have been deleted by
amendments recently published by the Environmental Protection Agency.
States will be given the flexibility to develop water quality standards
and related disinfection requirements of their publicly owned treatment
works according to local needs. Guidance on setting coliform bacteria
and chlorine standards is provided in the Agency's recently published
Quality Criteria for Waters, October 10, 1976. Criteria for fecal
coliform bacteria in bathing waters for secondary treatment is based
on a minimum of not less than five samples taken over a 30-day period,
the fecal coliform bacterial level should not exceed a log mean of
200 per 100 ml, nor should more than 10% of the total samples taken
during any 30-day period exceed 400 per 100 ml.
Waterville Valley Treatment Facility's 1976 average for total coliform
bacteria of 2.9 colonies per 100 ml is considerably below the suggested
new standard and questions the benefits achieved by chlorination.
The benefits achieved by disinfection should be weighed against
the environmental risks and cost. It is intended that the use of
chlorine disinfection would be considered only when there are public
health hazards to be controlled. The exclusive use of chlorine for
-45-
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disinfection should not be continued where protection of aquatic life
is a primary consideration. Alternate means of disinfection and
disinfectant control must be considered where public health hazards
and potential adverse impact on the aquatic and human environments
co-exist. Disinfection should not be required in those instances where
benefits are not present (Federal Register, 1976).
-46-
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Plate 1
Mad River Live Cage Fish Study-
Live cages placed in chlorinated effluent plume
determined by fluorescein dye.
-47-
-------
References
APHA-AWWA-WPCF, Standard Methods, For the Examination of Water and
Wastewater, 14th Edition, 1975,
Brungs, W.A., "Effects of Residual Chlorine on Aquatic Life". Journal
WPCF 45, 10, 1973.
EPA, Biological Field and Laboratory Methods, EPA-670/4-73-001, 1973.
EPA, "Disinfection of Wastewater—Task Force Report", MCD-21, EPA-430/9-
75-012, 1975.
EPA, Methods for Acute Toxicity Tests with Fish, Macroinvertebrates,
and Amphibians, EPA-660/3-75-009, April 1975.
EPA, Quality Criteria for Water, EPA-440/9-76-023, 1976.
Federal Register, Monday, July 28, 1976, Page 30784,
Litchfield, J. T., F. Wilcoxon, "A Simple Method of Evaluating Dose-
effect Experiments". Pharmacol. Exp. Ther. 96:99, 1949.
Riley, C. W., "Proportional Dlluter for Effluent Bioassays", Journal
WPCF 47, 11, pages 2620-2626, 1975.
Sprague, J. B., "Measurement of Pollutant Toxicity to Fish. I. Bioassay
Methods for Acute Toxicity." Water Res,, 3, 793, 1969,
U.S.F.W.S., "Production Potential of Atlantic Salmon in the Merrimack
River System", Fisheries Resources, Laconia, NH., May 1976.
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APPENDIX
Contents
Appendix Description Page
A Mad River A-l
Seven Day Low Flow
Calculations
B Letter, Town of A-2
Waterville Valley
C Mad River A-3
Rhodamine-B Dye Study
D New Hampshire WS&PCC A-4 -
Instream Rhodamine-B A-10
Dye Concentrations
-------
Appendix A
MAD RIVER
Waterville Valley, N.H,
Calculations for Seven-Day Low Flow
From Five Northern N.H. Watersheds (Averages)
Cubic Meters per Second
Annual 7.74 x 62.16* = .48 m^/sec. (16.9 cu. ft./sec.)
2-Year 3.56 x 62.16 = .22 m^/sec. (7.82 cu. ft./sec.)
10-Year 2.38 x 62.16 = .15 m^/sec. (5,23 cu. ft./sec.)
100-Year 1.77 x 62.16 = .11 m^/sec. (3.88 cu. ft./sec.)
*62.16 square kilometers (24 square miles) of Watershed upstream of
Waterville Valley Sewage Chalet.
A-l
-------
Appendex B
TOWN OF
WATERVILLE VALLEY
NEW HAMPSHIRE 03223
January 26, 1977
New England Regional Lab
Mr. Arthur Johnson
60 West View Street
Lexington, Mass. 02173
Dear Arthur:
The following is the information that you requested regarding Coliform
counts of our effluent before and after chlorination. Unfortunately, we do
not have that many official counts before chlorination as we are not required
to report these monthly. The readings we are giving you were taken off from
our monthly reports to the State of New Hampshire and E.P.A. for 1976.
Total Coliform Bacteria (Average) - After CL£ - 0/100 ML
- Before CL£ - 2.9/100 ML
Total Pond Acreage - 3.2 Acres
Sincerely,
Gu 'i-,.,—- /'¦
A1 Burbank,
Superintendent
Wastewater Treatment Facility
sjl
cc: Paul Leavitt, Town Manager
A-2
-------
Appendix C
MAD RIVER
RHODAMINE-B DYE STUDY*
July 26-27, 1977
Distance
Meters From
Width of
Downstream in
Meters
River Bank
River
(Meters
Outfall
6.4
(21
ft.)
13.7
(45 ft.
4.6
(15 ft.)
4.6
(15
ft.)
13.7
(45 ft.
15
(50 ft.)
6.4
(21
ft.)
13.7
(45 ft.
30.5
(100
ft.)
6.4
(21
ft.)
14.9
(49 ft.
45.7
(150
ft.)
7.3
(24
ft.)
18.3
(60 ft.
60.9
(200
ft.)
10.9
(36
ft.)
18.3
(60 ft.
76.2
(250
ft.)
6.4
(21
ft.)
9.1
(30 ft.
91.4
(300
ft.)
4.6
(15
ft.)
11.3
(37 ft.
106.6
(350
ft.)
7.6
(25
ft.)
12.8
(42 ft.
137.2
(450
ft.)
3.04
(10
ft.)
10.6
(35 ft.
*Detectlon of effluent plume in feet downstream from Waterville
Valley outfall and from river bank. Figures derived from N.H.
Water Supply and Pollution Control Commission Dye Study during
river flow of .86 m^/sec. (30.6 CFS).
A-3
-------
APPENDIX D
A4 , A 5
40
;"0 30
OUTFALL
0.07
0.04
DATE- 27 JULY 1976
-------
APPENDIX d
A-6 , A-7
200
150
100
DEPTH
(FT.)
JO
NEW HAMPSHIRE WATER SUPPLY $
POLLUTION CONTROL COMMISSION
RHODAMINE-B
DYE CONCENTRATIONS
V.S.
45
SO
DISTANCE DOWNSTREAM FROM
THE WATERVILLE VALLEY
OUTFALL TO THE MAD RIVER
DATE- 2,6 JULY 1976
-------
DEPTH
(FT.)
°'SC
APPENDIX D
A8
250,,
NOTE-ALL DYE CONCENTRATIONS
IN PARTS PER BILLION
-RIVER FLOW 30.6 C.F.S.
-OUTFALL 180 &P.M.
NEW HAMPSHIRE WATER SUPPLY $
POLLUTION CONTROL COMMISSION
RHODAMINE-B
DYE CONCENTRATIONS
VS.
DISTANCE DOWNSTREAM FROM
THE WATERVILLE VALLEY
OUTFALL TO THE MAD RIVER
DATE-27 JULY 1976
-------
depth
(FTJ H
APPENDIX D
A9, AIO
450
o.»»
MOTE-ALL DYE CONCENTRATIONS
IN PARTS PER BILLION
-RIVER FLOW 30.6 C5.S.
-OUTFALL 180 &PM.
NEW HAMPSHIRE WATER SUPPLY $
POLLUTION CONTROL COMMISSION
RHODAMINE-B
DYE CONCENTRATIONS
V.S.
DISTANCE DOWNSTREAM FROM
THE WATERVILLE VALLEY
OUTFALL TO THE MAD RIVER
DATE-2TJULY 1976
-------
Waterville Valley's Sewage Chalet
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