WATER POLLUTION CONTROL RESEARCH SERIES • 18050 DBB 12/71
INDUSTRIAL WASTES: EFFECTS ON
TRINITY RIVER ECOLOGY
FORT WORTH, TEXAS
U.S. ENVIRONMENTAL PROTECTION AGENCY
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WATER POLLUTION CONTROL RESEARCH SERIES
The Water Pollution Control Research Series describes the
results and progress in the control and abatement of pollution
in our Nation's waters. They provide a central source of
information on the research, development, and demonstration
activities in the water research program of the Environmental
Protection Agency, through in-house research and grants and
contracts with Federal, state, and local agencies, research
institutions, and industrial organizations.
Inquiries pertaining to Water Pollution Control Research
Reports should be directed to the Chief, Publications Branch
(Water), Research Information Division, R&M, Environmental
Protection Agency, Washington, D. C. 20460
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INDUSTRIAL WASTES: EFFECTS ON TRINITY RIVER ECOLOGY
FOR! WORTH, TEXAS
by
Texas Christian University
Department of Biology
Fort Worth, Texas 7612*
for the
Office of Research and Monitoring
ENVIRONMENTAL PROTECTION AGENCY
Project Number 18050 DBS
December 1971
For Hfe by tb» Superintendent of DocawBts, D.S. Government Printing Office, Washington, D.0.2MGB - Price «!.»
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EPA Review Notice
This report has been reviewed by the Office of Water
Programs of the Environmental Protection Agency and
approved for publication. Approval does not signify
that the contents necessarily reflect the views and
policies of the Environmental Protection Agency, or
does mention of trade names or commercial products
constitute endorsement or recommendation for use.
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ABSTRACT
Toxicity of industrial effluents discharged directly into or in close
proximity to the Trinity River was reflected through a 27-month period.
The investigation was concerned with four aspects—bioassay, growth and
development, chemistry, and benthos.
Three industries contributed toxic materials which had a significant
influence on the surrounding aquatic community. Toxicity ranges were
established for the respective effluents using mature minnows, fry, and
spawn. Fry surviving 96-hour exposure to some of the effluents later
developed orientation problems and varied noticeably in growth. Fry were
only slightly less resistant to the effluents than minnows, but were
judged to be reasonably reliable bioassay test organisms.
Effluents from a railroad equipment cleaning area, a plant producing
cracking catalysts used in processing combustion engine fuels, and a
sewage treatment plant influenced the water quality of the river down-
stream from the outfalls. The ranges of nitrates, phosphates, bio-
chemical oxygen demand and specific conductance for the river were
increased by the effluents.
Environmental stress was detected at the railroad equipment cleaning
area outfall and even more at the plant producing cracking catalysts.
Benthos were not able to live in the flocculent material discharged in
the latter effluent. The drastic reduction in invertebrates at the
sewage treatment plant is believed to have resulted from the chlorinated
effluent.
This report was submitted in fulfillment of Project Number 18050 DBB
under the sponsorship of the Water Quality Office of the Environmental
Protection Agency.
iii
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CONTENTS
Section
I
II
III
IV
V
VI
VII
VIII
IX
X
ABSTRACT
CONCLUSIONS
RECOMMENDATIONS
INTRODUCTION
METHODS
Bioassay
Growth and Development. . .
Chemistry
Benthos
OBSERVATIONS
Bioassay
Growth and Development. . .
Chemical Evaluation ....
Benthos
DISCUSSION
ACKNOWLEDGMENTS
REFERENCES FOR LITERATURE CITED
GLOSSARY
APPENDICES
Page
1
5
7
i ->
13
1 5
54
78
33
39
JI
99
1D1
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FIGURES
Figure Page
1. Map of Texas showing Trinity River system 11
2. Map showing Trinity River course through
Tarrant County 12
3. TL paper ^
m
4. Map of Station I showing substations Is
5. Map of Station II showing substations 19
6. Map of Station III showing substations -'.'"'
7. Map of Station V showing substations 21
8. Map of Station IX showing substations '-2
9. Map of Station X showing substations
10. TL _ values for Station I effluents using golden
shiners (Notemigonus crysoleucas (Mitchill)) as
tes t organisms
11. Station III outfall evidencing white floe in effluent. .
12. Plume in the Trinity River caused by floe in Station
III effluent
13. TL n values for Station III effluent using golden
shiners (Notemigonus crysoleucas (Mitchill)) and
fathead minnows (Pimephales promelas Rafinesque)
as tes t organisms
14. TL values for Station III effluent using golden
shiners (Notemigonus crysoleucas (Mitchill)) and
fathead minnows (Pimephales promelas Rafinesque)
as test organisms 36
15. Gills taken from Notemigonus crysoleucas. A. Gills
taken from control—not exposed to Station III effluent.
B. Gills taken from fish after exposure for 15 minutes
to a 100% concentration of Station III effluent 3£
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16. Map of Station VI study area showing respective
substations A3
17. TL values for Station VI effluent using golden
shiners (Notemigonus crysoleucas (Mitchill) as
test organisms. Substation E 4(
18. TL values for Station VI effluent using golden
shxners (Notemigonus crysoleucas (Mitchill) as
test organisms . Substation F.
19. TL n values for Station VI effluent using fathead
minnows (Pimephales promelas Rafinesque) as test
organisms. Substations are indicated by capital
letters 4£
20. Notemigonus crysoleucas exposed to a 100%
concentration of Station VI effluent.
A. Control—no exposure.
B and C. Exposed for 40 minutes to a 100% concentration
showing erosion of fins and body tissue.
C. Exposed to a weaker solution showing erosion of
tail and fins 49
21. TL values for combinations ,of effluents.
A and B. Equal mixture of Station I and Station III
using Micropterus salmoides as test organisms.
C. Equal mixture of Station III and Station I using
Notemigonus crysoleucas as test organisms.
D. Equal mixture of Station I, Station II, and Station
VI using Notemigonus crysoleucas as test organisms ... 52
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TABLES
Table £^§.
1. Ranges for various parameters of Station I
effluents 27
2. TL values in per cent for Station I effluent 29
3. TL values in per cent for Station II effluent 30
4. Ranges for various parameters of Station III effluent . . 31
5. Parameters of Station III monitored throughout a
seven-hour period 3^
6. TLS_ values in per cent for Station III . . ....... 37
7. TL value ranges for Station III effluent ........ 39
8. TL,- values in per cent for Station IV
9. TL<-n values in per cent for Station V
10. Ranges or values for various parameters of Station V. . . 41
11. pH value ranges at the respective substations of
Station VI ........................ 42
12. TL™ values in per cent for all Station VI
substations
13. Conductivity range in micromhos/cm for respective
substations of Station VI . . . . .
14. Turbidity ranges expressed in Jackson Turbidity
Units (JTU) for all Station VI substations ........ 50
15. Total seston, abioseston, bioseston and dissolved
solids values in mg/1 for Station VI ........... 50
16. TL,-n values in per cent of combinations of
Stations I, III, and VI ................. 51
17. Characteristics of Station VIII effluent ......... 53
18. Summary of test runs involving eggs and fry (1970). ... i»5
viii
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Table
Paee
19. Summary of test runs involving eggs and fry (1971). ... 57
20. TL values for eggs or fry using Station II effluent . . 59
21. TL values for eggs or fry using Station III effluent. . go
22. TL values for eggs or fry using Station VI effluent . . 62
IX
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SECTION I
CONCLUSIONS
1. Results of this 27-month investigation on the Trinity River support
the generally accepted idea that the discharge of untreated industrial
wastes directly into a stream of limited flow is capable of upsetting its
ecological balance to the extent that populations may be almost or
completely destroyed.
2. Data collected in this investigation show that certain industrial
wastes do alter the composition and distribution of faunal and floral
populations in a stream.
3 The Trinity River and streams of similar size usually do not have
a'volume of water to dilute toxic effluents sufficiently to render them
harmless to the river biota. This was especially true with respect to
Stations I, III, V, and VII.
4. Effluents containing fuel oil, grease, and detergents such as that
from Station I, a railroad equipment cleaning area, are quite toxic to
fish and benthic organisms. Effluent from this particular station varied
in quality but toxicity remained consistently high.
5. The following parameters of the Trinity River, pH, COD, BOD, phos-
phates, and specific conductance, were affected by efflueats containing
detergents, grease, and fuel oils.
6. Untreated or improperly treated sewage has adverse effects on fish
as observed in this study at Stations II and VII. The adverse effects
appear to result from oxygen depletion rather than direct toxicity.
Test organisms survived in 100% concentration of the effluents when
aerated.
7. Storm sewer effluent (Station II) did not appear to have an
appreciable effect on the Trinity River. However, conductivity of the
effluent was high and there was a slight rise in COD and nitrate values
downstream from the outfall.
8. Floe in effluent from a catalyst producing plant (Station III)
greatly altered the environment in the vicinity of the outfall and for
a considerable distance downstream. This was evidenced by fish floating
lifelessly in the effluent plume and presence of benthic organisms from
midstream to the bank opposite the outfall. The current usually did not
permit the effluent to spread over the entire width of the river.
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9 Station III effluents contained chemical substances that exerted
very adverse effects on the flora and fauna. These effects were appar-
ent for a considerable distance downstream. Flocculent material in this
effluent accumulated around the gills of fish. This suggested possible
adverse effects of a physical nature. Laboratory tests using super-
natant fluid showed less toxicity to test organisms than the intact
effluent.
10. Effluent from Station III stored for several days under laboratory
conditions showed no reduction in toxicity.
11. Fish exposed to Station III effluent suffered direct injury to the
gills. Blood was released from the gills and rather extensive gill
tissue erosion resulted from relatively short exposure in laboratory
tests.
12. Station III effluent affected the chemistry of the river water
with respect to the following parameters: pH, conductivity, alkalinity,
COD, nitrates and orthophosphates .
13. The volume of suspended material in Station III effluent that may
settle out was sufficient to impair benthic life regardless of toxicity.
14. Station III, as of July 1, 1971, diverted its waste effluents into
the sanitary sewer and through the sewage treatment plant. The region
near the outfall is clearing and in time populations are expected to
become established in areas formerly not inhabited.
15. Effluents from a plant primarily engaged in metal etching (Station
VI) were the most toxic of the effluents tested as demonstrated by
response of catfish eggs, fry and mature minnows. The buffering effect
of lime dumped into Station VI holding pool reduced toxicity of this
effluent for fish. It is concluded that direct discharge of Station VI
effluent into the Trinity River would have widespread effects on the
river biota.
16. Any combination of equal amounts of effluents from Stations I, III
and VI show antagonism. However, because of distance between the
respective industries, the ill effects of one may not be countered by
another.
17. Results from laboratory experiments indicate that fish spawn and
fry serve well as test organisms in bioassay work. However, limited
time of availability is possibly the greatest drawback to their use.
18. Laboratory observations suggest that embryonic membranes of pre-
hatched fish afford considerable protection against the various indus-
trial effluents studied.
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19 Fry surviving bioassay tests of Station I and III effluents lived
for periods up to 10 weeks when transferred to holding aquaria. Some
of these fry developed marked orientation problems while others showed
considerable variation in growth.
20 Sewage treatment plant effluents (Station V) caused a drastic
reduction in population at the outfall. Chlorination of the discharge
is believed to have contributed appreciably to the adverse effects on
the biotic community. The effluent also altered BOD, COD, and phosphates
of the river water.
21 Effluents from a food packing plant and other light industries
discharged into a tributary (Station X) apparently had no significant
effect on the Trinity River. Chemically, a slight increase in ortho-
phosphates was noticed.
22 Toxicity of a chemical company primarily engaged in production of
acids appeared to be held well under control as long as their present
treatment system (buffering) functioned properly .
23 Station VII, a sewage treatment plant, is very ineffective in its
present state of repair. Diversion of its effluent to the Fort^orth
sewage treatment system will alleviate any problem associated with it.
24. Organic materials from the stockyards and meat processing plants
made conditions favorable at the mouth of a small tributary (Station IX)
for large numbers of Tubificidae but decreased diversity of benthic
organisms. Nitrate and specific conductance values in the Trinity River
were increased below the mouth of this tributary.
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SECTION II
RECOMMENDATIONS
Ttie Trinity River in the study area, Tarrant County, Texas, is a stream
with limited volume of flow. Since the Trinity River is the sole ave-
nue for transporting industrial and domestic wastewater from the area,
great stress is placed on it especially during the mouths of low rain-
fall. Although all industries in the area do not discharge their
wastes directly into the river, those that do plus discharge from
sewage treatment plants somewhat likens the river to an open sewer in
places. To alleviate this situation by closing an industry or
industries is not necessarily the best solution to the problem.
There are several ways by which pollution abatement may be promoted.
Recommendations that will reduce or possibly eliminate pollution for
those industries that discharge wastewater directly into the Trinity
.River or any other stream are as follows:
1. It may be economically feasible to recover some of the basic mate-
rials from the effluent for reuse thus improving the quality of the
wastewater. A chemical plant discharging at Station III has initiated
this procedure since the beginning of this investigation. This prac-
tice should be given careful consideration by any industry whether or
not it discharges wastes directly into a stream or uses the sanitary
sewer system.
2. Wastewater may be reclaimed for reuse. Such is recommended espe-
cially in this general region. It serves as an available source of
water and lessens pollution. Companies using great amounts of water
such as the railroad equipment cleaning area at Station I and the
chemical plant at Station III may find it economically feasible to
consider this procedure.
3. Effluents may be held in pools permitting suspended materials to
settle and partially degrade prior to release. The railroad cleaning
facility uses a detention pool. Because of the high toxicity of its
effluent and the fact that effluent is discharged into the river below
a dam where flow is usually extremely limited, it is recommended that
the holding pool be increased in size permitting maximum degradation
before being released. It is further recommended that oil and grease
floating on the surface be siphoned off periodically and not permitted
to enter the pipe line to the Trinity River. Even under present
conditions the effluent should be released on a more gradual basis over
extended periods so that the impact on the river is not so great.
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4. The pollutant may be either removed from the effluent or treated to
render it less toxic. The metal etching plant at Station VI uses a
holding pool and treats the effluent from time to time with lime.
Since the effluent is still usually very acid from one area, a more
systematic and efficient buffering system should be considered. A
chemical company discharging at Station IV uses such a system with
favorable results. Not only the industries involved in this investiga-
tion but those in other areas as well should study their processing
procedures to determine changes that might be made which would
eliminate, or at least reduce the release of pollutants in the process
fluid.
5. Untreated and improperly treated sewage periodically enters the
Trinity River at Station II and Station VII. Every effort should be
made to prevent such material from being discharged into the Trinity
River.
6. It is recommended that results of this investigation be made
available to all industrial plants which discharge into the Trinity
River at stations mentioned in this report.
7. Additional studies should be made similar to this one to cover a
greater number and variety of industries. This would give a more
complete picture of the pollution situation along the upper Trinity
River and serve as an index of what may be taking place along other
streams of similar flow through an area of comparable industrialization,
The study should include long range survival of fry exposed to various
polluting effluents.
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SECTION III
INTRODUCTION
Since water supply, water pollution control and water reuse are so
important and vital to future economic growth, health and welfare,
Kalinske (1967) expressed concern that our nation had allowed the
existing water situation to become as critical as it has today.
Despite the fact that our water situation may be less than desired,
problems concerning water pollution were recognized over 100 years ago.
Penny and Adams (1863) investigated pollutants in the River Leven.
However, it was not until after the turn of the century that Shelford
and Wells began to concern themselves with related experimental work
in this country. As related by Mackenthun (1969), "Water quality
affects man in his direct use of ^the water; it affects also the
aquatic life that water contains".
The presence or absence of living organisms in accordance with their
individual demands and tolerances might well be indicative of water
quality. Disregard for aquatic life could result in compounded prob-
lems with respect to pollution abatement. Pollution and overfishing
have almost destroyed the fishery industry in Lake Erie and domestic
wastes have essentially obliterated shellfish industry of the upper
Mississippi Valley (Black, 1968).
Pollution damage results from three major causes - domestic, agricul-
tural and industrial wastes. Domestic and agricultural wastes are
quite common and widespread. Industrial pollution is very diverse and
critical. Hart, Doudoroff and Greenbank (1945) wrote a book dealing
with this aspect.
Among domestic wastes, detergents, soaps, liquids and organic substances
passed through disposals get into the sewer system and eventually into
streams. The effects of synthetic detergents and soaps on fish varies
with the type substance and quality of water (hard/soft) . Henderson,
Pickering and Cohen (1959) found that some household soaps were more
toxic to fathead minnows in soft water than synthetic detergents but
less toxic in hard water. Respiratory stress seems an apparent reac-
tion to synthetic detergents. Although detergents do not appear to
have a lethal potential comparable with cyanides, heavy metals and
insecticides, the increase in use and possible indirect effects on
aquatic life deems it necessary to keep detergents under constant
surveillance.
Ingredients of fertilizers such as phosphates and other chemicals, silt
eroded from cultivated fields and pesticides of various types are among
the agricultural wastes. The use of insecticides and herbicides is
increasing and is posing problems with respect to aquatic life.
Toxicity of insecticides is greater on a specific quantity basis (ppmj
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than herbicides (Jones, 1966). However, the use of herbicides for
control of aquatic plant life must be in such high concentrations that
they approach the lethal level for fish and other fauna. Henderson,
Pickering and Tarzwell (1959, 1960) did extensive work with chlorinated
hydrocarbon insecticides using bluegills, guppies and goldfish as test
organisms. Bluegills were most sensitive to the chemicals and endrin
was the most toxic of the insecticides. A comparison of toxicity of
organophosphorus insecticides to fish with that of chlorinated hydro-
carbons has shown that the latter are more toxic. Organophosphorus
insecticides are less stable in water than chlorinated hydrocarbons
which make them less dangerous to fish.
Industrial wastes are too numerous to name all but include lubricating
oils, grease, acid, alkali and heavy metals such as mercury, copper,
lead, zinc and others. The effects of heavy metals such as lead,
copper, zinc and others have received considerable attention. Lead,
copper and zinc have proved to be very toxic to various organisms .
Doudoroff (1952) demonstrated that a mixture of copper and zinc has a
synergistic effect on minnows (Pimephales). Jones (1938) demonstrated
that lead reduces the toxicity of copper to various freshwater inverte-
brates. Calcium reduces the toxicity of certain heavy metals, espe-
cially copper. According to Mount (1968) , results of bioassays made
only in soft water may be misleading.
With the increase in pollution and realization of its seriousness, field
and laboratory work have been instituted to obtain useful information
concerning source, type and control. Some of the early work was done
along the Illinois River by Forbes and Richardson (1913, 1919) and by
Forbes (1928) especially pertaining to organic pollution. Richardson
(1921) described variation in bottom fauna of the Illinois River
resulting from increased movement of sewage pollution. Purdy (1916)
demonstrated the value of certain organisms to indicate sewage discharges
in the Potomac River. Organic enrichment of running waters and abrupt
changes in biota following introduction of waste materials were reported
by Weston and Turner (1917), Butterfield (1929) and Butterfield and
Purdy (1931). They pointed out that as the wastes were consumed or
utilized there was gradual recovery of the biota downstream.
Species diversity and population studies have been used in several
instances to show proof of disruption of water quality suitable for
aquatic life. Cross and Braasch (1969) reported a great decrease in
the fish population in the Neosho River, Kansas between 1952 and 1967.
The greatest deterioration of the population occurred in an area where
previous fish kills had been reported due to cattle feed lot runoff .
Fish kills were reported by Williams et al. (1966) in the Ohio River in
the summers of 1962-1964. These fish kills were attributed to organic
matter and heavy metal accumulation in deep pools during periods of low
flow. The accumulation created serious problems during periods of high
flow when the organic matter aiv' heavy metal went into suspension, and
in conjunction with higher tempeiacures, the lowering of dissolved
oxygen (DO) occurred.
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Wheeler (1969) reported a decline in the fisheries on the Thames River
and attributed this to pollution. A winter fish kill in a reservoir in
Iowa was reported by McDonald and Schmickle (1968) and the ascribed
cause was high oxygen demand in runoff water. Kussat (1969) surveyed
two regions of the Bow River in Calgary, Canada, one region upstream
from Calgary, and the other below Calgary. He observed a reduction of
species of benthic invertebrates, changes in the chemical nature of the
river, and an increase in the condition factor for rough fish downstream
from Calgary. These changes were attributed to industrial and domestic
waste discharges. The effects of coal washer water in Kentucky were
observed by Charles (1966). He reported that bottom fauna used as fish
food were reduced, and that the predominant fish in the polluted region
were channel catfish and suckers. Tsai (1968) observed that discharge
of chlorinated wastewater into the upper Patuxent River in Maryland
acted as a toxic material initially, reducing fish species diversity
and abundance below the outfall. Downstream the water was de-oxygenated
due to enrichment.
Other studies have been done on various industrial effluents to deter-
mine their toxicity to fish. Toxicity studies on refinery effluents
were conducted by Graham and Dorris (1968) on fish. They reported
adverse effects from sub-acute concentrations of effluents over lengthy
exposures. Patrick et al. (1968) studied the effects of twenty common
industrial effluent components on diatoms, snails and blue gill sunfish.
Thtfy reported various levels of sensitivity by all these organisms and
for several components, the sensitivity difference between the three _
organisms was quite pronounced. Not all effects of effluents are detri-
mental. Beadles (1966) observed that when wastewater from a refinery
was diluted to a certain level the size of the fish increased. It is
also common knowledge that certain nutrients are very beneficial when
present in tolerable concentrations. From this it can be seen that
industrial and domestic waste discharges present complex problems and
more than one factor may be involved.
Maintenance of the biotic community is necessary for proper ecological
balance. Destruction of the populations retards uptake and/or decompo-
sition of polluting substances in the water, thus prolonging their
effects and time the material is present. Bartsch and Churchill (1949)
described biotic response to stream pollution and associated aquatic
organisms to zone of degradation, active decomposition, recovery and
clean water. Patrick (1949) also described regions of the stream in
relation to pollution, separated biota into groups and illustrated^group
response to stream conditions. As pollution progresses, bottom lue
changes. Those organisms sensitive to a specific pollutant cease to
exist and are succeeded by more tolerant ones. Lagler (1956) lists
tubificid worms, leeches, mosquito larvae, rat-tail maggots, filter fly
larvae and fungus as the organisms more nearly to become dominant in the
regions of organic pollution. However, Gaufin and Tarzwell (ly^j
state that because of the wide range of natural situations that these
organisms inhabit, they may not always be true indicators of polluted
areas.
9
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The Clear and West Forks of the Trinity River converge near the center
of Fort Worth and continue along a winding course through Dallas .
Approximately 700 industrial plants ranging from a few employees (less
than ten) to more than 5,000 located in Fort Worth, discharge their
waste effluents either directly into the Trinity River or indirectly
through Municipal Treatment Systems which discharge into the river.
Approximately 200 more plants of varied sizes are located in the urban
area between Fort Worth and Dallas (F.W.C.C., 1968). Domestic wastes
from the urban districts are also discharged through treatment plants
into the river. The Trinity River, limited in size, is the sole avenue
for transport of waste effluents from the Fort Worth Area (Figures 1
and 2) . The stress placed on the Trinity River is greatly increased
during the summer months when rainfall is reduced to a minimum. The
availability of a ready supply of usuable fresh waster greatly influ-
ences urban and industrial planning. The biota of a body of water
contributes to the maintenance of a balanced system. Fish play a
significant role in perpetuating ecological equilibrium.
This report summarizes 27 months of research directed toward qualitative
and quantitative effects of certain industrial waste effluents being
discharged directly or indirectly into the Trinity River on selected
species of fish and other biota. To obtain a broader picture of impact
of the effluents, the project was divided into four facets: bioassay,
chemistry, growth and development, and benthos. Information gained
about parameters associated with the above categories will provide
evidence concerning toxic potential of the type pollutants for the
organisms involved and possibly facilitate the formulation of water
quality standards.
10
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Figure 1: Map of Texas showing Trinity River system,
11
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West Fork
IS 20
Sycamore
Creek
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SECTION IV
METHODS AND MATERIALS
Bioassay
The toxicity of complex waste effluents from industrial plants was
determined by bioassay and the results (TL50 - median tolerance limit)
expressed as per cent. Both static and continuous flow through methods
were used.
Effluents were collected in the field in 5 gallon glass containers
and returned ^o the laboratory for processing. In order to avoid the
selection of solutions that might cause direct injury to test organisms,
static bioassay tests were conducted. A series of five concentrations
(100%, 75%, 25%, 12.5% and 6.25%) were used in the test. Two liters of
the respective concentrations were placed in wide mouth 1 gallon glass
jars along with two test organisms (fish). The lowest concentration
in which both test organisms were killed was selected as the highest
concentration to be used in the continuous flow system.
The continuous flow system used is a modification of the system
described by Mount and Brungs (1967). Modification was necessary in
order to deliver the large quantities of pollutant required. Diluent
water used was Fort Worth City water. A carbon filter was installed in
the water line to remove the chlorine. After moving through the carbon
filter the water passed slowly through a column of bone charcoal.
Approximately 200 gallons of filtered water was held in reserve.
The continuous flow system was equipped with six glass test tanks, each
with a capacity to the overflow of 20 liters. The complete volume of
fluid in each tank was replenished about six times in the course of
24 hours. The systems were arranged so that two series or duplicate
tests could be conducted concurrently. Each system had its own control
tank.
The test organisms (fish) were weighed in order to insure reasonably
uniform size. Ten fish were placed in each test chamber and the control
tank. This number made the results statistically significant. The
TL (concentration of toxicant in water that causes 50% mortality of
the test organisms in specified periods of time) was estimated from
observed mortality. Twenty-four, 48- and 96-hour time periods were
used. The fish were removed from the test chamber when dead. Deaths
.were recorded each 24 hours. Using semi-log paper (Figure 3) the con-
centration was plotted on the log scale against survival on the
arithmetic scale. Fifty per cent survival concentration was estimated
by a straight line graphical interpolation. The result is a direct
13
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Figure 3
TL PAPER
m
(Semi-log) shcet No- or Code:
1000
)0
)0
)0
10
10
»0
10
0
0
0
0
0
0
0
0
0
0
0
Lo
SC!
Startin^Date; Hour; .
Iim > IntprvaJ.s
Final TL
560 Results: '»
Concentrations Expressed as (circle one):
320 J L '
Dilution Water (source &i characteristics
180
Nr,t«.u- _..„__ .
100
56
32
1ft ...., .
0 50 100
g Percent Bioassay
lie Survival Concentrations
Note: This paper not commercially available.
BI. BIO. met. 15. 3.67
68-19
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comparative measure of toxicity under test conditions. A copy of the
semi-log paper was obtained through the Environmental Protection Agency
Water Quality Office in Cincinnati, Ohio, and duplicated.
The test organisms used in the bioassays were golden shiner
(Notemigonus crysoleucas (Mitchill)), fathead minnows (Pimephales
promelas Rafinesque), largemouth bass (Micropterus salmoides (Lacepede)),
channel catfish (Ictalurus punctatus (Rafinesque)), and hybrid sunfish
(longear - Lepomis megalotus (Rafinesque) and green sunfish - Lepomis
cyanella Rafinesque). The fish were obtained from the Fort Worth
National Fish Hatchery, Eagle Mountain Fish Hatchery and the Blue Top
Minnow Station. The chief sources of fish for the latter were fish
hatcheries in Arkansas. The fish were retained in a holding tank in the
laboratory for approximately 10 days to become acclimated to laboratory
conditions prior to use.
Turbidity was determined by a Hach Turbidimeter Modt 2100 and values
expressed in Jackson Turbidity Units (JTU) . A Sargent Portable pH
Meter was used to determine pH. A Yellow Springs Instrument Company
Model 54 Oxygen Meter was used to determine dissolved oxygen which was
expressed in parts per million (ppm). Other chemical parameters were
determined according to procedures in Standard Methods for the
Examination of Water and Wastewater (12th Edition) and FWPCA Methods
for Chemical Analysis of Water and Wastes, November, 1969.
Total seston was determined by the ignition method. The suspended
solids were removed from 4,000 ml of effluent by passing it through a
Foer^t continuous flow centrifuge. The residue was transferred to a
previously desiccated and weighed crucible. Fluid was evaporated from
the residue in an oven at approximately 130°F. After desiccation and
weighing the residue was placed in a muffle furnace and the temperature
was raised to 750°C. It was then cooled in a desiccator and weighed.
From the three weights, total seston, abioseston and bioseston were
calculated and expressed in milligrams per liter (mg/1).
Specific conductance was determined by using an Industrial Instruments,
Inc. Model RB3 Solu Bridge. The values are expressed in micromhos per
centimeter.
Growth and Development
Fish spawn and fry used were those available from the Fort Worth Federal
Fish Hatchery. Bass fry (Micropterus salmoides) averaging 21 mm in
length were available in mid May of 1971 and channel catfish (Ictalurus
punctatus) eggs and fry from two or three different spawnings were
available in June of both 1970 and 1971. One unsuccessful attempt was
made in March 1971 to use amphibian eggs as test material.
Most of the catfish eggs were brought into the laboratory in cooled
containers some four to five days prior to hatching where they were
-------
separated into reasonably small clusters before transferring to holding
aquaria. Thus they were available for some test runs prior to hatching
and other runs at various periods after hatching.
All tests (TL,-n) on eggs and fry were carried out at the same time
bioassays were being run on mature minnows or other fish. A modifica-
tion of the proportional diluter described by Mount and Brungs (1967)
was employed for all tests, Two batteries of six tanks each were
available at the beginning of these studies which permitted duplicate
test runs with the same effluent. By late June of 1970 two other
batteries of six tanks were completed permitting two duplicate test
runs using two different effluents. Dilutions of effluent used for
each test were based on static tests using mature minnows. Conducting
tests on fry simultaneously with tests on mature fish permitted later
comparison of survival values between immature and mature organisms.
Eggs and fry were suspended in clear plastic cups in each dilution of
the effluent. These cups were 3 inches high and tapered from 3 inches
in diameter at the top to 2 1/4 inches at the bottom. In the first
preliminary tests of 1970 the bottoms of these cups were removed and
replaced with silk bolting cloth. It was discovered in this initial
test run that the bolting cloth did not permit ready circulation of
fluid through the cups particularly when the effluent contained
flocculent precipitates. The cups were redesigned by leaving the
bottoms intact and drilling a number of 1/16 inch holes in the bottoms
and some half way up the sides. An average of 16 of these holes were
drilled in the bottom of each cup and 28 in the sides. It was found
that the drilled cups when submerged to a depth of about 2 inches
did permit adequate circulation of fluid through the cup during the
course of the test and in general gave a satisfactory performance.
The optimum number of test organisms per cup presented a problem in the
early stages of study. After the first two test runs where 20-50 eggs
per cup were used the number was reduced to 10 per cup and this worked
well for most of the remaining tests. In the case of the bass fry
tested in May 1971, it was found desirable to reduce the number of fry
to five per cup and to suspend two or more cups per tank.
During each test dead fry were removed from the test cups at regular
intervals, examined visually under low magnification for damage and then
preserved in 8% formalin for future study. Beginning with Series VIII
(June 1971) survivors from each cup for each test were transferred at
the end of the test to individual floating cups which were maintained in
the holding aquarium for periods up to 10 1/2 weeks. Fish were fed
daily and observed for morphological changes. Periodic survival counts
were made and dead fry were preserved in formalin. The floating cups
used here consisted of "SPECTRUM" white plastic cups measuring 3 inches
in diameter and 2 inches deep. Approximately two dozen holes (1/16 in.)
were drilled in the bottom of each cup and an additional 20 holes
drilled in the lower half of the sides. Four small styrofoam floats
16
-------
were attached to each cup just below the rim. The cups floated freely,
permitting adequate circulation of water through the pores and were
easily cleaned.
Chemistry
Samples were taken from two areas on the Clear Fork of the Trinity River
and from four areas on the Trinity River below the junction of the Clear
and West Forks of the Trinity River. Station I is an effluent from a
railroad equipment cleaning area which enters the Clear Fork of the
Trinity River just downstream from the new Vickery Street dam (Figure 4) .
An outfall from a storm sewer receiving effluents from small industries
and some untreated sewage is Station II (Figure 5) . Station III is an
outfall from a chemical plant which manufactures cracking catalysts
and enters the Trinity River just downstream from the North Main Street
viaduct (Figure 6). A sewage treatment plant outfall represents
Station V (Figure 7) while Stations IX and X are tributaries which
empty into the Trinity River (Figures 8 and 9) . Each of thfese sampling
areas or stations were subdivided into five substations: one sub-
station upstream from the outfall designated as "A", a second sub-
station at the outfall designated "B", a third substation designated
"C" at the point of initial mixing of the discharge with the river, and
fourth and fifth substations designated as "D" and "E", respectively at
a distance of 200-400 yards and 400-800 yards, respectively from the
point of discharge. All samples were taken in order "A", "B", "C",
"D" and "E" within the shortest possible time. Subsequent samples at
a station were taken at two day intervals except when weather
conditions, high water or construction prevented sample collection.
Samples were marked as "A", "B", "C", "D" and "E" for the first series
of samples then "A ", "B2", "C2", "D2" and "E2" for the second series
and so on through five series of samples for each station.
Three series of samples were taken at Station V, the sewage treatment
plant, before it was realized that there were two discharge outlets
for this plant. After this, four series of samples were then made up
of nine samples each. The first three series were designated in
the same manner as the other stations, but the next four series of
samples were made up of nine samples. Since this newly discovered
outfall was upstream, four new substations were designated. Substation
"A*" was upstream from the new outfall, "B*", new outfall, "C*", initial
point of mixing of new outfall and stream, and "D*", about 250 yards
downstream from the new outfall. The original Substation "A" was
redesignated as "E*" and was located about 400 yards downstream from the
south outfall and about 40 yards upstream of the north outfall. The
original "3", "C", "D" and "E" remained the same. The new series was
numbered "A *", "B4*", "C4*", "D4*", "E4*", "B4", "C " "D4" and "E4".
The asterisk designates the new stations from those downstream. This
series continued through "A*", "B *", "C *", "D *", "E *", "B ",
"C ", "D-," and "E ".
17
-------
Figure 4. Map of Station I showing substations
Scale: 1 inch - 2,000 feet.
18
-------
Figure 5. Map of Station II showing substations
Scale: 1 inch = 2,000 feet.
19
-------
Figure 6. Map of Station III showing substations
Scale: 1 inch = 2,000 feet.
N
•
20
-------
Sewage
Disposal
Plant
Figure 7. Map of Station V showing substations
Scale: 1 inch * 2,000 feet.
21
-------
(I
Figure 8. Map of Station IX showing substations
Scale: 1 inch - 2,000 feet.
22
-------
N
Figure 9. Map of Station X showing substations
Scale: 1 inch = 2,000 feet.
23
-------
Water samples were initially collected in 1 gallon, wide mouth jars.
Samples were taken in midstream at approximately half the distance
between surface and bottom, except where high water necessitated
collection nearer one bank.
When the samples arrived in the laboratory, they were each shaken
well, a portion was taken from each for immediate analysis and the
rest was stored at 4°C until needed for further analysis.
Water temperature was taken by using either a mercury thermometer in
shallow water or a Yellow Springs "Instruments Hydro thermometer stand-
ardized against a mercury thermometer in deeper water. All readings
were reported as degrees centigrade. Temperature was the only
parameter measured directly while in the field.
Dissolved oxygen samples were taken by using standard BOD bottles
which were filled at the river by using a hand barrel pump when
possible. Bottles were overflowed approximately three volumes and
care was taken to prevent entrapment of air bubbles. The method
used in analysis for dissolved oxygen was a sulfamic acid Alsterberg
modification of the Winkler method (Standard Methods for the
Examination of Water and Wastewater, 12th Edition, 1965) .
Determination of pH values were made in the laboratory using a calomel
glass electrode, a Sargent-Welch or a Beckman Zeromatic pH meter.
Alkalinity measurements (phenolphthalein and methyl orange) were made
in accord with Standard Methods for the Examination of Water and
Wastewater, 12th Edition, 1965 and expressed as mg/1 of CaCO .
The procedures for BOD (biochemical oxygen demand) determination were
those in Standard Methods for the Examination of Water and Wastewater,
12th Edition, 1965. Some samples, due to their high oxygen demand, were
diluted to 1/2 and 1/4 with downstream water from Substation E.
Station V required special dilution water because the oxygen demand of
the downstream water was too high. Dilution water was made according
to the procedures in Standard Methods for the Examination of Water and
Wastewater, 12th Edition, 1965. In the case of the sewage treatment
plant effluent, the BOD samples were diluted to 1/10 and 1/50.
Chemical oxygen demand (COD) was determined using the method proposed by
Standard Methods for the Examination of Water and Wastewater, 12th
Edition, 1965. The equipment used was 250 milliliter erlenmeyer flasks
with ground glass 24/40 necks and 300 mm jacketed or equivalent
condensers and hotplates .
The Brucine method was used for analysis of nitrates (Standard Methods
for the Examination of Water and Wastewater, 12th Edition, 1965) . Each
series of samples were accompanied by standards and a control blank.
The results were recorded in mg/1 NO_-N. This value was converted to
mg/1 NO by multiplying the value for mg/1 NO -N by 4.43.
24
-------
Orthophosphates and hydrolyzable phosphates were both determined using
the method prescribed by the Federal Water Pollution Control Adminis-
tration's publication, "FWPCA Methods for Chemical Analysis of Water
and Wastes", November 1969. Samples were analyzed as quickly as
possible after returning them to the laboratory.
Analysis for Ca, Mg, Cu, Zn and Fe followed those methods set forth by
"FWPCA Methods". This was accomplished by filtering 250 milliliters
of each sample through a 0.45 micron membrane filter. To the 250
milliliters of sample 0.75 milliliters of 1:1 HNO was added. The
1:1 HNO,, was made with demineralized water, using an ion exchange
column. Each sample was then analyzed for the individual elements
Ca, Mg, Cu, Zn and Fe. A Perkin-Elmer 303 Atomic Absorption Spectro-
photometer was used, using a Texas Instruments chart recorder, a
Boling three slot burner, and an air-acetylene flame. A standard
curve was prepared everyday for each element before each series of
samples were analyzed.
Per cent organics were determined for Stations I and III because of the
high suspended solids content found in these effluents. The filter
used in the analysis for Ca, Mg, Cu, Zn and Fe, was carefully oven
dried at 102°C for several hours. The thick residue on each filter
was carefully scraped into a pre-weighed combustion boat. This boat
was put into a Sargent combustion apparatus using anhydrone and
ascarite for collection of water and (XL respectively. A flow of
about 90 bubbles per minute of compressed oxygen was passed through
the combustion tube. The temperature of the combustion apparatus was
approximately 625°C for the stationary element and about 700°C for
the chain driven element. Per cent carbon was determined by
multiplying the weight gain of the ascarite by the decimal fraction
of carbon in CO .
Benthos
Effects of effluents on the benthic invertebrate populations were
studied at seven areas along the Trinity River. Samples were obtained
with a 1/25 W VanVeen grab sampler. One pint aliquots were taken
from the top of the grab making sure to get the surface down to several
inches. This allowed for more samples to be taken since the amount of
space required and the washing time for each sample was reduced
considerably. Taking samples in this manner also helped reduce error
resulting from variations in depth of the grab bite.
Ten samples were taken along each of four transects. Sample 1 was
taken on the side of the river nearest the outfall while number 10 was
near the opposite bank. Transects were located 25 yards upstream from
the mouth of the outfall; at the mouth; and approximately 30-70 yards
and 150-600 yards downstream from the outfall. The maximum depth of
penetration of the benthos was measured by core sampling.
-------
Samples were preserved in 10 per cent neutralized formalin and later
washed through a .25 mm standard mesh screen #60. The animals were
preserved in 70 per cent alcohol and identified to taxa.
Since benthos in this study were used primarily as monitors for toxic
materials, specific identification was not deemed necessary. When
pollution is heavy, whole taxonomic groups rather than individual
species are affected (Hynes 1960) .
Taxonomic resources included: Chu (1949), Eddy and Hodson (1961),
Pennak (1953), Edmondson (1959) and Stephenson (1930).
Station Identification
Station Description
I Outfall from a railroad equipment cleaning area
II Typical storm sewer receiving some effluent from small
industrial plants and some untreated sewage
III Chemical plant producing cracking catalysts for
processing combustion engine fuels
IX Chemical plant producing various types of acids
V Sewage treatment plant receiving industrial and domestic
wastes (trickling-filter type)
VI Plant primarily engaged in metal etching using various
acids
VII Sewage treatment plant in a poor state of repair
(Imh off-lagoon)
VIII Fuel oil and gasoline bulk loading station
IX Small tributary receiving effluents from meat packing
and rendering plants
X Tributary receiving effluents from various small industries
and a food packing plant
26
-------
SECTION V
OBSERVATIONS
Bioassay
Station 1: Railroad Equipment Cleaning Area
Effluent from a railroad equipment cleaning area was selected for
initial testing. This station is the farthest upstream (Trinity River)
that was studied. Discharge of effluent was not continuous but on an
intermittent basis. Fluid is released during the day and varies from
a slight trickle or no flow at all to approximately 3 gallons per
second. Quality of the fluid varied from time to time. Detergents,
fuel oils and grease were among the primary constituents of the
effluent. Other characteristics are listed in Table 1.
Table 1. Ranges for various parameters of Station I
effluent.
Effluent Range
Dissolved oxygen 2 - 9.4 ppm
Free carbon dioxide 0
Ph-th alkalinity 490 - 572 ppm
M.O. alkalinity 200 - 280 ppm
pH 10.1 - 11.5
Turbidity 50 - 55 JTU
Conductivity 1,500 - 2,400 micromhos/cm
Total seston 73.95 mg/1 - 185.5 mg/1
Bioseston 20.87 mg/1 - 48.75 mg/1
Abioseston 53.07 mg/1 - 136.75 mg/1
Dissolved solids 786.75 mg/1 - 1.483 g/1
Like other qualities of this effluent TL „ values varied. Several
tests were conducted involving a variety of test organisms in order
to establish a TL_n range. Table 2 and Figure 10 show the results
of the various tests.
In early stages of the study it was found that effluent stored in the
laboratory at room temperature for as long as five days increased in
toxicity. This was demonstrated through successive tests using
N. crysoleucas as test organisms. A satisfactory explanation has not
been established. The increase in toxicity may be accounted for in
part by the length of time effluent was held in detention pools in the
railroad yard before being released. Similar successive tests were
27
-------
;
i:
10
24 hr TL
48 hr TL
96 hr TL
mimiiiiiimn
II II II
11-7-69 11-12-69 11-19-69 11-22-69
11-27-69 12-5-69
20
II
12-10-69
1-9-70
1-12-70
9-4-70
9-9-70
6-16-71
Figure 10. TL^ values for Station I effluents using golden
shiners (Notemigonus crysoleucas (Mitchill)) as test
organisms.
£
-------
Table 2.
TL „ values in per cent for Station I effluent.
Date 24 hrs 48 hrs 96 hrs Test Organism Av.Wt.G,
11-7-69
11-12-69
11-19-69
11-22-69
11-27-69
12-5-69
12-10-69
1-9-70
1-12-70
9-4-70
9-9-70
6-16-70
6-16-70
3-13-70
3-13-70
3-18-70
3-18-70
3-24-70
6-22-70
6-22-70
8-17-70
3.0
8.0
12.0
3.4
*
10.4
13.0
16.0
14.0
14.4
14.5
*
*
18.0
14.0
16.0
15.0
16.0
11.5
11.5
4.4
5.5
.0
,6
.0
7,
7.
3.
7.5
9.0
12.0
12.0
11.0
12.5
10.5
18.0
20.0
17.0
14.0
15.0
12.2
15.0
10
10
3.5
4.6
5
75
6.0 N_.
6 .0 N_.
2.5 N_.
7.5 _N.
8.0 N_.
11.5 _N.
7.0 N_.
6.0 N_.
8.0 N_.
3.4 N_.
18.0 N_.
18.5 N_.
15.5 P_.
14.0 P^.
14.0 P_.
11.4 P_.
8.0 P_.
9 .2 M
6.5 M
2.5 1^. punctatus
3.3 _!_. punctatus
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
cryspleucas
crysoleucas
crysoleucas
Crysoleucas
crysoleucas
crysoleucas
crysoleucas
promelas
promelas
promelas
promelas
promelas
salmoides
salmoides
2.1
2.1
1.98
2.0
2.1
2.2
2.2
2.0
2.1
2.2
2.0
1.9
1.9
2.1
2.1
1
1
2.1
1.4
1.4
0.53
0.53
.98
.98
*No mortality
conducted but a marked increase in toxicity was not detected.
Pimephales promelas as well as N_. crysoleucas were used as test
organisms. It was observed that P_. promelas was more tolerant to
the effluent than N_. crysoleucas.
Although Station I effluents vary in quality from time to time, the
XL value is relatively consistent. The TL^Q does range between
2.5% and 18.5% for 96 hours but of the 22 tests conducted, only seven
values for 96 hours were above 10.0% (Table 2).
Heavy foaming accompanied the effluent because of its content of
detergent plus agitation as it was being discharged. The foam covered
a large area of the river in the vicinity of the outfall and extended
a considerable distance downstream. The presence of the foam is
normally considered to impair uptake of oxygen by the water and reduce
light penetration which in turn reduces photosynthesis and release of
oxygen. The toxic quality of the effluent combined with the insulating
effect of its foam result in definite undesirable effects on the biota
of the surrounding environment.
-------
Station II: Typical Storm Sewer Receiving Effluent from Small
Industrial Plants and Some Untreated Sewage
Station II outfall is located approximately 1 mile downstream from
Station I. Effluent from this outfall contained a variety of
substances including untreated sewage and nontoxic substances. The
pH ranged between 7.1 and 7.5, dissolved oxygen 3.0 - 7.0 ppm and
conductivity not over 750 micromhos per centimeter.
are listed in Table 3.
The TL values
Table 3. TL
Date 24 hrs
values in per cent for Station II effluent,
48 hrs 96 hrs Test Organism Av.Wt.G,
9-26-70
9-26-70
9-29-70
9-29-70
9-30-70
9-30-70
42
42
42
42
42
42
42
42
42
42
42
42
*
*
N_. crysoleucas
N_. crysoleucas
I_. punctatus
I_. punctatus
I_. punctatus
I_. punctatus
2.2
2.1
2.0
2.1
2.1
*No mortality
The test organisms, 1$. crysoleucas, did not survive more than 2 hours
in the 100% and 50% concentrations, but there was 100% survival in all
other concentrations. Using effluent from the same collection and
i- punctatus as test organisms, the test was repeated with identical
results. It was found that by aerating the 100% and 50% solutions for
1 hour before exposure both JU punctatus and N_. crysoleucas survived
in all concentrations throughout the 96-hour test period. This
observation indicated that the mortality in previous tests was probably
due to lack of oxygen. The effluent appeared to have a high content
of raw sewage from some place and the rapid decomposition of organic
material was considered to account for the low dissolved oxygen.
Subsequent tests of the effluent from this outfall resulted in no
mortality of the test organisms in 100% or lower concentrations, even
though none of the concentrations were aerated. It seems apparent that
the most undesirable quality of the Station II effluent is the raw
sewage that is present from time to time. Decomposition of the organic
matter could reduce the oxygen supply and effect an extensive
environmental stress on the fauna.
Station III: Chemical Plant Producing Cracking Catalysts for
Processing Combustion Engine Fuels
Station III is approximately 2 miles downstream from Station II.
Effluent is discharged through a tile sewer approximately 20 inches
30
-------
in diameter into a pool approximately 20 yards from the edge of the
Trinity River when it is at its normal level. It flows freely from
the pool into the river. During periods of excessive rain this outfall
is obscured by high water. The flow of effluent is intermittent and,
at times, may fill the tile sewer to a depth of 10 - 12 inches. A
valid estimate of peak flow in cubic feet per second was not
ascertained because of the volume and force of the flow.
The effluent contains a white floe which usually gives it a milky color,
although at times it may take on an aqua or orange tint (Figure 11).
The floe settles rapidly and is deposited in great quantities in the
area of the pool. An extensive plume caused by the floe may be seen
in the Trinity River (Figure 12). Other characteristics of the effluents
are listed in Table 4.
Table 4. Ranges for various parameters of Station III effluent.
Effluent Range
Dissolved oxygen 4.9 - 10.3 ppm
Free carbon dioxide 0
Ph-th alkalinity 0.00 - 1,480 ppm
M.O. alkalinity 3.4 - 2,046.0 ppm
pH 1.5 - 11.9
Turbidity 36 - 95 JTU
Conductivity 1,150 - 8,000 micromhos/cm
Total seston 9.1 - 556.1 mg/1
Bioseston 2.1 - 116.3 mg/1
Abioseston 28.8 - 434.7 mg/1
Dissolved solids 194.5 - 8,835.0 mg/1
Variations in pH as well as color prompted a continuous monitoring
of the station throughout a working day. Parameters monitored and
their values are listed in Table 5.
The TL,-n values for Station III were rather varied. Table 6,
Figure 13 and Figure 14 show the various test results.
Gills of each of the dead test organisms were examined and found to
be coated with a heavy layer of the white floe from the effluent. This
floe, imbedded in mucus, was of such copious supply that each operculum
was greatly distended. This suggested a possible physical effect on
the fish. Tests were repeated using fluid without the floe. The TL..Q
for fluid containing the floe was 24.0% for 24 hours, 12.5% for 48
hours and 7.0% for 96 hours. Using only the supernatant, the TL^ was
41.0% for 24 hours, 38.5% for 48 hours and 34.5% for 96 hours. The
test organism used was P_. promelas . Since effluents for the two tests
31
-------
Figure 11. Station III outfall evidencing white floe in effluent,
-------
Figure 12. Plume in the Trinity River caused by floe in Station
III effluent.
-------
Table 5. Parameters of Station III monitored throughout
a 7-hour period.
Time of
Surge
8:55
9:10
9:26
9:43
9:57
10:12
10:25
10:41
10:57
11:11
11:25
11:40
11:53
12:07
12:21
12:34
12:48
1:02
1:17
1:31
1:44
1:58
2:12
2:28
2:48
3:00
3:13
3:27
3:47
4:00
pH Temperature
Centigrade
7.5
5.8
6.2
1.9
3.0
4.5
6.2
6.5
6.4
6.6
6.5
3.3
1.8
3.35
4.4
5.7
6.1
6.3
5.9
6.1
2.25
2.8
4.5
6.35
6.1
2.5
2.1
2.8
5.7
6.6
25°
26°
25.5°
25°
24°
25°
26°
26°
23.5°
22°
22°
23.5°
23.5°
28°
28°
28°
28°
26°
23.5°
23°
23°
28°
28.5°
29°
26°
24.5°
25°
27°
30°
29°
Specific
Conductivity
2,050
2,050
1,600
-H-8,000
+8,000
4,000
3,750
3,250
3,000
2,250
2,200
+8,000
-H-8,000
6,500
3,750
4,500
3,500
3,000
2,500
4,000
++8,000
+8,000
4,000
3,500
3,250
+8,000
++8,000
5,500
5,500
8,000
Dissolved
Oxygen
6.15
5.7
5.7
5.8
5.6
5.8
5.7
5.6
6.0
6.0
6.1
5.9
5 .7
5.2
5.2
5.2
5.2
5.5
5.7
5.7
5.7
5.1
5.1
4.9
5.4
5.6
5.5
5.3
5 .0
5.1
+ = Greater than
++ = Much greater than
-------
•
'
M
24 hr TL
48 hr TL
50
96 hr TL
50
Plllllllllllllllll
II II II
*Pimenhales nromelas
**No mortality
2-24-70
2-28-70
4-6-70
4-24-70 5-20-70
5-23-70
6-3-70
6-9-70
6-13-70
Figure 13. TLsn values for Station III effluent using golden shiners (Notemigonus crysoleucas
(Mitchill)) and fathead minnows (Pimephales promelas Rafinesque) as test organisms.
-------
80
75
70
24 hr TL
5C
48 hr TL
5C
96 hr TL
50
•Illllllllllilllli
I II II II
*Pimenhales nromelas
65
60
55
50
30
25
20
15
10
6-25-71
TL values for Station III effluent using golden
shiners (Notemigonus crysoleucas (Mitchill)) and fathead
minnows (Pimephales promelas Rafinesque) as test
organisms.
-------
Table 6.
TL values in per cent for Station III.
Date
2-24-70
2-28-70
2-28-70
4-6-70
4-24-70
5-20-70
5-23-70
5-23-70
6-3-70
6-9-70
6-9-70
6-13-70
6-13-70
5-1-71
5-1-71
5-9-71
6-1-71
6-1-71
6-25-71
6-25-71
24 hrs 48 hrs 96 hrs Test Organism Av.Wt.G.
24.0
40.0
42.0
53.2
*
12.0
10.0
21.0
*
9,
9.
9,
9.0
78.0
78.0
30.0
8.0
7.2
3.3
3.3
.3
.3
.7
12.5
39.0
38.0
51.0
A
12.0
10.0
16.0
A
8.
,7
.6
.7
7
9
8.
74.0
74.0
30.0
8.0
7.0
3.3
3.3
7.0
39.0
30.0
45.0
A
12.0
10.0
16.0
A
6.2
5.6
8.6
6.6
56.0
56.0
30.0
6.5
6.5
3.3
3.3
P_. p r ome 1 as
P_. promelas
P_. promelas
N_. crysoleucas
N_. crysoleucas
—• crysoleucas
N_. crysoleucas
K[. crysoleucas
N_. crysoleucas
N[. crysoleucas
N_. crysoleucas
KL crysoleucas
N. crysoleucas
crysoleucas
crysoleucas
crysoleucas
p r ome 1 as
^ promelas
N_. crysoleucas
N_. crysoleucas
^
N_.
N_.
Itf.
P.
2.0
2.0
2.0
2.2
2.1
2.2
2.2
2.2
2.3
2.0
2.0
2.2
2.2
2.2
2.2
2.8
2.3
2.3
2.1
2.1
*No mortality
were collected at different times and since quality of the effluent
varied as reflected in Table 5, this and successive tests did not
prove conclusively that physical effects of the floe accounted for
the low TL values .
Gills of fish exposed to Station III effluent were examined grossly
and compared with gills of fish not exposed to the effluent. It was
observed that considerable gill tissue was eroded away after relatively
short periods of exposure in all concentrations (Figure 15) . Injury
to the gill membrane probably contributed to early death of some of
the test organisms .
Station III fluid was stored in the laboratory and successive tests
were conducted in an attempt to determine an increase or decrease in
toxicity with age. On the tests using N_. crysoleucas as test organ-
isms, it was observed that there was not more than 1.0% variation in
TL5Q values for 24, 48 and 96 hours, indicating that, this particular
collection of fluid was quite stable. However, variability in TL
values in previous tests plus differences in quality of the fluid
(Table 6) prohibit a conclusive statement about consistent stability
of Station III effluent. The variation in percentage for TL
determinations is shown in Table 7.
n
37
-------
. •1ft:
B
Figure 15. Gills taken from Notemigonus crysoleucas.
A. Gills taken from control—not exposed to Station III
effluent.
B. Gills taken from fish after exposure for 15 minutes
to a 100% concentration of Station III effluent.
38
-------
Table 7. TL5Q value ranges for Station III effluent
Time interval in hours 24 48 96
High % 78.0 74.0 65.0
Low % 3.3 3.3 3.3
Station III effluents varied extremely in quality as reflected in
Tables 5 and 6 and Figures 13 and 14. The pH and TL values were the
parameters most diverse in value. The cycling effect as indicated in
Table 5 accounted for the diversity in TL . When collecting the
effluent there was no way of telling what the stage of processing was.
While collecting sufficient fluid for a bioassay (150 - 175 gallons)
several surges occurred and pH frequently varied in the individual
containers. In an attempt to avoid great variation in quality of
effluent, no fluid was collected at the very start or very end of a
surge. However, quality of the fluid might vary from cycle to cycle.
The presence of the floe was very obvious as shown in Figures 11 and
12. The material greatly altered the environment in the vicinity of
the pool and the left bank of the river looking downstream. It had
a detrimental effect on the fish. On March 25, 1970, a rather
extensive fish kill was observed in the vicinity of the outfall. As
a result of high water, several gizzard shad (Dorosoma cepedianum
(LeSueur)) and river carpsuckers (Carpiodes carpio (Rafinesque))
were apparently trapped in the pool into which the effluent was
discharged. The fish were in such a state of decomposition when
discovered that an autopsy was inconclusive. At times fish were
observed floating lifelessly on their backs in currents of Station III
effluent.
On July 1, 1971, this chemical company completed its installation of
equipment to reclaim some of the material being discharged into the
Trinity River. Also, their effluent was diverted to the sanitary
sewer and directed through the Fort Worth Sewage Treatment Plant.
A sample of the effluent after it passed through the clarifiers and
released into the large holding pools was tested. There was no
mortality in the undiluted fluid. The system installed accounted for
a better quality of effluent. The area of the Trinity River into
which the effluent had been discharged originally has cleared
considerably. The presence of the floe plume in the river is no longer
apparent. Much of the deposit of floe except in the more isolated area
of the pr '• has been scoured from the region by the current of the rivet
39
-------
Station IV: Chemical Plant Producing Various Types of Acids
Effluent from Station IV is buffered through an automatic system and
then released into a drainage ditch which leads to the Trinity River.
Three successive tests in duplicate were run on this effluent.
Effluent for the first test was collected from the discharge unit next
to the plant immediately after passing through the buffering system.
The pH of the material was 8.7. All test organisms survived through-
out 96 hours at 100% and all other concentrations. Effluent for the
second test was collected four days later and approximately 75 yards
from the buffering system. The TL^ value for 24 hours was not
determined but it was 32.0% for 48 and 96 hours. The pH of this
fluid was 2.6. This indicated a malfunctioning of the buffering
system which was verified by one of the company officials. A third
test was conducted and all of the test organisms survived through-
out the 96 hours in all concentrations, as in the first test. The pH
of the effluent was 8.7. Channel catfish were used in all tests.
Results of work on effluent from this industry are shown in Table 8.
Table 8. TL „ values in per cent for Station IV.
Date 24 hrs 48 hrs 96 hrs Test Organism Av.Wt.G.
11-16-70 * * * !_. punctatus 11.2
11-16-70 ***!_. punctatus 11.2
11-20-70 * 32 32 !_. punctatus 11.1
11-20-70 * 32 32 I_. punctatus 11.1
11-24-70 * * * I_. punctatus 11.1
*No mortality
Based on these tests and using !_. punctatus as test organisms, it
appears that the buffering system, when functioning properly, is
effective so far as quality of effluent is concerned. It may be
deduced, however, that the effluent should be kept under constant
surveillance, and should receive immediate attention with the
slightest indication of malfunctioning of the buffering system.
Station V: Sewage Treatment Plant Receiving Industrial and Domestic
Was tes
Station V is located approximately 3 miles downstream from Station III
An average of approximately 30,000,000 gallons of effluent per day is
discharged through two outlets into the Trinity River. Fluid going
into the piaat as well as th^t leaving the plant was tested. It was
necessary to aerate the diluent water because of the low dissolved
-------
oxygen content of the fluids entering the plant. Tests were run in
duplicate using hybrid sunfish (longear - green sunfish) and
I. punctatus. There was no mortality in undiluted effluent from the
"outlets . There was mortality in the effluent going into the plant.
The TL,-n values for the above effluents are listed in Table 9 and other
characteristics are listed in Table 10.
Table 9.
TLsf. values in per cent for Station V.
Date
24 hrs 48 hrs 96 hrs Test Organism Av.Wt.G,
Outlet
10-16-70
10-16-70
10-21-70
10-21-70
*
*
*
*
*
*
*
*
*
*
Hybrid sunfish 2.3
Hybrid sunfish 2.3
I_. punctatus 2.3
I. punctatus 2.3
Inlet
10-16-70
10-16-70
11-3-70
11-3-70
15.0
21.75
13.5
13.5
12.7
18.0
10.5
10.5
10.5 I_. punctatus 2.2
17.0 I_. puuctatus 2.2
10.5 I_. punctatus 18.5
10.5 I. punctatus 18.5
*No mortality
Table 10. Ranges or values for various parameters of
Station V.
Parameter
Dissolved oxygen
PH
M.O. alkalinity
Turbidity
Conductivity
Total seston
Total seston
Total seston
Bioseston
Bioseston
Bioseston
Abioseston
Abioseston
Abioseston
Dissolved solids
Dissolved solids
Dissolved solids
Range/Value
0.8 - 6.1
6.7 - 7.3
190 - 280 ppm
10 - 17 JTU
820 - 1,048 micromhos/cm
146.7 mg/1 (inlet)
34.6 mg/1 (south outlet)
18.3 mg/1 (north outlet)
91.5 mg/1 (inlet)
23.2 mg/1 (south outlet)
10.9 mg/1 (north outlet)
55.2 mg/1 (inlet)
11.4 mg/1 (south outlet)
7.4 mg/1 (north outlet)
7,350 mg/1 (inlet)
6,535 mg/1 (south outlet)
6,237 mg/1 (north outlet)
-------
There was an appreciable amount of foaming as a result of agitation
plus detergents at each of the outlets. The foam persisted quite a
distance downstream before it dissipated. It was quite evident that
this factor had a deleterious effect on the fauna in the respective
areas .
The effect of treatment of wastewater in the sewage treatment plant for
the respective test organisms is reflected in Table 9. Although
toxicity of fluid at both outlets for the fish was nil at the time they
were exposed, quality of the effluent depends upon quality of the fluid
coming into the plant. It is necessary at this time to withhold a
positive statement indicating quality of effluent in the future.
Industrial plants as in the case of the chemical plant producing
cracking catalysts are gradually diverting their waste effluents to
the sanitary sewer and through sewage treatment plants. This will
have a definite influence on the quality of the effluent from the
sewage treatment plant and possibly on bioassay results.
Station VI: Plant Primarily Engaged in Metal Etching Using
Various Acids
Station VI is just east of the city limits of Fort Worth. This plant
is somewhat removed from the Trinity River but a number of gravel pits
close by are filled with the effluent which seeps through the soil
to channels and may eventually get into the river. A survey of the
premises and results of preliminary tests indicated that it would be
advisable to select several substations for study in order to ascertain
a better picture of the situation (Figure 16) .
Substations A and B are located at two outfalls into a holding pool and
Substation C is in the holding pool. Effluent from Substation D flows
to Substation B. Since there was no difference in their qualities,
Substation D was abandoned. Substation E is located below the holding
pool and Substation F is in the gravel pit most directly connected with
the holding pool and possibly most likely to overflow. Effluent from
Substation E seeks its own course in a very diverse manner into the
gravel pit some 150 yards from Substation E.
The pH of Station VI effluent varied at the respective substations as
shown in Table 11.
Table 11. pH value ranges at the respective substations of
Station VI.
Substation A B C E F
Low 0.8 7.0 6.8 1.9 6.8
High 7.6 11.0 8.0 10.4 8.9
-------
:
Figure 16. Map of Station VI study area showing substations.
Substations are indicated by letters A, B, C, E and F.
-------
Table 12.
values in per cent for all substations
ir,-,
of Station VI.
Date /Substation 24 hrs 48 hrs 96 hrs Test Organism Av .Wt .G ,
Substation A
12-3-70 8.4 8.4
12-3-70 8.4 8.4
12-16-70 10.5 3.0
12-16-70 10.0 3.75
Substation B
12-10-70 5.0 5.0
5-25-71 23.5 22.5
5-25-71 34.5 28.0
Substation C
1-5-71 * *
Substation E
1-11-71 5.5 4.75
1-17-71 5.4 5.4
1-17-71 5.6 5.6
1-23-71 31.5 31.5
1-23-71 33.25 32.25
2-6-71 * *
2-11-71 11.25 11.25
2-11-71 15.0 10.75
2-16-71 18.75 18.75
2-16-71 15.0 14.0
4-14-71 25.0 17.5
4-14-71 17.5 17.5
5-18-71 20.0 8.4
5-25-71 50.0 41.0
Substation F
3-10-71 56.0 56.0
3-10-71 56.0 56.0
3-25-71 75.0 70.0
3-25-71 75.0 70.0
4-1-71 * 90.0
4-14-71 7.5 7.0
4-14-71 7.5 5.5
6-3-71 55.0 51.75
6-3-71 55.0 55.0
6-10-71 73.0 73.0
6-10-71 75.0 71.0
*No mortality
//Total mortality
8.4
8.4
3.0
3.75
5.0
21.0
28.0
A
4.5
5.4
5.4
31.5
30.0
*
10.5
10.75
16.25
12.0
17.5
14.0
8.4
36.5
56.0
56.0
#
#
90.0
6.2
5.5
51.75
55.0
73.0
69.0
N.
N.
N.
N.
N.
P.
P_.
N.
N.
N.
N.
N.
N.
N.
N.
N.
N.
N.
N.
N.
P.
N.
N.
N.
N.
N.
N.
N.
N.
P.
P.
P.
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
promelas
promelas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
promelas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
crysoleucas
promelas
promelas
promelas
2.0
2.0
2.4
2.4
2.1
1.8
1.8
2.1
2.0
2.3
2.3
2.1
2.1
2.0
2.2
2.2
2.1
2.1
2.1
2.0
1.9
1.9
1.7
1.7
2.2
2.1
2.1
2.6
2.2
2.2
2.1
2.1
44
-------
Eighteen tons of lime were dumped into the holding pool (Substation C)
just prior to the first sampling of the area. This may have influenced
the pH values at Substations C, E and F.
Effluent at Substation A comes from an area where materials are removed
from an acid bath and washed. The pH varies according to the stage of
the process and the amount of diluent water. In collecting 160 gallons
of fluid from this substation the pH ranged between a low of 0.9 and a
high of 3.0. Substation B fluids come from tanks in another area with
a different type of processing from that of Substation A. Substation
C effluent is a mixture of Substations A and B, each with quite diverse
pH values. Substations C, E and F received the possible full effect of
the lime; however, the low reading at Substation E does not so indicate
(Table 11). Substation F received some fluid resulting from periodic
washing of concrete mixing trucks from a nearby concrete mixing plant.
The TL values, like pH, varied at the respective substations and be-
tween substations. Fluids from Substations A and E were most toxic.
Table 12 and Figures 17, 18 and 19 show the results of the bioassay.
Fish reacted very violently to some of the fluid collected. When
exposed to full strength material, death frequently occurred within 30
seconds. Eyes bulged abnormally and there was a general contortion of
the body. Tissues eroded away rapidly and when the fish were left in
the fluid for 30 to 45 minutes, the viscera were exposed (Figure 20).
Conductivity was expectedly high at Substation A ranging between 2,200
and greater than 8,000 micromhos per centimeter. The effluents come from
a part of the plant where metal etching is done. Conductivity values for
all substations are listed in Table 13.
Table 13. Conductivity range in micromhos/cm for respective
substations of Station VI.
Substation ABC E F
Low 2,200 700 1,800 690 1,250
High >8,000 2,200 2,200 >8,000 2,080
High toxicity of the Station VI effluent was usually associated with
high conductivity. Effluent from Substation A was usually very turbid.
Turbidity ranges for all substations are listed in Table 14.
High turbidity was usually associated with high conductivity of Station
VI effluents. Suspended solids and dissolved solids of Station VI
effluents varied considerably at each substation and from substation to
substation. The same was true with dissolved solids. Ranges of seston
and dissolved solids are listed in Table 15.
-------
24 hr TL5() Illlilllilllllllii
48 hr TL
50
96 hr TL
1-11-71
1-17-71
1-23-71
2-6-71 2-11-71
2-16-71
4-14-71
5-18-71 5-25-71
Figure 17. TLr0 values for Station VI effluent using golden shiners (Notemigonus crysoleucas
(Mitchill)) as test organisms. Substation E.
-------
48 hr TL
96 hr TL
24 hr TL5Q Illllllll Ill
3-10-71 3-25-71
4-1-71
4-14-71
II II II
Figure 18. TL values for Station VI effluent using golden
shiners (Notemigonus crysoleucas (Mitchill)) as test
organisms. Substation F.
-------
75
70
65
55
50
45
40
35
30
25
20
15
10
24 hr TL
48 hr TL
96 hr TL
Illlllllllllllllll
II II II
5-18-71 5-25-71
6-3-71 6-10-71
Figure 19. TL values for Station VI effluent using fathead
minnows (Pimephales promelas Rafinesque) as test
organisms. Substations are indicated by capital
letters .
-------
Figure 20. Notemigonus crysoleucas exposed to a 100% concentration
of Station VI effluent.
A. Control—no exposure.
B and C. Exposed for 40 minutes to a 100% concentration
showing erosion of fins and body tissue.
D. Exposed to a weaker solution showing erosion of tail
and fins.
-------
Table 14. Turbidity ranges expressed in Jackson Turbidity
Units (JTU) for all Station VI substations.
Substation
B
C E
Low 44455
High 220 11 9 56 16
Table 15. Total seston, abioseston, bioseston and dissolved
solids values in mg/1 for Station VI.
Substation Total Seston Abioseston Bioseston Dissolved Solids
Hi
A
B
C
E
F
256.1
756.7
176.1
59.7
171.2
Low Hi
178.0
4.3
17.1
Low
Low
240.0
445.3
142.5
48.0
22.1
16.1
104.8 311.4 73.2
33.5
3.5 11.7 0.8
3.1 16.8 2.1
High
4,897.0
1,690.0
*3.1287
1,183.7
2,548.5
Low
1,690.0
385.0
1,385.2
"g/1
A bright red effluent was discharged from Substation B on 5-24-71. This
appeared only once while collections were being made. The color was
attributed to a red dye used and confirmed by a company official. The
dye did not appear to be of significance with respect to mortality rate
of test organisms. According to the official, this condition occurs not
more than once every three or four months, and is not considered to
merit special monitoring.
Combinations of Station I, Station III and Station VI effluents
Station I, Station III and Station VI effluents were combined in an
attempt to determine possible synergistic and/or antagonistic effects .
Equal mixtures of Station I and Station III effluents resulted in no
mortality using 14. crysoleucas as test organisms . Based on the results
of these tests it may be said that the two effluents are antagonistic.
When using 1J. crysoleucas as test organisms and an equal mixture of
Station I and Station VI effluents the TL value was 18.0% for 24, 48
and 96 hours. This TL value is higher than all but one 96 hour value
recorded for Station I alone but not as high as some 96 hour values
recorded for Station VI. Data indicate that equal mixtures of Station
I and Station VI may tend toward stabilization of Station VI effluent
while weakening the effects of Station I as reflected by use of
N_. crysoleucas as test organisms (Table 2 and Table 12) . The
variability in quality of Station VI effluent may, in future testing,
lend different results.
-------
Equal mixtures of Station I, Station III and Station VI effluents
resulted in no mortality in successive tests. Based on this observa-
tion plus results of the above tests, it is indicative that Station III
effluent may act as an antagonistic substance for both Station I and
Station VI effluents . Results of combination values are shown in
Table 16 and Figure 21.
The effluents used in the above combination of tests are considered to
be the three most toxic of all effluents studied. When mixed equally
there is a definite reaction. The tests indicate a general antagonistic
effect. The respective plants are separated far enough from each other
along the river that it is most likely that individual effects would
probably have dissipated for the greater part before joining another.
This is especially true of Station I and Station VI effluents.
Table 16. TL-Q values in per cent of combination of Station I,
Station III and Station VI effluents.
Date 24 hrs 48 hrs 96 hrs Test Organism Av.Wt.G.
Station I 50% and Station III 50%
6-22-70
6-22-70
7-7-70
7-7-70
6-29-71
6-29-71
*
A
25.0
21.5
18.5
18.5
22.0
25.0
7.5
7.5
18.5
18.5
20.0
25.0
6.5
6.0
12.5
14.0
M.
M.
M.
M.
N.
N.
salmoides
salmoides
salmoides
salmoides
crysoleucas
crysoleucas
1.4
1.4
1.6
1.6
2.1
2.1
Station I 50% and Station VI 50%
7-24-71 18.0 18.0 18.0 N. crysoleucas 2.1
Station I 33 1/3%, Station III 33 1/3% and Station VI 33 1/3%
7-24-71 * *
*No mortality
* N. crysoleucas
2.2
Station VII: Sewage Treatment Plant in a Poor State of Repair
(Imhoff-lagoon)
Effluent coming into the sewage treatment plant was checked in
successive tests. The dissolved oxygen was less than 1 ppm and it
was necessary to aerate the diluent water in higher concentrations in
order for the test organisms, N_. crysoleucas, to survive. The TL
for 24 hours was 40.0%/37.5%, 37.0%/37.5% for 48 to 96 hours. Other
characteristics of the effluent are as follows: pH 7.3, turbidity 33
JTU and dissolved solids 5,372 mg/1.
This sewage treatment plant is much smaller than the Station V sewage
treatment plant. The toxicity of this inflowing fluid was not as
-------
30
24 hr TL5Q II Illimilil
48 hr TL
96 hr TL
II II II
*No mortalitv
25
20
15
6-22-70 7-7-7
6-29-71
7-9-71
Figure 21. TL,.n values for combinations of effluents.
A and B equal mixture of Station I and Station III
using Micropterus salmoides as test organisms.
C equal mixture of Station I and Station III using
Notemigonus crysoleucas as test organisms.
D equal mixture of Station I, Station II and Station
III using Notemigonus crysoleucas as test organisms.
-------
great as that of the Station V plant. This may be accounted for in
part by the fact that the Station VII plant receives primarily
domestic wastewater. The Station V sewage treatment plant receives a
great amount of industrial wastewater in addition to the domestic.
Station VIII; Fuel Oil and Gasoline Bulk Loading Station
Effluents from the Station VIII contain primarily grease, lubricating
oil and fuel oil, especially gasoline. There is rather extensive
spillage of fuel resulting from carelessness in filling of tank
trucks. The effluent is collected in a holding pit which may overflow
into the Trinity River.
Other characteristics of the effluent are listed in Table 17.
Table 17. Characteristics of the Station VIII effluent.
Effluent Value
Dissolved oxygen 4.6
pH 6.9
Turbidity 57.0 JTU
Conductivity 580 micromhos/cm
Total seston 34.65 mg/1
Abioseston 22.5 mg/1
Bioseston 12.5 mg/1
Dissolved solids 496.3 mg/1
The TL values for 24 hours was 18.75% and remained the same through
48 and 96 hours. The TL for a second test was 21.0% for 24, 48 and
96 hours.
Testing of this effluent was limited because the company was cognizant
of the inadequacy of the system and started construction to remedy the
situation.
Growth and Development
During the summers of 1970 and 1971 some 35 test runs (including dupli-
cates) were carried out using fish eggs or fry as test organisms. Eggs
or fry of the channel catfish (Ictalurus punctatus (Rafinesque)) were
available for 29 of these tests while largemouth bass (Micropterus
salmoides (Lacepede)) fry were used in the other six. One additional
unsuccessful run using frog eggs was attempted early in 1971.
53
-------
General Observations on 1970 Test Runs - The nine test runs carried out
in 1970 are summarized in Table 18 (where starting date, source of
effluent, range of concentration tested, total length of test and test
organisms used in each are recorded). All involved the use of catfish
eggs or newly-hatched young which became available from the Fort Worth
National Fish Hatchery early in June.
The first duplicate test runs (I-AC(A) and I-AC(B)) were preliminary
tests and did not lead to usable data but they did suggest several
changes in apparatus and techniques which were incorporated in all
subsequent tests on eggs or fry. These modifications are described
in the "Materials and Methods" section of this report.
Of the remaining seven test runs for 1970 it will be noted that three
used Station III effluent, two used Station I wastes and the last two
tested a half-and-half mixture of these two commercial effluents.
Three of the test runs (II-AC(A), II-AC(B) and III-AC(A)) were
continued for a total of eight days while the others were discontinued
at the end of four days. Data from these runs suggested that 96 hours
is a satisfactory test period. However, it will be noted below under
1971 results that it was considered desirable to continue some of
the 1971 test runs beyond the four day limit. The age of the catfish
employed in the seven test runs of 1970 varied from three days pre-
hatching (III-AC(A)) to 18 days post-hatching. Young at hatching
averaged some 11 mm in length and these had reached an average length
of 15 mm by 18 days of age. A total of 60 young fish were used in each
series making a total of 420 for the seven runs.
Some general comments on the seven successful test runs involving
catfish young carried out in June and early July of 1970 follow:
Series II-AC(A) and II-AC(B)-
Two simultaneous runs for total of eight days; Station III effluent;
maximum concentration of 12 1/2%; young catfish six days of age
post-hatching. All young fish were dead within 48 hours in strongest
concentration and about half survived the full eight days in the
6 1/4% solution. All young fish survived the full eight days in the
weaker concentrations and in the controls.
Series III-AC(A)-
Similar to above series except that the young used were about three
days of age pre-hatching. Only three remained alive in the 12 1/2%
solution after 48 hours and all were dead after 72 hours. All
surviving young had hatched by the end of three days and the hatchlings
survived well in all concentrations except the strongest (12 1/2%) for
the full eight days.
Series I-TP(C) and I-TP(D)-
Two simultaneous runs for four days duration; Station I effluent;
maximum concentration of 25%; young catfish of 18 days of age. All
-------
Table 18. Summary of test runs involving eggs and fry (1970) .
Run No. Date
Started
I-AC(A) 6-3-70
I-AC(B) 6-3-70
II-AC(A) 6-10-70
II-AC(B) 6-10-70
III-AC(A) 6-10-70
I-TP(C) 6-23-70
I-TP(D) 6-23-70
I-AC/TP(A) 6-23-70
I-AC/TP(B) 6-23-70
Effluent Concentration Total Length Test
Station Range Tested
Station 3.2 - 50%
III
Station 3.2 - 50%
III
Station 0.7 - 12.5%
III
Station 0.7 - 12.5%
III
Station 0.7 - 12.5%
III
Station 1.6 - 25%
I
Station 1.6 - 25%
I
1/2 Sta. 1.6 - 25%
1/1/2
Sta. Ill
1/2 Sta. 1.6 - 25%
1/1/2
Sta. Ill
of Test
42 hrs
4 days
8 days
8 days
8 days
4 days
4 days
4 days
4 days
Organisms
Catfish eggs
(4 days after
spawning)
Catfish eggs
(4 days after
spawning)
Young catfish
(6 days post-
hatching)
Young catfish
(6 days post-
hatching)
Catfish eggs
(about 3 days
p re -hatching)
Young catfish
(18 days post-
hatching)
Young catfish
(18 days post-
hatching)
Young catfish
(18 days post-
hatching)
Young catfish
(18 days post-
hatching)
-------
fish in these tests were dead within two and one-half hours in the
strongest concentration (25%) and all were dead in the 12 1/2% tank
within 24 hours. No fish survived for 48 hours in the 6 1/4% tank and
only one fish survived in the 3 1/8% solution for the full four days .
All survived in the 1 1/2% and control tanks for the full test period.
Series I-AC/TP(A) and I-AC/TP(B)-
Similar to preceding series except equal mixtures of Station III and
Station I effluents were used. In these combined runs all fish
survived for 24 hours in the 25% concentration, only 30% lived for
48 hours and none lasted for as long as three days . In the 12 1/2%
test tank survival was 100% for one day, 95% for two days, 50% for
three days and 40% for the full 96 hours. All fish survived in the
three test tanks of lesser concentration and in the control tank.
General Observations on 1971 Test Runs - Table 19 gives in summary
form starting dates, effluents tested, range of concentrations tested,
length of test and test organisms used in all studies carried out on
eggs or fry during the summer of 1971. A total of 27 test runs
(including duplicates) were made and 20 of these employed catfish
eggs or fry as test organisms. Young bass fry were used in six tests
and one unsuccessful attempt was made to utilize frog eggs in the late
gastrula stage.
Seven different pollutants or combinations thereof were tested in the
26 test runs involving fish eggs or fry. These were Station III (8),
Station VI (9), Station I (3), Station VII (1), combination of 1/2
Station I and 1/2 Station III (2), combination of 1/2 Station I and
1/2 Station VI (1), combination of 1/3 Station I, 1/3 Station VI and
1/3 Station III (2).
The bass fry used in four of the test runs (Series II-A through
IV-D) were obtained from the Fort Worth National Fish Hatchery on
April 30, 1971 when they were about one week old. They were
maintained in holding aquaria until used in the testing program. A
fresh supply of fry was obtained from the hatchery for the tests of
May 25, 1971 (Series V-A and VI-C).
Two lots of catfish eggs were obtained from the fish hatchery on June 1
and June 11, 1971. Hatching took place in the holding tanks in the
laboratory and these furnished material for all tests through those of
June 29. Three-week old fry obtained from the hatchery in early July
provided test organisms for all tests conducted in July.
Twenty-three of the 26 tests lasted a minimum of 96 hours but several
were continued for as long as ten days. The other three tests were
discontinued prior to the four days and the results of these are not
unable. In Series X-C the only survivors after 48 hours were the
controls. Series XIV-A and XIV-B were terminated early also as all
young catfish were dead at the end of 24 hours except for those in the
weakest concentration and in the control tank.
-------
Table 19. Summary of test rrr-
Run No .
I-A
II-A
III-A
IV-C
IV-D
V-A
VI-C
VIII-A
VIII-B
IX-C
IX-D
X-C
XI -AA
XI-AB
XII-C
XII-D
XIII
Date
Started
3-3-71
5-1-71
5-12-71
5-18-71
5-18^71
5-25-71
5-25-71
6-2-71
6-2-71
6-4-71
6-4-71
6-10-71
6-12-71
6-12-71
6-16-71
6-16-71
6-21-71
Effluent
Station
Station
VI
Station
III
Station
III
Station
VI (F)
Station
VI (F)
Station
VI (F)
Station
VI (B)
Station
III
Station
III
Station
VI (F)
Station
VI (F)
Station
VI (F)
Station
VI (F)
Station
VI (F)
Station
I
Station
I
Station
I
Concentration
Range Tested
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
- 100%
- 100%
- 100%
- 20%
- 20%
- 50%
- 50%
- 25%
- 25%
- 75%
- 75%
- 100%
- 10%
- 10%
- 25%
- 25%
- 25%
Total Lengt:-
of Tes L
4 J -.•••.-
4 days
8 days
4 days
4 days
4 days
4 days
10 days
10 days
4 days
''4 •'": '" S
2 d av s
9 days
9 days
10 days
10 days
5 days
'!'• . .: '"
Organisms
••-' ~^& tiggs-
••"?.<; trula stage
^•as,~ fry
Bass fry
B as s fry
Bass fry
Bass fry
Bass fry
Catfish eggs
(4 days pre-
hatching)
Catfish eggs
(4 <''-)\-> pre-
hai-j-iiug)
Catfi;'i eggs
( 3 A r - • •
\ •' • -
C 3t - .L ' ^-- .:. ,'- •?
'3 days pre-
riatchJ.ng)
Catfish fry
(5 days post-
hatching)
Catfish fry
(8 days post-
hatching)
Catfish fry
(8 days post-
hatching)
Catfish fry
(4 days post-
; latching)
Catiish fry
( -'; days post-
hatching)
Catfish fry
(9 days post-
hatching)
-------
Table 19. Continued
Run No. Date Effluent Concentration Total Length Test
XIV-A
XIV-B
XV-A
XV-B
XVI-C
XVI -D
XVI I- C
XVI I-D
XIX-C
XX-A
Started Station Range Tested
6-23-71 Station 0 - 50%
III
6-23-71 Station 0 - 50%
III
6-25-71 Station 0 - 20%
III
6-25-71 Station 0 - 20%
III
6-29-71 1/2 Sta. 0 - 25%
1/1/2
Sta. Ill
6-29-71 1/2 Sta. 0 - 25%
1/1/2
Sta. Ill
7-9-71 1/3 Sta. 0 - 25%
1/1/3
Sta. Ill/
1/3 Sta.
VI (F)
7-9-71 1/3 Sta. 0 - 25%
1/1/3
Sta. Ill/
1/3 Sta.
VI (F)
7-16-71 Station 0 - 50%
VII
7-24-71 1/2 Sta. 0 - 25%
1/1/2
Sta.
VI (F)
of Test
1 day
1 day
4 days
4 days
6 days
6 days
4 days
4 days
4 days
4 days
Organisms
Catfish fry
(11 days post
hatching)
Catfish fry
(11 days post
hatching)
Catfish fry
(13 days)
Catfish fry
(13 days)
Catfish fry
(17 days)
Catfish fry
(17 days)
Catfish fry
(24 days)
Catfish fry
(24 days)
Catfish fry
(31 days)
Catfish fry
(39 days)
-------
Observations and results for 1971 tests of fish eggs and fry are sum-
marized below according to commercial effluent tested. The TL Q values
reported here were determined in the same manner as described tor
mature fish in a preceding section of this report. The PH ranges shown
are based on daily recording of acidity"or alkalinity in the five test
concentrations .
Station I: Railroad Equipment Cleaning Area
This effluent is regularly slightly basic and contains primarily
detergents used in the various railroad cleaning operations.
Series XII-C and XII-D-
Duplicate tests with four day old catfish hatchlings were run with
25%, 12.5%, 6.25%, 3.13% and 1.56% concentrations of Station I
effluent for a total of 10 days. The pH range and the 48- and
96-hour TL are given in Table 20 below. Surviving the full 10
days were seven fry in the 6.25%, 17 in the 3.13%, 19 in the 1.56%
solution, and all 20 control organisms.
Series XIII-
A single run with seven day old fry was conducted simultaneously with
the last five days of the preceding Series XII tests. Survival of these
older fry was a bit better than those in Series XII; all fry survived in
the solutions of 6.25% concentration or less. Two- and four-day TL5Q
values are shown in Table 20.
Table 20. TLsn values for eggs or fry using Station I effluent.
Series pH Range Test Organisms TL5Q Values
24 hrs 48 hrs 96 hrs
XII-C 7.8 - 8.5 Catfish fry (4-day) -- 18.5% 11.1%
XII-D 7.8 - 8.5 Catfish fry (4-day) -- 18.7 11.1
XIII 7.7 - 8.0 Catfish fry (9-day) — 17.0 15.0
Station III: Chemical Plant Producing Cracking Catalysts for
Processing Combustion Engine Fuels
This effluent exhibited wide variability in pH, being highly acidic
or basic at different collection times. A white flocculent precipitate
is frequently associated with this effluent. Eight test series
(including duplicates) were carried out with this effluent; results
are summarized below. TL values and pH ranges are shown in Table 21.
59
-------
Series II-A-
A single run using bass fry with concentrations of 100%, 50%, 25%,
12.5% and 6.25% was continued for four days. Five fry were placed in
each cup and two cups were placed in each tank. No fry survived in
the two strong concentrations for 24 hours . There was 70% survival in the
25% tank for 48 hours and 40% survival for the full four days . All fry
survived in the two weakest concentrations for the full test time. The
pH ranged between 5.1 and 7.4.
Series III-A-
In this single eight-day test 20 bass fry (four cups of five fry each
per tank) were subjected to concentrations of 50%, 25%, 12.5%, 6.25%
and 3.12%. No fry survived in the 50% and 25% concentrations for 24
hours. Forty per cent survived 24 hours in the 12.5% tank but none
survived for 48 hours. Ninety per cent of the test organisms survived
for seven full days in the 6.25% tank at which time all died overnight.
All fry survived in the weakest concentration for the full eight days.
Variation in pH was 7.7 to 8.7.
Series VIII-A and VIII-B-
Duplicate tests with catfish eggs in concentrations of 25%, 12.5%,
6.25%, 3.13% and 1.56% were continued for a full ten days. Most of the
eggs hatched out on the fourth day of the run. The number of eggs in
each cup varied but a minimum of ten was included in each cup. The
eggs were quite tolerant of the effluent as shown by the TL values in
Table 21. It is possible that the egg membranes bestow increased pro-
tection to the developing embryos. Surviving the full 10-day period
were 23% of the fry in the 6.25% concentration, 76% in the 3.13% and
71% in the 1.56% tank. Some 87% of the controls survived. The
detection of a beating heart was the criterion used for determining
survival. The pH in this series varied from 2.8 to 7.4.
Series XV-A and XV-B-
Duplicate tests with concentrations of 20%, 10%, 5%, 2.5% and 1.3% were
continued for four days. Thirteen-day old catfish young were employed
in these series. The pH varied in these tests from 2.3 to 7.2.
Table 21.
TL.-Q values for eggs or fry using Station III effluent,
Series pH Range
II-A
III-A
VIII-A
VIII-B
XV-A
XV-B
5.1 -
7.7 -
2.8 -
2.9 -
2.3 -
2.3 -
7.4
8.7
7.4
7.5
7.2
7.2
Test Organisms
Bass fry
Bass fry
Catfish eggs
Catfish eggs
Catfish fry (13-day)
Catfish fry (13-day)
TL Values
24 hrs
37%
14
—
24.5
3.9
4.6
48 hrs
37%
12
14
19
3.2
4.2
96 hrs
28%
11.5
14
17.9
3.0
3.6
60
-------
Station VI: Metal Etching Plant Using Various Acids
Seven of the eight test runs summarized in Table 22 employed Station VI
effluent from Substation F while effluent from Substation B was used in
Series VI-C only. All of these effluents were alkaline varying from
7.7 to as high as 9.9. Observations on each of these test runs are
summarized as follows:
Series IV-C and IV-D-
Station VI effluent in 20%, 10%, 5%, 2.5% and 1.3% were used in these
tests. Bass fry were the test organisms. TL . values at 24 and 48
hours were both 2.0% for Series IV-C and 2.6% for Series IV-D. As
only 50% and 90% of the controls were surviving at 96 hours and as
fry were also dying in holding tanks at this time the results from
this test run are considered questionable.
Series V-A-
A new supply of bass fry from the hatchery was used in this single test
with Station VI effluent at 50%, 25%, 12.5%, 6.3% and 3.H concen-
trations. Although the fish were healthier, the TL . values were about
the same as in the Series IV runs. All fry in the highest four concen-
trations were dead overnight while five remained in the 3.1% solution
through the entire 96-hour period. The pH ranged from 7.9 to 9.7.
Series VI-C-
This is the only test in which pollutant from Substation B was used.
Young bass fry were test organisms. The effluent contained a bright
red dye which is not a regular component of Station VI wastes. Concen-
trations in the five tanks were the same as in the Series V test. The
pH varied from 7.7 to 9.6. The TL values remained constant (6.5%)
at 24, 48 and 96 hours. Seven of the fry survived the full 96 hours in
the weakest concentration. The red dye did make quite visible the
copious secretion of mucus which coated the bodies and gills of the
young fish.
Series IX-C and IX-D-
These duplicate tests used Station VI effluent in concentration of 75%,
37.5%, 18.8%, 9.4% and 4.7%. Catfish eggs in variable numbers were used
for this four-day test. Many of the eggs hatched during the second or
third day of the run. The pH varied 8.3 to 9.9 for this sample. Some
94% of the combined controls, 86% of young in the 4.7% tank, 38% from
the 9.4% concentration, 3.6% from the 18.8% concentration, and 24% from
the 37.5% tank remained alive at the end of the 96 hours.
Series XI-AA and XI-AB-
Station VI effluent was again used in these series. Catfish fry of
five days of age were used in Series XI-AA while newly hatched catfish
were used in the other series. These test runs were terminated at the
end of nine days. The series of concentrations used here included
10%, 5%, 2.5%, 1.3% and .65%. There were no survivors of older fry in
61
-------
the 10% tank after 48 hours, 20% survived in the 5% tank and 90 - 100%
of the older fry lived through the full nine days . Survival of the
younger fry was surprisingly higher as indicated by the TL5Q values
shown in Table 22.
Table 22. TL values for eggs or fry using Station VI effluent,
Series pH Range
TL Values
24 hrs 48 hrs 96 hrs
IV-C
IV-D
*VI-C
IX- C
IX-D
XI-AA
XI -AB
7.7
7.9
7.7
8.3
8.3
7.9
7.9
- 9.1
- 9.1
-9.6
-9.9
- 9.4
- 8.9
- 8.9
2%
2.6%
6.5%
—
52.5%
4.5%
—
2%
2.6%
6.5%
12.7%
23.1%
4.3%
5.6%
—
—
6.5%
9.8%
—
4.3%
5.1%
Test Organisms
Bass fry
Bass fry
Bass fry
Catfish eggs
Catfish eggs
Catfish fry, 5 day
Catfish fry, newly
hatched
*Substation B; all others from Substation F
Most of the studies to date have concerned themselves with effluent
wastes from three commercial firms located along the Trinity River:
a railroad equipment cleaning operation, a chemical plant producing
cracking catalysts and a metal etching plant. In addition, a few
tests have been conducted using combinations of these effluents and
one test run was conducted using effluent from a suburban sewage
treatment plant. The results of these test runs on young catfish are
briefly summarized.
Series XVI-C and XVI-D-
Duplicate tests using a half-and-half mixture of Station I and Station
III effluents were conducted. Maximum concentration was 25% and tests
were continued for six days. Range of pH was marked - from 4.9 to
7.6. The TL,-,. estimates for 24, 48 and 96 hours were 16%/18.5%,
9.3%/16% and 5.5%/9.5% for the two series respectively.
Series XVII-C and XVII-D-
Duplicate tests using mixture of equal amounts of Station III, Station
VI and Station I effluents. Maximum concentration was 25% and the
test organisms were 24 day old catfish fry. The pH variation in these
tanks was from 6.8 to 7.7. Sixty and 80% of the fry remained alive at
the end of 24 hours; the TL,.,. estimates for 48 and 96 hours were
18.8%/20.5% and 10%/11.5% respectively.
62
-------
Series XX-A-
Catfish fry (8 day of age) were tested in a half-and-half mixture of
Station I and Station VI effluents. The run lasted five days. The
pH range was from 7.6 to 8.9. The TL5Q values were 5.8%, 4.3% and 3.5%
for 24, 48 and 96 hours respectively.
Series XIX-C-
This single test used the supernatant of the inflow to the suburban ^
sewage treatment plant (Station VII) diluted to 50%, 25%, 12.5%, 6.3%
and 3.1% for a four-day test run. Catfish fry were 31 days of age.
The TL figures for this run were 33%, 18.5% and 9% for 24, 48 and 96
hours respectively.
Catfish and bass fry which died in the various concentrations during
each test run were examined under a low-power microscope for observable
morphological damage prior to preservation. Some general observations
are presented here. In most cases the dead fry exhibited excessive
accumulations of mucus over the entire body and on the gills. The
amount of mucus appeared to be more or less inversely proportional to
the survival time. Mucus was particularly obvious on specimens exposed
to stronger concentrations of Station III effluent where a white
flocculent precipitate became trapped in the mucus over the body and
within the gill cavity.
A corrosive effect on the skin and surface structures was quite
noticeable on fish fry exposed to some of the more caustic or acidic
test solutions. Barbels, opercular margin, caudal and other fins
and gills showed various degrees of erosion. In some cases the skin
on the belly wall was almost completely eroded through. These effects
became progressively less noticeable as the survival time of the fry
increased.
Examination of preserved specimens from all test runs is now being
carried out in order to more specifically identify morphological
damage.
Beginning with Series VII-A and VII-B surviving catfish fry from most
of the test runs were transferred to floating plastic cups in a holding
aquarium where they were maintained as long as possible. These sur-
vivors were fed daily with "starter food" and observed for damage.
Survival counts were carried out periodically and dead fry were
preserved for future examination.
Detailed results of these studies are not yet available but some
generalizations can be made. "Post-test survival" ranged from only a
day or two in some cases up to a maximum of almost ten weeks. Some of
the fry (e.g., Station I, Series XII, 10% and Station III, Series VII,
6.2%) showed marked orientation problems, swimming upside down most of
the time and feeding from floating food only. In other cups of survivors
there appeared to be quite marked variation in growth over the length of
the holding period.
63
-------
Chemical Evaluation
Some chemical influences of industrial effluents discharged into the
Trinity River were evaluated at six different stations. Five series of
samples were collected at each station on different dates. Each
station was subdivided into five substations. Each station is treated
separately and specific values are included in the Appendix.
Station I: Railroad Equipment Cleaning Area
Three series of samples were collected in January 1970 and two in March.
The sampling sequence was interrupted by construction along the channel.
This station is on the Clear Fork of the Trinity River. All specific
data are found in Appendices 1 - 5.
Temperature of the upstream station varied from 6°C - 14°C while that
of the raw effluent at Substation B varied from 8°C - 18°C. Temperature
of the three downstream Substations C, D and E varied from 6°C - 14°C.
Air temperature during this period ranged between 4°C - 24°C
(Appendices 1 - 5).
Dissolved oxygen ranged between 10.5 - 12.2 mg/1 for Substation A
while for the raw effluent the range was between 4.0 - 9.4 mg/1. Down-
stream at Substations C, D and E DO ranged between 9 .9 - 12.4 mg/1
(Appendices 1 - 5).
The pH value for Substation A ranged between 7.7 - 8.1 while for Sub-
station B the range was between 10.3 - 11.5 and downstream values at
Substations C, D and E ranged between 8.0 - 10.8 (Appendices 1-5).
Specific conductance ranged between 185 - 520 micromhos/cm at Substation
A; Substation B was between 1,130 - 1,600 micromhos/cm and at C, D and E
the range was between 230 - 1,000 micromhos/cm (Appendices 1 - 5) .
Turbidity at Substation A ranged between 21 - 84 JTU, for B between
57 - 80 and for C, D and E between 23 - 76 (Appendices 1 - 5) .
Phenolphthalein alkalinity at Substaion A was always 0.0 mg/1 as CaCO,.
while total alkalinity varied between 152 - 450 mg/1 as CaCO .
Phenolphthalein alkalinity for Substation B ranged between 2o2 - 362
mg/1 as CaCO,. and total alkalinity ranged between 428 - 638 mg/1 as
CaCO,.. For Substations C, D and E phenolphthalein alkalinity ranged
between 0.0 mg/1 as CaCO_ and the total alkalinity ranged between
146 - 428 mg/1 as CaCO- (Appendices 1 - 5).
Biochemical oxygen demand values for Substation A ranged between 1.1 -
3.8 mg/1 while for Substation B it ranged between 15.2 - 23.8 mg/1.
For Substations C, D and E the BOD values ranged between 0.0 - 22.0
mg/1 (Appendices 1 - 5) .
-------
Chemical oxygen demand value for Substation A was between 3.6 and 59.8
mg/1. Substation B ranged between 291.6 and 449.6 mg/1 while Substations
C, D and E ranged between 1.0 and 224.8 mg/1 (Appendices 1-5).
The range of nitrate concentration at Substation A was between 0.0 rag/1
NO (0.0 mg/1 NO -N) and 5.8 mg/1 NO (1.3 mg/1 NO -N) . The range for
Substation B was between 0.2 mg/1 NO (0.04 mg/1 NO^N) and 5.8 mg/1
NO (1.3 mg/1 NCL-N) while for Substations C, D and E the range was
between 0.0 N03 (0.0 mg/1 N03~N) and 6.6 mg/1 N03 (1.5 mg/1 N03-N)
(Appendices 1 - 5) .
Orthophosphate concentrations at Substation A ranged between 0.05 -
0.30 mg/1 P, while hydrolyzable phosphate ranged between 0.00 mg/1 and
0.03 mg/1 P. Substation B had a range of orthophosphate from 0.58 mg/1
P to 1.20 mg/1 P and hydrolyzable phosphates ranged between 0.30 mg/1 P
and 1.30 mg/1 P. Substations C, D and E ranged between 0.04 - 0.54 mg/1
P for orthophosphate and ranged between 0.00 - 0.18 mg/1 P.
Concentrations of dissolved calcium ranged between 56.0 - 86.5 mg/1
for Substation A while for Substation B, the range was between 12.0 and
24.0 mg/1. The Substations C, D and E ranged from 20.4 - 70.3 mg/1.
Dissolved magnesium concentrations ranged between 3.0 - 6.4 mg/1 for
Substation A, 0.2 - 3.6 mg/1 for Substation B and from 3.6 - 7.6 mg/1
for Substations C, D and E.
Concentrations of copper and zinc were all less than 0.25 mg/1 for
all substations while iron was less than 0.5 mg/1 for all substations.
The per cent organic matter of the suspended matter for Substation A
ranged between 14.9% - 33.0% while for Substation B, the range was from
46.9% - 59.5% and for Substations C, D and E the range for per cent
organic was 11.8 - 36.6%.
The overall stream quality above and below the Station I outfall appears
to be relatively the same. There does not appear to be any major change
in the chemical characteristics of the stream below the outfall, but
the effluent itself did effect the area directly around the discharge
point. The fact that the downstream areas did not appear affected could
be accounted for in part by the high discharge of the river at the time
of sampling which diluted the effluent.
The temperature, DO, turbidity, nitrate concentration and trace metal
concentrations of the effluent were within generally accepted levels
(Rambow and Sylvester, 1967), but the pH, specific conductance,
alkalinity, BOD, COD, phosphates and per cent organics were much greater
than those values for the river. The values for dissolved calcium and
magnesium were generally lower than those for the river (Appendices
1-5).
-------
The values for pH, BOD, COD, alkalinity, phosphates and per cent
organics indicate a future problem. During periods of low flow or no
flow on the Clear Fork Trinity River, the Station I effluent could
produce critical levels for these parameters and thus greatly affect
the fish life present in the pools or shallow water of the river .
Bioassays conducted on Station I effluent resulted in 96-hour TL5Q
values for minnows at concentrations of 4 - 9 per cent (Table 2,
Figure 8). So, in itself, the effluent is very toxic, not withstanding
the effects of the high BOD, COD, phosphates and greater per cent
organics which would tend to deoxygenate the water if it were not
reaerated. The low values for calcium and magnesium are probably due
to precipitation as carbonate salts in the alkaline effluent. The
high phenolphthalein alkalinity value reveals the presence of large
amounts of carbonate ion. The Federal Water Pollution Control
Administration (1968) recommends that the pH of a stream should not
be raised above a value of 9.0 or lowered below 6.0 by highly dis-
sociated materials. The values for the effluent generally were more
than three units higher than the river. If the river had been at a
lower discharge rate, the recommended values might have been exceeded.
The FWPCA also recommends total phosphates of not more than 0.1 mg/1.
This value may have been exceeded under a smaller discharge rate.
Rambow and Sylvester (1967) suggested that the stream BOD not be
increased by more than 2.0 mg/1 due to a waste discharge. This value
may well have been exceeded also during the low or no flow conditions.
The high BOD and per cent organic values indicate that the full effect
of the oxygen demand for the effluent was not shown by the BOD. The
organic load may have a more pronounced effect at lower river discharge
periods.
Station II: Storm Sewer Receiving Effluent from Small Industries
and Some Untreated Sewage
Five series of samples were collected during February and March 1970.
This station is located on the Clear Fork of the Trinity River. All
specific data are listed in Appendices 6-10. During the collecting
period the air temperature ranged between 13°C and 23°C. Water tem-
perature for Substation A ranged between 14°C - 18°C. For B the range
was between 17°C - 19°C and for C, D and E the range was between
14°C - 18°C.
Dissolved oxygen ranged between 7.2 - 9.8 mg/1 at A, between 3.0 - 4.0
mg/1 at B and between 6.8 - 10.0 mg/1 at C, D and E.
Values for pH ranged between 7.0 - 8.2 at A, from 6.4 - 7.9 at B, and
from 7.0 - 8.2 at C, D and E.
Measurements for specific conductance ranged between 500 - 530 micromhos/
cm at A, from 650 - 1,480 micromhos/cm at B and from 500 - 560 micromhos/
cm at C, D and E.
66
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Turbidity ranged between 21 - 35 JTU at Substation A, between 17 - 42
JTU at B and between 20 - 34 JTU at C, D and E.
Phenolphthalein alkalinity was recorded as 0.0 mg/1 as CaCO., for all
samples. Recorded values for total alkalinity ranged between 188 -
220 mg/1 as CaCO at Substation A, from 222 - 294 mg/1 as CaC03 at B
and from 174 - 222 mg/1 as CaCO at C, D and E.
The ranges for BOD at Substation A were between 1.2 - 4.0 mg/1, at B
between 13.6 - 32.0 mg/1 and at C, D and E between 0.8 - 4.2 mg/1.
The COD ranged between 8.3 - 28.0 mg/1 at Substation A, between 40.0 -
523.8 mg/1 at B, and between 0.0 - 93.1 mg/1 at C, D and E.
Nitrate concentrations observed ranged between 0.9 - 3.1 mg/1 NO
(0.2 - 0.7 mg/1 NO -N) at Substation A, between 3.1 - 5.8 mg/1 NO
(0.7 - 1.3 mg/1 NO^-N) at B and between 0.4 - 3.5 mg/1 NO (0.1 -
0.3 mg/1 N03-N) at C, D and E.
Orthophosphate observed at Substation A ranged between 0.02 - 10 mg/1,
while B ranged between 0.24 - 1.32 mg/1 P and C, D and E ranged
between 0.03 -0.12 mg/1 P. Hydrolyzable phosphate had the following
ranges: > 0.01 - 0.03 mg/1 P at Substation A, 0.09 - 0.64 mg/1 P at
Substation B, >0.01 - 0.03 mg/1 P at Substations C and D, and 0.02 -
0.04 mg/1 P at Substation E.
Calcium has a concentration range of 75.2 - 91.2 mg/1 at Substation A,
80.0 - 116.0 mg/1 at B and 67.2 - 107.2 mg/1 at C, D and E. Magnesium
ranged from 4.4 - 6.0 mg/1 at A, 5.2 - 9.6 mg/1 at B and 4.0 - 6.8
mg/1 at C, D and E.
Copper concentrations of all samples were less than 0.13 mg/1, while
zinc were all less than 0.13 mg/1 except one sample of the raw effluent
had a zinc concentration of 0.35 mg/1.
Iron concentrations were all less than 0.50 mg/1.
Most parameters for this station were near those values for the stream.
The only noticeably higher values were increases in BOD, COD, conductance,
nitrates and phosphates (Appendices 6 - 10). The flow rate of the
Station II effluent varied in accordance with rainfall.
The BOD and COD values were quite high for this effluent, but did not
appear to greatly alter values downstream (Appendices 6 - 10). This was
also true for nitrate and phosphate concentrations. It appeared that
the effluent was assimilated into the stream without a change in stream
values due to the small volume of effluent at the time samples were
taken.
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Station III: Chemical Plant Producing Cracking Catalysts for
Processing Combustion 'Engine Fuels
Five series of samples were collected at Station III during February
1970. This station is on the Trinity River downstream from where the
West Fork and Clear Fork of the Trinity join. All specific data are
listed in Appendices 11 - 15. The air temperature of sampling days
varied from -1°C to 10°C during this period (Figure 6, Appendices
11 _ 15). The water temperature ranged between 2°C - 5°C at Sub-
station A, between 13°C - 28°C at Substation B and 2°C - 18°C at
Substations C, D and E.
Dissolved oxygen concentration ranged between 12.2 - 12.8 mg/1 at
Substation A and 7.5 - 10.3 mg/1 at Substation B. The range was 8.0 -
12.8 mg/1 at C, D and E.
The pH value ranges at A, B, and C, D and E were 7.7 - 7.9, 5.3 - 11.9
and 6.2 - 9.6, respectively.
The range for specific conductance was between 400 - 520 micromhos/cm
at A, from 1,150- greater than 8,000 micromhos/cm at B and from
635 - 6,000 micromhos/cm at C, D and E.
Turbidity values ranged from 29 - 48 JTU at Substation A, from 36 -
95 JTU at B and from 25 - 91 JTU at G, D and E.
Phenolphthalein alkalinity was always 0.0 mg/1 as CaC03 at Substation
A, while at Substation B the range was between 0.0 - 1,480 mg/1 as
CaCO, and for C, D and E, it ranged between 0.0 - 276 mg/1 as CaC03.
Total alkalinity at Substation A ranged between 156 - 196 mg/1 as
CaCO,., at B between 34.0 - 2,046 mg/1 as CaC03 and at C, D and E
between 110 - 680 mg/1 -s CaC03.
The BOD values at A ranged between 0.0 mg/1 to 3.7 mg/1, at B between
0.1 mg/1 to 1.7 mg/1 and at C, D and E it ranged between 0.0 to 3.8
mg/1.
The range of values for COD were between 0.0 - 22.0 mg/1 at A, between
12.0 - 148 mg/1 at B and between 0.0 - 124 at C, D and E.
The concentration of nitrate ranged between 0.0 mg/1 N03 (0.0 mg/1
NO -N) to 6.6 mg/1 NO (1.5 mg/1 NO--N) at Substation A, from 7.1 mg/1
ml (1.6 mg/1 NO -N) to greater than 177.2 tag/1 NO (40.0 mg/1 M^-N)
at3B arid between 2.2 mg/1 NO (0.5 mg/1 NO^N) to 111.6 mg/1 N03
(25.2 mg/1 N03-N) at C, D and E.
Orthoph,3-.:hate concentration at Substations A, B, and C, D and E ranged
between 0.10 - 0.25 mg/1 P, 0.18 - 2.00 mg/1 P and between 0.02 - 0.88
mg/1 P, respectively, while hydrolyzable phosphates ranged between
0.00 mg/1 P to 0.10 mg/1 P at Substation A, between 0.00 mg/1 P to 0.12
mg/1 P at B and from 0.00 mg/1 P to 0.18 mg/1 at C, D and E.
68
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Dissolved calcium ranged between 64.0 - 105.6 mg/1 at Substation A,
from less than 0.25 - 4.0 mg/1 at B and between 2.4 mg/1 to 8.8 mg/1
at C, D and E.
Dissolved copper concentrations at all substations were always less than
0.25 mg/1.
Zinc concentrations were all less than 0.25 mg/1, except on two dates
when a concentration of 1.0 mg/1 was observed for B and on another
date when 0.50 mg/1 and 0.30 mg/1 were recorded for B and C, respectively.
Values for iron were all recorded as less than 1.0 mg/1.
Organic carbon percentages for suspended matter ranged between 28.8 -
48.3 per cent at Substation A, from 17.9 - 24.1 per cent at B and
between 18.6 - 31.7 per cent at C, D and E.
River discharges for the sampling days ranged between approximately
27 - 86 million gallons daily (Fort Worth Water Department).
The effluent from Station III appeared to have a great effect on the
chemical quality of the stream below the outfall and for several
hundred yards downstream.
The discharge from this station was generally a white to bluish color
and quite turbid due to a floe. Downstream portions of the West Fork
Trinity River were coated with this floe several inches deep in
numerous places. What appeared to be deposits of the floe were found
at another station a few miles downstream. The discharge rate is
quite variable, ranging between a trickle to a very heavy flow.
Generally the effluent exhibits high temperature, extreme pH changes,
high specific conductance, high turbidity, variable alkalinity, very
high nitrate values and occasionally high phosphate concentrations
(Appendices 11 - 15) . The calcium and magnesium values were generally
lower than those of the river (Appendices 11 - 15). During monitoring
over a seven-hour period, pH value ranged between a low of 1.8 to a ,
high of 7.5, while the temperature ranged between 22° and 30°C, the
conductance value ranged from 2,050 to more than 8,000 micromhos/cm.
Increased metabolism and degradation associated with the temperature
elevation may reduce DO in the river. Rambow and Sylvester (1967)
recommend as a standard to maintain water quality that the discharge
of effluents from industrial and domestic sources not be greater than
2°C above the natural temperature of the stream. The effluent is not
within this recommendation.
The drastic changes in pH observed (Appendices 11 - 15), probably cause
great stress on the organisms downstream from the outfall. The pH
changes may cause reduction in their tolerance to temperature, certain
metals and low DO. The FWPCA (1968) recommends that the pH of a stream
69
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not be lowered below 6.0 or raised above 9.0 by discharge of waste.
Station III effluent, during periods of low discharge rate of the
Trinity River, would probably raise and/or lower the pH outside
the standards set forth.
After studying reports compiled by the Fort Worth Water Department,
it was concluded that the major cause of the high conductance of the
Station III effluent was discharge of sulfate ions in large quantities.
The conductivity downstream at times reached levels of 200% greater
than upstream values (Appendices 11 - 15). This value exceeds
Rambow and Sylvester (1967) by almost 75%, as they recommended that
the conductivity not exceed 125% of the natural conductance of the
river or stream, and preferably not more than 110% of natural values.
The turbidity revealed high concentrations of suspended matter.
Although this matter has a relatively low organic content, the effects
of the floe may be many. High concentrations of suspended material
may, as mentioned, be in themselves harmful to fish by mechanically
damaging their gills. The suspended matter also reduced penetration
of light, thereby reducing the plant population downstream and
limiting photosynthesis. The floe may affect the benthic fauna by
coating the bottom to a depth of several inches covering the food
sources and spawning areas. The FWPCA (1968) suggested that the
turbidity not exceed 50 JTU in warm water streams due to waste
discharges. This value was exceeded at times (Appendices 11 - 15).
The values for nitrate and phosphate in the stream increased greatly
downstream from Station III outfall (Appendices 11 - 15) . This
probably stimulates growth of plankton and algae which cause an
increased BOD due to their decomposition.
Rainbow and Sylvester (1967) recommend no more than 0.4 mg/1 increase
in nitrates above natural values, as permissible, but state that
ideally, no more than 0.1 mg/1 increase should be permitted. For
phosphates they recommend no more than a 0.15 mg/1 increase over
natural conditions in the stream, but also point out that a more
desirable value would be no more than 0.03 mg/1 increase in total
phosphorus. The FWPCA (1968) states that the total phosphorus
concentration should not be increased to a level above 0.1 mg/1 P
and that the natural nitrogen-phosphate ratio should be maintained. All
these recommended values have been exceeded and at least for nitrates,
significantly increased.
The overall effect of the Station III waste effluent it appears is to
cyclically alter the natural conditions downstream from its outfall.
The rapid change in pH, conductance and turbidity might be too great for
most stream organisms to tolerate. It seems apparent that during periods
of low river discharge, that this effluent could greatly reduce the fish
population in the area downstream from the outfall, as well as
seriously damage the benthic fauna.
70
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Station V: Sewage Treatment Plant Receiving Industrial and
Domestic Wastes
This sewage treatment plant is located on the northeast side of Fort
Worth and discharges its effluent through two outlets into the Trinity
River. Samples were collected in the vicinity of each outfall during
June 1970. All specific data are found in Appendices 16-22.
The air temperature when sampling varied from 25°C - 30°C. Water
temperature ranged between 27°C - 29°C at Substation A*, between
27°C - 28°C at B* and between 28°C - 30°C at C*, D* and E*. Water
temperature ranged between 25°C - 29°C at B and between 25°C - 30°C
at C, D and E.
Dissolved oxygen ranged between 4.8 - 10.2 mg/1 at Substation A*, from
3.0 - 5.6 mg/1 at B* and between 1.6 - 7.4 mg/1 at C*, D* and E*. DO
ranged between 5.4 - 7.2 mg/1 at B and between 2.0 - 5.4 mg/1 at C, D
and E.
The pH values ranged between 7.4 - 7.8 at Substation A*, between 7.1 -
7.6 at B* and between 7.1 - 7.8 at C*, D* and E*. Values for pH at B
ranged between 7.1 - 7.7 and between 7.3 - 7.8 at C, D and E.
Specific conductance ranged between 850 - 1,300 micromhos/cm at
Substation A*, between 950 - 1,100 micromhos/cm at B* and between
660 - 1,250 micromhos/cm at C*, D* and E*. At Substation B and C,
D and E the range was 975 - 1,100 micromhos/cm and 720 - 1,125
micromhos/cm, respectively.
Turbidity ranged between 16 - 28 JTU at Substation A*, between 20 - 43
JTU at B*, between 13 - 37 JTU at C*, D* and E*, between 13 - 23 JTU
at B and between 12 - 32 JTU at C, D and E.
Phenolphthalein alkalinity was 0.0 mg/1 as CaCO,, for all samples
analyzed. Total alkalinity ranged between 164 - 182 mg/1 as CaCO.,
at Substation A*, between 220 - 306 mg/1 as CaCO., at B* and between
174 - 216 mg/1 as CaCO~ at C*, D* and E*. The range for B and C, D
and E were 202 - 298 mg/1 as CaCO and 186 - 238 mg/1 as CaCO-,
respectively.
The BOD data for this station were particularly inconsistent and
inconclusive.
The range of COD values was between 25.4 - 39.2 mg/1 at Substation A*,
135.7 - 275.6 mg/1 at B*, 38.2 - 76.3 mg/1 at C*, D* and E*, 72.1 -
101.8 mg/1 at B, and 42.4 - 89.0 at C, D and E.
Nitrate concentrations ranged between 2.8 - 13.3 mg/1 NO. (0.6 - 3.0
mg/1 NO^-N) at Substation A*, from less than 0.1 mg/1 NO to 31.0 mg/1
NO (0.03 - 7.0 mg/1 NO--N) at B* and from 0.9 - 11.5 mg/1 NO
71
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(0.2 - 2.6 mg/1 NO--N) at C*, D* and E*. Values at B and C, D and E
ranged between 21.3 - 48.7 mg/1 NO (4.8 - 11.0 mg/1 N03-N) and 6.2 -
29.2 mg/1 N03 (1.4 - 6.6 mg/1 NO^N, respectively.
The effects of the sewage treatment plant effluent on the West Fork
of the Trinity River were apparent by visual observation. The foam
from detergents processed by the plant is carried down the river for
several hundred yards. The foam alone creates serious ecological
problems by limiting the amount of light that enters the water and
by reducing reaeration of the stream water.
Only three parameters do not show a noticeable change from upstream
values to downstream values - water temperature, pH and turbidity
(Appendices 16 - 22).
Values for dissolved oxygen show a general depletion downstream from
the effluent, at times approaching zero. This may be attributed to
three major factors associated with the sewage treatment plant: high
organic content in the effluent, high concentrations of both nitrogenous
material and phosphates in the effluent and formation of foam which tends
to lower or to maintain a low DO by preventing reaeration. The nitrates
and phosphates promote growth of algae and aquatic plants . As the
plants decompose available oxygen is utilized. The DO values reported
reveal a serious threat to fish and other aquatic organisms. Ellis
(1937) and FWPCA (1968) suggest that stream dissolved oxygen in warm
water areas should be maintained above 5.0 mg/1 for a good, varied
warm water fish population. The FWPCA also states that DO values may
fall below 5.0 mg/1 for short periods but should not go below 4.0
mg/1 or be maintained at 4.0 mg/1 for any extended time. These
values are not maintained in the river downstream from the sewage
effluent.
Specific conductance varied in both the river and the effluent, but due
to the high rate of discharge of the effluent, the conductance values
for the river were affected by the effluent. The range was generally
not great, but the change did show the lack of dilution water in
relation to the volume of effluent discharged. At times the value
exceeded the 125 per cent above natural conditions set as a standard
by Rambow and Sylvester (1967).
The total alkalinity values for the effluent were generally much
higher than those for the river. This was due probably to an increase
in bicarbonates. Neel e_t _al. (1963) found that decomposition and/or
respiration both tended to increase bicarbonate concentration in raw
sewage stabilization ponds. The increase in alkalinity in the river
is noticeable but does not appear to be critical.
Biological oxvgen demand results for the effluent were not conclusive.
The results w..re far froi.i con-: *-pnt. Reasons for this might be due
to too great dilution of the effluent, increasing the lag phase for
72
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bacterial growth so that full utilization of the organics present
is not accomplished during the five-day period. Another possibility
for inconsistent BOD results might be that the dilutions were so great
as to reduce the organic material below a level to realize an oxygen
demand. Data collected by the local water department show values for
BOD for both plant effluents to average between 26 and 55 mg/1 for
those days sampled.
While the BOD results were inconsistent, the COD results showed that
the organic matter present in the effluent was very high, and this
effluent increased the COD value of the stream by almost three times.
The discharge of organic material is probably the main reason for
reduction of dissolved oxygen downstream from this plant. Rambow and
Sylvester (1967) recommend that no more than 2.0 mg/1 increase in
stream BOD should be effected by a waste discharge. It is obvious
that organic matter should not be added which might reduce the
concentration of DO below required levels.
Nitrate concentrations for this station increased the stream nitrates
by almost a factor of 10 (Appendices 16 - 22). Courchaine (1968)
revealed that most nitrogenous wastes in wastewater exist as ammonia
and organic nitrogen. When these were oxidized to nitrates,
significant quantities of oxygen are consumed. Courchaine (1968)
found that each mg/1 of NH.,-N oxidized to nitrate was equivalent to
4.57 mg/1 BOD. He reported that the single most important factor
affecting stream DO was nitrification in the critical reaches down-
stream from a sewage treatment plant. Courchaine also stated that
this nitrification accounted for 75 per cent of the total oxygen
demand. Although ammonia concentration was not determined by this
study, the Fort Worth Water Department (1970) showed ammonia concen-
trations of from 7-13 mg/1 on those days when samples were collected.
It can be seen that an additional oxygen demand of almost 60 mg/1
would be exerted by the effluent in the river due to oxidation of
NH -N to N03~N.
Orthophosphate and hydrolyzable phosphate levels were also high
(Appendices 16 - 22). Values for both hydrolyzable and orthophosphates
increased by almost a factor of 10 from the upstream to downstream from
the outfall. The phosphorus level recommendations of the FWPCA (1968)
and Rambow and Sylvester (1967) have not been maintained. The effect
of the high phosphate concentration probably will be realized several
miles downstream where the excessive growth of algae and other aquatic
plants might create an unpleasant condition due to their mass decompo-
sition. Metzler et_ aJ. (1958) reported that orthophosphate is seldom
removed by sewage treatment plants.
Dissolved calcium and magnesium concentrations in the effluent appear
to be somewhat lower than comparable values for the river. The possible
cause for this might be due to the uptake in the human body or in the
73
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microorganisms which inhabit the sewage treatment plant, or maybe the
original source of the water was lower in calcium and magnesium than
the river at this point.
The overall effect of this treatment plant appears to be a constant
disturbance of the natural state of the river. With the continual
discharge of sewage treatment plant effluent, a good, mixed fish fauna
would not be able to inhabit the downstream region of this river
effected by the disdiarge.
The effects might not be observed so easily during the winter months,
but during the summer months when the river discharge is at its
lowest, the sewage treatment plant's effluent may constitute 60 per cent
or more of the total river discharge below the outfall. This can be
pointed out more effectively by comparing the discharge rates of the
river and effluent on those days sampled. During the sampling period,
the river discharge ranged from about 13 - 20 mgd (preliminary
unpublished data from U. S. Geol. Surv.) while the discharge rate of
the effluent ranged from 25 - 33 mgd (Fort Worth Water Department data).
As can be seen, the effluent at that time made up generally more than
50 per cent of the total discharge of the river downstream from the
outfall. With lack of precipitation, it is not difficult to imagine
the effluent comprising almost 100 per cent of the discharge of the
river below the outfall.
Station IX; Small Tributary Receiving Effluents from Meat Packing
and Rendering Plants
This station is a tributary of the Trinity River and receives wastes
from the stockyards, packing houses and rendering plants. Five series
of samples were collected during April 1970. All specific data are
listed in Appendices 23 - 27.
The air temperature when sampling varied from 23°C - 27°C. The range
of water temperature was between 19°C - 22°C at Substation A, upstream
19°C - 22°C at Substation B, the tributary and 19°C - 22°C for
Substations C, D and E, downstream.
Dissolved oxygen measurements ranged between 8.6 - 9.2 mg/1 at
Substation A, between 8.2 - 9.0 mg/1 at B and between 8.4 - 9.4 mg/1
at C, D and E.
The pH values ranged between 7.4 - 7.9 at Substation A, 7.5 - 8.1 at
B and between 7.3 - 7.0 at C, D and E.
Specific conductance varied from 390 - 450 micromhos/cm at Substation
A, from 540 - 825 micromhos/cm at B and from 280 - 450 at C, D and E.
-------
Turbidity measurements varied from 40 - 63 JTU at Substation A, 16 -
43 JTU at B and from 38-63 JTU at C, D and E.
The value for phenolphthalein alkalinity was 0.0 mg/1 at CaCO^ for all
samples, while the total alkalinity ranged between 118 - 158 mg/1 as
CaCO at Substation A, 126 - 228 mg/1 as CaC03 at B and from 134 - 172
mg/1 as CaCO at C, D and E.
The BOD ranged from 1.4 - 1.8 mg/1 at Substation A, 1.8 -4.0 mg/1 at
B and from 0.0 - 1.9 mg/1 at C, D and E.
A range from 10.0 - 22.4 mg/1 at A, 16.6 - 19.9 mg/1 at B and from
10.0 - 22.4 mg/1 at C, D and E was observed for COD.
Nitrate ranges observed were less than 0.4 mg/1 NO (less than 0.1 mg/1
NO -N) at Substation A. Values at B ranged between 2.2 - 8.0 mg/1 NO^
(0?5 - 1.8 mg/1) and at C, D and E less than 0.4 mg/1 N03 (less than
0.1 mg/1 N03-N) to 3.1 mg/1 N03 (0.7 mg/1 NO^N) .
The orthophosphate range was between 0.05 - 0.09 mg/1 P at Substation
A, 0.09 - 0.42 mg/1 P at B and 0.05 - 0.10 mg/1 at C, D and E.
Hydrolyzable phosphate ranged from less than 0.01 mg/1 P to 0.01 mg/1 P
at Substation A, and C, D, E and from less than 0.01 mg/1 at 0.04
mg/1 P at B.
The concentration of calcium ranged between 42.0 - 54.0 mg/1 at Sub-
station A, between 60.0 - 82.0 mg/1 at B and between 42.0 - 52.0 mg/1
at C, D and E. Magnesium concentration varied between 4.8 - 6.4 mg/1
at Substation A, between 3.6 - 4.8 mg/1 at B and between 5.2 - 6.8 mg/1
at C, D and E.
Values for copper, zinc and iron were less than 0.13 mg/1 for all
samples.
River discharges on sampling days ranged from approximately 389 - 1,620
million gallons daily (provisional advanced unpublished data collected
by U.S.G.S. received from Fort Worth Water Department).
Station IX had generally higher values for nitrates, phosphates, specific
conductance, pH, alkalinity, BOD and dissolved calcium than the West Fork
Trinity but had lower values for turbidity and magnesium (Appendices
23 - 27). However, the entrance of Station IX had little apparent
effect on the Trinity River.
The high values for nitrates and phosphates may be due to some indus-
trial discharge, but are more likely due to domestic sources. The
nitrates may be due to fertilizer runoff, (Task Group Report, 1967),
while the phosphates may also be due to domestic runoff into storm
sewers, (Task Group Report, 1967).
75
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The values for pH, conductivity, alkalinity and dissolved calcium
are probably due to closer contact with local geological formations.
Station IX flows through a limestone area, and would have a tendency
to take into solution more calcium and bicarbonate which would increase
the alkalinity, pH and conductivity slightly.
The low values for turbidity for Station IX indicates that either the
suspended matter draining into this station is low, or that it is low
relative to the West Fork of the Trinity River, which was in a state
of high discharge. The lower turbidity of Station IX may be due to
drainage of an area which has more vegetation. The increase in BOD is
slight, but might indicate organic contribution by urban runoff.
This station does not appear to strongly affect the character, either
physically or chemically, of the West Fork of the Trinity River.
Station X: Tributary Receiving Effluents from Small Industries and
a Food Packing Plant
Station X is a tributary of the Trinity River. It receives waste
effluents from a food packing plant and other light industries. Five
series of samples were collected during May 1970. All specific data
are listed in Appendices 28-32.
The air temperature when sampling ranged from 24°C - 30°C. Water
temperature measurements were 24°C for Substation A, upstream, but
ranged between 23°C - 25°C for Substation B, C, D and E , the downstream
substations.
Dissolved oxygen concentrations ranged between 5.0 - 8.8 mg/1 at
Substation A, between 6.8 - 11.0 mg/1 at B and between 5.2 - 8.8 mg/1
at C, D and E.
The value for pH ranged between 7.1 - 7.7 at Substation A, between
7.4 - 7.9 at B and from 7.0 - 7.8 at C, D and E.
Specific conductance had a range of 480 - 790 micromhos/cm at
Substation A, 450 - 900 micromhos/cm at B and 495 - 780 micromhos/cm
at C, D and E.
Ranges for turbidity were between 17 - 36 JTU at Substation A, 4 - 45
JTU at B and 18 - 37 JTU at C, D and E.
Values for phenolphthalein alkalinity were 0.0 mg/1 at CaCO at all
substations. Total alkalinity ranged between 146 - 180 mg/1 at CaCO^
at Substation A, from 156 - 280 mg/1 as CaC03 at B and between 144 -
182 mg/1 as CaCC>3 at C, D and E.
The BOD values varied between 2.0 - 5.7 mg/1 at Substation A, between
2.0 - 13.6 mg/1 at B and between 1.7 - 6.4 mg/1 at C, D and E.
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The COD ranged between 20.0 - 25.9 mg/1 at Substation A, between 20.0 -
59.4 mg/1 at B and between 12.0 - 28.6 mg/1 at C, D and E.
Nitrates were observed in the ranges of 2.8 - 5.3 mg/1 NO., (0.6 -1.2
mg/1 N03-N) at Substation A, 0.9 - 4.9 mg/1 NO (0.2 -1.1 mg/1 N03~N)
at B and of 2.2 - 6.3 mg/1 NO (0.5 - 1.4 mg/1 NO -N) at C, D and E.
Orthophosphates ranged from 0.04 - 0.09 mg/1 at Substation A, 0.25 -
1.32 mg/1 P at B and between 0.03 - 0.29 mg/1 P at C, D and E, while
hydrolyzable phosphates ranged from less than 0.01 mg/1 P to 0.05 mg/1
P at Substation A, less than 0.01 mg/1 P to 0.08 mg/1 P at B and from
less than 0.01 mg/1 P to 0.07 mg/1 P at C, D and E.
Calcium ranged between 58.0 - 62.0 mg/1 at Substation A, between
54.0 - 102.0 at B and between 58.0 - 66.0 mg/1 at C, D and E.
Magnesium ranged between 5.8 - 7.4 mg/1 at Substation A, between
5.2 - 12.8 mg/1 at B and between 5.6 - 8.0 mg/1 at C, D and E.
Values for copper, zinc and iron were all less than 0.13 mg/1.
Generally, the dissolved oxygen, pH, BOD, COD and phosphates at Station
X were higher in the creek than in the river, while values for nitrate
and turbidity were lower for the creek than the river (Appendices
28 - 32). The values for conductance, alkalinity, dissolved calcium
and dissolved magnesium in the creek were quite variable (Appendices
28 - 32).
The higher DO values may be due to greater aeration in the more
shallow creek or greater photosynthesis. The creek bottom was
covered with plant growth, either algae or higher aquatic plants. The
pH values for the creek were only slightly higher than for the river
which may indicate the presence of a more alkaline drainage basin. The
BOD and COD values were probably higher due to public littering and
trash dumping. During previous preliminary investigations, it was
noticed that some areas upstream were almost blocked by trash and
litter. The BOD and COD could also have been increased by natural
litter contributed by the many surrounding trees. Natural leaf litter
could result in both a higher BOD and COD downstream. Another reason for
increased BOD and COD might be due to runoff from local small
industries.
Higher concentrations of phosphates at Station X than in the Trinity
River may be indications of runoff from local car wash services, urban
runoff or from natural deposits higher in phosphates.
Station X has a similar chemical character to that of the Trinity
River. The junction of this creek with the Trinity River does not
appear to cause any significant change in water quality downstream
from this junction.
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Trace Metal Investigation
A satellite investigation was conducted to determine concentrations
of selected toxic metals in water and sediments of the Trinity River
and Village Creek. Thirty-two water samples, 34 sediment samples and
eight plating effluents were analyzed.
Copper was the only metal detected in excess of 0.1 ppb in all waters
sampled, ranging between 2 and 52 ppb. Sediments contained up to 2,461
ppb copper, 1,604 ppb nickel, 126.0 ppb zinc, 221.5 ppb cadmium, 142.5
ppb lead and 1,200 ppb mercury. Effluents contained up to 300 ppb
cadmium, 24.5 ppb mercury, 25 ppb copper, 320 ppm nickel, 13.0 ppm zinc
and 147.5 ppm chromium. Sediments from the Industrial Area contained
the highest concentrations, with outfalls and dumps being the most
significant sources.
Benthos
Station I; Railroad Equipment Cleaning Area
Samples taken above Station I showed the greatest abundance and
diversity of taxa with the most favorable conditions apparently
existing in the center of the stream (Appendix 33) . There was a
total of 3,196 individuals and 14 taxa at this station as compared
with 735 individuals and eight taxa at the station located at the mouth
of the outfall (Appendix 34) . Samples taken 70 yards below the
discharge increased in diversity and abundance with 1,420 individuals
and 11 taxa, while those about 150 yards downstream showed a reduction
to 405 individuals and nine taxa (Appendices 35 - 36) .
The reduction in diversity and numbers of individuals at the mouth of
the outfall from those found upstream indicate an environmental stress
does occur at this station. There are some variations in physical
characteristics between these two stations. The depth is slightly
greater at the mouth of the outfall and is partially protected from
illumination by an overpass, but these factors should enhance rather
than suppress the abundance of benthos. It was concluded, therefore,
that the stress was due to the effluent at this site.
A considerable variation in abundance of benthos occurred at the two
stations located downstream. The increase in number of organisms from
samples 70 yards below the discharge was primarily due to the increase
in abundance of oligochaetes. The river widens at this point and
reduced current has resulted in deposition of fine sediments which
favors an abundant oligochaete population. An overpass at this
substation shades it from direct illumination during mid-day. The
river narrows again at the site farthest downstream and the bottom
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is very rocky resulting in a reduction of oligochaetes. The water is
also more shallow at this point causing greater instability arising
from seasonal fluctuation in water levels of the river (Appendices
33 - 36).
Station II; Typical Storm Sewer Receiving Effluent from Small
Industrial Plants and Some Untreated Sewage
The dominant organisms at all of the substations were oligochaetes.
Six hundred twenty-seven organisms representing eight taxa were taken at
the station above the outfall (Appendix 37). A slight increase in
numbers of oligochaetes was recorded at the mouth of the outfall
(Appendix 38) and consequently a small increase in total number of
organisms to 886. Six taxa were represented but rhis reduction was
not considered significant since the groups which were missing
occurred in such small numbers above the discharge. No significant
changes in benthos occurred 70 yards downstream with 733 individuals
and six taxa (Appendix 39) . A significant increase was recorded 600
yards downstream in the oligochaete population which increased the
total number of individuals to 1,215. This can be explained by the
softer nature of the bottom sediments at this site. Eight taxa were
found at this station (Appendix 40).
Core samples were taken above the outfall to determine the maximum
depth of penetration by the benthos . Oligochaetes were the deepest
burrowing organisms recovered, and they were found at depths up to
3 inches. These results correlated well with preliminary samples
taken in April 1970. The effluent at Station II was judged to have
very little effect on the invertebrate bottom fauna when compared
to samples taken above the outfall (Appendices 37 - 40).
Station III: Chemical Plant Producing Cracking Catalysts for
Processing of Combustion Engine Fuels
Four hundred twenty-five individuals representing ten taxa were found
above the outfall (Appendix 41). Diptera larva and oligochaetes
(Family Tubificidae) were predominant. Similar numbers were recorded
from samples taken at the discharge with respect to total taxa (13)
and number of individuals (343), but all of these were recorded from
the center of the stream to the bank opposite the outfall (Appendix 42).
There were no living organisms from the mouth of the outfall to mid-
stream. Similar results were observed 30 yards downstream, the bottom
being devoid of life under the plume of white floe (Appendix 43).
Samples taken 150 yards down from the discharge showed some degree
of recovery although the benthos was still quite sparse on the side
of the river most influenced by the effluent (Appendix 44).
79
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Whether the material was actually toxic to the organisms was not
determined but the volume of suspended matter was judged to be
sufficient to impair benthic life regardless of toxicity. Gammon
(1970) found significant reductions in populations of macroinverte-
brates resulting from increased loads of suspended inorganic solids.
The volume of solids at this outfall was so great that any bottom
dwelling organisms would probably be smothered by this material.
Benthic populations were established on the side of the river opposite
the site of discharge since the river current carried the floe down-
stream. The benthos from midstream to the bank opposite the outfall
approached that of samples taken above the discharge. Some degree of
recovery was observed 150 yards downstream since much of the suspended
solids had settled out by this time, but the very low population
indicated there was still much stress on the benthic community
(Appendices 41 - 44) .
Station V; Sewage Treatment Plant Receiving Industrial and
Domestic Wastes
There are two outfalls from the sewage treatment plant into the
Trinity River. Samples were taken between the two outfalls just above
and at the mouth of the lower one. Because of the increase in current
velocity samples 7-10 could not be obtained at the mouth of the
outfall. Samples below the lower outfall were not taken. Samples
taken above the outfall showed a predominance of oligochaetes
(Tubificidae) with nematodes being the second most abundant organisms
(Appendix 45). There was a total of 1,339 individuals in the ten
samples with six taxa represented.
A very drastic reduction in animals occurred at the mouth of the
outfall. Although samples 7 - 10 could not be obtained at this
station, there was an obvious difference of organisms in samples
1-5 (Appendix 46).
There was a considerable number of dead gastropods of the genus
Physa. Only five tubificids, one dipteran (Tendipedidae) and one
cyclopoid copepod were found in samples 1-5. Sample 6 was somewhat
richer with 21 nematodes, three tubificids and two tendipedids.
The low dissolved oxygen and high organic content associated with
streams polluted with sewage usually results in large numbers of
tubificids (Pennak 1953). The absence of this group as well as
others suited to this habitat is believed to result from the
chlorination of the effluent prior to its release into the river.
The concentrations of dead Physa may result in part from individuals
in the sewage plant being killed by the chlorine and passing out with
the effluent to settle into the river sediments. Since living Physa
were found above the outfall, many of the dead snails may also result
80
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from killing of individuals which move from above into the stream of
chlorinated effluent. The current becomes quite strong near the
center of the river causing the effluent to have less effect from
midstream to the far bank. This is reflected in the increase in
individuals in sample 6 taken near the center of the river
(Appendices 45 - 46) .
Station VI: Metal Etching Plant Using Various Acids
Twenty grab samples were taken at Station VI to see if organisms were
able to live in the effluent. Five samples taken in the holding
pool near the plant revealed no life. The effluent flows from the
holding pool into an abandoned gravel pit. Five samples were taken
along a transect across the entrance to the pit. Ten Odonata larvae
and one coleopteran were recovered from the sample nearest the bank.
Two transects consisting of five samples each were also taken
across the two main pools in the gravel pit. No life was found at
these stations.
Station IX: Small Tributary Receiving Effluents from Meat Packing
and Rendering Plants
Five hundred thirty-two individuals representing 11 taxa were taken in
samples above the junction of the tributary with the Trinity River
(Appendix 47). Of these, 407 were dipteran larvae and 94 were
oligochaetes (Tubificidae). At the mouth of the tributary there was
a significant increase in the number of tubificids (446) and a slight
decrease in dipterans (279) . There was a total of 740 individuals
and six taxa at this location (Appendix 48). The principal difference
was in the increase in number of tubificids which probably resulted
from increased organics. Thirty yards downstream the number of
individuals increased to 1,160 and the taxa to eight, and at 150 yards
the total count was 615 with eight taxa (Appendices 49 - 50) . Dipteran
larva and oligochaetes continued to be the dominant forms at these
stations (Appendices 47 - 50).
Station X: Tributary Receiving Effluents from Small Industries and
a Food Packing Plant
Nine taxa and 943 individuals with oligochaetes and dipterans the
dominant organisms were collected at this station (Appendix 51).
At the mouth of the tributary very little change was noted (Appendix 52)
Oligochaetes and dipterans still predominated; the total number of taxa
was six and the number of individuals was 1,064. The absence of three
taxa at the mouth as compared with samples taken upstream was not
considered significant since they occurred in such low abundance that
sampling error could have accounted for their absence. A continued
81
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abundance of dipterans and oligochaetes occurred at 70 and 150 yards
downstream and there was a reduction in dipteran number at 150 yards
(Appendices 53 - 54). There were 1,173 individuals with seven taxa
70 yards below and 1,076 individuals with eight taxa 150 yards below
the junction of the tributary with the Trinity. The total number of
individuals remained relatively constant. As oligochaete numbers
increased, dipteran numbers decreased (Appendices 51 - 54) .
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SECTION VI
DISCUSSION
The Trinity River is a small stream of relatively low flow and in an
area of somewhat limited precipitation especially during the summer
months. Discharge of the river is due primarily to runoff and seepage
from the drainage basin and controlled release from Benbrook Lake. The
Clear Fork drainage area is a 518 square mile sector of North Central
Texas while the West Fork drains 2,615 square miles of the same general
area (Water Resources Data for Texas, 1969, 1970). Both have dams up-
stream which provide flood control, water supplies and recreation for
the surrounding region. The West Fork has six major reservoirs upstream
from Fort Worth which are primary sources of water supply for the urban
area. Benbrook Lake is the main reservoir on the Clear Fork which is
primarily a part of the Trinity River Flood Control System.
Average annual precipitation in the Fort Worth region approximates 31
inches (Climatological Data, Annual Summary, 1969, 1970). This area
received 4.36 inches of rainfall above the annual average during 1969
and 4.77 inches in 1970. During the first seven months of 1971, only
July received as much as the average amount of rainfall (Appendix 55).
The low flow of the river resulted not only from limited precipitation
but also from the fact that 83,510 acre-feet were retained in reservoirs
of the West Fork for municipal and industrial use. In addition a total
of 267 acre-feet were diverted from the Clear Fork for irrigation (Water
Recources Data for Texas, 1969, 1970). However, added to this limited
volume are discharges from industrial activities and sewage treatment
plants. During months of low rainfall the greater percentage of volume
in the river may be attributed to industrial effluents and discharge
from sewage treatment plants. The above conditions contribute to the
rather poor quality of the water in the Trinity River and afford a
hazard for the biota present. Because of the limited volume of water
from seepage and runoff, the possibility of alleviation of the
undesirable effects of polluting effluents by dilution is quite remote.
Value of river, lake and reservoir waters is seriously impaired for
recreational purposes even by relatively small loads of sediment
(Gammon, 1970). Additives from domestic and industrial sources are
detrimental to other uses of water. This appears to be particularly
true of the Trinity River since much of its volume may result from
such sources. A true evaluation of the effect of suspended substances,
however, is difficult because of their diversity of origin. The effect
on river biota of floe associated with effluents from a plant producing
cracking catalysts had some semblance to that of various other types of
sediment. Much of the study on effects of sediments on life in streams
has been conducted in regions of mines and sediments resulting from
mining activities (Cordone and Kelley, 1961). Results of such studies
generally indicated adverse effects on stream organisms.
83
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Many of the effluents involved in this study were quite turbid.
Turbidity is usually an indicator of pollution. Turbidity reduces
the euphotic zone which in turn limits photosynthesis and the release
of much needed oxygen for aquatic life. This limits populations
especially fish with respect to number and variety. Ellis (1937) did
extensive turbidity studies and related adverse effects on fish.
Associated with the most turbid of the effluents studied was a
sizeable fish kill and repeated observations of fish floating life-
lessly through the plume of the effluent being discharged. It has
been found that various species of fish not only attempt to avoid turbid
waters but alter their feeding habits and tend to migrate (Sumner and
Smith, 1939; Bachman, 1958; Hofbauer, 1962). The heavy foaming
associated with Stations I and V effluents and floe of Station III are
conditions that suggest possible migration of fish. However, fish
surveys along the Trinity River were inconclusive as to quality,
quantity and migratory activity because of channeling procedure,
other construction and low water during the period of study.
The restricted size of the Trinity River coupled with the limited
rainfall especially during the warmer months, renders this body of
water quite vulnerable to industrial pollution. Almost any pollutant
in sufficient concentration and given enough time can greatly impair or
destroy a population. Some organisms such as fish may spend their
entire lives in a given region and a severe pollutant may eliminate
this species. A polluting agent from an outfall into a stream may
block passage of organisms from one region to another thereby
preventing their movement into breeding places. Copious amounts of
inert substances in the effluent can result in various problems such
as smothering spawn and fry, obliterating food supplies, concealing or
destroying protective physical features and clogging the gills of
fish resulting in possible decreased oxygen uptake. Of the industries
investigated, the railroad cleaning area and cracking catalyst
producing plant could readily contribute to the above conditions .
Domestic sewage and industrial pollution change water quality in
streams (Matthews and Neuhold, 1967). It is well known that organic
polluting substances greatly alter species structure and quality of
both flora and fauna (Wilhm, 1967). Trautman (1933) relates the
movement of fish upstream to a region above sewage outfalls especially
when stress may be accentuated by low water and elevated temperature.
Sewage and organic substances exert great effects on stream communities
through uptake of oxygen beyond normal balance of respiration and
photosynthesis in streams (Reid, 1961). Although fishes and other
organisms may be tolerant to effluents containing sewage and similar
wastes, indirect effects may be adverse to many species. Oxygen
depletion reduces resistance of fish to pathogens, reduces agility
thus limiting their ability to seek food and escape predators and
may result in direct death. Scavenger type organisms may accumulate
in these areas replacing predators. Katz and Gaufin (1952) found
in their investigation that although several species of fish were
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relatively tolerant to unfavorable conditions no species could be
designated or used as indicators of pollution. Effluents containing
untreated or inadequately treated sewage had high oxygen depleting
qualities. Effluents from the stockyards and various meat processing
plants may exert the same effect. At the time of study one sewage
treatment plant discharged effluent that differed very little from
the incoming untreated sewage. Consequently, its oxygen depletion
capacity was very high. It is reported that material going into
this plant is to be diverted to the sanitary sewer system of Fort
Worth and adverse conditions from this source will be averted.
Aquatic life is frequently thought of in terms of fish or some other
harvestable species. In order to maintain a population of fish it is
necessary to have supporting plants and animals that will afford a
ready supply of food. The destruction of the supporting organisms —
benthos, plankton and the like—in turn destroys the fish. Conse-
quently, any industrial effluent containing suspended or dissolved
foreign materials should be considered harmful until proven other-
wise. Bioassay tests are employed to establish possible toxicity of
such effluents ,
Results of bioassays revealed that effluents at Stations I, III and
VI were particularly toxic. When composite materials (effluents)
including dissolved and suspended foreign substances were used, the
TL values reflected high toxicity and potential ill effects of
these effluents on aquatic biota. Using an "application factor" of
10 (1/10 the TL value or a multiplier used to reduce the TL value
to a magnitude estimated to be relatively harmless to aquatic life
in the receiving stream) the volume of water in the Trinity River was
insufficient to dilute the effluents to a safe concentration for the
river biota. This was especially true during the first six months
of 1971 and the months of low rainfall in 1969 and 1970. Controlled
release of water from Benbrook Lake did help to alleviate the
situation but this was on a relatively limited schedule.
In the vicinity of a chemical plant producing cracking catalysts, the
quality of the Trinity River water has improved due primarily to
diversion of this effluent into the sanitary sewer system. Equipment
installed for clarifying and recovering some of the waste has also
improved the quality of the effluent going into the sanitary sewer as
compared with that formerly discharged into the river.
The railrc-c affluent is released from a holding pool within the
railroad yard. The wastes come from washing of railroad cars and
cleaning of heavy machinery thus accounting for high content of
grease, oil, fuel oil and detergent. The quality varied in accordance
with types of materials washed from the cars and machinery and amount
of fuel oil spillage that gets into the drainage sewers. Although
quality seemed to vary, toxicity was usually quite high.
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Station VI, the metal etching plant effluent from Substation A was
the most toxic of all effluents checked. It was consistently very
acid and extensive erosion of fin, gill and body tissues of fish was
effected in a very short period of exposure. In 100% material,
death of the test organisms often occurred within 30 seconds. Fluids
from other substations did not have the severe effect on fish and
strength or quality of the materials was more variable. Treatment
of the waste fluids with lime did buffer the material and presumably
rendered it less toxic. The company is cognizant of the toxicity
of the effluent and has taken preliminary steps to alleviate
such. Fortunately, the effluent goes into a holding pool and from
there it is collected in large abandoned gravel pits but does not
go directly into the river. Direct discharge of the effluent into
the Trinity River would have a serious effect on all living organisms .
Bioassays using various species of mature fish (minnows), eggs and
fry depicted a range of toxicity for respective effluents . Use of
eggs and fry as test organisms proved very successful. In a number
of the first tests involving fry, the fry of channel catfish appeared
very rugged and survived as well as the young bass and golden shiners
used in the same test. Eggs continued to develop and hatched in weak
Station I effluent. In later tests conducted with eggs and fry of
channel catfish using Station VI effluent, the channel catfish fry
exhibited a greater susceptibility to the toxic materials than the
golden shiner and fathead minnows being used simultaneously. Eggs
appeared to be more tolerant to all solutions than young fry, prob-
ably due to protection provided by the embryonic membranes . It may
be generally concluded from these results that eggs and fry can be
used successfully as test organisms in bioassays to produce significant
results. However, such tests are limited to a reasonably brief period
of the year when spawn and fry are available.
The pattern of dispersal of the waste effluents in the river was
determined by taking samples of the effluent and comparing with samples
of river water from stations above the outfall, at the outfall and at
various intervals downstream from the outfall. These samples were
analyzed using as many as 18 chemical and/or physical parameters. From
results of this phase of the investigation, it was concluded that the
various effluents and the two tributaries appear to have a definite
effect on water quality of the Trinity River. Station I and Station III
cause a definite stressed condition downstream from the outfall that
was not present above the outfall. The chemical data compiled on
the river appear to agree well with daily reports of the Texas Water
Development Board (December 1967) for the Clear Fork of the Trinity
River at Fort Worth between 1949 and 1952 and with data collected at
periodic times for the West Fork of the river at Fort Worth for 1952
through 1964. Ranges for a number of the parameters such as calcium,
magnesium, alkalinity, nitrates, specific conductance and pH were
within those determined by the Texas Water Development Board. The
Texas Water Development Board (February 1970) expressed the opinion
86
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that the Fort Worth area greatly affects the quality of the water in
the Trinity River. Water from the Trinity River analyzed at Grand
Prairie showed a marked increase in certain parameters over that of
water taken upstream in the area of Fort Worth. There was a
significant increase in the ranges of nitrates, phosphates, BOD
and specific conductance. Phosphate and nitrate values increased
by as much as 25 and 30 times respectively and BOD values increased
by a factor of nine. Station II effluent could possibly be diluted
sufficiently by the normal discharge of the river to prevent deleterious
effects on the stream but Stations I, III and V could not be diluted
sufficiently. Nicholson e_t _al. (1970) noted that stream quality could
be maintained if reservoir release upstream was controlled to allow
the river to naturally assimilate the waste from a sewage treatment
plant. To meet this requirement for the Trinity River, it would be
necessary to tax to a greater extent the reserve in Benbrook Lake.
It would also be necessary to accompany this by release of water
from some of the six reservoirs on the West Fork of the Trinity
River. Activity of this nature from the West Fork during the time
most needed would probably deplete the water supply reserved for
domestic and industrial uses beyond safe limits.
The stress placed on the Trinity River by introduction of domestic
and industrial wastes as reflected by results of bioassay and
chemical evaluation was supported for the greater part by the
benthos study. It was the general pattern that at the stations
discharging the more toxic effluents, organisms above the outfall
were more numerous and the number and variety at the outfall were
greatly reduced. In the area of the effluent plume, the number and
variety of organisms remained reduced.
One would be in error to consider this study as all inclusive. Neither
time nor facilities would permit an investigation of all or even a
major percentage of the industries in Fort Worth. However, those
selected for this project included a representative sampling and the
results afford a good picture of the pollution situation along the
Trinity River in the vicinity of Fort Worth and may well represent
the problems of other cities downstream. In order for this
metropolitan area to progress, it must keep abreast with the
industrial development and its impact on the environment. This can
be accomplished only through the promotion of further research of the
type completed in this investigation.
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SECTION VII
ACKNOWLEDGEMENTS
The grant director was Dr. Clifford E. Murphy, Prof-~p«or of Biology.
Dr. Leo W. Newland, Assistant Professor of Biology, Dr. John W. Forsyth,
Professor of Biology and Dr. Donald E. Keith, Assistant T'r,~.fessor of
Biology supervised specific aspects of thp project and assisted in the
authorship of this report.
This investigation was made possible by financial support from the
Water Quality Office of the United States Environmental Protection
Agency under Research Grant Number 18050 DBB. Mr. John E. Matthews,
Robert S. Kerr Water Research Center, was the project officer and his
full cooperation and many constructive suggestions are gratefully
acknowledged.
Eighteen students have been associated with this research project and
all have made important contributions. Among these, special recogni-
tion is extended to L. C. Miller and William Moore who have completed
graduate theses on specific aspects of the work and to Barbara Hudson
who has her thesis work well under way.
Many organizations, government and private, have contributed in various
ways to the success of this study. The Fort Worth Public Health Depart-
ment assisted in the general survey of the river including use of the
city helicopter for reconnaissance work. Mr. Gene Stum of the B.H.-,.' Top
Minnow Station donated minnows for bioassay studies throughout the
project, while the Fort Worth National Fish Hatchery provided catfish
eggs and fry and young bass fry when they were available.
Acknowledgement is also made of the assistance and cooperation of the
Fort Worth Water Department, Eagle Mountain State Fish Hatchery, Texas
Parks and Wildlife Department, U. S. Geological Survey and the U. S
Corps of Engineers . The American Cyanamid Company and Anadite of
Texas have both been most helpful during the course of this
investigation.
This research program was administered at Texas Christian University
and the assistance rendered by the Texas Christian University Research
Foundation is gratefully acknowledged.
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SECTION VIII
REFERENCES
1. Bachmann, R. W., "The Ecology of Four North Idaho Trout Streams
with Reference to the Influence of Forest Road Construction,"
Master's Thesis, Univ. Idaho, 97 pp (1958).
2. Bartsch, A. F. and W. S. Churchill, "Biotic Responses to Stream
Pollution During Artificial Stream Reaeration. Limnological
Aspects of Water Supply and Waste Disposal," Amer. Assn.
Advancement Science, Washington D.C., 33-48 (1949).
3. Beadles, J. K., "The Effect of Domestic and Oil Refinery Effluents
on Meristic and Morphometric Characteristics of Three Cyprinid
Fishes," Thesis, Okla. State Univ., 94 pp (1966).
4. Black, J. D., "The Management and Conservation of Biological
Resources," F. A. Davis Company, Philadelphia, 339 pp (1968).
5. Butterfield, C. T., "Experimental Studies of Natural Purification
in Polluted Waters. III. A Note on the Relation Between Food
Concentration in Liquid Media and Bacterial Growth," Public
Health Reports, 44:2,865-2,872 (1929).
6. Butterfield, C. T. and W. C. Purdy, "Some Interrelationships of
Plankton and Bacteria in Natural Purification of Polluted Water,"
Ind. & Eng. Chem., 23(2):213-218 (1931).
7. Charles, J. R., "Effects of Coal-Washer Wastes on Biological
Productivity in Martin's Fork of the Upper Cumberland River,"
Kentucky Fish. Bull. No. 27-B, Ken. Dept. of Fish and Wildlife
Res ources, Frankfort, Ky . (1966).
8. Chu, H. F., "How to Know the Immature Insects," Wm. Brown Co.,
Iowa, 234 pp (1949) .
9. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service. 76(1):1-31 (January 1971).
10. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(2):33-63 (February 1971).
11. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(3):65-95 (March 1971).
-------
12. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(4):97-127 (April 1971).
13. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(5):129-158 (May 1971).
14. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(6):159-192 (June 1971).
15. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(7);193-251 (July 1971).
16. "Climatological Data, Texas," U. S. Department of Commerce,
National Oceanic and Atmospheric Administration, Environmental
Data Service, 76(8):253-282 (August 1971).
17. "Climatological Data, Texas Annual Summary," U. S. Department
of Commerce, National Oceanic and Atmospheric Administration,
Environmental Data Service, 74(13):405-430 (1969).
18. "Climatological Data, Texas Annual Summary," U. S. Department of
Commerce, National Oceanic and Atmospheric Administration,
Environmental Data Service, 75(13):419-442 (1970).
19. Cordone, A. J. and D. W. Kelley, "The Influences of Inorganic
Sediment on the Aquatic Life of Streams," Gal. Fish and Game,
47(2):189-228 (1961).
20. Courchaine, R. J., "Significance of Nitrification in Stream
Analysis-Effects on the Oxygen Balance," Jour. Water Poll. Cont.
Fed., 40(5) Pt. 1, 835 pp (1968).
21. Cross, F. B. and Braasch, M., "Qualitative Changes in the Fish-
Fauna of the Upper Neosho River System, 1952-1967," Trans. Kansas
Acad. Sci., 71, 350 (1969).
22. Doudoroff, P., "Some Recent Developments in the Study of Toxic
Industrial Wastes," Proc. 4th Pacif . North West. Industr. Waste
Conf., State Coll. of Washington, 21-25 (1952) .
23. Eddy, S. and Hods on, A. C., "Taxonomic Keys to the Common Animals
of the North Central States," Burgess Publ. Co., Minn. 162 pp
(1961).
24. Edmondson, W. T., Editor, "Fresh Water Biology," John Wiley and
Sons, Inc., 1,248 pp (1959).
92
-------
5. Ellis, M. M. , "Detection and Measurement of Stream Pollution,"
U. S. Department of Commerce, Bureau of Fisheries, Bull. No. 22
(1937).
6. Federal Water Pollution Control Administration, Water Quality
Criteria, "Report of the National Technical Advisory Committee
to the Secretary of the Interior," (April 1, 1968).
7. Federal Water Pollution Control Administration, "FWPCA Methods
for Chemical Analysis of Water and Wastes," U. S. Department of
the Interior, FWPCA, Div. of Water Quality Research, Analytical
Quality Control Laboratory, 1014 Broadway, Cincinnati, Ohio,
280 pp (November 1969) .
'.8. Forbes, S. A., "The Biological Survey of a River System—Its
Objects, Methods and Results," 111. State Department Registration
Education, Div. Natural History Survey, 17(7):277-284 (1928).
19. Forbes, S. A. and Richardson, R. E., "Studies on the Biology of
the Upper Illinois River," 111. Natural History Survey Bull.,
9.(10) : 481-574 (1913) .
30. Forbes, S. A. and Richardson, R. E., "Some Recent Changes in
Illinois River Biology," 111. Natural History Survey Bull.,
JL3(6) : 139-156 (1919).
31. Fort Worth Water Department, "Preliminary Data and Conversation"
(1970) .
32. FWCC, "Fort Worth Chamber of Commerce, Directory of Manufacturers,"
42 pp (1969) .
33. Gammon, J. R., "The Effect of Inorganic Sediment on Stream Biota,"
Water Pollution Control Research Series, 1805DDWC 12/70, 141 pp
(1970).
34. Gaufin, A. R. and Tarzwell, C. M. , "Aquatic Invertebrates as
Indicators of Stream Pollution," U. S. Public Health Service
Public Health Report, 67(1) :57-64 (1952).
35. Graham, R. J. and Dorris, T. C. , "Long-Term Toxicity Bioassay of
Oil Refinery Effluents," Water Res. (Brit.). 2:643 (1968).
36. Hart, W. B., Doudoroff, P., and Greenbank, J., "The Evaluation of
Indus trial Wastes , Chemicals and Other Substances to Fresh-Water
Fishes," A Contribution of the Waste Control Laboratory,
Philadelphia, The Atlantic Refining Co. (1945).
37. Henderson, C., Pickering, Q. H., and Cohen, J. M., "The Toxicity
of Synthetic Detergents and Soaps to Fish," Sewage Industr. Wastes,
31:295-306 (1959).
93
-------
38. Henderson, C., Pickering, Q. H. and Tarzwell, C. M., "Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to Four
Species of Fish," Trans. Amer. Fish. Soc. 88:23-32 (1959).
39. Henderson, C., Pickering, Q. H. and Tarzwell, C. M., "The
Toxicity of Organic Phosphorus and Chlorinated Hydrocarbon
Insecticides to Fish," Trans. 1959 Seminar R. A. Taft Sanit.
Eng. Center Tech. Rep. W 60-3 (1960) .
40. Hofbauer, J., "Der Aufsteig der Fische in den Fishpassen des
mehrfach gestauten Maines," Arch. Fisch Wiss . 13;92-125 (1963).
41. Hynes, H. B. N., "The Biology of Polluted Waters," Liverpool
University Press, Liverpool, 202 pp (1960) .
42. Jones, J. R. E., "Fish and River Pollution," Butterworths,
London, 203 pp (1966).
43. Jones, J. R. E., "The Relative Toxicity of Salts of Lead, Zinc
and Copper to the Stickleback (Gasterosteus aculeatus L_.) and the
Effect of Calcium on the Toxicity of Lead and Zinc Salts,"
J. Exp. Biol. 15:394-407 (1938).
44. Kalinske, A. A., "Practical and Technical Aspects of Reusing
Effluent from Waste Treatment Plants," Proceedings, Seventh
Industrial Water and Waste Conference, Texas Water Pollution
Control Association, 161 pp (1938).
45. Katz, M. and Gaufin, A. R., "The Effects of Sewage Pollution on
the Fish Population of a Midwestern Stream," Trans. Amer. Fish .
Soc. 82:156-165 (1952).
46. Kussat, R. H., "A Comparison of Aquatic Communities in the Bow
River Above and Below Sources of Domestic and Industrial Wastes
from the City of Calgary," Can. Fish-Culturist, 40, 3(1969).
47. Lagler, K. L., "Freshwater Fishery Biology," Wm. C. Brown
Company, Dubuque, Iowa, 421 pp (1956) .
48. Mackenthun, K. M., "The Practice of Water Pollution Biology,"
U. S. Department of the Interior, Federal Water Pollution Control
Administration, 281 pp (1969) .
49. Matthews, J. E. and Neuhold, J. M., "Water Quality Effects on
Fish Movement and Distribution," Utah Acad. Proceedings 44:275-
297 (1967).
50. Metzler, D. F., Gulp, R. L., Stoltenberg, H. A., Woodard, R. L.,
Walton, G., Chang, S. L., Clarke, N. A., Flames, C. M., and
Middleton, F. M., "Emergency Use of Reclaimed Water for Potable
Supply of Chanute, Kansas," JAWWA, 50:1.021 (August 1958).
-------
51. Mount, D. I., "Test Animals for Water Quality," Amer. Fish Soc.
Newsletter, 12(54):1-12 (1968).
52. Mount, D. I. and Brungs, W. C., "A Simplified Dosing Apparatus for
Fish Toxicology Studies," Water Research, Pergamon Press, 1:21-29
(1967).
53. McDonald, D. B. and Schmickle, R. D., "Factors Affecting Winter
Fish Kills in the Coralville Reservoir, Iowa," Proc. Iowa Acad.
Sci., 72, 243 (1967) .
54. Neel, J. K. , Nicholson, H. P. and Hirsh, A., "Main Stem Reservoir
Effects on Water Quality in the Central Missouri River," U.S.
Department of Health, Education and Welfare, Public Health
Service, Reg. VI, DWSPC, 112 pp (Mimeo 1963).
55. Nicholson, G. A., Pyatt, E. and Moreau, D. H., "A Methodology for
Selecting Among Water Quality Alternatives," Water Resources Bull.,
6_, No. 1 (February 1970).
56. Patrick, R., "A Proposed Biological Measure of Stream Conditions,
Based on a Survey of the Conestoga Basin, Lancaster County,
Pennsylvania," Proc. Acad. Natural Sci. Philadelphia, 101:277-341
(1949).
57. Patrick, R. , Cairns, J., Jr. and Scheier, A., "The Relative
Sensitivity of Diatoms, Snails and Fish to Twenty Common
Constituents of Industrial Wastes," Progr . Fish-Cul t. ,_30 , 137
(1968).
58. Pennak, R. W., "Freshwater Invertebrates of the United States,"
Ronald Press Co.. N. Y., 769 pp (1953).
59. Penny, C. and Adams, C., "Fourth Report," Royal Commission on
Pollution of Rivers in Scotland," London,2:377-91 (1863).
60. Purdy, W. C., "Investigations of the Pollution and Sanitary
Conditions of the Potomac Watershed, Potomac Plankton and
Environmental Factors," U. S. Public Health Service Hyg. Lab.,
Bull. 104. 130-191 (1916) .
61. Rambow, C. A. and Sylvester, R. 0., "Methodology in Establishing
Water Quality Standards," Jour. Water Poll. Control Fed. 39(7);
1,155 (July 1967).
62. Reid G. K., "Ecology of Inland Waters and Estuaries," Reinhold
Publishing Corporation, New York, 375 pp (1961) .
95
-------
63. Richardson, R. E., "Changes in the Bottom and Shore Fauna of the
Middle Illinois River and Its Connecting Lakes Since 1913-1915 as
a Result of the Increase, Southward, of Sewage Pollution," 111.
Natural History Survey Bull., 14;33-75 (1921).
64. "Standard Methods for the Examination of Water and Wastewater,"
Twelfth Edition, (1965).
65. Stephenson, J., "The Oligochaeta," Oxford University Press, London,
978 pp (1930).
66. Sumner, F. H. and Smith, 0. R., "A Biological Study of the Effect
of Mining Debris, Dams and Hydraulic Mining on Fish Life in the
Yuba and American Rivers in California," U. S . District
Engineers Office Sacramento, Calif. Stanford Univ. California,
51 pp (1939).
67. Task Group Report, "Sources of Nitrogen and Phosphorus in Water
Supplies," AWWA Jour. 59:344-366 (1967).
68. Texas Water Development Board, Report 108, "Biochemical Oxygen
Demand, Dissolved Oxygen, Selected Nutrients and Pesticide,"
Record of Texas Surface Waters, 1968 (February 1970).
69. Texas Water Development Board, Report 67, "Reconnaissance of the
Chemical Quality of Surface Waters of the Trinity River Basin,
Texas," Dec. 1967.
70. Trautman, M. B., "The General Effects of Pollution on Ohio Life,"
Trans. Am. Fish. Soc., 63:69-73 (1933).
71. Tsai, Chu-Fa, "Effects of Chlorinated Sewage Effluents on Fishes
in Upper Patuxent River, Maryland," Chesapeake Sci., 9, 83 (1968).
72. "Water Resources Data for Texas," Part 1. Surface Water Records,
U. S. Department of the Interior, Geological Survey, 593 pp (1969) .
73. "Water Resources Data for Texas," Part 1. Surface Water Records,
U. S. Department of the Interior, Geological Survey, 613 pp (1970).
74. Weston, R. S. and Turner, C. E., "Studies on the Digestion of
a Sewage Filter Effluent by'a Small Otherwise Unpolluted Stream,"
Mass. Inst. Technology, San Res. Lab, and Sew. Exp. Sta., 10; 1-43
(1917).
75. Wheeler, A., "Fish-Life and Pollution in the Lower Thames: A
Review and Preliminary Report," Biol. Conserv. (Brit.), 2, 1
(1969).
-------
76. Wilhm, J. L., "Comparison of Some Diversity Indices Applied to
Populations of Benthic Macroinvertebrates in a Stream Receiving
Organic Wastes," Jour. WCPF 39:1,673-1,683 (1967).
77. Williams, L. G., Kopp, J. F. and Tarzwell, C. M., "Effects oi:
Hydrographic Changes on Contaminants in the Ohio River," Jour.
Amer. Water Works Assn., 58, 333 (1966).
-------
SECTION IX
GLOSSARY
Abioseston - Nonliving substances suspended in the water.
Antagonism - Reduction of the effect of one substance because of the
presence of another substance.
Benthos - Organisms which live in or on the bottom of the aquatic basin.
Bioseston - Living substances floating or swimming in water.
Biota - All life of a region.
BOD - Biochemical oxygen demand.
COD - Chemical oxygen demand.
Diluent - Diluting substance.
Euphotic - Region in water to a depth beyond which photosynthesis -
effective light fails to penetrate.
Floe - Aggregation of fine suspended particles.
JTU - Jackson Turbidity Units—evaluation of turbidity.
MGD - Million gallons per day.
Micromho - Unit of electrical conductance—mho reciprocal of ohm.
ppm - Parts per million.
Seston - Mass of living or nonliving substances in water.
Synergism - Joint action of two or more substances is greater than the
action of each of the individual substances.
Taxa - Taxonomic category of organisms.
Tubificid - Oligochaetes belonging to the taxonomic group Tubificidae.
Viscera - Internal organs .
99
-------
SECTION X
APPENDICES
Page
1. Water chemistry analyses for Station I outfall,
sampled January 12, 1970 100
2. Water chemistry analyses for Station I outfall,
sampled January 15, 1970 101
3. Water chemistry analyses for Station I outfall,
sampled January 27, 1970 102
4. Water chemistry analyses for Station I outfall,
sampled March 3, 1970 103
5. Water chemistry analyses for Station I outfall,
sampled March 5, 1970 104
6. Water chemistry analyses for Station II outfall,
sampled March 25, 1970 105
7. Water chemistry analyses for Station II outfall,
sampled March 27, 1970 106
8. Water chemistry analyses for Station II outfall,
sampled April 1, 1970 107
9. Water chemistry analyses for Station II outfall,
sampled April 7, 1970 108
10. Water chemistry analyses for Station II outfall,
sampled April 9, 1970 109
11. Water chemistry analyses for Station III outfall,
sampled February 5, 1970 110
12. Water chemistry analyses for Station III outfall,
sampled February 10, 1970 Ill
13. Water chemistry analyses for Station III outfall,
sampled February 12, 1970 «... 112
14. Water chemistry analyses for Station III outfall,
sampled February 17, 1970 113
101
-------
Page
15. Water chemistry analyses for Station III outfall,
sampled February 19, 1970 114
16. Water chemistry analyses for Station V outfall,
sampled June 9, 1970 115
17. Water chemistry analyses for Station V outfall,
sampled June 11, 1970 116
18. Water chemistry analyses for Station V outfall,
sampled June 16, 1970 117
19. Water chemistry analyses for Station V outfall,
sampled June 18, 1970 118
20. Water chemistry analyses for Station V outfall,
sampled June 20, 1970 120
21. Water chemistry analyses for Station V outfall,
sampled June 22, 1970 122
22. Water chemistry analyses for Station V outfall,
sampled June 24, 1970 124
23. Water chemistry analyses for Station IX, sampled
April 21, 1970 126
24. Water chemistry analyses for Station IX, sampled
April 23, 1970 . . 127
25. Water, chemistry analyses for Station IX, sampled
April 28, 1970 128
26. Water chemistry analyses for Station IX, sampled
May 6, 1970 129
27. Water chemistry analyses for Station IX, sampled
May 7, 1970 130
28. Water chemistry analyses for Station X, sampled
May 20, 1970 131
29. Water chemistry analyses for Station X, sampled
May 22, 1970 132
30. Water chemistry analyses for Station X, sampled
May 25, 1970 133
102
-------
31. Water chemistry analyses for Station X, sampled
May 27, 1970 •
32. Water chemistry analyses for Station X, sampled
May 29, 1970 •
33. Summary of benthos above Station I outfall 3
34. Summary of benthos at Station I outfall 137
35. Summary of benthos 70 yards below Station I outfall. . . . 138
36. Summary of benthos 150 yards below Station I outfall ... 139
37. Summary of benthos above Station II outfall 140
38. Summary of benthos at Station II outfall 141
39. Summary of benthos 70 yards below Station II outfall ... 142
40. Summary of benthos 600 yards below Station II outfall. . . 143
41. Summary of benthos above Station III outfall 1*'
42. Summary of benthos at Station III outfall 14:,
43. Summary of benthos 30 yards below Station III outfall. . . 146
44. Summary of benthos 150 yards below Station III outfall . . 147
45. Summary of benthos above Station V outfall 148
46. Summary of benthos at Station V outfall 149
47. Summary of benthos above tributary at Station IX 150
48. Summary of benthos at mouth of tributary at Station IX . . 151
49. Summary of benthos 30 yards below mouth of tributary at
Station IX -
50. Summary of benthos 150 yards below mouth of tributary
at Station IX
51. Summary of benthos above mouth of tributary at Station X
52. Summary of benthos at mouth of tributary at Station X. .
103
-------
Page
53. Summary of benthos 70 yards below mouth of tributary
at Station X 156
54. Summary of benthos 150 yards below mouth of tributary
at Station X 157
55. Rainfall distribution in inches for 1969, 1970 and 1971. . 158
104
-------
Appendix 1. Water chemistry analyses for Station I outfall,
sampled January 12, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolph thalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/D
Al
6
12.2
7.9
400
21
0.0
164
2.8
Bl
8
9.4
11.1
1,300
80
286
506
20.8
Cl
7
11.4
10.8
1,000
75
226
428
21.6
Dl
6
12.4
8.7
410
23
0.0
166
3.4
El
6
12.4
8.1
410
23
0.0
166
4.0
Chemical Oxygen 7.2 309.6 244.8 7.2 14.4
Demand (COD)
(mg/1)
Nitrates N03
mg/1 NO--N
1.3
5.8
0.05
1.1
4.9
0.66
1.3
5.8
0.54
1.3
5.8
0.05
1.5
6.6
0.0
Phosphate P04 as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate 0.01 0.26 0.18 0.01 0.01
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
PER CENT Organic
*ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
*ND - Not Determined.
105
-------
Appendix 2. Water chemistry analyses for Station I outfall,
sampled January 15, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(tnicr omhos /cm)
Turbidity (JTU)
Alkalinity
phenolph thalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N0~
mg/1 N03-N
mg/1 N03
Phosphate PO. as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A2 B2 L2
7 8 7
12.0 9.4 11.2
7.9 11.1 9.2
510 1,250 500
24 57 39
0.0 344 70
266 546 298
1.1 23.8 22.0
3.6 291.6 79.2
0.8 0.8 0.5
3.5 3.5 2.2
0.12 0.58 0.24
0.01 0.34 0.02
76.8 16.0 20.4
3.0 3.6 3.6
<0.25 <0.25 <0.25
<0.13 <0.13 <0.13
ND ND ND
2 2
7 7
12.0 11.8
8.0 8.0
515 510
23 24
0.0 0.0
256 246
1.6 1.6
0.0 0.0
1.0 0.8
4.4 3.5
0.10 0.10
0.01 0.01
72.0 76.8
7.6 6.0
<0.25 <0.25
<0.13 <0.13
ND ND
PER CENT Organic ND ND ND ND ND
106
-------
Appendix 3. Water chemistry analyses for Station I outfall,
sampled January 27, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micr omhos /cm)
Turbidity (JTU)
Alkali ni ty
phenolph thalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnes ium (mg / 1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A3
9
11.0
7.9
520
84
0.0
450
2.8
59.8
1.3
5.8
0.30
<0.01
86.5
6.4
<0.25
<0.13
ND
B3
11
8.2
11.5
1,600
57
362
638
21.8
373.1
1.3
5.8
0.69
>0.50
12.0
0.2
<0.25
<0.13
ND
C3
9
11.2
8.5
565
66
10.0
280
7.2
31.6
1.5
6.6
0.23
0.06
70.3
6.0
<0.25
<0.13
ND
D3
9
10.8
8.0
560
72
0.0
300
3.2
7.0
1.3
5.8
0.20
0.03
67.1
6.0
<0.25
<0.13
ND
E3
8
11.4
8.1
535
71
0.0
280
3.2
8.5
1.0
4.4
0.21
0.02
51.2
4.8
<0.25
<0.13
ND
PER CENT Organic 14.9 59.5 16.2 29.2 11.8
107
-------
Appendix 4. Water chemistry analyses for Station I outfall,
sampled March 3, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N03
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A4
14
10.5
8.1
330
73
0.0
258
3.8
46.2
0.7
3.1
0.27
O.01
56.0
4.0
<0.25
<0.25
<0.25
B4
18
4.4
10.3
1,130
69
266
470
15.2
449.6
1.0
4.4
1.20
1.30
20.8
0.4
<0.25
<0.25
<0.25
C4
14
9.9
8.1
340
76
0.0
268
5.4
37.8
0.7
3.1
0.18
< 0.01
56.0
4.4
<0.25
<0.25
<0.25
D4
14
10.6
8.3
325
74
0.0
256
3.4
25.2
0.7
3.1
0.11
0.12
56.0
4.0
<0.25
<0.25
<0.25
E4
14
10.5
8.1
230
76
0.0
236
3.2
25.2
1.0
4.4
0.22
0.01
56.0
4.4
<0.25
<0.25
<0.25
PER CENT Organic 28.2 46.9 25.4 ND 13.2
108
-------
Appendix 5. Water chemistry analyses for Station I outfall,
sampled March 5, 1970.
SUBSTATION A,- BS
PARAMETER
Temperature (°C) 11 16
Dissolved Oxygen 11.3 4.0
mg/1
pH Value 7.7 10.3
Specific Cone .'.ctivity 185 1,130
(micromhos /cm)
Turbidity (JTU) 30 63
Alkalini ty
phenolphthalein 0.0 262
alkalinity
(mg/1 as CaC03)
total alkalinity 152 428
(mg/1)
Biochemical Oxygen 1.2 17.0
Demand (BOD)
(mg/1)
Chemical Oxygen 21.0 348.6
Demand (COD)
(mg/1)
Nitrates NO.,
mg/1 NO--N J <0.1 0.04
mg/lNO^ <0-1 0.18
J
Phosphate PO^ as 0.12 1.2
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate 0.03 0.92
(mg/1 P)
Calcium (mg/1) 60.8 24.0
Magnesium (mg/1) 5.2 2.4
Copper (mg/1) <0-25 <0.25
Zinc (mg/1) <0-25 <0.25
Iron (mg/1) <0-5 <0 .5
5 5 5
12 12 12
11.2 11.1 11.1
8.6 7.8 7.8
400 350 350
38 27 29
or\ r\ n n f\
30 U .0 u .u
186 154 146
8.5 1.4
46.2 8.4 16.8
0.03 <0.1 <0.1
0.13 <0.1 <0.1
0.18 0.05 0.04
0.08 0.01 0.02
60.8 60.8 60.8
6.0 6.0 5.2
<0.25 <0.25 <0.25
<0.25 <0.25 <0.25
<0.5 <0.5 <0.5
PER CENT Organic
33.0 49.2 36.6 29.2 34.4
109
-------
Appendix 6. Water chemistry analyses for Station II outfall,
sampled March 25, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 NO--N
J
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
Al
16
9.0
7.0
500
35
^.0
200
3.0
19.4
0.7
3.1
0.10
0.02
83.2
4.4
<0 . 125
<0 .125
<0.5
Bl
18
3.6
6.4
800
42
0.0
294
1/1- 4.6
1/2-13.6
523.8
1.3
5.8
0.24
0.36
102.4
8.0
<0.125
0.35
<0.5
Cl
17
9.2
7.2
500
31
0.0
200
3.8
15.5
1.0
4.4
0.07
0.01
67.2
6.4
<0.125
<0 . 125
<0.5
Dl
16
8.4
7.0
500
31
0.0
196
3.4
93.1
0.7
3.1
0.07
0.03
68.8
6.0
<0 . 125
<0.125
<0.5
El
16
8.6
7.0
500
30
0.0
210
2.1
15.5
0.7
3.1
0.10
0.02
91.2
4.0
<0.125
<0 . 125
<0.5
PER CENT Organic ND ND ND ND ND
110
-------
Appendix 7. Water chemistry analyses for Station II outfall,
sampled March 27, 1970.
SUBSTATION
PAKAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
( mi c r omh os / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N0~
mg/1 NO -N
mg/1 N03
Phosphate PO^ as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A2
14
9.8
8.2
530
27
0.0
220
1.2
8.3
0.5
2.2
0.10
>0.01
91.2
4.8
<0.125
<0.125
<0.5
B2
17
3.0
7.5
740
23
0.0
250
1/1- 5.2
1/2-12.4
166.4
0.7
3.1
0.38
0.30
91.2
7.2
<0.125
<0.125
<0.5
C2 D2 E2
14 14 14
10.0 9.4 9.0
8.1 8.2 8.1
360 550 540
28 28 27
0 .0 0.0 0.0
220 214 222
2.8 0.8 1.2
8.3 8.3 4.2
0.7 0.5 0.5
3.1 2.2 2.2
0.12 0.09 0.10
0.01 >0.01 0.02
107.2 91.2 86.4
6.0 5.6 6.8
<0.125 <0.125 <0.125
<0.125 <0.125 <0.125
<0.5 <0.5 <0.5
PER CENT Organic ND ND ND ND ND
111
-------
Appendix 8. Water chemistry analyses for Station II outfall,
sampled April 1, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolph thalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N03
mg/1 N03-N
mg/1 N03
Phosphate PO^ as
Orthophosphate
(mg/1 P)
Hydro lyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
16 18 16 16 16
7.6 4.0 9.2 8.0 10.0
8.1 7.9 8.1 8.1 '8.0
520 770 520 520 520
35 21 34 32 29'
0.0 0.0 0.0 0.0 0.0
188 254 204 198 198
1.2 1/1- 9.2 1.4 1.8 1.8
1/2-22.4
20.6 182 8.2 4.1 >1.0
0.7 1.2 0.6 0.6 0.5
3.1 5.3 2.7 2.7 2.2
0.05 1.20 . 0.05 0.05 0.05
0.03 0.64 0.02 0.03 0.03
75.2 80.0 83.2 75.2 78.4
6.0 6.8 6.0 6.0 6.0
<0.125 <0.125 <0.125 <0.125 <0.125
<0.123 <0.123 <0.123 <0.123 <0.123
<0.5 <0.5 <0.5 <0.5 <0.5
PER CENT Organic ND ND WD ND ND
112
-------
Appendix 9. Water chemistry analyses for Station II outfall,
sampled April 7, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(mi cr omhos / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N00
3
mg/1 N03~N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A4
16
7.2
7.6
500
21
0.0
184
4.0
28.0
0.4
1.8
0.03
0.02
84
5.6
<0 . 125
<0 . 125
<0.5
B4
18
3.0
7.6
1,480
17
0.0
222
1/1- 4.7
1/2-13.8
1/4-22.4
40.0
1.0
4.4
0.49
0.09
116
9.6
<0.125
<0.125
<0.5
C4
17
7.2
7.9
510
27
0.0
178
3.6
16.0
0.5
2.2
0.03
0.02
72
4.8
<0.125
<0.125
<0.5
D4
17
7.2
7.8
520
27
0.0
200
3.8
24.4
0.6
2.7
0.05
0.05
76
5.6
<0 . 125
<0 . 125
<0.5
E4
17
8.4
7.9
500
31
0.0
176
4.2
12.2
0.5
2.4
0.12
0.04
72
5.6
O.125
<0 . 125
<0.5
PER CENT Organic ND ND ND ND ND
113
-------
Appendix 10. Water chemistry analyses for Station II outfall,
sampled April 9, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalini ty
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO.,
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A5
18
7.2
8.0
500
20
0.0
188
3.4
16.0
0.2
0.9
0.02
0.03
78.0
5.6
<0 . 125
<0.125
<0.5
B5
19
3.2
7.7
650
21
0.0
238
1/1- 5.2
1/2-12.4
1/4-32.0
72.0
0.7
3.1
1.32
>0.62
86.0
5.2
<0.125
<0 . 125
<0.5
C5
18
6.8
8.0
520
20
0.0
196
3.0
20.0
0.1
0.4
0.05
0.03
80.0
5.2
<0 . 125
<0.125
<0.5
D5
18
6.8
8.0
520
20
0.0
174
3.2
20.0
0.8
3.5
0.05
0.02
76.0
5.2
<0.125
<0.125
<0.5
E5
18
7.0
8.0
500
25
0.0
182
3.4
20.0
0.1
0.4
0.08
0.04
76.0
5.6
<0.125
<0.125
<0.5
PER CENT Organic ND ND ND ND ND
-------
Appendix 11. Water chemistry analyses for Station III outfall,
sampled February 5, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
2
12.8
7.8
500
28
8.0
11.9
>8,000
16
8.8
9.6
2,800
2
12.0
8.0
650
2
12.8
8.2
635
( mi cr omh os / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein 0.0 1,480 118 0.0 0.0
alkalinity
(mg/1 as CaCO )
total alkalinity 188 2,046 256 194 196
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/D
Nitrates N00
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
<0.1
<0.1
0.15
<0.01
76.8
4.8
<0.25
<0.25
>1.0
>4.4
0.30
<0.01
<0.25
<0.25
<0.25
<0.25
>1.0
>4.4
0.02
0.10
46.4
2.8
<0.25
<0.25
0.5
2.2
0.13
<0.01
78.5
5.2
<0.25
<0.25
0.5
2.2
0.13
<0.01
89.5
4.8
<0.25
<0.25
PER CENT Organic 39.0 18.8 20.7 ND 25.2
115
-------
Appendix 12. Water chemistry analyses for Station III outfall,
sampled February 10, 1970.
SUBSTATION A BZ GZ D2
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N03
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
5
12.4
7.9
520
29
0.0
196
1.2
8.0
0.8
3.5
0.10
0.05
105.6
5.2
<0.25
<0.25
<0.5
13
10.3
9.7
1,150
95
554
860
1.6
12.0
>20
>88
> 0.50
< 0.01
12.8
1.2
<0.25
<0.25
<0.5
11
11.9
9.2
2,000
55
276
680
28.0
>20
>88
> 0.50
< 0.01
28.8
2.4
<0.25
<0.25
<0.5
5
12.5
7.5
720
30
0.0
198
2.0
4.0
4.0
17.7
0.09
0.03
86.4
5.6
<0.25
<0.25
<0.5
5
12.6
7.4
730
30
0.0
200
1.3
7.8
3.2
14.2
0.09
0.03
96.0
5.2
<0.25
<0.25
<0.5
PER CENT Organic 39.4 24.1 22.0 30.2 30.2
116
-------
Appendix 13. Water chemistry analyses for Station III outfall,
sampled February 12, 1970.
SUBSTATION A- B3 C3 D3 E^
PARAMETER
Temperature (°C)
Dissolved Oxygen
rag/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N03
mg/1 N03-N
mg/1 NO,,
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydro lyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
5 26 18 6
12.7 7.8 12.8 12.6
7.8 5.3 6.8 7.0
480 >8,000 5,500 650
30 36 42 28
0.0 0.0 0.0 0.0
192 34.0 110 180
<1.0 1.7 2.0 2.1
<4.0 148 124 14.4
0.5 1.6 1.6 1.0
2.2 7.1 7.1 4.4
0.12 0.18 >0.50 0.12
0.07 <0.01 <0.01 0.03
105.6 25.6 28.8 86.4
5.2 3.2 3.2 6.0
<0.25 <0.25 <0.25 <0.25
<0.25 <0.25 <0.25 <0.25
<0.5 <0.5 <0.5 <0.5
5
11.8
6.5
900
25
0/-\
.0
124
1.9
7.2
2.0
8.9
0.10
0.05
86.4
80
.8
<0.25
<0.25
<0.5
PER CENT Organic
39.4 19.4 23.7 31.7 26.0
117
-------
Appendix 14. Water chemistry analyses for Station III outfall,
sampled February 17, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
3
12.2
7.8
400
48
0.0
156
3.7
27
7.5
6.3
>8,000
81
0.0
228
1.0
8
11.7
6.6
1,350
91
0.0
150
3.8
3
12.1
7.1
650
75
0.0
144
3.7
3
12.0
7.2
700
73
0.0
140
2.8
Chemical Oxygen 18.0 25.2 21.6 26.4 26.4
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 NO -N 1.5 > 40.0 25.2 7.3 7.5
mg/1 NO;: 6.6 >177 111.6 32.3 33.2
Phosphate PO, as 0.25 2.0 0.40 0.27 0.25
Orthophosphate
(mg/1 P)
Hydrolyzabla Phosphate 0.10 0.12 <0.01 0.06 0.02
(mg/1 P)
Calcium ing A) 67.2 19.2 70.4 64.0 76.8
Magnesium Cwg/1) 4.0 2.8 4.4 4.4 4.0
Copper (mg/J; <0.25 <0.25 <0.25 <0.25 <0.25
Zinc (mg/1) <0.25 1.0 <0.25 <0.25 <0.25
Iron (mg/1) <0.5 <0.5 <0.5 <0.5 <0.5
PER CENT Organic 28.8 17.9 21.4 20.4 26.2
118
-------
Appendix 15. Water chemistry analyses for Station III outfall,
sampled February 19, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N03
mg/1 NO3"
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
f.rmnpr ("iTlff/l)
As tf5 ^5
4 23 21
12.2 7.8 8.0
7.7 6.4 6.2
490 7,500 6,000
31 92 76
0.0 0.0 0.0
180 86 96
3.5 0.1 0.1
22.0 26.4 26.4
0.5 30.0 22.4
2.2 133.0 99.2
0.25 1.6 0.88
0.02 <0.01 <0.01
64.0 20.8 32.0
5.2 4.0 4.0
<0.25 <0.25 <0.25
"5 5
5 4
11.9 11.6
7.3 7.5
790 750
47 47
0.0 0.0
170 186
2.4 2.8
26.4 13.2
2.2 2.1
9.7 9.3
0.22 0.22
0.18 0.03
70.4 67.2
4.8 5.6
<0.25 <0.25
Iron (mg/1) <0 -5 <;
PER CENT Organic 48.3 19.8 18.6 26.2 24.0
-------
Appendix 16. Water chemistry analyses for Station V outfall,
sampled June 9, 1970.
SUBSTATION
E*
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 NO -N
mg/i NO;:
25
3.6
7.1
660
23
0.0
214
7.1
38.2
0.6
2.8
25
6.4
7.7
1,050
14
0.0
298
1/5-33.5
1/10-69 .0
72.1
6.0
27.6
25
4.2
7.3
720
24
0.0
220
1/2-13.6
1/4-28.0
46.6
1.4
6.2
25
5.0
7.4
800
18
0.0
236
6.3
46.6
2.8
12.4
4.8
7.4
810
17
0.0
236
6.4
42.4
2.8
12.4
mg/1 NO -N
mg/1 N0_
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
0.6
2.8
0.88
0.05
64.0
6.6
<0.125
< 0.1 25
<0.125
6.0
27.6
3.05
0.10
48.0
6.6
<0.125
<0.125
<0.125
1.4
6.2
1.34
<0.01
60.0
6.8
<0.125
<0.125
<0.125
2.8
12.4
1.68
<0.01
56.0
7.0
<0.125
<0.125
<0.125
2.8
12.4
1.68
<0.01
60.0
7.4
<0.125
<0.125
<0.125
PER CENT Organic
ND
ND
ND
ND
120
-------
Appendix 17. Water chemistry analyses for Station V outfall,
sampled June 11, 1970.
SUBSTATION E*o B? C2
PARAMETER
Temperature (°C)
Dissolved Oxygen
rag/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/D
Nitrates NO,
mg/1 N03-N
mg/1 NO
J
Phosphate PO^ as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
25 25 "5
3.3 7.2 .('• 4.4
7.1 7.3 7.3 7.3
740 1,020 770 820
33 18 32 29
0.0 0.0 0.0 0.0
182 256 186 204
6.2 1/5-4.5 1/2-7.8 3.4
1/10-14.0 1/4-13.6
46.2 79.8 46.2 54.6
1.1 6.4 1.5 2.6
4.9 29.4 6.6 11.5
1.08 4.35 1.48 2.00
0.32 O.01 0.01 <0.01
60 52 60 58.0
6.8 7.4 7.0 7.0
<0.125 <0.125 <0.125 <0.125
<0.125 O.125 <0.125 <0 .125
<0.125 O.125 <0.125 <0.125
4.0
7.4
830
26
0.0
196
4.0
50.4
2.6
11.5
2.15
<0.01
56.0
7.0
<0.125
<0.125
<0.125
PER CENT Organic
ND ND ND ND ND
121
-------
Appendix 18. Water chemistry analyses for Station V outfall,
sampled June 16, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO.,)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO.
mg/1 N03-N
mg/1 NO
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A*3
27
6.6
7.6
850
16
0.0
182
6.0
36.7
1.9
8.4
0.10
0.06
62.0
7.6
< 0.125
< 0.125
< 0.125
B3
26
5.4
7.5
975
19
0.0
246
1/10-3.0
1/50-
81.6
8.0
35.4
9.20
<0.01
54.0
8.2
< 0.125
<0.125
< 0.125
C3
27
4.0
7.5
925
19
0.0
216
1/2-12.0
1/4- 7.2
69.4
3.4
15.1
4.45
<0.01
58.0
8.0
< 0 . 125
< 0.125
<0.125
D3
27
3.8
7.5
925
17
0.0
222
1/2-11.2
69.4
3.9
17.3
4.60
<0.15
60.0
8.0
< 0.125
< 0.125
< 0 . 125
E3
27
2.6
7.5
925
13
0.0
218
1/2-11.8
65.3
3.5
15.5
4.65
0.01
58.0
7.8
< 0.125
< 0.125
< 0.125
PER GENT Organic ND ND ND ND ND
122
-------
Appendix 19. Water chemistry analyses for Station V outfall,
sampled June 18, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
Nitrates NO-
mg/1 NO -N
mg/i NO;;
J
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A* B* C* D*
2 1 1 1
29 28 29 30
10.2 7.4 2.8
7.8 7.6 7.8 7.8
775 1,100 850 850
16 20 18 18
0.0 0.0 0.0 0.0
172 306 210 216
5.7 1/10-34.0 1/2-12.2 1/2-12.5
1/50- 1/4-14.8
39.2 144 65.4 74.1
1.0 0.4 1.0 0.6
4.4 1.8 4.4 2.8
0.05 5.4 2.0 2.7
0.03 0.40 0.30 0.20
60 50.0 56.0 56.0
8.4 8.0 8.2 8.4
<0.125 <0.125 <0.125 <0.125
<0.125 <0.125 <0.125 <0.125
<0.125 <0.125 <0.125 <0.125
E*3
30
3.4
7.8
850
13
0.0
202
1/2-12.9
56.7
Oc
.5
2.2
2.3
0.40
58.0
8.2
<0.125
<0.125
<0.125
PER CENT Organic
ND ND ND ND ND
123
-------
Appendix 19. Continued
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 NO -N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1 )
Zinc (mg/1)
Iron (mg/1)
E*3
30
3.4
7.8
850
13
0.0
202
1/2-12.9
56.7
0.5
2.2
2.3
0.40
58.0
8.2
O.125
<0.125
<0.125
B4
29
5.6
7.6
1,100
16
0.0
280
1/10-10
1/50-
91.6
4.8
21.3
4.6
0.20
50.0
8.2
<0.125
<0 .125
<0.125
C4
30
4.4
7.8
850
13
0.0
220
1/2-12.5
1/4- 8.8
65.4
1.6
7.2
3.4
0.20
56.0
8.4
<0.125
<0.125
<0.125
D4
30
4.8
7.8
875
13
0.0
238
1/2-12.2
69.8
1.9
8.6
3.5
0.10
54.0
8.4
<0.125
<0.125
<0 . 125
E4
30
,5.0
7.8
850
13
0.0
212
1/2-10.8
61.0
1.8
8.0
3.8
0.10
56.0
8.4
<0.125
<0 . 125
<0.125
PER CENT Organic ND ND ND ND ND
-------
Appendix 20. Water chemistry analyses for Station V outfall,
sampled June 20, 1970.
SUBSTATION
PARAMETER
Temperature ( °C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity 1
( mi c r omh os / cm)
Turbidity (JTU)
Alkalinity
phen olph th ale in
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO,,
mg/1 N03-N
mg/1 NO
J
Phosphate PO^ as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A* B*
A 3 2
29
6.6 3.0
7.8 7.5
,250 1,000
28 26
0.0 0.0
172 286
3.7 1/10-15.0
1/50- 5.0
33.9 140.0
0.6 0.1
2.8 0.1
0.02 8.0
0.03 <0.01
68.0 48.0
9.2 8.0
<0.125 <0.125
<0.125 <0.125
<0.125 <0.125
C* D*
2 2
29 29
4.2 0.8
7.6 7.6
1,175 1,200
30 22
0.0 0.0
208 202
1/2- 6.9 1/2-12.4
1/4-11.6
67.8 55.1
0.5 0.4
2.2 1.7
2.9 2.6
<0.01 0.30
60.0 62.0
8.8 8.8
<0.125 <0.125
<0.125 <0.125
<0.125 <0.125
E*2
29
0.6
7.6
1,200
21
0.0
202
1/2-12.4
50.9
0.4
1.7
2.5
0.30
64.0
9.2
<0.125
<0.125
<0.125
PER CENT Organic
ND ND ND ND ND
125
-------
Appendix 20. Continued
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO-)
total alkalinity
(mg/1 as CaCOj
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 N03-N
mg/1 N0_
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydro lyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
E*4
29
0.6
7.6
1,200
21
0.0
202
1/2-12.4
50.9
0.4
1.7
2.5
0.30
64.0
9.2
O.125
O.125
0.125
B5
27
5.6
7.6
990
16
0.0
242
1/10-2.0
1/50-
80.6
6.0
27.6
7.6
0.20
48.0
8.4
<0.125
<0.125
<0 . 125
C5
28
2.6
7.6
1,125
20
0.0
218
1/2-10.8
1/4- 6.4
55.4
2.1
9.3
3.9
<0.01
58.0
8.8
<0.125
<0.125
<0 .125
D5
28
2.6
7.5
1,100
21
0.0
216
1/2-10.4
55.4
2.6
11.6
4.4
0.60
58.0
8.8
<0.125
<0.125
<0 . 125
E5
28
2.0
7.5
1,100
17
0.0
220
1/2-11.4
63.6
2.0
8.9
4.8
0.80
58.0
8.6
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
126
-------
Appendix 21. Water chemistry analyses for Station V outfall,
sampled June 22, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/D
Nitrates N0~
mg/1 N03-N
mg/1 N03
Phosphate PO, as
0 r th oph os ph a te
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A*
A 4
28
7.0
7.8
1,200
23
0.0
164
1/2-2.0
29.7
1.3
5.8
0.07
0.02
64,0
9.2
<0.125
<0.125
<0.125
B*3
27
4.6
7.1
950
20
0.0
220
1/10- 8.0
1/50-10.0
136.0
7.0
31.0
9.6
<0.01
54.0
8.8
<0.125
<0 . 125
<0.125
C*3
28
5.4
7.5
1,100
23
0.0
180
1/2-9 .4
1/4-3.6
63.6
2.6
11.5
3.8
0.10
62.0
9.2
<0.125
<0.125
<0.125
°*3
28
3.2
7.6
1,100
17
0.0
174
46.6
2.5
11.1
2.7
0.30
62.0
9.0
<0.125
<0.125
<0.125
E*5
28
3.8
7.1
1,100
14
0.0
176
1/4-3.2
42.4
2.5
11.1
2.7
0.10
64.0
9.4
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
127
-------
Appendix 21. Continued
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
( mi cromh os / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCOj
total alkalinity
(mg/1 as CaCO-)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 NO -N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
E*5
28
3.8
7.1
1,100
14
0.0
176
1/4-3.2
42.4
2.5
11.1
2.7
0.10
64.0
9.4
<0.125
<0.125
<0.125
B6
26
7.0
7.1
1,000
13
0.0
202
1/10-
1/50-
72.1
11.0
48.7
11.2
<0.01
56.0
9.8
<0 . 125
<0.125
<0.125
C6
27
5.4
7.3
1,050
14
0.0
198
1/2-2.4
1/4-1.6
59.4
6.6
29.2
6.8
<0.01
58.0
9.4
<0.125
<0.125
<0.125
D6
27
4.6
7.4
1,050
15
0.0
188
1/4-0.4
63.6
5.8
25.7
6.2
<0.01
58.0
9.4
<0.125
<0.125
<0.125
E6
27
3.4
7.3
1,050
12
0.0
188
1/4-1.2
59.4
5.7
25.3
6.4
<0.01
60.0
9.8
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
128
-------
Appendix 22. Water chemistry analyses for Station V outfall,
sampled June 24, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
TH ss nlved Oxv sen
A*5
28
4.8
B*4
28
5.6
C*4
28
4.8
D*4
28
3.2
E*6
28
2.8
mg/1
PH Value 7.4 7.4 7.4 7.4 7.4
Specific Conductivity 1,300 1,100 1,250 1,200 1,200
(mi cr omhos / cm)
Turbidity (JTU) 28 43 37 29 28
Alkalinity n -.
phenolphthalein 0.0 0.0 0.0 0.0 0.0
alkalinity
(mg/1 as CaC03)
total alkalinity 170 278 196 208 206
(mg/1 as CaC03)
Biochemical Oxygen 1/2-0.4 1/10- 1/2- 1/4-11.2 1/4-3.6
Demand (BOD) 1/50- 1/4-5.2
(mg/1)
Chemical Oxygen 25.4 275.0 72.1 76.3 72.1
Demand (COD)
(mg/D
Nitrates N03 Q 2
13.3 8.9 11.5 4.9 0.9
Phosphate P04 as 0.10 10.4 3.0 4.0 3.8
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate 0.03 0.40 <0.01 <0.01 0.20
(mg/1 P)
Calcium (mg/1) 70.0 48.0 62.0 62.0 62.0
Magnesium (mg/1) ^ £0^ ^.^ ^.^ ^-^
^.°(' ^ -,oc
-------
Appendix 22. Continued
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 N03-N
mg/1 NO
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
E*6
28
2.8
7.4
1,200
28
0.0
206
1/4-3.6
72.1
0.2
0.9
3.8
0.20
62.0
9.2
<0.125
<0 .125
<0.125
B7
27
6.2
7.4
1,000
23
0.0
244
1/10-
1/50-
102.0
5.6
24.8
8.4
<0.01
48.0
6.8
<0.125
<0.125
<0.125
C7
28
4.2
7.5
1,100
26
0.0
228
1/4-2.8
89.0
3.8
16.8
6.6
<0.01
54.0
8.4
<0 . 125
<0.125
<0 . 125
D7
27
4.2
7.5
1,100
20
0.0
222
1/4-7.2
84.8
3.0
13.3
5.8
<0.01
58.0
8.8
<0.125
<0 . 125
<0.125
E7
27
4.6
7.5
1,100
18
0 .0
224
1/4-13.6
84.8
2.7
12.0
6.2
<0.01
54.0
8.2
<0 . 125
<0.125
<0 . 125
PER CENT Organic ND ND ND ND W
130
-------
Appendix 23. Water chemistry analyses for Station IX, sampled
April 21, 1970.
SUBSTATION
PARAMETER
Temperature ( °C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(mi cromhos / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/D
Nitrates NO
mg/1 N03~N
mg/1 N03
Phosphate PO^ as
0 r th oph os pha te
(mg/1 P)
Hydro lyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
Al Bl 1 1 1
19 19 19 19 19
9.0 9.0 9.4 9.4 9.4
7.9 7.8 7.9 7.8 7.6
400 690 400 405 410
45 19 48 48 47
0.0 0.0 0.0 0.0 0.0
118 176 138 136 138
1.8 2.5 1.7 1-6 1-9
16.6 19.9 16.6 16.6 16.6
0.2 0.5 0.4 0.7 0.1
0.9 2.2 1.8 3.1 0.4
0.08 0.20 0.09 0.10 0.10
0.01 0.02 <0.01 <0.01 0.01
42 66 42 46 50
6 4 4.0 6.4 6.4 6.0
<0 125 <0.125 <0.125 <0 .125 <0.125
<0.125 <0.125 <0.125 <0.125 <0.125
<0.25 <0.25 <0.25 <0.25 <0.25
PER CENT Organic ND
ND ND ND ND
131
-------
Appendix 24. Water chemistry analyses for Station IX, sampled
April 23, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO,,
mg/1 NO -N J
mg/1 NO,,
Phosphate PO as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
PER CENT Organic
A2
21
8.6
7.9
450
40
0.0
138
1.5
10.0
0.6
2.8
0.05
<0.01
40.0
6.4
<0.125
<0.125
<0.25
ND
B2
22
9.0
8.1
800
16
0.0
202
2.6
16.6
1.0
4.4
0.35
0.02
78.0
4.8
<0.125
-------
Appendix 25. Water chemistry analyses for Station IX, sampled
April 28, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
pheno Iph th a le i n
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 NO--N
mg/1 N03
Phosphate PO as
Orthophosphate
(mg/1 P)
Hvdrolyzable Phosphate
' (mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A3
22
8.8
7.9
390
63
0.0
138
1.6
<0.1
<0.4
0.05
0.01
52
5.6
<0.125
<0.125
<0.25
B3
22
8.2
7.7
540
43
0.0
126
1.8
0.5
2.2
0.09
0.01
60
3.6
<0.125
<0.125
<0.25
C3
22
9.4
7.8
410
55
0 .0
138
1.0
<0.1
<0.4
0.05
0.01
50
5.2
<0.125
-0.125
<0.25
D3
22
8.4
7 .7
410
63
0.0
134
1.3
22.4
<0.1
<0.4
0.06
<0.01
50
5.6
-.0.125
<0.125
-0.25
E3
22
8.8
7.?
400
61
0.0
142
1.0
2.2.4
<0.1
<0.4
0.05
0.01
52
5 .6
--0.125
<0.125
-0.25
PER CENT Organic ND ND ND ND ND
133
-------
Appendix 26. Water chemistry analyses for Station IX, sampled
May 6, 1970.
SUBSTATION
PARAMETER
Temperature ( °C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as Ca(X>3)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Or thophospha te
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
20
9.2
7.4
400
63
0.0
158
1.4
22.4
0.10
0.44
0.08
0.01
54.0
5.2
<0 .125
O.125
<0.25
20
8.2
7.6
725
39
0.0
224
2.8
19.2
1.6
7.1
0.30
0.04
82.0
4.0
<0.125
<0.125
<0.25
20
9.0
7.5
405
61
0.0
156
1.2
22.4
0.4
1.8
0.10
<0.01
52.0
5.6
<0.125
<0.125
<0.25
20
8.6
7.6
410
63
0.0
172
1.5
22.4
0.2
0.89
0.09
<0.01
50
5.6
<0.125
<0.125
<0.25
20
8.6
7.6
405
59
0.0
166
1.5
22.4
0.1
0.44
0.10
<0.01
52.0
5.2
<0.125
<0.125
<0.25
PER CENT Organic ND ND ND ND ND
13*
-------
Appendix 27. Water chemistry analyses for Station IX, sampled
May 7, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos /cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO-
mg/1 NO,-N
o • J
mg/1 NO^
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
20
9.2
7.7
.400
61
0.0
156
1.7
13.0
0.1
0.44
0.09
<0.01
48.0
4.8
<0.125
0.125
<0.25
20
9.0
7.5
825
41
0.0
228
4.0
17.3
1.8
8.0
0.42
O.01
82.0
4.0
O.125
O.125
<0.25
20
9.2
7.7
415
61
0.0
170
1.6
13.0
0.1
0.44
0.1
<0.01
50.0
5.2
<0.125
<0.125
0.25
20
9.4
7.7
400
63
0.0
174
1.6
17.3
0.2
0,90
0.08
0.01
46.0
5.6
<0.125
<0.125
<0.25
20
9.4
7.7
415
62
0.0
154
1.6
13.0
0.1
0.44
0.09
O.01
50.0
5.6
<0.125
<0.125
<0.25
PER CENT Organic ND ND ND ND ND
135
-------
Appendix 28. Water chemistry analyses for Station X, sampled
May 20, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
( mi c romh os / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCOj
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates N0~
mg/1 N03-N
mg/1 N03
Phosphate PO^ as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
24
8.8
7.7
480
36
0.0
146
2.3
20
1.0
4.4
0.04
<0.01
58.0
7.4
<0.125
<0.125
<0.125
25
11.0
7.9
900
10
0.0
270
7.1
44
0.2
0.88
1.32
<0.01
102.0
12.8
<0.125
<0.125
<0.125
24
8.8
7.8
495
36
0.0
154
2.7
20
0.5
2.2
0.04
0.02
58.0
6.8
<0.125
<0.125
<0.125
24
9.0
7.8
495
36
0.0
144
2.6
20
1.0
4.4
0.04
<0.01
58.0
6.8
<0.125
<0.125
<0.125
24
9.0
7.8
495
37
0 .0
148
2.8
16
1.0
4.4
0.03
0.02
58.0
6.8
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
136
-------
Appendix 29. Water chemistry analyses for Station X, sampled
May 22, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
A2
24
6.2
7.3
690
B2
23
9.0
7.6
850
C2
24
6.6
7.4
700
D2
24
6.6
7.2
700
E2
25
6
7
700
.8
.3
(micromhos/cm)
Turbidity (JTU) 24 4 25 26 25
Alkalinity
phenolphthalein 0.0 0.0 0.0 0.0 0.0
alkalini ty
(mg/1 as CaC03)
total alkalinity 146 280 152 148 148
(mg/1 as CaCO )
Biochemical Oxygen 2.0 2.9 1.9 2.0 2.2
Demand (BOD)
(mg/1)
Chemical Oxygen 20 20 16 16 12
Demand (COD)
(mg/1)
Nitrates NO.,
mg/1 N03-N
mg/1 NO,.
Phosphate PO as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
1.1
4.9
0.04
0.03
58.0
7.4
<0 . 125
<0.125
<0.125
0.5
2.2
1.02
0.08
100.0
12.0
<0.125
<0.125
<0.125
1.2
5.3
0.05
0.04
62.0
8.0
<0.125
<0.125
<0.125
1.1
4.9
0.07
0.02
62.0
8.0
<0.125
<0.125
<0.125
1.2
5.3
0.05
0.04
60.0
8.0
<0.125
<0.125
<0 . 125
PER CENT Organic ND ND ND ND ND
137
-------
Appendix 30. Water chemistry analyses for Station X, sampled
May 25, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
( mi c romh os / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCOj
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A3
25
6.4
7.1
790
17
0.0
166
2.6
23.8
0.6
2.8
0.04
0.01
60.0
6.8
<0.125
<0.125
<0.125
B3
24
9.0
7.8
740
10
0.0
226
1/2- 8.6
1/4-16.4
59.4
0.5
2.2
1.20
0.04
62.0
9.6
<0.125
<0.125
<0.125
C3
25
7.0
7.3
770
18
0.0
182
3.2
27.7
0.6
2.8
0.29
<0.01
62.0
8.0
<0.125
<0 . 125
<0.125
D3
25
7.0
7.2
780
18
0.0
172
3.4
27.7
0.5
2.2
0.16
0.04
62.0
8.0
<0 . 125
<0.125
<0.125
E3
25
7.0
7.4
780
18
0.0
168
3.6
27.7
0.6
2.8
0.15
0.03
66.0
7.4
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
138
-------
Appendix 31. Water chemistry analyses for Station X, sampled
May 27, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(micromhos/cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaCO )
total alkalinity
(mg/1 as CaCO )
Biochemical Oxygen
Demand (BOD)
(mg/1)
Chemical Oxygen
Demand (COD)
(mg/1)
Nitrates NO
mg/1 NO -N
mg/1 NO,,
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
A4
24
5.0
7.4
690
28
0.0
180
5.7
24.5
1.0
4.4
0.05
0.05
62
7.2
<0.125
<0.125
<0.125
B4
23
6.8
7.4
470
45
0.0
160
1/1- 6.7
1/2-13.6
40.8
1.1
4.9
0.40
0.04
54.0
5.8
<0.125
<0.125
<0.125
C4
24
5.2
7.3
690
32
0.0
180
6.0
24.5
1.0
4.4
0.07
0.03
62.0
6.8
<0.125
<0.125
<0.125
D4
24
5.6
7.4
690
31
0.0
180
6.1
24.5
1.0
4.4
0.05
0.07
66.0
6.8
<0.125
<0.125
<0.125
E4
25
5.8
7.4
690
31
0.0
178
6.4
28.6
1.0
4.4
0.05
0.05
66.0
6.8
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
-------
Appendix 32. Water chemistry analyses for Station X, sampled
May 29, 1970.
SUBSTATION
PARAMETER
Temperature (°C)
Dissolved Oxygen
mg/1
pH Value
Specific Conductivity
(•mi cromhos / cm)
Turbidity (JTU)
Alkalinity
phenolphthalein
alkalinity
(mg/1 as CaC03)
total alkalinity
(mg/1 as CaC03)
Biochemical Oxygen
As
24
6.6
7.3
650
33
0.0
172
4.3
B5
24
8.2
7.6
450
15
0.0
156
1/1-2.1
C5
24
7.0
7.4
610
34
0.0
162
4.6
D5
25
7.0
7.4
625
34
0.0
168
4.6
E5
25
7.2
7.4
625
34
0.0
164
4.6
Demand (BOD) 1/2-7.2
(mg/1)
Chemical Oxygen 25.9 21.6 25.9 25.9 25.9
Demand (COD)
(mg/D
Nitrates NO
mg/1 N03-N
mg/1 N03
Phosphate PO, as
Orthophosphate
(mg/1 P)
Hydrolyzable Phosphate
(mg/1 P)
Calcium (mg/1)
Magnesium (mg/1)
Copper (mg/1)
Zinc (mg/1)
Iron (mg/1)
1.2
5.3
0.09
0.01
58.0
5.8
<0.125
<0.125
<0.125
0.7
3.1
0.25
0.01
54.0
5.2
<0.125
<0.125
<0.125
1.2
5.3
0.10
0.04
60.0
5.8
<0 . 125
<0.125
<0.125
1.2
5.3^
0.10
0.02
58.0
5.6
<0 .125
<0.125
<0.125
1.4
6.2
0.08
0.04
60.0
5.8
<0.125
<0.125
<0.125
PER CENT Organic ND ND ND ND ND
*
-------
Appendix 33. Summary of benthos above Station I outfall.
Total
J.Ct^VCl
Samples
Hydroida
Tricladida
Nematoda
Oligochaeta
Hirudinea
Cladocera
Ostracoda
Calanoida
Cyclopoida
Harpacticoida
Amphipoda
Coleoptera
Diptera
Gastropoda
*0ligochaete
cocoons
Total individuals
Total taxa
12345 6 789 10
13 3 9 675 343 17 1
1 4
2 12 7 14 1 168 34 70 7 6
60 42 68 45 61 232 115 71 88 60
1 2
121 25 22 8 6 38
13 7592
73 2
3 4 71 32 3 111 79 55 32 149
12121
1
3
1 4 32 104 47 42 6 7
1 10 40 3 2
4 3
65 60 168 108 79 1,339 687 276 144 270
3 ! 5 9 8 6 13 99 89
1,061
5
321
842
3
103
27
12
539
7
1
3
216
56
3,196
14
*Totals do not include Oligochaete cocoons
-------
Appendix 34. Summary of benthos at Station I outfall.
Taxa Number of Organisms Total
Samples 12345 6 7 8 9 10
Hydroida 57 8 5 3 11 4 7 16 111
Nematoda 1 124
Oligochaeta 8 10 36 15 11 4 13 3 10 22 132
Cladocera 26 55 12 84
Ostracoda 64 20 1 85
Cyclopoida 64 100 6 1 11 5 17 4 7 23 238
Diptera 97644 1 4 2 12 23 72
Gastropoda 121 149
Total individuals 172 192 107 30 31 13 46 13 40 91 735
Total taxa 65564 45477 8
-------
Appendix 35. Summary of benthos 70 yards below Station I outfall.
Taxa
Samples
Foraminifera
Hydroida
Nematoda
Oligochaeta
Hirudinea
Cladocera
Ostracoda
Cyclopoida
Coleoptera
Diptera
Pelecypoda
*01igochaete
cocoons
Total individuals
Total taxa
Number of
12345
211
74
2151
52 33 136 119 172
1
1
1
1 6
1
21 19 39 13 5
1
1 2
79 53 181 134 261
63448
Organisms
6 7 8 9 10
1
25 2 1
4 4 41 15
88 82 59 213 146
512
222
154
231
1
92 94 98 265 163
45764
Total
5
102
73
1,100
1
9
7
17
1
103
2
1,420
11
*Totals do not include Oligochaete cocoons
-------
Appendix 36. Summary of benthos 150 yards below Station I outfall.
Tax a
Samples
Hydroida
Nematoda
Oligochaeta
Cladocera
Ostracoda
Cyclopoida
Diptera
Hydra car ina
Gastropoda
Total individuals
Total taxa
Number of
12345
5
2
13 7 3 39
2 3
11 12
3
16 8 0 4 54
320 26
Organisms
6
24
4
13
2
3
4
7
1
58
8
7
9
17
10
2
1
1
40
6
8
21
40
8
2
6
77
5
9
11
10
2
27
6
4
60
6
10
20
10
49
7
1
1
88
6
Total
59
94
113
9
3
89
30
1
7
405
9
-------
Appendix 37. Summary of benthos above Station II outfall.
Taxa Number of Organisms Total
Samples 123
Foraminifera
Nematoda
Oligochaeta 39 63 1
Cladocera
Ostracoda
Calanoida
Cyclopoida
Diptera
*01igochaete
cocoons
Total individuals 39 63
Total taxa 11
*Totals do not include Oligochaete cocoons
1
.3
3
L7
3
4 5
1
1
17 119
1
6
3
2 2
1
19 133
2 7
6 7
1
1
86 139
2
1
1 1
89 143
3 5
8 9 10
28 56 23
2
3 6
2
2
1 1
37 63 24
532
2
3
583
3
17
2
6
11
627
8
-------
Appendix 38. Summary of benthos at Station II outfall.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Oligochaeta 18 63 60 114 66 108 185 121 122 14 871
Cladocera 1 1
Cyclopoida 1212 6
Coleoptera 1 1
Diptera 11 12 5
Gastropoda 2 2
Total individuals 18 64 61 116 67 110 186 123 127 14 886
Total taxa 12222 22341 6
-------
Appendix 39. Summary of benthos 70 yards below Station II outfall.
Taxa Number of Organisms Total
Samples
Foraminifera
Oligochaeta 18 119 77 110 197 124 3 706
Cladocera
Ostracoda
Cyclopoida
Diptera 155 6 20
Total individuals 21 34 5 22 119 79 118 202 124 9 733
Total taxa 21251 34212 6
1
20
1
21
2
23 45
1
34 4 18 119
1
1
1 1
34 5 22 119
1251
6 789
1
77 110 197 124
1
2
155
79 118 202 124
3421
10
3
6
9
2
-------
Appendix 40. Summary of benthos 600 yards below Station II outfall.
Taxa Number of Organisms Total
Samples
Foraminifera
Nematoda
Oligochaeta
Cladocera
Ostracoda
Cyclopoida
Diptera
Gastropoda
Total individuals
Total taxa
L
1
56
5
1
4
•7
5
2 3
48 218
1
1
18
2
48 240
1 5
45 6 7 8 9 10
1 1
260 168 126 45 32 69 68
1 12
11 22
263 169 128 47 36 69 68
42 32311
2
1
1,170
I
1
27
9
4
1,215
8
-------
Appendix 41. Summary of benthos above Station III outfall.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Nematoda 2 43 12132 18
Oligochaeta 86 44 21 27 46 23 21 13 209
Calanoida 1
Cyclopoida 1 33 114 13
i i 2
Ephemeroptera J- L
Coleoptera 1
Trichoptera 1
Diptera 10 19 22 47 26 6778 22 174
Hydracarina 11 1
Gastropoda 1 2 3
Total individuals 18 29 22 102 56 34 58 32 33 41 425
Total taxa 25187 35444 10
-------
Appendix 42. Summary of benthos at Station III outfall.
Tax a Number of Organisms Total
Samples
Rhabdocoela
Ne ma to da
Bryozoa
Oligochaeta
Calanoida
Cyclopoida
Harpacticoida
Ephemeroptera
Coleoptera
Trichoptera
Diptera
Hydracarina
Gastropoda
Total individuals
Total taxa
12345
19
0 0 0 0 19
00001
6
7
1
53
1
1
1
18
82
7
7 8
3 10
23 8
1
1
1
16 39
2
2
43 63
4 7
9 10
2
8 4
1
8 14
3
3
5
1
38 48
1
58 78
5 8
2
32
2
106
5
4
1
5
2
1
178
2
3
343
13
150
-------
Appendix 43. Summary of benthos 30 yards below Station III outfall.
Taxa
Samples
Nematoda
Bryozoa
Oligochaeta
Hirudinea
Cyclopoida
Coleoptera
Trichoptera
Diptera
Hydracarina
*Gastropod egg
cases
Total individuals
Total taxa
*Not counted in totals
Number of Organisms
Total
2345
2
1
2
20003
10002
6 7 8 9 10
11 65
1 1
9 4 10 16
1
5 4
1 1
1
8 20
3
2
15 39 6 17 21
47332
13
2
41
1
10
2
1
30
3
103
9
151
-------
Appendix 44. Summary of benthos 150 yards below Station III outfall.
Taxa
Samples
Rhabdocoela
Nematoda
Oligochaeta
Cyclopoida
Ephemeroptera
Coleoptera
Diptera
Hydracarina
Gastropoda
Total individuals
Total taxa
Number of
12345
3 2
1 11
52 37
75889
1
12 8 9 14 29
23234
Organisms
6 7
9 1
14 5
18
37 26
78 32
4 3
8
5
18
10
15
1
49
5
9
8
4
28
1
1
33
75
6
10
1
7
12
16
1
40
1
1
79
8
Total
1
35
65
89
1
2
188
1
3
385
9
152
-------
Appendix 45. Summary of benthos above Station V outfall.
Tava Number of Organisms Total
id .A. a. . .—, _w— i .
1
108
293
1
3
3
32
86
440
6
2 3
1
209 51
4
16 6
47 9
230 57
4 2
4 5
63 100
1 14
1
4 3
65 114
3 2
<-^
6 7 8 9 10
2 1 149
1 90 5 157
432
2+ 19
1 20
5 3 94 6 325
21323
261
969
1
3
31
74
1,339
6
Samples
Nematoda
Oligochaeta
Coleoptera
Trichoptera
Diptera
Gastropoda
*01igochaete
co co ons
Total individuals
Total taxa
+Dead individuals - not counted in totals
*Not counted in totals
153
-------
Appendix 46. Summary of benthos at Station V outfall.
Tax a Number of Organisms Total
Samples
Nematoda
Oligochaeta
Cyclopoda
Diptera
Gastropoda
Total individuals
Total taxa
12345 6 789 10
21 -
4 1 3 -
1 _
1 2 -
+ + + + +
16 99 531 - - - -
40111 26----
10111 3 _ _ _ _
21
8
1
3
33
4
~*~Dead individuals - not counted in totals
-Samples 7 - 10 not taken
-------
Appendix 47. Summary of benthos above tributary at Station IX.
Taxa
Samples
Nematoda
Oligochaeta
Hirudinea
Cladocera
Cyclopoida
Ephemeroptera
Odonata
Coleoptera
Trichoptera
Diptera
Gastropoda
Total individuals
Total taxa
Number of Organisms
1 1
10 20 11 9 5
1
22 13
1 21
1 2
1
22 76 11 87 96
11 4
37 100 27 99 109
65645
11
2 11
10
51 13 17 28 6
63 22 19 41 15
33233
Total
2
94
1
1
8
5
3
1
4
407
6
532
11
155
-------
Appendix 48. Summary of benthos at mouth of tributary at Station IX.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Oligochaeta 71 245 80 23 7 55631 446
Hirudinea 1 1
Cyclopoida 11 12 5
Hemiptera 1 1
Diptera 27 24 88 59 6 8 39 24 2 2 279
Gastropoda 2213 8
Total individuals 99 272 170 82 15 15 49 30 5 3 740
Total taxa 35323 44222 6
156
-------
Appendix 49. Summary of benthos 30 yards below mouth of tributary at
Station IX.
Xaxa Number of Organisms Total
Samples 12345 6 789 10
Nematoda 111 3
Oligochaeta 214 67 90 45 32 83 7 12 2 10 562
Hirudinea 21 3
O
Cladocera 3
Cyclopoida 25 6 7 1 3 4 46
Trichoptera ! 11 3
Diptera 63 31 33 126 63 93 53 23 15 17 517
Gastropoda 45244 112 23
Total individuals 312 111 133 176 102 181 60 36 19 30 1,160
Total taxa 76544 42344 8
157
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Appendix 50. Summary of benthos 150 yards below mouth of tributary at
Station IX.
Taxa
Samples
Nematoda
Oligochaeta
Hirudinea
Ostracoda
Cyclopoida
Trichoptera
Diptera
Gastropoda
*01igochaete
cocoons
Total individuals
Total taxa
Number of
1
1
105
1
1
19
2
127
5
2
63
2
1
47
2
115
5
3
1
15
3
1
29
1
50
6
4
1
5
4
4
32
4
50
6
5
17
1
6
28
2
54
5
Organisms
6 7
30 36
1
2 5
15 18
6 2
53 62
4 5
8
1
46
4
21
3
2
75
5
9 10
1 3
1
21 1
1 1
23 6
3 4
Total
4
321
9
1
26
1
231
22
615
8
*Not included in totals
158
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Appendix 51. Summary of benthos above mouth of tributary at Station X.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Foraminifera 21 3
Nematoda 1 1114
Oligochaeta 41 79 13 38 77 57 73 75 163 95 711
Hirudinea 11 2
Cladocera 1 1
Calanoida 1 1
Cyclopoida 1 131 6
Diptera 1 5 17 33 1 1 53 83 13 6 213
Gastropoda 2 2
Total individuals 43 85 31 71 80 59 127 163 181 103 943
Total taxa 33323 33564 9
159
-------
Appendix 52. Summary of benthos at mouth of tributary at Station X.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Foraminifera 1 1
Nematoda 4432 2 1 16
Oligochaeta 81 61 121 40 53 132 66 85 19 17 675
Cyclopoida 12 1 4
Diptera 6 16 7 4 15 9 88 150 67 362
Gastropoda 33 6
*01igochaete
cocoons 1222
Total individuals 92 87 134 46 53 150 75 173 169 85 1,064
Total taxa 46431 42223 6
*Not included in totals
160
-------
Appendix 53. Summary of benthos 70 yards below mouth of tributary at
Station X.
Taxa Number of Organisms Total
Samples 12345 6 789 10
Nematoda 1 1
Oligochaeta 23 18 44 23 64 101 59 12 72 112 528
Cyclopoida 111 3
Isopoda 1 1
Ephemeroptera 1 1
Diptera 150 60 232 76 40 14 18 23 14 4 631
Gastropoda 31 21 1 8
Total individuals 177 81 278 100 106 116 77 35 87 116 1,173
Total taxa 45433 32232 7
-------
Appendix 54. Summary of benthos 150 yards below mouth of tributary at
Station X.
Taxa Number of Organisms Total
S amp les
Foraminifera
Nematoda
Oligochaeta
Cladocera
Cyclopoida
Diptera
Hydracarina
Gastropoda
*01igochaete
cocoons
Total individuals
Total taxa
1
17
2
19
2
2345
2
3
18 329 203 76
1
18 33 42 2
2 11
2
38 366 246 81
3434
6 789
3 1
2 4
31 56 111 48
231
1 53
1
2
1
37 58 123 56
4264
10
6
42
1
3
52
4
6
15
931
1
7
109
1
6
1,076
8
162
-------
Appendix 55. Rainfall distribution in inches for 1969, 1970 and 1971,
January
February
March
April
May
June
July
August
September
October
November
December
Annual
1969
Total
1.26
1.99
3.62
3.40
7.12
0.63
0.77
2.56
4.55
5.82
1.22
2.75
35.69
Departure
-0.78
-0.25
+1.11
-0.20
+2.53
-2.35
-0.98
+0.88
+2.01
+3.23
-1.24
+0.40
+4.36
1970 1971
Total Departure Total Departure
0.72
4.78
3.49
4.68
3.62
0.61
0.94
6.85
6.25
2.95
0.20
1.01
36.10
-1.32
+2.54
+0.98
+1.08
-0.96
-2.37
-0.81
+5.17
+3.71
+0.36
-2.26
-1.34
+4.77
0.19
1.32
0.34
2.76
1.88
0.83
3.60
-1.85
-0.92
-2.17
-0.84
-2.70
-2.14
+1.85
(Taken from Annual Summary, Climatological Data, Department
of Commerce.)
163
oU.S. GOVERNMENT PRINTING OFFICE: 197a 484-487/348 1-3
-------
SELECTED WATER
RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
i /. Report Jfo.
3. Accession No.
w
4. Title
INDUSTRIAL WASTES: EFFECTS ON TRINITY RIVER ECOLOGY
FORT WORTH, TEXAS,
7. Aathor(s)
Murphy, C. E., Newland, L. W., Forsyth, J. W., and Keith, D. E.
5. Report Date
j 8. I -. rfoTmi' • g Orga tn zat/on
Report- No,
9. Organization
Texas Christian University
Department of Biology
Fort Worth, Texas
10. Project No.
11. Contract I Grant No.
EPA WQO 18050 DBS
13 Typ< i- Repo and
Period Coveted
12.', Sr' o&orittp Ozgaxo -atioa
IS. Supplementary Notes
is. Abstract Toxicity of industrial effluents discharged directly into or in close proxim-
ity to the Trinity River was reflected through a 27-month period. The investigation was
concerned with four aspects—bioassay, growth and development, chemistry and benthos.
Three industries contributed toxic materials which had a significant influence on the
surrounding aquatic community. Toxicity ranges were established for the respective efflu-
ents using mature minnows, fry and spawn. Fry surviving 96-hour exposure to some of the
effluents later developed orientation problems and varied noticeably in growth. Fry were
only slightly less resistant to the effluents than minnows, but were judged to be reason-
ably reliable bioassay test organisms. Effluents from a railroad equipment cleaning area,
a plant producing cracking catalysts used in processing combustion engine fuels and a
sewage treatment plant influenced the water quality of the river downstream from the out-
falls. The ranges of nitrates, phosphates, biochemical oxygen demand and specific con-
ductance for the river were increased by the effluents.
Environmental stress was detected at the railroad equipment cleaning area outfall and
even more at the plant producing cracking catalysts. Benthos were not able to live in th<
flocculent material discharged in the latter effluent. The drastic reduction in inverte-
brates at the sewage treatment plant is believed to have resulted from the chlorinated
effluent.
This report was submitted in fulfillment of Project Number 18050 DBB under the sponsor-
ship of the Water Quality Office of the Environmental Protection Agency.
17a. Descriptors
*Bioassay, *Water quality, Industrial effluents, *Water pollution, *Toxicity, *Sewage
effluents, *Benthic fauna, *Seston, *Fish, Minnows, Fry, Channel catfish, Shiners, Bass,
Sun fish, Fish eggs, Trace metals, Biochemical oxygen demand, Chemical oxygen demand,
Conductivity, Food processing wastes, Acid wastes.
17b. Identifiers
*Fish development, *Abioseston, *Bioseston, *Fort Worth, Texas, *Trinity River,
*Tarrant County, Quantitative study, Distribution, Invertebrates, Turbidity, River
discharge, Food processing wastes, Dissolved oxygen.
17c. COWRR Field & Group 05C
IS. Availability
9, Security Class,
•*Q.
2f, tfoiW
Pages
••12, • -Pries'•'
Send To:
WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S. DEPARTMENT OF THE INTERIOR
WASHINGTON. D. C. 2O24O
Abstractor C. E. Murphy
I institution Texas Christian University'
WRSIC I O2 (REV. JUNE 1971)
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