TRACE MATERIALS IN
WASTES DISPOSED TO COASTAL WATERS:
Fates, Mechanisms, and Ecological Guidance & Control
vyyATFBy
FEDERAL WATER
QUALITY
ADMINISTRATION
NORTHWEST REGION
PACIFIC NORTHWEST
WATER LABORATORY
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TRACE MATERIALS IN WASTES DISPOSED
TO
COASTAL WATERS
Fates, Mechanisms, and Ecological Guidance and Control
by
MILTON H. FELDMAN
Chief, Chemical and Biological Oceanography Branch
National Coastal Pollution Research Program
Working Paper 78
United States Department of the Interior
Federal Water Quality Administration, Northwest Region
Pacific Northwest Water Laboratory
200 SW 35th Street
CorvalUs, Oregon 97330
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CONTENTS
Chapter Page
I. AVAILABLE TRACE MATERIAL DATA 1
Natural Processes 1
Coastal Waters 1
TM = TE + TC 2
Composition of Municipal Wastes 6
"Organic" Analyses of Sewage Effluents 8
Inorganic and TE Analyses 12
TE Analyses 12
TE Content of Seawater 17
Influence of Sea Borne TM 17
II. SOME MECHANISMS OF TM IN COASTAL WATERS 21
III. SOME ASPECTS OF TM IN ESTUARINE AND COASTAL WATERS ... 27
IV. THE SAWDUST MULCH PROBLEM AND THE POSSIBLE USE OF
WASTES: GUIDANCE AND CONTROL 35
V. APPENDIX 41
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As an example of specific problems, we might cite the concen-
trating of metal atoms. It is immediately apparent that the
concentration of certain metal atoms by aquatic biota, e.g., the
often cited Zn65 in mollusca off the Columbia River, is becoming
a more sophisticated problem.
Is the atom concentrated by similarity and is it laid down
with chemically similar atoms as strontium or plutonium in bone,
or is it like vanadium to some blood systems as iron to some others?
Is the atom concentrated as an essential metabolic agent and is it
then found in the liver, or is it merely an accidental ingestion
with no mechanism available for excretion and is it then found in
the kidney? In other words, the atom's role in the life cycle is
the reason we should study it,not merely to record that here is an
element significantly concentrated (with possible food chain
significance), or an easy to follow tracer convenient to observe.
We need to know the mechanism whereby it is secluded, the
metabolic threshold, active level, and harmful level, and the
speciation requirements, and absolute rates in and out of the
compartments of which coastal waters, sediments, chemical system
phases, and biota may be considered as composed.
It was done for DDT and it ought to be done for the set of
wastes' constituents whose management is properly our problem.
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INTRODUCTION AND SUMMARY
The essence of the argument implicit in this analysis might
be expressed as follows:
The kinetics of bloom phenomena and the culmination biomass
achieved are not the specific problem we address, nor are the gross
nutrients although all these questions are certainly related and of
interest. What we ask is which algae, and which benthic and pelagic,
species will be "crucially" aided or hindered by the trace material
ambient we can create through our waste management procedures. What
specific mechanisms operating via trace guidance and control materials
are available to us for species control rather than total biomass
control?
We are aware of and concerned with the work of our colleagues
studying eutrophication of lakes; but eutrophication levels of
phosphorus and the utility of reduction of phosphorus introduced
into waters from various effluents is not necessarily the problem
from our oceanic point of view; nitrogen supply may well be more
limiting in the ocean than phosphorus. The role of silicon at the
origin of the food chain is undetermined.
If we can ensure a desirable crop propagation, then it might be
wiser to give that crop all the phosphorus, nitrogen, or silicon it
can beneficially use.
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I.
AVAILABLE TRACE MATERIAL DATA
Natural Processes
In studies of the chemical, geochemical, and biologically
directed chemical and physical mechanisms controlling the behavior
and fate of waste materials introduced into the sea, it is apparent
that the controlling mechanisms are "natural," i.e., not different,
but obeying the same chemical and biological laws as control the
naturally introduced materials. Details of rates, concentrations,
and specific materials will vary from point to point and these
differences are to be understood by means of the same practices
and principles as have been applied to chemical and biological
oceanography (Richards, 1969).
Coastal Waters
The truly significant difference, however, is one of locale
and of the specific physical, chemical, and biological mechanisms
prevailing in that ambience - the near coastal waters and estuaries,
the zones of rapid mixing of the world ocean waters, and the fresh
waters run off from the land. Since this zone extends from well
inland in some instances, to the entire sea mass in others, it
represents the gamut of possibilities and, of course, of difficulties.
It is possible, however, to treat the important coastal waters as a
fairly well-defined area in any given case, with more or less input
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2
TM = TE + TC
It will become apparent from a consideration of the documents
studied and listed in the references that our subject rapidly
became trace materials (TM), both trace elements (TE) and trace
organic compounds (TC) in the coastal and estuarine zones of the
neritic ocean. It is not claimed that all the answers to the
fate of and the influence of wastes disposed of in the coastal zones
devolve into a question of TM only. But the need for detailed in-
formation on the behavior, mechanisms, and fate of TM has been
apparent. Provasoli (1963), Johnston (1963, 1964), Goldberg (1965).
In a meeting at Jackson Hole, Wyoming, July 7-12, 1969, com-
mittees of various disciplines addressed to the question - the
rational management of waste disposal in coastal and estuarine
waters: especially the chemistry and biology panels emphasized the
need for TM information, descriptive and mechanistic, but also the
Committee on Monitoring listed the need for a specification of
trace elements and suitable procedures for a complete monitoring
system (NASCO-NAECO, 1969).
We deal with TM which
(a) are known violently noxious materials
Pb++, (CN)g» Hg++
(b) are biostimulatory for some species
cobalamin, iron chelates, thiamin,
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3
(c) are bioinhibitory for at least some species
in various mechanisms.
DDT, Se, Mn, Mg.
Thus, cobalamin is a catalyst, EDTA is a solubility and
concentration conViol material, Mn is an enzyme. c.o-^a.cXon.% and
other mechanisms certainly occur. Case (a) is not included in our
discussion except to refer to it as covered by Sharp (1969). But
the cases (b) and (c) are the subject of our proposed Guidance and
Control for ecologically useful use of wastes in the coastal
environments.
We have limited our assessment to'chemistry and biology, and
having assumed that chemistry and biology determine ecology and
ethology, have concluded they can provide possible means for
guidance and control.
The words contaminant, pollutant, which here have negative
connotation, are in far more popular use these days than words like
recharge, useful use of nutrients, ecological guidance and control*,
which have positive connotations. This is not an isolated phenomenon.
A review of Roget's Thesaurus shows that there are generally more
ways to describe bad situations than good, more ways to denigrate
*The words guidance and control are words suggestive of technologically
feasible ends; management of wastes in coastal waters implies legal
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than praise. Our language is part of how we think. Since in the
case of environmental quality control the need is for positive
thinking of solutions to problems, it is suggested here that "proper
guidance and control" of wastes disposed of to the marine environ-
ment can result in positive contributions - good rather than
deleterious effects. The only prerequisite to this desirable state
of affairs is knowledge - sufficient understanding of how things
work. While this point of view, that knowledge engenders good, is
no longer so generally accepted as it once was, it probably is still
a useful approach to technological problems.
The author, therefore, has evaluated the available information
on the probable TM content of domestic wastes input to coastal
waters and has considered their possible impact. As will be seen,
the quantitative data on the input and its chemical, biological,
and physical behavior and fate is scanty indeed, but every indication
from known and suspected relations in chemical and biological
oceanography is that while the impact could be most significant,
it may be controllable.
Even with the considerable ecological knowledge apparently
available prior to the widespread use of DDT on land to control
certain insect species, it is now clear that much more basic
biological, chemical, and physical information would have been
desirable. We are already putting very large amounts of general
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5
wastes (Arnold, 1950) into the coastal waters, and even such
materials as chemical warfare reagents have been subjects (numerous
newspaper reports, mid-1969) for oceanic disposal. It is claimed
that large scale oceanic dumping can be safely carried out without
damaging the coastal and oceanic environment (Sport Fishing Institute,
1969). However, Waldichuk (1968) has listed the wide ranging needs
for improved methodology in the required long-term studies. The
basic knowledge to be drawn upon to enable the safe disposal claimed
(Sport Fishing Institute, 1969) is not referenced and does not seem
to be available at this time (November 1969), but what information
is available seems to indicate that the results might be slow in
eventuating but startling in their finality. Thus, consider the
early optimism, based on lack of sufficient data, during an examina-
tion of the benthos in a very limited area of acid-iron waste dump-
ing off New York City (Arnold, 1950). Compare that early optimism
with the later guarded pessimism based on observed benthic deple-
tion and diversity reduction (Sport Fishing Institute, 1969) in
the same general location, but now covering a much larger area.
Given the sediment scouring and washback to the Long Island beaches,
we see the need for prior study and conservative extrapolation.
Incidentally, the sediment scouring and washback to the beaches of
Long Island could have been predicted from known long-term phenomena
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At the same time as these oceanic questions are raised, the
Congress is reviewing and passing legislation designed to provide
funds to clean up the Great Lakes, once considered a good place to
dump wastes with insufficient prior knowledge of levels, mechanisms,
and fates.
Composition of Municipal Wastes
In studying the problem of safe and practical disposal of
municipal wastes, it would seem that a first question requiring
reliable data acquisition would be what is the material to be
disposed of? What is its chemical composition? This, however,
was not the order of data acquisition. The use of secondary
(biological) sewage treatment plants preceded the systematic ana-
lysis of wastes by a long time (Sawyer, 1965). The earliest reason-
ably complete attempt at a domestic sewage analysis found was that
of Painter and Viney (1959)^ . This contribution from the Water
Pollution Research Laboratory, Stevenage (Herts), describes the
organic composition of whole domestic sewage from a new town. Four
physically separated fractions, settling, centrifugating, candle
filtration, and filtrate were analysed. Presumably, the three solids
fractions would parallel the solids utilized in the pioneer effort
~Superscript numbers accompanying references, e.g., Painter and
Viney (1959)^, refer to a table or figure excerpted from the
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in the USA by Heukelekian and co-workers (Hunter, 1965^;
Heukelekian, 1959^).
Almost all the work done on characterizing and estimating the
components of municipal sewage effluents has been carried out with
some other end in mind than a simple, detailed specification of
that composition.
Painter (1958)^ had previously examined the same new town
municipal sewage for inorganic composition. In spite of the
detailed effort and careful examination by Painter and of Heukelekian,
et al., it is clear they only account for at most 65-80 percent of
the gross organics (on this point, see also Bunch, 1964); they made
no attempt to describe the trace organic compounds (TC), and they
were severely conditioned by the overall engineering requirements
for materials handling on the large scale. Furthermore, they had
a need to know the gross chemical composition of their substrate in
terms of C, N, P, since that, so far as contemporary sanitary engineer-
ing thinking was concerned, was the problem. A review of eutrophication
history (Stewart, 1967) shows this thinking to be typical also of
the other disciplines involved. Although it was at about this time
that oceanographers and marine microbiologists became aware of the
probable role of TM, this was still new and not yet generally
disseminated. Painter and Viney (1959) and Heukelekian (1959) seem
(5)
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on organic composition of a variety of substrates, seems aware of
the possible importance of sewage TM in ecological questions.
Painter (1958)^) analyzed, for inorganic composition, the
Stevenage new town sewage based on evaporation to dryness, and
without fractionation of the total dried solids determined the
major ions. This procedure not only abandons the possible develop-
ment of information on speciation which is essential to understand-
ing the role of TE, but only gives an approximate view of the gross
inorganic composition, as well. As will be shown, later, more
detailed inorganic analysis in the USA, while apparently containing
much more information, in reality does not offer much beyond Painter
(1958).
"Organic" Analyses of Sewage Effluents
J. R. Vallentyne (1957), in a review directed toward the
biochemical aspects of ecology, listed known molecular forms of
organic matter found in lakes and oceans and in terrestrial soils
and sewage. He discussed the probable nature of organic substances
known to exist, but whose composition or compositions had not yet
been established - toxins and materials secreted or excreted by
phytoplankton which apparently determined succession of other plank-
ton or even in the case of GymnodivUum b/ieve (red tide organisms),
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It is impractical to review a literature review for detailed
information contained. The reader, concerned with essential back-
ground for any experimental approach to the fate and possible
effects of sewage on neritic waters and sediments and on the biota
in the neritic zone, should certainly have available for reference
Vallentyne (1957), Raymont (1966), and Provasoli (1963).
One conclusion we have drawn'from Vallentyne (1957), Raymont
(1966), and Provasoli (1963), inter alia, is simply this: whenever
the question arises: does a given class of TC occur in sewage,
detailed examination will probably show it, or its precursors to
exist in various waste waters. A specific TC material may not
have been experimentally demonstrated in waste, but it is not safe
to conclude that it is not present. The question is, how much is
present and what possible mechanisms are available for its fate.
The balance of TE and TC in a given coastal situation and the needs
of the desirable versus undesirable biota constitute the relations
to be determined by chemistry and biology. Vallentyne (1956) has a
succinct statement in PUtters Hypothesis*. "The hypothesis
has never been rigorously tested even though excellent tools are
now available (isotopes, microfilters, chromatography)." This is
now (1969) no longer a controversial matter. The question now is
the delineation of the detailed mechanisms and quantities.
*Putters Hypothesis is that lower forms ingest a significant amount
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Heukelekian and Balmat (1959) and Hunter and Heukelekian
(1965) represent two reasonable analyses of the organic composition
of sewage. In the first (Heukelekian and Balmat, 1959) it was
recognized that protein, carbohydrate, and fat occur in sewage,
but that detailed compositional data were unavailable. They
examined the gross organic constituents occurring as solids, namely
settleable, supracolloidal, and colloidal.
Hunter and Heukelekian,(1965) pointed out that prior examina-
tions of wastewater organic composition generally concerned the
detection and composition of individual compounds of a particular
interest. This is a limited approach and, of course, leaves most
of the individual wastewater organic compounds (especially TC)
undetected. Using a typical residential community sewage, they
performed careful composite sampling and analyzed all fractions.
While their results are still in the sanitary engineering vein,
lumping together types of material (grease - 7%; amino acids - 19$;
carbohydrates - 24%, in particulate fraction), because the engineer-
ing problem of large scale materials handling as a physical process
is the important question for this work, the results are reasonably
detailed and show that the composition, mutatis muXandU, is very
like the composition of the British sludge samples (Painter, 1959).
Minor constituents (TC) mentioned, sterols, vitamins, creatine-
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Murtaugh and Bunch (1965)^ analyzed for the acidic components
of sewage effluent and river waters; the acidic components from a
variety of secondary plant effluents were described. Some of the
fatty acids observed are known to coordinate some of the TE of
interest; some of the lower fatty acids constitute stages in the
metabolism of high molecular weight materials down to ultimate COg.
How they will figure in the metabolic pathways in a given coastal
situation is still to be determined (Provasoli, 1963). What the
effect is, of compounds of this nature on TE en route to the coast
is unknown.
A somewhat more detailed examination of the organic components
of sludge was made by Teletzke, et al. (1966)^ who examined the
products of low temperature oxidation of sludge in order to determine
the nature of the solids residue (the liquid being "accessible" to
biological processing and, therefore, of no interest to them) in
order to devise satisfactory procedures for further treatment.
Assuming, with the APHA Standard Methods (1965), that proteins sugars,
starch, lipids, and crude fibers were the principal constituents
(by mass), that was what was determined in their analyses. Nucleic
acids, with their considerable potential for biological activity,
were ignored as relatively unimportant. An observation made, was
that among the reactions occurring was hydrolysis of proteins to
free amino acids (FAA) an observation of significance in any planned
coastal disposal of the products of waste treatment processes (Clark,
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sludge that has been subjected to heat and oxygen, and while sug-
gestive, has only an oblique relevance here.
Inorganic and TE Analyses
Numerous reports of analyses for a selected group of TE occur
in the U.S.A. and other literature, but all are subject to serious
question, so that this subject must be considered an open matter.
For example, one of the most completely documented, apparently, sets
of TE analysis data is that of the Hyperion outfall system in Santa
Monica Bay, California, as described by Hume, Gunnerson, and Imel
(9)
(1962)v ' and later Bargman and Parkhurst (unpublished compilation,
1969)^^. In the Hume-Gunnerson (1962) data, the Hyperion TE
composition is described in detail in time sequences: up to
September 1957, present data 1957-1960, and projected data 1960
et.seq. All the tables bear an astonishing reproducibility of the TE
data (the 1957 table is appended) "observed" for a series of TE
estimates in a large tributary population in an industrialized metro-
politan area. At the time these data were taken, no attempt at
speciation was made in the absence of prevailing suspicions that
this might be of mechanistic importance.
TE Analyses
In the U.S.A., R. N. Thompson, et al. (1964)^^ examined the
effluent analysis data from a large number of sewage treatment
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concluded, "Numerous studies of the gross composition of sludge
have been made, usually with the soil building capabilities in
mind." They mention some comparisons of C, N, P, and of ash content
of various sludges, but conclude that "although isolated reports
have been made on the exact inorganic chemical composition of sludge,
comprehensive studies are apparently lacking."
They undertook a detailed spectrographs analysis* of air-
dried sewage sludge with no provision for distinguishing inorgani-
cally from organically bound metal atoms. However, this work
constitutes a real advance over the previous dearth of reliable
data. While some of the internal ratios of elements are apparently
inconsistent, it is believed their results represent a fairly good
and complete list of TE in the "organic" composition of sludges.
Other TE analyses have been carried out by various workers
interested in the ground water recharge, agricultural use of sewage
(12)
(Wilson, 1968) , and the TE content of rivers as they approach the
(13)
sea (Turekian, 1965, et seq.)v . These results are of general
interest, but the data cannot be extrapolated to coastal waters since
en route to the coast, the average TE composition and the relative
TE composition and speciation will change, as will the particulate
burden and its adsorbed TE. For example, the data of Turekian (1965,
1968), the data from Wilson (1968), and the Hyperion data are notice-
ably variant. Is this due to the differences in original sources, the
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differences in the particulate chemistry, or the differences in the
dissolved organics, or possibly, the methods of analysis employed?
Assuming reliable estimates on the part of each set of experiments,
it may be possible to understand the mechanisms of interaction and
change of TE composition of waters on their way to the sea.
(14)
Neale (1964)v ' presents the more common inorganic constituents
of some 22 typical municipal water supplies and then through effluent
analytical data for these cities' sewage plants shows the mineral
increment per once through domestic usage. His interest, the
sanitary engineering of distillation purification plants depending
on such effluent supplies for input with concomitant scaling pro-
blems, restricts his examination of effluent composition to the
major components and to such catch-all specifications as hardness,
alkalinity, total solids.
Outright errors and internal inconsistencies (lack of material
balance) are to be noted in these tables, but the tables are
reproduced in the Appendix as among the best available data of this
kind.
An interesting comparison would be the natural waters TE
composition and the TE composition of sewage generated in the
population dependent on those natural waters. To some extent,
(Turekian, 1965-1968; Livingstone, 1963; Wilson, Becket, 1968; and
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A comparison of Hyperion outfall TE and the seawater TE
concentration isopleths in the vicinity is not available, but
would be most illuminating for ecological comparisons.
Since the TE elementary composition of sewage is largely a
reflection of TE composition of the original natural water supply
in the locale, it might be supposed they are similar (but not
congruent) in the geometric sense. This is a view implicitly
assumed by various workers (Bunch, 1964; Wilson, 1968; Eckenfelder,
1969) who compiled data on trace element increments in once-
through domestic usage. The organic complexity of sewage effluents
as compared to most municipal water supplies (similarities may
occur for natural water supplies - Vallentyne, 1957) means that the
TE binding to particulates (Turekian, 1967) to chelate systems
(Duursma, 1966) and speciation in general, must be reevaluated
(NASCO-NAECO, 1969). Perhaps the same question should be raised
concerning TC.
In general, the trace element composition of the wastewater is
related to that of the natural waters in the vicinity and these have
been tabulated (Livingstone, 1963; Turekian, 1965; and Bowen, 1966).
As is to be expected, the relative concentrations will vary some-
what, since there are other inputs to human diet and since man, no
less than mollusca, can concentrate some atoms. And, of course,
the concentrations in wastewaters will be increased over the natural
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/
presence of large quantities of water with its TE content, but we
expect changes. Put in more familiar terms, this means that the
concentration of specific TE by the metabolic processes of organisms
is now a well-recognized phenomenon. (Nelson and Evans, 1969;
Radioactive Wastes, 1966).
Another change to be expected is that the organic linkages of
the TE must certainly change. The enzyme cofactor relations, co-
ordinate complexes with amino acids, chelate compounds, the relation
of TE to surfactants, all these speciation considerations must be
significant to subsequent mechanisms in ecological consequences.
However, no information was found.
However, the reverse case, the action of TE on the processes
occurring in secondary plants has been investigated from the
sanitary engineering point of view -- does a slug input of a
particular ion interfere with the normal operation of a (activated
sludge process) sewage treatment plant? This proposition was con-
sidered for a number of ions (Ettinger, 1965) without regard for
mechanisms, and it was shown that ultimately the slug input was
passed on and the plant resumed its previous efficiency. Long-term
input was not carried out nor was speciation of input considered.
Apparently, no one has asked what the effect would be of large
scale inputs of TM via sewage effluent systems to coastal waters,
although some comparisons have been made of ocean sediment organic
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As this report was in press, there appeared a news report on
the establishment of classes of biodegradability for various
synthetic organics passing through typical activated sludge plants
(Buzzell, 1969). About 7 out of 22 classes were appreciably passed
by the plant, though in batch processing they were more susceptible.
No detailed information was available on trace materials.
TE Content of Seawater
The overall trace element analysis of seawater, while in far
from complete form, especially in near coastal zones, is in a
(15)
reasonably useful stage. The compilation of Bowen (1966)v is
very useful, the analytical methods and compilation of Chow (1968)^^
more specifically addressed to oceanography and pollution, is a
particularly valuable review. Goldberg's chapters (1961, 1963)
also are useful summaries and discussions of the minor elements
(13)
(TE in our notation). Turekian (1965)v ' has summarized the TE
content of certain rivers and their TE input from industries as the
rivers approach the coast.
Influence of Sea Borne.TM
One estuary of some considerable size, and a freshwater flow
of some magnitude, where sewage plant effluent is planned for the
near future as a significant fraction of average flow, and possibly
much greater than lower flow values, is the Duwamish estuary above
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Green River from the Cascade Mountains at 340-20,000 m3/min. The
mean flow is reported (Welch, 1968) as 1,700 m3/min.
Welch says that the proposed ultimate capacity of the plant
is to be 545,000 m3/d (about 380 m3/min., but subject, obviously,
to time of day minimum-maximum variations.
A simple study of the phytoplankton "blooms" in the estuary
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The study using phosphate/nitrate ratios and chlorophyl a^
observations at various stations over seasonal variations showed
that the chlorophyl did not increase where the "nutrients" were
greatest, but did increase markedly lower in the estuary where
nutrients were supposedly lower in concentration. The suggestion
was made that these phenomena represent the results of fresh water
at the upper reaches versus salt water introduced at the lower
reaches. The possible importance of trace materials was recognized,
but with no discussion. However, some data on trace elements at
the station of greatest phytoplankton abundance are given. No
mention was made of the possible introduction of control, catalytic,
or limiting nutrients with the salt water entering the lower estuary.
Physical factors (light intensity, water column stability,
D.O.) were considered, but these did not clearly influence blooms
from place to place in the Duwamish estuary. The discussion
concentrated on "nutrients" and it was claimed that there was no
difference in mean total phosphate concentration during the three
summers of observations, but that the tidal prism was better
correlated to timing of the bloom initiation and biomass achieved
correlated best to the time over which the tidal prism remained
high relative to the fresh water input. No mechanism is suggested,
but the tidal importation of relevant materials cannot be ignored
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Young, et al. (1967) examined the question of the bio-
degradability of organics which increase continually in number,
complexity, and potential for ecological effects. They measured
the biodegradability of classes of organics by relative rates of
TOC or COD disappearance versus oxygen uptake and total bacterial
growth using a small wastewater inoculum and allowing sufficient
time for "acclimation." "Acclimation" may have meant that a single
species present grew in and did essentially all the biodegrading,
the species varying from material to material, since, acclimation
times varied.
No consideration was given to possible complexities arising
in a natural locale where many other species and components (TE
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II.
SOME MECHANISMS OF TM IN COASTAL WATERS
Evaluation of pollutants at low concentration and their
chemical and biological interaction is difficult on two scores:
1. The problem of detection of the long term "subtle effects"
is even more tedious and difficult in epidemiological theory and
practice than determination of the more familiar LD5q, a severe
problem in its own right (Waldichuk, 1968). Forensic methods
involving histochemistry, blood serum electrophoresis, hematrocrit,
and other hematological examinations, enzyme activity inhibition,
are all available for such studies. All are of substantial com-
plexity in the doing and in the interpretation. Examples are known
of avoidance and the like, effects on learning capacity, aggressive-
ness, territorial ism and courting. M. Blumer (1969) commented that
many marine animals produce minute amounts of chemicals that perform
functions essential to maintaining the cycle of life. These
chemicals act as attractants during the mating process. They aid
predators in locating their prey, and conversely, give warning to
potential victims that they are being stalked by predators. Oil
whether from a single big spill or a buildup of repeated small
doses - may well upset these vital chemically-triggered processes.
The above paragraph mentions the effects possible on forms
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forms ingesting (and excreting) minute amounts of key TC and TE
from colleague and precedent forms may have their normal metabolic
behavior made impossible with potentially catastrophic results.
Recognizing the fact of our ignorance of the details of these
processes (Provasoli, 1963) emphasizes the dangers of proceeding.
Surely ignorance here, where we are introducing a large variety of
TC and TE from every outfall and barge dump operation, is no basis
for optimism.
2. The chemistry of detecting, characterizing, and quantitat-
ing micro amounts of relevant TC is one of considerable difficulty
(Park, 1962; Jeffreys and Hood, 1958; and Clark, 1969), while the
estimation of TE is of such complexity and experimental difficulty
that only intercomparison of results by a variety of methods can
lead to a degree of confidence (Bowen, 1966).
The effects of substantial additions of specific pollutants
on various biota has, of course, a large literature (Sharp, 1969).
These evaluations of higher animal susceptibilities to gross
pollution or to specific poisonous materials constitutes an
important area not dealt with in this work. In addition, no
discussion is given here concerning the profound chemical and bio-
logical reaction changes which may be induced by changes in the
thermodynamic variables, such as temperature, radiation, ionic
strength (Cawley, 1969). Similarly, the effects of gross organic
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deposits with anaerobic phenomena (^S production, concentration of
iron), have all been noted near sewer outfalls or at barge sludge
dumping operations. Only Vallentyne (1957) has attempted a com-
parison of the organic TC of coastal and fresh waters with the
possible input from sewage. The impact for microorganics (TC) as
for TE would be:
(a) Strangeness (no previous experience of the
species with the material)
(b) Concentration possibilities
(c) Metabolic interferences (stimulatory
or inhibitory)
One very practical reason that more is not known about TC and
their effects in the coastal zone is that, not only do these change
from place to place, but also at each point a complete description
might be a life's work addressed to subtle effects and complicated
chemical questions. Yet, the instance.of DDT present in very low
concentrations indicates such information is essential. The world
wide subtle effects* from TC in sewage may, as in the case of DDT,
affect the world ocean even where the local dramatic effect*
*We distinguish here two phenomena: In one, the local dramatic
effect, a violent noxious material may kill 1 or 1000 individuals
in a strictly local catastrophic event. Natural degradation pre-
vents widespread disaster. In the other, the world wide subtle
effect leads to no immediately newsworthy results and remains open
to discussion for long periods. The physical and chemical differences
which lead to these distinct possibilities are, among others, low
biodegradability, accumulation from low concentrations in the environ-
ment by biota, passage and concentration up the food chain, key
metabolic effects as hormone or enzyme reactions interferences, all
-------
24
does riot occur. The analogy to the DDT case for trace compounds
put into the marine environment is a distinct possibility.
Goldberg (to be published) quotes the well-known saying, "For
every chemical element, there is at least one planktonic species
capable of spectacularly concentrating it." Then extrapolating to
other chemical material inputs to the oceans, he suggests some
species will occur for taking up each modern technologically advanced
material. This is undoubtedly an open question. Based on given
clones in existence and the synthesis of new exotic materials, never
before in existence, the chance of many of these establishing a
beneficial rapport seems small indeed. Certainly, the situation is
not analogous to the TE case where the TE have always co-existed
with the evolving clones which have genetically determined abilities
to accept, reject, or concentrate TE.
In my opinion, the specificity of most biochemical reactions
rules out any general tolerance situation but massive introduction
of strange materials to a given area will probably always result in
changes in the clones, numbers and types. In the case of low level
or TM introduction, it is to be expected that these same principles
apply but due to our present lack of experience, we cannot predict
steady-state concentrations of either material or respondent.
On the other hand, it is just this specificity which allows us
to state there is a theoretical possibility of the use of "guidance
-------
25
surplus undesired nutrient. What these will be for any given
habitat remains to be demonstrated.
The fallacies in considering the oceans as infinite sinks,
therefore, are:
1. We do not have detailed knowledge of input, inventory,
removal for most trace materials (TM)(Bowen, 1966;
Goldberg, 1965).
2. We do not have detailed knowledge of their inter-
actions with the biota (Provasoli, 1963; Raymont,
1966).
3. We tacitly assume the TM put into neritic and estuarial
waters will be mixed quickly, removed permanently to
the sediment or the deep ocean. Both of these removal
mechanisms are probably not beneficially operative
in determining the fate of the TM introduced (Turekian,
1965; Postma, 1967).
In actual fact, recycling by benthic biota of TM from sediments
may be a most important mechanism tending toward long term avail-
ability of TE from the inventory in the sediment (Hood, 1969). In
addition, it is now suspected that the deep ocean is actually supply-
ing TM to the coastal zone (Turekian, 1965) rather than acting as a
sink. Postma (1967) has described physical processes occurring in
-------
26
We have noted (Provasoli, 1963) that we are dealing with
inorganic TE requirements and resentments and with organic TC
requirements and resentments. Stimulation, inhibition, poisoning,
and feeding regulation have all been described for individual
cases. We have noted (Waldichuk, 1969) that the methodology of
evaluation of long-term low-level pollution is not neat and quanti-
tative, but needs considerable work.
The specificity of species enhancement noted in most cases of
pollution has been undesirable species at the expense of desired
species; but there seems no reason in theory why by proper and
judicious management, the beneficial species could not be enhanced
-------
III.
SOME ASPECTS OF TM IN ESTUARINE AND COASTAL WATERS
The question of trace materials in the marine environment is
no longer - do any species use dilute dissolved material as energy
sources, but which species prefer which compounds and to what extent
can they obtain the required energy in this way, and what are the
rate controlling steps? Such usage seems confirmed as high up the
phylla as Enchinodermata, in which instance work is presently under-
way (M. Clark, 1969). One may speculate on the results of a know-
ledge of the dissolved organics preferences of the steps culminat-
(18)
ing in a predatory fish. The food web is pyramidal in the folk-
lore of salmon and trout nutrition. In a web, alternate pathways
of equivalent efficiency occur and interferences at one point cannot
stop ultimate propagation of the end product species. But in fact,
(19)
it is most selective at each level constituting more of a chainv '
or a network of preferred time sequential interlocking reticules*
(with possibly a greater number entering at the base). In a chain,
there are a number of points at which interference can have sub-
stantial effect on ultimate propagation of the end product species.
If we assume ecological interdependences other than the food pyramid
-------
metabolic contributors of other kinds - odors, sizes of food
particles, poisons, antibiotics, the chance of control and of the
useful use of wastewater increases substantially. For the trout
or salmon, often successful in apparently oligotrophic surroundings,
it is apparent that addition of gross nutrients is not the whole
story (Powers, 1969) (See page 39, Mansueti in kz Sea Bass).
Cronin (1967) presents some Ideas on specificity, balance,
and control by means of nutrient, catalytic, and TM control. These
ideas may also apply to use of selected biocide materials (Butler,
1963) since competitive species may be differentially affected by
small quantities of one or other biocide. The design of "competition
biocides" systems may be as simple as addition of a vitamin required
by one of the species to elaborate toxin or hormonal additions to
prevent regeneration in one, but not the other species.
Cronin (1967) points out the significant variation between
species' response to classes of chemical materials and says that
irregularity in the results of field tests suggests the reasonable
probability that actual toxicity might be affected by temperature,
silt, flushing rates, salinity, and other environmental factors.
Under the designation "other" one might well suspect ecologically
determined nutrition and metabolic responses. So, species A, A'
..., not affected much in laboratory experiments while B, B'...,
are affected. In the field, however, the effects on species C, C'
..., must have some feedback effect on the relative reactions of
-------
29
The competitive synthesis (in a single exponentially growing
species) of protein and carbohydrate is a severely conditioned
matter depending on availability of various nutritional materials
14
even while the apparent C rate is a constant. Thus, the avail-
ability of metabolites, natural or waste product, may be affecting
the overall productivity in ways that have not been measured by
procedures and over long periods not previously considered.
During photosynthesis, it is well known (Fogg, 1964; Burke,
1962) that synthetic material is liberated in the water. The
significance attributed to these materials in determining bloom
succession patterns may indicate how direction and control may be
achieved by application of the information we ought to have before
placing large amounts of wastes in ocean locations.
Wood (1967) in discussing the cycling of nutritional elements
from sediments to supernate waters points out that bacteria are
obviously not doing it all: he dismisses the colorless protozoa as
unimportant in this overall processes. See, however, Johannes
(1965), a reference Wood seems aware of, but not in this context.
The benthic recycling of chemical species plays a role in the
diagenesis of estuarial sediments and vice versa (Hood, 1969). The
elucidation of these chemical reaction possibilities remains an
-------
30
The regeneration of nutrients by biochemical action in
sediments is, of course, only the positive aspect of the problem.
Gahler (1969) observed that sediment from Klamath Lake could be
used in laboratory plankton (Se£zncu>tAum) growth studies (stirring
the sediment presumably allowed escape of the nutrients to the
supernate water, but there are other possibilities); but sediments
from Woahinke Lake diminished the growth of SeZe.na6tn.um in lake
water, which without the presence of the sediment did support growth*.
The more detailed experiments, at various ocean locations, of
Johnston (1963, 1964) offer some clues as to what processes may be
occurring.
What the results would have been for species other than
SeXmcatuuv cannot be specified, but Lackey, at a seminar, quoted
in Symons (1964) was aware that the question of nutrients versus
species specificity could lead to complex relations. "When we
note the condition of blooms in the field, it is at once apparent
that there is much variation of the conditions under which they
appear, and at best our knowledge of what nutrient substance and
amounts are related to algal densities is merely a guess.
*0ne possible explanation offered by these workers is "manganese"
known to be present in Woahinke sediments; however, manganese is
a prerequisite for photosynthesis. The conclusion here would seem
to turn on concentration, speciation, and availability of some
-------
31
"There has been considerable discussion of the possibility
of removing PO^ from the effluents of conventional treatment plants.
It is suggested here that this may change only the composition of
the bloom. There are algae whose PO^ requirements are extremely
low, below the concentration which might remain after treatment."
Lackey evidently conceived of the source of "P" as only inorganically
bound "P" coming from effluent. Organically bound "P", directly
used, or subject to ultimate mineralization or emanating from sedi-
ment, was not part of his scheme, but its existence reinforces his
thesis.
Provasoli (1963) points out that a number of species do very
well on organic "P" compounds (no apparent inorganic "P" require-
ment) and this may in part account for rapid bloom succession based
on quickly available "P", rather than waiting for complete degradation
to mineral "P". Not many studies have been made of this speciation
phenomenon which is of considerable mechanistic interest. The
standard method for "P" as ortho-phosphate will not detect organically
bound "P", in general (Standard Methods, 1965).
The secondary treatment of wastes familiarly referred to as
"the mineralization" (reduction of BOD) quite possibly results in
the organic-metal atom fixing of TE in the same general way as P
and N are reduced from soluble inorganics and organics to insoluble
-------
32
Hanes and White (1968) showed that seawater concentration
affects the oxygen uptake rate of a benthal system in an estuary.
They also showed that addition of "nutrients" from sewage treatment
plant sludge increased the oxygen uptake by the benthic system
regardless of the salinity of the supernate water, but the effect
was greater for greater concentration of seawater implying the
seawater contributed some key material as was inferred from the
sludge only addition.
Carriker (1967) has discussed the estuary ecology with
particular emphasis on the oceanic input to the estuary. The
significance of chelation of TE on plankton at various oceanic
locations has been discussed at length (Johnston, 1963, 1964). But
Duursma (1966) claims chelation is relatively unimportant though he
claims "some effect" and suggests free amino acids, for example,
may be effective. Free amino acids are an identified set of TC in
all sewage and their possible effects on specific ecological systems
may be most significant (Clark, 1969), either as key nutrients,
control media as chelators, or other pathway contributors.
Growth factors and organic control and/or specific metabolic
accelerations are exemplified by the chelating material that makes
iron "available." Presumably, this occurs by simply increasing the
total dissolved iron as against previously insoluble iron, though a
pathway of lower activation energy requirement, or provision of a
-------
33
mechanisms for getting iron across the cell wall would jibe with
geometric specificity of biochemical reactions. At any rate, such
a material is a metabolic "control" rather than a nutrient. It is
also apt to be a concentration, pH, and ionic strength dependent
rate controlling step. If it is a control mechanism and itself a
controllable step, the way to use it for overall guidance and control
seems apparent. Therefore, we say: to speak loosely of the gross
P, N, C input to coastal waters cannot be the whole story for these
elements appear in various molecular arrangements rather than as the
elements. Thus, carbohydrates, protein, fats (and lipids in general)
must be covered in any working hypothesis of mechanisms of appearance
and disappearance of species. Furthermore, without a concurrent
explanation of TM, vitamins and other substances, no coherent story
-------
IV.
THE SAWDUST MULCH PROBLEM AND THE POSSIBLE USE OF WASTES:
GUIDANCE AND CONTROL
The "sawdust mulch problem" is a familiar one to the home
gardener, whereas the professional and the academic may have once
recognized it, but are now off on other tangents and have left
this important problem to the organic gardener and other
doct/vinaJjizi>.
Briefly stated, the sawdust mulch problem arises from the use
of organic mulch to improve the tilth of soils for agricultural use.
The plowing under of green manures being perhaps better but slower,
the addition of manure is experimentally practical and desirable;
the growth of the microorganisms which mediate the agricultural
chemistry of the soil is enhanced, water absorption is increased,
plant roots have better bedding, and in general, numerous desirable
ends are served by adding such mulches to the surface or plowing
them under. But the simple observed fact is that sawdust actually
holds up the growth of plants. As is well known, the sufficient
answer to this problem is that the organisms using the sawdust (break-
ing it down) also use up the immediately available nitrogen compounds.
Given sufficient time, cycling of all of the nutrients would make it
available again, but the immediate need is for the addition of
-------
36
secondary plant sludges for example - we can get the same or even
faster response from the added fertilizer alone. Or, on a dollar
basis and for the short term, it is better to omit the organic
manure and use the familiar N, P, K,inorganic fertilizer which
generally contains TE or to which TE can be readily added. It can
be argued that the situation, based on history (Euphrates Valley)
and on projection (Lake Mead irrigation) is more complex than that
simple solution contemplates. Be that as it may, a conclusion for
the useful addition of wastewaters to agricultural lands (Wilson,
1968) or to coastal and estuarine waters is this: to obtain a
desired result, the propagation of desired forms* - we may need to
revise the TE or TC balance or availability via chemical manipulation
in the same way we have to provide nitrogen in the sawdust mulch
instance.
Control of the available inorganic nitrogen and phosphorus
may be useful, but not sufficient, mechanistically speaking, in
coastal waters where the available data suggest that N, rather
Fertilization which enhances the biomass by substituting thistle-
weed for corn is not a desirable state of fertility. Initiation
and sustenance of a bloom comprised of Gymnodinium b-teve is an
obvious bad result. There are certainly more subtle, longer term,
TM relations to be considered. Change in species present in
coastal waters is exemplified by the replacement of Hltz&cKLcl by
NannochJLoii6 atomuA and by S£ichoc.occu6 -ip. shown (Ryther, 1954)
to occur in Moriches Bay. These, in turn, are known to be
undesirable as food (Ketchum, 1967). In short, they are weeds
growing rapidly where the balance of added fertilizer is somehow
-------
37
than P, is the limiting macronutrient and where organic compounds
of these materials offer alternate pathways. Additionally, the
interaction of these macronutrients with TE may be the rate
controlling steps in complex overall situations. For example,
Gymnodtviium bteue concentrates titanium and zirconium, two somewhat
unusual TE so far as living forms are concerned. But these two
are among the ones best co-precipitated with PO^ introduced as the
salt of or into iron and calcium containing waters. Why this species
blooms off the Florida coast and its relation to the phosphate con-
tent of runoff waters from Florida would suggest an interesting
relation involving TE mechanisms (Dragovich, 1961). It has been
suggested (Morgan, 1969) that the red tide is a natural phenomenon
and as such, one that water pollution workers will not wish to spend
their efforts in studying. It might be asked what is natural, and
what is unnatural? If the red tide mechanism is fully understood
as a result of research, wouldn't this help us to understand the
mechanisms of waste induced or supported blooms and enable us to
avoid undesirable blooms? In the introduction, we have emphasized
that the chemical and biological processes we need to understand are
all "natural" processes.
We need to know the details of the individual food web, chains,
cycles, and alternative pathways in considerably greater detail than
-------
38
The basic Monod relationships and mechanisms of limiting
nutrient depend on a variety of mechanisms*. Thus, inorganic
phosphate may be limiting or not, depending on availability of
organic phosphorus. Further, in recycling via the earthworm effect**
the organics may be available much sooner than the ultimately
mineralized phosphorus. Mediating forms (chelates for TE) will
depend on pH rather sensitively. The cycling of materials via the
earthworm effect will be dependent on what else is available. To
make the proper TM, whether micro iron or vitamin B.^ or biotin,
available to desired phytoplankton, may require that we add additional
or other TM to the milieu.
Consider the graphs depicting the very specific eating habits
of some desirable pelagic biota (Green, 1968)^^. If we wish
phytoplankton M- to be available to feed (i.e., be part of the chain
leading to) UicAopogon undulatiii (Atlantic croaker) or Anchoa
mctckilti (bay anchovy) to provide for the predatory fish we wish
to propagate, then we must provide TM (M.) to that benthic organism
which recycles the TM (M-) required by the phytoplankton M.. The
14
*Like the Steeman-Nielsen C measurements of "productivity" these
observations of a resultant must be interpreted in terms of internal
mechanisms; in our view often the outcome of TM mechanisms.
**The 'fearthworm effect" is the overall benthic recycling of nutrient
elements from within the sediment to the surface of the sediment
and vice versa. This mechanism is, of course, part and parcel of
-------
39
addition of wastes containing nutrients favoring still other webs
or chains from the benthos onward based on TM (My) will not help
propagate the predator fish feeding on HicAopogon undulctfuA or on
Anckoa. rnitokilti, but by a variety of mechanisms will hinder their
propagation.
Wood (1967) asks what phytoplankton and zooplankton are
preferred by what fish. To some extent, ecologists are recognizing
the importance of this question (Green, 1968) and it is clear that
the older idea of food webs is not sufficient. The idea of food
chains must be utilized also in attempting to predict the pelagic
outcome of benthic waste sediment chemical reactions.
Mansueti (1961) described the apparent increase in a desirable
fish population in an important estuary with a number of tributaries.
No mechanisms related to nutrients or other relevant materials were
offered other than a correlation of estimates of fish taken in a
number of years and of population growth in the watershed supplying
the terrigenous waters. Whether, in fact, a fish production growth
curve was observed in the period of population growth is moot; the
important thing is that such an outcome is desirable and possible.
McHugh (1967) has discussed the estuarine nekton from the
point of view of food cycles, energy exchange, and biological
productivity (i.e., desirable useful productivity). The feeding
of soluble organics, labeled as required, at various levels of
-------
40
14
to the familiar C primary productivity measurement, but more
14
incisive. The C method is an overall measurement - a resultant
of competing or additive reactions and details of mechanisms
prevailing and controlling specificity and dominance are not
directly obtained. By the use of sets of organics chosen for the
milieu and the competitive plankton under study, some further
insight would be obtained. The methodology of such experiments is
well worked out (Young, 1967). We should note in this regard that
Wood (1967) points out that the relative rates of photosynthesis
and dissolved organic uptake is in favor of the uptake when light
available is low. Then such possible heterotrophic mechanisms for
use of abundant natural and waste organics in estuaries become
-------
V.
-------
1. Painter, 1959
COMPOSITION OF WHOLE SEWAGE
Consti tuent
Concentration
Sample 2
in Whole Sewage (p.p.
m. carbon)
Sample 3
In
Solution
In
Suspension
TOTAL
In
Solution
In
Suspension
TOTAL
Carbohydrates - total
21
12
33
40
15
55
Amino acids - free
2
0
2
5
0
5
- bound
6
19.5
25.5
8
23
31
Higher fatty acids
0
74
74
0
71
71
Soluble acids
28.5
6.0
34.5
17
4
21
Esters
0
37.2
37.2
0
28.2
28.2
Anionic surface-active
agents
12
5
17
11
3
14
Amino sugars
0
0.9
0.9
0
0.5
0.5
Amide
0
1.2
1.2
0
1.5
1.5
Creatini ne
2.7
0
2.7
3.5
0
3.5
Total - by analysis
82
218
300
106
205
311
- by addition
72.2
155.8
228
84.5
146.2
230.7
Proportion accounted for,
% 88.0
71.4
76.0
79.7
71.3
-------
1. Painter, 1959
COMPOSITION OF SUSPENDED SOLIDS FROM SEWAGE
(Figures in brackets are the ratios of hexose to pentose)
Concentration,-Expressed as Carbon of Total Carbon, %
Settled
Soli ds , A
Centrifuqed Solids, B
Candle-filtered
Solids, C
Mean of
3
Mean of 3
Constituent Determinations
RANGE
Determinations
RANGE
Sample 2
Sample 3
Carbohydrates succes
sively extracted by
EtOH
1.9 (5.4)
1.5- 2.7
0.4 (1.4)
0 - 0.7
1.5 (1.5)
0.5 (1.4)
HC10„
3.4 (2.2)
1.7- 4.5
1.4 (1.5)
0.6- 2.2
2.1 (1.4)
2.8 (1.5)
HC1
2.9 2.0)
2.4- 3.3
1.6 (3.3)
1.2- 2.5
2.1 (3.5)
1.0 (5.0)
HjSO^
0.7 (2.5)
0.2- 1.6
0.3 (3.8)
0.1- 0.8
0.2 (3.0)
0.6 (5.0)
TOTAL
8.9 (2.6)
6.8-10.9
3.7 (2.1)
2.5- 4.8
5.9 (2.0)
4.0 (2.1)
Amino Acids -
Combined
9.5
7.3-11.5
9.9
8.2-11.8
17.1
13.0
Acids - insoluble
25.5
11.5-35
31.9
25.0-38.6
33.8
35.8
- soluble
2.0
1.4- 2.4
3.2
2.5- 4.0
1.7
1.9
Esters
15.8
11.5-20.8
13.4
12.2-14.0
9.6
10.6
Anionic surface-
active agents
1.3
0.5- 2.3
1.4
0.8- 1.8
3.2
1.8
Amino sugars
0.3
0.3- 0.3
0.2
0.1- 0.4
1.2
0.4
Total accounted for
63.3
45 -74.6
63.7
57.2-71.3
72.2
68.4
4>
-------
1. Painter, 1959
INDIVIDUAL SUGARS PRESENT IN FILTERED SEWAGE AND HYDROLYSED SUSPENDED SOLIDS
-p»
Sugar
Hydrolysed
Settled Solids
(A)
Hydrolysed
Centrifuged Solids
(B)
Hydrolysed Candle-
Filtered Solids
(C)
Candle
Sample 1
Filtrate
Sample 2
Glucose
+++
+++
+++
51
16
Galactose
++
+
+
9
<3
Mannose
Trace
Trace
-
-
-
Lactose
-
-
-
13
17
Sucrose
-
-
-
16
63
Maitose
Trace
-
-
-
Arabinose
++
+
Trace
+
+
Xylose
+
+
+
+
+
Ribose
-
Trace
+
-
-
Rhamnose
+
+
++
-
-
Fucose
-
-
Trace
-
-
Fructose
-
-
-
++
+
Total Anthrone
reacting
89
96
Note: The symbols give only a very rough indication of the proportion present. Numerical
values under "candle filtrate" are percentages of anthrone-reacting sugars pipetted on to
-------
2. Hunter, 1965
ANALYTICAL METHODS FOR DETERMINATION OF ORGANIC COMPONENTS OF WASTEWATER
Component
Source of Method
Remarks
Particulate fraction:
Separation into groups
Total grease:
Total acid-free grease
Phospholipids
Total unsaponifiable
matter
Constituents of unsaponifi-
able matter
Cholesterol
Total glyceride fatty acids
Total free fatty acids
Polyunsaturated fatty acids
Monosaturated fatty acids
Saturated fatty acids
Individual saturated fatty
acids
Phenols
Detergents
Balmat
Scott
Bloor
Association of Official
Agricultural Chemists
Rosen and Middleton
Brown et al.
Association of Official
Agribultural Chemists
Scott
Hausen and Wiese
Mueller
Calculation
Mueller
Faust and Aly
Kramer and Kroner
Includes linoleic, linolenic
and arachidonic acids
Oleic acid
ABS
-------
2. Hunter, 1965 (Cont.)
ANALYTICAL METHODS FOR DETERMINATION OF ORGANIC COMPONENTS OF WASTEWATER
•i*
o>
Component
Source of Method
Remarks
Miscellaneous alcohol-
soluble matter:
Hexose
Tannins
Nitrogenous matter
Amino acids
Carbohydrates and lignin
Pecti n
Hemicellulose
Cellulose
Lignin
Alcohol-insoluble nitrogenous
matter
Neish
Standard Methods
McKensie and Wallace
Rosen
Breston
Breston
Norman and Jenkins
Norman and Jenkins
Same as for alcohol -
soluble nitrogenous matter
Alcohol-soluble matter
prepared for analysis by
24-hour reflux with 6-N HC1,
evaporation, and removal of
NH,.
Soluble Fraction
Ethyl-ether-soluble group
Braus et al.
Separated into acids, bases,
neutrals, and amphoterics;
acids corrected for deter-
gents, neutrals corrected for
cholesterol
-------
2. Hunter, 1965 (Cont.)
ANALYTICAL METHODS FOR DETERMINATION OF ORGANIC COMPONENTS OF WASTEWATER
Component
Source of Method
Remarks
Ethyl-ether-soluble group (cont.
Individual acids
Detergents
Phenols
Cholesterol
Indole and skatole
Volatile acids
Individual volatile acids
Ether-insoluble compounds:
Hexose
Pentose
Total amino acids
Creati ne-creati ni ne
Uric acid
)
Mueller et al
Kramer and Kroner
Faust and Aly
Brown et al.
Rudolfs and Ingols
Heukelekian and Kaplovsky
Manganelli and Brofazi
Neish
Mejbaum as modified by
Albaum and Umbreit
Rosen
Bonses and Toussky
Hawk, Oser, and Summerson
After acid hydrolysis by
method of Cummins and
Harris
-------
2. Hunter, 1965
ORGANIC CONSTITUENTS OF THE ALCOHOL-SOLUBLE, ETHER-INSOLUBLE MATTER AS
PERCENT OF FRACTION TOTAL SOLIDS
Organic
Constituent
Winter-Spring, 1959
Settleable Supracolloidal Colloidal
Fraction Fraction Fraction
Fall-Winter, 1959-60
Settleable Supracolloidal Colloidal
Fraction Fraction Fraction
Amino acids
Sugars
Tannins
Undected*
18.5
4.6
8.6
68.3
12.0
5.5
3.6
78.9
32.0
4.9
8.4
54.7
15.1
4.1
8.0
72.8
6.1
7.0
3.2
83.7
41.5
8.0
11.8
38.7
-------
2. Hunter, 1965
CONTRIBUTION OF THE NON-NITROGENEOUS, ALCOHOL-INSOLUBLE MATTER
(CARBOHYDRATES AND LIGNIN) TO WHOLE SEWAGE
Winter-Spring, 1959 Fall-Winter, 1959-60
Organic Settleable Supracolloidal Colloidal Settleable Supracolloidal Colloidal
Constituent Fraction Fraction Fraction Fraction Fraction Fraction
(mg/1) (mg/1) (mg/1) (mg/1) (mg/1) (mg/1)
Pectin 1.48 2.16^ 1.35 1.30 1.32 1.35
Hemicellulose 3.53 4.32 1.33 3.21 5.36 0.94
Cellulose 11.50 3.15 2.43 21.58 2.05 2.34
Lignin 1.54 0.97 0.98 1.66 0.58 1.20
-------
2. Hunter, 1965
CONTRIBUTION OF THE PARTICULATE FRACTIONS TO WHOLE SEWAGE
CJV
O
Winter-Spring, 1959 Fall-Winter, 1959-60
Settleable Supracolloidal Colloidal Settleable Supracolloidal Colloidal
Fraction Fraction Fraction Fraction Fraction Fraction
Component (mg/1) (mg/1) (mg/1) (mg/1) (mg/1) (mg/1)
Total grease 11.70
Alcohol-soluble
matter* 4.62
Amino acids
Alcohol-soluble 1.05
Alcohol-insoluble 7.54
Carbohydrates and
lignin 18.05
Total organic
matter 43.01
Volatile solids 52.25
9.57
2.01
0.28
12.56
10.60
35.02
41.29
5.55
1.40
0.66
4.71
6.09
18.41
20.64
11.25
4.93
0.87
11.54
27.75
56.34
63.89
8.65
1.83
0.12
12.14
9.31
32.05
36.86
6.06
0.70
0.49
4.27
5.83
17.35
18.79
-------
2. Hunter, 1959
ORGANIC CONSTITUENTS OF SOLUBLE FRACTIONS
Winter-Spring, 1959
Fall-Winter, 1959-60
Constituent
mg/11
Percentt
mg/11
Percentt
Ether-soluble — I
Acidst 22.56
Bases 3.24
Amphoterics 4.80
Neutrals§ 13.59
Ether-soluble - II
Detergents (ABS) 3.94
Phenols 0.12
Cholesterol 0.03
Volatile acids 0.34
Ether-insoluble
Uric acid 0.33
Creatine-creatinine 0.20
Amino acids 9.05
Hexoses 9.77
Pentoses 0.77
Sum 68.74
Volatile solids 72.19
9.25
1.33
1.97
5.57
1.62
0.05
0.01
0.14
0.13
0.08
3.71
4.00
0.31
28.15
29.60
33.95
3.55
7.17
17.31
4.02
0.10
0.05
0.31
0.34
0.17
9.01
8.65
0.66
85.29
87.86
11.91
1.25
2.51
6.07
1.41
0.03
0.02
0.11
0.12
0.06
3.16
3.03
0.23
29.91
30.81
~Constituent concentration in original sewage.
+As percent of soluble fraction total solids.
±Corrected for detergent and phenol content.
-------
2. Hunter, 1959
CONTRIBUTION OF THE ALCOHOL, ETHER-SOLUBLE MATTER S
(TOTAL GREASE) TO WHOLE SEWAGE
Winter-Spring, 1959 Fall-Winter, 1959-60
Organic Settleable Supracolloidal Colloidal Settleable Supracolloidal Colloidal
Constituent Fraction Fraction Fraction Fraction Fraction Fraction
(mg/1) (mg/1) (mg/1) (mg/1) (mg/1) (mg/1)
Free fatty acids
Unsaturated 0.18
Saturated 0.71
Phenols
Detergents
0.004
0.08
Glyceride fatty acids
Unsaturated 1.13
Saturated 5.33
Phospholipids 0.00
Unsaponifiables 2.99
Sum 10.424
Total grease 11.70
0.24
1.40
0.002
0.14
0.88
3.60
0.02
2.16
8.442
9.57
0.20
1.28
0.002
0.10
0.24
1.48
0.04
1.86
5.202
5.55
0.17
0.97
0.005
0.11
0.94
5.48
0.00
2.57
10.245
11.25
0.21
1.45
0.001
0.13
0.71
3.40
0.02
1.53
7.451
8.65
0.11
1.71
0.001
0.09
0.25
1.41
0.03
1.88
5.48
-------
3. Heukelekian, 1956
CONCENTRATION OF MINERAL CONSTITUENTS OF SEWAGE FRACTIONS
Sewage Fractions (ppm in raw sewage)
Element
Settleable
Supracolloidal
Colloidal
Dissolved
Sum of Frac
CI
20.0
20.1
Si
3.33
0.416
0.11
0.07
3.93
Fe
0.348
0.105
0.168
0.149
0.770
A1
0.075
0.035
0.015
0.007
0.132
Ca
0.512
0.300
0.857
8.15
9.82
Mg
0.415
0.24
0.19
9.46
10.31
K
0.20
0.19
0.10
5.43
5.92
Na
0.18
0.10
0.16
22.8
23.2
Mn
0.12
0.007
0.015
0.33
0.47
Cu
0.113
0.037
0.082
1.33
1.56
Zn
0.086
0.059
0.214
<0.04
0.359
Pb
0.30
0.067
0.11
<0.05
0.48
S
0.046
0.12
0.18
10.0
10.3
P
0.55
0.99
0.57
4.45
6.56
Sum of elements
6.28
2.67
2.77
82.3
93.8
Mineral weight*
6.61
2.77
2.78
83.2
95.3
Recovery (percent)!-95.1
96.3
99.9
99.0
—
~Fixed solids by a separate determination and calculated in terms of the total elemental
content.
tCalculated from the sum of individual determinations and separate total fixed solids de-
terminations.
in
-------
54
4. Painter, 1958
CONCENTRATION OF SOME INORGANIC CONSTITUENTS IN
TWO 24 HOUR COMPOSITE SAMPLES OF SETTLED DOMESTIC SEWAGE
Concentration (p.p.m.)
lst-2nd October 30th April - 1st May
Constituent 1956 1957
Chloride
68
85
Sodium
—
100
Potassium
—
20
Calcium
109
109
Magnesium
3.5
6.5
Iron
2.1
0.8
Copper
0.55
0.2
Nickel
—
0.06
Zinc
0.75
0.65
Chromium
—
0.18
Manganese
—
0.05
Cadmium
—
nil
Lead
. •>
-------
5. Vallentyne, 1957
SESTON (freshwater and marine)
Free: aphanicin, aphanin (=myxoxanthin), arginine, biotin(?).
3-carotene, choline, cystine, flavacin, fructose,
glucose, hentriacontane (?), histidine, lysine, maltose
monomethylamine, niacin, sucrose, thiamin, trimethyl-
amine, tryptophan, tyrosine, vitamin A, vitamins D,
vitamins B12.
In hydrolysates:
Sugars: galactose, glucose, rhamnose, xylose.
Amino acids: a-alanine, arginine, aspartic acid,
glutamic acid, glycine, histidine, hydroxyproline,
leucine, phenylalanine, proline, tryptophan,
tyrosine, valine.
Other compounds: aphanizophyll (=myxoxanthophyll?),
¦astacene, cetyl alcohol, cholesterol (?), glucuronic
acid, glycerol, lutein, peridinin.
DISSOLVED ORGANIC MATTER (freshwater and marine)
Free: biotin, dehydroascorbic acid, glucose, niacin (?),
sucrose, thiamin, vitamins Bi2.
In hydrolysates: a-alanine, aspartic acid, cystine, glutamic
acid, glycine, histidine, tryptophan, tryosine.
AQUATIC SEDIMENTS (freshwater and marine)
Free:
Sugars: arabinose, fructose, fucose, galactose, glucose,
maltose, ribose, sucrose, xylose.
Amino acids: a-alanine, glutamic acid.
Carotenoids: a-carotene, B-carotene, flavorhodin (?),
leprotene.(?), myxoxanthin (?), rhodopurpurin (?),
rhodoviolascin, torulene (?).
Other compounds: acetic acid, biotin, n-butyric acid,
cellulose, formic acid, pentatriacontane, B-sitosterol,
thiamin (?), trimethyl amine, tritriacontane, vitamins B12.
In hydrolysates:
Sugars: arabinose, fructose (?), fucose, galactose, glucose
mannose, rhamnose, ribose, xylose.
Amino acids: a-alanine, arginine, aspartic acid, cystine,
glutamic acid, glycine, histidine, isoleucine, leucine,
lysine, serine, tryosine, valine.
Carotenoids: antheraxanthin (?), fucoxanthin (?), petalox-
-------
56
5. Vallentyne, 1957 (Cont.)
In hydrolysates (cont.):
Other compounds: adenine, arachidic acid, behenic acid,
caproic acid, caprylic acid, cerotic acid, cytosine,
galacturonic acid, guanine, heptacosanoic acid, hepta-
cosanol, heptoic acid, montanic acid, uracil.
SEWAGE AND ACTIVATED SLUDGE
Free: acetic acid, biotln, n-butyric acid, folic acid (?),
indole (?), niacin (?), pantothenic acid (?),
propionic acid, pyridoxine {?), riboflavin (?),
skatole (?), thiamin, tryptophan, tyrosine, n-valeric
acid (?), vitamins B12.
TERRESTRIAL SOILS
Free:
Sugars: no free sugars identified.
Amino acids: a-alanine, y-aminobutyric acid, arginine,
asparagine, aspartic acid, glutamic acid, glutamine,
glutamine, glycine, leucine and/or isoleucine, lysine,
serine, threonine, valine.
Other acids: acetic acid, acrylic acid, p-aminobenzoic
acid, 3,5-cresotic acid, ct-crotonic acid, cyanuric acid,
8,9-dihydroxystearic acid, formic acid, a-hydroxystearic
acid, lignoceric acid, oxalic acid, a-picoline-y-carboxylic
-------
6. Murtaugh, 1965
LOWER FATTY ACIDS IN PRIMARY EFFLUENTS
Sample
Source
Total
Organic
Acids
(ye/1)
Formi c
(yg/1)
Acetic
(yg/i)
Propionic
(yg/1)
Individual Acids
Isobutyric Butyric
(yg/i) (yg/i)
Isovaleric
(yg/1)
Valeric
(yg/1)
Caproi c
(yq/D
Portion
of Organic
Acids*
(%)
PLANT A
460
587
12,000
3,550
428
1,540
541
379
135
64
530
105
8,350
3,800
370
647
294
180
321
40
PLANT B
463
155
7,500
1,500
209
260
174
77
61
34
163
46
1,700
237
114
112
122
24
16
23
PLANT C
161
148
145
16
12
23
125
4.7
15
4.7
240
106
605
54
12
17
84
3.7
36
6.0
~Based on ye/1.
cn
-------
6. Murtaugh, 1965
LOWER FATTY ACIDS IN SECONDARY EFFLUENTS
in
oo
Total
Organic
Individual Acids
Portion
of Organic
Sample
Acids
Formi c
Aceti c
Propionic
Isobutyric Butyric
Isovaleric
Valeric
Caproic
Acids*
Source
(ye/1)
(yg/l)
(yg/1)
(yg/l)
(ug/1) (yg/l)
(yg/l)
(yg/l)
(yg/l)
(%)
PLANT
A
81
127
187
68
143
112
524
20
--
19
101
66
156
30
90
69
120
40
420
11
99
144
172
8.6
51
111
195
16
--
10
96
85
243
22
5.7
38
76
5.3
26
8.2
84
124
192
10
29
39
102
14
18
10
PLANT
B
71
58
122
15
8.3
11
14
2.5
11
5.7
99
77
100
6.6
2.8
4.4
3.0
0.8
14
3.8
115
87
115
6.5
3.8
5.4
3.5
1.8
28
3.7
PLANT
C
90
51
25
1.2
4.2
2.6
4.0
0.8
9.6
1.9
90
147
105
1.8
3.9
1.3
1.8
0.8
23
5.8
75
89
157
5.1
0.2
1.6
1.3
0.6
28
6.6
PLANT
D
79
66
68
2.4
0.9
1.3
0.8
0.7
30
3.7
102
68
51
1.6
1.3
1.9
1.1
1.4
15
2.4
-------
6. Murtaugh, 1965
LOWER FATTY ACIDS IN RIVER WATER
Sample
Source*
Total
Organic
Acids
(ye/1)
Formic
(yg/U
Acetic
(yg/1)
Propioni c
(yg/1)
Individual Acids
Isobutyric Butyric
(yg/D (yg/1)
Isovaleric
(yg/1)
Valeri c
(yg/D
Caoroi c
(yg/D
Portion
of Organic
Acidst
(%)
Ohio, up
34.9
24
72
0.1
0.2
0.2
0.2
0.2
3.2
5.1
Ohio, up
13.0
39
15
0.4
0.2
0.2
0.3
0.1
0.8
8.6
Ohio, down 14.8
31
13
0.4
0.3
0.2
0.3
0.1
2.0
6.1
Ohio, up
31.1
12
13
0.7
0.3
0.2
0.2
0.3
6.2
2.2
Ohio, down 28.7
17
13
0.3
0.2
0.1
0.1
0.1
0.3
1.8
Little
Mi ami, i
up 25.2
10
12
0.4
0.2
0.2
0.2
0.1
0.3
1.7
Little
Mi ami,
down
18.4
11
6
0.5
1.3
0.4
1.7
0.2
0.9
2.1
Tanners
Creek
22.3
19
25
0.8
0.5
0.3
0.2
*Up and down refer to upstream and downstream from a municipality.
tBased on ye/1.
0.3
1.7
4.0
cn
-------
7. Teletzke, 1967
AMINO ACIDS FOUND IN RAW AND OXIDIZED SLUDGES
o
Raw
Concentration in Sludge Oxidized at Given Temperature
175°C
200°C
225°C
250c
C
(mg/1
Free*
Total**
Free Total
Free Total
Free
Total
total
aa
aa
aa aa
aa aa
aa
aa
Amino Acids
aa N)
(mg/1)
(mg/1)
(mg/1) (mg/1)
(mg/1) (mg/1)
(mg/1)
(mg/1)
Aspartic
97.6
9.5
44.7
1.5
5.1
Trace
1.8
None
None
Glutamic
250.0
82.8
254.8
56.8
78.2
9.0
15.3
None
None
Serine
87.5
8.3
47.7
Trace
Trace
None
None
None
None
Glycine
112.0
47.0
108.8
14.0
32.0
4.3
10.3
3.3
3.2
Threonine
88.4
None
43.2
None
6.3
None
None
None
None
Alanine
277.0
97.3
206.2
31.0
46.7
2.6
6.8
None
None
3 Alanine
None
20.5
30.6
23.6
28.2
25.0
30.0
10.0
10.5
Argini ne
90.5
None
None
None
None
None
None
None
None
Tyrosine
None
None
None
None
None
None
None
None
None
Histidine
None
None
None
None
None
None
None
None
None
Vali ne
85.2
5.9
58.8
2.8
11.8
1.2
1.8
None
None
Methionine
148.2
2.3
66.5
4.6
None
None
None
None
None
Isoleuci ne
51.6
9.8
57.3
7.9
9.6
None
None
None
None
Leucine
91.4
9.4
52.5
5.1
7.1
None
None
None
None
Proline
40.8
6.1
40.2
Trace
Trace
None
None
None
None
y Amino butyric None
5.4
14.6
8.4
17.1
5.0
10.8
1.2
7.3
Unknown
11.5
2.5
13.9
2.7
4.3
1.6
2.0
None
None
Total
1,432
307
1,040
158
246
49
79
14.5
21
*Free aa = free amino acid as determined on the unaltered sample.
-------
a. curt, mi
stoma HjO [m ru/i>*
S1U
Id.
cut*
Or? tit
tr*
Cr-»
l/«
Kit
ftl«
As?
«>/
kf
*)•
«ft*
111
T*ir
r»*
I to
Lrj
Jrp*
T«nw iti
T«!1o» I
Ttllor I|
U J»1U
II
10 1 to
» 7
ts e
16.7
11. 9
113 2
77 I
Iftft 2
133 «
43 5
ft 9
*i 9
«2 ft
31 2
4 8
29 ft
tt e
• l»tf c Ulp
it
10 I 66
7 4
74 7
70 *
33 7
37 2
141 3
83 <
tu 0
213 ft
ftS 1
19 0
1 9
19 3
39 I
9 ft
17 9
9 I
10 9
1 8
¦-ft
t:?il 9qo i ioio s
by
32 0
118 1
73
3
63 2
7ft 4
25 3
«5 7
10 3
41 6
34 S
42 0
-
71
5
41 2
107 0
55 4
60 0
52
34
27 0
<7 7
*
-
-
•
•
-
.
•
•
12 9
-
-
-
»
-
•
•
.
15.7
11 8
•
-
•
-
-
-
29
3
10 5
9 0
2 1
-
.
3
H 1
2 0
238« 4
3098
4
208ft 0
297ft 3
1977 9
2743 8
781
2087 6
2281 3
2ft 79 0
* tt
»
13 t 69
la-
in 4
411 2
149 1
173 8
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235 8
738 &
e?9 o
351 ft
88 4
22 4
125 7
*35 «
5? 9
;« i
74 3
<9 7
11 9
9 1
4010 0
CT\
-------
9. Hume, 1962
ORIGINAL HYPERION EFFLUENT AND SEA WATER CHARACTERISTICS
cr»
ro
To Sept. 1957
Component
Characteristics Sea Water
CI = 18.55%
(mg/1)
1-Mile Outfall 265 mgd — High Rate
Activated Sludge Effluent and
Elutriation Overflow
mg/1
lb/day
Hardness (as CaC03)
__
212
469,000
Alkalinity (as CaC03)
—
272
602,000
Ca
389
50
111 ,000
Mg
1,262
23
51,000
Na
10,293
214
473,000
K
376
16
35,000
S0.»
2,597
148
327,000
CI
18,550
234
518,000
A1
0-.02
0.04
88
As
0.003-0.03
0.01
22
Cd
0.00003-0.00001
0.05
110
Cr (hexavelent)
—
0.10
220
Cu
0.001-0.025
0.20
440
Fe
0.001-0.06
1.3
2,880
Mn
0.001-0.01
0.04
88
Ni
0.0001-0.006
0.35
770
Pb
0.003-0.005
0.08
180
Zn
0.008-0.021
0.35
-------
9. Hume, 1962 (Cont.)
ORIGINAL HYPERION EFFLUENT AND SEA WATER CHARACTERISTICS
To Sept. 1957
1-Mile Outfall 265 mgd -- High Rate
Characteristics Sea Water
Activated Sludge Effluent and
Component
CI = 18.55%
Elutriation Overflow
(tig/i)
mg/1 lb/day
B
5-25
1.0 2,210
F
1.3-1.4
1.5 3,320
Si02
0.01-6
20 44,000
Suspended solids
--
165 365,000
Volatile SS
--
100 220,000
BOD
--
80 177,000
Oil and grease
--
1-10 2,210-22,100
Detergent (ABS)
0
7-8 15,500-17,700
Phenol
0.02 44
Cyani de
--
0.09 200
Sulfide (dissolved)
--
0.0-0.1 0-220
Total nitrogen
0.03-0.9
40-50 88,500-111,000
Phosphate-phosphorus
0.001-0.06
8 17,700
Vitamin Bi2
2 x 10~7-20 x 10~7
5 x 10"3 11.06
o%
-------
9. Hume, 1962
FUTURE HYPERION EFFLUENT CHARACTERISTICS
cn
Future (1960)
1-Mile Outfall
, 120 mgd
7-Mile
Outfall, 5 mgd
5-Mile Outfall,
140 mgd
Component
Standard Rate
Activated
Digested Sludge
Primary Effluent
Sludge Effluent
mg/1
lb/day
mg/1
lb/day
mg/1
lb/day
Hardness
212
212,000
212
9,000
212
248,000
Alkalinity
272
272,000
272
12,000
272
318,000
Ca
50
50,000
50
3,000
50
58,000
Mg
23
23,000
23
1,000
23
27,000
Na
214
214,000
214
9,000
214
250,000
K
16
16,000
16
300
16
18,700
SO-
148
148,000
148
6,000
148
173,000
CI
234
234,000
234
10,000
234
274,000
A1
0.04
40
0.04
1
0.04
47
As
0.01
10
0.01
<1
0.01
12
Cd
0.05
50
0.05
2
0.05
58
Cr (hexavalent)
0.10
100
0.10
3
0.10
117
Cu
0.20
200
0.20
6
0.20
234
Fe
1.3
1,300
1.3
60
1.3
1,520
Mn
0.04
40
0.04
1
0.04
47
Ni
0.35
350
0.35
10
0.35
410
Pb
0.08
80
0.08
6
0.08
94
Zn
0.35
350
0.35
10
0.35
-------
9. Hume, 1962 (Cont.)
FUtURE HYPERION EFFLUENT CHARACTERISTICS
Future
(1960)
1-Mile
Outfall, 120 mgd
7-Mile Outfall, 5 mgd
5-Mile
Outfall, 140 mgd
Component
Standard Rate-Activated
Digested Sludge
Primary Effluent
Sludge Efflubht
mg/1
1b/day
mg/1
lb/day
mg/1
lb/day
B
1.0
1,000
1.0
40
1.0
1,170
F
1.5
1,500
1.5
60
1.5
1 ,760
Si02
20
20,000
20
600
20
23,400
Suspended solids
25
25,000
7,000
367,000
225
263,000
Volatile solids
15
15,000
3,500
183,000
175
204,000
BOD
12
12,000
4,000
210,000
200
234,000
Oil & grease
1-5
1,000-5,000
-
-
10-20
11 ,700-23,400
Detergent
2-7
2,000-7,000
-
-
8-10
9,300-11 ,700
Phenol
<0.005
<5
-
-
0.03
35
Cyanide
0.08
80
-
-
0.10
117
Sulfide
0.0
0
-
-
0.5
584
Total nitrogen
40-50
40,000-50,000
175
7,300
40-50
46,700-58,400
Phosphate
8
8,000
245
10,200
8
9,300
Vitamin B12
1 X 10"
3 1.00 150 x 10 3
6.26
'o
X
CO
3 3.51
-------
66
10. Bargman and Parkhurst, 1969
Wastewater constituents discharged to the ocean from Hyperion
(340 mgd) and Whites Point (360 mgd). Tributary population -
7 million. (For the year 1968)
Consti tuent Tons/Day
Dissolved Solids 3,600
Chloride (CI)* 1,150
Sodium (Na)* 880
Sulfate (S04) 610
Suspended Solids (including
digested sludge) 565
BOD 560
Total Nitrogen (N) 165
Phosphate (PO^) 100
Grease 90
Potassium (K) 82
Thiosulfate (S) 50
Detergents 21
Phenols 9
Iron (Fe) 7
Fluoride (F) 5
Boron (B) 4.4
Zinc (Zn) 2.4
Chromium, Total (CR) 1.3
Copper (Cu) 1.0
*Does not include individual direct discharges of oil field
brine to ocean.
-------
10. Bargman and P.arkhurst, 1969 (Cont.)
67
Wastewater constituents discharged to the ocean from Hyperion
(340 mgd) and Whites Point (.360 mgd). Tributary population -
7 million. (Forthe year 1968)
Constituent
Pounds/Day
Nickel (Ni)
1,125
Cyanide (CN)
930
Lead (P.B)
730
Manganese (Mn)
400
Cadmium (Cd)
270
Arsenic (As)
100
Selenium (SE)*
55
Hexavalent .Chromium (CR+^)
30
Barium (,BA)*
0
Silver (AG)*
0
~Determined for Los Angeles City only; -not reported for County
-------
CT\
CD
11. Thompson, 1964
SPECTROGRAPHS ANALYSIS FOR METALS CONTENT OF AIR-DRIED SEWAGE SLUDGE
(As percent of air-dried sludge)
Okla.Clty Okla.Clty
Nichols Northslde Northside Okla.Clty Broken Norman Norman
Elements Hills1 No. I2 No. 22 Southslde3 Bow1* Idabel* No. I6 No. 2s Holdenvllle7 Hugo1 Lawton1 Enid*
MAJOR
Aluminum
Calcium
Iron
Magnesium
Silicon
Titanum
INTERMEDIATE
Barium
Copper
Manganese
Sodium
Nickel
Tin
Vanadium
Zinc
Silver
Zirconium
Major
Major
Major
Major
Major
Major
Major
Major
Ml nor
Major
Major
Major
Major
Major
Major
Major
1.30
Major
Mi nor
3.00
1.00
Minor
M1 nor
Major
2.00
2.00
2.00
1.30
2.00
2.00
1.50
1.50
2.00
2.00
2.00
2.00
1.00
1.50
1.00
1.50
1.00
1.00
1.30
1.30
0.10
0.50
1.00
1.00
Major
Major
Major
Minor
Major
Major
Major
Major
Minor
Major
Major
Major
1.50-2.00
1.50-2.00
1.50-2.00
1.00-1.50
1.50-2.00
1.50-2.00
1.50-2.00
1.50-2.00
0.10
1.00-2.00
0.50
0.70
0.30
0.30
0.30
0.30
0.30
0.50
0.70
0.10
0.01
0.10
0.10
0.50
0.50
0.30
0.30
0.60
0.10
0.08
0.20
0.20
0.10
0.10
0.10-0.20
0.30
0.10+
0.10+
0.10+
0.10
0.07
0.09
0.10
0.10
0.01
0.10
0.05
0.10
0.05
0.07
0.05
1.00
0.10
0.10
1.00
1.00
0.20
0.20
1.00
0.70
0.08
0.05
0.05
0.30
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.10
0.10
0.06
0.20
0.05
0.05
0.07
0.06
0.05
0.05
0.10
0.10
1.50
0.10
0.10
0.10
0.07
0.20
1.00
1.00
0.05
0.05
0.03
0.07
0.30
0.50
0.50
0.70
0.50
0.70
0.70
0.70
0.50
0.50
0.30
0.30
0.01
0.01
0.01
0.10
0.01
0.01
0.01
0.01
0.05
0.05
0.01
0.03
0.05
0.05
0.05
0.05
1.00
1.00
0:50
0.10
0.01
0.01
0.03
0.05
(Continued)
Federation»^Vol^S^No^e^Daae0^?3? 1Water Pol1ution Control
-------
11. Thompson, 1964 (Cont.)
SPECTROGRAPHIC ANALYSIS FOR KETALS CONTENT OF AlR-DRIED SEWAGE SLUDGE
(As percent of sir-dried sludge)
Elements
Nichols
Hills1
Okla.Clty
NorthSlde
No. 1*
Okla.Clty
Northslde
No. 2*
Okla.Clty
Southslde'
Broken
1 Bow"
Idabel*
Norman
No. 1*
Norman
No. 2*
Holdenv1lle:
' Hugo1
Lawton1
Enid1
TRACE
8oron
0.01
0.01
o.oi
0.007
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
Beryllium
-
-
-
-
-
-
-
_
.
-
T
T
Chromium
0.06
0.01
0.01
0.10
0.01
0.01
0.01
0.01
T
T
T
0.03
Cobalt
0.01
0.05
0.05
-
T
T
-
-
-
0.005
0.005
0.01
Gel Hum
0.01
0.C1
0.01
T
0.005
0.005
0.005
01005
0.005
0.005
0.003
0.001
Molybdenum
0.007
0.007
0.005
tO.10
0.01
0.01
0.01
0.01
T
T
0.03
0.03
Yttrium
T
T
T
-
T
T
T
T
_
T
T
T
Ytterbium
T
T
T
-
-
-
-
-
-
-
-
T
ASH CONTENT
(X)
45.70
49.30
54.50
47.00
76.00
66.00
59.00
64.00
65.20
63.20
43.01
S4.90
'Primary settling, standard-rate trickling filter, final settling, separate sludge digestion.
*Pr1mary settling, activated sludge, final settling, separate sludge digestion.
'Primary settling, two-stage filtration, final settling, separate sludge digestion.
'Clarlgester, standard-rate high-rate trickling filter, final settling.
'Primary settling, standard-rate trickling filter, separate sludge digestion.
'Blosorptlon, final settling, separate sludge digestion.
7Irahoff tank, standard-rate f1*ed-nozzle filter, final settling.
G\
-------
12. Wilson, 1968
EFFLUENT AND RECHARGED EFFLUENT QUALITY
Concentration in Effluent Concentration in Recharged Effluent
mg/1 mg/1
Calcium
34
82
Magnesium
51
92
Sodium
200
220
Potassium
14
16
Bicarbonate
451
560
Chloride
177
255
Sulfate
160
220
Nitrate
18
72
PH
7.6
7
COD
115
0
BOD
100
0
Total Dissolved Solids
1,807
-------
13. Turekian and Scott, 1967
Suspended Load
Parts
per Million
River and State
mg/1
Cr
Ag
Mo
Ni
Co
Mn
1.
Brazos, Texas
954
100
0.4
11
30
20
690
2.
Colorado, Texas
150
82
0.6
10
40
17
780
3.
Red, Louisiana
436
37
0.3
5
6
7
320
4.
Mississipi, Arkansas
185
150
0.7
18
100
33
2,300
5.
Tombigbee, Alabama
25
220
1.0
22
200
31
5,900
6.
Alabama, Alabama
54
150
4.0
19
100
34
3,700
7.
Chattahoochie, Georgia
71
190
7.0
20
100
35
2,400
8.
Flint, Georgia
12
210
1.0
28
100
39
5,100
9.
Savannah, S. C.
30
460
2.0
35
250
36
4,400
10.
Wateree, S. C.
37
200
1.5
24
100
34
7,000
11.
Pee Dee, South Carolina
188
150
0.4
15
100
23
1,300
12.
Cape Fear, North Carolina
61
130
0.7
16
70
21
1 ,700
13.
Neuse, North Carolina
36
380
4.0
22
70
30
3,000
14.
Roanoke, North Carolina
33
240
4.9
21
100
45
7,900
15.
James, Virginia
41
290
7.0
29
300
60
15,000
16.
Rappahannock, Virginia
28
140
1.0
31
80
46
2,200
17.
Potomac, Virginia
34
170
1.5
23
400
94
7,700
18.
Susquehamma, Pa.
54
290
15.0
32
>1000
>500
12,000
¦"-J
-------
13. Turekian and Scott, 1967 (Cont.)
ro
Suspended Load Parts per Million
River and Country mg/1 Cr Ag Mo Ni Co Mn
Rhone, France
Avignon, June 1966 296 150 0.7 14 60 29 820
Rio Maipo, Chile
Puente Alto, S. of
Santiago, September 1966 41 68 1.0 44 c 40 76 2,400
Shales (Turekian and
-------
Reference ABCDEFGHI
Organic*,
pprn:
BOO 0
COO 0
ABS
Cations,
ppra:
Na+
K+
27
21
30
97
269
-
-
100
5
as
0
-
-
0
0
0
.
0
_
Caw
Mg++
Fe+++
39
37
0.05
28
1
56
17
29
7
17
3
37
Tr
45
25
-
87
29
Anions,
ppn:
CI
13
35
59
53
250
49
150
20
97
NO]
9
-
-
-
-
9
22
0
5
NOj
-
-
-
-
-
-
-
-
.
HCO",
312
35
263
281
347
149
342
268
149
col
0
10
0
0
0
0
0
-
0
14. Neale, 1964
TAP WATER ANALYSES
J
K
L
M
N
0
P
Q
R
S
T
U
V
AVS
MAX
MIN
6
0.5
1
2
6
0
-
-
-
-
27
8
42
4
1.4
0
27
.
2
12
42
0
0
0
0.05
0.04
0.02
4.2
0.04
0.02
0.02
0.02
0
0.01
0.37
4.2
0
33
17
25
8
18
17
14
10
49
269
8
4
2
2
-
-
-
-
2
2
2
1.6
-
2
3
5
1.6
2
0
0
~ >
am
-
-
-
0
0
0
0
-
0
0.1
2
0 .
22
58
53
¦w
.
_
13
20
22
12
108
96
42
108
12
16
7
8
4
-
-
35
5
11
11
30
-
21
16
37
0
"
•
•
~
32
13
16
15
22
22
518
12
17
9
22
6
16
66
518
6
2
4
9
-
0.5
0.1
3.0
0.1
6.2
5.3
0.37
-
2.7
5
9
0
0.3
-
-
-
-
-
0.18
0.03
0.01
0.13
0.31
-
0.03
0.14
0.30
0.01
137
176
181
66
-
-
210
27
46
49
379
-
358
198
379
27
-
0
0
0
-
-
5
1
0
0
0
-
-
0.1
10
0
Continued
—J
-------
—J
•p-
14. Neale, 1964 (Cont.)
TAP WATER ANALYSES
Reference
A
B
C
D
E
r
G
H
I
J
K.
L
H
N
0
P
Q
R
S
T U
V
AVG
MAX
MIN
so;
34
19
21
8
0
58
75
19
291
17
44
47
12
_
84
56
79
56
96
53
56
291
0
SiOj
71
13
30
35
35
-
-
-
11
-
-
-
8
-
-
-
-
-
•
-
-
29
71
11
PO;(Total)
0
2
0
0
3
0
0
0
-
2.5
0
0
0
0.5
3.5
3.8
0.04
0.05
0.03
0.02 -
-
8.1
3.8
0
PO:(Ortho) 0
0.5
0
0
1.5
0
0
0
-
-
0
0
0
-
-
3.3
0
0.01
0.01
0
-
0.3
3.3
0
Other:
-
Hardness
(as CaCOi)
ppm
249
74
210
101
55
120
215
220
337
121
174
164
59
178
71
100
75
150 -
326
158
337
55
Alka.linltv
(as CaCOj)
ppn
255
45
210
230
284
122
280
220
122
112
144
148
54
180
24
38
40
311 -
294
164
311
24
Total
dissolved
solids,ppm
364
161
650
504
917
327
500
265
700
271
317
100
214
185
1130
98
177
140
520 155
344
382
917
98
PH
7.8
8.8
7.7
7.8
7.3
7.2
7.8
-
8.0
-
7.7
7.6
8.3
-
-
9.0
8.8
8.2
8.3
7.8 -
7.4
8.0
9.0
-------
Reference ABCDEFGHI
Organlcs,
ppm
BOO
COO
AOS
10
-
18
Cations,
ppm
Na+
K+
8S
29
-
NHt
22
-
-
Ca++
96
78
62
Mg++
12
16
23
Anions,
PP* .
CI
85
55
121
no!
26
-
-
NOl
-
-
-
hco;
303
209
-
COl
0
0
0
45
10
-
-
-
-
180
384
232
200
-
-
-
-
-
20
15
3
5
-
8
44
45
42
40
58
-
97
16
17
Tr
26
-
30
90
450
165
260
173
197
-
-
-
-
4
2
420
385
110
298
293
398
0
0
0
0
.
0
14. Neale, 1964
SECONDARY - EFFLUENT ANALYSES
0
K
L
M
N
0
P
Q
R
S
T
U
V
AVG
MIN
MAX
10
8
33
9
33
18
19
9
45
-
-
-
-
135
44
158
163
99
79
49
.
78
101
44
163
6
9
2.9
2.4
10.0
10.1
7.2
6.3
4.6
7
9
6.8
2.4
10.1
67
118
99
50
68
63
112
55
124
29
232
11
-
-
-
-
-
-
14
9
11
10
-
12
12
9
20
8
-
-
-
-
-
36
9
21
29
25
-
0
17
0
44
33
68
60
-
-
-
-
64
53
54
109
•
97
66
33
109
17
13
16
•
~
•
•
14
20
22
33
-
22
19
Tr
30
69
143
79
137
77
64
532
52
67
49
124
90
62
143
52
532
11
-
-
-
0.04
3.9
6.2
26
22
0.62
26
-
20
12
0.04 26
2
-
-
-
-
-
0.62
2
0.3
0.26
1.1
-
1.8
1.5
0.26 2
200
219
403
146
-
-
327
212
243
314
428
-
409
296
110
428
-
-
-
0
-
-
0
0
0
0
0
-
.
0
0
0
-0
-------
—
o\
14. Neale, 1954 (Cont.)
SECONDARY - EFFLUENT ANALYSES
Reference
A
B
C
0
E
F
G
H
I
J
K
L
M
N
0
P
Q
R
S
T
U
V
AVG
MIN
KAX
so;
42
57
45
43
20
115
96
70
300
30
75
69
31
_
105
95
91
108
111
99
84
20
300
Si of
80
30
43
57
49
-
53
25
25
-
-
-
22
-
-
-
-
-
-
-
-
-
43
22
80
P0;(Total)41
9
37
33
25
50
29
12
-
10
35
43
21
8
5
29
35
19
20
18
-
29
25
5
50
P0;(0rtho)40
8
34
30
23
32
27
-
-
-
-
-
-
-
-
21.8
33.8
17.9
19
16.9
-
28
25
8
40
Other.
Hardness
(as CaCO,)
ppn
290
259
250
175
175
153
250
230
366
153
224
213
100
218
215
227
411
332
235
100
411
AUalinlty
(as CaCO,)
ppm
248
172
344
316
90
244
240
326
164
180
331
120
268
174
198
257
351
_
335
242
90
351
Total
solids,
ppm
727
477
844
872
1362
730
1041
540
1065
683
566
410
519
410
1302
472
525
597
648
480
492
703
410
1362
Suspended
solids, pp.ii
-
-
-
-
-
-
-
-
-
-
-
-
18
-
-
-
-
-
-
-
-
-
—
-
-
pH
6.5
7.1
7.5
7.8
7.3
7.0
8.0
-
7.0
-
-
-
6.9
.
-
7.6
7.5
7.3
7.8
7.8
-
7.4
7.4
6.5
-------
77
15. Bowen, 1966
ELEMENTARY COMPOSITION OF SOIL SOLUTIONS
AND
RIVER WATERS IN PPM1
Soil Solution2
River Water3
Element
Median
Range
Median
Range
Ag
A1
Ar
As
Au
B
Ba
Be
Br
C(HC0~)
Ca
Cd
CI
Co
Cr
Cs
Cu
4
32
10
0.03-10
<0.001-
0.01
2-7
1-60(-1500)
7-50(-8000)
0.01-0.06
0.00013
0.24
0.6
0.0004
<0.00006
0.013
0.054
0.001
0.021
11
15
0.08
7.8
0.0009
0.00018
0.0002
0.01
0.00001.
0.0035
0.01-
2.5
<0.0004-
0.23
0.01-1
0.009-
0.15
0.0001-
0.001
0.005-
140
6-19
4-120
5-35
<0.006
0.0001-
0.08
0.00005-
0.0002
0.0006-
-------
78
15. Bowen, 1966 (Cont.)
ELEMENTARY COMPOSITION OF SOIL SOLUTIONS
AND
RIVER WATERS IN PPM1
Element
Soil Solution2
Median
Range
River Water3
Median
Range
F
Fe
Ga
Hg
i
K
Li
Mg
Mn
Mo
N (NO"3)
Na
Ni
P
Pb
Ra
Rb
Rn
S
3.5
25
15
0.005
0.1-0.25
(-25)
0.01
1-11(-400)
0.7-100
(-2400)
0.02-2
(-800)
<0.001
2-800
9-30(-3500)
0.001-30
<3-5000
0.09
0.67
<0.001
0.00008
0.002
2.3
0.0011
4.1
0.012
0.000035
0.23
6.3
0.01
0.005
0.005
3.9xlO"10
0.0015
1.7x10"15
3.7
0.01-1.4
1.4-10
0.00007-
0.04
1.5-6
0.00002-
0.13
<0.007
0.01-08
3-25
0.0002-
0.02
0.001-
0.3(-12)
0.0006-
0.12
<0.008
-------
79
15. Bowen, 1966 (Cont.)
ELEMENTARY COMPOSITION OF SOIL SOLUTIONS
AND
RIVER WATERS IN PPM1
Soil Solution2 River Water3
Element Median Range Median Range
Se 0.001-3 <0.02
Si 0.5-12 6.5 2-12
Sn 0.00004
Sr <0.1 0.08 0.003-
0.8
Th 0.00002
Ti «?0.07 0.0086 <0.11
U 0.001 0.00002-
0.05
V 0.001 <0.007
Zn 0.1-0.3 0.01 0.0002-1
Zr 0.0026 0.00005-
0.022
*Many elements vary in abundance in river water seasonally (e.g., Si)
or even from day to day (e.g., Mn). Abnormal ranges are given in
parentheses.
2Swaine (1955), Wiklander (1958), Vinogradov (1959), Fried and
Shapiro (1961), Barber, et al. (1963), Bowen and Cawse (1965).
-------
80
15. Bowen, 1966
THE ELEMENTS IN SEA WATER1
Element Chemical Form ppm
Residence Time Percentage
(years x 1000) Retention
Ag
A1
Ar
As
Au
B
Ba
Be
Bi
Br
C
Ca
Cd
Ce
CI
Co
Cr
Cs
AgCl2-
Ar
As04H2'
AuCl !~-
B(0H)3
Ba++
Br
C03H",
organic C
Ca2+
Cd2+
Cl"
Co2+
Cs+
0.0003
0.01
0.6
0.003
0.000011
4.6
0.03
0.0000006
0.000017
65
28
400
0.00011
0.0004
19000
0.00027
0.00005
0.0005
2100
0.1
560
84
0.15
45
8000
500
6.1
18
0.35
40
0.4
0.00001
140
0.15
0.25
46
0.006
0.00002
0.01
2300
12
0.9
0.05
0.0006
13000
0.001
0.00004
-------
81
15. Bowen, 1966 (Cont.)
THE ELEMENTS IN SEA WATER
Residence Time Percentage
Element Chemical Form ppm (years * 1000) Retention
Cu
Cu2+
0.003
50
0.005
F
F
1.3
0.2
Fe
Fe(OH)3
0.01
0.14
0.000016
Ga
0.00003
1.4
0.0002
Ge
Ge(0HK
0.00007
7
0.004
H
h2o
108000
6850
He
He
0.0000069
20000
0.05
Hf
<0.000008
<0.00024
Hg
HgCl,2"
0.00003
42
0.03
I
I", I03-?
0.06
1.1
In
<<0.02
K
K+
380
11000
1.6
Kr
Kr
0.0025
130
La
0.000012
0.44
0.009
Li
Li +
0.18
20000
0.75
Mg
Mg2+
1350
45000
5.1
Mn
Mn2+
0.002
1.4
0.002
Mo
MoOu2"
0.01
500
0.6
N
Organic N,
NO3-, NHi»+
0.5
2.5
-------
82
15. Bowen, 1966 (Cont.)
THE ELEMENTS IN SEA WATER
Element Chemical Form ppm
Residence Time Percentage
(years x 1000) Retention
Na
Nb
Ne
Ni
0
P
Pa
Pb
Ra
Rb
Rn
S
Sb
Sc
Se
Si
Sn
Sr
Na+
Ne
Ni2+
0H2, 02,
SO,2'
P0,H2'
Pb
2 +
Rb+
Rn
SO,2"
Si(OH) i
Sr
9 +
10500
0.00001
0.00014
0.0054
857000
0.07
2 x 10"9
0.00003
6 x 10"11
0.12
6 x 10"16
885
0.00033
<0.000004
0.00009
3
0.003
8.1
260000
0.3
18
270
350
5.6
8
100
19000
40
0.00004
2
0.005
164
0.006
0.13
0.000002
0.006
0.12
0.1
300
0.15
<0.00002
0.16
0.001
0.1
-------
15. Bowen, 1966 (Cont.)
THE ELEMENTS IN SEA WATER
83
Residence Time Percentage
Elements Chemical Form ppm (Years * 1000) Retention
Ta
<0.0000025
<0.0001
Th
0.00005
0.35
0.0005
Ti
0.001
0.16
0.00002
T1
T1 +
<0.00001
<0.002
U
IKMCOah*"
0.003
500
0.1
V
VO5H32"
0.002
10
0.001
W
WO*2"
0.0001
1
0.006
Xe
Xe
0.000052
300
y
0.0003
7.5
0.0008
Zn
Zn2+
0.01
180
0.01
Zr
0.000022
0.000012
-------
16. Chow, 1968
SCOPE OF ISOTOPE-DILUTION ANALYSIS OF SEAWATER*
CO
-p>
Class
Element
Isotope Pairt
Concentration in
Seawater (yg/kg)
Method Used
I-a. Major constituents
B
10
and
11
4.3 x 103
Volumetri c
of seawater with
C
12
and
13
2.8 x lo"
Gasometri c
unique isotope pairs
Mg
24
and
25
1.294 x 106
Volumetric
Si
28
and
29
3.0 x 103
Colorimetric
S
32
and
33
8.84 x 10s
Gravimetric
CI
35
and
37
1.90 x 107
Volumetric
K
39
and
41
3.90 x 10s
Flame photometric
Ca
42
and
43
4.24 x 10s
Flame photometric
Br
79
and
81
6.7 x to*
Volumetric
Sr
86
and
88
8.1 x io3
Flame photometric
Isotope dilution
I-b. Minor constituents
Li
6
and
7
170
Isotope dilution
of seawater with
Be
9
and
10
0.0006
Spectrographs
unique isotope pairs
Ti
47
and
49
1
Colorimetric
Cr
52
and
53
2
Neutron activation
Fe
56
and
57
8
Colorimetric
Ni
60
and
61
5
Neutron activation
Cu
63
and
65
3
Colorimetric
Zn
66
and
67
5
Neutron activation
Ga
69
and
71
0.03
Colorimetric
Ge
72
and
73
0.06
-------
16. Chow, 1968 (Cont.)
SCOPE OF ISOTOPE-DILUTION ANALYSIS OF SEAWATER*
Concentration in
Class Element Isotope Pair Seawater (ug/kg) Method Used
Se
77
and
80
0.4
Colorimetric
Zr
90
and
91
0.02
Fluorometric
Mo
95
and
97
10
Colorimetric
Ru
99
and
101
No data
-
Ag
107
and
109
0.3
Neutron activation
Sn
117
and
118
0.8
Neutron activation
Te
125
and
128
No data
-
Ba
135
and
138
50
Isotope dilution
Nd
145
and
146
0.003
Neutron activation
Sm
147
and
149
0.0005
Neutron activation
Eu
151
and
153
0.0001
Neutron activation
Gd
155
and
157
0.0007
Neutron activation
Dy
161
and
163
0.0009
Neutron activation
Er
166
and
167
0.0009
Neutron activation
Yb
171
and
172
0.0008
Neutron activation
Hf
178
and
179
<0.008
Neutron activation
W
182
and
183
0.1
Colorimetri c
Os
188
and
189
No data
-
Ir
191
and
193
No data
-
Pt
194
and
195
No data
-
00
-------
16. Chow, 1968 (Corit.)
SCOPE OF ISOTOPE-DILUTION ANALYSIS OF SEAWATER*
00
cn
Concentration in
Class Element Isotope Pairt Seawater (yg/kg) Method Used
Hg 201 and 202
T1 203 and 205
Pb 206 and 208
Th 230 and 232
U 235 and 238
II. Minor constituents V 50 and 51
of seawater with suit- Rb 85 and 87
able isotope pairs Pd 105 and 106
Cd 110 and 111
In 113 and 115
Sb 121 and 123
I 127 and 129
Cs 133 and 135
La 138 and 139
Ce 140 and 142
Lu 175 and 176
Ta 180 and 181
Re 185 and 187
0.1
Col ori metric
0.01
Spectrographic
0.08
Isotope dilution
0.002
Alpha activity
3
Isotope dilution
2
Colorimetric
120
Isotope dilution
No data
-
0.1
Col ori metric
<20
Spectrographic
0.3
Neutron activation
64
Amperometric
0.3
Flame photometric
0.003
Neutron activation
0.001
Neutron activation
0.0002
Neutron activation
<0.002
Neutron activation
No data
-------
16. Chow, 1968 (Cont.)
SCOPE OF ISOTOPE-DILUTION ANALYSIS OF SEAWATER*
Concentration in
Class Element Isotope Pairt Seawater (yg/kg) Method Used
III. Dissolved gases H 1 and 2
in seawater with unique He 3 and 4
isotope pairs N 14 and 15
0 16 and 18
Ne 20 and 21
Ar 38 and 40
Kr 84 and 86
Xe 128 and l;
IV. Mono-isotopic F 19
elements in seawater Na 23
A1 27
P 31
Sc 45
Mn 55
Co 59
As 75
Y 89
Nb (Cb) 93
No data
-
0.007
Isotope dilution
1.55 x iow
Gasometric
6.0 x 103
Volumetric
0.120
Isotope dilution
450
Isotope dilution
0.210
Isotope dilution
0.047
Isotope dilution
1300
Colorimetric
1.8 x 107
-
1
Fluorometric
88
Colorimetric
0.004
Neutron activation
1.9
Neutron activation
0.4
Neutron activation
2.6
Neutron activation
0.001
Neutron activation
0.02
-------
16. Chow, 1968 (Cont.)
SCOPE OF ISOTOPE-DILUTION ANALYSIS OF SEAWATER*
00
00
Concentration in
Class Element Isotope Pairt Seawater (yg/kg) Method Used
Rh
103
No data
-
Pr
141
0.006
Neutron activation
Tb
159
0.001
Neutron activation
Ho
165
0.0002
Neutron activation
Tm
169
0.0002
Neutron activation
Au
197
0.01
Neutron activation
Bi
209
0.02
Spectrograph!" c
*For detailed information, see Gol dberg, Ri 1 ey and Skirrow
-------
17. Young, 1968
OXYGEN UPTAKE, LAG, AND TIMES OF BACTERIAL PEAKS
89
O2 Uptake l_ag Bacterial Peak
Classification Compound (Days) (Days)
Readily degraded Acetone 2 3
Benzaldehyde 0 4
Benzoic acid 0 2
o-Cresol 1 3
Ethanol 0 2
Ethyl acetate 1 2
Hydroquinone 1 3
Maleic acid 1 2
Methanol 1 2
Methyl ethyl ketone 1 3
Oxalic acid 0 2
Acclimation Acrylonitrile 12 12
Aniline 3 5
Ethylene glycol 4 7
Isopropanol 5 7
Monoethanolamine 2 3
Pyridine 9 2
Slightly oxidized tert-Butanol - 3
Diethylene glycol 0 3
Toluene 1 2
Control Seed Blank 0 2
Glucose-glutamic
-------
VO
o
CHAIN FEEDING SUCCESSION
NET OR WEB FEEDING SUCCESSION
Figures 18 and
19:
-------
20. Green (1968)
TROPHIC SPECTRUM OF THE FISH IN LAKE PONTCHARTRAIN, LOUISIANA
(after R. M. Darnel 1)
CONSUMER SPECIES |
FOOD
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VI.
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-------
92
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-------
93
Carritt, Dayton E. , "Recent Developments in Chemistry and Hydro-
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-------
94
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95
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