United States
Environmental Protection
Agency
Environmental
Research Laboratory
Narragansett, Rl 02882
EPA-600/3-78-005
January 1978
Research and Development
Third Annotated Bibilography
on Biological Effects of Metals
in Aquatic Environments
(No. 1293-2246)
Ecological Research Series
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S Environmental
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This document is available to the public through the National Technicallnforma-
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EPA-600j3-78-00S
January 1978
THIRD ANNOTATED BIBLIOGRAPHY ON BIOLOGICAL EFFECTS OF
METALS IN AQUATIC ENVIRONMENTS
[No. 1293-2246]
by
Ronald Eisler, Daniel J. O'Neill, Jr.
and Glen W. Thompson
Office of Health and Ecological Effects
Environmental Research Laboratory
Narragansett, Rhode Island 02882
ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
NARRAGANSETT, RHODE ISLAND 02882
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DISCLAIMER
This repor~ has been reviewed by the Environmental Research
Laboratory-Narragansett: U.S. Environmental Protection Agency, and
approved for publication. Mention of trade names or commerical
products does not constitute endorsement or recommendation for use.
ii
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FOREWORD
The Environmental Research Laboratory of the U.S. Environmental
Protection Agency is located on the shore of Narragansett Bay, Rhode
Island. In order to assure the protection of marine resources, the
laboratory is charged with providing a scientifically sound basis for
Agency decisions on the environmental safety of various uses of marine
systems. To a great extent, this requires research on the tolerance
of marine organisms and their life stages as well as of ecosystems to
many forms of pollution stress. In addition, a knowledge of pollutant
transport and fate is needed.
This report lists 954 titles of selected articles from the world
technical literature on the subject of toxicological and physiological
effects of toxic cations and heavy metals to aquatic biota. Each article
is annotated at length, and cross-indexed by metal, by taxon, and by
author in cumulative indices that include the two preceding volumes
in this series. It is part of a continuing effort by this laboratory
to construct a meaningful platform for use in future research in this
area, and for providing a sound data base in updating of existing
water quality criteria for metals in freshwater and marine environ-
ments.
Eric D. Schneider,
Director
iii
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ABSTRACT
Titles of 954 technical articles are listed on the subject of
toxicological, physiological and metabolic effects of stable and radio-
labelled chemical species of metal cations to marine, estuarine and
freshwater flora and fauna. Each reference was annotated and subse-
quently indexed by metal, by taxa, and by author, in cumulative indices
which encompass this volume and the initial volumes in this series
(Eisler, R. 1973. Annotated bibliography on biological effects of
metals in aquatic environments [No. 1-567]. U.S. Envir. Proto Agen.
Rept. R3-73-007: 287 pp; Eisler, R. and M. Wapner. 1975. Second
annotated bibliography on biological effects of metals in aquatic en-
vironments [No. 568-1292]. U.S. Envir. Proto Agen. Rept. 600/3-75-008:
400 pp).
lV
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CONTENTS
Foreword
iii
Abstract
iv
Acknowledgment
vi
I.
Introduction
1
II.
References
2
III.
Index
361
v
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ACKNOWLEDGMENTS
We are obligated to Dr. Eric D. Schneider and Dr. Donald K.
Phelps, Director and Scientific Director, respectively, of the USEPA
Environmental Research Laboratory/Narragansett, for their encouragement
and financial support of this compilation. We are especially grateful
to Ms. Gloria Gaboury for her assistance and cooperation in proofing,
filing, indexing and cross-indexing; to Ms. Patricia Clem for technical
assistance in early phases of this project; to Mss. Denise McNulty,
Patricia Bussiere and Josephine DeVoll for secretarial assistance; and
to Mrs. Janice Steele for final typing. Finally, we owe a special debt
to Ms. Rose Ann Gamache, Librarian at the ERL, and her assistant Ms.
Karen Gardner, for their efforts in procuring the original articles for
consultation through interlibrary loan and other sources.
Vl
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SECTION I
INTRODUCTION
As was true in the two preceding volumes in this series, published as
EPA reports R3-73-007 and 600/3-75-008, respectively, the present
account lists journal articles and reports resulting from laboratory
and field investigations on toxicological, physiological and metabolic
effects of stable and radioactive species of heavy metals and other
cations to aquatic life. Most of the references listed herein were
published within the five year period between 1971 and 1976, but a sub.
stantial minority have been in print for some time and have only
recently become available to us. For this issue we selected articles
which emphasized the following response parameters: survival; growth;
reproduction; behavior, bioaccUID~lation; retention; translocation;
histopathology; baseline data on elemental composition; changes in
exogenous salt content on responses including internal changes in salt
balance of body fluids and tissues; interaction effects of metals and
their salts in combination with other substances; and finally, modify-
ing effects of boitic and abiotic factors on all parameters examined.
As more information becomes available, and future volumes in this
series are produced, it is hoped that contamination standards for each
metal can be established administratively at levels which neither
jeopardize the stability of aquatic ecosystems nor present a public
health hazard via aquatic food chains.
1
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SECTION II
REFERENCES
References are arranged alphabetically by author and then numbered.
Each reference is indexed by metal(s), by author(s) and by taxonomic
group(s) in the index (Section III).
2
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1293.
Aarkrog, A. 1971. Radioecological investigations of plutonium
in an arctic marine environment. Health Physics 20:31-47.
On 21 January 1968, a B-52 bomber from the U.S. Strategic Air
Command crashed on the ice in Bylot Sound 11 km west of Thule Air Base,
Greenland. Ry impact with the ice the chemical explosive in four un-
armed nuclear weapons carried by the aircraft detonated, and some kilo-
grams of plutonium were released to the environment. Most of the con-
tamination was confined within a drop-shaped area of approximately 700
x 150 m stretching southward from point of impact. Bomb debris, wreck-
age from the plane and the surface layer of the contaminated snow in
the drop-shaped area were removed by the U.S. Air Force during the
first few months after the accident and shipped in the autumn to the
Savannah River plant in the United States. During summer of 1968, soil,
water and biota were collected from the vicinity of the accident.
Elevated levels of plutonium, present mainly as insoluble plutonium
oxide particles, were found in the marine environment of Bylot Sound.
Plutonium concentration in sea water increased by a factor of two. In
sea bottom sediments the increase was one order of magnitude and two
orders of magnitude beneath the impact area. Bivalves showed increased
levels up to a distance of 15 km from the crash area. The median level
in bivalves was one order of magnitude above the fall-out background,
and in the crash area it was three orders above. Macoma contained more
plutonium than the other species of bivalves. Crustaceans, polychaetes,
and echinoderms showed median levels about 1000 times the fall-out
background. Fish living near the sea bottom, e.g. the Greenland hali-
but, contained plutonium levels one to two orders of magnitude above
the fall-out background. The other samples: zooplankton, sea plants,
sea birds, seals and walruses did not contain plutonium levels signif-
icantly different from the fall-out background. Plutonium was not
detected with certainty in human urine samples.
1294.
Abbott, N.J., R.B. Moreton, and Y. Pichon. 1975. Electro-
physiological analysis of potassium and sodium movements in
crustacean nervous system. Jour. Exp. BioI. 63:85-115.
Estimates were made on half-times for Na+ and K+ entry and
efflux from extra-axonal space in peripheral nerve and central nervous
connectives of the marine crab Carcinus maenas, and freshwater crayfish
Procambarus clarkii; results were qualitatively similar. Peripheral
nerve showed no evidence for diffusion barriers, K+ entry and efflux
being rapid, and proceeding at comparable rates. In connectives, K+
entry was extremely slow, with a half-time> 100 min, while K+ efflux
was relatively rapid (T~ = 6 min). Na+ movements were less re-
stricted, but entry was more rapid than efflux. Potassium experiments
were compared with behavior of a theoretical model system. Evidence
is presented for diffusional restriction to K+ at connective peri-
3
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neurial layer; this pro~ess involves changes in premeability or acti-
vation of an ion pump in perineurial layer.
1295.
Abdullah, M.I., J.W. Banks, D.L. Miles and K.T. O'Grady. 1976.
Environmental dependence of manganese and zinc in the scales
of Atlantic salmon, Salmo salar (L) and brown trout, Salmo
trutta (L). Freshwater BioI. 6:161-166.
Manganese and Zn concentrations in scales of salmon and trout
from North Wales showed significant dependence on environmental levels.
In Lake Bala, mean dissolved Mn was 23 ug/l and Zn 36 ug/l; Zn and Mn
content of scales of salmon from Lake Bala were 654 and 133 mg/kg
respectively; trout scales averaged 532 Zn and 121 Mn. The River
Downey had 4 ug Mn/l and 62 ug Zn/l; salmon from the Downey had mean
Zn and Mn contents of 1090 and 74 mg/kg, respectively. The upper River
Twymyn had highest dissolved Zn levels at 307 ug/l; for Mn this was 11
ug/l; Twymyn trout scales had means of 2075 mg Zn/kg, and 77 mg Mn/kg.
Another site at River Twymyn contained Mn levels of 4 ug/l and Zn of
116 ug/l; trout scales from this site contained 844 mg Zn/kgand 39 mg
Mn/kg. It is suggested that there is a minimum concentration of zinc in
scales at approximately 20-60 mg/kg, above which there is a direct pro-
portion between environmental and scale concentration.
1296.
Abdullah, M.I., L.G. Royle and A.W. Morris. 1972. Heavy metals
concentration in coastal waters. Nature 235:158-160.
Concentrations of Cu, Pb, Cd and Zn were determined polaro-
graphically in water samples collected from a depth of 5 m at Liverpool
Bay, Cardigan Bay and Bristol Channel. Very high concentrations of Cd
(up to 4.2 ug/l), Pb (up to 5.0 ug/l), zinc (up to 47.6 ug/l) and Cu
(up to 4.7 ug/l) found over wide areas appear to be associated with
industrial and domestic waste. This may have been caused partly by
poor survival of one of the natural agencies of trace metal removal and
control, i.e. phytoplankton and zooplankton, in heavily polluted waters.
1297.
Abraham, M. 1975. The pituitary of Mugil cephalus during adap-
tation to biotopes of different salinities. Aquaculture 5:
199-204.
Epithelial and nervous components of the pituitary of mullet,
a euryhaline fish, were analyzed by histological and electron micro-
scope techniques in specimens taken from freshwater ponds, from the
se~ and from a hypersaline lagoon. Pronounced differences were found
in prolactin secreting cells and neurosecretory axons. Changes in cell
structure in different biotopes were also found in somatotrophs,
4
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gonadotrophs, corticotrophs and lead-cells of the intermediate lobe.
During spawning season, gonadotroph cell region of seawater specimens
is characterized by a large number of both A- and B-type neurosecretory
axons. It is suggested that Mugil breeders find a method of stimulat-
ing synthetic and secretory activity of the gonadotrophs by chlomiphene-
like factors as a means towards achieving gonadal activity in freshwater
specimens.
1298.
Adams, E.S. 1975. Effects of lead and hydrocarbons from snow-
mobile exhaust on brook trout (Salvelinus fontinalis).
Trans. Amer. Fish. Soc. 104:363-373.
Fingerling trout were held in live cages in a Maine pond.
This pond contained contaminants accumulated during the previous winter
when snowmobile operation on the pond was equivalent to one snowlllobile
burning 250 liters of fuel per season on a 0.405 h pond (average depth
of one m). Lead content of water rose from 4.1 ug/l before snowmobil-
ing to 135 ug/l at ice-out; exposed trout contained 9 to 16 times more
lead than controls. Hydrocarbon levels undetectable prior to snow-
mobiling reached 10 ug/l in water and 1 ug/l in exposed fish. Trout
held in aquaria for 3 weeks in melted snow containing different concen-
trations of snowmobile exhaust showed an increase over controls; those
held at the highest concentration (12.5 ug/l Pb in medium) contained
910 ug/kg in fish; controls exhibited 4 ug/l and 640 ug/kg in water and
fish, respectively. Digestive tract tissue contained the most lead (2
mg/kg) and gills the least (0.2 mg/kg). Stamina, as measured by the
ability to swim against a current, was significantly less in trout ex-
posed to snowmobile exhaust than among control fish.
1299.
Adelman, I.R., and L.L. Smith, Jr. 1976. Fathead minnows
(Pimephales promelas) and goldfish (Carassius auratus) as
standard fish in bioassays and their reaction to potential
reference toxicants. Jour. Fish. Res. Bd. Canada 33:209-214.
Minnows and goldfish were compared for suitability as stand-
ard bioassay fish. Both species showed the same variability when
tested with sodium chloride, pentachlorophenol, Cr6+ and Guthion.
Minnows were recommended on basis of small size and use in complete
life cycle tests. On basis of minimum variability of bioassay results,
NaCl was superior for use as a refereHce toxicant. Pentachlorophenol
and NaCl were capable of detecting abnormal fish. For minnows the 24
hr and 96 hr LC-50's were 7910 mg/l and 7650 mg/l for NaCl, and 140
mg/l and 48 mg/l for Cr6+. For goldfish the 24 hr and 96 hr LC-50's
were 9952 mg/l and 7341 mg/l for NaCl, and 261 mg/l and 120 mg/l for
Cr6+.
5
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1300.
Adelman, I.R., L.L. Smith, Jr., and G.D. Siesennop. 1976.
Acute toxicity of sodium chloride, pentachlorophenol,
Guthion, and hexavalent chromium to fathead minnows
(Pimephales promelas) and goldfish (Carassius auratus)
Jour. Fish. Res. Bd. Canada 33:203-208.
LC-50 (96 h) values for NaCl vs minnows and goldfish were
7650 and 7341 mg/l, respectively; for hexavalent chromium these were
48 and 120 mg/l. Threshold LC-50's were reached in 6 days for NaCl
(7650 mg/l for fathead min~ows; 7322 mg/l for goldfish), but were not
attained in 11 days with Cr6+ (18 and 33 mg/l). With Cr6+, goldfish
were more resistant than minnows throughout the II-day test. With
NaCl, goldfish were initially more resistant but at attainment of a
threshold LC-50, were less resistant. Use of toxicity curves for
assessment of acute mortality permits interpretation not possible in
96 hr tests where LC-50's are computed at 24 hr intervals.
1301.
Adema, D.M.M., S.I. De Swaaf-Mooy and P. Bais. 1972. Labora-
tory investigations concerning the influence of copper on
mussels. (Mytilus edulis). TNO-nieuws 27:482-487. (In
German, English Summary.)
At ambient copper concentrations> 45 ug/l, mussel tissues con.
tained from 50 to 90 mg Cu/kg dry weight after 3 days vs 20 mg/kg for
controls. All mussels subjected to 45 ug Cull died within 10 days;
greater Cu concentrations produced more rapid mortality. At ambient Cu
concentrations of 25 ug/l, 60 mg Cu/kg dry weight was found in mussel
tissue within 10 days, and high mortality occurred within 30 days. At
17 ug Cull, a Cu content of 80 mg/kg dry weight was reached in 30 days,
with only slight mortality. A Cu concentration of 12 ug/l produced no
mortality in 30 days although tissue levels rose to 35 mg Cu/kg dry
weight. No mortality or elevated tissue Cu levels. were produced after
exposure for 30 days to 10 ug Cull.
1302.
Agnedal, P.O. 1966. Calcium and strontium in Swedish waters
and fish accumulation of 90Sr. In Aberg, B. and F.P. Hungate
(eds) Radioecological Concentration Processes. Proc. Inter.
Symp. Stockholm, April, 1966. Sym. Pub. Div. Pergamon Press,
New York: 879-896.
Various chemical parameters, including Ca, Sr, Mg, Na, and K
concentrations in water, are given for 3 Swedish lakes. Average bone
concentrations of Ca, in g/kg wet wt, were 45, 36, and 35 for pike,
perch, and roach, respectively; with low variations in bone Ca content
despite high variations in water. Muscle tissue contained 0.56 (pike),
0.43 (perch), and 0.76 (roach) g Ca/kg. Skin, including scale, con-
6
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centrations were 33, 73, and 50 g Ca/kg. Respective Sr values for pike,
perch, and roach, in mg/kg wet wt, were 51, 53, and 47 in bone; 0.6,
0.7, and 1.3 in muscle; and 50, 108, and 135 in skin and scales. Ratios
of Sr:Ca in these fish were 12 to 50% that of water; with Sr substitu-
tion most prevalent at low Ca concentrations. Highest Sr:Ca ratios
occurred in roach, a mollusc feeder, suggesting intake of Ca and Sr with
food. Sr-90 concentrations in fish from Swedish lakes indicates that no
hazard to human health is involved if fish are consumed.
1303.
Ahokas, R.A. and F.G. Duerr. 1975. Salinity tolerance and
extracellular osmoregulation in two species of euryhaline
teleosts, Culaea inconstans and Fundulus diaphanus. Compo
Biochem. Physiol. 52A:445-448.
The LC-50 (96 h) value at 20 f 1 C for Culaea inconstans was
2.1% seawater, and for Fundulus diaphanus, 3.4% seawater. With accli-
mation followed by gradual increase in salinity, the maximum salinity
tolerance for ~. diaphanus was increased to 4.0% seawater. Blood
osmolality of both species is maintained relatively constant at salin-
ities tested, predominantly by regulation of blood sodium and chloride.
Increased blood glucose and potassium in E. diaphanus held in distilled
water appears to be a response to stress rather than an osmoregulatory
response.
1304.
Ahokas, R.A. and F.G. Duerr. 1975. Tissue water and intra-
cellular osmoregulation in two species of euryhaline tele-
osts, Culaea inconstans and Fundulus diaphanus. Compo
Biochem. Physiol. 52A:449-454.
Tissue water; chloride space, and intracellular osmotic con-
stituents in muscle of ~. inconstans and~. diaphanus acclimated in
distilled water and various salinities of seawater for 96 hr at 20 C
were determined. Tissue water increased with increasing salinity in
C. inconstans (0-17.50/00) but remained constant in F. diaphanus at all
salinities (0-40%0). At highest salinities tolerated, chloride space
increased in both species, apparently because of shifts in body water
from intracellular to,extracellular phase. In C. inconstans, intra-
cellular Na and Cl levels were low (Na, l56-266-mg/kg cell H20; Cl,
105-149 mg/kg) and K was high (4426-4582 mg/kg) but none changed sig-
nificantly with changing salinity. In F. diaphanus, intracellular Na,
0-
Cl, and K were lower in 0, 10, and 30 /00 (Na, 100-163 mg/kg; Cl, 82-
147 mg/kg; K, 3471-4212 mg/kg) than in 400/00 (246 mg/kg, 270 mg/kg,
and 4446 mg/kg, respectively). Free ninhydrin-positive substances
play an active role in intracellular osmoregulation in F. diaphanus,
but not in C. inconstans.
7
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1305.
Ahsanullah, M. 1976. Acute toxicity of cadmium and zinc to seven
invertebrate species from Western Port, Victoria. Austral.
Jour. Marine Freshwater Res. 27:187-196.
Static acute toxicity bioassays were conducted at 340/00 salin-
ity, 17-20 C, pH 7.8-8.1, with dissolved oxygen at saturation. The most
sensitive species to Cd was the amphipod Allorchestes compressa with a
120 hr LC-50 of 0.2 mg/l; other species tested were mussel Mytilus edulis
planulatus with a 96 hr LC-50 of 1.62 mg/l; shrimp Palaemon sp. wlth 120
hr LC-50 of 2.30 mg/l; the polychaete worm Neanthesvaali with 168 hr
LC-50 of 6.4 mg/l; and crab Paragrapsus quadridentatus with a 168 hr
LC-50 of 14.0 mg/l. Results of 96 hr static zinc bioassays exhibited
the following sensitivities and LC-50's, in mg Zn/l; A. compressa 0.58;
M. e. planulatus2.5; Neanthes vaali 5.5; Palaemon sp. 9.5; and Para-
grapsus quadrldentatus 11.0. Results for the echinoderm PatirieIIa
exigua and the mollusc Neotrigonia margaritacea were inconclusive due
to difficulty in determining point of death. Continuous flow bioassays
were conducted with Palaemon sp., Paragrapsus quadridentatus and~. ~.
planulatus, producing LC-50 values that were slightly higher than those
in static bioassays.
1306.
Ahuja, S.K. 1964. Salinity tolerance of Gambusia affinis.
Indian Jour. Exp. BioI. 2:9-11.
In culture media containing added NaCl, KCl, CuC12, MgS04,
Na2S04 and NaC03 at a total rate of 2 g/l/day, the freshwater fish G.
affinis showed mortalities of 3 to 5% in 100/00 salinity, 25 to 30%-in
30u/oo salinity and over 95% in salinities of 800/00. Saltwater-
adapted fish showed decreased activity. Salinity stress was accompanied
by sluggish behavior and dorsal surface blood clots.
1307.
Akiyama, A.
compounds
stages of
563-570.
1970. Acute toxicity of two organic mercury
to the teleost, Oryzias latipes,in different
development. Bull. Jap. Soc. Sci. Fish 36(6):
Differential susceptibilities of eggs, developing embryos,
fry, and adults of the freshwater fish O. latipes, were determined for
phenylmercuric acetate (PMA) and methoxyethylmercuric chloride (MEMC).
MEMC, an aliphatic organic mercury, was less toxic than PMA, an aro-
matic organic compound. MEMC LC-50 (24 hr) values for eggs, fry, and
adults were 0.50-1.30 mg/l, 1.48 mg/l, and 1.74 mg/l, respectively;
for PMA these were 0.18-0.26 mg/l, 0.03 mg/l, and 0.21 mg/l, respec-
tively. LC-50 (24 hr) values for adults using mercuric chloride and
copper sulphate (for comparison purposes) were 1.4 mg Hg/l and 40.0 mg
Cull. Adult fish were more tolerant in all cases than fry- Tolerance
8
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increased logarithmically with age; however, eggs in PMA were most
resistant.
1308.
Alderdice, D.F. and C.R. Forrester. 1971. Effects of salinity
and temperature on embryonic development of the petrale sole
(Eopsetta jordani). Jour. Fish. Res. Bd. Canada 28:727-744.
Newly-fertilized eggs were incubated at 13 combinations of
salinity and temperature between 20 and 350/00, and 4.1 and 8.5 C.
Larval length at mean hatching time averaged 2.84 rom for all trials.
Percentages of eggs hatching and producing viable larvae were examined
with respect to salinities and temperatures of incubation. Calculated
optima were: total hatch 29.470/00 S, 6.65 C; viable hatch 27.93%0 S,
7.00 C. At 6.3, 7.2, and 8.1 C, larvae grew to 5.5-5.7 mn total length
prior to exhaustion of yolk 246-393 hr after hatching. It was concluded
that greatest numbers of viable larvae of largest size at yolk exhaus-
tion would occur from incubation at 27.5-29.5 /00 Sand 6-7 C. Labora-
tory results are related to available hydrographic and meteorological
data for a spawning area off the west coast of Vancouver Island. Esti-
mates are given of direction, depth, and duration of drift of the
pelagic stages until yolk exhaustion. Environmental variabillty in
spawning period is related to existing measures of year-class strength.
Effect of temperature on egg development is related to range of species
in terms of estimated temperatures available at spawning depths.
1309.
Alexander, G.V. and D.R. Young. 1976. Trace metals in southern
Californian mussels. Marine Poll. Bull 7(1):7-9.
Ranges of metals in mg/kg dry wt in Mytilus californianus
digestive glands were: 2 to 38 for Pb; 14 to 69 for Cu; 2 to 61 for
Cr; 0.7 to 33 for Ag; 46 to 110 for Zn; and 3 to 20 for Ni. Authors
suggest that Pb distribution was dominated by diffuse inputs, while Cu,
Cr, and Ag were related to urban point sources. No pattern for Ni or
Zn was observed.
1310.
Alexander, J.E., J. Foehrenbach, S. Fisher and D. Sullivan.
1973. Mercury in striped bass and bluefish. New York Fish
Game Jour. 20:147-151.
In bluefish from ~10ntauk Point, Long Island, Hg levels in
mg/kg wet wt were: < 0.5 for fish weighing < 2.4 kg;~0.5 for 2.4 to
5.6 kg individuals; and> 0.5 for fish weighing> 5.6 kg. Correspond-
ing weight categories for striped bass were: < 3.2 kg, 3.2 to 5.7 kg,
and> 5.7 kg, respectively.
9
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1311.
Allee, W.C. and E.S. Bowen. 1932. Studies in animal aggre-
gations: mass protection against colloidal silver among
goldfishes. Jour. Exp. 2001. 61(2):185-207-
A group of 10 goldfish survived longer than isolated gold-
fish in similar volumes and concentrations of colloidal Ag. When ex-
posed to the same volume of colloidal Ag per individual, grouped and
isolated fishes showed similar susceptibility. In a processionary
series of fishes in the same suspension of colloidal silver, later
individuals survived longer. Grouped fishes removed more colloidal Ag
from suspension than isolated fishes; this alone could account for
greater group survival. Suspensions of colloidal Ag in which fishes
died, or lived up to 24 hrs contained less unadsorbed Ag than controls,
even when double the amount is added. C02 did not protect the group
from colloidal Ag. Urinary excretions, feces, and slime secretions
protect fish from colloidal Ag; depressed metabolism was not an im-
portant protective mechanism.
1312.
Allee, W.C. and J.F. Schuett. 1927. Studies in animal aggre-
gations: the relation between mass of animals and resist-
ance to colloidal silver. BioI. Bull. 53:301-317.
Using annelid worms, crustaceans, platyhelminthes, coelen-
terates, echinoderms, higher plants and molluscs, it was shown that
there is greater protection with increasing biomass on exposure to
equal amounts of colloidal silver and water. Protection is due to
fixation of toxic substance by the mass of animals with each receiv-
ing a sub-lethal dose; isolated individuals in same concentration re-
ceive a stronger dose. Colloidal Ag may be differently fixed in dif-
ferent animals but in slime-secreting animals like planarians it is
absorbed on the slime. Protection furnished by mass is independent of
species. Authors suggest that other inert substances capable of fixing
colloidal Ag by absorption should produce the same effect.
1313.
Allen, K. 1961. The effect of salinity on the amino acid con-
centration in Rangia cuneata (Pelecypoda). BioI. Bull.
121 (3) : 419-424.
Concentration of 4 amino acids increased in clams with in-
creasing salinities from 3%0 to 17%0. Further salinity increases
to 25%0 resulted in decreased amino acid content/gm tissue dry wt.
An abundance pattern of alanine> glycine> glutamic acid> aspartic
acid did not change throughout the study. Increased environmental
salinities resulted in water loss from tissues.
10
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1314.
Amiard, J.-C. 1975. Interpretation d'une etude
du metabolisme du radiostrontium chez la plie
platessa) a l'aide des analyses factorielles.
Oceanogr. Med. 39-40:177-212.
experimentale
(P leuronectes
Rev. Intern.
Several studies were conducted on Sr metabolism in flatfish
~. platessa, as influenced by various biotic and abiotic factors.
Using Sr-85, strontium uptake occurred mainly in soft tissues during
the earliest contamination stage; after the 12th day it occurred mainly
in hard tissues. Colder temperature, the passage from brackish to sea-
water, and from gravel to sand, were all associated with lowered stron-
tium uptake. Within experimental limits Ca concentration had no effect
on Sr uptake.
1315.
Amiard. J.-C. 1976. Phototactic variations in crustacean
larvae due to diverse metallic pollutants: demonstrated by
a sublethal toxicity test. Marine Biology 34:239-245. (In
French, English summary.)
Orientation of crab zoae (C. maenas) to light during 96 hr
period was disrupted by 0.01 to 0.1 mg COC12/l, 0.01 to 0.1 mg AgN03/1,
or 100 mg SrC12/l. For shrimp zoae Palaemon serratus, corresponding
values in mg/l, were 100 to 500 for CoC12> 100 for AgN03 and 500 for
SrC12. C. maenas photokinesis was decreased by amounts of 0.001 mg/l
of CoC12-or AgN03 within a period of 2 to 3 days.
1316.
Amiard, J.-C., J.C. Harduin and G. Odilon. 1976. Etude de
l'influence d'une surcharge en chlorure de cobalt sur la
composition en acides amines libres de l'hemolymphe du
crustace decapode: Carcinus maenas L. Cahirs BioI. Marine.
17:295-303.
Crabs exposed to 10 mg/l of cobalt chloride for 8 days at
15 C, exhibited changes in haemolymph amino acid composition. When
compared to controls, cobalt-exposed crabs showed increases in 10
"non-essential" amino acids (cyteic, aspartic and glutamic acids, gly-
cine, alanine, l-methylhistidine, arginine and ASN+glutamine) and
decreases in concentrations of 3 "essential" amino acids (methionine,
lysine and histidine).
1317.
Amiard-Triquet, C. and J.-C. Amiard. 1975. Etude experimentale
du transfert du cobalt 60 dans une chaine trophique marine
benthique. Helgol. wiss. Meeresunters 27:283-297.
Experiments were conducted to quantify transfer of Co-60 from
11
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the environment to various components of a benthic food chain. The
food chain tested comprised diatom Navicula sp., bivalve Scrobicularia
plana, shore crab Carcinus maenas, and rat Rattus rattus. Diatoms take
up large quantities of radiocobalt. The radioactivity accumulated (per
unit weight) by organisms studied decreases from one trophic level to
the next: from about 3200 nCi/g in Navicula at equilibrium to 40 in
Scrobicularia at equilibrium to 12 in Carcinus to 0.03 in rats. There
is some biological control in Co-60 uptake by these species. For all
species except Na/icula the quantity of Co-60 assimilated is independ-
ent of quantity ingested with food. Preferential sites of cobalt
accumulation are liver and kidneys in rat, and hepatopancreas in the
two invertebrate species examined.
1318.
Arniard-Triquet, C. and J.-C. Arniard. 1976. L'organotropisme
du 60Co chez Scrobicularia plana et Carcinus maenas en
fonction du vecteur de contamination. Oikos 27:122-126.
(In French, English summary.)
In the bivalve mollusc ~. plana, and crab f. maenas, the
surrounding water is the primary source of external Co-60 contamination;
internal contamination results largely from food intake. In both
species Co-60 is accumulated in large quantities by digestive gland.
Edible parts of ~. plana are contaminated with Co-60, whereas digestive
gland of C. maenas is not generally eaten.
1319.
Arnie 1 , A.J., G.M. Friedman and D.S. Miller. 1973. Distribution
and nature of incorporation of trace elements in modern ara-
gonitic corals. Sedimentology 20:47-64.
Experiments based on dissolution rate of aragonite in dis-
tilled water and the substitution of Sr and Mg by Ca and Na have shown
that the main site for Sr in corals is in the aragonite lattice. For
Mg, 25% of the total occurs in adsorbed sites and organic compounds.
The remaining Mg may be located in the aragonite lattice, but is easily
removed by leaching or replacement with Ca. About 12% of total Na is
in adsorbed sites and included in organic compounds; remaining Na may
be in lattice replac~ng Ca. K is in adsorbed sites and incorporated
in organic compounds to a higher degree than other elements examined
(30% of total K). After 5 months in the substitution experiment, cal-
cite replaced aragonite on coral surfaces after inhibitor Mg was ex-
changed from surface sites and replaced by Ca. Organic compounds of
corals contain about 500 mg/kg Sr, 190-325 mg/kg Mg, 600-620 mg/kg Na
and < 100 mg/kg K.
12
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1320.
Ancellin, J., P. Bovard, and A. Vilquin. 1967. New studies on
experimental contamination of marine species by ruthenium-
106. Actes du Congres Int. sur la radioprotection du milieu
Soc. Franc. de radioprot. Toulouse, France, 14-16 Jan. 1967:
213-234. (In French.)
Laboratory uptake studies of Ru-106 from medium by various
species of marine alga, coelenterates, molluscs, crustaceans, ascidians,
and teleosts were conducted. In 200-250 hours, concentration factors
ranged from 100 to 200 for algae, 20 to 50 for invertebrates, and about
1 for fish. The algae Corallina officinalis and the ascidian Dendrodoa
grossularia were the most active concentrators.
1321.
Anderlini, V. 1974. The distribution of heavy metals in the
red abalone, Haliotis rufescens on the California coast.
Arch. Environ. Contamin. Toxico1. 2(3):253-265.
Ranges of mean metal levels in mg/kg dry wt of gills of
abalones (mollusc) from 5 localities were 13 to 129 for Ag, 4 to 20 for
Cd, 0.6 to 4.0 Cr, 19 to 124 Cu, always <0.1 for Pb, 0.08 to 0.27 Hg,
69 to 112 Ni, and 28 to 54 Zn. Mantle values were 16 to 54 for Ag, 3
to 13 Cd, 0.0 to 13 Cr, 9 to 20 Cu, always <0.1 for Pb, 0.02 to 0.33
Hg, 19 to 57 Ni, and 42 to 74 for Zn. Digestive glands contained 14 to
60 Ag, 184 to 1163 Cd, 2 to 13 Cr, 11 to 78 Cu, 9 to 41 Pb, 0.12 to
4.64 Hg, 3 to 11 Ni, and 536 to 980 for Zn. Foot tissue levels in
mg/kg dry wt, were 1 to 44 for Ag, 0.2 to 0.5 for Cd, below detection
levels for Cr, 1 to 13 for Cu, <0.1 for Pb, 0.03 to 0.09 for Hg, 0.2
to 1.6 for Ni and 38 to 46 for Zn. Metal concentrations were not corre-
lated with size of organism; however Cu and Ag concentrations were in-
versely correlated, with Cu decreasing and Ag increasing from north to
south. High Hg concentrations in La Jolla-Long Beach area reflect
pollutant inputs; elsewhere,Hg levels appeared to derive from natural
sources.
1322.
Andersen, A.T., A. Dommasnes and I.H. Hesthagen. 1973. Some
heavy metals in sprat (Sprattus sprattus) and herring (Clupea
harengus) from the inner Oslofjord. Aquaculture 2:17-22.
Respective mean metal levels, in mg/kg dry wt of sprat, and
herring, were 5.6 and 4.4 for Cu, 133 and 119 for Zn, 0.3 and <0.2 for
Cd and 8.2 and 7.0 for Pb.
1323.
Andryushchenko, V.V. and G.G. Polikarpov. 1974. An experi-
mental study of uptake of Zn65 and DDT by VIva rigida from
13
-------
seawater polluted with both agents.
41-46.
Hydrobiol. Jour. 10(4):
Uptake of Zn-65 by algae VIva rigida was reduced 12 to 36%
over controls by 1 mg DDT/l.
1324.
Annett, C.S., F.M. D'Itri, J.R. Ford, and H.H. Prince. 1975.
Mercury in fish and waterfowl from Ball Lake, Ontario. Jour.
Environ. Qual. 4:219-222.
A total of 323 fish samples representing 8 species, and 26
waterfowl samples of 3 species were collected from the Ball Lake area
of the Wabigoon-English River systems in NW Ontario and analyzed for
total mercury by flameless atomic absorption. The average total Hg
concentrations of walleye and pike (teleosts) were 3.24 and 5.55 mg/kg
wet wt, respectively. The highest total Hg concentrations in fish dur-
ing the entire study were 19.71 and 16.09 mg/kg wet wt, respectively,
in muscle tissue of a walleye and a pike. Frequency distributions of
total Hg levels in fish are presented by species and sampling location.
The highest average Hg levels in breast muscle and liver tissue of three
species of waterfowl were 8.3 (breast)and 98.5 (liver) mg/kg wet wt.
1325.
Annett, C.S., M.P. Fa~ow, F.M. D'Itri, and M.E. Stephenson.
1972. Mercury pollution and Lake Erie fishes. The Michigan
Academician 4(3):325-337.
To assess extent of mercury contamination of Lake Erie in
the vicinity of the Raison River, 79 fish and 37 sediment samples were
analyzed. The average Hg content in mg/kg dry wt in fish species were
0.49 in perch Perca flavescens, 0.28 in goldfish Carassius auratus,
0.19 in carp Cyprinus carpio, 1.7 in sheepshead Alpodinotus grunniens,
0.4 in pumpkinseed Lepomis gibbosus, 0.18 in carpsucker Carpiodes, and
0.67 in a carp-goldfish hybrid. Total Hg concentrations of surface
water samples were nearly always <0.1 ug/l; levels in sediments were
evenly distributed with a range of 0.19 to 0.53 mg/kg dry wt. No
correlation was evident between size of fish and total Hg content with-
in a given species. A trend in Hg accumulation was observed among
species, with mean total Hg levels having a declining order in perch,
goldfish and carp.
1326.
Anon. 1915 (1916). Dept. of Biology, N.J. State Agric. Exper.
Station, 1915, Annual Report. Trenton, N.J., Section 5:
246-249.
Numerous conjectures are made concerning the green color of
14
-------
oysters. The primary hypothesis proposed here is that green color is
related to a deficiency of oxygen in water, producing an increase or
compositional change in respiratory pigment of these oysters. It is
suspected t~at uncolored oysters always have this substance present and
with suitable culturing techniques oysters could be produced in any
desirable hue. Blue oysters contained approximately 26.7 mg Cu/g dry
wt compared to approximately 8.4 mg/g for white oysters.
1327.
Anon. 1972. Mercury pollution investigation in Georgia 1970-
1971. Georgia Water Quality Control Board, 47 Trinity Ave.,
Atlanta, Ga.: 117 pp.
In 7 major freshwater river basins exclusive of the Savannah
River, average mercury contents in mg/kg wet wt were 0.38 for large-
mouth bass and 0.20 for catfish. In the Savannah River from Augusta to
Savannah, largemouth bass and American shad contained 1.5 and 0.23 mg
Hg/kg, respectively. In the Savannah Estuary, shrimp, blue crabs,
flounders and eastern oysters had average Hg contents of <0.5 mg/kg.
Blue crabs from the Georgia coast exclusive of the Brunswick area con-
tained 0.14 mg Hg/kg. In the Brunswick area, Hg content of blue crabs
decreased from 1.09 to 0.56 mg/kg during the study interval. The
Savannah River from Augusta to Savannah and the Brunswick area were
characterized by biotic Hg levels greater than 0.5 mg/kg (the current
Food and Drug Administration Hg limit for food). Both regions received
discharges from mercury-ceIl-type chlor-alkali plants.
1328.
Anon. 1974. Progress and projections, Fisheries and marine
service, Vancouver laboratory; 6640 N.W. Marine Drive,
Vancouver, B.C.: 21 pp.
Inclusion of 8% herring meals (containing 0.17 to 0.22 mg/kg
mercury) in diet of laying birds (chickens) had no effect on mortality,
fertility, hatchability; or rate of lay and egg quality; Hg did not
accumulate in meat or eggs.
Another study reports on effects of Cd and Cu salts on lactic
acid oxidation from gills of exposed fish. However, this test had
value only at high exposure levels (1.1 mg/l Cd or 0.06 mg/l Cu).
A third study documented stress response of salmon to low
levels of copper. Yearling sockeye salmon exposed to low concentra-
tions of Cu for 1 to 24 hr; exhibited abnormal plasma cortisol and
cortisone concentrations. The highest concentration tested of 0.635
mg/l Cu caused sharp increase in cortisol concentration in 1 hr and was
fatal in 8 to 24 hrs; 0.0635 mg/l Cu produced stress but no deaths in
24 hrs; 0.00635 mg/l produced slight effect which was not measurable
after 4 hrs.
15
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1329.
Anon. 1975. Great Lakes environmental contaminants survey 1973.
Avail. from Int. Joint Comm. Great Lakes Reg. Off., 100
Ouellette Ave., Windsor, Ontario, Canada.
Residues of DOT's, PCB's, dieldrin, and mercury in flesh of
Great Lakes fishes were determined by several resource agencies.
Highest mercury values recorded in Lake Huron teleosts in mg/kg wet wt,
were 0.55 t 0.36 for walleyes, and 0.60 t 0.12 for catfish. For Lake
Erie teleosts highest individual Hg values were 0.56 t 0.16 for walleye,
0.55 for yellow perch, 0.54 for white bass, 0.48 t 0.26 for drum, and
0.34 t 0.19 for carp. For Lake Michigan, highest Hg values were noted
in selected lake trout (0.57), and salmon (0.55). One lake trout in
Superior contained 0.80 t 0.30 mg Hg/kg wet wt, but all other samples
and species therein contained <0.20. Mercury levels were comparatively
high in Lake St. Clair walleyes (1.11 t 0.46), yellow perch (0.52) and
white bass (0.35).
1330.
Antia, N.J. and J.Y. Cheng. 1975. Culture studies on the
effects from borate pollution on the growth of marine phyto-
plankters. Jour. Fish. Res. Bd. Canada 32:2487-2494.
Growth rates of 19 species of marine algae were unaffected by
incorporation of 5 to 10 mg B/l into a nutrient-enriched, pH-controlled
seawater medium. However 26% of the species were strongly inhibited by
50 mg of B/l and this proportion increased to 63% at 100 mg of B/l.
Several species required prolonged periods of adaptation before ex-
ponential growth with 50 to 100 mg of B/l. Both adaptation period and
degree of inhibition were gradually mitigated on sequential transfer of
certain species from lower to higher B concentration. This suggested
that the majority of species inhibited initially could maintain good
growth at 50 mg but not 100 mg B/l (a concentration lethal to 37% of
species).
1331.
Antonini-Kane, J., S.W. Fowler, M. Heyraud, S. Keckes, L.F.
Small and A. Veglia. 1972. Accumulation and loss of
selected radionuclides by Meganyctiphanes norvegica M.
Sars. Rapp. Comm. Int. Mer Medit. 21(6):289-290.
Concentration ratios, defined as activity per mg live wt
divided by activity per ml water, for euphausiids after exposure for
12 hrs were: 85 for Zn-65, 65 for Ce-14l, 30 for Fe-59, 20 for Ru-l06
(Cl form) and 3 for Ru-l06 (N form). After 12 hrs in isotope-free
medium, 10% of Ce-14l, 25% of Zn-65, 30% of Fe-59 and 35% of Ru-l06
was lost. Molting reduced isotope contents of animals drastically;
provided that initial uptake was directly from medium. When uptake
vector was food chain, molting loss was insignificant.
16
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1332.
Argiero, L., S. Manfredini and G. Palmas. 1966. Absorption de
produits de fission par des organismes marins. Health
Physics 12:1259-1265. (In French, English summary.)
Accumulation of Sr-90 and Cs-137 by mussel, Mytilus gallo-
provincialis, from seawater was determined. With Sr-90, equilibrium
is maintained after 120 hrs with concentration factor of 3.6 (fresh
wt) and 98.3 (ash wt). For Cs-137, equilibrium is reached in about
100 hrs. The Cs-137 c.f. varied from 4.3 for adults to 6.4 for juve-
niles (fresh wt basis); on an ash wt basis c.f. ranged from 117 for
adults to 175 for juveniles.
1333.
Arima, S. and S. Umemoto. 1976. Mercury in aquatic organisms --
II Mercury distribution in muscles of tunas and swordfish.
Bull. Jap. Soc. Sci. Fish. 42(8):931-937. (In Japanese,
English summary.)
Total mercury concentrations ranged from 0.74 to 2.34 mg/kg
in muscle of bigeye tuna Thunnus obesus, bluefin tuna T. thunnus, and
swordfish Xiphias gladius. Myofibrillar proteins contained 57 to 68%
of total muscle Hg; combined myofibrillar and sarcoplasmic protein
fractions contained 71 to 89% of total muscle Hg. At low Hg residues
levels, Hg was preferentially incorporated into myofibrillar proteins.
At higher levels, both myofibrillar and sarcoplasmic proteins incor-
porated Hg.
1334.
Armstrong, F.A.J. and A.L. Hamilton. 1973. Pathways of mercury
in a polluted Northwestern Ontario lake. In: Singer, P.C.
(ed). Trace metals and metal organic interactions in natural
waters. Ann Arbor Sci. Publ., Ann Arbor, Mich.: 131-156.
The Wabigoon River-Clay Lake-English River-Winnipeg River
system in western Ontario and eastern Manitoba was studied because of
its high mercury content. The source of the contamination was a
chlorine-alkali plant which during 8 years of unregulated operation,
1962-1969, may have discharged 9,000 to 11,000 kg Hg. Elevated Hg
concentrations were found in top 5-6 cm of sediments. Biological
sampling showed that organisms living in bottom sediments or attached
to littoral vegetation had much higher concentrations than organisms
living or feeding in water column. Zooplankton always contained <0.1
mg Hg/kg wet wt, while mayfly and midge larvae from bottom sediments
contained 0.1 to 1.0 mg Hg/kg wet wt. Hg was related to food selection
for omnivores, organisms feeding on detritus, or bottom-dwelling in-
vertebrates such as annelids, molluscs and crustaceans. These had much
higher Hg levels than herbivores or organisms feeding on zooplankton.
It appears that Hg uptake via food chain is more significant than
17
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direct uptake from water or sediment. A survey of Hg concentrations in
crayfish Orconectes viri1is showed that Hg accumulates unevenly through-
out body with highest levels in abdominal muscle. Most of the Hg con-
centrated by crayfish is in methylated form, with a definite age-
mercury concentration relationship. Hg levels in crayfish decreased as
a reflection of improving conditions; the use of Orconectes as an indi-
cator of Hg pollution is proposed.
1335.
Aronson, J.L., M. Spiesman and A.K. Aronson. 1976. Note on the
distribution of mercury in fish species in three Ohio lakes.
Environ. Po1lut. 10:1-7.
Sunfish Lepomis macrochirus and~. gibbosus, yellow perch
Perca f1avescens, channel catfish Ictalurus punct,atus, bullhead !.
nebu10~is,and white bass Morone chrysops from two large non-industrialized
lakes in Ohio contained about 0.1 mg Hg/kg. Carp Cyprinus carpio, con-
tained 0.25 mg Hg/kg. At Fairport Harbor, Lake Erie, all speci~s con-
tained 0.25 to 0.35 mg Hg/kg. Authors suggest that ubiquitous carp,
rather than fish higher in food web, may be best biological magnifiers
for inter-lake comparisons of Hg in unpolluted, moderately eutrophic
lakes.
1336.
Avio, C.M. and L. Lenzerini. 1963. Captazione del Cs137 da
parte di Chlorel1a vulgaris. Pubb1. Staz. Zool. Napoli
33:69-82. (In Italian, English summary,)
Growth of the alga Chlorel1a was not affected by 0.9 ug of
CS/1, but was inhibited by 100 ug CS/l. Cs-137 was accumulated in a
linear fashion with a concentration factor of 0.0011 for 106 cells.
Cesium uptake was a direct function of cell number and Cs concentration
in medium.
1337.
Bache, C.A., W.H. Gutenmann, and D.J. Lisk. 1971. Residues of
total mercury and methylmercuric salts in lake trout as a
function of age. Science 172:951-952.
Whole yearling trout Salve1inus namaycush, from Cayuga Lake,
N.Y. contained 0.19 to 0.28 mg Hg/kg wet wt; methyl-Hg constituted
3.0 to 35.0% of the total Hg. Total Hg and proportion of Me-Hg to
total Hg showed increases with age; 12 year old trout contained 0.44
to 0.62 mg Hg/kg wet wt of which 66.9 to 88.4% was Me-Hg.
1338.
Bachenheimer, A.G. and E.O. Bennett. 1961. The sensitivity
of mixed populations of bacteria to inhibitors I. the
18
-------
mechanism by which Desulfovibrio desulfuricans protects Ps.
aeruginosa from the toxicity of mercurials. Antonie van
Leeuwenhoek Jour. Microbiol. Serol. 27:180-188.
Concentration of phenylmercuric lactate required to completely
prevent growth of Pseudomonas aeruginosa increased from 200 in pure
culture to 900 mg/l when D. desulfuricans was introduced. Similar
results obtained from hydrogen sulfide leads to the conclusion that
hydrogen sulfide produced by ~ulfate-reducers protects both organisms
from mercurial inhibition.
1339.
Bachmann, R.W. and E.P. Odum. 1960. Uptake of Zn65 and primary
productivity in marine benthic algae. Limnol. Oceanogr.
5(4):349-355.
Uptake of Zn-65 by six species of algae occurred in the light,
but not in the dark. Initial rate of uptake in light was proportional
to gross oxygen production which varied with species. Apparent equili-
brium uptake rates in Chaetomorpha at different light intensities were
proportional to net oxygen production. In marine seaweeds, Zn is taken
up and accumulated in proportion to gross oxygen production; consequently,
Zn-65 has possibilities as a tool for measurement of primary productivity.
1340.
Backstrom, J. 1969. Distribution studies of mercuric pesti-
cides in quail and some fresh-water fishes. Acta Pharmacol.
Toxicol. 27 (Supp. 3):3-103.
Using Japanese quail and several species of freshwater fish
the localization of Hg was followed after parenteral or peroral admini-
stration of methyl mercury, phenyl mercury, methoxyethyl mercury, and
inorganic mercury (Hg2+); mercurials were labelled with Hg-203. In some
avian experiments the stability of the carbon-mercury bond in methyl and
phenyl mercury was examined by comparative studies of compounds double-
labelled with Hg-203 and C-14. Administration route was of minor im-
portance for the final qualitative distribution of mercury; methyl
mercury was readily absorbed after ingestion while the other compounds
were less well absorbed. The methyl mercury radical was comparatively
stable in the avian body, but phenyl mercury was rapidly decomposed to
inorganic mercury. Distribution of methyl mercury in quail differed
from other mercurials, the latter presenting great simil~rities with
each other. Methyl mercury was characterized by an even distribution
of mercury in most organs including kidneys, and by a slow excretion.
After injection of methyl mercur~ brain slowly reached a high concen-
tration of Hg. Injection of other mercurials resulted in negligible
cerebral uptake of Hg. An increased dosage of phenyl, methoxyethyl
and inorganic mercurials resulted in more Hg being excreted via the
19
-------
eggs. With the methyl mercurial a higher dose increased excretion only
slightly. Plumage and other keratinized structures strongly concen-
trated Hg for all Hg compounds given, and this seems to be an important
route of excretion of mercurials, especially methyl mercury. A pro-
nounced concentration and retention of Hg was observed in avian anterior
pituitary with phenyl, methoxyethyl and inorganic mercurials. Depend-
ing on type of mercurial, accumulations of Hg were observed in adrenal
medullary cells, in pancreas, in certain nuclear areas in brain, in
ganglia, in germinal discs and in epididymis. With phenyl and methoxy-
ethyl mercurials the Hg-ratio between blood corpuscles and blood plasma
was similar to that of the methyl mercurial, but after longer survival
times it was more similar to the inorganic mercurial. This finding is
consistent with a decomposition of the two organo-mercurials to in-
organic mercury. Electrophoresis, combined with autoradiography and
isotope scanning of the avian blood proteins demonstrated marked sex
differences in the localization of mercury. Electrophoresis was also
run with yolk and egg white samples from Hg-contarninated eggs, which
resulted in characteristic localizations of Hg depending on type of
mercurial.
In the piscine experiments, the most outstanding feature was
the slow kinetics of mercury once distributed. No great differences
in distribution of mercury were observed between species. Differences
between various compounds were less prominent than in the avian experi-
ments. The principal distribution otherwise showed many similarities
with corresponding patterns in birds. However, thyroid and spleen
demonstrated a much higher uptake of mercury in fishes than in birds.
Injection of phenyl mercury into fishes also resulted in a strong re-
tention of mercury in the wall of gall bladder and in cortical layer
of myocardium. These localizations of mercury were not observed in
birds. After injection of methyl mercury there was a steadily increas-
ing uptake of mercury in fish muscle and brain throughout the study.
Injection of the inorganic mercurial resulted in a similar increasing
uptake in kidney, spleen, and liver. A pronounced difference was ob-
served between white and red flesh, the latter accumulating consider-
able more Hg than the former. Phenyl mercury strongly accumulated in
piscine liver, which may be related to a green color presumably caused
by bile pigments, which appeared in flesh of pikes kept in water con-
taining phenyl mercury. A high uptake of mercury was noted in gills
and pseudobranch. The significance of these localizations is uncer-
tain, but damage to these organs in fishes poisoned by mercurials have
been reported.
1341.
Baker, P.F., H. Meves and E.B. Ridgway. 1973. Effects of
manganese and other agents on the calcium uptake that
follows depolarization of squid axons. Jour. Physiol.
231:511-526.
20
-------
Tetrodotoxin-insensitive components were blocked, reversibly,
by concentrations of Mn, Co and Ni that reduced but did not block
tetrodotoxin-sensitive component. Late component was also blocked by
La3+ and organic Ca antagonists 0-600 and iproveratril. Mn2+, C02+,
and Ni2+ and the drug 0-600 all reduced Na currents, but had little
effect on either outward or inward K currents. Tetraethyl-ammonium
blocked outward K current but had no appreciable effect on tetrodotoxin-
insensitive entry of Ca. Concentrations of Mn between 0.28 and 2.8 g/l
substantially reduced light output during a train of action potentials
and slightly reduced rate of action potential rise. It was concluded
that a tetrodotoxin-insensitive component of Ca entry does not represent
Ca ions passing through K permeability channels. There must exist a
potential-dependent late Ca channel distinct from Na and K channels of
the action potential.
1342.
Baker, P.F., H. Meves and E.B. Ridgway. 1973. Calcium entry
in response to maintained depolarization of squid axons.
Jour. Physiol. 231:527-548.
External K concentrations >2.0 g/l produced a phasic light
response. Light rose to a peak in a few seconds and then fell in 0.5
to 5 min to a new steady level that was greater than level in absence
of K. Phasic light response seems to reflect a phasic entry of Ca in
response to depolarization. Similar phasic responses were produced by
prolonged electrical depolarization. Results were consistent with
depolarization serving both to activate and also to inactivate Ca entry.
Following inactivation and return to normal seawater, there was an
appreciable relative refractory period during which the response both
to K-rich seawater and electrical depolarization was reduced in size;
complete recovery took 10-15 min. Pre-treatment with 7.4 or 14.8 g
KCl/l reduced response to 30.3 g KCl/l. Phasic Ca entry produced by
K-rich solutions was insensitive to external tetrodotoxin and internal
tetraethylammonium ions, but was blocked by external Mn2+, C02+ and
Ni2+ ions and by 0-600 and iproveratril, suggesting that phasic Ca
entry involves the late Ca channel. Outward K current recovery after
a long depolarization was faster than recovery of late Ca entry system,
providing support for view of distinct K and late Ca channels.
1343.
Bakunov, N.A. 1975. The ~iological test organism in marine
radioecological investigations. Soviet Jour. Ecol. 5:67-70.
Cesium-137 content in six species of fishes from the Caspian
Sea was determined. Herring Clupeonella engrauliformis contained 53
to 97 pCi/kg wet wt, or less variation in this parameter than other
fish species examined; mean radioactivity values were intermediate.
Because C. engrauliformis is planktiverous and abundant over a wide
21
-------
range, it is recommended as an appropriate indicator of radionuclide
pollution.
1344.
Ball, E.G. and B. Meyerhof. 1940. On the occurrence of iron-
porphyrin compounds and succinic dehydrogenase in marine
organisms possessing the copper blood pigment hemocyanin.
Jour. BioI. Chern. 134:483-493.
Iron-porphyrin compounds were found in tissues of horseshoe
crab Limulus polyphemus, whelk Busycon canaliculatum, lobster Homarus
americanus, and squid Loligo pealii; hemocyanin is the blood pigment in
these species. Myoglobin was present in high concentration in radula
muscles of Busycon. Authors concluded that oxygen utilization in these
organisms is similar to that in mammals except for substitution of hemo-
cyanin for hemoglobin. Substitution can not be ascribed to inability
to utilize Fe or to synthesize porphyrin group characteristic of Fe
respiratory pigments. Two additional hemochromogens occurred in
Limulus. One in the clot obtained from blood, the other in eggs. A
hemin was also found in eggs of sea urchin, Arbacia punctulata.
1345.
Banus, M., I. Valiela, and J.M. Teal. 1974.
salt marshes. Marine Poll. Bull. 5:6-9.
Export of lead from
Lead accumulates in shallow salt marsh sediments with subse-
quent uptake by grasses including Spartina alterniflora. Since about
half the annual grass crop is transported to the sea after the grass
dies, this may contribute to movement of Pb to deeper waters. Where
nitrogen additions increase biomass of grasses, or where heavy Pb con-
tamination takes place, substantial amounts of Pb may be removed by
tides from marsh surfaces. A model was constructed in which authors
estimated Pb inputs from atmosphere into marsh at about 12 mg Pb/m2;
this is reflected as 730 mg Pb/m2 in sediments, 28 in grasses, and 14
mg Pb/m2 losses to the sea. Higher values were calculated for ferti-
lized plots with ultimate losses to the sea at 58 mg Pb/m2.
1346.
Bargmann, G.G. and G.W. Brown, Jr. 1973. Fish muscle alpha-
glycerophosphate dehydrogenase and its inhibition by metals.
In: Research in Fisheries Annual Rept. ColI. Fisheries,
Univ. of Wash., Seattle, Wash.: 56.
Activity of alpha-glycerophospate dehydrogenase of rainbow
trout Salmo gairdneri muscle was reduced to 50% of control value by
addition, in mg metal/kg wet wt muscle, of 0.2 Hg2+, 1.1 Cd2+, 3.3
Zn2+, 6.4 Cu2+, 83 Pb2+, or 120 Ni2+.
22
-------
1347.
Barnard, H.E.
7:145-148.
1911.
Some poisons found in food.
Pure Products
Arsenic values, in ug/kg were 27 to 39 in mackerel and 1 to
76 in shrimp. In lobsters, As contents, in ug/kg, were 22 in muscle
tissue, 357 in eggs and fat, 1040 in flesh, and 453 in the whole body.
Oysters contained 40 to 447 mg copper/kg fresh weight.
1348.
Barnes H. and F.A. Stanbury. 1948. The
and mercury salts both separately and
harpacticid copepod, Nitocra spinipes
BioI. 25:270-275.
toxic action of copper
when mixed on the
(Boeck). Jour. Exp.
At a concentration of 0.6 mg Hg/l and no Cu, 50% of N.
spinipes died after 24 hrs. Copper alone at 0.026,mg Cull killed 1.3%.
but when added to 0.6 mg Hg/l the mixture killed 62%. Different con-
centrations of Cu and Hg showed similar synergistic effects when mixed,
and suggest that the two toxicants act in a different manner.
1349.
Bartlett, L., F.W. Rabe and W.H. Funk. 1974. Effects of copper,
zinc and cadmium on Selanastrum capricornutum. Water
Research 8:179-185.
Algicidal and a1gistatic effects of copper, zinc and cadmium
on the freshwater green algae ~. capricornutum were determined. Algi-
cidal concentrations of Cu, Zn and Cd were 0.30, 0.70 and 0.65 mg/l,
respectively. Initial growth rate inhibition occurred for Cu, Zn and
Cd at concentrations of 0.05, 0.03, and 0.05 mg/1, respectively. A
5/1, 5/2 and 5/3 ratio of Zn/Cu (0.5 mg Zn/l + 0.1, 0.2 and 0.3 mg
Cull) produced growth rates similar to 0.6, 0.7, and 0.8 mg Zn/l; the
same combinations of Zn and Cd also resulted in rates similar to Zn.
Combinations of Cu and Cd produce greater growth than an equal concen-
tration of Cu suggesting that Cd inhibits toxicity of Cu.
Selanastrum could exist in water from the upper South Fork and
North Fork of the Coeur d'Alene River, where Zn and other metals were
in low concentrations. This species was unable to tolerate Zn con-
centrations greater than 0.5 mg/l from other parts of the drainage, and
this is consistent with laboratory findings.
1350.
Baudouin, M.F. and P. Scoppa. 1974.
metals to freshwater zooplankton.
Toxicol. 12:745-751.
Acute toxicity of various
Bull. Environ. Contamin.
Cyclops abyssorum, Eudiaptomus padanus, and Daphnia hyalina
23
-------
were used to determine the toxicity of various metal salts. For
Daphnia, the most sensitive of the three, the 48-hr LC-50's, expressed
in mg/l were 3000 for Ca, 75 for Sr, 32 for Mg, 7.4 for Cs, 1.9 for
Ni, 1.32 for Co, 0.60 for Pb, 0.055 for Cd, 0.05 for Cu, 0.04 for Zn,
0.022 for Cr+6, and 0.0055 for Hg.
1351.
Beadle, L.C. 1931. The effect of salinity changes on the water
content and respiration 6f marine invertebrates. Jour. Exp.
BioI. 8(3):211-227.
On transference to low salinity medium, both body weight and
respiration rate of Nereis diversicolor, a polychaete, at first in-
creased and then fell. With N. cultrifera, weight increased but did
not subsequently fall; respiratory rate also increased, but less than
that of N. diversicolor. Differences in respiratory rate were greater
in l6.6%-seawater than in 25% SW. N. diversicolor maintained activity
but N. cultrifera became inert in dllute water and died after exposure
for 50 hrs to 16.6% SW.
Respiratory rate of Gunda ulvae, a marine flatworm,
proportionally to initial osmotic gradient between animal and
ment. Swelling of Gunda was due to vacuolation of gut cells;
tissues appeared unaltered. Osmotic resistance mechanisms in
diversicolor and G. ulvae are different.
increased
environ-
other
N.
1352.
Beal, A.R. 1974. A study of selenium levels in freshwater
fishes of Canada's Central Region. Canada Dept. Environment
Fish. Marine Servo Tech. Rept. Ser. CEN/T-74-6: 14 pp.
A survey was conducted of selenium content in fishes of the
Central Region fishery, namely Ontario, Manitoba, Saskatchewan, Alberta,
and the Northwest Territories. Fish samples were ground and digested
in a nitric-perchloric-sulphuric acid mixture. Analyses were performed
using the fluorescence measurement of the selenium - 2, 3 - diamino-
naphthalene complex extracted into cyclohexane. Interfering elements
were masked with EDTA prior to extraction. Selenium ranged from a low
of 0.04 mg/kg to a high of 2.00 mg/kg with an average value of 0.33
mg/kg neglecting one result of 3.57 mg/kg obtained from a canned Beluga
Whale (Muktuk) sample. The overall average from each area is linked to
human population density; values were highest in the high population
areas (Great Lakes) and decreased in low population areas (Saskatchewan,
Alberta, and the Northwest Territories).
1353.
Beasley, T.M. and S.W. Fowler. 1976. Plutonium isotope ratios
in polychaete worms. Nature 262:813-814.
24
-------
Deposit-feeding Nereis diversico1or were exposed to: sedi-
ments labelled with Pu-238 and Pu-239 + 240, to sediments collected from
a former weapons test site, and to sediments from a nuclear fuel re-
processing plant. No preferential uptake of Pu-238 over Pu-239 + 240
was observed. .
1354.
Beasley, T.M. and S.W. Fowler. 1976. Plutonium and americium:
uptake from contaminated sediments by the polychaete Nereis
diversico1or. Marine Biology 38:95-100.
Nereid worms were exposed to marine sediments contaminated
with Pu and Am from testing of nuclear devices, or to sediments contain-
ing liquid wastes discharged from a nuclear fuel reprocessing plant.
In both cases uptake of Pu and Am was about 0.5% of the concentration
in sediments. Degree of relative uptake of Pu from both sediment types
was comparable; relative uptake of Am from sediments contaminated from
waste effluent was greater than that from nuclear test debris sediments.
Authors concluded that water may be the primary pathway for Pu accumu-
lation by deposit-feeding worms.
1355.
Beaven, G.F. 1946. Effect of Susquehanna River stream flow on
Chesapeake Bay salinities and history of past oyster mortal-
ities on upper bay bars. Contrib. No. 68, Ann. Rept., Mary-
land Bd. Nat. Res.:1-l1.
Meteorological and hydrographic evidence suggests that re-
corded major oyster mortalities at Head-of-the-Bay, Chesapeake Bay,
between 1908 and 1946 were associated with low salinities caused by
high run-off from the Susquehanna River.
1356.
Beck, A.B. 1956. The copper content of the liver and blood of
some vertebrates. Australian Jour. Zool. 4:1-18.
Copper in blood and liver of a wide range of vertebrate
species did not show phylogenetic trends. Mean liver concentrations
from 36 marine and aquatic species, including seal, humpback whale,
petrel, penguin, tortoise, crocodile, frog, elasmobranch, and fish
ranged from 10 to 256 mg Cu/kg dry fat-free weight. Mean blood con-
centrations from 13 diverse species ranged from 10.3 to 1.29 mg/l.
No differences attributable to sex were observed except in salmon
Arripis trutta; males contained 15 mg Cu/kg liver and females 45
mg/kg.
25
-------
1357.
Bellamy, D. 1961. Movements of potassium, sodium and chloride
in incubated gills from the silver eel. Compo Biochem.
Physiol. 3:125-135.
Isolated gills from fresh and salt water silver eels, Anguilla
anguilla, were incubated aerobically and anaerobically in either tap
water or seawater. Net changes in K, Na, and Cl content were determined
Under all conditions, isolated gills were nearly impermeable to K, re-
taining a K content of 1.6 mg/g wet wt. Gills incubated in freshwater
had an initial drop in Na from 1.4 to 1.2 mg/g wet wt, while salt water
gills gained Na from an initial 1.9 mg/g to 2.5 mg/g. A constant level
of sodium chloride was maintained in isolated gills under aerobic con-
ditions against the normal diffusion gradient to which the eel was
adapted. The constant Na content appeared to result from a steady state
in which passive diffusion was balanced by an active movement of Na in
the opposite direction.
1358.
Bellrose, F.C. 1951.
fowl populations.
135.
Effects of ingested lead shot upon water-
Trans. 16th North Amer. Wildl. Conf.:125-
Of 4561 mallards trapped during autumn of 1949 and 1950, an
average of 7.69% contained ingested lead shot, with the percentage in-
creasing as the hunting season progressed. Ducks fed one shot and then
released averaged about 9.0 km per day before being shot; those fed two
shots travelled 6.7 km per day. Control ducks averaged 11.3 km daily
before being shot. Of ducks banded and released in 1950, the total
amount of bands returned by hunters were 11% for controls, 14% for ducks
fed one shot, and 22% for ducks fed two pellets.
1359.
Benayoun, G., S.W. Fowler, and B. Oregioni. 1975. Flux of cad-
mium through euphausiids. Marine Biology 27:205-212.
In 15 days, Megancytiphanes norvegica accumulated Cd-l09 by a
factor of 180 directly from water and 240x from a water and food
(Artemia) milieu. Approximately 10% of ingested Artemia Cd-l09 was in-
corporated into internal tissue. After 1 month, Cd accumulated directly
from water was most concentrated in viscera with lesser amounts in eyes,
exoskeleton and muscle. Cd concentration from ingested food increased
nearly 5x during passage through ~. norvegica and accounted for 84% of
total Cd flux through the euphausiid. Fecal pellet deposition is the
principle downward Cd transport mechanism by this species. Natural
euphausiids had Cd concentrations in mg/kg dry wt, of 0.7 in whole
animal, 2.1 in molts, 9.6 in feces and 0.3 in eggs. Food, consisting
of phytoplankton, microcrustacea and detritus had 2.1 mg Cd/kg dry wt.
26
-------
A simple model, assuming that Cd intake equals Cd released
plus that accumulated in tissue, allowed assessment of various meta-
bolic parameters in controlling Cd flux through euphausiids.
1360.
Bender, J.A. 1975. Trace metal levels in beach dipterans and
amphipods. Bull. Envir. Contamin. Toxicol. 14(2):187-192.
Over a seven week period beach hoppers Orchestoidea cornicu-
lata and marine flies (Coelopa vanduzeei, Fucellia rufitibia) from four
California beach sites were analyzed for trace element levels. Flies
showed consistently higher levels of Zn, Fe, Cu, and Cd than hoppers.
The approximate ranges (in mg/kg) in flies and hoppers, respectively,
were: Zn150->300and 60-120, Fe 100-225 and 30-115, Cu 10-125 and 5-70,
Cd 40-150 and 10-30. Manganese was low «10 mg/kg) in all beach arthro-
pods tested. Lead, nickel, and silver occurred only in trace amounts.
Metal levels were similar in adult and juvenile hoppers. No difference
was found between the two species of marine flies. Iron levels in the
hopper fluctuated greatly over time; Cu, Pb, and Zn fluctuated moderately,
but Cd, Mn, Ag, and Ni remained stable.
1361.
Bender, M.L., R.B. Lorens, and D.F. Williams. 1975. Sodium,
magnesium and strontium in the tests of planktonic foramin-
ifera. Micropaleontology 21:448-459.
Na/Ca, Mg/Ca and Sr/Ca atom ratios of planktonic foraminifera
analyzed from sediments of the North Atlantic and Tasman Sea ranged from
1.2 x 10-3 to 7.1 x 10-3. Na and Sr appear to be homogenously distrib-
uted throughout the test; Mg is more variable. Na/Ca, Mg/Ca, and Sr/Ca
atom ratios of individual species from an Upper Pleistocene core section
in the Tasma Sea decrease with increasing growth depth of each species.
Atom ratios of Globigerinoides sacculifer and G. ruber samples from
recent North Atlantic sediments vary similarly-to those of Tasman Sea
sample, but do not show any statistical temperature dependence. Na/Ca
and Sr/Ca atom ratios in the foraminiferal calcite are higher by a fac-
tor of 5 to 10 than predicted from distribution coefficient data; Mg/Ca
atom ratios are lower than predicted, assuming crystal growth occurs in
a solution of composition similar to sea water.
1362.
Bengtsson, B.-E. 1974. The effect of zinc on the ability of the
minnow, Phoxinus phoxinus L., to compensate for torque in a
rotating water-current. Bull. Environ. Contamin. Toxicol.
12(6):654-658.
"Critical rpm"-defined as the point when a fish, unable to
compensate for the torque of a rotating flow, is forced to rotate-was
27
-------
determined for undery€arlings, yearlings, and mature fish exposed to sub-
lethal concentrations of zinc. For underyearlings, mean critical rpm
decreased significantly at zinc levels of 0.06 mg/l and 0.16 mg/l after
108 days of exposure. After 109 days, yearlings exposed to 0.16, 0.33,
and 0.78 mg/l Zn exhibited lower critical rpm's than controls; no effect
was observed at 0.06 mg/l. Yearlings were also less sensitive after 150
days of exposure to Zn; only 0.30 mg/l level producing a decrease.
Adults showed decreasJs at levels of 0.20 and 0.31 mg/l after 100 days;
after 270 days of exposure only 0.30 mg/l level produced a reduction.
Reduced swimming ability may be caused by vertebral damage.
1363.
Bengtsson, B.-E. 1974. The effects of zinc on the mortality and
reproduction of the minnow, Phoxinus phoxinus L. Arch.
Environ. Contamin. Toxicol. 2:342-355.
Long-term effects of zinc nitrate on repr~duction and mortal-
ity during different developmental stages of the freshwater teleost
Phoxinus phoxinus were studied. Mortality of newly-hatched fry was the
most sensitive parameter when compared to: numbers of eggs deposited;
hatchability; and mortality of underyearlings, yearlings and mature min-
nows. Fry showed an increased mortality at a Zn concentration of 0.08
mg/l, which is 1/40th of the 96-hr LC-50 estimated for adults.
1364.
Bengtsson, B.-E. 1974. Vertebral damage to minnows Phoxinus
phoxinus exposed to zinc. Oikos 25:134-139.
Adult minnows exposed to different concentrations of Zn(N03)2
in fresh water, developed hemorrhages and lesions. Vertebral damage
occurred between 0.20 and 2.4 mg/l of Zn; this is below the LC-50(96h)
value of 3.2 mg/l. The striking similarity between symptomology of zinc
and that produced by organophosphate compounds is discussed.
Bengtsson, B.-E. 1974. Effect of zinc on the movement pattern
of the minnow, Phoxinus phoxinus L. Water Research 8:829-833.
A shoal of 30 minnows developed hyperactivity as a response to
a gradually increased zinc concentration from 0.00 to 0.39 mg Zn/l. The
increase in rate of activity seems to be more closely related to rate of
increase in concentration of Zn, rather than concentration itself. This
behavior was followed by a period when the fish displayed hypoactivity.
Besides quantitative alterations in activity there were also changes in
the distribution between diurnal and nocturnal activity.
1365.
28
-------
1366.
Bengtsson, B.-E. 1974.
Phoxinus phoxinus.
Effect of zinc on growth of the minnow,
Oikos 25:370-373.
Reduced growth occurred in yearlings and adults of tris fresh-
water fish following exposure over a ISO-day period to <0.02, 0.05, 0.13,
0.20, and 0.30 mg/l of zinc, as zinc nitrate. Yearlings were more sensi-
tive than adults and showed reduced growth at 0.13 mg/l Zn as compared to
0.20 mg/l for adults; these values correspond to 1/25 and 1/16 of the
estimated LC-50 (96 hr), respectively. Suppressed growth was associated
with reduced Tubifex consumption. -
1367.
Bengtsson, B.-E., C.H. Carlin, A. Larsson, and O. Svanberg.
1975. Vertebral damage in minnows Phoxinus phoxinus L. ex-
posed to cadmium. Ambio 4:166-168.
The 70-day continuous flow LC-50 value for Phoxinus and cad-
mium chloride at 60/00 salinity and 12.9 C was 0.420 mg/1 Cd2+; the LC-50
(96 hr) value was 39.0 mg/l Cd2+. About 30% of all survivors at 70 days
developed lesions in the spinal column; these injured fish survived due
to adequate shelter, food, and Jack of enemies in test aquaria, but
probably would have died under natural conditions. Concentrations as
low as 0.0075 mg/l were sufficient to produce vertebral damage; about
33% of the survivors exhibited damage at 0.100 mg/l; maximum number of
vertebral abnormalities (67%) were associated with 0.960 mg/l of Cd2+.
There were no spinal deformations in controls.
1368.
Benijts-Claus, C. and F. Benijts. 1975. The effect of low lead
and zinc concentrations on the larval development of the mud-
crab, Rhithropanopeus harisii Gould. In: Koeman, J.H. and
J.J.T.W.A. Strik (eds.). Sublethal effects of toxic chemi-
cals on aquatic animals. Elsevier Sci. Publ. Co., Amsterdam:
43-52.
Up to 50 ug/l of Zn2+ or Pb2+ significantly delays larval
development of mudcrabs. Mean development time, in days, from hatch to
megalopa stage was 14.35 in controls, 15.40 for 25 ug Zn2+/l, 15.20 for
50 ug Zn2+/l, 14.56 for 25 ug Pb2+/l, 15.40 for 50 ug Pb2+/l, but only
13.48 for a mixture of 25 ug Zn2+/l and 25 ug Pb2+/l, and only 14.73 for
a mixture of 50 ug Zn2+/l and 50 ug Pb2+/l. The effect of Pb2+ masks
that of Zn2+ when mixtures are tested. Some combinations neutralize
toxic effects of lead and may even accelerate larval growth.
1369.
Beninson, D., E.V. Elst and D. Cancio. 1966. Biological aspects
in the disposal of fission products in surface waters. In:
Disposal of Radioactive Wastes into Seas, Oceans and Surface
29
-------
Waters, Int. Atom. Ener. Agen., Vienna, Austria:337-354.
Studies conducted by the Argentine Atomic Energy Commission
on uptake of fi$sion products, including isotopes of Ca, Ce, Cs, K, Ru,
Sr; and Zr, by fresh water teleosts, molluscs, crustaceans and vascular
plants are summarized. In transfer of Sr via aquatic food chains, Sr-
to-Ca discrimination factors were more significant for risk estimation
than concentration factors (CF). Vascular plants slightly prefer Sr
to Ca with discrimination factors (DF) ranging from 1.0 to 2.5. Mol-
luscs and freshwater discriminate against Sr with factors ranging from
0.35 to 0.75 according to species; DF hold over a wide range of Ca and
other ion concentrations in water, and allow reliable predictions of
biota levels. Cesium-to-potassium ratios were dependent on K concen-
tration. Uptake of Cs is therefore characterized by CF. Aquatic vas-
cular plants substantially concentrate Cs, Ru, Zr and rare earth radio-
nuclides; CF ranging from 200 to 30,000 according to species and nuclide.
Particularly important concentrations are found for Ceo Molluscs and
teleosts have much lower CF for these nuclides (from 10 to a few
hundreds).
In field conditions, substantial fractions of disposed acti-
vities are removed from water by exchange with bottom materials and
sedimentation of suspended particles carrying radioactivity. Results
in natural ponds with low water-renewal rates show removals of 90% of
Cs, 40% of Ru, 60% of Zr and 90% Ce radionuclides. Some species tested
were reasonably good indicators, including "present level indicators"
which follow changes in environment and "integrating monitors" which
relate cumulative environmental contamination.
1370.
Benoit, D.A. 1975. Chronic effects of copper on survival,
growth, and reproduction of the bluegill (Lepomis macro-
chirus). Trans. Amer. Fish. Soc. 104(2):353-358.
During 22-month exposure of sunfish to copper in soft water,
survival of adults was reduced, growth retarded, and spawning inhibited
at 162 ug/l of copper. Tissue residue analysis of gill, kidney, and
liver indicated that Cu had accumulated in some or all of these tissues
at test water concentrations of 40 to 162 ug Cull. Copper residues in
brain, spleen, gonad and muscle tissue of fish exposed to 162 ug Cull
did not differ significantly from residues in controls. Survival of
larval fish after exposure for 90 days to copper was adversely affected
at 40 to 162 ug Cull. The maximum acceptable toxicant concentration of
copper to this species in water with a hardness of 45 mg/l and pH range
7 to 8 lies between 21 and 40 ug Cull, or 1.9 to 3.6% of the mean 96-hr
LC-50 for juveniles (1,100 ug Cull).
30
-------
1371.
Benoit, D.A. 1976. Toxic effects of hexavalent chTomium on brook
trout (Salvelinus fontinalis) and rainbow trout (Salmo
gairdneri). Water Research 10:497-500.
Brook trout exposed for 22 months and rainbow trout for 8
months to hexavalent chromium showed increased alevin mortality at 0.35
mg/l and temporarily retarded growth at 0.10 mg/l, the lowest level
tested. Reproduction and embryo hatchability of brook trout were un-
affected at Cr+6 concentrations deleterious to survival of newly hatched
alevins. Maximum acceptable toxicant concentration for brook and rainbow
trout exposed to Cr+6 in water with a hardness of 45 mg/l (as CaC03) and
a pH range of 7-8 lies between 0.20 and 0.35 mg Cr/l. LC-50 (96 h)
values for brook and rainbow trout were 59 and 69 mg Cr+6/1, respectively.
1372.
Benoit, D.A., E.N. Leonard, G.M. Christensen, and J.T. Fiandt.
1976. Toxic effects of cadmium on three generations of brook
trout (Salvelinus fontinalis). Trans. Arner. Fish. Soc. 105:
550-560.
Three generations of trout were exposed to cadmium at dif-
ferent concentrations ranging between 0.06 and 6.4 ug Cd/I. Cadmium at
3.4 ug/l caused significant numbers of deaths in first-and second-gener-
ation adult males during spawning, and retarded growth of juvenile
second-and third-generation offspring. In Lake Superior water (hardness
44 mg/l as CaC03, pH 7-8), the maximum allowable toxicant concentration
fell between 1.7 and 3.4 ug Cd/I. Kidney, liver and gill tissue accumu-
lated the greatest amounts of cadmium which reached an equilibrium con-
centration in first- and second-generation trout after 20 weeks. No
increases in Cd were found in edible muscle in any Cd concentration
tested. Cadmium loss from gill tissue of second-generation trout was
rapid after transfer to Cd-free water for 12 weeks but there was no loss
from liver and kidney.
1373.
Benoit, R.J., J. Cairns, Jr., and C.W. Reimer. 1968. A limno-
logical reconnaissance of an impoundment receiving heavy
metals, with emphasis on diatoms and fish. Reservoir Fish.
Resources Symp., Arner. Fish Soc., Apr. 5-7, 1967: 31 pp.
Causes of fishkills occurring sporadically below a reservoir
near Redding, California, were investigated. A survey indicated that
upper tributaries of the reservoir had typical varieties of flora and
fauna but a lower tributary and its two branches were severely degraded
by acid mine drainage. This degrading influence was also detected at
the lower portion of the reservoir and upper portion of a lake which
lies below the reservoir. Diatometer surveys confirmed these results
and indicated increased damage to diatom flora in the lower portion of
31
-------
the reservoir and upper portions of the lake during high water flow due
to dam regulation. Waters of the lower tributary had very low pH and
high concentrations of iron (up to 512 mg/l), zinc (up to 164 mg/l), and
copper (up to 64 mg/l). Delta muds of this tributary also contained
high levels of Fe (170 and 126 mg/g), Zn (3.5 and 2.9 mg/g) and Cu
(0.2 and 0.1 mg/g dried mud). Large quantities of hydrous iron oxides
were sedimented in the reservoir below the tributary entrance.
LC-50's were determined for waters from the branches of the
lower tributary and for suspensions of tributary mud. LC-50 (48 hr)
values for native chinook salmon Oncorhynchus tschawytscha, ranged from
1.33 to 0.56% test water in dilution water. For hatchery fish these
values were 0.55% to 0.56%. In the lower tributary, LC-50 was 8.3% for
both native and hatchery fish. Results show that both tributary water
and delta sediments were toxic; analysis of flow conditions indicated
that toxic conditions could also develop in the lower reservoir and upper
lake due to acid water and heavy metals discharged from the tributary.
1374.
Benson, W.W., D.W. Brock, J. Gabica, and M. Loomis. 1976. Swan
mortality due to certain heavy metals in Mission Lake area,
Idaho. Bull. Environ. Contamin. Toxicol. 15:171-174.
Swans Olor columbianus found dead in the Mission Lake area of
lower Couer d'Alene-Tiver valley in Idaho were autopsied and analyzed
for lead. Mean Pb levels in mg/kg wet wt from 13 swans were 74.5 in
spleen, 45.1 in kidney, 40.3 in bone, 8.6 in heart, 8.9 in brain, and
11.0 in flesh. Lead poisoning probably resulted from local mines and
smelters. Only one bird had lead shot in the gizzard. Authors state
that ingestion of Pb contaminated vegetation is the probable cause of
death.
1375.
Benson, W.W., D.W. Brock, J Gabica, and M. Loomis.
cide and mercury levels in pelicans in Idaho.
Contamin. Toxicol. 15:543-546.
1976. Pesti-
Bull. Environ.
Twelve white pelicans Pelicanus erythrorhynchos were col-
lected and analyzed for mercury and pesticide residues. Mean Hg con-
tent in mg/kg wet wt was 12.5 for liver, 3.7 for feathers, 3.8 for
kidney, 2.3 for heart, 0.3 for bone, 3.4 for muscle, and 1.2 for brain.
Since Hg concentrations in fish from the same area ranged from 0.12 to
0.94 mg/kg wet wt, it was concluded that pelicans accumulated Hg from
their fish diet.
1376.
Benson, W.W., W. Webb, D.W. Brock, and J. Gabica. 1976. Mer-
cury in catfish and bass from the Snake River in Idaho.
32
-------
Bull. Environ. Contamin. Toxicol. 15:564-567.
Catfish Ictalurus punctatis, and bass Micropterus dolomeieu,
of different age groups from impounded and free flowing sections of the
Snake River in Idaho were analyzed for mercury. An increase was observed
in Hg content from 0.59 to 0.72 mg/kg wet wt, between two and four year
old bass from impounded waters, and 0.67 to 1.15 mg/kg wet wt, for the
same age period in free flowing waters. There was an increase in mean
values from 0.65 to 0.79 for bass from impounded to free flowing waters.
For catfish, both trends seemed to be reversed. Mercury concentration
for catfish decreased from 0.60 to 0.51 mg/kg wet wt, between ages 5 and
8 yrs in impounded waters, and from 0.36 to 0.27 mg/kg wet wt for the
same year classes in free flowing waters.
1377.
Bentley, P.J., J. Maetz and P. Payan. 1976. A study of the uni-
directional fluxes of Na and Cl across the gills of the dog-
fish, Scyliorhinus caniculata (Chondrichthyes). Jour. Exp.
BioI. 64:629-637.
Dogfish gills were more permeable to Cl than to Na. Net
accumulation of Cl could be accounted for by diffusion along observed
electrochemical gradient but Na movement was more consistent with an
electrically neutral active Na transport mechanism. When external pH
was changed from 7.8 to 6.9 influxes of Na and Cl were depressed,
effluxes were unaffected, and fish became slightly less electronegative.
In artificial solutions in which concentrations of Na and Cl were lowered
and replaced with urea to maintain total osmotic concentration, Na in-
flux displayed saturation kinetics, while Na efflux increased with de-
creasing Na concentrations. Cl influx decreased linearly but Cl efflux
remained constant. Efflux of Cl could not be reconciled with a process
of passive diffusion along any of the observed electrochemical gradients
and this could reflect presence of an active transport mechanism.
1378.
Berg, A. 1968. Studies on the metabolism of calcium and
tium in freshwater fish. I. Relative contribution of
and intestinal absorption. Mem. 1st. Ital. Idrobiol.
161-196.
stron-
direct
23:
Using Sr-85 as a tracer added to water or food, exchange
rates were estimated for Ca and Sr in goldfish Carassius auratus. A
depressed exchange rate occurs in starved fish when compared to fish
fed a maintenance ration. Accumulation of Sr-85 is constant over a
wide range of Sr concentrations in water and food. For stable Sr, ex-
change rate is directly proportional to these concentrations. Ca ex-
change rate from food is proportional to Ca levels in food, but Sr ex-
change rate for a definite Sr concentration in food is reduced by in-
33
-------
creasing Ca levels in food. An inverse proportionality was found be-
tween accumulation rate of Sr-85 and Ca concentration in water. Result-
ing accumulation rate of Ca may be considered as constant over a range
of 2.3 mg Call to 23 mg Call in water. In presence of Ca in food, accumu.
lation rate of Ca from water increases regularly with Ca concentration in
water. In natural conditions, where Sr/Ca ratio in food is lower than in
water, and Ca concentration in food does not exceed 4,000 mg/kg, contri-
bution of direct exchange for Ca and Sr is >80% for Lake Maggiore water
(22-23 mg/l Ca) and >65% for Ca ~oncentration in water as low as 4.5
mg/l. Scales are the most important tissue in fish for Ca and Sr ex-
change. This exchange in scales is due to direct absorption through
gills and secondary accumulatiop in scales via blood.
1379.
Berg, A. 1969. Use
bution of direct
freshwater fish.
active Materials.
of Sr-85 for the determination of the contri-
and intestinal absorption of Ca and Sr in
In: Environmental Contamination by Radio-
-Proc. Seminar. IAEC, Vienna: 325-338.
Ca and Sr exchanges were studied in goldfish under conditions
of zero growth. Exchange rate from water increased asymptotically with
Ca concentration in water when Ca concentration in food equalled 8000
mg/kg; this is constant when Ca concentration in food is zero. Exchange
rate of Ca from water into fish body is not dependent on absolute value
of influx rate from water but on value of ratio between influx rate from
water: total influx rate from water and food.
1380.
Berg, W., A. Johnels, B. Sjostrand, and T. Westermark. 1966.
Mercury content in feathers of Swedish birds from the past
100 years. Gikos 17:71-83.
Tail feathers from 11 species of birds dating back to 1829
were analyzed for Hg. During the years 1840-1940, levels varied between
species but were roughly constant with each species. Differences between
species were due primarily to different food chains. In the 1940's Hg
levels increased 10-20x. The main Hg sources commencing in the 1940's
~ere the methyl-Hg compounds, and these were chiefly responsible for the
lncrease. The mean level for the white-tailed eagle Haliaetus albicilla
from 1832 to 1940 was 6600 ng/g, with a range of 2700 to 15,000 ng/g.
In 1965 these fish-eating sea eagles had Hg levels as high as 65,000
ng/g, with Hg concentrations in eggs of 5,000 to 11,000 ng/g; eggs with
these levels seldom hatched.
1381.
Berland, B.R., D.J. Bonin, V.I. Kapkov, S.Y. Maestrini and D.P.
Arlhac. 1976. Action toxique de quatre metaux lourds sur
34
-------
la croissance d'algues unicellulaires marines. C.R. Acad.
Sci. Paris, t. 282, Ser. D: 633-636. (In French.)
Chloride salts of Hg, Cd, Cu, and Pb were tested against 18
species of unicellular marine alga. Concentrations causing growth
inhibition after 17 days at 20 C, in ug metal/I, ranged from <5 to 15
for Hg, 5 to 250 for Cd, 10 to 500 for Cu, and 250 to 2000 for Pb.
Lethal concentrations during this same interval ranged from 10 to 25 ug/l
for Hg, 50 to >1000 ug/l for Cd, 20 to >1000 ug/l for Cu, and 2000 to
>2000 ug/l for Pb. Dinoflagellates were comparatively sensitive to
copper.
1382.
Bernhard, M. and A. Zattera. 1975. Major pollutants in the
marine environment. In: Pearson and Frangipane (eds.).
Marine Pollution and Marine Waste Disposal. Pergamon Press,
New York: 195-300.
Data are reviewed, summarized, and tabulated on concentrations
of Hg, Cd, Pb, Cu, Ni, Zn, Cr and As in seawater, sediments and various
groups of marine biota--including algae, higher plants, crustacea, brya-
zoa, coelenterata, mollusca, teleosts, echinoderms, annelids, mammals,
and fish-eating birds. Toxicity of these and other compounds (pesti-
cides, petrochemicals, detergents) to marine organisms are tabulated and
reviewed. Calculations are presented on maximum permissible weekly in-
take of various pollutants by man; results suggest that Hg intake from
fish is excessive for certain minorities such as fishermen and their
families.
1383.
Bernheim, F. 1971. The effect of cyanogen iodide and mercuric
chloride on the permeability of cells of Pseudomonas aeruginosa
and the antagonistic action of sulfhydryl compounds. Proc.
Soc. Exp. BioI. Med. 138:444-447.
Mercurials increased swelling rates of P. aeruginosa in NaCl
~o a much greater extent than sodium sulfate; sodium phosphate had an
intermediate effect. The rapid but reversible reaction of HgC12 with
cell sulfhydryl groups makes possible determination of degree of pene-
tration of various antagonists to different sulfhydryl sites. Mercuric
chloride reacts with 30-50% of all available reactive sulfhydryl groups
in cell within 10 sec of incubation at 23 C, with 80-90% reacting in 9
min. These rapidly reacting sulfhydryl groups can be considered to be
on or near the surface of the membrane and probably also react with non-
penetrating p-hydroxymercuribenzoate. The more slowly reacting sulf-
hydryl may be in the membrane or prevented from reacting rapidly by
steric hindrance. Since effect of Hg is reversible, the antagonist
35
-------
should be equally effective regardless of time of its addition if the
antagonist has access to all sites of interaction. This is true for
mercaptoethylamine, cysteine hydantoin, and dithiothreitol, but not for
cysteine. This compound cannot apparently penetrate the membrane very
far because it becomes increasingly less effective in reversing effect
of Hg as latter is allowed to react for longer periods of time with cells.
1384.
Bertine, K.K. and E.D. Goldberg. 1972. Trace elements in clams,
mussels, and shrimp. Limnology and Oceanography 17:877-884.
Compositional changes in trace element content of shells of
mussels and clams that might be related to man's influence on the compo-
sition of inshore marine waters over the past hundred years were sought
but not found. The following average values were found in the clams
Ensis arcuatus and E. siliqua, respectively, in mg/kg dry wt: Fe 66 and
75; Co 0.034 and 0.035; Sb 0.028 and 0.014; Zn 1.40 and 0.84; Sc 0.005
and 0.008; Se 0.060 and 0.033; Ag 0.022 and 0.017; Cr 0.14 and 0.13; and
Hg 0.11 and 0.10. Values for the mussel, Mytilus edulis, also in mg/kg
dry wt, for both shell and fresh soft part (1971 specimens only) were,
respectively: Fe 8.9 and 776; Co 0.029 and 1.74; Sb 0.022 and 0.11; Zn
0.59 and 40; Sc 0.004 and 0.19; Se 0.046 and 4.5; Ag 0.006 and 0.15; Cr
0.10 and 1.23; and Hg 0.49 and 0.97. Contamination from preservatives
was evident in shells and tissues of museum specimens. Elemental concen-
trations in calcareous shells, both aragonitic and mixed aragonitic-
calcite, are similar and may reflect composition of waters in which they
lived, rejection by organisms, or surface associated features.
Proteinaceous molts of shrimp contained high levels of these
elements, in agreement with previous investigations. These levels in
molts (as compared to tissue levels), in mg/kg dry wt, were: Rb 3.2
(4.8); Fe 32 (62); Co 0.47 (0.46); Sb 0.03 (0.15); Zn 76 (39); Se 5.0
(6.1); Ag 1.1 (0.24); and Hg 1.3 (1.3). With 20 to 25 mOlts/shrimp/year,
the molting shrimp discharges its body burden of trace elements at least
20 to 25 times, causing a significant redistribution of these elements
within the marine enviropment.
1385.
Bertrand, G. 1902. Sur l'existence de l'arsenic dans l'organisme.
Compt. Rend. Acad. Sci. (Paris) 134:1434-1437.
Arsenic was normally present in many species of birds and
mammals including thyroid glands of seals Phoca barbata captured off
Spitzberg; seal thyroids contained about 0.2 mg As/kg wet wt.
1386.
Bertrand G.
animale.
1902. Sur l'existence de l'arsenic dans la serie
Compt. Rend. Acad. Sci. (Paris) 135:809-812.
36
-------
Arsenic, in mg/kg dry wt, ranged between 0.05 and 0.15 for
various and diverse tissues of marine organisms collected at depths up
to 1800 m between Gibralter and the Azores. Tissues examined included
skin of killer whale Orca gladiator; feathers of petrals (birds); skin,
muscle or scales from several species of fishes and elasmobranchs; whole
cuttlefish, holothurians, sea urchins, anemones, starfish, and sponge;
and soft parts of gooseneck barnacles.
1387.
Bertrand, G. and R. Vladesco. 1921. Sur les causes de variation
de la teneur en zinc des animaux vertebres: influence de
l'age. Compt. Rend. Acad. Sci. (Paris) 172:768-770.
Individuals of 3 species of fishes were analyzed for whole
body zinc. Ide Idus orfus, of age 7, 19, and 33 months, contained 142,
36, and 18 mg Zn per kg wet wt, respectively. For tench of age 7, 19,
33, and 84 months, Zn was 60, 81, 88, and 31 mg/kg wet wt, respectively.
In herring, smaller fish contained 22 and larger herring 50 mg Zn/kg wet
wt. These results do not conform exactly to the general conclusion based
on other studies conducted by authors with birds and mammals that body
burdens of zinc decrease with increasing age.
1388.
Bertrand, G. and R. Vladesco. 1923. Sur la teneur en zinc du
corps et de certains organes des invertebres. Bull. Soc.
Chim. France 33:341-345.
Zinc in mg/kg wet wt in whole body meats and selected tissues
was determined for several species of marine molluscs and crustaceans.
Whole oyster Ostrea edulis ranging in age from 18 months to 4 years con-
tained 16 to 27 mg/kg; values were considerably higher for Portuguese
oysters Gryphea angulata of similar age range: 500 to 1310 mg/kg. Zinc
content of other bivalve molluscs including mussels, clams, cockles, and
scallops did not exceed 35 mg/kg except scallops (93 mg/kg). Gastropod
molluscs, including the land snail Helix asperata, squid Sepia offici-
anilis, and lobster were all below 59 mg Zn/kg whole body wet wt.
Mantle tissue of 4-year old Portuguese oysters contained up to 1074 mg
Zn/kg wet wt, but this was quite variable. Edible muscle of crabs and
other crustaceans did not exceed 67 mg Zn/kg wet wt.
1389.
Betzer, N. and Y. Kott.
II. Cladophora sp.
1969. Effects of halogens on algae -
Water Research 3:257-264.
Along with halogens, copper sulphate was tested for its
effects on the filamentous algae Cladophora sp. Copper sulphate had no
effect in 24 hrs at concentrations below 20 mg/l. At 20 mg/l there was
slight leaking of cell content through cell wall after 3 hrs. This
37
-------
effect became stronger at 50 mg/l, along with contraction of cytoplasm
and change in cell morphology after 24 hrs. At 100 mg/l these effects
were more pronounced at longer exposure periods. A concentration of 5
or 10 mg/l CuS04 was fatal: all algae died in 4 days; 40 mg/l CUS04 at
5 hrs was also lethal. Penetration of CUS04 into algal cell caused total
enzymatic inhibition, with chlorophyll disappearing and cell becoming
discolored.
1390.
Betzer, S.B. and M.E.Q. Pilson. 1975. Copper uptake and excre-
tion by Busycon canaliculatum L. BioI. Bull. 148:1-15.
Pathways of copper into the gastropod Busycon canaliculatum
and sites of accumulation were investigated in uptake experiments using
Cu-64. Routes of possible copper loss were investigated in excretion
experiments and by determination of copper content of egg capsules. Up-
take of dissolved Cu-64 followed a smooth curve, slowing with time.
About 2/3 of the available Cu-64 was absorbed by 48 hr; the rate was pro-
portional to concentration of the medium. Among soft tissues, Cu-64
appeared first on gills, which in 1 hr reached a normalized concentration
100 times that initially present in the medium, and in the blood and kid-
ney (normalized concentration = 1 at 1 hr). By 6 hr Cu-64 appeared in
gut and digestive gland (normalized concentration = 5). Cu-64 continued
to accumulate in digestive gland; by 48 hr, this tissue contained 50% of
the total copper taken up by gill and organs comprising visceral mass.
Transfer of absorbed copper to digestive gland continued even when whelks
were removed to unlabeled seawater for 24 hr. Separations carried out on
blood from whelks labeled with Cu-64 indicated that the absorbed copper
in the blood was nonspecifically bound to hemocyanin. Excretion rates
for copper averaged 7 ug/24 hr per 100 g fresh tissue weight, and
appeared unaffected by the copper concentration of the medium. Under
normal environmental copper concentrations, rates of dissolved copper
uptake and of copper excretion are probably about equal. The average
copper content of egg capsules was 23 ug/capsule. Spawning may be a
significant route for copper loss, and an increase in copper excretion
in autumn is also suggested as an explanation for a drop in tissue copper
concentrations at this season.
1391.
Betzer, S.B. and P.P. Yevich. 1975. Copper toxicity in Busycon
canaliculatum L. BioI. Bull. 148:16-25.
The effects of high concentrations of copper in seawater upon
the gastropod Busycon canaliculatum were followed histologically, by
determination of tissue Cu concentrations, and by tracing uptake with
Cu-64. Whelks showed a high resistance to ionic Cu with a tolerance
limit between 200-500 ug/l at normal habitat temper~tures for the ex-
posure periods used (54-77 days). At lethal concentrations of 500 and
38
-------
1000 ug/l, Cu was accumulated by gill and osphradium; these tissues also
showed progressive histopathologic change, consisting of swelling of gill
filaments, amebocytic infiltration of connective tissues, and necrosis
and sloughing of mucosa.
1392.
Bieri, R. and D.M. Krinsley. 1958. Trace elements in the pelagic
coelenterate, Vellela lata. Jour. Mar. Research 16:246-254.
Trace element content for whole body of V. lata, expressed as
percent of ash, ranged from 5.0 to 7.1 for Mg, 0.56~0~ for Ca, 0.16
to 0.36 for AI, 0.071 to 0.22 for Cu, 0.0007 to 0.0041 for Mn, 0.0033 to
0.022 for Ni, and 0.046 to 0.14 for Ti. Conversion factors are given to
convert ash weight to dry or wet wt. Other elements measured qualita-
tively were in concentrations greater than the following limiting sensi-
tivities, in mg/kg: Fe 10, Si 10, Cr 100, Sr 200, V 70, Ba 100, Ag 3,
Pb 10, and Mo 10.
1393.
Biesiot, P. and A. Venkataramiah. 1974. Effect of salinity on
behavior and survival of postlarval shrimp, Penaeus aztecus
in relation to ageing. Amer. Zool. 14:1259.
"Normal," "critical" and "lethal" salinity tolerance ranges
of postlarval shrimp acclimated to 320/00 were determined by direct
transfer to 16 test salinities ranging from 1.8 to 360/00. Effects of
acclimatization to intermediate concentrations (25 and 180/00) on
salinity tolerance were also determined. Testing began with 10 day
post larvae (6.0 mm) and repeated at 3 day intervals up to 31 days when
larvae were 19.6 mm. Salinity tolerance in young shrimp was size and
age dependent; large postlarvae had a wider normal range than smaller
shrimp of identical age. Normal tolerance range expanded as shrimp became
older. By acclimation, post larvae from 18 and 250/00 extended their
tolerance to very low salinities at a younger age than those from 320/00
S. At 19 days shrimp initiated escape behavior from the stress, the
strength of which increased with age. This reaction plus greater sur-
vival rates for older and larger animals suggest the gradual development
of osmosensitive and osmoregulatory mechanisms enabling shrimp to with-
stand reduced salinity. The impact of heavy spring rain on summer
shrimp populations is discussed.
1394.
Billen, G., C. Joiris and R. Wollast. 1974. A bacterial methyl-
mercury-mineralizing activity in river sediments. Water
Research 8:219-225.
A bacterial activity involving mineralization of methyl-
mercury was observed in bottom sediments of the river Sambre in Belgium,
39
-------
in a zone heavily polluted with inorganic mercury. After 90 hrs incuba-
tion with an initial concentration of 1000 bacteria/ml and 85 ug Hg/l as
methylmercury, the methylmercury decreased to <10 ug Hg/l while metallic
mercury increased from <5 ug Hg/l to 40 ug Hg/l. Bacterial density
dropped to 30/ml after 15 hours. At this point, mercury resistant bac-
teria were selected with exponential growth observed until final density
of 5 x 106 bacteria/ml was reached. Mineralizing capacity of the com-
munity can be increased in response to increased concentrations of
methylmercury, through selection of methylmercury-resistant bacterial
species, among which organisms responsible for methylmercury mineraliza-
tion constitute only a part. Authors suggest that some equilibrium can
be reached between degradation of methylmercury and its addition to, or
its production in, mercury polluted environments.
1395.
Birdsong, C.L. and J.W. Avault, Jr.
chemicals to juvenile pompano.
1971. Toxicity of certain
Prog. Fish-Cult. 33:76-80.
Toxicity of therapeutic chemicals routinely used in parasite
and disease control, including copper sulfate, acriflavin, formalin, and
potassium permanganate was determined for juvenile pompano, Trachinotus
carolinus at different salinities. LC-50 (96 hr) values in mg/kg of
copper sulfate at salinities of 10, 20 and 300/00 were 1.4, 1.5 and 2.0,
respectively. LC-50 (96 hr) values, in mg/kg of potassium permanganate
at salinities of 10, 20 and 300/00 were 2.9, 1.6 and 1.6, respectively,
and demonstrated that pompano were more sensitive to permanganate at
increased salinities.
1396.
Birke, G., A.G. Johnels, L.O. Plantin,
and T. Westermark. 1972. Studies
mercury through fish consumption.
77-91.
B. Sjostrand, S. Skerfving
on humans exposed to methyl.
Arch. Environ. Health 25:
Humans exposed to methylmercury through consumption of fish
were studied during and after varying degrees of exposure. Methyl-Hg
comprised half or less of total blood cell Hg in "normal" subjects; this
proportion was higher in heavily-exposed subjects. There was a relation
between exposure to methylmercury via ingestion of fish with blood Hg
levels, and between Hg levels in blood and hair. No symptoms and signs
indicating methylmercury poisoning were observed in subjects exposed at
most to 0.8 mg of Hg as methyl-Hg per day and having Hg levels up to
1,2?0 mg/kg blood cells and 185,000 mg/kg hair. After exposure, bio-
10glC half-life of Hg was 33 to 120 days in hair and 99 to 120 days in
blood cells in 5 and 2 subjects, respectively.
40
-------
1397.
Black, G.A.P., D.J. Hinton, H.C. Johnston, and J.B. Sprague.
1976. Annotated list of copper concentrations found harmful
to aquatic organisms. Dept. Environ. Canada, Fish. Marine
Servo Tech. Rept. 603: 44 pp.
A summary is presented of 101 selected papers which relate
concentrations of copper in water to deleterious effects on aquatic
organisms. Tables containing 169 items are arranged by increasing con-
centrations for various species of the following groups: fish, amphibia,
crustacea, mollusca, insecta, rotifera, protozoa, algae, annelida,
echinodermata, and higher plants. Listed concentrations range from 0.01
to 63,500 ug/l. Some findings on toxicities of various forms of copper
in water are presented.
1398.
Black, V.S. 1951. Changes in body chloride, density, and water
content of chum (Oncorhynchus keta) and coho (0. kisutch)
salmon fry when transferred from-rreshwater to-seawater.
Jour. Fish. Res. Bd. Canada 8(3):164-177.
o
Chum and coho salmon fry tolerated 50% seawater (8-9 /00 Cl).
Chum fry survived direct transfer from freshwater to seawater (15-170/00
Cl), but showed a marked increase in body chloride during first 12 hrs,
followed by a return to normal between 12 and 24 hrs. Coho, however,
died within 36 hrs, after a 60% increase in chloride. Coho fry lost more
water than chum fry after introduction to seawater. Density of both
species approximated that of the water within an hour of transfer to new
medium. When returned to fresh water after 12 hrs in seawater, body
chloride, density, and water content of both species regained normal
levels within 10 hrs. Coho fry did not permanently acclimatize to sea-
water in this study.
1399.
Blackwelder, P.L., R.E. Weiss and K.M. Wilbur. 1976, Effects of
calcium, strontium and magnesium on the coccolithophorid
Cricosphaera (Hymenomonos) carterae, I. Calcification.
Marine Biology 34:11-16.
Effects of Ca, Sr, and Mg on calcification and mineralogy of
calcified bodies of alga C. carteraewerestudied. The capacity of cells
to calcify in various concentrations of these ions was examined follow-
ing preliminary decalcification in C02' At a concentration of 0.4 g
Call, 75% of cells formed coccoliths within 24 hrs and almost all cells
were recalcified after 2 days. At 0.04 or 0.004 g Call, no recalcifica-
tion occurred. With addition of Sr to Ca-deficient media, calcification
took place as shown by observations of coccoliths and Ca analysis; per-
centage of calcified cells increased with increasing concentrations of
Sr. Strontium added to a Ca-deficient media was more effective than an
41
-------
equivalent concentration of Ca; no Sr was deposited in coccoliths. X-ray
analysis demonstrated that calcite was deposited by cells in all concen-
trations of Ca and Sr at which calcification took place. At concentra-
tions of Mg in media from 0.0 to 1.01 g/l, cells retained ability to
calcify although calcification was reduced in absence of Mg. In low Mg
concentrations (3.12 x 10-3 to 1.01 x 10-4 g/l), the coccoliths were 60%
calcite and 40% aragonite; in absence of Mg, only calcite was formed.
1400.
Blake, N.J. and D.L. Johnson. 1976. Oxygen production - con-
sumption of the pelagic Sargassum community in a flow-through
system with arsenic additions.. Deep-Sea Res. 23:773-778.
In a laboratory study, metabolism of a Sargassum community
(algae, bacteria, coelenterates, crustacea, teleosts) was unaffected by
addition of 0.028 mg As+5/l. When steady-state distribution of As
species was altered experimentally, the community re-established ambient
seawater As+3/As+5 ratio.
1401.
Blanc-Livni, N. and M. Abraham. 1970. The influence of environ-
mental salinity on the prolactin and gonadotropin-secreting
regions in the pituitary of Mugil (Teleostei). Gen. Compo
Endocrinol. 14:184-197.
Two species of Mugil were collected from freshwater, from
seawater, and from a hypersaline lagoon. In~. capito, the rostral
pars distalis occupied 8% of the total hypophysis in fish from the
hypersaline lagoon (7.80/00 S) and 42% in fish from freshwater. Volu-
metric changes of proximal pars distal is are the inverse of those of
the rostral pars dista1is. Proximal pars distalis changes were most
pronounced in M. cephalus; this lobe occupied 35% of hypophysis in
specimens collected from the Mediterranean Sea during spawning season,
as compared with 7% of hypophysis in freshwater specimens. Pituitary
prolactin content in M. cephalus was high in freshwater specimens and
low in specimens from-the sea. Striking histological changes, possibly
indicative of a degenerative process, were observed in nucleus lateralis
tuberis of M. cephalus confined to freshwater for several years. These
changes and-their relationship to volumetric variations of rostral and
proximal pars distalis of pituitary are discussed. Respective plasma
Na levels, in g/l, of~. cephalus and M. capito from freshwater, 350/00
and 780/00 salinity were 3.7 and 4.3,4.1 and 4.8, and 5.3 and 5.1.
1402.
Blankenship, M.L. and K.M. Wilbur. 1975. Cobalt effects on cell
division and calcium uptake in the coccolithophorid Crico-
sphaera carterae (Haptophyceae). Jour. Phycol. 11:211-219.
42
-------
Cell division rate of a calcifying alga increased slightly
when cobalt concentration of medium increased from 0 to 0.6 mg/l, above
which division rate decreased linearly to zero at 6 mg Co/I. Inhibition
of division was reversible after 2 days in Co. Protein content was
elevated in Co-treated nondividing cells but at 6 mg Co/I the protein
synthesis rate was reduced to 19% of the control culture medium value
(5.4 ug Co/I). Cell volume increased with Co concentration; after 72 h
in 12 mg Co/I, volume was 3.2x that of culture medium. After 48 h, cal-
cium uptake had increased 53% in 6 mg CO/I and decreased 40% in 12 mg
Co/I as compared with cells in 5.4 ug CO/I. Ultrastructurally, Co
caused enlargement of cell vacuole and appearance of membrane-bound
vacuoles containing electron dense bodies.
1403.
Blum, H.F. 1922. On the effect of low sali~ity on Teredo
navalis. Univ. Calif. Publ. Zool. 22(4):349-368.
Effects of low salinity on extension of Teredo siphons indi-
cate that Teredo is normally active in salinities as low as 90/00.
Below 70/00, activity decreases rapidly until at 30/00 siphon extension
ceases. The average lethal salinity for Teredo was determined at 50/00.
Below 50/00 Teredos obtain some temporary protection by stopping the
mouth of the burrow with pallets. A period of 33 days below 40/00
salinity destroyed 90% of Teredos in piles at Crockett, California.
1404.
Bodansky, M.
poisson.
1922. La repartition du zinc dans l'organisme du
Compt. Rend. Acad. Sci. (Paris) 173:790-792.
Zinc content in various tissues of two species of marine
teleosts was determined. Concentration in mg/kg fresh wt for red
snapper Lutjanus aya was lowest in muscle (2.3) and highest in spleen
(43.5) and liver 155.5); bony tissues were intermediate in value. For
catfish Ailurichtys marinus muscle was lowest (8.1), bony tissues high-
est (93-102), and liver intermediate (31).
1405.
Bohm, E.L. 1972. Concentration and distribution of AI, Fe, and
Si in the calcareous alga, Halimeda opuntia (L) (Chlorophyta,
Udoteaceae). Int. Revue ges. Hydrobiol. 57:631-636.
Mean concentrations of Si, AI, and Fe in dry Halimeda were
0.20%, 0.028% and 0.024%, respectively. Concentration factors of AI,
Fe, and Si were 2500, 2500 and 250, respectively. Approximately 90%
of the Si02 and Al is associated with water insoluble and water soluble
organic fractions from the algal cell wall. Passive adsorption rather
than active transport is favored for silicate uptake.
43
-------
1406.
Bohm, E.L.
algae.
1973. Studies on the mineral content of calcareouS
Bull. Marine Science 23:177-190.
Maximal mineral contents in g/kg dry wt of calcareous algae
were 970 for Halimeda, 600 for Penicillus and Rhipocephalus, and 370 for
Udotea. In some species of Halimeda mineral content increased with
depth. MgC03 concentration varied with genus and species, and within
different parts of the same organism. In Halimeda, Penicillus, and
Rhipocephalus, MgC03 was 0.2 to 3.0 mol %. In Udote~, MgC03 ~as 3 ~o 4
mol %. In most algae investigated, MgC03 concentratl0n was hlgher ln
younger scarcely calcified segments of the apical region, than in fully
developed more heavily calcified segments farther below. Juvenile
Udotea and Penicillus contained more MgC03 than adult individuals. Mean
mineral contents, in g/kg dry wt, of H. opuntia, were 14.6 for Na, 0.9
for K, 2.1 for Mg, 311 for Ca and 7.7-for Sr.
1407.
Bohn, A. 1975. Arsenic in marine organisms from West Greenland.
Marine Poll. Bull. 6(6):87-89.
A baseline study was conducted in a Greenland inlet within
6 km of a lead-zinc mining project which became operational in the fall
of 1973. Dry weight As levels in marine biota during summer of 1972
and 1973 ranged from 17 to 307 mg/kg in fish fillets, and from 7 to 512
in fish livers. Arsenic i,l wolffish, halibut, and sculpin muscle tis-
sues were positively correlated with fish size; this was not observed
for liver. For mussel (Mytilus edulis) and rockweed (Fucus vesiculosis)
As values were 14 to 16 and 35, respectively. Prawns Pandalus borealis
had arsenic levels up to 80 mg/kg in abdominal muscle; this contrasts
with the 6 mg/kg reported for planktonic copepods. Arsenic appears to
accumulate at higher trophic levels in this ecosystem. Overlapping
food habits of wolffish and plaice suggest that arsenic accumulation in
these fishes may depend on metabolic characteristics rather than diet
exclusively.
1408.
Bohn, A. and R.O. McElroy. 1976. Trace metals (As, Cd, Cu, Fe,
and Zn) in Arctic cod, Boreogadus saida, and selected zoo-
plankton from Strathcona Sound, Northern Baffin Island.
Jour. Fish. Res. Bd. Canada 33:2836-3840.
Average concentrations of As and Zn were higher fn Arctic
cod fillets at 46 and 34 mg/kg dry wt, respectively, than in livers from
the same fish at 4.4 and 19 mg/kg dry wt, respectively. Cd and Fe con-
centrations were higher in liver at 0.68 and 40 mg/kg dry wt than in
fillets, while the Cu concentration in fillets, at 4.0 mg/kg dry wt was
not significantly higher than liver. Arsenic and Zn in whole fish, and
As in fillets, were positively correlated to body weight, Cu and Fe
44
-------
were negatively correlated and Cd showed no relation. Cd levels in
unsorted planktonic copepods were 5.0 mg/kg dry wt which is 5 to 8 x
higher than in Arctic cod. As, Cu, Fe and Zn were higher in fish than
the levels of 5.6, 3.7, 78 and 60 mg/kg dry wt, respectively, fourd in
copepods. Metal levels in amphipods, in mg/kg dry wt were: As 7.9.
Cd 7.0, Cu'26, Fe 87, and Zn 43. Average levels in chaetognaths, in
mg/kg dry wt ranged in As from 7.5-7.7, Cd 1.2-1.3, Cu 5.6-6.3, Fe 32-
33 and Zn 76-90.
1409.
Boney, A.D.
algae.
1971. Sub-lethal effects of mercury on marine
Marine Poll. Bull. 2:69-71.
Sporelings of red alga Plumaria elegans were immersed in
solutions containing 0.12, 0.25, 0.5, or 1.0 mg/l Hg as HgC12. A 50%
growth inhibition was obtained after 6 hrs in 1 mg/l Hg, 12 hrs in 0.5
mg/l, and 24 hrs in 0.25 mg/l. Survival rates were high during post-
exposure. However, longer exposure to 1.0 or 0.5 mg/l Hg killed most
sporelings. Organic mercury compounds of n-alkyl mercuric chloride
types showed increasing toxicity with increasing number of C atoms in
the side chain. After 2.5 min in 0.5 mg/l Hg as n-C3H7 HgCl, plants
showed 50% growth inhibition, and after 5 min, a 70% growth inhibition.
With Hg as n-C4HgHgCl greater inhibition was observed. With n-CH3HgCl
a 50% growth inhibition occurred after 17.5 min immersion in solutions
containing 0.08 mg/l Hg; a similar pattern occurred in 0.04 mg/l Hg.
1410.
Boney, A.D. and E.D.S. Corner. 1959. Application of toxic
agents in the study of the ecological resistance of inter-
tidal red algae. Jour. Mar. BioI. Assn. U.K. 38:267-275.
Poisons of high lipid solubility (n-C3H7HgCl and 1:2-
naphthoquinone) are far more toxic than one of low lipid solubility
(HgC12) to sporelings of Plurnaria elegans, Polysiphonia lanosa and
Sperrnothamnion repens; but when Antitharnnion plurnula, Ceramium pedi-
cellatum and Ceramium flabelligerurn are used the relative toxicities of
the poisons are much closer in value. Toxic effects of HgC12 to spore-
lings of Plurnaria develop slowly at normal temperature and more quickly
at elevated temperatures. When sporelings of Antitharnnion are used,
toxic effects develop rapidly at both normal and raised temperatures.
The relative toxicities of n-C3H7HgCl and HgC12 to sporelings of
Plurnaria, Polysiphonia and Sperrnotharnnion are markedly reduced when the
test material is first treated with sub-toxic amounts of kerosene, a
substance known to distort the lipid moiety of the cell membrane. When
Antithamnion, f. pedicellaturn and f. flabelligerurn are used as the test
material, the effect of kerosene is negligible. These results are
consistent with the view that proportion of lipid material present in
4S
-------
cell membrane is important in determining susceptibility' of an inter-
tidal red alga to increased sea-water temperature.
1411.
Boney, A.D., E.D.S. Corner and B.W.P. Sparrow. 1959. The
effects of various poisons on the growth and viability of
sporelings of the red alga Plumaria elegans (Bonnem.).
Schm. Biochem. Pharmac. 2:37-49.
Exposure of sporelings of P. elegans in seawater at pH 8.1
to 1.0 mg/l for one week of mercury, silver, copper or arsenic salts
allowed 11, 0, 0, and 18% respectively, to develop as opposed to 77%
in controls. After one week, 10 mg/l concentrations of non-metallic
inhibitors hydrocyanic, and hydrazoic acid and 50 mg/l concentrations
of iodoacetic, flouroacetic and molonic acid and 2:4-dinitrophenol
allowed between 33 and 75% of the spore lings to develop, proving to be
less toxic than the heavy metals. Toxicities of Hg and As are in-
creased when found in organic compounds. Thus methyl-, ethyl-,
n-propyl, n-butyl-, isopropyl-, isoamyl- and phenyl-mercuric chlorides
and phenylmercuric iodide are more toxic than mercuric chloride;
phenarsazine chloride is more toxic than arsenite. Toxicities of
organic derivatives of Hg and As are reduced in presence of an excess
of glutathione, which also reduces the toxicity of Cu, Ag and arsenite.
When spore lings immersed in toxic solutions of all poisons are subse-
quently washed with reduced glutathione, toxic effects are diminished.
Toxicities of a homologous series of primary n-alkylmercuric chlorides
increased to a maximum with n-C3H7HgCl. Mercuric iodide was 1.7x more
toxic as HgClz to adult copepods Acartia clausi, and 24x more toxic to
brine shrimp, Artemia salina; various organic derivatives of Hg were
markedly more toxic to crustaceans but not Plumaria in presence of
excess KI.
1412.
Born, J.W. 1968. Osmoregularity capacities of two caridean
shrimps Syncaris pacifica (Atyidae) and Palaemon macro-
dactylus (Palaemonidae). BioI. Bull. 134:235-244.
~. pacifica, restricted to FW has a blood chloride level of
~185 meq/l. Blood chloride level rises in brackish water, becomes iso-
tonic with medium at ~290 meq/l, and remains isotonic at still higher
salinities. At final chlorinity of 510 meq/l (95% SW), Syncaris showed
slight hypotonicity to medium, equivalent to approx. 0.1% NaCl. Total
osmotic pressure of blood and urine show that hyper-regulation is main-
tained by Syncaris below 50% SW and that antennal gland plays a role
in osmo-regulation by producing urine hypotonic to blood. With in-
creasing salinity between 10 and 30% SW blood concentration rises and
urine rapidly becomes isosmotic with blood. Maximum rate of change of
urine concentration occurs at 30-50% SW. In 50% SW urine and blood are
,
46
-------
isosmotic at ~125% medium concentration. In 70% SW,urine, blood and
environment are in equilibrium. Palaemon macrodactylus (Palaemonidae)
is a strong regulator over the range 2-150% SW, and inhabits a wide
range of salinities. Hyper-regulation occurs below 60% SW, and hypo-
regulation in higher salinities.
1413.
Boroughs, H., W.A. Chipman, T.R. Rice. 1957. Laboratoryexperi-
ments on the uptake, accumulation, and loss of radionuclides
by marine organisms. In Rept. Comm. Effects Atom. Radiation
Ocean. Fish. U.S. Natl~Acad. Sci. Res. Coun. Publ. 551:80-
87.
Uptake, accumulation and depuration studies were conducted
with isotopes of Y, Sr; Cs, Zn and Ru with various species of marine
teleosts, echinoderms, mollusks, crustaceans and algae. Sr-90 and Y-90
were accumulated by algae from solution in highly variable ratios when
media contained both elements. Brine shrimp Artemiasalina, shrimp
Panaeus setiferus, blue crab Callinectes sapidus, clam Venus mercenaria,
and bay scallop Pecten irradians rapidly accumulated Sr from seawater.
In oyster Crassostrea virginica, Sr-89 accumulates mainly in shell; con-
taminated soft tissues depurate to 10% of previous radioactivity levels
within 1 day. Oysters fed Sr-89-labelled Carteria cells reached steady
state in 8 days. Most Sr-89 administered per os to skipjack tuna
Euthynnus yaito, dolphin Coryphaena hippurus, and yellowfin tuna
Neothunnus macropterus was eliminated rapidly. Gill, bone and integu-
ment were major accumulation sites. Tilapia, a sluggish bottom fish,
excreted Sr-89 more slowly. Post-larval flounder took up Sr-89 more
rapidly from seawater at 20 C than at 10 C. For Cs-137, the highest
reported concentration factor (CF) for 3 families of algae was 3.1.
CFts for Cs-137 were 6 after 20 d for V. mercenaria and 8 after 10 d
for scallops. Various tissues of tuna-were also examined for Cs uptake
and depuration. Studies with Nitzschia closterium show algae rapidly
take up Zn from seawater. After 2 hr exposure, Zn-65 CFts for scallop
ranged from 0.8 for rectum to 82 for kidney, with an average soft
tissue value of 20. Oysters concentrated Zn-65 up to l7,800x that in
seawater. Croaker Micropogon undulatus, concentrate Zn-65 administered
per ~ in liver ,and spleen, showing a slow turnover in skin, muscle and
bone, and a rapid turnover in internal organs. Nitzschia studies show
dividing plankton algae can take up large amounts of Ru-l06. Particles
of Ru-l06 co-precipitated with CaC03 were ingested by sea urchin
Arabacia punctulata, and bay scallop but radioactivity was not found in
organs other than digestive tract. Menhaden Brevoortia tyrannus, did
not incorporate Ru-l06 from a CaC03 precipitate in water or from food
sources into tissues to an appreciable extent.
47
-------
1414.
Boroughs, H. and D.F. Reid. 1958. The role of the blood in the
transportation of strontium 90_yttrium90 in teleost fish.
BioI. Bull. 115(1):64-73.
Mixing time of Sr-90-Y-90 injected intraventrically into
Tilapia mossambica is about 30 min. After 24 hrs, 0.8 to l.~% of the
injected dose remained in blood. Most Sr-90 in whole blood 1S plasma-
borne; very little is found in cells or on cell walls. Y-90 is present
in stroma. Pattern of internal distribution of intravascularly injected
Sr-90-Y-90 is same as that found for either intramuscular or oral admin-
istration. Authors observed that vascularized tissues have a greater
avidity for Y-90 than Sr-90.
1415.
Boyden, C.R.
molluscs.
1974. Trace element content and body size in
Nature 251:311-314.
When trace element concentrations in shellfish are expressed
on a weight-specific basis, highest values are often recorded in the
smallest individuals. In those cases it is difficult to assess whether
observed differences in element tissue concentrations between popula-
tions reflect real differences in environmental trace element constitu-
tion, or are due to variations in body size. This problem can be
avoided by determining element concentrations over a range of body sizes
and reference made to a specific size for comparative purposes.
In this account concentrations of Cd, Cu, Fe, Ni, Pb, and Zn
were measured in individual molluscs over a wide size range. Six
estuarine species were examined: limpet Patella vulgata, and P. inter-
media; cockle, Cerastoderma edule; mussel, Mytilus edulis; and-clam
Mercenaria mercenaria, and Venerupis decussata. Total trace element
content per individual Y relates to body weight W as a power function
expressed by:
b
Y = aW
(1)
which on logarithmic transformation (base 10) yields a regression of
the form:
log Y = log a-b log W.
The weight specific relationship Y to body weight is
similar. Dividing (1) throughout by W yields:
Y~ = Y/W - aWb/W = awb-l,
Logarithmic transformation produces a linear function:
(2)
essentially
(3)
Log Y~ = log a+(b-l) log W. (4)
Clearly, equations (2) and (4) have related regression co-
efficients and share a common intercept (Y and Y~ = log a) when W =
1.0, log W = O. The precise relationship between trace element content
48
-------
(~g) and dry body weight (g) differs depending on element and species.
Three general relationships have been identified. First, element content
is related to ~0.75 power of body weight; this was evident for copper in
all species examined; several other elements exhibited the same relation-
ship. Second, element content is directly related to body weight (b ~
1.00). Nickel in all bivalve species examined and also Pb and Zn in M.
mercenaria, Fe and Zn in V. decus5ata and Cd in M. edulis exhibited this
relationship to body weight. In these cases, tissue element concentra-
tions are independent of size. Third, element content is related to
square of body weight (b ~ 2.00). This pattern was only observed for
Cd in limpet ~. vulgata. Therefore in this case, element tissue concen-
tration is directly proportional to body weight. Some earlier observa-
tions in the literature are consistent with the above relationships. A
regression slope of 0.77 dictates that smaller individuals contain a
higher concentration of metal than larger individuals. Such differences
have been recognized for Pb in M. edulis, Zn in P. vulgata and Cu and Fe
in M. mercenaria. The converse-situation, with higher concentrations of
Cd Tn large limpets compared with small individuals, has previously been
reported for P. vulgata collected from the Severn Estuary. In the
molluscs studTed, however, it was usual for element concentrations to
decrease or remain constant with increasing body weight.
In molluscs, absolut~ tissue element concentrations are re-
lated or determined by environmental concentrations. Within each
species, however, different elements display different relationships to
body weight. Regression coefficients related to body weight by a power
of 0.77 implies a connection with metabolism, as many metabolic processes
display a similar relation to body weight. The common regression co-
efficient of 0.77 is not significnatly different from 0.75 describing
the relationship of respiration of poikilotherms to body weight, a value
generally accepted to relate many metabolic functions to body weight.
Thus in cases where an element is related to 0.77 body weight some
aspect of metabolism could well be influencing final trace element con-
tent. Where the element content is directly related to body weight, as
has been found for a variety of elements in several species, then a
function of body weight such as the binding of specific compounds with-
in tissues may play some role in determining total body element burden.
But the absolute amount of metal is not dictated by the amount of such
binding compounds within the tissues; certain metals such as cadmium
and nickel in Mytilus, retain a specific slope relation of ~1.00
between total body element content and body weight, even though abso-
lute amount of metals within tissues differed by 12x for cadmium and
2x for nickel between two separate populations studied. A relation to
square of body weight as shown by cadmium in limpets can best be ex-
plained as being due to removal of this element from body circulation
and accumulation within specific tissues, possibly as a result of some
exceptional affinity. The slope value of 2.00 in the limpet population
examined may be due to the unusually elevated environmental cadmium
49
-------
concentration in the Severn Estuary. Populations of limpets from other
areas, where environmental cadmium concentrations are lower; exhibit
slopes between 1.3 and 1.5 suggesting that in this case, slope is vari-
able and related to environmental cadmium concentration.
Knowledge of regression coefficients relating trace element
content (or weight-specific concentration) to body weight is poten-
tially a considerable aid in monitoring of metals within shellfish.
Evidence is being gathered which suggests that in most cases regression
coefficient relating element content to body weight remains constant
regardless of season or environmental element concentration. The only
case so far identified where slope differs between populations is that
for cadmium in P. vulgata, though other exceptions may also be expected.
If values of b are indeed constant for a particular element within a
species, data pertaining to element content or concentration mean tissue
weight for a sample of similar sized individuals may be substituted,
together with the appropriate slo?e for element and species in question,
into equations (2) or (4). The calculated intercept (log a) converted
to real values may then be used for comparison between populations re-
gardless of size of individuals sampled. .
1416.
Boyden, C.R. and M.G. Romeril. 1974. A trace metal problem in
pond oyster culture. Marine Poll. Bull. 5:74-78.
Oysters Crassostrea gigas reared in power station cooling
water at Hinkley Point on Severn Estuary, accumulated copper and zinc
at levels up to 6,480 and 99,220 mg/kg dry wt, respectively. Cause of
high Zn concentrations was attributed to corrosion of galvanized zinc
trays upon which oysters were suspended. Increased copper levels were
due to corrosion of phosphor bronze blades of recirculating pump. It
is shown that considerable caution should be exercised with accessories
used in rearing marine animals, particularly molluscs.
1417.
Boyden, C.R., H. Watling and I. Thornton. 1975. Effect of
zinc on the settlement of the oyster Crassostrea gigas.
Marine Biology 31:227-234.
For late oyster larvae (21 to 26 days old), the LC-30 (5
day) value for zinc was 500 ~g/l. Larval settlement was impaired by
125 ~g Zn/l when compared to control (20-25 ~g Zn/l). Exposure to this
concentration of Zn immediately prior to settlement slowed behavioral
development. However; larvae which settled in presence of Zn,when
grown in clean water were as viable as controls. Zn at concentrations
of 250 and 500 ~g/l suppressed spat growth, but recovery was rapid in
clean water conditions.
so
-------
1418.
Boyle, P.J. and E.J. Conway. 1941.
muscle and associated changes.
Potassi~~ accumulation in
Jour. Physio1. 100:1-63.
The study of K, Na and chloride changes in frog sartorii
shows that K can be accumulated to upwards of 3x over normal levels.
The significance of this and other changes observed are included in a
general discussion of K concentration mechanisms in muscle.
1419.
Bradley, H.C. 1904. The occurrence of zinc in certain inverte-
brates. Science 19(474):196-197.
Ashed hepatopancreas of Sycotypus canaliculatus, a marine
gastropod, contained between 10.8 and 23.4% ZnO, 0.84% Fe, and approxi-
mately 8% Cu. Zinc was also found in blood of Sycotypus and ash of
Fulgur carica. Zinc was not detected in other marine forms analyzed
including the gastropod Urosalpinx cinerea, the bivalves Mytilus edulis,
Modiola p1icatula, Argina pexata, Ostrea virginica, and two species of
decapod crustaceans.
1420.
Braek, G.S., A. Jensen, and A. Mohus. 1976. Heavy metal toler-
ance of marine phytoplankton. III. Combined effects of
copper and zinc ions on cultures of four common species.
Jour. Exper. Mar. BioI. Ecol. 25:37-50.
Combined effects of Cu and Zn on growth of 3 species of
marine diatoms and one dinoflagellate in culture were studied. Over
a 10-day period, growth inhihition of Amphidinium carteri was observed
at 50 ~g/l of Cu2+ and 50 ~g/l of Zn2+; for Thalassiosira pseudonana
this was 50 ~g/l of Cu2+ and 400 ~g/l of Zn2T; for Skeletonema costatum,
75 ~g/l Cu2+ and 100 ~~/l Zn2+; for Phaeodactylum tricornutum, 250 ~g/l
Cu2+ and 8000 ~g/l Zn2. The two metals act synergistically to all
algae except P. tricornutum. With this species an antagonistic effect
was observed.- Addition of zinc ions reduced inhibition of growth caused
by the more toxic copper ions. Zinc toxicity to this alga increased at
low concentrations of magnesium, indicating a common route for divalent
metal ions in general.
1421.
Brafield, A.E. and P. Matthiessen. 1976. Oxygen consumption by
sticklebacks (Gasterosteus aculeatus L.) exposed to zinc.
Jour. Fish BioI. 9:359-370.
During exposure to 1 mg/l Zn in calcium-free water, oxygen
uptake by sticklebacks tends to rise followed by erratic values before
declining as death approaches. Behavioral abnormalities such as in-
creased ventilation rate, loss of balance, and long periods of inactivity
51
-------
alternating with spasmodic swimming also occur. Exposure to 6.5 mg/l Zn
in high-Ca water causes a rise in oxygen consumption, followed by fluctu-
ations in uptake rate, but without behavioral abnormalities. If re-
stored to Zn-free water after 40 hr exposure to Zn, recovery is generally
complete, although fluctuating rates of oxygen uptake persist.
Brenko, M.H. and A. Calabrese. 1969. The combined effects of
salinity and temperature on larvae of the mussel Mytilus
edulis. Marine Biology 4:224-226.
Survival of larvae at salinities from 15 to 400/00 is uni-
formly good (70% +) at temperatures from 5 to 20 C, but is reduced
drastically at 25 C, particularly at high (400/00) and low (200/00)
salinities. Larval growth decreases at 25 C and also at 10 C with de-
cline most pronounced at high and low salinities.
1422.
1423.
Brenner, F.J., S. Corbett and R. Shertzer. 1976.
ferric hydroxide suspension on blood chemistry
shiner, Notropus cornutus. Trans. Amer. Fish.
455.
Effect of
in the common
Soc. 105:450-
Shiners were exposed to 3 mg/l ferric hydroxide for periods
from two to eight weeks. Serum protein as separated by electrophoresis
was divided into three major groups: 1 (bands 1-2); 2 (bands 3-5); and
3 (band 6). Group 1 proteins comprised about 55% of total serum pro-
tein in fish not exposed to ferric hydroxide. Serum proteins in groups
1 and 2 fractions decreased significantly, after a two-week exposure
while group 3 fraction increased significantly to approx. 44% of total
protein fraction compared with 20% in controls. After 4-week exposure
to ferric hydroxide, group 1 fraction replaced group 3 as most prevalent,
comprising 43% of total. All three protein groups increased following
a 6-week exposure with fractional counts not significantly different
from controls. After exposure for 8 weeks to ferric hydroxide, protein
fractions decreased with all three fractions significantly less than
controls. Blood sugar decreased from approx. 85 to 8 mg glucose/IOO ml
after a 2-week exposure and remained unchanged for next two weeks. In
weeks 4 to 6, blood sugar level increased to approx. 65 mg glucose/IOO
ml, but was still significantly less than controls at approx. 85 mg
glucose/lOO mI. Serum potassium decreased from 2.2 to 1.9 m moles/I,
while sodium ions increased from 1.2 to 1.5 m mOles/l after a 2-week
exposure to ferric hydroxide. After 4-week exposure, K increased to
2.3 m moles/l while Na ions decreased to 1.2 m mOles/I; K concentration
remained significantly greater than controls for remainder of study
while Na content approximated control values.
52
-------
1424.
Briese, L.A., C.T. Garten, Jr. and R. R. Sharitz. 1975. Distri-
bution of radiocesium in vegetation along a contaminated
stream. In: Howell, F.G., J.B. Gentry and M.H. Smith (eds.).
Mineral Cycling in Southeastern Ecosystems. U.S. Energy
Res. Dev. Admin.: 509-517. Available as CONF-7405l3 from
NTIS, U.S. Dept. Camm., Springfield, VA 22161.
Leaves of arrowhead Sagittaria latifolia, black willow Salix
nigra, smartweed Polygonum punctatum, and woolgrass Scirpus cyperinus
at 8 sites along a 20-km stream contaminated by radioactive effluent from
nuclear production reactors contained mean levels of 488, 303, 192 and
86 n Ci CS/kg dry wt, respectively. Cs-134-l37 distribution in vegeta-
tion was species specific and independent of distance from entry point
of effluent into stream, but concentrations were generally higher in
plants where streamflow rates decreased. At all sites, Cs-134-l37 in
leaves were log normally distributed. Mean Cs-134-l37 concentrations
were linearly related to variance for all species, but slope and inter-
cept values were species dependent.
1425.
Bringmann, G. and R. Kuhn. 1959. Vergleichende wassertoxi-
kologische Untersuchungen an Bakterien, Algen und Klein-
krebsen. Gesundheits-Ingenieur 80:115-120. (In German)
The following concentrations of metals salts, in mg metal
per liter, began to show toxic effects upon the bacteria Escherichia:
Ag 0.04, Cu 0.08, Cd 0.15, Ni 0.1, Hg 0.2, La 0.4, Cr 0.7, Ce 0.75 to
1.5, Th 0.8, Pb 1.3, Zn 1.4 to 2.3, U 1.7 to 2.2, Co 2.5, Sb 33, Se 90,
W 167, and As 290. Toxic effects upon the algae Scenedesmus sp. were
first evident at the following concentrations, in mg metal/I: Hg 0.03,
Ag 0.05, Cd 0.1, Ce 0.14, La 0.15, Ce 0.15 to 0.2, Cu 0.15, Th 0.4 to
0.8, Cr 0.7, Ni 0.9 to 1.5, Co 1.0, Zn 1.0 to 1.4, Al 1.5 to 2.0, Ti
2.0, U 2.2, Pb 2.5, Se 2.5, Sb 3.5, Cr 4 to 6, Rb 14, Ba 34, As 35-46,
Mo 54 and W 110. For the freshwater crustacean Daphnia sp" toxic
effects were first observed at the following concentrations in mg/l:
Hg 0.02 to 0.03, Ag 0.03, Cd 0.1, Cu 0.1, Cr 0.7, Zn 1.8, Se 2.5, As
4.6, Ti 4.6, Pb 5.0, Co 5.0, Ni 6.0, Sb 9.0, U 13, Li 16, Cr 42, Mn
SO, La 160, Ba 170, Sr 210, and W 350.
1426.
Brock, T.D. and J. Gustafson. 1976. Ferric iron reduction by
sulfur- and iron-oxidizing bacteria. Appl. Environ. Microb.
32:567-571.
Acidophilic bacteria of the genera Thiobacillus and Sulfolobus
can reduce ferric iron when growing on elemental sulfur as an energy
source. It has been thought previously that ferric iron serves as a
nonbiological oxidant in formation of acid mine drainage and in leaching
53
-------
of ores, but results suggest that bacterial catalysis may playa sig-
nificant role in reactivity of ferric iron.
1427.
Brooks, R.R., J.R. Lewis and R.D. Reeves. 1976. Mercury and
other heavy metals in trout of central North Island, New
Zealand. New Zealand Jour. Mar. Freshwater Res. 10(2):233-
244.
Respective mean mercury, cadmium, copper, iron, manganese and
zinc levels, in mg/kg wet wt, of trout from Lake Taupo, New Zealand,
were 0.19 (Hg), 0.06 (Cd), 1.0 (Cu), 30.0 (Fe), 0.36 (Mn) and 7.9 (Zn)
for flesh; 0.12, 0.15, 0.48, 72.0, 2.5 and 100.0 for gills; 0.16, 0.06,
5.5, 76.0, 1.5 and 51.0 for gonads; n.d., 0.12, 4.1, 115.0, 0.57 and
24.0 for heart; 0.53, 0.10, 2.4, 291.0, 0.83 and 30.0 for kidney; 0.35,
0.07, 184.0, 413.0, 1.2 and 34.0 for liver; and 0.36 (Hg), 0.11 (Cd),
2.1 (Cu), 1090.0 We), 0.65 (Mn) and 27.0 (Zn) for spleen.
In trout from 17 other New Zealand lakes, flesh metal levels,
in mg/kg wet wt, ranged from 0.34 to 2.7 for Cu, 8.0 to 46.0 for Fe,
0.32 to 1.0 for Mn, and 7.6 to 18.0 for Zn. Hg levels ranged from 0.22
to 2.8 mg/kg wet wt, in some cases exceeding the accepted maximum of
0.5 mg/kg wet wt.
1428.
Brown, B. and M. Ahsanullah. 1971. Effect of heavy metals on
mortality and growth. Marine Poll. Bull. 2:182-187.
LC-50's and sublethal effects on growth of Hg, Cu, Zn, Cd,
Fe, and Pb on the polychaete Ophryotrocha labronica, and the brine
shrimp Artemia salina, were determined. At a metal concentration of
1.0 mg/l, the time in hours to LC-50 for adult Ophryotrocha was 0.5 in
Hg, 4.5 in Cu, 13.0 in Zn, 410 in Cd, 500 in Fe, and over 600 in Pb.
For adult Artemia, these times were 25 for Hg, 168 for Cu, 240 for Cd,
300 for Fe, 312 for Zn, and 576 for Pb. Artemia larvae were more
susceptible to solutions of Cu and Zn than adults, reaching LC-50 after
110 h in 1.0 mg/l Cu and 150 h in 1.0 mg/l Zn. Artemia showed no sig-
nificant suppression of growth in copper (at 1.0 mg/l), but reduced
growth was obtained with Zn and Pb at concentrations of 10, 5, 2.5, and
1.0 mg/l Zn and 10 and 5 mg/l Pb. Ophryotrocha showed growth inhibition
at Cu concentrations of 0.1 and 0.05 mg/l; none was obtained in 0.1 mg/l
Zn or 10 mg/l Pb.
1429.
Brown, B.E. 1976. Observations on the tolerance of the isopod
Asellus meridianus Rae. to copper and lead. Water Research
10:555-559.
54
-------
Isopods from sites receiving mine-drainage in the rivers Hayle
and Gannel in Cornwall have been shown by toxicity tests and growth rate
experiments to be particularly tolerant to Cu and Pb. Animals from the
Hayle where Cu water concentrations ranged from 0.01 to 0.1 mg/l and Cu
sediment concentrations ranged from 126 to 2398 mg/kg but Pb concentra-
tions were only <0.1 in water and 112 to 258 in sediments, are tolerant
to both Cu and Pb. LC-50 (48 hr) values for Cu ranged from 1.65 to 2.50
mg/l and from 1.00 to 2.80 mg/l for lead. Animals from the River Gannel,
with water Cu of 0.04 mg/l, sediment Cu of 1964 mg/kg and Pb concentra-
tions of 0.19 and 6614 mg/l in water and sediments, respectivel~ are
markedly tolerant to Pb. The LC-50 (48 hr) value for Pb was 3.50 mg/l;
for Cu 1.90 mg/l. Copper concentrations of A. meridianus collected from
the Hayle ranged from 67 to 304 mg/kg dry wt-and 89 mg/kg dry wt for
those found in River Gannel. Only specimens collected from River
Gannel showed significant traces of Pb at 446 mg/kg dry wt. Tolerance
to lead was shown to persist in animals from the Gannel F2 generation
which had been cultured in the laboratory.
1430.
Brown, V.M., T.L. Shaw, and D.G. Shurben. 1974. Aspects of water
quality and the toxicity of copper to rainbow trout. Water
Research 8:797-803.
Effects of sewage effluent, an amino acid, humic substances
and suspended organic matter on acute toxicity of water containing
copper sulphate to trout Salmo gairdnerii was determined. In all cases
toxicity of a given total concentration of copper was quantitatively
reduced. Median periods of survival of rainbow trout in percolating
filter effluent in presence of 2.0 mg Cull was raised from 8 hours in
no effluent, to 26 hrs in 50% effluent and 80 hrs in 100% effluent.
Glycine raised the 72 hr LC-50's of total Cu from 0.67 mg Cull in 0.25
mg glycine/I, to 1.4 mg Cull in 2 mg glycine/I, and to 4.7 mg Cull in
10 mg glycine/I. Median periods of survival of trout in 2.0 mg Cull
and humic substances was raised from 470 min in no humic substances to
760 min in 1.5 mg humic substances/I, to 1050 min in 4.5 mg humic sub-
stances/I. The importance of suspended organic matter was shown when in
its presence 70% of added copper was removed within 1 to 2 hrs whereas
some 70 to 80% of added copper remained in solution in absence of organic
solids. Authors concluded that data from toxicity tests with Cu in
which natural surface waters are used for dilution purposes cannot de-
fine true toxicity for Cu or have application to other natural waters
except when concentrations of toxic chemical species are known.
1431.
Brown, V.M., D.G. Shurben and D. Shaw. 1970. Studies on water
quality and the absence of fish from some polluted English
rivers. Water Research 4:363-382.
55
-------
Acute toxicity to rainbow trout, brown trout and dace was
determined of water from rivers and an estuary contaminated by Zn, Cu and
other pollutants. LC-50 (48 hr) concentrations of these waters diluted
with clean water were 65% of those predicted from chemical qualities of
the waters.
1432.
Brungs, W.A., J.R. Geckler, and M. Gast. 1973.
toxicity of copper to the fathead minnow in
variable quality- Water Research 10:37-43.
Acute and chronic
a surface water of
Acute and chronic toxicity tests were conducted with fathead
minnow Pimephales promelas, and copper. The source of dilution water was
a natural stream to which a sewage treatment plant upstream contributed
a variety of materials known to affect copper toxicity- Nominal total
copper LC-50 (96 hr) values, determined with static testing procedures,
ranged from 1.6 to 21 mg/l. Dissolved copper LC-SO (96 hr) values ranged
from 0.60 to 0.98 mg/l. The maximum acceptable toxicant concentration
based on survival, growth, reproduction, and hatchability of eggs, was
between 0.066 and 0.118 mg/l.
1433.
Brunker, R.L. and T.L. Bott. 1974. Reduction of mercury to the
elemental state by a yeast. Appl. Microbiol. 27:870-873.
Cryptococcus isolated from a stream was capable of reducing
mercury to the elemental state. This organism grows in Wickerham broth
supplemented with high concentrations of mercury (II) chloride (180 mg
of mercury per liter) and will metabolize (14C) glucose in this medium
as do cells in absence of mercury. Mercury was associated with cell
wall and membrane~ and in vacuoles within cytoplasm.
1434.
Bryan, G.W. 1966. The metabolism of Zn and 65Zn in crabs,
lobsters and freshwater crayfish. In: Radioecological Con-
centration Processes. Proc. Inter.;Symp., Stockholm, Apr.
25-29. Sym. Pub. Division, Pergamon Press, New York: 1005-
1016.
Tissue zinc content in shore crab Carcinus maenas, lobster
Homarus vulgaris, and freshwater crayfish Austropotamobius pallipes
pallipes, was determined in seawater containing about 5 ug/l Zn. Whole
body concentrations were 24, 22, and 24 mg/kg fresh weight, respectively.
Hepatopancreas, with 56, 34, and 92 mg/kg Zn, respectively, and leg
muscle, with 44 and 64 mg/kg Zn for crab and lobster, respectively, con-
tained the highest levels. Distribution of Zn differed between tissues
of the three species.
56
-------
When placed in 25 ug/l and 100 ug/l Zn seawater (far from
toxic levels), the crab maintained a comparatively constant Zn content
so that the potential equilibrium concentration factor for Zn-65 is
almost inversely proportional to the seawater Zn content (i.e. CF
~3400 when seawater Zn = 7.3 ug/l and CF ~270 when seawater Zn = 100-
115 ug/l). By processes which involve Zn binding by blood, plus
possible facilitated uptake in low Zn seawater, Zn-65 can be absorbed
directly from seawater across the body surface (gills). Turnover of Zn
is more rapid in high Zn seawater and consequently in high Zn seawater,
Zn-65 reaches lower equilibrium concentration factors more rapidly, and
is lost more rapidly. Absorption of Zn-65 and Zn from food is a com-
paratively rapid and complete process and is likely to be a more im-
portant route for uptake of radiozinc than direct absorption from sea-
water. Also, absorption of stable Zn from food increases the rate of
loss of Zn and Zn-65 across the body surface and causes further losses
to occur in faeces and urine. The lobster is generally very similar ex-
cept that Zn loss in urine tends to take the place of loss across the
body surface. The impermeability of freshwater crayfish eliminates
Zn-65 absorption and loss across body surface. Therefore, apart from
contamination of body surface due to adsorption, Zn-65 must all be
absorbed from food. Hepatopancreas absorbs Zn and Zn-65 from food in
stomach and regulates body Zn content. Removal of Zn and Zn-65 occurs
in faeces and cannot be continued unless food is eaten and faeces pro-
duced.
1435.
Bryan, G.W. 1967. Zinc concentrations of fast and slow contract-
ing muscles in the lobster. Nature 213:1043-1044.
Various slow muscles from lobster Homarus vulgaris, contained
93, 101, and 105 mg Zn/kg tissue, which was 5 to 7 times more Zn than
fast muscles (13, 15, and 20 mg/kg), and twice as much Zn as any other
lobster tissue. Muscle/blood ratios for Zn-65 in slow muscle are
roughly double those for fast muscle which implies that slow muscle is
more permeable to Zn. Author suggests that the differences between
muscle-types may be related to differences in enzyme content.
1436.
Bryan, G.W. 1974. Adaptation of an estuarine polychaete to
sediments containing high concentrations of heavy metals.
In: Vernberg, F.J. and W.B. Vernberg (eds.). Pollution and
Physiology of Marine Organisms. Academic Press, New York:
123-135.
Populations of Nereis diversicolor from metal-polluted
estuaries were more tolerant to metals than populations from lower
metal content environments in S.W. England. For Cu, Cd, Pb, and Ag,
body concentration was directly proportional to that of sediment.
57
-------
Populations from high metal environments had 96-hr LC-50's of 2.3 mg Cull
and 94 mg Zn/l. Polychaetes from low metal sediments had 96-hr LC-50's
of 0.54 Cull and 55 mg Zn/l. Tolerance to Cu, and possibly Ag and As,
appears to depend on a better detoxification system. Zn tolerance is
due to decreased body surface permeability.
1437.
Bryan, G.W., A. Preston and W.L. Templeton.
of radionuclides by aquatic organisms of
in the United Kingdom. In: Proc. Symp.
Radioactive Waste into the Seas, Oceans,
Int. Atom. Ener. Agen., Vienna: 623-637.
1966. Accumulation
economic importance
on the Disposal of
and Surface Waters.
Extent to which radionuclides and stable ,isotopes of Cs, Sr,
Ru, Ce, Zr, Nb, Mn, Co, and Zn can be accumulated by edible plants,
molluscs, crustaceans and fish in sea and fresh water was conducted in
the United Kingdom. Results from laboratory experiments on rates of
uptake and factors affecting them have been combined with results from
field work at Windscale, from fallout studies and from stable isotope
analyses. Cs:K and Sr:Ca concentration factor ratios are also examined.
1438.
Bryan, G.W. and E. Ward. 1962. Potassium metabolism and the
accumulation of 137caesium by decapod crustacea. Jour. Mar.
BioI. Assn. U.K. 42(2):199-241.
In starved lobsters Homarus vulgaris, and prawns Palaemon
serratus, Cs-137 is taken up and lost far more slowly than K-42. Al-
though all inactive K in animals can be exchanged with K-42, higher
Cs-137 concentration factors of 8 for lobsters and 25 for prawns were
reached because both species have higher plasma/medium ratios for Cs-137
than K at equilibrium despite selective Cs-137 excretion. Except for
hepatopancreas in lobsters and fed prawns, all soft tissues can probably
attain higher tissue/plasma ratios for Cs-137 than inactive K. In fresh-
water crayfish Austropotamobius pallipes pallipes, in 0.1% seawater,
concentration factors of 50-200 and 4500 were obtained for Cs-137 and
K, respectively. Crayfish selectively excrete Cs-137 in urine relative
to K at a lower concentration than in plasma. Muscle is the principal
limiting factor in uptake and loss of Cs-137 by all species, but body
surface is limiting to K-42 exchange. Authors suggest that for prawns
in a constant environment, feeding is probably less important than up-
take over body surface; but in crayfish, feeding is probably more
important.
1439.
Buhler, D.R., R.R. Claeys and B.R. Mate. 1975. Heavy metal and
chlorinated hydrocarbon residues in California sea lions
58
-------
(Zalophus californianus californianus).
Canada 32:2391-2397.
Jour. Fish. Res. Bd.
Healthy sea lions collected from the central Oregon coast in
1971 had total mercury (% methylmercury) values, in mg/kg wet wt of 74
(3.7%) in liver; 6.9 (17.2%) in kidney, 1.2 (88.6%) in muscle, 0.6
(88.1%) in heart, 0.5 (59.4%) in cerebellum, 0.4 in cerebrum, and 0.2 in
fat. Sick animals (apparently with leptospirosis) collected in 1970
and 1971 had similar Hg levels except in liver (161 mg/kg) and muscle
(1.6 mg/kg).
Respective tissue cadmium levels, in mg/kg wet wt, of healthy
sea lions collected during 1971 and 1973, and sick animals collected
during 1970 and 1971, were 2.0 and 2.6 for liver, 10.2 and 10.1 for
kidney, 0.13 and 0.07 for muscle, 0.14 and n.d. for heart, 0.05 and 0.06
for cerebellum, 0.04 and 0.17 for cerebrum, and 0.04 and n.d for fat.
Although Hg and Cd levels in tissues of some sick sea lions were sig-
nificantly higher than those present in healthy animals, authors con-
clude that it is not possible to relate these differences to onset of
leptospirosis.
1440.
Buikema, A.L., Jr., J. Cairns, Jr. and G.W. Sullivan. 1974.
Evaluation of Phi10dina acuticornis (Rotifera) as a bioassay
organism for heavy metals. Water Resources Bull. 10:648-661.
After 96 hrs in soft water, effective concentrations causing
50% immobilization (EC-50) of various metal salts to the rotifer P.
acuticornis, in mg/l, were: Cd 0.2 (as sulfate) and 0.5 (as chloride),
Cu 0.6, Hg 0.8, Zn 1.2 (as sulfate) and 1.5 (as chloride), Ag 1.4, Ni
2.9 (as chloride), Cr 3.1, Ni 7.4 (as sulfate), Pb 50.4, and Co 59.0.
The 96 hr EC-50 values in hard water were: Cd 0.3 mg/l, Cu 1.1, Hg
2.1, Cr 15.0 and Pb >150. Cadmium sulfate and zinc sulfate were more
toxic than their chloride forms in soft water after 96 hrs, while the
opposite was true for nickel. Increased water hardness decreased the
toxicity of metals tested. Results suggest that P. acuticornis may be
more sensitive than bluegill sunfish to Cd, CU, NT, Zn and Cr but less
sensitive to Pb. P. acuticornis was also tested for exposure to
ammonium chloride and phenol and was found to be extremely tolerant to
both. The feasibility and economics of using P. acuticornis as a bio-
assay organism were discussed. -
1441.
Burkett, R.D. 1975. Uptake and release of methylmercury-203
by Cladophora glomerata. Jour. Phycol. 11:55-59.
C. glomerata, a freshwater alga, was exposed to 10, 50, or
100 ug CH3 Hg-203Cl/l. Formalin-killed alga was exposed to a concen-
S9
-------
tration of 50 ug CHg Hg-203Cl/l. Uptake was monitored for 16 days,
after which Cladophora was placed in uncontaminated water and release
of CHg Hg-203 monitored for up to 16 days. Sorption occurred at all
concentrations; live algae accumulated more methylmercury than formalin-
killed algae. Accumulation by live Cladophora peaked at 2 days for all
exposure concentrations, suggesting that uptake rate was independent of
CHg Hg-203 concentration. A maximum concentration factor of 5597 was
obtained for exposure to 50 ug CHg Hg-203/1 for 24 hrs. Desorption was
nominal during 16-day reletse period. Mechanisms of CHg Hg-203 uptake
by Cladophora are discussed.
1442.
Burovina, I.V., V.V. Glazunov, V.G. Leont'yev, V.P. Nesterov,
I.A. Skul'skiy, D.G. Fleyshman and M.N. Shmitko. 1963.
Lithium, sodium, potassium, rubidium and cesium in the muscles
of marine organisms of the Barents and Black Seas. Doklady
Akad. Nauk SSSR 149:170-172.
Ratios of concentration of selected elements in 100 g of
fresh muscle tissue to those in 100 ml of seawater were determined for
various species of coelenterates, annelids, molluscs, crustaceans and
echinoderms. Ratios were as follows: Li, 0.52; Na, 0.30; K, 8.7; Rb,
11.0; and Cs, 5.8. Similar ratios for fish and elsamobranchs were:
Li, 0.36; Na, 0.12; K, 15.2; Rb, 19.6; and Cs, 8.4.
1443.
Burton, J.D. and T.M. Leatherland. 1971. Mercury in a coastal
marine environment. Nature 231:440-442.
Clams Mercenaria mercenaria, from Southampton Water, England,
contained 0.18 to 0.57 mg mercury/kg dry flesh wt (0.03 to 0.12 mg/kg
wet wt). Values reported for various molluscs, including Mercenaria,
collected off the coasts of North America are in the higher but over-
lapping range of 0.4 to 21 mg Hg/kg dry wt.
1444.
Burton, R.F. 1975. A method of narcotizing snails (Helix pomatia)
and cannulating the haemocoel and its application to a study
of the role of calcium in the regulation of acid-base balance.
Compo Biochem. Physiol. 52A:483-485.
Exposure of snails to 10% C02 caused haemolymph concentrations
of HCOg and Ca to increase up to 1220 and 520 mg/l in 4 hours but Na
and Mg levels were not measurably affected. Results indicate that HCOg
and Ca are in a 2:1 ratio in the haemolymph. Infusion of NaHCOg led
to subsequent loss of HCOg and Ca from the haemolymph in more than 2:1
ratio. Infusion of CaC12 led to subsequent loss of HCOg and Ca in a
60
-------
ratio of 2:1 or less. This indicates that other unidentified ions are
involved in response to C02.
1445.
Butterworth, J., P. Lester, and G. Nickless. 1972. Distribution
of heavy metals in the Severn Estuary. Marine Poll. Bull.
3(5):72-74.
Concentrations of zinc, cadmium, and lead in water, sediments,
seaweeds, and shore animals were determined at numerous locations on the
southern shore of the estuary. Abnormally high levels of the metals
were transmitted to living material, with particularly high concentra-
tions accumulated in the dog whelk, Thais. Highest concentrations, con-
sistently found in the upper estuary, in mg/kg, are given for Zn, Cd,
and Pb, respectively: Fucus vesiculosus 800, 220, 8.5; Littorina
littorea 520, 210, 3.0; Patella vulgata 580, 550, 9.5; Thais lapillus
3100, 425, 27.0; sediment 590, 4.7, 200; and seawater (in ug/l) 52, 5.8,
2.5. Contamination was detectable 144 km downstream of the most heavily-
impacted area.
1446.
Buyanov, N.I. and T.M. Antonenko. 1975. Cesium-137 concentra-
tion hydrobionts, water and substrate of bodies of water with
a different mineral ~omposition. Jour. Ichthyology 15(1):
159-163.
Comparison of Cs-137 content from a mineral-poor reservoir
(K content 0.6 mg/l) with a TIlineral-rich reservoir (K content 20 mg/l)
showed that Cs-137 content in fishes is inversely related to K content.
In the mineral-poor reservoir Cs-137 content, in 10-12 Ci/kg, was:
0.6 in water, 280 in zooplankton, 380 in cisco Coregonus albula, 1320
in perch Perea fluviatilus, and 1220 in pike Esox lucius. Cs-137 con-
centrations in the mineral-rich reservoir were:--0.2 in water, 1 in
phytoplankton, 40 in zooplankton, 10 in the mollusk Dreissena poly-
morpha, 10 in roach (teleost) Rutilus rutilus, 18 in perch and~in
pike. Authors suggest that food chain dynamics may indirectly affect
entry of radioisotopes into fish.
1447-
Caines, L.A. and A.V. Holden. 1976. Stream pollution by an
organomercury compound. Bull. Environ. Contamin. Toxicol.
16:383-391.
Industrial treatment of seed potatoes with methoxyethyl-
mercuric chloride occurs during a 10-week period in autUTIlTI. One result
is that sediment Hg levels in a small stream increased from 6 mg/kg in
August to 100 mg/kg in October at the outfall point. The submerged
macrophyte Callitriche sp. showed an increase in mercury from 1 mg/kg
61
-------
dry wt to 2215 mg/kg dry wt during this period. The emergent Myosotis
sp. reached 300 mg Hg/kg dry wt in October compared to less than 1 mg/kg
dry wt in August. Trout Salmo trutta, and grayling Thymallus thymallus,
caught upstream from the outfall had Hg muscle concentrations of less
than 0.1 mg/kg wet wt. However, at the outfall point, trout and gray-
ling had Hg muscle concentrations of up to 20 and 12 mg/kg wet wt,
respectively. Following adoption of a revised waste treatment program
in 1973, few fish exceeded 0.5 mg/kg wet wt; in 1974, none exceeded
0.4 mg/kg wet wt.
1448.
Cairns, J., Jr., A.G. Heath and B.C. Parker. 1975.
of temperature upon the toxicity of chemicals to
organisms. Hydrobiologia 47(1):135-171.
The effects
aquatic
The literature on temperature impact on toxicity of zinc,
cadmium, copper, chromium, and mercury salts as well as other compounds
to fish, algae, bacteria, protozoa, mollusca, and crustacea is reviewed.
1449.
Cairns, J., Jr., G.R. Lanza and B.C. Parker. 1972. Pollution
related structural and functional changes in aquatic com-
munities with emphasis on fresh water algae and protozoa.
Proc. Acad. Nat. Sci. Philadelphia 124(5):79-127.
Use of microbial communities for monitoring pollution in
aquatic environments is proposed. Past approaches, including "target
species" and "saprobian system" techniques are reviewed. Characteris-
tics of algal and protozoan community structure and function are dis-
cussed. Importance of environmental parameters, such as organic pollu-
tion, availability of nutrients, temperature and presence of toxic sub-
stances, including halogens, pesticides, surfactants, oils, suspended
solids, reducing agents, radioactive wastes and metals in influencing
species composition are discussed in terms of previous work. Litera-
ture reviewed includes effects of Zn, Cu, Cd, Li, Cr, Hg, Ni, Pb, Ca,
Mg, Fe on aquatic fungi, bacteria, algae, protozoa and fish.
1450.
Cairns, J" Jr., and D. Messenger. 1974. An interim report on
the effects of prior exposure to sublethal concentrations of
toxicants upon the tolerance of snails to thermal shock.
Arch. Hydrobiol. 74(4):441-447.
The possibility that freshwater snails suffer higher mor-
tality rates from rapid heat shock if previously subjected to sublethal
concentrations of Zn, Cr2 and phenol was investigated. Forty-eight hr
LC-50's for Cr+3 and Zn+ (in mg/l),respectively, for Goniobasis
livescens were 2.4 and 7.7, for LYmnaea emarginata 42.0 and 4.1, for
62
-------
Physa integra 0:4 and 4.4, and Zn+ only for Helisoma anceps 5.2. Sub-
lethal concentrations tested were 0.2x these values. In heat-shock
experiments G. livescens had mean mortality rates 12 to 60% higher when
previously exposed to toxicants. Authors conclude that prior or con-
comitant exposure to toxic chemicals may decrease tolerance to increased
temperature; however, responses are species and chemical specific, with
no general pattern evident.
1451.
Cairns, J., Jr., W.H. van der Schalie and G.F- Westlake. 1975.
The effects of lapsed time since feeding upon the toxicity
of zinc to fish. Bull. Environ. Contamin. Toxicol. 13(3):
269-274.
Groups of 10 goldfish were placed into 181of water con-
taining a lethal concentration (100 mg/l) of zinc as ZnS04 at 0, 1, 2,
4, 6, 12, 24, and 72 hours after feeding. Time until death was re-
corded for individual fish. Statistical analysis revealed a slight but
non-significant increase in survival time as the interval between feed-
ing and exposure to zinc increased. These variations in survival time
are not of sufficient magnitude to support the standard acute bioassay
requirement that fish not be fed for 24 or 48 hours prior to exposure
to a toxicant.
1452.
Calabrese, A. 1969. Individual and combined effects of salinity
and temperature of embryos and larvae of the coot clam,
Mulinia lateralis (Say.). BioI. Bull. 137:417-428.
Embryos of M. 1ateralis held at 25 C developed satisfactorily
(70% or more of maximum) within salinity range of 22.5 to 30%0;
27.5%0 was optimum. Ten percent of embryos survived at salinities as
low as 15%0 and 1.2% as high as 37.5%0. Some larvae survived at
all salinities tested (7.5 to 37.5%0) with 70% or more survival with-
in the range of 20 to 27.5%0, and an optimum of 25%0. Salinity
tolerance range of embryos narrowed above and below 22.5 C. Survival
of larvae was relatively uniform at temperatures of 7.5 to 27.5 C and
at salinities from 10 to 35%0. Growth of larvae was most rapid in
the salinity range 20 to 35%0 and temperature range 22.5 to 27.5 C.
1453.
Calabrese, A., F.P- Thurberg, M.A. Dawson and D.R. Wenzloff.
1975. Sublethal physiological stress induced by cadmium and
mercury in winter flounder, Pseudopleuronectes americanus.
In: Koeman, J.H. and J.J.T.W.A. Strik (eds.). Sublethal
effects of toxic chemicals on aquatic animals. Elsevier
Sci. Pub. Co., Amsterdam: 15-21.
63
-------
After 60 days exposure to 0.005 and 0.010 mg/l cadmium,
flounder gill-tissue oxygen consumption was reduced from about 675 to
590 ~l/hr/g. Fish exposed to 0.010 mg/l mercury increased respiration
from 560 to 640 ~l/hr g, while fish exposed to 0.005 mg/l Hg respired
at same rate as controls. There was no significant difference between
controls and cadmium-exposed fish for any hematological test, but sig-
nificant differences were no~ed in mercury-exposed fish. Plasma pro-
tein rose from 5.4 to 6.3% in fish exposed to 0.005 mg/l Hg with a
decrease in plasma osmolality; normally hyposmotic blood became even
more so. Exposure to 0.010 mg/l Hg also resulted in a significant rise
in plasma protein while hemocrit, hemoglobin and mean corpuscular hemo-
globin decreased. Significant levels of Hg, but no detectable amounts
«0.2 to 0.3 mg/kg wet wt) of Cd were found in blood and gill tissues.
Mean levels of 20.6 and 42.8 mg Hg/kg wet wt were present in gills of
fish exposed to 0.005 and 0.010 mg/l Hg, respectively, as opposed to
<0.14 in controls. Blood accumulated Hg significantly at 2.9 and 3.8
mg/kg wet wt for exposures of 0.005 and 0.010 mg/l. Mean Hg levels in
blood of control flounder was <0.04 mg/kg wet wt.
1454.
Carbonneau, M. and J.-L. Tremblay. 1972. Etude
Scirpus americanus Pers. dans la depollution
taminees par les metaux lourds. Naturaliste
523~532.
du role de
des eaux con-
Canadien 99:
Natural lev8ls of mercury in the St. Lawrence River during
August 1971 ranged from <0.04 to 0.11 ~g/l; levels in rhizomes of Scirpus
americanus contained more mercury (0.83 mg/kg) and lead (34.0 mg/kg) than
stems (0.19 mg/kg Hg; 6 mg/kg for Pb) and suggested to authors that this
plant can be utilized as a natural depolluting agent.
In laboratory studies on Scirpus, Eleocharis smalli, and
Bidens cernua (other bog-like plants) with salts of Cd, Hg, and Pb, rela-
tively high concentration factors were demonstrated in rhizomes. Initial
concentrations of Pb in the water of 0.05 mg/l resulted in 336 mg/kg in
Scirpus rhizomes; at 1.0 mg/l, levels of 376 and 1782 were observed in
Scirpus and Eleocharis rhizomes, respectively; at 1.5 mg/l of Pb Scirpus
contained 885, Eleocharis 3321, and Bidens 625 mg Pb/kg wet wt after
72 hrs (levels in stems were substantially lower). With inorganic
mercury salts, initial concentrations in the media between 0.1 and 0.5
mg Hg/l produced levels in Scirpus rhizomes from about 75 to 350 mg
Hg/kg wet wt in 72 hrs; for Scirpus stems, Hg values were lower at the
same test concentrations, viz 8 to 42 mg/kg. Cd levels of 0.05, 0.1,
an~ 0.4 mg/l in water produced Cd values in mg/kg wet wt of Scirpus
rhIzomes of 26, 129, and 238, respectively, in 72 hrs; maximum value
reached in stems was 14 mg/kg.
64
-------
1455.
Cardiff, 1.0. 1937. Observations with reference to arsenic on
apples and other foodstuffs. Proc. Wash. State Horticulture
,Assn. 33:153-168.
Levels of As and Pb in various foods as determined from pre-
vious studies, in mg/kg, are: marine algae--Chondrus 61 As, Laminaria
110 As; shrimp 2 to 9 As and as high as 150 As; prawn 25 As, 147 Pb;
lobsters 2 to 25 As, 22 to 82 Pb; cockles 14 As, 22 Pb; clams 1.2 to 2.2
As; scallops 25 As, 44 Pb; mussels 25 As, 93 Pb; oysters 1.2 to 2.0 As;
haddock 4.8 As; tuna 0.6 As; codfish 2.2 As; cod liver oil (U.S.) 0.5
As; cod liver oil 0.6 to 1.1 As; and sardine oil 1.0 As.
1456.
Carlisle, O.B.
1958.
Niobium in ascidians.
Nature 181:933.
Mussels Mytilus edulis contained 0.22 mg vanadium and <0.001
mg niobium per kg dry flesh. Phallusia marnrnillata, an ascidian, con-
tained 1260 mg V and <0.001 mg Nb per kg dry wt. Respective average V
and Nb contents in mg/kg dry wt of Molgula manhattensis another ascidian,
were 16.0 and 1.9 in test, 101 and 56 in flesh without test, and 54.0
and 26.5 in whole organism. Individual Molgula contained either 29 to
98 mg V and <0.001 mg Nb per kg dry wt, or 25 to 75 mg Nb and <2 mg V
per kg dry wt. If, as has been suggested, the V present in petroleum
deposits is derived from ascidians, it seems likely that these may also
be the source of the Nb which is also present on these deposits.
1457.
Carlisle, O.B. 1968. Vanadium and other metals in ascidians.
Proc. Roy. Soc. London B. 171:31-42.
Ascidian blood contains V, Nb, Ta, Ti, Cr, Mn, Fe, and pos-
sibly Zr, Mo and W. In the family Ascidiidae, V is the only heavy metal
in blood; other families have two or more of those metals with V and Nb
usually predominating. But the mixture of metals in ascidians may be
dictated by availability in seawater. Metal-holding pigments are power-
ful reducers, and may assist in transport of molecular oxygen in
Ascidiidae during times of low 02 tension.
1458.
Carpenter, K.E. 1930. Further researches on the action of
metallic salts on fishes. Jour. Exp. Zool. 56(4):407-422.
In 0.2 to 0.0005 M solutions of lead nitrate or lead acetate,
13 species of freshwater teleosts formed Pb-mucous films over gills and
body surfaces, causing respiratory distress, and death if sufficient Pb
concentrations were present. In a multi-species collection of fish,
susceptibility to soluble Pb was directly correlated with metabolic rate.
In Notropis cornutus and Hyborhynchus notatus, body weight and tempera-
65
-------
ture were inversely related to susceptibility and metabolism. Starvation
for 4 to 5 weeks decreased both metabolic rate and susceptibility; subse-
quent starvation increased both. A certain minimum volume of solution
was necessary to provide maximal lethal action for a constant concentra-
tion of PbN03' This volume increased for decreasing PbN03 concentrations.
From studies of several fish in the same solution, and the replacement
of one fish by another in the same solution, author suggests that critical
volume for maximal lethal action is proportional to total weight of fish
used. Survival times for N. cornutus, weighing 2.5 g, in 4 1 of medium,
were 42 minutes in 21 g Pb7l and 67 minutes in 5 g Pb/l.
1459.
Cearley, J.E. and R.L. Coleman. 1974. Cadmium toxicity and bio-
concentration in largemouth bass and bluegill. Bull. Environ.
Contamin. Toxicol. 11:146-151.
A 6-month static bioassay, utilizing 0.85, 0.08, 0.008 and
0.0005 mg/l cadmium concentrations was conducted on bluegill Lepomis
macrochirus, and bass Micropterus salmoides. Fifty-percent mortality
was shown within 56 days by bass at 0.85 mg Cd/I; for 0.08 mg Cd/l the
LC-50 was 82 days. Bass exposed to 0.008 mg Cd/l had l2~2% mortality
in the 6-month period. Fifty percent of the bluegills exposed to 0.85
mg Cd/l died within 138 days. Those exposed to 0.08 and 0.008 mg Cd/l
survived the 6-month study. Bass appeared to be more sensitive than
bluegill to Cd. The first abnormal behavior patterns of a toxic reac-
tion occurred during the third week for bass exposed to 0.85 mg Cd/I,
during the seventh week for 0.08 mg Cd/l and the twelfth week for 0.008
mg Cd/I; these behavior patterns, indicative of neurological damage were
observed in bluegill during the thirteenth week of exposure at 0.85 mg
Cd/I. Quantity of metal accumulated increased as exposure concentration
increased. Equilibrium developed between concentrations of metal in
water and in tissues after 2 months. Cadmium accumulations in bass
tissues were higher in internal organs, followed by gills and remainder
of body.
1460.
Cedeno-Maldonado, A. and J.A. Swader. 1974. Studies on the
mechanism of copper toxicity in Chlorella. Weed Sci. 22(5):
443-449.
In Chlorella sorokiniana, photosynthesis and respiration were
inhibited within 2 to 5 min after addition of 64 mg Cu2+/l. Cells incu-
bated for a short time in concentrations of Cu2+ that completely inhibited
photosynthesis were unable to grow when cultured in Cu-free medium,
indicating destruction of photosynthetic apparatus and autotrophic growth
ability. Dark preincubation, as well as high bicarbonate concentrations,
decreased inhibition. Cu2+ reduced cellular chlorophyll and sulfhydryl
66
-------
content, but anaerobiosis, which increased toxicity, had little effect
on sulfhydryl content.
1461.
Cedeno-Maldonado, A., J.A. Swader and R.L. Heath. 1972. The
cupric ion as an inhibitor of photosynthetic electron trans-
port in isolated chloroplasts. Plant Physiol. 50:698-701.
Strong inhibition of uncoupled photosynthetic electron trans-
port by Cu2+ in isolated spinach chloroplasts was observed by measuring
changes in 02 concentration in reaction medium. Inhibition was depend-
ent not only on the concentration of Cu2+, but also on the ratio of
chlorophyll to Cu2+. Binding of Cu2+ to chloroplast membranes resulted
in removal of Cu2+ from solution. When chloroplasts were exposed to
preincubation in light, there was increased inhibition as a result of
Cu2+ binding to inhibitory sites. Preincubation in dark resulted in
Cu2+ binding to noninhibitory sites and decreased inhibition. Degree
of inhibition was lower at low light intensities than at high light
intensities. Of the two photosystems examined, I was more resistant to
inhibition than II. Oxidizing site of photosystem II was site most
sensitive to Cu2+.
1462.
Chapman, A.C. 1926. On the presence of compounds of arsenic in
marine crustaceans and shell fish. Analyst (London) 51:
548-563.
Edible seaweeds contained between 5 and 125 mg/kg of arsenic
(as arsenious oxide on the air dry substance). British oysters con-
tained 3-10 mg/kg wet wt but values for Portuguese oysters were higher
(33-70 mg As per kg wet wt). Whole scallops contained 36-85 mg/kg wet
Wt; As content was practically uniform in all tissues examined. Ranges
for mussels, cockles, whelks, and periwinkles, on a mg/kg wet wt basis,
were 36-119. 17-40, 12-40, and 20-36, respectively. Lobster flesh con-
tained between 18 and 110 mg As/kg wet wt; boiling for 20 minutes appears
to have no effect upon As content of flesh. Prawns, Nephrops norvegicus,
contained 36-80 mg/kg wet wt in flesh, but one pooled sample of two
dozen was anomalously high (174 mg As/kg wet wt). Other crustaceans
examined (crabs, shrimps, spiney lobster--Palinuris vulgaris) contained
between 17 and 70 mg As/kg wet wt. Arsenic in seawater averaged 0.33
mg/l (range 0.14-1.0). Flounder-like fishes (plaice, sole, dab) con-
tained between 3 and 10 mg As/kg wet wt; a sample of Russian caviar had
5 mg As/kg wet wt. Preliminary studies indicated that arsenic in lobster
was present as a complex organic substance. Freshwater snails, crusta-
ceans, and fishes were much lower in As than their marine counterparts
(range 0.4-1.4 mg AS/kg wet wt). Canned prawns, crayfish, and oysters
ranged from 0.5-40 mg AS/kg wet wt; crabs contained up to 85 mg/kg wet
wt.
67
-------
Limited studies with humans fed lobster showed large amounts
of As excreted in the urine, the concentration being proportional to the
amount of lobster ingested.
1463.
Chau, Y.K., P.T.S. Wong, B.A. Silverberg, P.L. Luxon, and G.A.
Bengert. 1976. Methylation of selenium in the aquatic
environment. Science 192:1130-1131.
Conversion of inorganic and organic selenium compounds to
volatile selenium compounds, such as dimethyl selenide, dimethyl
diselenide, and an unknown compound, by microorganisms in lake sediments
of the Sudbury area of Ontario, has been observed. This conversion
could be effected by pure cultures of Aeromonas sp., Flavobacterium sp.,
Pseudomonas sp. and an unidentified fungus, all found in lake sediments
exhibiting methylation. Production of volatile seleniUm was temperature
dependent with 25% less (CH3)2Se produced at incubation temperatures of
10 C as at 20 C; reduction was 90% at 4 C.
1464.
Chave, K.E. 1954. Aspects of the biogeochemistry of magnesium.
I. Calcareous marine organisms. Jour. Geology 62:266-283.
Percent MgC03 in calcareous parts of many species of marine
organisms were determined. This ranged from 0.3 to 15.9% for foramin-
fera, 5.5 to 14.1% for sponges, 0.1 to 0.7% for madreporian corals,
6.0 to 13.8% for alcyonarian corals, 5.5 to 15.9% for echinoids, 2.0 to
10.2% for echinoid spines, 8.6 to 16.1% for asteroids, 9.2 to 16.5% for
ophiuroids, 8.3 to 15.9% for crinoids, 6.4 to >16.5% for annelid worms,
0.09 to 2.8% for pelecypods, 0.08 to 2.4% for gastropods, 0.05 to 7.0% for
cephalopods, 5.2 to 11.7% for decapod crustaceans, 2.0 to 10.2% for
ostracod crustaceans, 1.35 to 4.6% for barnacles, and 7.7 to 28.7% for
calcareous algae. Increased ambient water temperature resulted in
greater % MgC03 in calcareous hard parts.
1465.
Cherr~ D.S., R.K. Guthrie, J.H. Rodgers, Jr., J. Cairns, Jr.,
and K.L. Dickson. 1976. Responses of mosquitofish (Gambusia
affinis) to ash effluent and thermal stress. Trans. Amer.
Fish. Soc. 105:686-694.
Gambusia was the only fish species inhabiting a drainage
system that received high coal ash concentration at one end and thermal
discharges at the other. Concentrations of 40 elements were determined
in this aquatic system. The order for the most abundant elements in
water was Fe > Al-Si > Ca > Na > K > Mg > Ti > Ba > Rb > Cu > Zn > Sr >
Ce > Cr. The order of abundance and concentration in mg/kg wet wt, in
mosquitofish was Ca 5,752; K 1,946; Na 309; Mg 307; Al-Si 215; Fe 154;
68
-------
Sr 36; Ba 20; Ti 15; Zn 12; Rb 10; Mn 10,; Se 9; and Cu 8. Relatively
low levels of the following were present: Cd, Sn, Se, Mn, Sb, Co, As,
W, V, Hg, Ta, Mo, Th, La, Cs, Yb, U, Hf, Sc, Sm, Au, Lu, and In. The
most active ash removal mechanism was settling since 35 of the 40 ele-
ments were most highly concentrated in the sediment. Elements that
underwent biological magnification were Se, Zn and Ca.
1466.
Cherry, R.D., S.W. Fowler, ~.M. Beasley, and M. Heyraud. 1975.
Polonium-210: its vertical oceanic transport by zooplankton
metabolic activity. Marine Chemistry 3:105-110.
Previous work has shown that Po-210 is removed from the upper
mixed layer at a rapid rate, expressible by a turnover (or mean residence)
time of 0.6 years. Since Po is known to be highly concentrated in
numerous marine species, a method was devised to assess the importance
of marine zooplankton in removing this radionuclide from the surface
waters. Measurements of Po-210 losses from living zooplankton (euphasiids)
lead to a rapid turnover time of the order of 0.9 years due to zooplankton
metabolic activity alone. It is shown experimentally that fecal pellet
deposition constitutes a major mechanism in transporting the radio-
nuclide from surface to deeper waters.
1467.
Chervinski, J. and E. Hering. 1973. Tilapia zilli (Gervais)
(Pisces, Cichlidae) and its adaptability to various saline
conditions. Aquaculture 2:23-29.
Maximum salinity tolerance of T. zilli on direct transfer is
between 60-70% seawater (S=23.4 to 27.30/00). Through gradual adapta-
tion, the fish can withstand up to 100% seawater (S=390/00). T. zilli
collected from a hypersaline lagoon, and from a freshwater body showed
differences in ratio of: head to standard length, depth to standard
length, preorbital to standard length and interorbitol to standard
length.
1468.
Chervinski, J. and M. Zorn. 1973. Pampano, Trachinotus ovatus
L. (Pisces, Carangidae) and its adaptability to various
saline conditions. Aquaculture 2:241-244.
Laboratory experiments were conducted to determine the adapt-
ability of pampano, a marine fish, to low salinities. The minimum
salinity tolerated by juveniles on direct transfer is 7.8%0. Through
gradual adaptation pampano can withstand salinity as low as 1.5%0.
69
-------
1469.
Childs, E.A.
capacity.
1974. Functionality of fish muscle: emulsification
Jour. Fish. Res. Bd. Canada 31:1142-1144.
. Emulsification capacity of English sole Parophrys vetulus,
sand sole Psettichthys melanostictus, petrale sole Eopsetta jordani,
lingcod Ophiodon elongatus, and orange rockfish Sebastes pinniger showed
little variation from four catches spaced over a period of 3 months.
Frozen storage (-40 C) caused no apparent decrease in emulsifying capa-
city after 12 months of storage. Addition of 0.02% free fatty acid to
white muscle homogenate of rockfish caused a >20% increase in emulsify-
ing capacity. Exposure to 0.04, 0.08, or 0.20% formaldehyde or 50, 100,
or 200 mg/l CUC12 produced decreases in emulsifying capacities which did
not show dose relationships; but 50, 100, or 200 mg/l CuCl had no sig-
nificant effect.
1470.
Chipman, W.A. 1958. Accumulation of radioactive materials by
fishery organisms. Proc. Gulf Caribb. Fish. Inst. 11:97-110.
Laboratory studies are described on uptake, retention and
translocation of isotopes of Sr, Co, Zn, and Cs by various species of
marine algae, crustacea, fish and molluscs.
1471.
Chipman, W.A., T.R. Rice and T.J. Price. 1958. Uptake and accu-
mulation of radioactive zinc by marine plankton, fish, and
shellfish. U.S. Fish. Wild. Servo Fish. Bull. 135, Vol. 58:
279-292.
Zinc concentrations in sea water collected from inshore
waters along the Atlantic and Gulf of ~1exico coasts averaged 10.6 ug/l
(range: trace to 24.56 ug/l). Oysters, clams, and scallops concentrate
large amounts of Zn, with oysters containing the greatest amounts by
several orders of magnitude. Radioactive zinc added to water was
quickly taken up in great amounts by shellfish. Considerable accumula-
tion of the nuclide occurred in gills of these mollusks, with high con-
centrations in kidneys of scallops, and considerable amounts in hepato-
pancreas. Nitzschia closterium, a marine phytoplankter, took up large
amounts of zinc-65 and apparently concentrates zinc, thus allowing its
transfer to marine animals. Marine fish rapidly take Zn into the body
from the digestive tract, with most being quickly excreted. A rapid
uptake of radioactive zinc from an oral dose took place in the kidney,
liver, and other internal organs, but loss of the nuclide was also
rapid. A slow and long-continued accumulation was observed in bone,
integument, and muscle tissues. Although there was immediate loss of
contained radioactive zinc when marine fish were returned to flowing
seawater, a small percentage remained with only very slight loss over
many days.
70
-------
1472.
Chopra, T. 1971. Decreased uptake of cadmium by a resistant
strain of Staphylococcus aureus. Jour. Gen. Microb. 63:265-
267.
Cadmium uptake was estimated by adding Cd-115mC12 (final
conc.: 10-4~1) to exponentially growing cultures of sensitive and resist-
ant strains of S. aureus. The nonspecific binding of Cd2+ was 170 x
1012 ions/ml medium, equivalent to 15% of total Cd2+ accumulated by one
ml of culture from the sensitive strain. Total uptake of Cd by Cd-
sensitive cells was about 15 x that of resistant strains; uptake was
about 106 x 104 Cd2+/mg dry wt for sensitive organisms. Exchange experi.
ments were performed in which sensitive organisms were labelled for 40
min and then resuspended in non-radioactive medium. About 60% of the
Cd-115m was displaced, suggesting that about 40% of the Cd2+ taken up
by Cd-sensitive staphylococci were bound to some structure within the
cell rather than adsorbed adventitiously to the surface.
1473.
Chow, T.J., C.C. Patterson and D. Settle.
lead in tuna. Nature 251:159-161.
1974.
Occurrence of
Lead content of pectoral fin tissue of yellowfin tuna Neo-
thunnus macropterus was 5.3 mg/kg wet wt; for skipjack Katsawanus---
pelamis this was 4.1; and for albacore Thunnus alalunga, 0.45. Albacore
muscle contained 0.0002 to 0.0003 mg/kg wet wt. Tuna epidermis concen-
trated lead at comparatively high levels: 1.4 to 1.7 mg/kg wet wt.
Tuna scales and dermis contained 0.06 and 0.01 mg Pb/kg wet wt, respec-
tively. Commercial canned tuna had lead concentrations of 0.10 to 0.93
mg/kg wet wt, suggesting that industrial lead contamination was 1,000x
greater than biological uptake.
1474.
Chow, T.J., H.G. Snyder and C.B. Snyder. 1976. Mussels (~1ytilus
sp.) as an indicator of lead pollution. Science Total Envir.
6:55-63.
Lead in Mytilus californianus and M. edulis, collected along
the Pacific coast from Piedras Blancas, California to Punta Banada, Baja
California was determined by isotope dilution method and showed a defi-
nite correlation between lead content and man's activity along the
coastal zone. For regions in California such as Piedras Blancas, Cayuco
and Gaviota, which are sparsely populated, Pb content of soft parts of
M. californianus was low with means ranging from 0.32 to 0.85 mg/kg wet
wt. Highest average for M. californianus was found in La Jolla speci-
mens, at 7.96 mg/kgdry wt. Mytilus edulis from docks and pilings in
marinas and bays contained up to 33 mg/kg dry wt (Anaheim Bay); gills
contained highest amounts of Pb, followed by stomach. No difference was
observed in average isotope ratios of Pb in both species.
71
-------
1475.
Christiansen, M.E. and J.D. Costlow, Jr. 1975. The effect of
s.alini ty and cyclic temperature on larval deve 10pment of the
mud-crab, Rhithropanopeus harrisii (Brachyura: Xanthidae)
reared in the laboratory. Marine Biology 32:215-221.
Larvae of R. harrisii were reared to first or second crab
stages in 11 combinatlons of salinities and cyclic temperatures. Larvae
survived to megalops and first crab stages in all salinities and cycles
of temperature other than 5%0 S at 30 to 35 C. Best survival to mega-
lops (94%) and first crab (90%) stages occurred in 20%0 S, 20 to 25 C.
Duration of larval stages was affected significantly by temperature;
salinity effects were inconsistent. Development to first crab stage was
shortest in 20%0 S, 30 to 35 C (mean 12.3 days), and longest in 5%0
and 35%0 S 20 to 25 C (mean 22.6 days and 21.6 days, respectively).
, °
Megalops larvae reared in 35 /00 S at all cycles of temperature, as well
as larvae in 20%0 and 25%0 S, 30 to 35 C, showed abnormalities, with
highest percentage occurring in 35%0 S, 30 to 35 C. Authors suggest
that larval development of R. harrisii is strongly influenced by environ-
mental factors and not solely related to genetic differences.
1476.
Ciereszko, L.S., E.M. Ciereszko, E.R. Harris and C.A. Lane.
1963. Vanadium content of some tunicates. Compo Biochem.
Physiol. 8(2):137-140.
In 12 ascidian species of the order Phlebobranchia, V occurred
at levels of 206 to 4123 mg/kg organic dry weight. Centrifuged blood
cells of Ascidia nigra had 14.6 g V/kg wet wt. Vanadium was not detected
in four species of salps: Salpa democratica, S. maxima, S. confederata
and Ihlea punctata. V was not detected in ascldians of the families
Synoicidae, Polycitoridae and Styelidae. Eggs of Phallusia mami1lata
had 0.17 g V/kg dry wt.
1477 .
Cintr6n, G., W.S. Maddux and P.R. Burkholder. 1970. Some conse-
quences of brine pollution in the Bahia Fosforescente, Puerto
Rico. Limnology Oceanography 15(2):246-249.
Brine pollution from a sea-salt works occasionally flows into
Bahia Fosforescente causing stagnation, severe anoxia and accumulation of
hydrogen sulfide (89 ml/liter) with consequent toxic effects on local
flora and fauna including several species of algae and higher plants,
lobsters (Panuluris sp.) and fish (Jenkinsia). The bottom brine
(salinity 57%0) constitutes a lethal trap which accumulates and kills
phytoplankton so that the water turns yellow-green and reaches a chloro-
phyll a (actually pheophytin) content of about 2,000 ug/l as compared
with chlorophyll levels of about 4 ug/l in the normal surface water.
Colonization of the bay bottom by benthic plants and animals may have
72
-------
been prevented by limited light and intermittent brine pollution since
the adjacent salt works was established in 1937.
1478.
Clausen, C.D. and A.A. Roth. 1975. Estimation of coral growth
rates from laboratory 45Ca-incorporation rates. Marine
Biology 33:85-91.
Calcification ratios were obtained for 2 species of herma-
typic corals by incubating apical (fast growing) portions of freshly
collected coral branches in Ca-45. Results, in ng/mm2/h were 483 and
2304 for side and end cores, respectively, for Porites compressa and 73
and 415 for lateral and terminal regions of Pocillopora damicornis.
Ca-45 exchange across the coenosarc was insignificant. P. damicornis
demonstrated diurnal fluctuations with the calcification-rate at noon
being twice as rapid as at midnight. Growth rates, calculated from Ca-45
incorporation data, were 20 and 6 mm/yr for P. compressaandP. damicornis,
. ~-
respectlvely, and compare favorably with fleld growth rates of 24 and
14 mm/yr.
1479.
Cleland, K.W. 1953. Heavy metals, fertilization and cleavage in
the eggs of Psammechinus miliaris. Exp. Cell Res. 4:246-248.
Copper sulphate additions, in mg/l, had the following effects
on sea urchin embryogenesis: 1.6--no sperm penetration; 0.8--no membrane
elevation but mostly normal and polyspermic cleavage; 0.4--excentric mem-
brane elevation; 0.16--no effect. Membrane elevation was suppressed by
124 mg Pb/l. Zn additions, in mg/l, caused following effects: 6.5--no
sperm penetration; 0.65--no elevation of fertilization membrane, abnormal
cleavage; 0.065--separation of fertilization membrane, cleavage abnor-
malities and polyspermic cleavage.
1480.
Clemens, H.P. and K.E. Sneed. 1958. The chemical control of some
diseases and parasites of channel catfish. Prog. Fish-Cult.
20(1):8-15.
LC-50 (72 hr) values of two prophylactic compounds, pyridyl-
mercuric acetate (80% active) and phenylmercuric acetate (10% solution),
to catfish Ictalurus punctatus, were 0.49 and 0.60 mg/l, respectively.
Pharmaceutical worth of these compounds to fish is discussed.
1481.
Clendenning, K.A. and W.J. North. 1959. Effects of wastes on the
giant kelp, Macrocystis pyrifera. In: Pearson, E.A. (ed.).
Proc. 1st Conf. Waste Disposal Marine Environ., Berkeley,
Calif.: 82-91.
73
-------
Effects of sewage effluent, organic and inorganic pollutants
on M. pyrifera in the field and laboratory were studied. The following
concentrations in mg/l of inorganic ions caused 50% inactivation of photo-
synthesis in bottom kelp fronds during 4 day exposure: 0.05 for Hg, 0.1
for Cu, 2.0 for Ni, 5.0 for Cr+6, 10.0 for Zn, and >10.0 for Pb.
1482.
Cocoros, G., P.H. Cahn and W. Siler. 1973. Mercury concentra-
tions in fish, plankton and water from three western Atlantic
estuaries. Jour. Fish BioI. 5:641-647.
For Core Sound, Chesapeake Bay and Oyster Bay, mercury levels,
in mg/kg dry wt, were 0.11 to 0.13 for plankton (primarily phytoplankton),
0.19 for plankton (primarily zooplankton) and 0.27 to 0.50 for menhaden
Brevoortia tyrannus. High visceral Hg contents in fish suggested food
chain uptake. Authors concluded, however, that no evidence of strong
food chain intensification exists.
1483.
Coleman, R.D., R.L. Coleman and E.L. Rice. 1971. Zinc and cobalt
bioconcentration and toxicity in selected algal species.
Botanical Gazette 132:102-109.
Growth inhibition and bioaccumulation of Zn and Co in 3 species
of freshwater algae was investigated. Zinc adversely affected growth of
Pediastrun tetras and Euglena vividis at 18.0 mg/l in 3 weeks, but
Chlorella vulgaris was not affected at 35.5 mg/l in a similar period.
Concentrations of 4.2 mg/l Zn promoted growth of all species. Concentra-
tions of cobalt above 0.04 mg/l, i.e. 0.55 mg/l and higher, retarded
growth of all species. The 3 species accumulated Zn and Co on exposure
to high environmental levels. For zinc, concentration ranged from 0.1
mg/kg dry wt at 1.88 mg/l environmental Zn2+ to 80 mg/kg dry wt at 35.5
mg/l Zn2+. Similar trends were exhibited for cobalt, with final concen-
tration factors for both Zn and Co ranging between 1400 and 2446 for all
species and concentrations tested. It was concluded that algae might
accumulate Zn and Co to the point where they were toxic in the food web.
On the other hand these species might be effective as biological filters
for waters polluted by Zn and Co.
1484.
Collier, A.
brevis
1953.
Davis.
Titanium and zirconium in bloom of GYmnodinium
Science 118:328.
Total solids (33.7 g/l) of a red-tide dinoflagellate bloom in
the Gulf of Mexico contained 0.01 to 0.1% of titanium and 0.001 to 0.01%
zirconium.
74
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1485.
Colwell, R.R. and J.D. Nelson, Jr. 1974. Bacterial mobilization
of mercury in Chesapeake Bay. Proc. Inter. Conf. Transport
Persistent Chern. in Aquatic Ecosys., Ottawa, Canada: 111:1-10.
The total number of mercury-resistant bacteria is an index of
microbiological Hg transformation. There was a greater number of resist-
ant populations associated with plankton than with water or sediments.
Resistance and metabolism of Hg2+ and P~~ (phenylmercuric acetate) are
related and inducible in Pseudomonas. PMA metabolism ceased at <8.2%
seawater. Percentage of Hg resistant bacteria in bay sediments peaks
sharply at 30% in the spring.
1486.
Colwell, R.R. and J.D. Nelson, Jr. 1975. Metabolism of mercury
compounds in microorganisms. U.S. EPA Rept. 600/3-75-007.
U.S.EPA, Office Res. Dev., Envir. Res. Lab., Narragansett,
R.I.: 84 pp.
Aerobic heterotrophic bacteria, resistant in varying degrees
to mercuric ion, organomercurials, PMA (phenylmercuric acetate) and Me
HgCl (methylmercuric chloride), were isolated from water, sediment, and
plankton of Chesapeake Bay. Resistance is derived from ability to degrade
Hg compounds with formation of HgO, this capability being correlated with
ability to grow in presence of these compounds. Hg resistance is also
related to conditions of incubation, being lower under anaerobic condi-
tions6 and increasing with temperature and extreme salinity conditions
(26.5 600 and 2.6%0) while decreasing at intermediate salinities
(11.38 /00). The ionic requirement for activity is met by ~1g2+ ions
alone, with a concentration of 5-10 mM optimum for PMA degradation, and
1.2 to 5.6 roM optimum for resistance, the latter being the approximate
average in situ concentration of ~1g. When resistance to other heavy
metal ions was tested, variable results were obtained indicating that
resistance is not generalized. Metals tested and ran~e of maximum con-
centrations survived (in mg/l) were: A13+ 16-167; Pb + 167; Ag+ 1.7-
16.7; As5+ 501; C02+ 18-334; Cu2+ 334; Zn2+ 18-167; Cd2+ 16-167; C~+ 1.7-
668; and Hg2+ 4-50.
Numbers of Hg-resistant, aerobic, heterotrophic bacteria at
6 locations in Chesapeake Bay were monitored over a 17 mo. period, as
well as total ambient Hg concentrations in water (0.080 to 0.490 ug/l)
and sediment (0.007 to 0.860 mg/kg). Hg resistance reached a reproduc-
ible maximum in spring and was positively correlated with dissolved
oxygen and sediment Hg concentration and negatively correlated with water
turbidity. A relation between mercury resistance and metabolic capa-
bility for reduction of mercuric ion to the metallic state was estab-
lished by surveying a number of HgC12-resistant cultures. The reaction
was also observed in microorganisms isolated by differential centri-
fugation of water and sediment samples. Hg2+ exhibited an average half
life of 12.5 d in the presence of ~105 organisms/mI.
75
-------
Cultures resistant to 6 mg/l of HgC12 (4.43 mg/l Hg) and 3
mg/l of PMA (1.79 mg/l Hg) were classified into 8 generic categories.
Pseudomonas spp. were the most numerous of those bacteria capable of
metabolizing both compounds; however, PMA was more toxic and was more
selective for Pseudomonas. Hg resistant generic distribution was dis-
tinct from that of total bacterial generic distribution and differed
significantly between water and sediment, positionally, and seasonally.
The proportion of non-glucose-utilizing Hg resistant Pseudomonas spp.
was positively correlated with total bacterial Hg resistance. Concen-
trations as low as 1.2 ug/l HgC12 or PMA inhibited a measurable portion
of total population. It is concluded from this study that numbers of
Hg-resistant bacteria as established by plate count can serve as a
valid index of in situ Hg2+ metabolism.
The majority of PMA bound to components of the cell envelope;
with Hg, in general, impairing normal cell wall and membrane synthesis
and function. Concentrations of >1 mg/l produced a lag phase in the
growth pattern, at which time Hg-resistant mutants were selected which
were capable of releasing HgO from the growth medium. To determine the
role of bacteria in moving Hg through the food chain, short-term experi-
ments with oysters were set up with controls, addition of Hg-resistant
bacteria, and addition of Hg-accumulating bacteria. Uptake by oysters
was 22%, 39.3%, and 36.9% of initial Hg (10.2 ug/l), respectively.
Gills accumulated Hg most rapidly, with average concentration factors
of 620, 2974, and 2779, respectively; while average whole body concentra-
tion factors were 173, 425, and 390, respectively. It is concluded that
bacteria may have a demonstrable effect on Hg accumulation in those
food chains which include filter feeding components.
1487.
Colwell, R.R., G.S. Sayler, J.D. Nelson, Jr., and A. Justice.
1976. Microbial mobilization of mercury in the aquatic
environment. In: Nriagu, J.D. (ed.). Environmental Bio-
geochemistry, Vol. 2. Metals Transfer and Ecological Mass
Balances. Ann Arbor Sci. Publ., Ann Arbor, Mich.: 437-487.
A total of 364 bacterial isolates resistant to HgC12 were
cultured from Chesapeake Bay; 97.5% of these comprised 7 genera and more
than 60% were pseudomonads. Approximately 90% of the 70 strains of
phenylmercuric chloride-resistant bacteria were identified. Mercury-
resistant bacteria in this study were resistant to HgC12 at concentra-
tions up to 50 mg/l after adaptation in HgC12 or PMA (phenylmercuric
acetate) media. There were no significant differences between water and
sediment in proportions of Hg-resistant bacteria isolated from 3 sites.
Some morphological distortions seen in Enterobacter strains grown in
media containing 2 ~g HgC12/ml for 24 hrs included lysed cells and cells
with abnormal cross wall formation. Oysters Crassostrea virginica
collected from Tolley Bar region of Chesapeake Bay were dosed with
76
-------
bacteria capable of accumulating mercury on, or in the cell or of reduc-
ing and volatizing both organic and inorganic mercury. All three tests
were run in a 10 g/l Hg-203 labeled HgC12 solution. The mercury reduc-
ing Pseudomonas strain reduced 25.4 ~g HgC12 to elemental mercury from
a solution containing 6 mg HgC12/l; the mercury-accumulating Pseudomonas
strain accumulated 12 ~g HgC12/mg cells/IS min from a solution contain-
ing 6 mg HgC12' After 96 hr, accumulations in whole oysters, in ~g
Hg/kg wet wt, were 201 for controls, 312 for those with Hg-reducing
bacteria and 463 for those with Hg accumulating bacteria. Highest and
most rapid accumulations were found in oyster gill tissue with accumu-
lations in ~g Hg/kg wet wt, of 647 in controls, 1747 in oysters with
mercury-reducing bacteria and 2850 in oysters with mercury-accumulating
bacteria.
1488.
Conte, F.P. and H.H. Wagner. 1965. Development of osmotic and
ionic regulation in juvenile steelhead trout Salmo gairdneri.
Compo Biochem. Physiol. 14:603-620.
Development of seawater adaption preceded seaward migration
and smolt transformation by several weeks. Regression of adaptation
occurred during terminal stages of migration period. Chronological
time is only important in that it determines how long it takes fish to
reach a critical size; in steelheads it is 14-15 cm. In non-adapting
individuals, Na and Cl do not represent the 85-90% total osmotic concen-
tration found for freshwater fish. This suggests that other types of
solutes constitute a vital role in seawater homeostasis and pathogenesis
of seawater death. Increased thyroid activity was found during the
period of migration but this did not appear to be causally related to
seawater adaption.
1489.
Conte, F.P" H.H. Wagner, J. Fessler, and C. Gnose. 1966.
Development of osmotic and ionic regulation in juvenile coho
salmon Oncorhynchus kisutch. Compo Biochem. Physiol. 18:1-15.
Development of seawater adaptation preceded seaward migration
and parr-smolt transformation by 6-7 months with no regression observed
following terminal stages of migration period. Seawater survival for
various salinities (20-300/00) was a function of size and not chrono-
logical age. Relative survival times were O. kisutch > Salmo gairdneri
> S. salar > S. clarki> S. trutta. Variabllity of osmotic and ionic
regulatory system was indIcated by deviation between blood concentra-
tions of freshwater fish (control) and fish exposed to seawater during
the premigratory, migratory, and post-migratory periods.
77
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1490.
Cook, A.M. and K.J. Steel. 1959. The antagonism of the anti-
bacterial action of mercury compounds. Part IV. Qualita-
tive aspects of the antagonism of the antibacterial action
of mercuric chloride. Jour. Pharm. Pharmacol. 11:162-168.
Molar amounts which bracket the no-effect, frank effect
responses for antagonism of one mole of mercuric chloride inhibition
of E. coli are listed. These values were 1.7 and 2.1 for cysteine,
0.7-an~1 for dimercaprol, 1.9 and 2.1 for glutathione, and 1.9 and
2.2 for thioglycollic acid. When used to revive HgC12-treated cells,
larger amounts were needed; horse serum was ineffective. Cells treated
with HgC12 in presence of a nutrient medium derived some protection from
media constituents.
1491.
Cornell, J.C. 1974. A reduction in water exchange rates in an
osmoconforming crab. Amer. Zool. 14:1259.
Data from Libinia emarginate, an osmoconformer, on weight
gain, urine production and osmotic concentration suggested that there
was a reduction in water exchange when animals were transferred to a
dilute medium. This hypothesis was tested by measuring water exchange
rate with 020. The rate constant in 100% SW was 8.49. After exposure
for one hour to 80% SW the value dropped to 5.96, indicating a 30%
reduction in water exchange. A possible mechanism for reduction in
water exchange was proposed when it was found that transferring animals
to a dilute medium caused a reduced heart rate. If reduced heart rate
causes reduced flow of blood in gills, this might account for reduced
water exchange. Flow rate in gills was not measured. However; when
isolated gills were perfused with a peristaltic pump, water exchange was
proportional to rate of perfusion. This suggests that changes in cir-
culation may be responsible for changes in water exchange rates.
1492.
Cossa, D. 1976. Sorption du cadmium par une population de la
diatomee Phaeodactylum tricornutum en culture. Marine
Biology 34:163-167. (English summary.)
Uptake of cadmium by the marine diatom P. tricornutum in
batch culture as a function of successive growth stages, and of chemical
form of cadmium in culture medium, was determined over a 12 day period.
Ionic and complexed Cd at 10 ug/l produced up to 16% growth inhibition
by the 12th day; chelated Cd had little effect on growth during this
period. Concentration of ionic Cd in medium influenced uptake by
diatoms: 8300 mg Cd/kg wet wt algae was observed at 1 mg Cd/I; how-
ever, when cadmium was chelated by ethylenediaminetetraacetate, uptake
was negligible. In absence of chelating agents, uptake varied with
growth phase of the culture, with major part of uptake by adsorption.
78
-------
Two opposite phenomena seem to be responsible for the processes ob-
served: adsorption of cadmium on the cell walls followed by a gradual
elution (desorption) by external metabolites. Author suggests that Zn
(from culture media) and Cd compete for adsorption sites.
1493.
Costa, M.R.M. and M.I.C. da-Fonseca. 1967- Teor do arsenico em
mariscos. Revista Portuguesa de Farmacia 17 (1) : 1-19. (In
Portuguese, English summary.)
Arsenic levels in mg/kg dry wt from edible parts
of molluscs ranged from 1.3 to 129.6, with a range of means
83.8. Edible parts of 9 species of crustacea contained 5.6
As/kg dry wt with a range of means of 8.6 to 96.2.
of 21 species
from 7.1 to
to 22 0 . 2 mg
1494.
Coulson, E.J., R.E. Remington and K.M. Lynch. 1935.
in the rat of the naturally occurring arsenic of
compared with arsenic trioxide. Jour. Nutrition
270.
Metabolism
shrimp as
10(3):255-
In an analysis of seafJod, shrimp contained the highest con-
centrations of As: 1.2 to 41.6 mg/kg wet, or 4.9 to 171.0 mg/kg dry.
A seasonal effect on As levels was seen in shrimp from one area, with
highest levels in Oct. and lowest levels in May and June. Using shrimp
as an organic As source, rats were fed a stock diet (0.2 mg As/kg), a
low As shrimp diet (1.2 mg As/kg), a high As shrimp diet (17.7 mg As/kg),
a stock diet with inorganic As203 (17.9 mg As/kg) and a low As shrimp
plus As203 diet (17.9 mg As/kg), for one year. During the first 3
months an equilibrium level of As was reached and maintained in rat
bodies, being 18% of ingested As203, compared with O. 7% if "shrimp As"
was ingested. Livers of rats contained ~3 mg As/kg wet when fed high
As shrimp, while rats fed inorganic As contained ~55 mg As/kg wet. No
rats showed evidence of toxicity in growth, physical appearance, acti-
vity, or in histological examination of liver, spleen and kidney. Rats
excreted nearly 100% of "shrimp As," but only 20% of inorganic As;
whereas humans excreted 114% of "shrimp As" and from 74 to 103% of
inorganic As. Results indicated that As held in a complex combination
in shrimp upon digestion in an animal organism, will not release As but
rather a soluble and readily diffusible product rapidly eliminated by
kidneys.
1495.
Courtois, L.A. and R.D. Meyerhoff. 1975. Effects of copper
exposure on water balance. Bull. Environ. Contamin. Taxicol.
14(2):221-224.
79
-------
Plasma volume of the freshwater striped bass Roccus saxati1is
was 2.50-2.86% of total body weight. After exposure to 1 mg/1 Cu (as
CUS04) for 6 to 15 minutes, an expansion of 0.95-0.97% was found and
suggests that copper affects the exterior border of gill membrane to
produce passive osmotic diffusion.
1496.
Cowen, J.P., V.F. Hodge and T.R. Folsom. 1976. In vivo accumu-
lation of radioactive polonium by the giant kelp:JMacrocystis
pyrifera. Marine Biology 37:239-248.
Rates of accumulation of Po-210 by young, growing lamina of
kelp from La Jolla beds were 0.78 x 10-9 pCi/cm2 sec (1.73 x 10-9 dpm/cm2
sec) and 1.17 x 10-9 pCi/cm2 sec (2.60 x 10-9dpm/cm2 sec) for observed
and growth-corrected data, respectively. Inert, foulable surfaces ex-
posed to kelp bed environment had Po-2l0 accumulation rates of 0.64 x
10-9 pCi/cm2 sec (1.42 x 10-9 dpm/cm2 sec).
1497.
Cowey, C.B., T.L. Coombs and J.W. Adron. 1976. The renal and
serum concentrations of calcium, magnesium and phosphorous
in captive and wild turbot (Scopthalmus maximus). Marine
Biology 38:111-115.
Concentrations of Ca, Mg and P in kidney, serum, and ultra-
filtrates of serum in wild flatfish were compared to those reared in
captivity and which exhibited a hepato-renal syndrome of renal tubule
calcification. No differences in renal Ca or Mg were found. Serum from
wild turbot contained significantly higher total and ultrafilterable Mg
than serum from turbot reared in captivity. No relationship, causal or
indirect, was suggested between hepato-renal syndrome and disturbance
of Ca/Mg metabolism.
1498.
Cowgill, U.M. 1976. The chemical composition of two species of
Daphnia, their algal food and their environment. Science
Total Environ. 6:79-102.
D. magna and D. pulex cultured in spring water and fed
Euglena gracilis supplemented occasionally with a mixed algal culture
contained 54 detectable elements, while the water had 53. Major dif-
ferences were noted between the two species of Daphnia, with D. magna
exhibiting greater accumulation in mg/kg dry wt of K (13,839)~ Na
(1,180), Ca (76,643), Sr (81.9), and D. pulex having a greater Co con-
tent (3.3). Daphnia and algae contained different amounts of Na, K,
Mg, Cu, Zn, AI, Sc, La, Nd, Sn, Ti, Fe, Mn, Ni, Zr, Cu, Ag, Be, Si, Pb,
and Hg. Other elements determined were Rb, Cs, Li, Cd, Ba, Ce, Pr; Sm,
Eu, Gd, Dy, Er, Yb, Ga, B, Hf, As, Bi, V, Nb, Se, Cr, Mo, and Co.
80
-------
Chemical composition of Daphnia is governed by mixed algal culture and
the spring water. Daphnia rejected E. gracilis which did not contribute
to their chemical composition. Composition of algal cultures is
apparently governed by that of the spring water.
1499.
Cowgill, U.M. and C.W. Burns. 1975. Differences in chemical
composition between two species of Daphnia and some fresh-
water algae cultured in the laboratory. Limnol. Oceanog.
20: 1005-1011.
Daphnia pulex and D. magna were cultured in spring water and
fed with a monoculture of Euglena gracilis and occasionally with a mixed
algae culture containing mainly Chlorophyceae. Fifty-three elements were
detected in the spring water and fifty-four in plankton. By comparing
the mean concentration (dry wt. basis) of the 2 species of Daphnia and
the 2 algae cultures, the following concentration factors of Daphnia
over algae were found: Ca (6.9), Na (4.5), Sc (2), Nd (2), La (2), Zr
(2), and Ni (2). Algae, on the other hand, accumulated greater concen-
trations of Mo (13.4), Fe (12.2), Mg (10.6), Sn (8.1), Ag (7.5), Ti (6.1),
Be (3.7), Cu (3.0), Zn (2.7), Mn (2.3), Al (1.7), As (1.6), Co (1.7),
K (1.5), Pb (1.3), Hg (1.4), Si (1.1), and contain about the same concen-
tration of Cd as Daphnia. Concentration of Ca was 2.1 times higher in
D. magna than in Q. pulex.
1500.
Cox, H.E. 1925. On certain new methods for the determination
of small quantities of arsenic, and its occurrence in urine
and in fish. Analyst 50:3-11.
Ranges in concentrations (mg/kg) of arsenic as As406 in edible
fish muscle were: whiting 0.1-0.4, hake 0.2-0.3, john dory 0.1, brill
0.1-0.3, halibut 0-0.3, turbot 0.2-1.8, perch 0.8, plaice 0.3-3.0, sole
0.1-0.3, herring 0.1-0.8, cod 0.1-2.0, haddock 0.1-0.6, and mackerel 0.1-
0.5. It was noted that certain Whitstable oysters contained up to 3.7
mg/kg As, and algae up to 0.7 mg/kg As. Fish, particularly plaice, are
believed to accumulate As from bivalves, algae, and other food organisms.
Arsenic is subsequently transferred to humans consuming fish, with
quantities of As excreted in urine within 24 hours.
1501.
Craig, S. 1967. Toxic ions in bivalves.
Assn. 66:l000-l00~.
Jour. Arner. Osteop.
Two species of edible molluscs Venus mercenaria and Spisula
sp. were analyzed for Pb, Cu, and Hg. Venus from Cape Henlopen on the
Delaware Bay contained concentrations (in mg/kg wet wt) of 1.0 Pb, 0.9
Cu, and 1.1 Hg, while Spisula had 7.3 Pb, 1.1 Cu, and 0.8 Hg. Specimens
81
-------
from Woods Hole of Venus contained 2.5 mg/kg Pb, 19.2 Cu, and 2.3 Hg,
while Spisula contained 1.1 Pb, 0.7 Cu, and 0.8 Hg.
1502.
Cugurra, F. and G. Maura. 1976. Mercury content in several
species of marine fish. Bull. Environ. Contamin. Toxicol.
15:568-573.
Mercury in canned tuna, anchovies, sardine and mackerel,
frozen umbina, dried and fresh cod fish and sardines and oculata from
Genoa, Italy was determined. Total mercury in mg/kg wet wt of canned
tuna was 0.64 for Parathunnus obesus, 0.27 for Neothunnus macropterus,
0.27 for Katsuwonas pelamis and 1.32 for Tunnus thynnus. Total mercury
in other species of fish were 0.41 for anchovy Engraulis encrasicholus,
0.21 for sardines Clupea sardina bought in Genoa, 0.16 for f. sardina
fished and packed in Spain, and 0.25 for mackerel Scomber scomber.
Total Hg for non-canned fish, was 0.48 for Clupea sardina, caught near
Genoa, Italy, 2.59 for Oblata melamura, caught near Genoa, 0.70 for
Umbrina cirrhosa and 0.326 for Gadus morrhua.
1503.
Culkin, F. and J.P. Riley. 1958. The occurrence of gallium in
marine organisms. Jour. Mar. BioI. Assn. U.K. 37:607-615.
Gallium, copper, aluminum and iron levels, in mg/kg dry wt,
were: 0.01 to 0.56 Ga, 5.6 to 86 Cu, 34 to 4420 AI, and 34 to 4680 Fe
for algae; 0.18 Ga, 111 Cu, 973 Al and 1148 Fe for Ramulina, a forami-
niferan; 0.93 Ga, 59.5 Cu, 3700 Al and 4040 Fe for Halichondria panicea,
a sponge; 0.05 Ga, 62 Cu, 435 Al and 438 Fe for Alcyonium digitatum, a
coelenterate; 0.03 to 0.36 Ga, 35 to 29 Cu, 166 to 1041 Al and 146 to
1045 Fe for crustacea; 0.008 to 0.036 Ga, 1.6 to 7.9 Cu, 32 to 174 Al
and 41 to 239 Fe for shells and 0.007 to 0.16 Ga, 37 to 102 Cu, 186 to
346 AI, and 86 to 1415 Fe for soft parts of molluscs; 0.02 to 0.35 Ga,
20 to 90 Cu, 159 to 1830 Al and 149 to 1700 Fe for echinoderms.
Viscera and digestive organs of molluscs, Pecten maximus, Buccinum
undatum, Chlamys opercularis and Porania pulvillus contained elevated
Ga levels, presumably from ingested inorganic material. Ga:Al ratio
varied from 1 to 7 x 10-4 (average 2 to 3 x 10-4), which compares well
with average Ga:Al ratio of lithosphere, and contrasts with ratio of
25 x 10-4 for seawater. Authors concluded that organisms examined
derived their Ga, Al and Fe from bottom muds rather than from seawater.
1504.
Cumbie, P.M. 1975.
freshwater fish.
14(2):193-196.
Mercury levels in Georgia otter, mink, and
Bull. Environ. Contamin. Toxicol.
Mercury levels are reported in aquatic mammals and fish from
82
-------
a region of the Georgia Lower Coastal Plain; this area is not associated
with recognized point sources of mercury contamination. Mercury concen-
trations detected in hair of otter Lutra canadensis ranged from 9.3
mg/kg to 67.9 mg/kg. An adult male otter with 35.3 mg/kg Hg in hair
had 1.97 mg/kg Hg in skeletal muscle. Mink Mustela vison hair mercury
levels ranged from 2.3 mg/kg to 17.3 mg/kg. Mean mercury levels in
mg/kg wet wt from axial muscle of various species of fish were: large-
mouth bass Micropterus salmoides 0.44, chain pickerel Esox niger 0.81,
bowfin Amia calva 0.45, gar Lepisosteus sp.0.42, chubsucker Erimyzon
oblongus 0.14, and red fin pickerel Esox americanus 0.39.
1505.
Cunningham, P.A. and M.R. Tripp. 1975. Factors affecting the
accumulation and removal of mercury from tissues of the
American oyster Crassostrea virginica. Marine Biology 31:
311-319. '
Adult oysters were held in seawater containing 10 or 100 ug/1
of mercury as mercuric acetate for 45 days. After 45 days, average mer-
cury tissue concentration was 91,600 and 12,100 ug/kg wet wt in the 100
and 10 ug/l groups, respectively. A slight decline in mercury residues
in the 100 ug/1 group during the accumulation period was attributed to
spawning. Clearance of mercury from tissues was studied in a constant
temperature regime (25 I 2 C) for 25 days and in a declining temperature
regime (25 to 5 C) for 80 days by exposing treated adults to estuarine
water with no mercury added. The biological half-life of mercuric
acetate was 16.8 and 9.3 days in the 25 C temperature regime, and 35.4
and 19.9 days in the declining tem~erature regime, for the 10 and 100
ug/l groups, respectively. Smaller oysters (up to 7 g) consistently
accumulated more mercury per gram wet wt than larger oysters (7 to 20 g)
in populations exposed to 10 and 100 ug/l mercury.
1506.
Cunningham, P.A. and M.R. Tripp. 1975. Accumulationi tissue
distribution and elimination of 203HgC12 and CH3 03HgC1
in the tissues of the American oyster Crassostrea virginica.
Marine Biology 31:321-334.
Oysters were exposed for 3 days to mercury-203 labeled HgC12
or CH3HgC1 added directly to artificial seawater or added preconcentrated
on marine diatoms Phaeodacty1um tricornutum. The concentration of mer-
cury in 5 tissues was measured for 45 days after mercury was removed from
the ambient water. At the beginning of depuration, highest concentra-
tions of mercury in tissues were attained in: gill> digestive system>
mantle> gonad> muscle in oysters exposed to water containing mercury;
and in digestive system> gill> mantle> gonad> muscle in oysters fed
labeled algae. This same distribution pattern is seen for both chemical
forms of mercury. Although initial pattern of accumulation was identical
83
-------
for both mercury compounds within each exposure group, the fate of
accumulated mercury was different after 45-days depuration. In oysters
accumulating mercury directly from seawater, inorganic mercury residues
rapidly declined in gill and digestive tissue, but were slowly reduced
in mantle, gonadal, and muscle tissue. This pattern was duplicated by
oysters exposed to methyl mercuric chloride in seawater except that
gonadal and muscle residues greatly increased during depuration. It
oysters ingesting labeled P. tricornutum cells, mercuric chloride and
methyl mercuric chloride residues rapidly declined in gill and diges-
tive tissue, remained constant in the mantle, but sharply increased in
gonadal and muscle tissue during depuration.
1507.
Cutshall, N. 1974. Turnover of zinc-65 in oysters.
Physics 26:327-331.
Health
Uptake and loss of Zn-65 by Pacific oysters Crassostrea
gigas are fitted by solutions to a first-order, linear differential
equation that describes "single-compartment" isotope substitution kinetics
Rate constants for loss are related to rate constants for uptake and to
steady-state concentration factors for stable Zn and Zn-65. Single-
compartment solutions adequately fit uptake and loss data from field
experiments extended as long as several hundred days; therefore, author
concludes that either individual organs of oysters have closely similar
turnover-rate constants for Zn, or at least that dominant organs in
whole-body Zn content turnover at similar rates. Rate constant esti-
mated from loss data is 5490 days and that from uptake data is 4930 days.
Apparent importance of multiple compartments can be affected in experi-
ments ~here uptake times are short.
1508.
Dabrowski, K.R. 1976. The effect of arsenic on embrional develop-
ment of rainbow trout (Salmo gairdneri, Rich.). Water Research
10:793-796.
Survival of trout eggs increased as As+5 concentration of
medium increased from 0.05 to 50.0 mg/l, but survival was not related
to As+3 level over this concentration range. Accumulation rates of As+3
and As+5 were related to ambient concentrations.
1509.
D'Agostino, A. and C. Finney. 1974. The effect of copper and
cadmium on the development of Tigriopus japonicus. In:
Vernberg, F.J. and W.B. Vernberg (eds.). Pollution and Physi-
ology of Marine Organisms. Academic Press, New York: 445-463.
Egg development in T. japonicus, an estuarine copepod, was
inhibited by exposure to 0.04 mg Cdz+/l or 0.064 mg Cu2+/l. Cadmium was
84
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acutely toxic to ovigerous females and nauplii at 4.4 mg/l in 72 hrs;
Cu at 6.4 mg/l in 48 hrs. Females did not become ovigerous when ex-
posed to 4.4 ug Cd2+/l and 4.6 ug Cu2+/1 simultaneously. Phenylmercuric
acetate, in concentrations of 5.96 to 0.00596 mg Hg2+/1 killed ovigerous
females in 4 to 72 hrs. Acute toxicity tests were conducted with resi-
dues from industrial mycelial fermentation operations. These contained
in mg/kg wet wt: Cd, 0.03; Cr, 2.6; Cu, 2.8; Mn, 9.7; Mg, 0.02; Ni,
<0.06; Fe, 160; and Zn, 360. At 100 mg residue/l females did not pro-
duce eggs; at 1000 mg/l death occurred within 6 days.
1510.
Dalton, J.C. 1958. Effects of external ions on membrane poten-
tials of a lobster giant axon. Jour. Gen. Physio1. 41(3):
529-542.
Decrease in external concentration of sodium caused a re-
versible reduction in amplitude of action potential of the lobster giant
axon and its rate of rise, but resting potential was not affected.
Changes were of same order of magnitude, but greater than would be pre-
dicted for an ideal Na electrode. Resting potential was inversely
related to external K concentration. Lowering external Ca below 1 g/l
caused a reduction in resting and action potentials, and occasional
occurrence of repetitive activity. Decrease in action potential was
not solely attributable to a decrease in resting potential. Increase
of external Ca from 1 to 2 g/l caused no change in transmembrane poten-
tials. Variations of external Mg concentration between 0 and 1.2 g/l
had no measurable effect on membrane potentials. Studies did not indi-
cate a clear choice between use of seawater and perfusion solution as
better external medium for studies on lobster nerve.
1511.
Dalton, J.C. 1959. Effects of external ions on membrane poten-
tials of a crayfish giant axon. Jour. Gen. Physiol. 42(5):
971-982.
Magnitude of action potential in crayfish giant axon was a
linear function of the log of external sodium concentraticn, as pre-
dicted for an ideal Na electrode. Resting potential was an inverse
function of external K concentration, but behaved as an ideal electrode
only at the higher external K concentrations. Decrease in external Ca
resulted in a decrease in both resting potential and action potential;
an increase in external Ca above normal had no effect on magnitude of
transmembrane potentials. Magnesium could partially substitute for Ca
in maintenance of normal action potential magnitude, but appeared to
have very little effect on resting potential. All ionic effects were
completely reversible.
85
-------
1512.
Danil'chenko, O.P. and N.S. Stroganov. 1975. Evaluation of
toxicity to the early ontogency of fishes of substances
discharged into a body of water. Jour. Ichthyology 15(2):
311-319.
Highest concentration tested of triethyl lead chloride (TELC)
not affecting development of various species of freshwater fish pro-
larvae was 0.1 mg/l. However, larval symptoms such as elongation of
heart chambers, pericardium dropsy, and absence or retardation of in-
flation of swim bladder, occurred at exposures above 0.01 mg TELC/l.
1513.
Davidson, D.E. 1974. The effect of salinity on a marine and a
freshwater ascomycete. Canad. Jour. Botany 52:553-563.
An isolate of Lulworthia medusa, a marine fungi, grew sig-
nificantly better in seawater than freshwater. Growth of Ophiobolus
graminis, a freshwater isolate, was reduced by 50% in seawater; growth
of both species was similar in natural and artificial seawater. Neither
species grew under anaerobic conditions. Respiration of the freshwater
species is reduced in seawater; percent reduction was about equal to
reduced growth in seawater, as compared to freshwater. Respirational
rates of L. medusa in sea and freshwater were similar. Yet growth in
seawater was much greater than in freshwater. Consequently, it was
proposed that respiratory energy produced in a freshwater environment
was used for cellular functions other than biomass increase. In con-
trast to the marine isolate, metabolic processes of O. graminis were
severely affected by seawater.
1514.
Davidson, D.E. 1974. Wood-inhabiting and marine fungi from a
saline lake in Wyoming. Trans. Brit. Mycol. Soc. 63(1):143-
149.
Forms known as marine fungi Monodictys pelagica, Nais
inornata are reported from the saline but non-marine environment of a
MgS04oNa2S04 lake in southeastern Wyoming. Occurrence of marine fungi
in saline lakes without a recent outlet to the sea is unusual.
1515.
Davies, A.G. 1974. The growth kinetics of Isochrysis galbana
in cultures containing sublethal concentrations of mercuric
chloride. Jour. Mar. BioI. Assn. U.K. 54:157-169.
The marine alga I. galbana concentrated intracellular mer-
cury at levels up to 1 g/l after exposure to 10.5 ug Hg/l for 5 days.
Specific cellular growth rate was linearly reduced by increasing intra-
cellular levels of Hg, with no growth at 2 g Hg/l. Loss by volatiliza-
86
-------
tion of reduced Hg from cultures allowed growth to resume, eventually
yielding control population levels. Intracellular Hg increased cell
volumes up to 2x at highest sublethal concentrations examined. Author
suggests that Hg combines with certain sulphur-containing compounds
which are essential for successful cell division.
1516.
Davies, A.G. 1976. An assessment of the basis of mercury
tolerance in Dunaliella tertiolecta. Jour. Mar. BioI. Assn.
U.K. 56:39-57-
Specific growth rate of a green flagellate was unaffected by
mercury concentrations up to 2.03 ~g at/I. At 10 ~g at/l it was reduced
by 84% but growth continued, giving a final level of cell material only
13% below that of a mercury-free control. At this concentration, growth
was largely uncoupled from division and giant cells were produced. This
might be due to effect of mercury upon production of methionine which is
implicated in process of cell division. Mercury tolerance was investi-
gated in terms of (1) mercury detoxication in the culture medium by com-
plex or compound formation between metal and metabolites produced by
cells (2) concentration of sulphydryl groups both within cells as
possible sequestration sites and in cell membrane where any molecular
disruption and permeability changes produced by the metal first occur
(3) absence of cellular potassium leakage and (4) resistance of cell mem-
brane to uptake of mercury ions. Results indicated that Hg tolerance
of D. tertiolecta is partly related to slower rate of Hg accumulation,
but-is largely due to detoxication of Hg within cell possibly by pre-
cipitation of a highly insoluble Hg compound.
1517.
Davies, P.H., J.P. Goettl, Jr., J.R.
1976. Acute and chronic toxicity
Salmo gairdneri, in hard and soft
10:199-206.
Sinley, and N.F. Smith.
of lead to rainbow trout
water. Water Research
Static bioassays conducted in hard water (353 mg/l as CaC03)
produced LC-50 (96 h) range of 1.32 to 1.47 mg dissolved Pb/l vs total
Pb LC-50's (96 h) of 542 to 471 mg/l. In flow-through bioassay in soft
water (28 mg/l as CaC03), LC-50 (96 h) of 1.17 mg/l expressed as either
dissolved or total Pb was obtained. Symptoms of chronic low-level ex-
posure included occurrence of black tails, lordoscoliosis, paralysis,
muscular atrophy and caudal fin erosion. Maximum acceptable toxicant
concentrations (MATC's), as determined by black tail occurrence, the
most sensitiv~ criterion used, were between 18.2 and 31.7 micrograms
dissolved Pb/l vs 120 to 360 ug total Pb/l in hardwater. In soft water,
where exposure to Pb was initiated at eyed egg stage of development, the
MATC was between 4.1 and 7.6 ug/l. With exposure to Pb beginning after
87
-------
hatching and swim-up of fry, the MATC was between
Authors conclude that fish were more sensitive to
eggs.
7.2 and 14.6 ug/l.
Pb when exposed as
1518.
Davis, J.J" R.W. Perkins, R.F- Palmer, W.C. Hanson and J.F.
Cline. 1958. Radioactive materials in aquatic and terres-
trial organisms exposed to reactor effluent water. In:
Proc. Second U.S. Int. Conf. Peaceful Uses Atomic Energy,
Vol. 18 Waste Treat. Environ. Aspects of Atomic Energy,
Geneva: 423-428.
Accumulation of radioisotopes by aquatic organisms downstream
from Hanford nuclear reactors on the Columbia River was measured. Green
algae, Stigeoclonium lubricum, contained higher levels and greater
diversity of Sc-46, Cr-5l, Mn-54, Mn-56, Fe-59, Co-60, Cu-64, Zn-65,
As-76, Zr-95, Nb-95, Ru-l03, Cs-137, Ba-140, La-140, Ce-14l, Np-239, and
Sr-90, than other organisms analyzed: sponge Spongilla lacustris;
.insect larvae Hydropsyche cockerelli; gastropod Stagnicola nuttaliana;
crayfish Astacus trowbridgii; minnow Richardsonius balteatus; several
other species of teleosts including sucker Catostomus macrocheilus,
sturgeon Acipenser transmontanus, squawfish Ptychocheilus oregonensis
and whitefish Prosopium williamsoni; and also Barrow goldeneye duck
Bucephala islandica.
1519.
Davis, K.B. and B.A. Simco. 1976. Salinity effects on plasma
electrolytes of channel catfish, Ictalurus punctatus. Jour.
Fish. Res. Bd. Canada 33:741-746.
Plasma sodium and chloride levels of catfish increased after
5-day exposure to 10 and 12 g/l NaCl. Exposure of fish to 4 and 8 g/l
for 5 days resulted in plasma electrolyte levels higher than those of
fish kept in aged tap water, but were not different from values usually
found in freshwater fish. These observed differences may have been due
to handling. Tests were performed during several months and no effect
due to season was observed. When fish in July (27 C) were exposed to
10 g/l NaCl, plasma electrolyte concentration increased for 48 hrs and
then stabilized. Exposure to the same concentration in March (9 C) pro-
duced a slow increase of plasma electrolytes throughout the 13 day study.
Injection of 100 ~g/kg cortisol had no effect on plasma electrolyte
increase during 48 hrs after transfer to 12 g/l NaCl.
1520.
DeClerck, R., J. Van de Velde, and W. Vyncke. 1973. On the
effects of dumped organic industrial waste deriving from the
production of proteolytic enzymes on density, distribution
and quality of fish and shrimps. Aquaculture 2:323-335.
88
-------
A one-year study was conducted in a dump area off the Belgian
coast in order to define effects of dumped industrial organic wastes
resulting from production of proteolytic enzymes. A total of 36 species
were examined, with primary emphasis on plaice Pleuronectes platessa,
dab Limanda limanda, sprat Sprattus sprattus, whiting Gadus mer1angus,
sole Solea solea, and shrimp Crangon crangon. The dumped waste con-
sisted of 61.7% water; dry matter was 38.3% diatomaceous earth and 56%
organic matter; ash contained l-5%-Ca, P, Al and S, 0.1-0.3% Fe and Mg,
0.03-0.1% B, and 0.01-0.03% Pb, Cu, Ti and Ga. This waste material
sinks rapidly to the bottom with a high rate of dispersion. Some
obstacle to fishing occurs during a few days after dumping due to waste
lumps present. Dumped material showed no negative effects on fish and
shrimp stocks. The behavior of shrimps in an aquarium system indicated
no adverse effects. The organic waste did not influence the quality
and shelf life of shrimps.
1521.
DeClerck, R., R. Vanderstappen and W. Vyncke. 1974. Mercury
content of fish and shrimps caught off the Belgian coast.
Ocean Manage. 2:117-126.
Total mercury was determined in 800 samples of plaice
Pleuronectes platessa, whiting Merlangus merlangus, cod Gadus morhua,
sprat Clupea sprattus and shrimp Crangon crangon caught off the Belgian
coast during a one-year period. Most of the values were less than 0.25
mg/kg wet wt with highest frequencies occurring between 0.10 and 0.25
mg/kg. Significant positive regressions between length of fish and
mercury content were found for male and female whiting and male cod,
but not other species. The Hg concentration in seawater off the Belgian
coast averages 0.15 ug/l which seems to be normal for surface waters.
Sediments contained about twice as much mercury as in more distant water
(0.27 vs 0.15 mg/kg). Therefore it was not unexpected that Hg concen-
trations in Belgian inshore fish appeared higher than from fish caught
in distant waters where reported Hg levels were almost exclusively be-
low 0.10 mg/kg.
All analyses on shrimps were made on whole crustaceans. How-
ever; a specific investigation on mercury distribution in body of shrimps
showed a distribution of 56% in flesh, 32% in cephalothorax, 12% in shell
and 0% in telson. Taking into account an average percentage of 30%
shrimp flesh, a mean content of 0.186 mg Hg/kg was present in edible
flesh. Neither season nor fishing ground had a significant influence
on the mercury content of shrimps.
1522.
DeJong, L.E.D.D. 1965. Tolerance of Chlorella vulgaris for
metallic and non-metallic ions. Anton. v. Leeuwenhoek
31:301-313.
89
-------
Preliminary experiments of 3-4 month duration were conducted
with the freshwater alga C. vulgaris and analytical reagent grades of
various metals salts. Highest concentrations tolerated in g atoms/I,
are shown below in tabular form; with minor exceptions the same con-
centration- range also produced growth inhibition.
Highest Concentration Tolerated Element
0.000001 to O.OOOOl-----------------Co, Ni
0.00001 to O.OOOl-------------------Cu, Cd, Hg, Tl, Sb, As
0.0001 to O.OOl---------------------Th, Sn
0.001 to
O.Ol-----------------------Be,
Sm,
Lu,
AI,
Ba, U, Sc, Y, La, Ce, Pr, Nd,
Eu, Gd, Tb, Dy, Ho, Er, Tm, Yb,
Ti, Zr, V, Nb, Cr, Mn, Fe, Zn,
In, Pb, Bi, Se, Te, B
0.01 to O.l-------------------------Li, Na, Cs, Mo, W
0.1 to 1.0--------------------------K, Rb, Mg, Ca, Sr
1523.
DeMarte, J.A. and R.T. Hartman. 1974. Studies on absorption of
P-32, Fe-59, and Ca-45 by water-mi1foi1 (Myriophyllum exa1-
bescens Fernald.). Ecology 55:188-194.
Autoradiographs and radioactivity measurements provided
direct evidence that P-32, Fe-59 and Ca-45 were absorbed by roots of
M. exa1bescens, an aquatic vascular plant, and translocated to shoot
tissues. Data from experimer.ts designed to compare effects of substrate
type (sand or muck) and presence or absence of light showed that Fe-59
was not absorbed and translocated to the shoot when rooted in sand and
maintained in light during uptake period. Positive results for Fe-59
uptake were obtained for all other treatments. Upward translocation of
Ca-45 occurred only when plants were rooted in sand and maintained in
light. Autoradiography showed that Fe-59 and Ca-45 were generally dis-
tributed throughout shoot tissues, with a noticeable accumulation of
each in stem.
1524.
DeSilva, S.S. and P.A.B. Perera. 1976. Studies on the young
grey mullet, Mugi1 cepha1us 1. Effects of salinity on food
intake, growth and food converstion. Aquaculture 7:327-338.
Effects of different levels of salinity (30, 20, 10, and
<10/00) on growth, food intake and food conversion efficiency of young
grey mullet were studied. Daily food intake was variable at all 4
salinities; intake was salinity-dependent when food was presented in
excess. There was no appreciable difference in rate of growth when
fed 8% of body weight or in excess; maximum growth efficiency occurs at
90
-------
20%0. Percentage conversion efficiency of fish fed
at 100/00 was highest; with a constant ration percent
ciency decreased with increasing salinity.
on an excess diet
conversion effi-
1525.
Dick, J. and L.I. Pugsley. 1950. The arsenic, lead, tin, copper,
and iron content of canned clams, oysters, crabs, lobsters,
and shrimps. Canad. Jour. Res. F. 28:199-201.
A survey of heavy metal content of canned shellfish and
crustaceans sold on the Canadian market has been made. With the excep-
tion of one sample of clams having 5 mg/kg of lead, one of lobster having
13 mg/kg of lead, and another of lobster containing 7 mg/kg of arsenic
(as As203) the values for the remaining 120 samples analyzed were not
significantly above limits established for heavy metal content of foods.
Mean values of arsenic trioxide for all samples ranged from 0.10 to 1.33
mg/kg (range of individual values 0.0 to 7.0); for lead, mean values
ranged from 0.33 to 0.83 mg/kg (individual values 0.0 to 13.0); for tin
the means extended from 0.92 to 28.33 mg/kg (smoked oY5ters ranged from
25 to 30 mg/kg); for copper; means ranged from 2.4-37.7 with all values
between 0.0 and 65 mg/kg; and finally mean iron values fell between 8.1
and 64.1 mg/kg (range of individual samples 0.0 in crabs to 110.0 for
clams).
1526.
Dimock, R.V., Jr., and K.H. Groves. 1975. Interaction of tempera-
ture and salinity on oxygen consumption of the estuarine crab
Panopeus herbstii. Marine Biology 33:301-308.
Crabs were acclimated to all combinations of 10 and 23 C and
5 and 300/00 S. Rate of oxygen consumption was measured at 10 and 25 C
in experimental salinities of 5, 15, 30 and 400/00. Following acclima-
tion to 23 C and 50/00 S, rate of oxygen consumption by females was sig-
nificantly lower than males. No other experimental treatments resulted
in significant rate differences between sexes. This suggests that warm-
acclimated females, i.e. during reproductive periods, are excluded from
areas of low salinit~Oxygen consumption increased on exposure to low
salinity and low temperature, as well as to high salinity and high tem-
perature. Unpredictable response patterns were elicited by specific
experimental manipulations of temperature and salinity. Thermal sensi-
tivity of oxygen uptake as reflected by Q10 was also influenced by
experimental conditions and further substantiated occurrence of
temperature-salinity interactions.
1527.
D'Itri, F.M. 1972. Mercury in the aquatic ecosystem. Tech. Rep.
No. 23, Inst. Water Res. Michigan State University, Lansing,
Mich.: 101 pp.
91
-------
Role of mercury in the aquatic environment is reviewed in-
cluding introduction through industry, consumer products, and energy
production. Abundance in marine, freshwater and terrestrial ores, rocks,
waters, soils and sediments is examined. Biological aspects of Hg'in-
c1ude biological methylation and other conversions, biological magnifi-
cations including pathways, mode of toxic action, and resultant impli-
cations to both freshwater and marine ecosystems. Taxa discussed in-
clude bacteria, fish, algae, mammals, birds, molluscs, crustacea, higher
plants, insects, bryazoa, and annelids.
1528.
Dobkin, S. and R.B. Manning. 1964. Osmoregulation in two species
of Pa1aemonetes (Crustacea: Decapoda) from Florida. Bull.
Mar. Sci. Gulf Caribb. 14:149-157.
The euryha1ine shrimp P. intermedius maintained a constant
osmotic concentration in salinities from 5 to 390/00. Blood of P.
pa1udosus, a freshwater shrimp, was hypertonic in salinities up to
300/00. Regulation appeared to break down at salinities >200/00.
1529.
Dodge, R.E. and J. Thomson. 1974.
growth records in contemporary
Atlantic and Caribbean. Earth
322.
The natural radiochemical and
hermatypic corals from the
Planetary Sci. Letters 23:313-
Skeletal banding was observed in vertical cross-sections of
Montastrea annu1aris from Jamaica and Dip10ria 1abrynthiformis from
Bermuda. This was confirmed to be annual by ingrowth of Th-228 towards
radioactive equilibrium with Ra-228 taken up from seawater. Dip10ria
has incorporated Pb-210 at a constant specific activity over the last
30 years.
1530.
Donaldson, E.M. and H.M. Dye. 1975. Corticosteroid concentra-
tions in sockeye salmon (Oncorhynchus nerka) exposed to low
concentrations of copper. Jour. Fish. Res. Bd. Canada 32:
533-539.
Yearling salmon were eXtosed for 1-24 h to 0.00635, 0.0635,
or 0.635 mg/1 of copper (10-7, 10- , or 10-5 M cupric sulphate, respec-
tively). Cortisol, cortisone, and "total" corticosteroid levels were
significantly higher than controls after exposure for one hour to 10-5
or 10-6 M copper. "Total" corticosteroid and cortisone concentrations
were significantly higher than control concentrations after 2 and 4 h
of exposure to 10-7 M copper; respectively. Fish exposed to 10-5 M
copper died between 8 and 24 h. These data reflect a rapid corti-
costeroid stress response to lethal and sublethal concentrations of
92
-------
copper. The technique may be of use for rapid evaluation of effluents
containing heavy metals, especially those containing a mixture of toxi-
cants.
1531.
Doolittle, R.F., C. Thomas and W. Stone, Jr. 1960.
pressure and aqueous~humor formation in dogfish.
132:36-37.
Osmotic
Science
Concentrations in mg/l of aqueous humor, and blood plasma,
of dogfish Mustelus canis were 27 and 31 for K, 7 and 7 for Mg, 621 and
623 for Na, and 12 and 18 for Ca. Aqueous humor had a lower osmotic
pressure than plasma by 25 milliosmoles.
1532.
Dorigan, J.L. and K.M. Wilbur. 1973.
inhibition in coccolithophorids.
Calcification and its
Jour. Phycol. 9:450-456.
The protein synthesis inhibitors cycloheximide and chloram-
phenicol, and transport inhibitors LaC13, oligomycin, and ethacrynic
acid reversibly inhibit Ca uptake, coccolith formation, and cell divi-
sion in the coccolithophorid Cricosphaera (Hymenomonas) carterae. With
some compounds recovery of calcification was retarded, and in the case
of oligomycin, incomplete. Glycerol at 0.5 M, partially reversed in-
hibitory effect of chloramphenicol on calcification but not on division.
Ouabain was without significant effect on Ca uptake but slowed division
in 3 of 5 experiments. Ruthenium red inhibited neither calcification
nor division. In absence of light, calcification did not occur.
1533.
Dorn, P. 1976. The feeding behavior of Mytilus edulis in the
presence of methylmercury acetate. Bull. Environ. Contamin.
Toxicol. 15:714-719.
Initial mean feeding rate (no Hg added) of mussels was 6,704
diatoms/mussel. At 0.4 mg/l methyl mercury, it was 659; at 0.8 mg/l
methyl mercury, 181; and at 2.4 mg/l, 53 diatoms/mussel. Author suggests
that decreased feeding may be result of neurological disruption in
ciliary activity.
1534.
Dove, G.R., O.W. Tiemier and C.W. Deyoe. 1976. Effects of three
diets on growth and mineral retention of channel catfish
fingerlings. Trans. Amer. Fish. Soc. 105:481-485.
Supplemental feeds containing different Ca and P compositions
significantly affected whole-fish and lipid-free bone levels of Ca, P
and Mg of fingerling catfish, Ictalurus punctatus. More dietary Ca and
93
-------
P than supplied in supplemental feeds may be required during season of
rapid growth.
1535.
Dowden, B.F. and H.J. Bennett. 1965. Toxicity of selected
chemicals to certain animals. Jour. Water Poll. Contr. Fed.
37(9):1308-1316.
LC-50 values during a 24 to 96 hour test period for 86
chemicals and combinations of chemicals, including Ca, Cr, Fe, Mg, and
Zn were determined using representative freshwater species of amphipods,
amphibians, fish, insects, planarians and snail (Lymnaea) eggs. Snail
eggs had LC-50's comparable to those of adults of other forms due to
protective egg case. LC-50 values for Ca ranged between 649 and 2573
mg/l at 96 h; for chromium compounds, values were 0.03 to 0.22 mg/l at
48 h; for iron, 15 mg/l at 96 h; for magnesium, 788 to 6250 mg/l at 96 h;
and for zinc, 1 mg/l at 24 h.
1536.
Doyle, M., S. Koepp and J. Klaunig. 1976. Acute toxicological
response of the crayfish (Orconectes limosus) to mercury.
Bull. Environ. Contamin.Toxicol. 16:422-424.
After exposure to HgC12 for 96 hrs, 93% survival was obtained
by crayfish in 0.18 mg Hg/l, with little behavioral differences from con-
trols. Survivors of the calculated LC-60 (0.74 mg/l Hg) were sluggish
in response to mechanical stimulation. After 96 hrs only 15% survived
1.3 mg Hg/l, 8% at 1.8 mg Hg/l, and no survivors at 3.7 mg Hg/l. In
general, decrease in percent survival was proportional to both time and
toxicant concentration, with greatest number of deaths occurring between
24 and 72 hrs.
1537.
Drifmeyer, J.E. 1974. Zn and Cu levels in the eastern oyster,
Crassostrea virginica, from the lower James River. Jour.
Wash. Acad. Sci. 64(4):292-294.
Shucked whole bodies of oysters contained up to 10,000 mg
Zn/kg and 584 mg Cu/kg, with average values of 3915 mg Zn/kg and 180 mg
Cu/kg. These levels are upper limits of values reported elsewhere and
are considerably higher than levels reported in a previous survey of
the same area. Data may indicate increased Zn contamination of lower
James River oysters between 1971 and 1973.
1538.
Duggan, W.P. 1975. Reactions of the bay scallop, Argope~ten
irradians, to gradual reductions in salinity. Chesapeake
Sci. 16(4):284-286.
94
-------
Scallops acclimated to salinity of 260/00 at 10 to 15 C or
20 to 25 C showed measurable changes with decreasing salinity. Tran-
sition from a state of full extension of tentacles, gaped shells and
occasional clapping of shells to full retraction of tentacles, closed
shells and no shell clapping occurred over salinity range of 23 to 150/00
1539.
Dunstan, W.M., H.L. Windom and G.L. McIntire. 1975. The role
of Spartina alterniflora in the flow of lead, cadmium and
copper through the salt-marsh ecosystem. In: Howell, F.G.,
J.B. Gentry and M.H. Smith (eds.). MineraY-Cycling in
Southeastern Ecosystems. U.S. Energy Res. Dev. Admin.:
250-256. Available as CONF-7405l3 from NTIS, U.S. Dept.
Comm., Springfield, VA 22161.
Mean metal levels of marsh grass Spartina from 6 southeastern
U.S. rivers, in mg/kg, were 0.6 for Cd, 4 for Cu, and 5 for Pb.
Spartina seedlings exposed to 100 mg/l levels of Cu and Pb showed growth
inhibition in both cases, complete mortality after 2 weeks in Cu treat-
ments, and 50% mortality after 8 weeks exposure to Pb. Exposure of
seedlings for 8 weeks to 100 mg Cd/l did not affect growth although
residues up to 94 mg Cd/kg were recorded. Authors conclude that this
plant plays only a minor role in cycling of Cd, Cu and Pb in estuaries.
1540.
Dunster, H.J., R.J. Garner, H. Howells and L.F.U. Wix. 1964.
Environmental monitoring associated with the discharge of
low activity radioactive waste from Windscale works to the
Irish Sea. Health Physics 10(5):353-362.
Plaice Pleuronectes platessa, a marine flatfish, collected
from the Windscale radioactive outfall region contained 0.77 to 4.2
pCi/g wet wt of Ru-l06 and 0.017 to 0.056 pCi/g wet wt of Sr-90. Corre-
sponding values for Porphyra umbilicalis, an edible seaweed, were 35 to
170 for Ru-l06 and 0.04 to 0.14 for Sr-90. Mean activity levels, in
pCi/g wet wt, of specific nuclides in bulked samples of edible seaweed
were 0.038 to 0.13 for Sr-89. 0.023 to 0.29 for Sr-90, 54 to 221 for
Ru-l06, 1.0 to 4.8 for Y plus rare earths, 1.6 to 6.4 for Ce-144, 0.76
to 1.5 for Zr-95, 1.4 to 3.4 for Nb-95 and 0.04 to 1.5 for Cs-137.
1541.
Edwards, R.R.C. 1967. Estimation of the respiratory rate of
young plaice (Pleuronectes platessa L.) in natural conditions
using zinc-65. Nature 216:1335-1337.
Rate of zinc-65 elimination is proposed as a means of study-
ing respiratory rate of marine animals in natural habitat. For 0 group
95
-------
(less than 1 yr old) plaice at 16 C, loss of 35% of Zn-65 occurred in
first 5 days after exposure after which elimination rate decreased;
Zn-65 level stabilized in 43 days. Under various temperatures and
feeding situations, Zn-65 levels measured from day 7 showed increased
elimination with increased respiration.
1542.
Eftekhari, M. 1975.
Golfe Persique.
250:9-10.
Teneur en mercure de quelques crevettes du
Science et Peche, Bull. Inst. Peches marit.
Whole commercial shrimp from the Persian Gulf contained
between 0.005 and 0.012 mg Hg per kg wet wt.
1543.
Eganhouse, R.P., Jr. 1975. The measurement of total and organic
mercury in marine sediments, organisms, and waters. So.
Calif. Coastal Water Res. Project TM 221, 1500 E. Imperial
Highway, El Segundo, Calif.: 25 pp.
Samples of Palos Verdes shelf sediment showed total Hg con-
centrations of 0.26 to 4.05 mg/kg dry wt; recovery of total, inorganic,
and organic Hg from spiked sediment, water, orchard leaves, and tuna
samples ranged from 77.2 to 106.4%. These methods appear useful for
the routine measurement of mercury in marine samples.
1544.
Ehrlich, H.L. 1976. Manganese as an energy source for bacteria.
In: Nriagu, J.O. (ed.). Environmental Biogeochemisty.
Vol. 2. Metals Transfer and Ecological Mass Balances. Ann
Arbor Sci. Publ., Ann Arbor, Mich.: 633-644.
A gram-negative, motile, oxidase-positive rod isolated from
ferromanganese nodules used Mn (II) oxidation to satisfy all or part of
its energy requirements for assimilation of organic carbon. In a study
of ATP-synthesis by a high-speed fraction of this culture, ratio of ATP
synthesized to Mn removed from solution by enzyme catalysts (ATP/Mn)
ranged from 0.032 to 0.101; the real efficiency may be up to lOx greater,
as Mn assay measured total Mn absorbed including Mn oxidized. Of all
Mn (II) concentrations tested, 0.004 M MnS04 had optimal effect on ATP
production. Results suggest that at least 1 mole of ATP may be synthe-
sized per mole Mn (II) oxidized, if synthesis were 100% efficient.
Inhibitor studies imply that as many as 2 moles of ATP could be formed
for each mole of MN (II) oxidized. Responses from inhibitor studies
suggest an electron transport system by this bacterial strain in oxi-
dizing Mn (II) including use of flavoproteins, cytochromes of band c
types and cytochrome oxidases.
96
-------
1545.
Eiben, R. 1976. Influence of wetting tension and ions upon
settlement and beginning of metamorphosis in bryozoan
larvae (Bowerbankia gracilis). Marine Biology 37:249-254.
(In German, English abstract.)
Contractions which initiate metamorphosis, and metamorphosis
itself, were induced in free swimming larvae of B. gracilis by appli-
cation of CsCl or KCl; MgC12 prevents onset of metamorphosis but not
adhesion.
1546.
Eisler, R. and G.W. Kissil. 1975. Toxicities of crude oils and
oil-dispersant mixtures to juvenile rabbitfish, Siganus
rivulatus. Trans. Amer. Fish. Soc. 104:571-578.
Juvenile rabbitfish are strongly euryhaline, and can withstand
without apparent deleterious effect abrupt transplantation from 200/00
seawater (after a residence time of 7 days) to 600/00 for at least 8 days,
and vice versa. Rabbitfish survival at a given petrochemical concentra-
tion was highest at intermediate salinities of 30-500/00 in the salinity
o
range tested of 20 to 60 /00.
1547.
Eisler, R. and M. Wapner.
on biological effects
(No. 568-1292). U.S.
600/3-75-008: 400 pp.
Springfield, VA 21161.
1975. Second annotated bibliography
of metals in aquatic environments.
Environ. Protect. Agen. Rept. EPA-
Avail. from Nat. Tech. Inform. Serv.,
A total of 725 references are listed on the toxicological,
physiological, and metabolic influence of stable and radiolabelled
chemical species of metal cations to marine, estuarine, and freshwater
fauna and flora. References were annotated and subsequently indexed by
metal, by taxa, and by author, in cumulative indices which encompassed
this volume and the initial volume in the series (Eisler, R. 1973.
Annotated bibliography on biological effects of metals in aquatic
environments [No. 1-567]. U.S. Envir. Proto Agen. Rept. R3-73-007:
287 pp.).
1548.
Elder, J.F-, K.E. Osborn and C.R. Goldman. 1976. Iron transport
in a Lake Tahoe tributary and its potential influence upon
phytoplankton growth. Water Research 10:783-787.
Iron concentrations of water from Ward Creek, a tributary of
Lake Tahoe, showed marked seasonal variability. Total Fe transport
during a one-year period in 1972-73 was approximately 6000 kg, or 0.2%
of total Fe content of Lake Tahoe. Most Fe in stream water of Lake
97
-------
Tahoe basin results
particulate forms.
mechanisms, this Fe
from erosion, producing a high predominance of
Because of possibility of various breakdown
is potentially stimulatory to lake algal growth.
1549.
Elderfield, H., L. Thornton and J.S. Webb. 1971. Heavy metals
and oyster culture in Wales. Marine Poll. Bull. 2:44-47.
Zinc, lead and copper in water and particulate matter
(>0.45 ~) were measured over a period of one year in the Conway Estuary,
North Wales to establish causality between levels and poor larval pro-
ductivity in a local oyster hatchery. Zinc and Pb of water and particu-
late matter were highest in February and lowest in June. Zinc content
in February was 264 mg/kg and 9.0 ~g/l for particulate matter and water,
respectively, and 64 mg/kg and 2.4 ~g/l in June. Lead content was 89
mg/kg and 2.9 ~g/l for particulate matter and water, respectively, in
February and 21 mg/kg and 0.8 ~g/l in June. Maximum Cu content in
particulate matter was 91 mg/kg in January and 2.8 ~g/l for water in
February. Minimum Cu content of particulate matter was 56 mg/kg in
March and 2.2 ~g/l for water which occurred in April. Preliminary ex-
periments have shown that Zn at concentrations of less than 100 ~g Zn/l,
had minimal effects; at 300 ~g/l larval growth rate was considerably
reduced and at 500 ~g/l larvae either died or failed to metamorphose.
1550.
Ellis, M.M.
(2):97.
1934.
Arsenic storage in game fish.
Copeia 1939
Two of seven gamefish collected from the Yellowstone River
contained measurable levels of arsenic (2.4-2.7 mg/kg wet wt) in their
musculature. Author suggests that trout and whitefish had stored arsenic
cumulatively from stone-fly nymphs taken as food, and not from the water.
During the past 10 years several sportsmen and others have reported
sudden violent illness suggestive of arsenic poisoning following meals
including game fish caught in this part of the Yellowstone.
1551.
Ellis, M.M., H.L. Motley, M.D. Ellis and R.O. Jones. 1937.
Selenium poisoning in fishes. Proc. Soc. Exp. BioI. Med.
36:519-522.
Exposure of goldfish to 2 mg Sell resulted in death in 18 to
46 days, preceded by equilibrium loss and lethargy. Death occurred in
4 to 10 days upon exposure to 5 mg Sell. Intraperitoneal injection of
a 0.5% solution of sodium selenite into catfish Ictalurus punctatus in
the amount of 3 mg Se/kg fish was fatal in <48 hr at 10 C. Increased
temperature increased Se toxicity. Symptoms of acute Se poisoning
included contraction of dermal chromatophores, loss of coordination and
98
-------
muscle spasms. Delayed symptoms produced by lower doses and occurring
after 7 days included protrusion of eyes, pendulous abdomen and degenera-
tion of liver about central veins. Blood contained less hemoglobin,
fewer red blood cells, and more white blood cells than controls.
1552.
Ellis, M.M., B.A. Westfall and M.D. Ellis. 1941. Arsenic in
freshwater fish. Indust. Engineer. Chern. 35:1331-1332.
Arsenic, as the trioxide, was determined in 15 species of
freshwater teleosts collected from inland waters of Florida, Georgia,
Alabama, and Texas. Maximum concentrations recorded on a wet wt basis
ranged from 0.5 to 2.7 mg/kg. On a dry wt basis this was 1.7 to 14.2
mg/kg. The maximum values recorded for fish oil ranged from 2.8 to
160.7 mg/kg. Values for oil were similar to those reported for marine
macrofauna. Arsenic analyses of freshwater crustaceans ranged from 3.2
to 5.4 mg/kg on a dry wt basis and from 4.6 to 25.4 mg/kg in oil.
Author suggests there is ample arsenic in these crustacea which are
regularly eaten by freshwater fishes to supply the arsenic found in
fish oils.
1553.
Elroi, D. and B. Komarovsky. 1961. On the possible use of the
fouling ascidian Ciona intestinalis as a source of vanadium,
cellulose and other products. Proc. gen. Fish. Coun. Medit.
6:261-267.
Tunicates, growing on rafts in Haifa and Kishon harbors,
Israel, contained between 0.04 and 0.7% vanadium on an ash weight basis.
Figures obtained confirm published data as to high content of V in
ascidians in general and in Ciona intestinalis in particular.
1554.
Elson, P.F. 1974. Impact of recent economic growth and indus-
trial development on the ecology of Northwest Miramichi
Atlantic salmon (Salmo salar). Jour. Fish. Res. Bd. Canada
31:521-544.
The history of salmon runs of the Miramichi from 1950 to
1973 is reviewed. Decreases are related to degrading of ecological
conditions in the river's rearing reaches due to adverse chemical con-
ditions attributable to recent developments in forest management and
mining of Cu and Zn. Diversion of indigenous adult stocks into other
streams, and loss of rearing ground because of home stream pollution
by mining, pulp mill, and other human activities are examined. Increase
of commercial catches as a result of pollution-caused delay in the
estuary of migrating adults is analyzed. Grave depletion of stocks due
99
-------
to combined effects of these factors plus distant-water fishing is
identified, as is incipient recovery of stocks when home-water commer-
cial fishing was eliminated and pollution abatement measures intro-
duced. A suppressing effect of heavy angling pressure on stock abund-
ance when stocks are low is noted.
1555.
Elson, P.F., A.L. Meister, J.W. Saunders, R.L. Saunders, J.B.
Sprague and V. Zitko. 1973. Impact of chemical pollution
on Atlantic salmon in North America. Int. Atlantic Salmon
Symp., St. Andrews, New Brunswick 6:83-110.
Effects of pesticides, industrial and agricultural chemical
wastes including polychlorinated biphenyls, pentachlorophenol, oils,
agricultural runoff, industrial and municipal effluents and heavy metals
on Atlantic salmon populations are listed.
In a study of the Northwest Miramichi River, lethal thresh-
olds of 48 ~g Cull (=1 toxic unit) or 600 ~g Zn/l (=1 toxic unit) were
found for salmon parr. In combination, deleterious effects of the two
metals was additive. In the laboratory, parr avoided Cu-Zn solutions
of 0.02 toxic unit concentrations. In field studies 0.35 to 0.43 toxic
unit was required before avoidance and fall back of upward-moving salmon
occurred. At 0.8 toxic unit, upstream migration was completely blocked.
Death, due to extensive lesions associated with epidemic bacterial in-
fection, was ascribed to a previous heavy surge of Cu-Zn pollution.
Alteration of previous migration patterns was also noted. New Brunswick
surface waters contain significant amounts of humic materials, which
decrease the acute toxicity of Cu but not Zn ions. Mercury levels in
both juvenile and adult salmon are ~O.l mg/kg, present as methyl-Hg.
1556.
Elvehjem, C.A. 1935. The biological significance of copper and
its relation to iron metabolism. Physiol. Rev. 15:471-507.
Concentrations of copper in marine molluscs, in combination
with blood hemocyanin, were, in mg/l: Octopus vulgaris 180 to 235;
Sepia officinalis 237; and Helix pomatia (gastropod) 65 to 125. For
crustaceans these were: Astacus fluviatilis 70; Palinurus vulgaris 95;
Homarus vulgaris 100; Cancer pagurus 60; Carcinus maenas 90; Maia
squinado 35; and Squilla mantis 61. Copper was present in all fish
studied, except pigfish, at an average of 2.5 mg/kg; clams had little
or none; oysters 24 to 60 mg/kg; shrimps and crabs varied between 2.5
and 24, primarily in exoskeleton; jellyfish (Aurelia) and Portuguese
man-of-war (Physalia) were about equal in copper content to fish, on a
wet basis. Whale tissue and sea lion blood had no detectable copper,
but muscle, liver, spleen, and bile of sea lion contained trace amounts.
The respiratory capacity of blood and oxygen:Cu ratios are discussed;
roo
-------
presence of Zn in bJood of Busycon canaliculatum and B. carica (gastro-
pods) and vanadium in blood of Ascidians is noted.
Copper is also discussed as an element in the avian pigment
turacin, as an iron supplement in hemoglobin formation, as a nutritional
supplement and as a requirement for growth of higher plants, yeasts, and
some microorganisms. The toxic effect of Cu is mentioned briefly: rats
receiving 527 mg/kg Cu from "green oysters" or CUS04 (7 x human consump-
tion rate, at one serving/day) were unaffected.
1557.
Elwood, J.W. and L.D. Eyman. 1976. Test of a model for predict-
ing the body burden of trace contaminants in aquatic con-
sumers. Jour. Fish. Res. Bd. Canada 33:1162-1166.
Model parameters were determined in a single-feeding experi-
ment using bluegill, Lepomis macrochirus, and food 'labeled with Cs-137.
Independent of this single-feeding experiment, bluegill were allowed to
ingest Cs-137 contaminated food over a l6-day period; afterwards the
predicted and measured body burden of radionuclide were compared. Model
realistically simulated absorption of Cs-137 from gastrointestinal tract
and its accumulation over l6-day period. Average body burden of Cs-137
in fish was within 25% of predicted body burden when experiment was
terminated. Apparent equilibrium of Cs-137 in bluegill by day 16 sug-
gests that this two-compartment linear model does not apply to long-
term accumulation of cesium in fish. The model appears most applicable
for predicting body burdens of trace contaminants under acute exposure
conditions that simulate an accidental release.
1558.
Elwood, J.W., S.G. Hildebrand and J.J. Beauchamp. 1976.
bution of gut contents to the concentration and body
of elements in Tipula spp. from a spring-fed stream.
Fish. Res. Bd. Canada 33:1930-1938.
Contri
burden
Jour.
Larvae of Tipula spp., a detritus-feeding aquatic insect,
collected from an unpolluted stream were analyzed for Na, K, Rb, Cs, Ca,
Ba, Zr, Th, V, Ta, Cr, Mn, Fe, Co, Zn, Hg, AI, Se, Sc, La, Ce, Nd, Eu,
and other elements before and after gut evacuation to determine contri-
bution of gut contents to whole-body concentrations. Chromium and Al
concentrations were inversely related to body size, suggesting surface
contamination. All elements analyzed except Na, Cr, Hg, Zn, and Se
were significantly lower in concentration after gut evacuation (18%
decrease for K to approximately 70% for V, Mn, Hf, and some of the rare
earths). Ratios of variances of mean concentrations in organisms with
guts filled to those with guts evacuated indicate that gut contamination
is a major source of variation in measured whole-body concentrations of
many elements. Calculated percentage of element body burden associated
101
-------
with gut contents ranged from <1% for Na to 89% for Zr, with a mean for
all elements analyzed of 57 ! 8%. Calculated trophic transfer factors
(TTF = element concentration in larvae with guts evacuated/concentration
in leaf detritus) for elements which are obtained primarily through the
food' chain were significantly >1 only for Zn; TTFs for all other elements
were <1.
1559.
Engel, D.W. and J.W. Angeiovic. 1968. The
and temperature upon the respiration of
Compo Biochem. Physiol. 26:749-752.
influence of salinity
brine shrimp nauplii.
Respiration rates of day old nauplii of Artemia salina de-
creased with increasing salinity at all five temperatures tested (10,
15, 20, 25, and 30 C). The change in QIO value (respiration rate) per
unit change in temperature decreased with increasing salinity (0.89 at
50/00, 0.76 at 500/00, 0.77 at 100%0, 0.54 at 150%0, and 0.43 at
200%0). Q10 values were significantly affected by temperature at the
0.01 probability level; however. salinity and temperature-salinity inter-
actions were not statistically significant at the .05 level and lower.
1560.
Epstein, F.M., A.I. Katz and G.E. Pickford. 1967. Sodium- and
potassium-activated adenosine triphosphatase of gills: role
in adaptation of teleosts to salt water. Science 156:1245-
1247.
Activity of Na+ and K+-activated ATPases was higher in gill
and pseudobranch of killifish, Fundulus heteroclitus, adapted to salinity
of 260/00 than those adapted to freshwater. Hypophysectomy reduced
AT~ase activity in gills. Authors suggest that this enzyme is involved in
Na excretion by gills and that adaptive increase which occurs in sea-
water is influenced by hypophysis.
Establier, R. 1975. Concentracion de mercurio en los cabellos
de la poblacion de Cadiz y pescadores de altura. Investi-
gacion Pesquera 39(2):509-516. (In Spanish, English summary.)
. Hair of Cadiz city inhabitants contained 0.7 to 8.0 mg Hg/kg,
w~th a mean of 4.0 mg Hg/kg. Fishermen had 10.3 to 45.4 mg Hg/kg hair,
wIth a mean of 19.8 mg Hg/kg. Hg content of an infant's hair fell from
17.5.to 3.5 mg.Hg/kg ~n 2 years after removal of sword fish Xiphias
gl~dIU: from dIet. FIshermen showed no definite symptoms of methyl-Hg
pOIsonIng.
1561.
102
-------
1562.
Establier, R. 1975. Contenido en mercurio de las anguilas
(Anguilla anguilla) de la desembocadura del rio Guadaliquivir
y esteros de las salinas de la zona de Cadiz. Investigacion
Pesquera 39(1):249-255. (In Spanish, English summary,)
Eels from the Guadalquivir River estuary and environs con-
tained between 0.19 and 0.27 mg total Hg/kg wet wt. Mullet, Mugil
cephalus and~. aurata, contained <0.12 mg Hg/kg wet wt. Sedimentary
Hg levels from intertidal areas of Cadiz Bay ranged between 0.12 and
0.18 mg/kg.
1563.
Etges, F.J. 1963. Effects of some molluscicidal chemicals on
chemokinesis in Australorbis glabratus. Arner. Jour. Trop.
Med. Hyg. 12:701-704.
Snails, A. glabratus, were repelled by sublethal concentra-
tions of 0.01 and 0~256 ~g/l of CUS04 and ZnC12' respectively. ZnO,
BaC03, BaC12, Co(N03)2 and SnC12 at levels of 80 mg/l, did not repel
snails. LC-50 (140 hr) level for ZnO was 100 mg/l; egg production was
inhibited by 10 mg ZnO/l.
1564.
Eustace, I.J. 1974. Zinc, cadmium, copper
species of finfish and shellfish caught
Estuary, Tasmania. Austral. Jour. Mar.
209-220.
and manganese in
in the Derwent
Freshwat. Res. 25:
In the 7 species of elasmobranchs studied, highest concentra-
tions (and range of median values) of Zn, Cd, Cu, and Mn, in mg/kg wet
wt, were: 9.6 (4.6 to 5.0), 0.3 «0.05), 4.3 «0.25 to 0.7), and 1.6
«0.5), respectively. The one species of Holocephalan examined
(Callorynchus millii) contained up to 6.7 Zn (median 5.0), <0.05 Cd,
3.6 Cu (median 0.4), and 0.6 Mn (median <0.5). Twenty-three species of
finfish were analyzed and highest concentration found were: 146.7 Zn
(median 5.0 to 13.5), 0.3 Cd (median <0.05 to 0.06), 14.4 Cu (median
0.5 to 2.1), and 15.0 Mn (median <0.5 to 1.3). Eight species of in-
vertebrates were analyzed; levels of Zn, Cd, Cu, and Mn (in rng/kg)
found in each, respectively, were: Ostrea angasi (oyster) 5,657.0,
10.7, 57.9, 2.5; Mytilus edulis (mussel) 45.8, 5.5, 3.1, 2.5;
Notodarius gouldi (squid) 18.5, <0.05, 5.3, <0.5; Octopus sp. 18.5,
<0.05, 7.0, 0.6; Clibanarius strigimanus (hermit crab) 74.3, <0.05,
15.8,0.8; Patiriella regularis (mud starfish) 245.0,0.7, 31.4, 51.7;
Coscinasterias calamaria (red starfish) 40.6, 0.6, 10.4, 6.9; and
Ascidiacea sp. (tunicate) 64.0, 0.2, 8.3, 112.6.
Differences in levels of Zn and Cu in fish muscles are
attributed to different feeding habits. No abnormal levels of heavy
103
-------
metals were found in fish. With minor exceptions no relationships exist
between tissue metal content and length of fish. Molluscs', particularly
the edible species of oysters and mussels, accumulated much higher
levels of metals than fish, Zn and Cd exceeding levels specified by food
regulations (40 mg/kg Zn, 5.5 mg/kg Cd, 30 mg/kg Cu) in both species.
Since elevated metal concentrations in seawater are not reflected in
muscle tissues of finfish, the monitoring of commercial fish species
caught in the River Derwent provides a much less sensitive index of
pollution than would monitoring of oysters or mussels.
1565.
Evans, D.H., C.H. Mallery and L.
sion by a fish acclimated to
biochemical description of a
Exp. BioI. 58:627-636.
Kravitz. 1973. Sodium extru-
sea water: physiological and
N&-for-K exchange system. Jour.
+ .
Na extruslon by Dormitator maculatus acclimated to seawater
is coupled with K uptake and mediated by enzyme Na-K-activated ATPase.
1566.
Evans, D.H., J.C. Carrier and M.B. Bogan. 1974. The effect of
external potassium ions on the electrical potential measured
across the gills of the teleost, Dormitator maculatus. Jour.
Exp. BioI. 61:277-283.
Transfer of fish to various KCl solutions is correlated with
changes in trans gill potential (TGP), which are insufficient to account
for known K stimulation of Na efflux. Transfer to K-free seawater re-
sults in negligible change in TGP while previous results have shown that
such a transfer is correlated with a 22% reduction of Na efflux. Trans-
fer to fresh water results in a reduction of TGP and this is sufficient
to account for instantaneous reduction in Na efflux. While changes in
TGP can account for the "Na-free effect," they cannot account for K
effects on Na extrusion. Authors suggest that Na efflux and K influx
are chemically linked.
1567.
Evans, D.H., K. Cooper and M.B. Bogan. 1976. Sodium extrusion
by the seawater-acclimated fiddler crab Uca pugilator: com-
parison with other marine crustacea and marine teleost fish.
Jour. Exp. BioI. 64:203-219.
Total body and haemolymph Na contents of Uca in seawater were
5.0 and 10.4 g/kg. Blood Na concentration and transepithelial electri-
cal potential (T. E. P.) across !:!.. pugilator acc"1imated to seawater indi-
cate that Na is maintained out of electrochemical equilibrium with sea-
water. Resulting net Na influx as well as Na gain due to ingestion of
the medium must be balanced by extrarenal Na extrusion. The small T.E.P.
104
-------
and "transport numbers" of Na and C 1 indicated that permeabi Ii ty to
these ions is equivalent. Removal of external K results in a signifi-
cant stimulation of unidirectional Na efflux that is dependent upon
external Na but is not inhibited by ouabain.
Transfer of Uca to K and Na-free seawater results in a 54%
decline in unidirectionar-efflux, which is not due to T.E.P. changes.
Readdition of 975 mg K/l stimulates Na efflux much more than can be
accounted for by changes in the T.E.P. Readdition of 575 mg Na/l to
K-free seawater does not change Na efflux. Results indicate that Na
extrusion by Uca is via a Na/K exchange mechanism which partially in-
hibits Na/Na exchange. Cessation of Na/K exchange (in K-free seawater)
removes this inhibition and allows rapid Na/Na exchange. It is not
known whether Na/K and Na/Na exchange are via the same or parallel
carrier systems.
Fagerstrom, T., R. Kurten, and B. Asell. 1975. Statistical
parameters as criteria in model evaluation: kinetics of
mercury accumulation in pike Esox lucius. Gikos 26:109-116.
Some processes involved in mercury accumulation by individual
fish were studied using computer simulations. In general, temporal
variations of processes at the individual level are reflected in popu-
lation statistical parameters. Hg uptake rate per unit weight probably
covaries with body weight. This conclusion is derived from a qualitative
analysis approach where correlation, within age classes, between body
weight and Hg concentration proves useful. This correlation may be more
informative than the correlation calculated without accounting for age.
1568.
1569.
Fange, R., U. Lidman, and A. Larsson. 1976. Comparative studies
of inorganic substances in the blood of fishes from the
Scagerac Sea. Jour. Fish BioI. 8:441-448.
Main plasma inorganic electrolyte concentrations were deter-
mined for several orders of marine fishes. Mean concentrations were
462 mM for the cyclostome, Myxine glutinosa, 317 mM for the holo-
cephal an, Chimaera monstrosa, from 234 t~ 282 mM for elasmobranchs and
from 162 to 198 mM for teleosts. Mean K concentrations were 9.0 mM
for M. glutinosa, 7.9 ~ for C. monstrosa, from 3.9 to 5.4 mM for
elasmobranchs, and from 3.9 to 8.0 mM for teleosts. Mean Ca2+ concen-
trations were 6.3 mM for M. glutinosa, 4.3 mM for C. monstrosa, from
3.4 to 4.5 mM for elasmobranchs, and from 1.8 to 4~5 mM for teleosts.
Mean Mg2+ concentrations were 10.1 mM for M. glutinosa, 3.8 mM for C.
monstrosa, from 1.3 to 2.2 mM for elasmobranchs, and from 0.7 to 5.3
mM for teleosts.
105
-------
Federighi, H. 1931. Salinity death-points of the oyster drill
snail, Urosalpinx cinerea Say. Ecology 12:346-353.
Oyster drills collected from areas in Hampton Roads, Virginia,
where the summer salinity was 15 and 200/00, had salinity death-points
of 12.5 and 11.70/00. Snails collected at Beaufort, North Carolina,
where environmental salinity is >300/00, showed lethal salinities of
15.6 and 17.60/00. Author concludes that environmental salinity in-
fluences death point salinity, although the relation is not directly
proportional, since, as the animal becomes adapted to lower salinities,
the salinity factor of safety (difference between average environmental
salinity and death point salinity) becomes smaller.
1570.
1571.
Filip, D.S. and R.I. Lynn. 1972. Mercury accumulation by the
freshwater alga, Selenastrum capricornutum. Chemosphere 6:
251-254.
Using test concentrations of 0.1 mg Hg/l, Hg uptake by live
algal cells either in light or dark, was not significantly higher than
uptake by killed cells. Therefore, the mechanism of Hg uptake appears
to be solely of a passive absorptive nature. Since both living and dead
cells rapidly absorb dissolved inorganic mercury, even at very low con-
centrations, this algae should be considered as a possible point of entry
of Hg into the aquatic food web at the lowest trophic level.
1572.
Finesinger, J.E. 1926. Effect of certain chemical and physical
agents on fecundity and length of life and on their inheritance
in a rotifer, Lecane (Distyla) inermis (Bryce). Jour. Exp.
Zool. 44:63-96.
In pure springwater, parthenogenetic rotifers increased egg
production when 0.63 to 2.5 mg FeS04/1 was added. Addition of 4.5 and
0.45 mg FeC13/1 decreased egg production over a 12 week period; life-
span was not affected by Fe additions. No adverse effects were evident
after exposure to 0.45 mg FeC13/1 treatment in first generation after
return to normal. However, effects of 4.5 mg FeC13/1 treatment were
retained for two generations.
1573.
Fingal, W. and H.W. Kaplan. 1963. Susceptibility of Xenopus
laevis to copper sulfate. Copeia (1963)1:155-156.
Female toads X. laevis were placed in semidarkness at 22 C in
dechlorinated tap water-and varying concentration of copper sulphate
solution. In 30-day experiments, no mortalities occurred in concentra-
tions up to 0.1 mg/l of Cu2+. In 0.15 mg Cu2+/l, mortalities first
occurred on day 6 with total mortality by day 15. In 0.25 and 0.5 mg
106
-------
CU2+/l deaths occurred on the first day, with all dead by day 9. At 2.5
and 10.0 mg Cu2+/l, all toads died on the first day. For all toxic Cu2+
concentrations, output of mucous increased markedly over whole body sur-
face; eyes appeared especially irritated. In low concentrations, heart
rate first increased then decreased; in toxic concentrations, rate pro-
gressively dropped to subnormal levels, and in some cases became arhythmic
Neuromuscular coordination was disturbed, general activity decreased, and
postural reflexes disappeared in terminal days; skin peeled off in
immersed body areas.
1574.
Finkle, B.J. and D. Appleman. 1953.
centration on growth of Chlorella.
The effect of magnesium con-
Plant Physiol. 28:664-673.
In 49 mg Mg/l, cell populations of algae C. vulgaris increased
and synthesis of cell material proceeded rapidly without Mg limitation.
Cells decreased greatly in size during rapid growth and remained small.
Symptoms of Mg deficiency appeared in cultures initially containing
<1.0 mg Mg/l, while only some of these deficiency effects were apparent
in cultures with 2.8 mg Mg/l. Mg deficiency interrupted multiplication
at cell population sizes proportional to original Mg concentrations.
Cell material synthesis was not arrested; cell size increased greatly,
some cultures deficient in Mg produced cells that were more than 20X
larger than controls. Increases in cell size were paralleled by pro-
portional increases in nitrogen content and dry weight. It was concluded
that multiplication requires a larger concentration of Mg than does pro-
duction of cell material. Anatomical observations suggest that cell
division was taking place in Mg deficient cultures but this was not
apparent owing to lack of cell separation.
1575.
Finley, M.T., M.P. Dieter and L.N. Locke. 1976. Lead in tissues
of mallard ducks dosed with two types of lead shot. Bull.
Environ. Contamin. Toxicol. 16:261-269.
Mallards Anas platyrhynchos pen-reared for 6 months were
sacrificed one month after ingesting one number 4 all-lead shot or one
number 4 lead-iron shot containing 47.5% lead. Necropsy of sacrificed
ducks showed no tissue lesions usually associated with lead poisoning
in waterfowl. Lead levels in ducks given all-lead shot averaged about
twice those in ducks given lead-iron shot, reflecting amount of lead in
the two types of shot. Lead in blood of ducks dosed with all-lead shot
averaged 0.64 mg/l; and for ducks given lead-iron shot this was 0.28
mg/l. Lead residues in livers and kidneys of females given all-lead shot
were significantly higher than males. In both dosed groups, lead levels
in wingbones of females were 10 times those in males, and were signifi-
cantly correlated with number of eggs laid after dosage. Lead levels in
contents and shells of eggs laid by hens dosed with all-lead shot were
107
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twice those in eggs laid by hens dosed with lead-iron shot. Eggshells
best reflected levels of lead in blood. Authors conclude that mallards
maintained on a balanced diet and dosed with one lead shot may not
accumulate extremely high lead levels in liver and kidney. But extremely
high lead deposition may result in bone of laying hens after ingesting
sublethal amounts of lead shot as a result of mobilization of calcium
from bone during eggshell formation.
1576.
FleTning, W.R., J. Nichols and W.T.W. Potts. 1974. The effect of
low-calcium seawater and actinomycin-D on the sodium metabo-
lism of Fundulus kansae. JOUT. Exp. BioI. 60:267-273.
Transfer of F. kansae from 80% sea water to a low-calcium
water containing 16 mg-Ca++/2 resulted in a sharp rise of sodium efflux
producing a transient drop in whole-body Na levels within 1 to 2 days.
Both Na and K levels were normal after 9 days exposure to low-Ca media.
Exposure to low-Ca water significantly increased rates of radio-
phosphorus incorporation into gill RNA. Actinomycin-D blocked stimula-
tion of Na turnover after transfer into low-Ca sea water, but did not
affect whole-body Na or K levels of long-term sea-water adapted animals.
Actinomycin-D reduced Na efflux of short-term sea-water adapted animals
regardless of environmental Ca concentration, and upset the balance of
Na fluxes in those animals held in low-Ca sea water. Authors suggest
that in addition to effect of Ca on permeability to monovalent ions and
water, Ca inhibits synthetic processes regulating Na metabolism and
stabilizes metabolic processes already present.
1577.
Fletcher, G.L., E.G. Watts, and M.J. King. 1975. Copper, zinc,
and total protein levels in the plasma of sockeye salmon
(Oncorhynchus nerka) during their spawning migration. Jour.
Fish. Res. Bd. Canada 31:78-82.
Copper concentrations in blood plasma decreased from about 1.4
to about 0.5 mg/l for salmon migrating to the Chilko spawning ground,
British Columbia, in 1971. Loss occurred primarily during spawning.
Zinc content dropped from about 0.23 to 0.05 mg/l, mostly during the
transition from seawater to freshwater. Copper:plasma protein ratios
remained constant, but zinc:protein ratios decreased, indicating inde-
pendent removal mechanisms.
1578.
Floch, H., R. Deschiens and Y. Le Corroller.
molluscicide elective de l'oxyde cuivreux
du chlorure cuivreux. Bull. Soc. Pathol.
138.
1964. Sur l'action
du cuivre metal et
Exotique 57(1):124-
108
-------
Lethality of various copper salts was determined using gastro-
pod vectors of bilharziosis (Australorbis glabratus, Bulinus contortus
and Lymnea stagnalis) and non-target organisms including teleosts,
crustaceans, aquatic insect larvae, and aquatic plants. In general
gastropods were more sensitive to copper compounds than othel groups
tested. Colloidal copper was most effective, killing all gastropod
vectors at 0.075 mg Cull in 3-5 days.
1579.
Foster, P. 1976. Concentrations and concentration factors of
heavy metals in brown algae. Environ. Pollut. 10:45-53.
Samples of Fucus vesiculosus from the Menai Straits had mean
concentrations (in mg/kg) of 116 for Zn, 9 for Cu, 103 for Mn, 8 for Ni,
218 for Fe, 2 for Cd, 3 for Pb, and 4 for Cr; Ascophyllum nodosum con-
tained 149 Zn, 12 Cu, 21 Mn, 5 Ni, 86 Fe, 2 Cd, 2 Pb, and 3 Cr. The
concentration factors (in mg/kg dried seaweed per ug/ml dissolved metal
in seawater) from this and previous studies were found to be: 1.3 x
104 for Zn, 8.6 x 103 for Cu, 3.9 x 103 for Mn, and 4.6 x 103 for Ni in
Ascophyllum; and 1.0 x 104 to 6.4 x 104 for Zn, 3.7 x 103 to 2.7 x 104
for Cu, 4.6 x 103 to 2.6 x 104 for Mn, and 2.8 x 103 to 6.8 x 103 for Ni
in Fucus. When samples were analyzed from the mouth of Dulas Bay, an
area of high metal pollution, levels (in mg/kg) increased in Fucus to:
306 Zn, 71 Cu, 71 Mn, 6 Ni, and 75 Fe; and in Ascophyllum to: 199 Zn,
68 Cu, 16 Mn, 5 Ni, and 30 Fe. Both species of algae can be used as
environmental indicators of Cu, and Fucus can be used for Zn. Neither
species showed direct relationships between concentrations of Fe and Mn
in the weeds and water. Concentrations of Cd, Pb, and Cr were less for
seaweeds in Dulas Bay; contrary to the higher levels of these metals in
the water; in Fucus, concentrations were 1.8, 2.3, and 3.8, respectively,
and in Ascophyllum, 1.5, 2.2, and 2.2, respectively. This suggests that
in highly polluted areas algal concentrations of minor elements do not
reflect water concentrations.
1580.
Fowler; B.A., D.A. Wolfe, and W.F. Hettler. 1975. Mercury and
iron uptake by cytosomes in mantle epithelial cells of quahog
clams (Mercenaria mercenaria) exposed to mercury. Jour. Fish.
Res. Bd. Canada 32:1767-1775.
Mercury increased and Fe decreased in mantle fringes of clams
exposed to 0, 0.1, 1, and 10 mg Hg2+/l.After 6 days Hg and Fe contents
in mg/kg wet wt were respectively 0.90 and 16.7 (controls), 2.0 and 9.6
(0.1 mg Hg2+/l), 3.9 and 6.0 (1 mg Hi~l) and 6.6 and 15.3 (10 mg Hg2+/l)
A dose-related increase of electron dense cytosomes was observed by
electron microscopy in mantle tentacle epithelial cells of Hg-treated
clams.
109
-------
1581.
Fowler, J.R. 1931. The relation of numbers of animals to sur-
vival in toxic concentrations of electrolytes. Physio1. Zool.
4:215-245.
In 20 m1 of solution, single Daphnia 10ngispina exhibited
greater survival than groups of 20 individuals at electrolyte levels,
in g/l, of 4.13 for CaC12, 1.85 for KC1, 3.5 for MgC12, 32.4 for MgS04,
4.9 for Ca(N03)2, 0.19 for Zn(N03)2, 6.38 for NaN03, 2.9 for NaC1, 0.024
for NaOH, and 0.0084 for KOH. Groups of 20 individuals were favored in
higher metal solutions, in g/l, of 7.15 for CaC12, 3.7 for KC1, 4.7 for
MgC12, 43.2 for MgS04, 8.2 for Ca(N03)2, 2.8 for Zn(N03)2, 11.5 for
NaN03, 8.7 for NaCl, 0.2 for NaOH, and 0.14 for KOH. Introduction of
C02 into toxic solutions with Daphnia increased their survival time in
strong concentrations and decreased their survival time in weak concen-
trations. Author concluded that C02 is an important factor in causing
differential survival between groups of Daphnia and single individuals
when exposed to toxic solutions.
1582.
Fowler, S.W. 1966. Uptake and retention of zinc-65 by Euphausia
pacifica Hansen. M.A. Thesis. Oregon State University,
Corvallis, Oregon: 58 pp.
Uptake, retention and desorption of Zn-65 by live and forma1in-
preserved ~. pacifica were observed at 5, 10 and 15 C and at concentra-
tions of 10 and 25 ~c Zn-65/1. There was proportionately more weight-
specific uptake of Zn-65 at 25 ~c Zn-65/1 than at 10 ~c/1. Uptake in
live animals was dependent upon water temperature, size of animal, and
concentration of Zn-65 in water. Weight-specific uptake was linear over
the 5-15 C range, with uptake lowest at 5 C and highest at 15 C.
Weight-specific uptake and concentration factors (ratios of cpm/g dry
weight to cpm/m1 water), corrected to 44 hours, generally decreased as
weight increased, particularly at 5 and 10 C. There was a general
similarity of concentration factors at 10 and 25 ~c/1 for animals of
similar weight at any given temperature; a temperature dependency was
noted with lowest concentration at 5 C and highest at 15 C. Loss rates
were dependent upon initial Zn-65 concentration in euphausiids, with
greatest loss in animals with the highest specific activity (cpm/mg).
Loss rates were weight dependent, and also temperature dependent, with
greater loss at higher temperatures. Considering losses of activity due
to moulting during uptake (34%) and during desorption (17%), a realistic
figure for loss of Zn-65 through moulting averaged about 25% of total
body activity. Since weight-specific uptake and loss of Zn-65 was
dependent upon weight (perhaps surface area) and concentration of iso-
tope, and since similar responses to Zn-65 uptake and loss were achieved
with formalin-preserved euphausiids as well as live ones, it was con-
cluded that Zn-65 accumulation by euphausiids was an adsorptive process,
110
-------
and that temperature increases might somehow alter exoskelton consti-
tuents so as to present additional sorption sites.
Concentration factors computed from field data were 7 to 24
times greater than those from laboratory data. Although several factors
tended to show that the data were not comparable, the possibility existed
that euphausiids could accumulate more Zn-65 from low chronic levels than
from high temporary concentrations of the isotope. The importance of
euphausiids in transport and cycling of Zn-65 is discussed with respect
to moulting, predation and diel migration.
1583.
Fowler, S.W. 1974. The effect of organism size on the content
of certain trace metals in marine zooplankton. Rapp. Comm.
into Mer Medit. 22(9):145-146.
Assays with euphausiids and pelagic shrimp showed that concen-
trations of Zn, Fe, and Mn were inversely correlated with dry body wt.
Depending upon crustacean species, concentrations of metals in smaller
individuals were 1.2 to 4.1 times greater than larger individuals of the
same species. Copper concentration tended to be a direct function of
dry weight. Concentrations of Zn, Fe and Mn were generally higher in
molts and dissected exoskeletons than muscle tissue; however, the
opposite was true for Cu. Material shed by euphausiids in molting
ranged from 4.7 to 10.9% of dry body wt with smaller animals tending to
lose a greater percentage of body wt than larger specimens. These
molts (40-50% ash)contained 15-20, 19-45, 28-40 and 15% of total body
Zn, Fe, Co, Mn, respectively. Only 5% of total body Cu content was
associated with the molt. In addition, molts from smaller crustaceans
had higher concentrations of Zn and Fe than larger species. Results
suggest that surface sorption is important in accumulation of Zn, Fe and
Mn. Some metals in exoskeleton may serve a metabolic function since
certain metalloenzymes are associated with new shell of crustaceans just
before molt. However, a relatively large fraction of animal's metal
content is associated with outermost layer of exoskeleton which is
relatively inactive metabolically. Ecologically, the rapid molting fre-
quency of these crustacea (every 4-10 days), the relatively high con-
centration of certain metals in the exuviae, and the slow breakdown of
the chitinous molt, make the process of molting an important vector in
the downward transport of metals in the sea.
The direct relationship between Cu content and body weight in
Pasiphaea plus the fact that Cu values were lower in molts than in
muscle tissue of other crustaceans indicate that surface area is probably
not of major importance in concentration of Cu by planktonic crustaceans.
Cu is associated with respiratory pigment haemocyanin, therefore, a
greater pigment concentration to facilitate more rapid gas exchange in
larger carids might account for the relationship between Cu and body size
in Pasiphaea; although presence of haemocyanin in euphausiids is only
111
-------
speculative at this point. Analyses of different size groups of crus-
taceans show that changes in metal content within one species may be
attributable to size alone; therefore, care should be taken to include
this factor when establishing baseline levels of metals in aquatic
organisms.
1584.
Fowler, S.W. and G. Benayoun. 1976. Selenium kinetics in marine
zooplankton. Marine Sci. Communications 2:43-67.
Radiotracer studies of bioaccumu1ation and excretion kinetics
of selenium in the euphausiid Meganyctiphanes norvegica showed that Se
is accumulated both from water and through food chain with highest con-
centration factors occurring through food. As much as 66% of ingested
dose of Se is accumulated into internal tissues. Authors conclude that
Se uptake in nature occurs primarily through food chain. Stable Se
tissue concentrations were highest in viscera at 11.7 ~g Se/g dry wt,
followed by eyes, muscle and exoskeleton at 7.81, 1.77 and 0.84 ~g Se/g
dry wt, respectively. Turnover of Se was rapid; biological half-time of
only 37 days was computed for a Se pool which exhibited slowest rate of
isotope excretion. Fecal pellet deposition and soluble excretion pro-
cesses accounted for 54% and 43%, respectively, of total Se excreted.
Fecal pellets which contain higher Se concentrations than original food,
were assessed as possible biological mechanism for the downward vertical
transport of Se.
1585.
Fowler, S.W. and G. Benayoun. 1976. Influence of environmental
factors on selenium flux in two marine invertebrates. Marine
Biology 37:59-68.
Over a Se concentration range 0.1 to 100 ~g Sell, bioaccumu1a-
tion of Se by mussels Myti1us ga110provincia1is was strongly dependent
on ambient Se concentration in seawater. Mussels accumulated Se4+ to a
greater extent than Se6+. Increasing temperature from 13 C to 24 C
approximately doubled Se concentration factor after 13 days uptake.
Mussels were typed according to size, with different concentration
factors for each group. For mussels averaging 2.1 g wet wt, the mean
C.F. was 46; for 13.2 g wet wt, the C.F. was 29; and for 21.8 g wet wt,
it was 13. Presence of varying amounts of Hg significantly altered Se
uptake kinetics in mussels. Shrimp Lysmata seticaudata accumulated Se
to a lesser extent than mussels, with difference in concentration factors
attributable to the large amount of sorbed isotope lost with shrimp
molts. Once incorporated, Se was lost more rapidly from shrimp than
from mussels. Temperature influenced Se loss from mussels but not from
shrimp. Neither the chemical form of Se nor Hg concentration affected
loss of Se from mussels. More rapid loss of Se was noted from shrimp
which had absorbed the isotope directly from water than via food chain.
112
-------
Biological half-times for Se ranged from 58 to 60 days for shrimp and
63 to 81 days for mussels. In the case of mussels, turnover rates
measured in animals maintained in the laboratory differed from those in
field. Obse~ved variations in flux rate may have been due to differences
in food availability in the two experimental systems.
1586.
Fowler, S.W. and G. Benayoun. 1976. Accumulation and distribu-
tion of selenium in mussel and shrimp tissues. Bull. Environ.
Contamin. Toxicol. 16(3):339-346.
Mussels Mytilus galloprovincialis and shrimp Lysmata seti-
caudata collected near the port of Monaco were subdivided into several
groups. One group of mussels and shrimp was maintained in seawater con-
taining 0.8 J.l Ci/l Se-75 (>160 J.l Ci/J.lg Se as sodium selenite). Another
group of shrimp were maintained in flowing seawater and fed ad libitum
on mussels that had previously accumulated Se-75 for several~ays. The
remaining shrimp and mussels were analysed for stable selenium. Mytilus
readily accumulated Se-75 from the medium and did not appear to have
reached a steady state after 63 days; highest Se-75 concentrations were
in visceral mass, followed by gills, muscle, and mantle in that order.
Shrimp, over a 51-day period, accum~lated Se-75 from the water with
highest concentrations found in exoskeleton (60-90% of total Se-75 body
burden). When Se-75 uptake in shrimp occurred via food chain, the
highest activity was in viscera and exoskeleton, suggesting that in-
gested Se is readily translocated from internal to external tissues.
During uptake, molting did not significantly affect Se-75 concentration
in exoskeleton, since the percentage of the Se-75 body burden retained
in molts was relatively low (about 6%). Concentrations of stable
selenium in shrimp, on a mg Se/kg dry wt basis, were as follows: viscera,
7.0; eyes, 4.8; whole shrimp, 2.6; muscle, 1.9; exoskeleton, 1.5; and
molts, 0.3. For mussel, these values were: gills, 7.0; whole soft
parts, 6.1; mantle 5.2; viscera 3.2; muscle, 1.9; and shell, <0.05 mg
Se/kg dry wt. The relative order of stable Se levels in mussels were
quite different from that achieved by tissues accumulating Se-75 from
the water, indicating that water route may be relatively unimportant in
attaining equilibrium for selected tissues. The relative order of stable
Se concentrations in shrimp tissues agrees with that observed for Se-75
in tissues after uptake for 51 days via the food chain.
1587.
Fowler, S., M. Heyraud and T.M. Beasley. 1975. Experimental
studies on plutonium kinetics in marine biota. In Impacts of
nuclear releases into the aquatic environments. Int. Atom.
Ener. Agen., Vienna, Paper SM-198/23:l57-l77.
Laboratory experiments were conducted to measure plutonium
flux through marine organisms and to clarify pathways by which this
113
-------
element is cycled in the marine environment. Use of a specially pre-
pared isotope, plutonium-237 (1/2 life 46 days), allowed measurements
to be made with standard NaI(Tl) scintillation techniques. Mussels
Mytilus galloprovincialis, shrimp Lysmata seticaudata, and worms Nereis
diversicolor accumulated plutonium-237 from seawater for up to 25 days.
Accumulation by shrimp was relatively slow with degree of uptake strongly
influenced by molting. Cast molts contained large fractions of the
shrimps' plutonium content, indicating the high affinity of Pu for sur-
face areas. Only small amounts of the isotope in molt are lost to water;
hence, molting is considered to be an important biological parameter in
biogeochemical cycling of plutonium. Mussels attained higher concentra-
tion factors than shrimp with most of the accumulated isotope (>80%)
located in shell. Byssus threads often contained large fractions of the
mussels' plutonium-237 content and reached e.F. up to 4100. Worms
readily accumulated plutonium-237 in either the +4 or +6 state, reach-
e.F. of approximately 200. Retention studies indicated a relatively
slow loss of plutonium-237 from all animals studied. With mussel, a com-
puted half-time for most of the animals' plutonium content was about 2
years. The more rapid loss from shrimp (Tb!/2 = 1.5 months) was due
principally to the large fraction of plutonlum lost at molt. Food chain
studies with shrimp indicated that tissue build-up via plutonium inges-
tion would be a slow process. Total excretion was not entirely a result
of passing contaminated food through the gut; approximately 15% of the
ingested plutonium was removed from the contaminated food and subsequently
excreted by processes other than defecation of labelled food. Ratios
of four different plutonium isotopes used in the experiments showed that
when isotopes were present together in the same physicochemical form, no
differences in isotopic behavior were evident--even when total mass of
certain isotopes in the system differed by 103. Authors concluded that
plutonium-237, because of its relatively high specific activity. offered
the best possible means for tracing plutonium biokinetics in aquatic
systems in which the experimental design dictates that total plutonium
concentrations approximate those currently found in the environment.
1588.
Fowler, S.W., J. LaRosa, M. Heyraud, and w.e. Renfro. 1975.
Effect of different radiotracer labelling techniques on radio-
nuclide excretion from marine organisms. Marine Biology 30:
297-304.
Amphipods Gammarus locusta, which accumulated Zn-65 under a
close approximation of natural conditions excreted the radiotracer dur-
ing a 3-month period at a markedly different rate than amphipods
labelled with Zn-65 in the laboratory via different combinations of
radioactive food and seawater. Shrimp Lysmata seticauda, administered
Zn-65 by 3 different methods in the laboratory displayed different
excretion kinetics during the first 2 months of loss. Differences among
excretion rates most likely were a reflection of degree to which various
114
-------
zinc pools within shrimp had equilibrated with Zn-65. During the next
several months all Zn-65 loss rates were quite similar, probably indicat-
ing that radiotracer excretion was taking place from similar zinc pools
within shrimp. Importance of adequate radiotracer labelling techniques,
as well as proper design of subsequent excretion experiments in studies
on flux rates of the corresponding stable metal is discussed. Authors
concluded that laboratory radiotracer experiments which are intended to
supply information on actual situations in the sea require careful de-
sign and execution.
1589.
Fowler, S.W. and B. Oregioni. 1976. Trace metals in mussels
from the N.W. Mediterranean. Marine Poll. Bull. 7:26-29.
Mean content of selected metals, in mg/kg dry wt, of Mytilus
galloprovincialis soft parts from 15 sites in the NW Mediterranean Sea
were: 0.76 for Ag, 1.9 for Cd, 2.8 for Co, 7.5 for Cr, 18.0 for Cu,
443 for Fe, 21 for Mn, 4.3 for Ni, 21 for Pb, and 209 for Zn. Highest
values for most metals were in samples from port cities and areas near
river discharges. SeasGnal variations were evident, with an overall
increased concentration in March 1974 attributed to high precipitation
and runoff. Data comparison indicates that average metal levels in NW
Mediterranean mussels do not differ markedly from those of similar
species throughout the world.
1590.
Fowler, S.W., L.F. Small and J. LaRosa. 1972. The role of
euphausiid molts in the transport of radionuclides in the sea.
Rapp. Comm. Int. Mer Medit. 21(6):291-292.
Meganyctiphanes norvegica in a mixed-isotope seawater medium
for 5 days, shed molts containing 53, 39, 59 and 75% radioactive Co,
Mn, Zn, and Fe, respectively. Percentages were reduced to 3.5, 2.4,
3.3 and 10.6% when isotopes were accumulated by grazing on radioactive
Artemia. Radioisotope content of molts decreased sharply in subsequent
molts. Molts which disintegrated in 48 to 96 hrs lost incorporated
isotopes at an exponential rate. Decreasing loss rate order was Mn-54,
Zn-65, Co-57 and Fe-59. Authors concluded that euphausiid molts consti-
tuted important vehi~les of radioisotope transfer into marine ecosystems.
1591.
Frazier, J.M. 1975. The dynamics of metals in the American
oyster, Crassostrea virginica. I. Seasonal effects.
Chesapeake Science 16:162-171.
Seasonal dynamics of Mn, Fe, Zn, Cu, and Cd were investigated
in a genetically similar population of hatchery-reared oysters. Con-
centrations in whole soft tissues, in mg/kg, for Mn ranged from 30 (Oct)
115
-------
to 2 (Dee); Fe ranged trom 510 (Oct) to 150 (Dee); Zn from 5,000 (Aug)
to 2,100 (Nov); Cu from 250 (Aug) to 50 (Oct); and Cd from 16 (Aug) to
3 (Oct). Average shell concentrations (in mg/kg dry wt) were Mn 505,
Fe 19. Zn 2.5, Cu 0.16, and Cd <0.1. Bottom sediments had average con-
centrations (in mg/kg dry) of 18,200 for Fe, 57 for Mn, 46 for Zn, 32 for
Cr, 11 for Pb, 6 for Cu, 6 for Ni, 2.7 for Co, and 0.3 for Cd.
Metals were grouped into two classes according to their dynam-
ics: (1) Mn and Fe concentrations in soft tissues were significantly
correlated with shell deposition. A high rate of Mn turnover in soft
tissues (~2X the body burden/day) occurred during shell growth seasons,
(2) Zn and Cu concentrations were not correlated with shell growth.
Zn and Cu body burdens exhibited a gradual increase during spring and
early summer followed by a rapid loss during August-September in which
33% of Zn and 50% of Cu was lost in <4 weeks. Cd behavior was similar
to Zn and Cu with a 50% reduction in body burden duri~g an 11 week period
between July and October.
1592.
Frazier, J.M. 1976. The dynamics of metals in the American
oyster, Crassostrea virginica. II. Environmental effects.
Chesapeake Science 17:188-197.
Hatchery-reared oysters were exposed in situ to metal-
contaminated sediments (experimental) and non-contaminated (control)
environments from September 1972 to August 1973. The amount of contam-
ination was reflected in levels of Mn, Fe, Zn, Cu, and Cd in sediment
samples. For experimentals this was (mg/kg dry wt) 90 Mn, 26,300 Fe,
232 Zn, 123 Cu, 0.7 Cd; for controls 50 Mn, 18,800 Fe, 48 Zn, 5.6 Cu, and
0.3 Cd. On a dry wt basis Zn and Cu were accumulated in soft tissues of
experimental oysters to levels of 4,100 mg Zn/kg and 450 mg Cu/kg; for
controls these were 1,700 mg Zn/kg and 60 mg Cu/kg. Relative accumula-
tions of metals in soft tissues of experimentals when compared to con-
trols reflected relative metal concentrations between the two environ-
ments. Growth of oysters, measured by soft tissue dry weight and shell
dimension was identical for the two groups but shells of experimentals
were 16% thinner than controls. Trace metal incorporation into shell was
affected with Mn incorporation surpressed and Fe, Zn and Cu slightly
increased. Uptake of metals by oyster soft tissues was seasonally
dependent with rapid uptake occurring in summer and fall but delayed up-
take in the early spring.
1593.
Freeman, H.C. and D.A. Horne. 1973. The total mercury and
methylmercury content of the American eel (Anguilla rostrata).
Jour. Fish. Res. Bd. Canada 30:454-456.
Total Hg content of Nova Scotian eels was 0.72 i 0.05 mg/kg
wet wt; methylmercury content was 0.40 ! 0.06 mg/kg wet wt. Since the
116
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mean total Hg content was less than 1 mg/kg wet wt and the toxic methyl-
mercury content was 50% of this, or less than the 0.5 mg/kg wet wt
guideline, such eels were considered acceptable for human consumption.
1594.
Freeman, L. and I. Fowler. 1953. Toxicity of combinations of
certain inorganic compounds to Daphnia magna. Sewage Indust.
Waste. 25(10):1191-1195.
The concentration of sodium chromate which immobilized 50% of
treated microcrustaceans, D. magna, decreased from 0.42 mg/l when
applied alone, to 0.276 mg71 in combination with 2984 mg sodium sulfate/I,
and to 0.159 mg/l when combined with 93 mg sodium silicate/I. Further
reductions occurred when additional inorganic Na salts were added.
1595.
Fretter, V. 1953. Experiments with radioactive strontium (90Sr)
on certain molluscs and polychaetes. Jour. Mar. BioI. Assn.
U.K. 32:367-384.
In Arion hortensis, a land pulmonate, dietary Sr-90 was taken
up by digestive cells, haemocoel, and digestive gland lime cells, where
it eventually concentrated around Ca spherules. Some Sr-90 entered the
body through the intestinal wall. Ca stores surrounding the blood
vessels and mantle Ca cells also concentrated Sr-90. In marine molluscs
Aplysia punctata and Acanthodous pilosa Sr-90 from surrounding water
passed through body surfaces and gills. In A. pilosa, ions which enter
tissues from seawater accumulated around Ca concretions in mantle. Both
marine species obtained cations directly from water as well as food.
Mytilus edulis localized Sr-90 for excretion within 10 hrs; ions were
aggregated in pericardial glands. When mussels were kept in a medium
with elevated Sr content, amoebocytes containing Sr-90 and its decay
product yttrium were found in connective tissue of labial palps and in
gill blood spaces. Amoebocytes of Calyptraea chinensis accumulated
Sr-90 from filtered seawater; lymphoidocytes of Platynereis dumerili, a
polychaete, concentrated Sr-90 and transported it to outer body surface.
1596.
Fujiki, M. 1963. Studies on the course that the causative agent
of Minamata Disease was formed, especially on the accumulation
of the mercury compound in the fish and shellfish of Minamata
Bay. Jour. Kumamoto Med. Soc. 37(9):494-521. (In Japanese)
A series of studies were initiated to measure mercury content
in fish and shellfish from Minamata Bay, to determine accumulation by
shellfish under laboratory conditions, and to establish mercury trans-
fer from shellfish to rats in feeding studies.
117
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Mercury content in whole clam Hormomya mutabilis from Minamata
Bay ranged up to 85 mg/kg dry wt; most active sites were ganglion (181
mg/kg), gill (87 mg/kg) and digestive gland (73 mg/kg). Edible muscle
from 5 species of fishes collected from Minamata Bay contained, in mg/kg
dry wt, 0.9, 14, 16, 58, ~nd 309, respec~ively. .U~take studies with2+
clam Venus japonica held ln seawater medla contalnlng 0.3 mg/l of Hg ,
and 0.3 mg/l of other compounds including arsenic or selenium indicated
that after 7 to 12 days survivors contained 39 to 148 mg Hg/kg whole
body; most clams died during exposure. Uptake was higher and death rate
greater when methylmercury compounds were tested. Some accumulation of
Hg was observed in kidney and liver of rats fed Venus cultured in sea-
water containing mercury compounds. However, mercury content was sub-
stantially higher in rat liver (up to 440 mg/kg dry wt), kidney (383
mg/kg) and brain (86 mg/kg) when fractions of the mercury sludge from
the acetaldehyde plant were administered.
1597.
Fujita, M. and K. Hashizume. 1975. Status of uptake of mercury
by the freshwater diatom, Synedra ulna. Water Research 9:889-
894.
Preliminary studies of 8 days duration established a lethal
concentration of mercuric chloride between 10 and 50 ug/l. Using Hg-203
labelled mercuric chloride, Synedra took up mercury rapidly from sur-
rounding water. Cells attained maximum uptake during the first 7 h.
Comparison of mercury uptake by dividing cells with that of non-dividing,
heat killed cells and their silicate shells showed that factors other
than cell-division or photosynthesis were responsible for mercury uptake
by Synedra. About 20% of the total amount of mercury found in dividing
cells was taken up by passive adsorption; about 50% was accumulated in
the inner part of cells. Synedra took up 0.45 urn filterable or ionic
mercury rather than particulate mercury larger than 0.45 urn.
1598.
Fujita, M., E. Takabatake and K. Iwasaki. 1976. Effects of
light, magnesium and cyanide on accumulation of mercury by a
freshwater diatom, Synedra. Bull. Environ. Contamin. Toxicol.
16:164-172.
Uptake of mercury by Synedra was much higher under illumination
than in darkness. Increasing concentrations of magnesium were associated
with increasing Hg uptake by Synedra until an optimal concentration of
0.1 mM is reached. At higher concentrations of Mg2+, Hg uptake is
drastically reduced. These increases suggest the presence of an active
uptake linked to energy metabolism which requires light and Mg2+.
Cyanide and azide, potent inhibitors of respiratory enzymes, effectively
prevented Hg uptake. In presence of 0.01 mM CN-, uptake was reduced to
50% of controls. Azide also inhibited uptake but less effectively.
118
-------
Mercury accumulation observed in dark or by dead cells was attributed
to passive adsorption.
1599.
Fujita, T. 1971. Concentration of major chemical elements in
marine plankton. Geochem. Jour. 4:143-156.
Plankton samples collected in coastal and off-shore areas
near Japan were sorted and analyzed for Na, K, Ca, Mg and Si. Mean
values for zooplankton samples of single species, which included crus-
taceans, tunicates, protozoa, coelenterates and chaetognaths, in mg/g
dry wt were: Na 4.0, K 5.0, Ca 3.9, Mg 3.8 and Si 4.3. Mean values for
mixed zooplankton in mg/g dry wt were: Na 2.8, K. 9.8, Ca 8.7, Mg 4.8,
and Si 27. Mean values for samples of mixed phytoplankton species in
mg/g dry wt were: Na 1.4, K. 68.7, Ca 6.4, Mg 5.9. and Si 195.
1600.
Fujita, T. 1972. The zinc content in marine plankton.
Oceanog. Works Japan 11(2):73-79.
Records
Zinc content in 48 samples of zooplankton representing crus-
taceans, coelenterates, tunicates, and chaetognaths of single species
and 18 samples of phytoplankton of mixed species ranged from 20 to
1,069 mg/kg dry wt in zooplankton, and 104 to 1,757 mg/kg dry wt (aver-
age 590 mg/kg) in phytoplankton.
1601.
Fujita, T., T. Yamamoto, I. Yamazi and T. Shigematsu. 1969.
contents of ash, iron and manganese in marine plankton.
Jour. Chern. Soc. Japan 90:680-686. (In Japanese)
The
Iron and manganese values in plankton species collected
between 34°59' north latitude 136°41' and 34°57' - 136°47' are shown
for crustaceans, chaetognaths, annelids, molluscs, algae and tunicates.
Iron values in g/kg wet wt ranged from 0.1 for euphasiids to 5.2 for
Acartia clausi, a copepod; for Mn, these were 0.002 g/kg wet wt
(euphasiids) to 0.188 for Acartia clausi. Fe/Mn ratios ranged from a
low of 5.6 for salps to 93.2 for euphasiids.
1602.
Fukai, R. 1965. Analysis of trace amounts of chromium in marine
organisms by the isotope dilution of Cr-5l. In Radiochemical
methods of analysis, Int. A~om. Energy Agency:-Vienna: 335-351.
Chromium concentrations, in mg/kg dry wt, of various marine
organisms from the Mediterranean Sea were 1.55 for algae Entermorpha
linza; 1.42 for algae Cystoseira myriophylloides; 1.52 for copepod
Acartia clausi; 0.11 for soft parts of shrimp Parapenaeus longirostris;
119
-------
0.48 for meat of crab Eriphia verrucosa; 0.97 for soft parts of mussel
Mytilus edulis; 1.29 for soft parts of gastropod Murex trunculus; 0.28
for muscle of sea cucumber Holothuria forskalii; 0.14 for muscle of
sardine Sardina pilchardus; and 0.22 for muscle of bogue (teleost)
Boops boops.
1603.
Fukai, R. and D. Broquet. 1965. Distribution of chromium in
marine organisms. Bull. Inst. Oceanogr. 65(1336):1-19.
Chromium content for various species of seaweeds ranged from
0.4 to 2.5 mg Cr/kg dry wt, with 60% of the values in the range of 0.6
to 1.5. Values for Zostera were higher at 1.3 to 4.2 mg Cr/kg dry wt.
Variations in Cr content of seaweeds were apparently unrelated to species,
seasons, or collection locales. Chromium in seaweeds may be the result
of surface contamination through silt or other particles. Cr content in
mg Cr/kg dry wt was high in polychaetes at 8.1 to 14.7; for crustaceans
Cr ranged from 0.09 in king crab meat Paralithodes kamtschatica, to 2.1
for whole copepods Clausocalanus and Paracalanus. Cr content in soft
parts of bivalves and gastropods ranged from 0.5 to 1.6 mg Cr/kg dry wt;
for cephalopods this was 0.07 to 0.12. The lower Cr content of cephalo-
pods may be due to their pelagic rather than benthic mode. Cr content
in echinoderms ranged from 0.3 to 1.2 mg Cr/kg dry wt; and for fish it
was 0.03 to 0.5. Iron content of samples was also determined in order
to compare the Fe/Cr ratio with that of marine sediments, since Cr+3 in
seawater is coprecipitated with iron hydroxide.
1604.
Fukai, R. and W.W. Meinke. 1959. Some activation analyses of
six trace elements in marine biological ashes. Nature 184:
815-816.
Metal levels, in mg/kg ash, for the seaweed Ulva were 5.9 to
13.3 for vanadium, 0.13 to 0.18 for tungsten, 0.046 to~73 foy rhenium,
0.015 to 0.093 for gold and 5.4 for arsenic. Porphyra, an alga, con-
tained 262 and 17 mg/kg ash of V and molybdenum, respectively. Clams
Tapes japonica, and prawns Pandalus sp, contained respective levels, in
mg/kg ash wt, of 15 and 1.1 for V, <0.05 and 0.83 for As, 0.46 and
<0.005 for W, 0.064 and <0.005 for Re, and 0.079 and 0.0046 for Au.
Mackerel Pneumatophorus, japonicus flesh had, in mg/kg ash wt, 0.34 for
As, <0.014 for W, <0.008 for Re, and 0.0026 for Au.
1605.
Fukai, R. and W.W. Meinke. 1962. Activation analyses of
vanadium, arsenic, molybdenum, tungsten, rhenium, and gold in
marine organisms. Limnol. Oceanogr. 7:186-200.
Metal levels, in mg/~g dry wt, of alga Ulva sp. and Porphyra
sp., were 1.3 to 3.1 for vanadIum, 1.2 for arsenic, n.d. to 1.0 for
120
-------
molybdenum, 0.029 to 0.042 for tungsten, 0.011 to 0.016 for rhenium, and
0.021 to 0.0035 for gold. Respective values, in mg/kg dry wt, for soft
parts of clam Tapes japonica, soft parts of prawn Pandalus sp., and
muscle of mackerel Pneumatophorus japonicus, were: 1.1, 0.07, and n.d.
for V; <0.004, 0.05 and 0.015 for As; 0.03, <0.0003 and <0.0006 for W;
0.0046, <0.0003 and <0.0004 for Re; and 0.0057, 0.00028 and 0.00012 for
~.
1606.
Furukawa, K. and K. Tonomura. 1972. Induction of metallic
mercury-releasing enzyme in mercury-resistant Pseudomonas.
Agr. BioI. Chern. 36(13):2441-2448.
Formation of metallic mercury-releasing enzyme (MMR-Enz) which
catalyzes reduction of mercurials to metallic Hg was induced when the
organism was grown with mercurials such as phenylmercuri'c acetate (PMA).
p-chloromercury benzoate (pCMB), sodium ethyl mercuric thiosalicylate
(merzonin), mercuric chloride (MC) and metallic mercury. It was not
induced when grown with HgS or other metals such as Ag, Cd, Cu, Fe, Co, or
Sn. Cadmium and Cu inhibited MMR-Enz formation. D-glucose:NAD oxi
doreductase or L-arabinose:NADP oxidoreductase and cytochrome c-I which
were all involved in decomposition of mercurials together with MMR-Enz
were present in the crude extract regardless of mercurial addition.
Authors suggest that MMR-Enz plays a conclusive role in decomposition
reaction of mercurials.
1607.
Gajan, R.J. and D. Larry. 1972. Metals and other elements.
Determination of lead in fish by atomic absorption spectro-
photometry and by polarography. I. Development of the
methods. Jour. Assoc. Off. Anal. Chemists 55:727-732.
A method for determination of Pb in 12 species of freshwater
and marine fish species by atomic absorption spectrophotometry and
polarography is described with good agreement between the two at levels
of 1.0 to 10.0 mg/kg. Over this range, recoveries averaged 96.1% for
polarography and 93.8% for A.A.S. Determinations of Pb levels in fish
using both methods were, in mg/kg ash wt, between 0.1 and 0.4 for salmon,
0.2 and 0.8 in sucker, 0.1 and 0.9 in coho salmon, 0.1 and 0.8 in sheep-
head, 0.2 and 0.8 in carp, 0.2 and 0.8 in catfish and between 0.1 and
1.3 in perch.
1608.
Galtsoff, P.S. 1942. Accumulation of manganese and the sexual
cycle in Ostrea virginica. Physiol. Zo01. 15:210-215.
Manganese levels, in mg/kg dry wt, of oysters collected
throughout the year, were 51 to 59 for ripe ovaries, 4 to 7 for ripe
121
-------
testes, 17 (winter) to 38 (summer) for gill, 8 (winter) to 17 (late
summer) for mantle, and 3 to 9 for adductor muscle, yielding whole body
concentrations of 7 to 11 in winter and 28 to 57 in summer. Peak Mn
concentrations coincided with maximum gonad development and sexual
activity, apparently, in response to accumulation in ovaries. Gills in
both sexes showed similar seasonal trends.
1609.
Galtsoff, P.S. 1953. Accumulation of manganese, iron,
and zinc in the body of American oyster, Crassortaea
virginica. Anatom. Rec. 117:601-602. (Abstract)
copper,
(Ostrea)
Oysters contained metal levels in mg/kg dry tissue, of 9 to 60
for Mn, 140 to 800 for Fe, 670 to 3000 for Cu and 500 to 13,700 for Zn;
concentrations were highest from June to October. Mn and Fe levels were
more stable than Cu and Zn. Cu, Fe and Zn were stored in gill and
mantle; Mn was concentrated during reproduction in ovaries, but not in
testes. Fe and Cu concentrations in oysters were increased by addition
of salts of these metals to water in which mollusks were kept. Iron
oxide was adsorbed primarily by phagocytes present on gill surface, even
during winter suppression of feeding. During feeding season, Fe was
absorbed through digestive tract, although greatest portion of metal
delivered to intestines was discharged with feces. Excretion was by
diapedesis and through mantle mucous cells.
1610.
Galtsoff, P.S. and D.V. Whipple. 1930. Oxygen consumption of
normal and green oysters. U.S. Dept. Commerce, Bull. Bur.
Fisheries 46:489-508.
Green pigment of oysters is not a hemocyanin or copper pro-
teinate of any kind; the compound exists in a highly dissociated state.
Copper content of normal oysters varies between 8.21 to 13.77 mg/IOO
grams dry wt, or from 0.16 to 0.248 mg per oyster. Copper content of
green oysters analyzed during the investigation varied between 121 and
271 mg per 100 grams dry wt, or from 1.24 to 5.12 mg per oyster. Green
oysters show a slight increase in oxygen consumption over normal
oysters; the significance of this difference is, however, doubtful.
1611.
Ganther, H.E., C. Goudie, M.L. Sunde, M.J. Kopecky, P. Wagner,
S.-H. Oh, and W.G. Hoekstra. 1972. Selenium: relation to
decreased toxicity of methylmercury added to diets containing
tuna. Science 175:1122-1124.
Samples of canned tuna muscle show average levels of 1.91 to
2.91 mg Se/kg wet wt and 0.32 to 2.87 mg Hg/kg. Se and Hg in tuna
appear to be accumulated in a relatively constant ratio. Japanese
122
-------
quail, Corturnix corturnix japonica, given 20 mg methy1-Hg/kg in diets
containing 17% (by wt) tuna survived longer than quail given this con-
centration of methy1-Hg in a corn-soya diet. Methy1-Hg toxicity in rats
was decreased 'by dietary Se supplement comparable to that supplied by
tuna. Authors concluded that selenium in tuna, far from being a hazard
in itself, may lessen the danger to man of mercury in tuna.
1612.
Garder, K. and O. Sku1berg. 1966. An experimental investigation
on the accumulation of radioisotopes by freshwater biota.
Arch. Hydrobio1. 62(1):50-69.
Representative species of algae, higher plants, fishes and
invertebrates were exposed for 5 months in river water to radioisotopes
of selected metals. Exposure levels in ~CiX10-6/1, were 1.2 for Zr-95-
Nb-95, 2.1 for Cs-137, 6.0 for Ce-144, 7.8 for Sr-89 and 7.8 for Ru-103.
Mean post-exposure values in ~Ci/kg wet wt in algae Vaucheria wa1zii
were 2.1 for Zr-Nb, 1.0 for Cs, 7.2 for Ce, 2.9 for Sr and 132 for Ru.
For Eurycercus lame11atus, a c1adoceran, and Anodonta piscina1is, a
1ame11ibranch, these were 0.8 and 0.8 for Cs-137, 4.8 and 0.4 for Sr-89,
2.3 and 0.8 for Ce-144, and 0.7 and 0.2 for Zr-95-Nb-95. After 9 days
exposure to Cs-137 at levels of 10-2 ~Ci/1, Cs-137 levels in the vascular
plants A1isma p1antagoaquatica and E1atine triandra were 0.05 and 0.12
~Ci/kg wet wt, respectively. Brown trout Sa1mo trutta, and minnows
Phoxinus phoxinus, accumulated Cs-137 up to lOX media concentrations.
1613.
Gardner, G.R. 1975. Chemically induced lesions in estuarine or
marine te1eosts. In Ribe1in, W.E. and G. Migaki (eds). The
pathology of fishe~ Univ. of Wisconsin Press, Madison, Wisc.:
657-693.
Damage to sensory organ systems of teleosts was demonstrated
by salts of Cu, Hg, Ag, Cd, and Zn and also methoxychlor; crude oil, and
pulp mill effluents. Initial studies with chloride salts of silver at
5 mg/l, cadmium at 65 mg/l, copper at 15 mg/l, mercury at 1 mg/l, and
zinc at 70 mg/l were conducted to measure effects on gills after 48 hrs
exposure. Concentrations of these five metals, considered to be acutely
toxic to mummichog Fundulus heteroclitus, elicited a heavy gill-mucus
response. Heavy mucus concentrations did not occur uniformly across any
one gill arch, or cause complete collapse of respiratory structure.
Accumulations were lower in animals exposed to Cd and Hg than Ag, Cu,
and Zn. Apical areas of many gill filaments were necrotic following
exposures to Cd and Hg, with cartilaginous filament rods being denuded
and exposed. Mercury, Ag, and Cu were neurotoxic with lesions observed
in olefactory and lateral line systems; damage syndromes were not similar.
Cadmium and Zn exposures did not cause morphological anomo1ies of neuro-
sensory structures of mummichog.
123
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Mercury levels of 0.5 mg/l or higher caused severe cytoplasmic
and nuclear degeneration of all cellular elements of the lateral line
canals in mummichog. The necrocytosis affected secretory cells of canal
lining, squamous epithelium of canal walls, and canal's secretory and
mucus cells. Neurosensory hillocks within these canals usually were
necrotic. Severe degenerative changes in murnrnichog olfactory organs
also accompanied Hg concentrations of 0.5 mg/l and higher. Various
degrees of cellular ~egeneration were identifiable in neurosensory cells
of these organs. However; no evidence of hyperplasia or widespread
necrosis, such as that observed following copper exposures, could be
associated with the sustentacular cells. The degree of morphological
alteration to neurosensory cells was generally uniform throughout the
organ, except basally where the lesion had progressed further.
Silver, like Hg and Cu, exerted a toxic effect within canals
of the cephalic lateral line extension of murnrnichog. The change was most
similar to those following Cu exposures. Epithelial lining of olfactory
pit and sustentacular epithelium of olfactory organs were affected, as
indicated by widespread cellular degeneration. Sensory organs were
usually apically necrotic in these cases. Although all fish exposed to
Ag did not exhibit these changes, at least one did at every Ag concentra-
tion studied. In spite of the small number of animals tested, the occur-
rence of the lesion in lateral line and olfactory organs seemed to be an
"all or none" reaction. The condition was always severe if present,
regardless of toxicant concentration.
No identifiable lesions were associated with intestine, kidney,
or circulating blood cells of murnrnichog exposed to 5 mg/l of Cd at any
time during test of one year duration; these tissues in murnrnichog are
known to be altered by higher levels of Cd. However, subtle alterations
were observed in thyroid. The thyroid of several animals was hyperplastic
following 3 months of continuous exposure, as evidenced by a marked in-
crease in number of follicles. This condition was evident through the
eighth month of continuous exposure, but not as pronounced afterwards.
Approximately 10% of the specimens examined in the third and eighth
months had the thyroid condition; the proportion rose to nearly 80%
during the seventh month (September). Because of the early loss of con-
trol organisms, it was not possible to link hyperplasia with Cd.
1614.
Gardner, W.S., H.L. Windom, J.A. Stephens, F.E. Taylor and R.R.
Stickney. 1975. Concentrations of total mercury in fish and
other coastal organisms: implications to mercury cycling.
In Howell, F.G., J.B. Gentry, M.H. Smith (eds.). Mineral
Cycling in Southeastern Ecosystems. U.S. Energy Res. Dev.
Admin.: 268-278. Available as CONF-7405l3 from NTIS, U.S.
Dept. Cornrn. Springfield, VA 22161.
Total and methyl Hg concentrations were determined for a
variety of aquatic organisms from several estuaries of the southeastern
124
-------
U.S. Roots of Spartina, a prominent marsh plant, had higher concentra-
tions of Hg than stems or leaves (0.78 vs. 0.23 mg/kg dry wt) with no
methylmercury detected. Hg levels in muscle of 20 fish species generally
ranged between 0.1 and 1 mg/kg dry wt with exceptional values of 1.8 and
2.9 in sea catfish Arius felis, and toadfish Opsanus tau, respectively.
Average Hg muscle concentrations in 8 species of elasmobranchs ranged
from 1.5 to 4 mg/kg dry wt. Methylmercury accounted for 70% of total
mercury in muscle of fish and elasmobranchs. Relative quantity of
methylated Hg in livers of fish and elasmobranchs ranged from 3% for
Carcharhinus milberti (sand bar shark) to 48% of total Hg for flounder.
Of crustaceans examined, blue crab muscle contained 0.45 mg Hg/kg dry wt
of which 68% was methylated. Average Hg muscle concentration of 4 species
of shrimp was 0.22 mg/kg dry wt of which 43% was methylated.
Preliminary studies have shown that methyl mercury potentially
can be transported upward through Spartina plants. If the mercury is
released to water column, it could be taken up by fish, and this could
account for the higher mercury levels in finfish than intermediate food-
chain members.
1615.
Gebhards, S., F. Shields and S. O'Neal. 1971. Mercury levels in
Idaho fishes and aquatic environments, 1970-71. State of
Idaho Fish & Game Dept. and Dept. of Health. 23 pp.
Maximum mercury concentration found in 1,096 fish representing
26 species was 1.7 mg/kg wet wt in a squawfish. Piscivores exhibited
higher Hg levels than plankton or insect feeders. Warmwater non-game
fish species contained 2X the Hg levels found in coldwater (trout and
whitefish) game fish. Mercury levels in fish from reservoirs were
higher than those from contributing streams. Fifty-nine fish or 5.3%
of the total contained >0.5 mg Hg/kg wet wt.
1616.
George, S.G., B.J.S. Pirie and T.L.
of accumulation and excretion of
edulis (L.) and its distribution
Mar. BioI. Ecol. 23:71-84.
Coombs. 1976. The kinetics
ferric hydroxide in Mytilus
in the tissues. Jour. Exp.
Using Fe-59-labelled ferric hydroxide it was found that Fe-59
accumulates in linear proportion to seawater concentration and is found
in all tissues: concentration factors for viscera, kidneys, gills,
muscle-mantle is 25:6:4:1, respectively. Particulate iron is taken up
by pinocytosis by special epithelial cells in gills, gut, kidney and
possibly labial palps and held in membrane-bound vesicles, unaccompanied
by mucus in gills and kidney, but with mucus present in the digestive
diverticulum and mid-gut cells. There is no free iron within the cyto-
plasm. Approximately 30% of iron presented to gut is not absorbed,
being voided with feces. Absorbed iron is exocytosed and then passed
125
-------
on to amoebocytes in haemolymph for transport to other tissues, a major
fraction being excreted by transfer to byssal threads.
1617.
Getsova, A.B. and G.A. Volkova. 1962. The accumulation of
radioactive isotopes by certain aquatic insects. Entomol.
Rev. 41:61-70.
The concentration, accumulation factor, and rate of desorption
of Ca-45, Cr-5l, Fe-59, Co-60, Zn-65, Sr-90, Zr-35, Ru-l06, Cd-lIS,
Cs-137, Ce-144, and Hg-203, were determined at different developmental
stages of mosquitoes Culex pipiens pipiens, Theobaldia alaskaensis;
caddisflies Halesus interpunctatus, Phryganea grandis, Leptocerus sp.;
and dragonflies of the genera Aeschna and Lestes. Accumulation of radio-
isotopes was different in different species for the sa~e element and for
different elements in the same species. In all species the larval
stages accumulated more than the pupal stage. Accumulation of radio-
active elements is a function of time, with concentrations and accumula-
tion factors increasing with time in some but reaching a plateau in
others. Increasing the temperature of the medium increases metabolic
rate of insects and facilitates accumulation. The addition of EDTA
complexone to water increased desorption of Ru, Ce, Cs, and Sr in caddis-
fly larvae.
1618.
Ghidalia, W., J.M. Fine and M. Marneux. 1972. On the presence
of an iron-binding protein in the serum of a decapod crusta-
cean [Macropipus puber (Linne)]. Compo Biochem. Physiol.
4lB:349-354.
Two protein fractions in serum of male ~. puber were able to
chelate free Fe. One was a Cu protein, perhaps hemocyanin. The second,
devoid of Cu, had the same electrophoretic mobility on paper as human
transferrin and seemed to be a metal-binding protein.
1619.
Ghiorse, W.C. and H.L. Ehrlich. 1976. Electron transport com-
ponents of the Mn02 reductase system and the location of the
terminal reductase in a marine Bacillus. Appl. Environ.
Microbiol. 31(6):977-985.
Mn02 reduction with glucose by uninduced whole cells and cell
extracts of a marine bacterium, Bacillus 29, was strongly inhibited by
0.1 mM dicumarol, 100 mM azide, and 8 mM cyanide but not by atebrine or
carbon monoxide, suggesting involvement of a vitamin K-type quinone and
a metalloenzyme in electron transport chain. Mn02 reduction with ferro-
cyanide by uninduced cell extracts was inhibited by 5 mM cyanide and 100
mM azide but not by atebrine, dicumarol, or carbon monoxide, suggesting
126
-------
that the metalloenzyme was associated with terminal oxidase activity.
Mn02 reduction with glucose by induced whole cells and cell extracts
was inhibited by 1 mM atebrine, 0.1 mM dicumarol, and 10 mM cyanide but
not by antimycin A, 2n-nonyl-4-hydroxyquinoline-N-oxide (NOQNO),
4,4,4-trifluoro-l-(2thienyl), 1,3-butanedione, or carbon monoxide.
Induced cell extract was also inhibited by 100 mM azide, but stimulated
by 1 mM and 10 mM azide. Induced whole cells were stimulated by 10 mM
and 100 mM azide. Results suggeste~ that electron transport from glu-
cose to Mn02 in induced cells involved such components as flavoprotein,
a vitamin K-type quinone, and a metalloenzyme. Stimulatory effect of
azide on induced cells was explained on the basis of a branching in
terminal part of electron transport chain, one branch involving a
metalloenzyme for Mn02 reduction, and other involving a metalloenzyme
for oxygen reduction. Spectral studies showed presence of a-, b-, and
c-type cytochromes in membrane but not in soluble fractions. Of these
cytochromes, only c type may be involved in electron transport on Mn02,
owing to lack of inhibition by antimycin A or NOQNO. Terminal Mn02
reductase appears to be loosely attached to cell membrane of Bacillus
29 because on cell fractionation it is found associated with both
particulate and soluble fractions. Electron photomicrographs of bacilli
attached to synthetic Fe-Mn oxide revealed an intimate contact of cell
walls with oxide particles.
1620.
Ghiretti-Magaldi, A., A. Giuditta and F. Ghiretti. 1958. Path-
ways of terminal respiration in marine invertebrates. I. The
respiratory system in cephalopods. Jour. Cell. Compo Physiol.
52:389-429.
Octopus Octopus vulgaris, contained iron and copper levels,
in mg/kg dry wt, of 1920 and 2550 for hepatopancreas, 399 and 93 for
branchial heart, 188 and 111 for gill, 160 and 43 for central heart,
112 and 48 for kidney, 47 and 28 for body muscle, and 0 and 2450 for
hemolymph. Further experiments indicate that terminal respiration is
catalysed by Fe but not Cu enzymes.
1621.
Giblin, F.J. and E.J. Massaro. 1975. The erythrocyte transport
and transfer of methylmercury to tissues of the rainbow trout
(Salmo gairdneri). Toxicology 5:243-254.
In vitro studies showed that approximately 3 min after addi-
tion of 5 mg/l Hg as MeHgCl to whole blood, 84% of the Hg was retained
in washed trout red blood cells (RBC). Uptake reached 89% after 1 hr
and remained constant. In vivo, 95% of whole blood Hg was contained in
the soluble contents of the RBC's 2 weeks after an intragastric dose of
MeHg-203Cl at 4 mg Hg/kg body wt. The binding of MeHg was freely
reversible in both. Hemoglobin appeared to be the main MeHg transport
127
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protein in trout blood since it bound 90% of whole blood Hg following
intragastric dose. MeHg, injected intracardially as MeHgS-cysteine was
present in blood and bound almost completely to hemoglobin by 10 days
post-injection, suggesting an ability of hemoglobin to compete for and
bind MeHg bound to other sulfhydryl (SH) compounds. The number of
reactive-SH groups per molecule of trout Hb was determined to be 4. The
concentration of Hb reactive -SH groups in trout RBC was calculated to
be at least 20 roM which accounts for the high affinity of RBC for MeHg.
1622.
Gibson, C.I., T.O. Thatcher and C.W. Apts. 1976. Some effects
of temperature, chlorine, and copper on the survival and
growth of the coon stripe shrimp. ~ Esch, G.W. and R.W.
McFarlane (eds.). Thermal Ecology II. U.S. Energy Res. Dev.
Admin.: 88-92. Available as CONF-750425 from NTIS, U.S. Dept.
Comm., Springfield, VA 22161.
Toxicity bioassays were conducted with the marine shrimp
Pandalus danae, acclimated at 8 C and exposed to CuS04.5H20 at 10, 15,
and 20 C. Mean LC-50 (96-hr) values, in mg Cull, were 0.051 at 10 C,
0.035 at 15 C and 0.037 at 20 C. Net growth of shrimp, of initial size
1-2 g, exposed to various copper concentrations for one month at 16 C
was also determined: average wt gain, in g, was 0.04 at 0.041 mg Cull,
0.12 at 0.009 mg Cull, 0.14 at 0.005 mg Cull and 0.09 at 0.002 mg Cull.
Similar data were collected for selected thermo-chlorine regimens.
1623.
Gilfillan, E. 1972. Reactions of Euphausia pacifica Hansen
(Crustacea) from oceanic, mixed oceanic-coastal, and coastal
waters of British Columbia to experimental changes in tempera-
ture and salinity. Jour. Exp. Mar. BioI. Ecol. 10:29-40.
Euphausids from coastal waters of Saanich Inlet show a
general but small decrease in oxygen uptake with decreased salinity.
~. pacifica can withstand 21%0 S at 5, 10, or 15 C in summer, and
at 5 or 10 C in winter with little reduction in oxygen uptake.
Euphasids from the mixed oceanic-coastal water of Juan de Fuca Strait
showed a slight immediate reduction in 02 uptake with initial dilution
from 34%0 and then no further reduction until a critical low salinity
is reached. The lowest salinities tolerated by Juan de Fuca Strait
euphausids was 240/00. All died at 21%0 when acclimation temperature
was 15 C. Open-ocean euphausids demonstrate independent oxygen uptake
in the salinity range 34 to 24%0. There is an effect in 24%0 at 15 C
and perhaps also at 10 C for winter animals. None survived 21 0/00 S
regardless of temperature of elevation. Only animals from coastal
waters of Saanich Inlet reflected the increased temperature regime from
February to June by a larger increase in respiration between 10 and 15 C
in winter as opposed to summer.
128
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1624.
Glooschenko, W.A. 1969. Accumulation of 203Hg by the marine
diatom Chaetoceros costatum. Jour. Phycol. 5:224-226.
Dividing and nondividing cell populations of C. costatum were
placed in light; nondividing populations were also placed in the dark,
and one population was killed by formalin. No difference in Hg-203
uptake was seen in nondividing cells in the light and in the dark, but
dead cells accumulated about 2 times as much Hg-203 as living cells,
presumably by surface adsorption. Dividing cells in light accumulated
Hg-203 longer than did nondividing cells, suggesting the possibility of
some active uptake of Hg.
1625.
Goettl, J.P. Jr., J.R. Sinley and P.H. Davies. 1973. Study of
the effects of metallic ions on fish and aquatic organisms.
Job Progress Report. State of Colorado Dept. Nat. Res. Job
6 Proj. No. F-33-R-8: 23-115.
On basis of studies reported herein, many of a preliminary
nature, authors recommend that maximum acceptable toxicant concentra-
tions for rainbow trout be set at 135 to 250 ~g/l for Zn, 12 to 19 ~g/l
for Cu, 4 to 8 ~g/l for Pb, and 0.09 to 0.16 for Ag.
Threshold toxicity levels of Pb, Zn, and Cu to stoneflies
Pteronarcys californica, were 19.2, 13.6 and 10.1 mg/l respectively.
LC-50 values of Pb and Cu to mayflies Ephemerella grandis, were 3.5 and
0.2 mg/l, respectively. Both species of insects accumulated these
metals in a predictable manner.
1626.
Goldberg, E.D. 1952. Iron assimilation by marine diatoms.
BioI. Bull. 102:243-248.
Using radioactive iron, author found that Asterionella
japonica utilized only particulate and/or colloidal iron as a growth
nutrient, whereas ionically complexed ferric ion as citrate, ascorbate,
or artificial humate was not available for uptake. A minimal content
of Fe/cell needed for further division was established as 10 x 10-8
uM/l, or 5.6 x 10-9mg/l. The ratio of minimal iron to minimal phos-
phate was determined to be 3.6, which agrees substantially with the Fe/P
ratio in natural plankton samples.
1627.
Goldberg, E.D. 1957. Biogeochemistry of trace metals.
Soc. Amer. Memoir 67(1):345-358.
Geol.
General aspects of chemistry of trace metals in marine life
are discussed including biochemistry of uptake, metal ratios and paleo-
ecological aspects of marine biogeochemistry. From previously published
129
-------
data, author concludes: (1) heavy metals are concentrated by marine
organisms from seawater (2) trace metals are retained by organisms by
strong chemical bonds (3) concentration factors vary between species
and (4) relative concentration factors for metals parallel stability
of metal ions with ligands. Metals discussed include Ca, Sr, V, Y, Ni,
Co, Zn, Ti, Zr, Mg, Cr, Mo, Mn, Fe, Cu, Ag, Au, Cd, Ga, Tl, Ge, Sn, Pb,
As, Sb, Bi, Pd, Ba and Ra. Organisms mentioned include algae, tunicates,
molluscs, coelenterates, sponges, sharks, protozoa, and crustacea.
1628.
Goldberg, E.D. 1962. Elemental composition of some pelagic
fishes. Limnol. Oceanog. 7(Suppl.):72-75.
Concentration sites of fission products encountered when dis-
posing of radioactive wastes were determined in various species of com-
mercially important fishes: albacore, yellowfin tuna Neothunnus macrop-
terus, skipjack tuna, and anchovetta Engraulis ringenus. Manganese, Cu,
Ni, and Zn concentrate in viscera with highest levels, in % composition
of ashed samples, being 0.014, 0.075, 0.24, and 1.04, respectively.
Calcium and Sr accumulate in bone. and cartilage with highest concentra-
tions being 50 and 0.2, respectively. Transition elements were most
abundant in viscera except heart, flesh, and skin (Zr up to 0.27%, Ti
up to 0.032%, and V up to 0.055%); these were least abundant in bony
tissues. Rubidium and Cs were expected to be at least as strongly
assimilated by organisms relative to Na as was K. Concentration levels
for Na, K, P, Mg, Si, AI, Fe, Ba, B, Cr, Pb, Mo, and Ag, as well as
whole animal compositions, are also given.
1629.
Goldberg, E.D. (No publ. date given) Review of trace element
concentrations in marine organisms. Vol. I and Vol. II.
Published by Puerto Rico Nuclear Center, Mayaguez, P.R.
535 pp.
This is a limited distribution edition of an annotated biblio-
graphy of selected technical articles on stable and radiolabelled
species found in marine organisms. Almost all articles were published
between 1958 and 1965. For each article, data are presented in tabular
and graphical form and arranged by element. Elements include AI, As,
Ba, Be, B, Cd, Ca, Ce, Cs, Cr; Co, Cu, Ga, Au, Fe, Pb, Li, Mg, Mn, Mo,
Ni, Nb, Pu, K, Ra,Re, Rb, Ru, Sc, Si, Ag, Na, Sr, Ta, Th, Sn, Ti, W, U,
V, Y, Zn, Zr, Dy, Eu, Ho, La, and Pro
1630.
Goldberg, E.D., W. McBlair, and K.M. Taylor. 1951. The uptake
of vanadium by tunicates. BioI. Bull. 101:84-94.
130
-------
Vanadium contents of California ascidians in mg/kg dry wt
were: 0 for Styella montereyensis and S. bonharti, 475 for Euherdmania
clauiformis, and 100 for Ciona intestinal is. For various body parts of
C. intestinalis, V content in mg V/kg dry wt was 0 for tunic, mantle,
heart, excurrent siphon, esophagus, branchial basket, 76 for ovary, 109
for incurrent siphon, 911 for anterior gut, 178 for posterior gut, and
248 for stomach, leading to a total level of 95 mg V/kg dry wt. V con-
tent of fecal pellets and mature eggs extruded into peribranchial cavity
varied between 0 and 800 mg/kg. In Ascidia ceratodes, phosphate will
inhibit uptake of V. Authors suggest that V in ionic form rather than
colloidal V is adsorbed by tunicates. Dietary requirement of V for
tunicates could be met by direct adsorption of particulates from sea-
water, with an efficiency of assimilation estimated at 2~2% for unfed
animals.
1631.
Gorgy, S., N.W. Rakestraw, and D.L. Fox.
sea. Jour. Marine Res. 7:22-32.
1948.
Arsenic in the
The total arsenic present in seawater varied from 0.2 to 0.5
ug atom/I. Of this, from 50 to 60% is in the form of arsenite, and from
8 to 16% each of arsenate, dissolved organic arsenic, and arsenic in the
suspended particulate matter. The relative proportion of arsenite was
slightly greater in the upper levels. Arsenic content, in mg/kg, for
various species of marine biota were determined: 0.121 wet wt in octo-
pus (tentacles) Octopus bimaculatus; 0.085 wet wt in mussel Mytilus
edulis; 1.26 dry wt in the echinoderm Pisaster ochraceus; and 17.3 dry
wt in brown kelp Macrocystis pyrifera (this is about 1000 X the concen-
tration of As in seawater).
Sea anemones which originally contained 6.6 mg As/kg dry wt
were kept in two aquaria to which increasing amounts of arsenite and
arsenate were added periodically. Individuals were removed occasionally
for analysis; concentration of As increased more rapidly in those
exposed to arsenite. All anemones died after exposure to concentrations
up to 90 ug As3+/l, at which point they contained 21.2 mg As/kg dry wt.
Animals exposed to arsenate concentrations up to 160 ug As+5/l were
alive and contained only 10 mg As/kg. Anemones dying from As+3 exposure
were analyzed for arsenic: 91% of the As was in the protein fraction,
1% in the lipid fraction, and 7% soluble inorganic arsenic.
1632.
Gould, E., R.S. Collier, J.J. Karolus and S. Givens. 1976.
Heart transaminase in the rock crab, Cancer irroratus, exposed
to cadmium salts. Bull. Environ. Contamin. Toxico1. 15:635-643.
Crabs exposed for 4 days to 1 mg/1 Cd2+ as chloride salt
exhibited mean aspartate aminotransferase (AAT) activity in heart muscle
preparation of 2963 units (1 AAT unit ~ change in absorbance of 0.001/
131
-------
min/mg protein); control value was 1784 units. When crabs were exposed
to 1 mg/kg Cd as the nitrate salt, heart AAT was depressed at 1510
units, suggesting that Cd is more toxic as the chloride than nitrat~.
Mean residual AAT activity in frozen and thawed crab heart preparatIons
exposed to 1 mg/l Cd as CdC12 were 64% of original activity while con-
trols and those exposed to 1 mg/l Cd as Cd(N03)2 exhibited 31 and 19%,
respectively.
1633.
Grant, F.B., P.K.T. Pang and R.W. Griffith. 1969. The twenty-four-
hour seminal hydration response in goldfish (Carassius auratus)-
I. Sodium, potassium, calcium, magnesium, chloride and
osmolality of serum and seminal fluid. Compo Biochem. Physio1.
30:273-280.
Spermiation was induced in goldfish by an IP injection of carp
pituitary extract. Seminal fluid levels of major electrolytes were un-
changed from control values, in mg/l, of 2369 for Na, 2153 for K, 68 for
Ca, and 42 for Mg, giving a total osmolality of 289 m Osm/1. Serum from
treated goldfish, however, contained 3333 mg/1 Na and 580 mg/l K and
these were significantly different from control levels of 3255 Na and
77 K. Calcium and Mg values of serum were the same as control levels
of 126 for Ca and 35 mg/1 for Mg. In whole testis, an increase of K
from 34 to 49 g/kg dry wt and Na from 29 to 53 g/kg was greater than
could be accounted for by addition of seminal fluid.
1634.
Gray, J.S. 1974. Synergistic effects of three heavy metals on
growth rates of a marine ciliate protozoan. In Vernberg, F.J.
and W.B. Vernberg (eds.). Pollution and Physiology of Marine
Organisms. Academic Press, N.Y.: 465-485. .
Using factorial experimental designs, the short-term growth
rate of a ciliate protozoan Cristigera was optimum at 270/00 salinity
and 16 C. Significant interaction occurred between salinity and tem-
perature on growth rates. Mercury (HgC12) at a concentration of 0.005
mg/l reduced growth rate by 12%, lead (Pb(N03)2) at 0.3 mg/1 by 11%, and
zinc (ZnS04) at 0.25 mg/l by 14%. On mixing these concentrations,
growth rate was reduced by 67%, whereas on an additive basis 37% was
predicted. Regression equations and graphical response surfaces are
shown for 2 and 3 factor interactions; some interactions were antago-
nistic, others synergistic. Toxic effects were lower, or as low as,
the most sensitive known organisms suggesting Cristigera as a poten-
tially useful test organism. Consideration of adaptation problems,
robustness and ecological roles of organisms, is given in relation to
the selection of species for use in toxicity testing programs.
132
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1635.
Gray, J.S. and R.J. Ventilla. 1971. Pollution effects on micro-
and meiofauna of sand. Marine Poll. Bull. 2:39-43.
Effects of Hg, Pb, and Cu on the bacterivorous sediment-
living ciliate Cristigera was examined. Mercuric chloride was lethal
at 0.02 mg/l.' Lead, as Pb(N03)2, reduced growth rate at >0.3 mg/l but
did not inhibit growth at 0.1 to 0.3 mg/l. Copper had no effect at
2 mg/l, but this was attributed to absence of ionic Cu due to complexion
or chelation with organic matter. Significant interactions between
lead/mercury and copper/mercury imply synergism.
1636.
Green, F.A., Jr., J.W. Anderson, S.R. Petrocelli, B.J. Presley
and R. Sims. 1976. Effect of mercury on the survival,
respiration and growth of postlarval white shrimp, Penaeus
setiferus. Marine Biology 37:75-81.
LC-50 (96 h) value of mercury to shrimp of 17 ug/l was un-
affected by size of shrimp, over range of 7 to 35 mm, or pre-exposure
to 0.5 and 1.0 ug Hg/l for 57 days. Exposure for 60 days to 0.5 and
1.0 ug Hg/l did not affect respiration, growth, or molting rates of
postlarval shrimp.
1637.
Greenaway, P. 1971. Calcium regulation in the freshwater
mollusc Limnaea stagnalis (L.) (Gastropoda: Pulmonata).
Calcium movements between internal calcium compartments.
Jour. Exp. BioI. 54(3):609-620.
II.
Calcium, in g/kg wet wt, of selected tissues were: shell 382,
blood 0.2, total wet tissue 0.9, mantle 2.0, digestive gland 1.5 and
reproductive organs 0.6. Ca-45 absorbed from medium appeared first in
blood, then shell and other tissues; uptake plateaued at 20 hrs for
blood and 30 hrs for total fresh tissue. About 30% of tissue Ca and
about 20% of mantle Ca exchanged with blood Ca; continual exchange
between shell and blood Ca occurred. During net Ca loss from L.
stagnalis, a net movement of Ca from shell to blood occurred at a rate
similar to rate of net loss; a similar pattern was observed during net
Ca uptake.
1638.
Greenaway, P. 1972. Calcium regulation in the freshwater cray-
fish Austropotamobius pallipes (Lereboullet). I. Calcium
balance in the intermoult animal. Jour. Exp. BioI. 57(2):
471-487.
Mean Ca influx and efflux on intermoult crayfish in artificial
tapwater were 0.56 (influx) and 0.92 mg Ca/kg/hr. Ca uptake was against
133
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a small electrochemical gradient; part of influx occurred by.active
transport. Most of Ca loss occurred across gills; urine contribution
was small. Ca-depleted animals showed only a small drop in haemolymph
Ca concentration; Ca uptake was not significantly increased by depletion.
1639.
Greenaway, P. 1974. Total body calcium and haemolymph calcium
concentrations in the crayfish Austropotamobius pallipes
(Lereboullet). Jour. Exp. BioI. 61:19-26.
Variations in concentration of Ca in haemolymph and total body
Ca in crayfish show that haemolymph Ca concentration was independent of
both sex and body size. During premoult, Ca level of haemolymph rose
from 11.8 to 15.0 mM/l. After moult, Ca level remained high during
stages A and B (maximum of 15.6 mM/l, stage A) but declined to the
intermoult level during stage C. Total body Ca was directly proportional
to fresh body wt. Concentration of magnesium in haemolymph varied be-
tween 4.2 to 0.56 mM-Mg/l, and showed little correlation with body wt.
Ratio of total Ca:Mg was 53:1, and exoskeleton Ca:Mg was 44:1, both
largely independent of body size. Haemolymph Ca:Mg ratio did vary with
size, having a mean of 7.8:1. Concentrations of Ca in haemolymph (in
roM/I) of freshwater crustacea, derived from numerous studies, are given
for water Ca levels of 0.038 to 2.75 roM/I: ~. pallipes 6.5 - 18.0,
Astacus astacus 6.5 - 15.2, Orconectes limosus 6.5 - 13.5 (and up to
20.5 mM/kg H20), Potamon niloticus 12.7, Eriocheir sinensis 11.5, and
Gammarus pulex 5.85 - 7.65. The marine crustacea Carcinus had a similar
level of 12.4 mM/l. In contrast, calcium concentrations in haemolymph
of freshwater molluscs was reduced: Limnaea stagnalis 4.9, Anodonta
6.0, and Viviparus viviparus 5.7.
1640.
Greenaway, P. 1974. Calcium balance at the premoult stage of
the freshwater crayfish Austropotamobius pallipes (Lereboullet).
Jour. Exp. BioI. 61:27-34.
The premoult stages are characterized by a net loss of Ca which
increases with development to a maximum of 0.83 ~moles/g/h. Net loss of
Ca in urine at later stages is approximately 0.006 ~moles/g/h, which
represents only a small fraction of observed Ca loss. The concentration
of ionized Ca in haemolymph does not increase during premoult stage
although there is an increase in complexed Ca (7.4 roM/I ionized, 8.8
roM/I complexed). The electrochemical gradient across the body surface
is similar to that at the intermoult stag~ and favors Ca outflux. Possible
routes for Ca net loss are discussed, and a mechanism for elimination
of Ca proposed.
134
-------
1641.
Greenaway, P. 1974. Calcium balance at the postmoult stage of
-the freshwater crayfish Austropotamobius pallipes (Lereboullet).
Jour. Exp. BioI. 61:35-45.
Net uptake of Ca by Austropotamobius begins 15-30 min after
moult and rapidly reaches a maximum (0.08 mg/g/h at 10 C); this is main-
tained throughout stages A and B. At stage Cl rate of net uptake falls
sharply to a lower level which is gradually reduced until equilibrium
is reached at C4' The uptake mechanism is near-saturated at 16 mg-Ca/t
and half-saturated at 5.2 mg-Ca/t. The concentration of ionized Ca in
haemolymph (~280 mg/t) remains unchanged during intermoult cycle, although
level of non-ionized Ca is greater during stages D4 and Al (~560 mg/t)
than at other stages. In absence of external HC03-' net uptake is
reduced by 60%; uptake in the remaining 40% proceeds through use of
metabolic C02'
1642.
Greenaway, P. 1976. The regulation of haemolymph calcium con-
centration of the crab, Carcinus maenas (L.). Jour. Exp.
BioI. 64:149-157.
Carcinus was able to maintain Ca balance after acclimation in
dilute seawater (35-100%), but not in low calcium seawater. Of total
haemolymph Ca (9.54 mM), 71% was ionic as compared to 91% (9.9 mM) in
seawater. On acclimation to dilute seawater, Ca activity of haemolymph
was greater than medium, the difference bein~ maintained by active Ca
uptake. Carcinus is highly permeable to Ca2 , influx from seawater
being 0.513 ~moles/g/h and time constant for Ca influx 4.3 hr. Ca space
represented ~25% wet body wt independent of body size or salinity of
acclimation medium.
1643.
Greenfield, S.S. 1942. Inhibitory effects of inorganic com-
pounds on photosynthesis in Chlorella. Amer. Jour. Bot. 29:
121-131.
Under light intensity of 22,000 lux, photosynthesis in ~.
~u1garis was inhibited 50% by 0.0008 g/l CUS04, 31 g/l COS04, 32 g/l
ZnS04, 53 g/l KCl, and 119 g/l NiS04' These concentrations did not
produce residual effects on growth when cells were transferred to a cul-
ture medium. Photosynthesis inhibition by MgS04, MnS04 or KN03 occurred
at concentrations which caused osmotic stress. Treatment with 6.8 mg
HgC12/l completely inhibited photosynthesis but 2.7 mg HgC12/1 had no
effect; 27 mg HgC12/l impaired apparent health for 3 days after innocu-
lation into culture medium. Only the dark reaction was retarded by ZnS04,
NiS04, and KCl. Effect of CUS04, H3B03, and KI was retardation of dark
reaction and a lesser inhibition of the light stage; COS04 depressed both
the dark and photochemical stages of photosynthesis.
135
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1644.
Greenwald, L., L.B. Kirschner, and M. Sanders. 1974. Sodium
efflux and potential differences across the irrigated gill of
sea water-adapted rainbow trout (Salmo gairdneri). Jour. Gen.
Physiol. 64:135-147.
Sodium extrusion and potential difference (TEP) were measured
across gills of seawater-adapted trout using a gill-irrigation system of
small volume. Na efflux was usually between 100-250 ~ eq/lOOg/h, 10 X
faster than freshwater-adapted trout, but slower than reported for any
other marine teleost. When the external medium was changed from SW to
FW Na efflux was reduced to about 25% of initial value, and TEP was
reduced by 40-50 mV. Addition of either Na+ or K+ in SW concentrations
reversed the changes; Na efflux increased and the gill repolarized.
Electrical behavior and Na efflux in irrigated trout gill is the same as
reported for unanaesthetized free-swimming fish of other species. Thus,
irrigated gill provides an adequate model for studying mechanisms of Na
extrusion in marine teleosts.
1645.
Greig, R.A. 1975. Comparison of atomic absorption and neutron
activation analyses for determination of silver, chromium and
zinc in various marine organisms. Anal. Chern. 47:1682-1684.
Neutron activation analyses and atomic absorption were used
to determine Ag, Cr and Zn levels in marine biota. Silver concentration,
in mg/kg wet wt ranged from 0.39 to 1.3 in muscle of surf clam Spisula
solidissima; 0.21 in muscle to 6.3 in digestive diverticulum of rock
crab Cancer irroratus; 0.53 in gills to 32.0 in digestive diverticula
in channeled whelk Busycon canaliculatum; 0.37 to 0.54 in muscle of
lobster Homarus americanus; and 0.18 to 0.32 in liver of white hake
Urophycis tenuis. Silver concentration in zooplankton ranged from 1.1
to 3.1 mg/kg dry wt. Chromium concentration, in mg/kg wet wt, ranged
from 0.22 to 0.68 in muscle of summer flounder Paralichthys dentatus;
0.24 in dig. div. to 4.2 in gills of channeled whelk; 0.74 to 2.7 in
muscle of surf clam; and 0.20 to 0.59 in liver of white hake. Concen-
tration of Cr in plankton ranged from 0.48 to 53.0 mg/kg dry wt. Zinc
concentration, in mg/kg wet wt, ranged from 2.9 to 3.8 in muscle of
white hake; 4.2 to 4.4 in muscle of yellowtail flounder Limanda
ferruginea; 23 to 28 in muscle of windowpane flounder Scopthalmus
aquosus; 35 to 43 in digestive diverticulum of rock crab; and 25 in
muscle to 2600 in dig. div. of whelk.
1646.
Greig, R.A., B.A. Nelson and D.A. Nelson. 1975. Trace metal
content in the American oyster. Marine Poll. Bull. 6:72-73.
Two groups of Crassostrea virginica containing significantly
different levels of copper and cadmium were induced to spawn. Eggs from
136
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both groups contained the same amount of Cu at 27.8 and 28.9 mg/kg dry
wt; in both groups Cd content was below detectable limits of <1.6 mg/kg
dry wt. These similar concentrations suggest that amount of metal trans-
ferred from adult to egg is fairly constant and not dependent on level
available in adults. Silver, lead and zinc concentrations were also
determined; levels of these metal~ were similar for adult and eggs of
the two groups examined.
1647.
Greig, R.A., D.R. Wenzloff, and J.B. Pearce. 1976. Distribution
and abundance of heavy metals in finfish, invertebrates and
sediments collected at a deepwater disposal site. Marine
Poll. Bull. 7:185-187.
Concentrations were determined of Ag, As, Cd, Cr, Cu, Hg, Ni,
Pb and Zn in 4 species of deepwater demersal finfish, one species of
benthic invertebrate (red crab Geryon quinquedens), and 3 species of
pelagic fish collected from the area of a deepwater disposal site in the
New York Bight. Highest values of Cd, Cu, Ni, Pb and Zn were in livers
of Nematonurus armatus at 1.3, 4.8, 0.8, 1.6 and 50.0 mg/kg wet wt,
respectively. Highest values of Ag, As and Hg were in muscle of Antimora
rostrata at 0.1, 21.1 and 0.6 mg/kg wet wt, respectively. The highest
value of Cr at 1.1 mg/kg wet wt was in liver of Holosauropsis macrochir.
These 3 species are generally regarded as bottom dwellers. Comparison
of metal content of red crah with coastal green crab Carcinus rnaenas,
showed that Ni was significantly higher in Carcinus but other metals
were the same. Comparison of Hg content in deepwater fish taken off
Cape Hatteras with one collected 90 years previously showed no signifi-
cant variations with area or time, suggesting that other metal levels
are normal for this group. Deepwater bottom dwelling teleosts when com-
pared to fish species collected from the continental shelf contain lower
overall metal content in muscle and liver.
1648.
Greig, R.A., D. Wenzloff and C. Shelpuk. 1975. Mercury concen-
trations in fish, North Atlantic offshore waters--197l.
Pestic. Monit. Jour. 9:15-20.
Mercury concentrations in muscle of 41 spe~ies of fish and
elasmobranchs collected from North Atlantic offshore waters in 1971
ranged from <0.05 to 0.35 mg/kg wet wt, with an average of 0.154 mg/kg.
Fish liver Hg concentrations ranged from <0.05 to 0.42 mg/kg wet wt.
Mercury levels in the 9 plankton samples taken were less than 0.05 mg/kg
wet wt. Mercury concentrations in lobster Homarus americanus were 0.31
and 0.60 mg/kg in muscle and live~ respectively. Mercury content was
<0.05 to 0.06 mg/kg in whole squid Illex illecebrosas, and <0.05 in
edible muscle of scallops Placopecten magellanicus.
137
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1649.
Griffith, R.W. 1974. Environment and salinity tolerance in the
genus Fundulus. Copeia (2):318-331.
A comparison was made of environmental salinities, ability to
survive in freshwater and upper salinity tolerance for over 20 species
of the teleost genus Fundulus. All species occur, at times, in fresh-
water and are able to survive in this medium in the laboratory. Species
found in brackish environments have upper salinity tolerances ranging
from 74-1140/00, while most species characteristic of freshwaters are
unable to survive in salinities above 290/00. Notable exceptions are
F. zebrinus, an inland species commonly found in saline waters; f.
diaphanus, a freshwater form which often enters dilute brackish
estuaries; and F. waccamensis, a Pleistocene lacustrine derivative of
f. diaphanus. Since brackish-water species are tolerant of life in
freshwater while the reverse is not the case, it is suggested that fresh-
water species of Fundulus were derived from fully euryhaline ancestors
which gradually lost ability to live in seawater during extended isola-
tion from brackish or marine environments.
1650.
Griffith, R.W., M.B. Mathews, B.L. Urnrninger, B.F. Grant, P.K.T.
Pang, K.S. Thomson and G.E. Pickford. 1975. Composition of
fluid from the notochordal canal of the coelacanth, Latimeria
chalumnae. Jour. Exper. Zool. 192:165-172.
Notochordal canal fluid of Latimeria was analyzed for major
inorganic and organic constituents and compared with blood serum from
the same fish. Lower levels of Na, Mg, Ca, bicarbonate, sulfate, total
carbohydrates, glucose, lactate, cholesterol, bound phosphate and total
proteins were found in notochordal fluid than in serum, whereas K,
chloride, urea, trimethylamine oxide, and total free amino acids were
higher and inorganic phosphorus essentially identical. Osmolarity of
notochordal fluid (1058 mOsm) exceeds that of serum (942 mOsm). A 0
whitish precipitate in the fluid consisted of a matrix of fibers 100 A
in diameter and of indefinite length. It resembled a sialoglycoprotein
in composition and was stabilized by disulfide bonds. The fluid con-
tained cellular debris.
1651.
Griffith, R.W., B.L. Urnrninger, B.F. Grant, P.K.T. Pang, L.
Goldstein and G.E. Pickford. 1976. Composition of bladder
urine of the coelecanth, Latimeria chalumnae. Jour. Exp.
Zool. 196:371-380.
Inorganic cation levels of urine from bladder of a live
Latimeria were compared with serum levels from same fish. Content in
urine in mg/l, was 4209 for Na, 330 for K, 66 for total Ca, and 727 for
Mg. Osmolarity is identical in serum and urine. Mg, P04, S04, creatine,
138
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creatinine and glucoronate were highly concentrated in urine; Cl-,
bicarbonate, protein and glucose were lower in urine than in serum.
Total Ca levels in urine were less than serum total Ca. Urea levels
were identical in both fluids.
1652.
Griffith, R.W., B.L. Umminger, B.F. Grant, P.K.T. Pang and G.E.
Pickford. 1974. Serum composition of the coelacanth,
Latimeria chalumnae Smith. Jour. Exp. Zool. 187:87-102.
Blood serum from a living coelacanth contained 6300 mg Na/l,
235 mg K/l, 127 mg Mg/l, and 198 mg Call. Cl-, HC03-, P04, S04, and
organic concentrations were also determined. Osmolarity of serum (932
mOsm/l) was lower than seawater (1035 mOsm/I), indicating that coela-
canths are hypoosmotic to medium in contrast to elasmobranchs, holo-
cephalians and hagfish. Evolutionary implications of Latimeria serum
chemistry to that of other marine fishes are discussed.
1653.
Gromov, V.V. and V.I. Spitsyn. 1974. Assimilation of plutonium,
ruthenium and technetium by phytoplankton. Acad. Sciences
USSR, Hydrobiology 215(1):214-217.
Accumulation of Pu-239, Ru-l06, and Tc-99 by the marine green
algae Platymonas viridis was observed under different conditions of
illumination during a 6-day period. There was little or no accumulation
of Tc-99 under the conditions of this study. On a live wt basis Ru was
accumulated to a greater degree than Pu (40% of total isotope available
vs 16%). Similar results were obtained with mixed phytoplankton cul-
tures; uptake of both was apparently unaffected by light intensity.
1654.
Gromov, V.V. and V.I. Spitsyn. 1974. Influence of ~hytoplankton
on the physicochemical state of pu239, Rul06, Tc9 , and C060
in seawater. Acad. Sciences USSR, Hydrobiology 215(2):451-453
(Doklady BioI. Sci. 215:151-153).
Effect of Platymonas viridis on sorption properties of Pu-239.
Ru-l06, Tc-99 and Co-60 by deep water red clays was studied. Sorption
is reduced by factors of about 3000 for Pu-239, 2500 for Ru-l06, 15 for
Tc-99 and zero for Co-60. Sorption of all isotopes was inversely
related to particle size (surface area) of adsorbing substrate.
1655.
Gross, R.E., P. Pugno and W.M. Dugger. 1970. Observations on the
mechanism of copper damage in Chlorella. Plant Physiol. 46:
183-185.
139
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Addition of excess copper (about 63 mg/l Cu) to non-growing
cells of a normal green alga caused reduction in total pigments and
inhibition of photosynthesis. Within 5 to 10 min after addition of
6 mg/l CUS04, chlorophyl~lessyellow and white mutant strains of t~e
same alga showed a rise in non-specific absorption and a decrease ln
packed cell volume. Respiration rose from 3.6 to 7.9 ul 02/mg dry wt/hr
in the yellow strain. Glutathione prevented all copper-induced changes,
whereas MnC12 protect~d only partially. Selective inhibition of some
responses to copper was observed when 02 was absent or antitoxicants
present.
1656.
Gross, W.J. 1957. An analysis of response to osmotic stress in
selected decapod crustacea. BioI. Bull. 112:43-62.
Emerita, Callianassa, Upogebia, Cancer antennarius, ~. gracilis
and Pugettia cannot regulate osmotically and from lack of tolerance are
generally stenohaline. Pachygrapsus, Birgus, Hemigrapsus and Uca can
regulate osmotically in concentrated and dilute seawater. Hemigrapsus
is the weakest hypoosmotic regulator of the 4 species, able to regulate
up to 33% for 20 hours in 150% SW. Where osmotic regulation occurs, it
is established immediately and sustained perfectly in moderate stresses
(75% to 125% SW) for a few hours. Regulation diminishes gradually until
equilibrium blood concentration is reached ($24 hrs). Fluctuations
occasionally occur later when extreme stresses are imposed. Solute
space volumes were calculated as 40% for Emerita, 54% for Pachygrapsus,
and 50% for Birgus. Concentration changes occurring in blood of Pachy-
grapsus and Emerita are caused by salt more than by water exchanges.
There is a dynamic flux of salt and water in gill chambers of Pachygrapsus,
furnishing further evidence that gills are osmo-regulatory organs.
Osmotic regulating crustaceans Cambarus, Pachygrapsus, ~. nudus, and ~.
oregonensis have exoskeletons 1/3 less permeable than the non-regulators,
Cancer gracilis, ~. antennarius and Pugettia. Pachygrapsus, Uca, ~. nudus and
oregonensis sustain greater osmotic gradients when greater osmotic
stresses are imposed, the gradient between blood and external medium
being 45-50% SW when medium concentration is 25% SW. Two species of
Hemigrapsus are weak regulators in small stress (>75% SW) but osmo-
regulatory behavior increases as stress does. A sensitivity to absolute
salinities is suggested. Consumption of 02 by Uca in 50% SW was 108% of
that in 100% SW, and in' tap water it was about 135% of the amount of 02
consumed in 100% SW. Author noted that increases in metabolism were not
direct reflections of increased osmotic work but of muscular activity
due to resistance to osmotic stress.
1657.
Gryzhankova, L.N., G.N. Sayenko, A.V. Karyakin and N.V. Laktionova.
1973. Concentration of some metals in the algae of the Sea of
Japan. Oceanology 13:206-210.
140
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Metal levels, in mg/kg dry wt, of 9 species of red and brown
algae ranged from 189 to 886 for Fe, 16 to 455 for Mn, 2 to 7 for Cu,
8 to 27 for Ni, 2 to 147 for Co, 5 to 147 for Ti, 4 to 24 for V, and
2 to 14 for Cr. For 3 species of green algae, metal contents were 82 to
596 for Fe, 5 to 805 for Mn, 3 to 8 for Cu, 5 to 31 for Ni, 2 to 31 for
Co, 1 to 41 for Ti, 4 to 21 for V, and 1 to 6 for Cr.
1658.
Guary, J.-C., M. Masson and A. Fraizier. 1976. Etude pre-
liminaire, in situ, de 1a distribution du plutonium dans
differents tissus et organes de Cancer pagurus (Crustacea:
Decapoda) et de P1euronectes p1atessa (Pisces: P1euronectidae).
Marine Biology 36:13-17. (In French, English summary)
Plutonium levels in pCi/kg wet wt of crab were 102 for gills,
2.2 for exoskeleton, 0.5 for meat, 0.5 for gonads, 0.4 for remainder,
1.9 for hepatopancreas, 2.2 for gastro-intestina1 tract, 0.3 for hemo-
lymph, with a whole organism value of 3.5. P1aice~. p1atessa levels
in pCi/kg wet wt, were 2.3 for gills, 0.6 for skin, 64.2 for gastro-
intestinal tract, 0.5 for liver, 2.9 for spleen, 2.2 for kidney, 0.9
for gonads, 0.1 for meat, 0.1 for remainder, with a whole organism value
of 3.1. Data indicate contamination of crab by surface absorption of
gills and exoskeleton; in plaice, feeding processes are implicated.
Authors conclude that edible parts of these species, particularly the
flesh, do not constitute an important source of Pu contamination to man.
1659.
Guegueniat, P., P. Bovard, and J. Ance11in. 1969. Influence de
1a forme physico-chimique du ruthenium sur 1a contamination
des organismes marins. C.R. Acad. Sci. Paris, t. 268:976-979.
Nitrosyl-ruthenium compounds produced by irradiated waste
treatment reclamation and subsequently discharged into marine environ-
ments are either soluble, insoluble or "intermediate"-the exact per-
centages vary according to the quantity of suspended materials in water.
Field studies with marine algae (Chondrus crispus, Coral1ina officinalis).
coelenterates (Actinia equana), molluscs (Mytilus), and crustaceans
(Leander serratus) suggest that particulate ruthenium species are taken
up in greatest concentration. For example, algae exhibit concentration
factors between 750 and 3000 for particulate Ru, and 80 to 120 for
soluble forms.
1660.
Gunter, G. 1955. Mortality of oysters and abundance of certain
associates as related to salinity. Ecology 36:601-605.
Author concludes that number of species of marine animals
declines along salinity gradients towards freshwater, and that
141
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comparatively high oyster mortality observed at higher salinities were
due to greater incidence of predation and parasitism.
1661.
Gunter; G. 1967. Vertebrates in hypersaline waters.
Inst. Mar. Sci. Univ. Tex. 12:230-241.
PubIs.
Hypersaline areas, including lagoons, pools and shore ponds,
and salt flats or salinas, occur only along sea coasts in arid or semi-
arid zones, and have salinities ranging from 45 to 206%0. Brine
flies Ephydra, are found in waters up to 140 and 150%0, a few fish
can survive at 100%0, and Cyprinodon variegatus, a euryhaline teleost,
has been recorded at 142%0. Fauna of hypersaline lagoons is pre-
dominantly derived from nearby brackish waters rather than the sea.
1662.
Hagen, A. and A. Langeland. 1973. Polluted snow in southern
Norway and the effect of the meltwater on freshwater and
aquatic organisms. Environ. Poll. 5:45-57.
In polluted snow and ice-trapped and surface water of southern
Norwegian lakes and brooks, maximal metal contents, in ug/l, were: Cd
10; Cu 15; Pb 77; Zn 120; Fe 180; Ca 1300; Mg 700; and Mn 35. In some
cases pH values near 3.34 were observed; in those instances bottom
fauna, consisting mostly of chironomids, were depleted. Authors con-
cluded that high Zn levels and low pH are also potentially hazardous to
fishes.
1663.
Hagiwara, S., H. Hayashi and K. Takahashi. 1969. Calcium and
potassium currents of the membrane of a barnacle muscle fibre
in relation to the calcium spike. Jour. Physiol. 205:115-129.
Membrane currents in giant muscle fiber of Balanus nubilus
are composed of two components: an early transient current, and a late
outward component. Early transient current consists of two parts: an
inward current, carried by Ca ions and suppressed by conditioning
depolarization, cobalt ions, and decreased external Ca level; and an
outward current, carried by K ions, and suppressed by procaine, but not
by conditioning depolarization or decreased external Ca levels. Authors
concluded that early conductance increase of muscle fiber membrane
occurred only with Ca but not K, although membrane potential at spike
peak was determined by both.
1664.
Hajj, H. and J. Makemson. 1976. Determination of growth of
Sphaerotilus discophorus in the presence of manganese.
Appl. Environ. Microb. 32:699-702.
142
-------
Cultures of Sphaerotilus, a filamentous bacteria, to which
0.005% MnS04 was added, exhibited reduced growth and biomass when com-
pared to controls. Manganese oxidation occurred only during the latter
portion of logarithmic growth and into the stationary phase.
1665.
Hall, J.W., J.C. Arnold, W.T. Waller, and J. Cairns, Jr. 1975.
A procedure for the detection of pollution by fish movements.
Biometrics 31:11-18.
An "alarm" system using fish movement has been developed to
provide rapid information concerning accidental spills of pollutants.
Statistics used to transform data of a non-stationary stochastic pro-
cess to a stationary one are given. Using Zn as the pollutant, tests
indicate that bluegill sunfish Lepomis macrochirus, will show abnormal
behavior patterns within 6 hrs at 13.32 mg/l, but not for 80 hrs at
3.65 mg/I.
1666.
Hara, T.J., Y.M.C. Law and S. MacDonald. 1976. Effects of
mercury and copper on the olfactory response in rainbow trout,
Salmo gairdneri. Jour. Fish. Res. Bd. Canada 33:1568-1573.
Lowest concentrations of mercury as HgC12, and copper as
CUS04, that depressed electrical response of trout olfactory bulb to
stimulant L-serine within 2 hrs were 0.1 mg Hg/l and 0.008 mg Cull.
Depression increased with increase in concentration of Cu and Hg, and
with exposure time. Recovery was slower with higher concentrations
and longer exposure.
1667.
Harriss, R.C. 1971. Ecological implications of mercury pollu-
tion in aquatic systems. Biological Conservation 3:279-283.
Sources and effects of mercury pollution in aquatic systems
are reviewed. In experimental ponds, algae had concentration factors
of 200-1200; large plants, 4-2400; invertebrates, 400-8400, and pike in
natural waters had CF of 3000. Biomagnification in upper trophic
levels is shown in Great Lakes where plankton-feeding fish had levels
of Hg from 0.2 to 1.0 mg/kg; top predators, such as walleye, pike and
white bass had levels from 1.0 to 2.0 mg Hg/kg. Waterfowl and other
fish-eating animals contained up to 20 mg Hg/kg. Low-level Hg pollu-
tion may not kill macrofauna, but may seriously deplete planktonic food
supply. Organomercury compounds reduced photosynthesis in the marine
diatom Nitzchia delicatissima to less than 10% of controls after 24 hr
exposure to 0.01 mg/l. These low levels can eliminate plankton with
subsequent emigration or death of fish. Behavioral, physiological,
genetic and synergistic effects, and need for environmental standards
are also discussed.
143
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1668.
Harza, T. and L. Matyas. 1976. Seasonal variations of sodium and
potassium concentrations in different parts of the frog myo-
cardium. BioI. Bull. 151:306-313.
Respective mean Na and K concentrations, in g/kg wet wt, in
heart of frog Rana esculenta, were 2.4 and 0.9 for sinus venosus, 1.7
and 1.1 for atrium and 1.2 and 2.2 for ventricle. Na concentrations
varied seasonally; differences between minimum (in winter) and maximum
(in summer) values representing 46% (sinus venosus), 30% (atrium), and
34% (ventricle) of spring-autumn values. Although K level in ventricle
declined in the second half of the year, other portions of the heart
showed no variation with respect to K.
1669.
Hassall, K.A. 1963. Uptake of copper and its physiological
effects on Chlorella vulgaris. Physiologia Plantarum 16:323-
332.
Effects of salts of Ba, Mg, AI, Mn, Zn, Ni, Pb, Fe, Cu, Hg,
Ag and Au, upon growth and respiration of f. vulgaris were studied.
Significant toxic effects, as % respiration of untreated cells 3 to 5
hrs after addition, were exhibited by Cu at 7 X 10-2M CUS04 with 97% and
8% respiration in aerated and unaerated flasks. Mercury at 3 X 10-4M
HgC12 showed 10% and 5% respiration (aerated and unaerated); Ag at 2 X
10-4M AgN03 showed 15% and 14% respiration (aerated and unaerated); and
Au at 2 X 10-3 NaAuC14 showed 65% and 2% respiration (aerated and un-
aerated). Copper was unique in that it was highly toxic when applied
under anerobic conditions, but seldom reduced respiration at high concen-
trations in aerated vessels. Comparison of rates of uptake of copper by
living and previously scalded cells, show that dead cells absorb copper
extremely rapidly, but that total sorbed is same as when copper itself
kills cells by prolonged anaerobic contact. Two-thirds of the copper is
firmly retained, even by dead cells, and resists removal by washing.
Cells supplied with glucose as energy source grow in higher copper con-
centrations than cells relying upon photosynthesis.
1670.
Hassall, K.A. 1967. Inhibition of respiration of Chlorella
vulgaris by simultaneous application of cupric and fluoride
ions. Nature 215:521.
In algae C. vulgaris, an alternate respiratory pathway
induced by fluoride blockage of the main route was inhibited by ~ 12.7
mg Cull.
144
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1671.
Hassall, K.A. 1969. An asymmetric respiratory response occurring
when fluoride and copper ions are applied jointly to Chlorella
vulgaris. Physiologia Plantarum 22:304-311.
Algal suspensions, when treated simultaneously with 10-2 M
CUS04 and 4 X 10-2 M NaF, almost completely cease respiring though the
two ions individually have little inhibitory effect. If cells are pre-
treated with CUS04 before adding NaF, inhibition of respiration becomes
more severe as pretreatment time is lengthened, except at high Cu levels
which alone inhibit respiration. When pretreatment is with F ions,
inhibition becomes less as pretreatment time is lengthened, with no
inhibition at 90 min. In absence of F, Cu content of cells after contact
with 9.6 X 10-3 M CUS04 was 5.2 mg/kg dry wt of cells in 5 hrs, less than
half that absorbed by cells pretreated with Cu or by cells pretreated
with F, which indicates cause cannot be ascribed to differences in rate
of Cu uptake. Author suggests that F blocks main respiratory pathway
and Cu blocks the hexose monophosphate shunt.
1672.
Haug, A., S. Melsom and S. Omang. 1974. Estimation of heavy
metal pollution in two Norwegian fjord areas by analysis of
the brown alga AscophyllUIT nodosum. Environ. Poll. 7:179-192.
Concentrations, in mg/kg dry wt, in algae from Reine in Lofoten,
a relatively unpolluted region, ranged from 60 to 110 for Zn, 4 to 8 for
Cu, <3 for Pb, <0.7 for Cd, and 0.05 to 0.08 for Hg. Levels in mg/kg
dry wt of algae from metals-impacted Trondheimsfjord ranged from 66-640
for Zn, 4 to 240 for Cu, <3 for Pb, <0.7 to 1.0 for Cd, and 0.05 to 0.18
for Hg. Cu and Zn contents increased with increasing age of vegetative
tissue, but no pronounced seasonal variation was observed. Algae from
the polluted Hardangerfjord contained, in mg/kg dry wt, 240 to 3700 of
Zn, 3 to 160 of Cu, <3 to 95 of Pb, 0.7 to 16 of Cd, and 0.05 to 20 of
Hg; Zn, Cd and Hg levels were elevated in algae collected 90 km from
the main source, but Cu and Pb levels were normal 35 km from source.
Authors suggest that analysis of seaweeds is a useful and inexpensive
method for evaluating metal contamination.
1673.
Haug, A. and O. Smidsrod. 1967.
of alginates. Nature 215:757.
Strontium-calcium selectivity
Using alginates of Laminaria digitata and ~. hyperborea, the
latter was found to be more efficient in reducing Sr uptake from the
diet due to its larger content of guluronic acid residues.
145
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1674.
Healy, W.B., S. Cheng, and W.O. McElroy. 1955. Metal toxicity
and iron deficiency effects on enzymes in Neurospora. Arch.
Biochem. Biophys. 54:206-214.
Optimal growth rate for the fungi N. crassa occurred at 0.3 mg
Fe/I; growth was reduced 50% by addition, in mg/l, of 200 Cu, 950 Mn,
3500 Mo, 500 Zn, 100 Co, or 150 Ni. Of these, only Co addition produced
effects similar to Fe deficiency, as determined by activities of cyto-
chrome oxidase, catalase, peroxidase, and succinic dehydrogenase enzyme
systems known to contain Fe. Co toxicity and Fe deficiency also pro-
duced similar effects on the activities of nitrate reductase, "glucose
6-phosphate dehydrogenase," isocitrate dehydrogenase, DPNase, and alka-
line phosphatase enzyme systems not known to involve Fe. Increased Fe
levels may partially offset the effects of Co toxicity on catalase and
peroxidase. Authors suggest that Co competes with Fe.
1675.
Heisinger, J.F. and W. Green. 1975. Mercuric chloride uptake
by eggs of the ricefish and resulting teratogenic effects.
Bull. Envir. Contamin. Toxicol. 14(6):665-673.
Zygotes collected from adult Oryzias latipes were incubated
for 16 days in solutions containing 10, 15, 20, or 30 ug/l of Hg. Mean
hatchability of controls was 46.7%. Experimentals incubated in 10 and
15 ug/l Hg had hatching percentages of 58.3 and 20.8, respectively;
there was no hatch at 20 or 30 ug/l Hg. Hemorrhaging, blood vessel
deterioration and loss of blood cells were observed in 79% of embryos
in 15 ug/l; this was 100% at 20 and 30 ug/l. Neither controls nor
those in 10 ug/l demonstrated any of these abnormalities. LC-100 (384 h)
was between 20 and 30 ug/l; the LC-50 (16 days) value lies between 10
and 15 ug/1. Concentration factors for zygotes in 10, 15, 20, and 30
ug/1 solutions were 1600, 19,000, 27,000, and 19,000 X, respectively;
Hg residues after 16 days, in mg/kg, were 16, 29, 54, and 56, respec-
tively.
1676.
Held, E.E., V.A. Nelson, W.R. Schell and A.H. Seymour. 1973.
Amchitka radiobiological program progress report. March 1972
to December 1972 (NVO-269-l9). Univ. Washington, ColI. Fish.,
Lab. Radiat. Ecol., Seattle, Wash. 92 pp.
The present program was initiated in July 1970 at the request
of the U.S. Atomic Energy Commission. It was designed to provide a
periodic documentation of radionuclides, both naturally occurring and
man-made, in biological and environmental samples from Amchitka and its
environs (Aleutian chain). Seafoods and radionuclides potentially
~vailable to man through the food web were emphasized. However, organ-
Isms other than food organisms were also collected and analyzed in a
146
-------
search for indicator organisms (species that significantly concentrate
one or more radionuclides). Concentrations of radionuclides other than
those potentially hazardous to man were measured as a means of providing
clues to the origin of radionuclides at Amchitka. Unexpected combina-
tions or concentrations of radionuc1ides would indicate the presence of
newly added radionuclides to the environment, presumably from fresh
world fallout, nuclear-powered vessels, or from nuclear detonations at
Amchitka Island.
The first progress report covered the period July 1970 to
April 1971. It concluded that artificial or man-made radionuclides did
not originate at Amchitka except for tritium which had previously been
reported to be present in pond water and test holes near devices deto-
nated in 1965 and 1969. A second progress report covered the period
May 1971 to February 1972 and concluded that there was no release of
radioactivity as a result of a third test. This report extends the
account of the program through 1972. It includes analyses for: gamma-
emitting radionuclides (K-40, Co-60, Zr-95, Nb-95, Ru-l06, Sb-125, Cs-
137) in air filters, seawater, freshwater, marine algae, marine inverte-
brates, marine fish, sea otter, and freshwater aufwuchs, moss, plants,
and fish; strontium-90 in rats and birds; and tritium in seawater, fresh-
water and fish. Tables from the previous reports were revised recalcu-
lating values for zirconium-95 and niobium-95 and adding data for
beryllium. The results of the recent analyses indicate that no new
radionuclides are present. The most abundant radionuclides are naturally
occurring Be-7 and potassium-40. Trace quantities of fission products,
induced radionuclides and H-3 present are from world fallout, and a
trace of H-3 contamination remains in some ponds as previously reported.
It is concluded that there were no radionuclides of detonation origin
in water, plants, and animals of Amchitka Island.
1677.
Heneine, I.F., G. Gazzinelli and W.L. Tafuri. 1969. Iron
metabolism in the snail Biompha1aria glabrata: Uptake,
storage and transfer. Compo Biochem. Physiol. 28:391-399.
After exposure to 0.02 mCi Fe-59/l for 120 hrs, Fe-59 distri-
buted in tissues of B. glabrata as follows: 45% hepatopancreas, 13%
ovotestis, 4% mantle~ 2% albumen gland, 4% digestive gland, 0.4% male
genitalia, 0.7% female genitalia, 9% kidney, 0.4% central nervous
system, and 22% in cephalopodal mass. Fe-59 was taken up directly by
hepatopancreas and transferred to ovotestis. Ferritin, hemosiderin or
both were present in hepatopancreas and ovotestis. It was concluded that
hepatopancreas is an active metabolic storage depot for Fe.
1678.
Heslinga, G.A. 1976. Effects of copper on the coral-reef
echinoid Echinometra mathaei. Marine Biology 35:155-160.
147
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Effects of copper-enriched seawater on fertilization success,
early cleavage, larval skeletal development, and survival of adult ~.
mathaei were tested. Fifty percent reduction of fertilization success
occurred at 0.18 mg Cull; for 50% cleavage success to the 8-cell stage
this was 0.42 mg Cull. Adults had respective 48- and 96-hr LC-50
values of 0.54' and 0.30 mg/l. Larval skeletal development was
suppressed in 0.02 mg/l. The latter process appears to be very sensi-
tive and may be most suitable for assessing effects of stress on this
species.
1679.
Hessler, A. 1974. The effects of lead on algae. I. Effects of
Pb on viability and motility of Platymonas subcordiformis
(Chlorophyta: Volvocales). Water, Air, and Soil Poll. 3:371-
385.
Effects of lethal and sublethal concentrations of PbC12 on
reproduction, viability, and motility of a marine unicellular green
flagellate alga were studied under controlled laboratory conditions.
Severity of effects depended primarily upon Pb concentration and dura-
tion of treatment. Log phase cells were more sensitive than stationary
phase cells. Sublethal amounts of Pb (2.5 and 10 mg/l Pb) tended to
retard population growth by delaying cell division and daughter cell
separation; higher levels (60 mg/l Pb) caused growth inhibition and
death. Various intracellular abnormalities resulted from Pb treatment:
flagella were shed or altered in a variety of ways, depending on Pb
concentration; motility was least affected by low Pb and completely
impaired by high Pb; normal wild-type cells appeared to be more sensi-
tive to Pb than mechanically sheared (flagella-less) cells, and cells
of a non-flagellate mutant of Platymonas. Exposure of cells to Pb in
non-growth conditions of dark and cold (2 C) had little negative effect.
1680.
Hessler, A. 1975. The effects of lead on algae. II. Mutagenesis
experiments on Platymonas subcordiformis (Chlorophyta: Volvo-
cales). Mutation Res. 31:43-47.
Under conditions in which two known mutagenic agents, ultra-
violet irradiation and nitrosoguanidine, induced high proportions of
mutations, chiefly those affecting growth rate and colony form, it was
observed that sublethal concentrations of PbC12 ranging from 100 to 500
mg/l of Pb, and a lethal concentration of 1000 mg/lg Pb2, produced no
appreciable increase in incidence of such mutant types above the spon-
taneous frequency in Platymonas subcordiformis.
148
-------
1681.
Heyraud, M. and S.W. Fowler. 1973. Comparative studies on the
bioretention of radionuclides under laboratory and field
conditions. Thalassia Jugoslavica 9:127-137.
For clam Tapes decussatus, polychaete Hermione hystrix, and
crab Pachygrapsus marmoratus, there were no significant differences in
Zn-65 loss rate within each organism when held in seawater collected
in situ or in seawater from the laboratory system. Addition of 100 ~g
Zn/l to the medium accelerated Zn-65 flux rates. Simultaneous laboratory
and field experiments indicated that Zn-65 loss rates in clam and mussel
Mytilus galloprovincialis, were similar whether animals were held in
field or laboratory. Mussels labelled for 75 days lost Zn-65 more
slowly than those labelled for 11 days. During the summer, crabs lost
Zn-65 significantly faster in the laboratory than in the field. But
during winter, when water temperatures were lower, no differences in
loss rates between systems were observed. Seasonal differences may be
due to variations in molt cycle. Authors concluded that care should
be taken when comparing lab and field results for the same species.
1682.
Heyraud, M., S.W. Fowler, T.M. Beasley and R.D. Cherry. 1976.
Polonium-2l0 in euphausiids: A detailed study. Marine
Biology 34:127-136.
Polonium-2l0 concentration in Meganyctiphanes norvegica
decreases from 1.1 pCi/g dry material to 0.4 pCi/g dry material as the
mean dry wt increases from 19 to 76 mg. This higher concentration in
smaller specimens cannot be explainec on basis of surface absorption
but is probably related to food ingestion. Muscular mass, eyes and
exoskeleton of euphausiids all contain 1 pCi/g dry wt or less, whereas
alimentary tract has 9.9 pCi/g and hepatopancreas 23.6 pCi/g. A model
was formulated to determine flux of Po-2l0 through M. norvegica. Cal-
culations confirmed that food is the main source of-Po-2l0 and fecal
pellets constitute the major elimination route. Extrapolation of data
to zooplankton leads to the conclusion that zooplankton metabolic
activity is important in transport of Po-2l0 from surface to oceanic
depths.
1683.
Hidaka, I. 1970. The effects of transition metals on the
palatal chemoreceptors of the carp. Japanese Jour. Physiol.
20:599-609.
Electrical responses of the palatine nerve innervating the
palatal organ of Cyprinus carpio when stimulated by sucrose, were
depressed by external application of low concentrations of Na2PtC16,
NaAuBr4, NaAuC14, HgC12, and TlC13' Response to NaCl was not affected
or occasionally enhanced. CUS04, ZnS04, AgN03, and U02(CH3COO)2
149
-------
depressed both sucrose and NaCl responses. Depression of sugar receptor
increased with rising NaAuC14 concentration and was recovered by
cysteine. It appears that reaction of receptor with chloraurate occurs
at the receptor membrane. N-ethylmaleimide and iodoacetate depressed
sucrose and NaCl responses non-selectively. Histidine could recover
gold depression of sugar receptor, though more weakly than cysteine.
It was concluded that some reactive groups other than sulfhydrils were
responsible for receptor membrane reaction with gold ions, but -SH
groups were responsible for other metals effects.
1684.
Hiltibran, R.C. 1971. Effects of cadmium, zinc, manganese,
and calcium on oxygen and phosphate metabolism of bluegill
liver mitochondria. Jour. Wat. Poll. Contr. Fed. 43:818-823.
Cadmium and zinc, at levels of 0.37 mg/l and 2.14 mg/l,
respectively, were found to alter oxygen metabolism. Both oxygen and
phosphate metabolism were altered by calcium (levels of 6.8 and 13.2
mg/l, respectively) and manganese (93.5 mg/l for both). Results indi-
cate that Cd and Zn can disrupt energy production by inhibition of
oxygen uptake within cell, and that this disruption can occur at rela-
tively low levels and be of such severity as to cause death of fish,
particularly bluegill.
1685.
Hiltner, R.S. and H.J. Wichmann.
BioI. Chern. 38:205-221.
1919.
Zinc in oysters.
Jour.
Zinc is present universally in oysters, at least in those
grown in Atlantic waters. There is no direct relation between Zn content
and body wt of oysters, nor uniformity of ratio of Zn to Cu, nor corre-
lation between Zn content of oysters and water in which they grew.
Vegetation and organic matter dredged up with oysters in the locality
studied contained notable quantities of Zn and in some instances traces
of Cu. As in Sycotypus, a predatory snail, Zn is probably always asso-
ciated with Cu. It seems probable that Zn, as well as Cu, can be
absorbed and retained in tissues of oysters in quantities far in excess
of ~unctional requirements, especially in oysters grown in waters badly
polluted with metallurgical and factory wastes. Concentrations of Zn in
oysters, in mg/kg wet wt, was determined for a variety of locations by
several investigators and ranged between 26 and 2298; for Cu this was
6 to 539; for arsenic, none to 1.47.
1686.
Hochberg, M.L. and M.L. Sargent. 1973. Regulation of repressible
alkaline phosphatase by organic acids and metal ions in
Neurospora crassa. Canadian Jour. Microbiol. 19:1487-1492.
150
-------
Various organic acids used in standing cultures of Neurospora
regulate specific activity of mycelial repressible alkaline phosphatase.
Regulatory control occurs primarily through chelation of metal ions
which are necessary for the production or stability of the enzyme. Both
Fe2+ and Zn2+ were needed in growth medium for maximum enzyme level,
while a high Cu2+ concentration depressed enzyme level. Concentrations
of 2.55 M Fe2+, 1.75 x 10-5M Zn2+ and 1.75 x 10-4M Zn2+ added to a
citrate medium increased mycelial enzyme activities 25%, 63%, and 73%,
respectively. Electrophoresis of mycelial extracts on gradient poly-
acrylamide gels demonstrated that the organic acids and Fe2+ do not
have these regulatory effects on repressible or constitutive acid
phosphatases of Neurospora.
1687.
Hodgkin, A.L. and B. Katz. 1949. The effect of sodium ions on
the electrical activity of the giant axon of the squid. Jour.
Physiol. 108:37-77.
Measurements made using a microelectrode in squid giant axons
showed that in absence of Na, action potential is abolished, but will
return to normal when seawater is applied. Dilution of seawater will
slightly increase resting potential, but produce a large and reversible
decrease in height of action potential, with reversed potential dif-
ference going to zero when Na concentration is <30% normal. Hypertonic
solutions of NaCl produce an increase of action potential but have no
effect on resting potential. The rate of rise (up to 140%) or decline
(to 10%) of action potential is directly proportional to external Na
concentration. Conduction velocity undergoes substantial decrease in
solutions of low Na content. Changes produced by dilution of seawater
with isotonic dextrose appear to be caused by reduction of the Na con-
centration and not by alterations in concentrations of other ions.
Removal or addition of external K produces an increase or decrease,
respectively, in both action and resting potentials. It was concluded
that permeability conditions of membrane in active state are reverse of
those in resting state, with resting membrane more permeable to K than
Na, and active membrane more permeable to Na than K. The reverse is
thought to be caused by variations in Na permeability only, with a
reversed membrane potential occurring when external Na is greater than
Na in axoplasm.
1688.
Hodson, P.V. 1975. Zinc uptake by Atlantic salmon (Salmo salar)
exposed to a lethal concentration of zinc at 3, 11, and 19 C.
Jour. Fish. Res. Bd. Canada 32:2552-2556.
Salmon acclimated to 3, 11, and 19 C accumulated high concentra.
tions of zinc in gill tissues during exposure to 14 mg Zn/l for 8 hrs.
Using Zn-65 as a tracer, rate of Zn uptake increased from a minimum at
151
-------
3 C to a maximum at 19 C. Among fish dying during exposure, Zn con-
centrations in gill were highest at 19 C and lowest at 3 and 11 C.
1689.
Hodson, P.V. 1976. Temperature effects on lactate-glycogen
metabolism in zinc-intoxicated rainbow trout (Salmo gairdneri).
Jour. Fish. Res. Bd. Canada 33:1393-1397.
Lactate production and glycogen utilization in dorsal white
muscle of rainbow trout increased during exposure for 18 hrs to 14-15
mg of Zn/l. Exposure at 3, 11 and 19 C did not affect timing or per-
cent change of lactic acid production or utilization of glycogen. It
was concluded that previously observed high tolerance of Zn by warm-
acclimated fish is not due to increased resistance to tissue hypoxia
caused by gill damage.
1690.
Hodson, P.V. and J.B. Sprague. 1975. Temperature-induced
changes in acute toxicity of zinc to Atlantic salmon (Salmo
salar). Jour. Fish. Res. Bd. Canada 32:1-10.
Three groups of salmon were acclimated to water temperatures
of 3, 11, and 19 C, and exposed to zinc concentrations of 1 to 30 mg/l.
Cold-acclimated salmon (3 C) survived longer (300 h) but were less
tolerant (LC-50 = 3.5 mg/l Zn) than warm-acclimated (19 C) salmon (LC-50
[22 hr] = 5 mg/l). Moderate (8 C) and severe (16 C) heat stresses
shortened time to mortality and either increased (8 C) or caused no
change (16 C) in tolerance. Moderate and severe cold stresses lengthened
time to mortality similarly, but decreased tolerance. When acclimated,
rate of mortality was a function of temperature; a 10 C increase in
acclimation temperature caused a 3.1-3.3 X increase in mortality. When
exposure temperature (Te) does not equal acclimation temperature (Ta),
LC-50 may be predicted by the equation LC-50 = 1.9611-0.1873 Ta +
0.8699 Te - 0.0414 Te2 + 0.00004 Ta Te3. Using this model and field
measurements, authors predicted that extensive mortality may occur
among salmon in the Miramichi River, New Brunswick in winter when
copper and zinc pollution exceeds 4.0 toxic units (threshold lethality =
1.0 toxic units).
1691.
Hoese, H.D. 1960. Biotic changes in a bay associated with the
end of a drought. Limnol. Oceanogr. 5:326-336.
When Mesquite Bay, Texas underwent a salinity drop of 300/00
due to heavy river discharge, complete mortality of stenohaline marine
sessile and infaunal molluscs occurred. Mortality of euryhaline molluscs
occurred when salinities fell below 3%0. A high salinity Ostrea
equestris-Brachidontes exustus community was replaced by a Crassostrea
152
-------
virginica-Brachidontes recurvus community. Rapid lowering of salinity
apparently did not kill fishes and other motile forms. It was concluded
that these species must have emigrated, although several stenohaline
species were found in very low salinities immediately after influx of
fresh water~
1692.
Holden, A.V. 1973. Mercury in fish and shellfish.
Jour. Fd. Technol. 8:1-25.
A review.
A review of the mercury problem is given beginning with Hg
measurements in salt water fish of 0.04 to 0.15 mg/kg in the 1930's.
Recent values for over 16 species of freshwater fish from 7 different
countries ranged from 0.01 to 11.2 mg/kg fresh tissue. In marine
regions concentration factors of 1000-2500 for organic Hg and 1-50 for
inorganic Hg, taken up directly from seawater, were measured. Compiled
from various studies, the following ranges in Hg concentrations, in mg/kg
wet wt, are given: plaice 0.031-3.10; flounder <.01-2.5; herring 0.013-
1.39; menhaden 0.34; anchovy 0.44; cod 0.013-2.70; tuna 0.032-1.0;
swordfish 0.82-1.00; lobster 0.08-0.75; crab 0.06-0.15; oyster 0.02-0.20;
mussel 0.02-0.65; clams 0.02-0.11; adult harp seals 0.34 (meat) and 5.12
(liver); gray seal 1.13 (muscle) and 99 (liver); freshwater ringed seal
197 (flesh) and 210 (liver); Atlantic finwhale 0.06; humpback whale 0.24;
and Beluga whale 0.97 (meat) and 8.87 (liver). Also given are various
lethal dose studies and methods used to determine Hg.
Effects of Hg on man, including the Minimata incident, are
discussed. Man's impact on equilibrium level of Hg in the oceans, its
long term effects and biological magnification of Hg along food chain
are considered in determining a safe and practical maximum Hg level for
consumption. Author concludes that a maximum residue level of 1 mg/kg
would be well within acceptable limits for man and cause little diffi-
culty to fisheries (except for some areas where freshwater fish are
involved). If the maximum were reduced to 0.5 mg/kg or less, serious
problems could arise with certain species, particularly tuna and sword-
fish.
1693.
Holden, A.V. 1973. Mercury and organochlorine residue analysis
of fish and aquatic mammals. Pestic. Sci. 4:399-408.
Methods for methylmercury and total mercury analysis have been
found suitable for the majority of types of fish tissue and for dried
fish meal, but those of high lipid content occasionally present diffi-
culties. Lipids which have not been completely digested in the first
stage of analysis for total mercury may lead to interference. A number
of organic and inorganic substances, such as iodides, ozone, sulphides,
acetone and cyclic compounds interfere at the same wavelength as mercury.
153
-------
Nevertheless, reproducibility of the total mercury method described is
good, the standard deviation found for most fish tissue being f4 to 8%.
Methylmercury is the most toxic form of the element and therefore of
interest in the analysis of fish, but the technique described is less
reproducible, and slower, than that for total mercury. Because the
proportion in the methyl-form is at least 80% in fish and commonly about
95%, the total mercury technique is the method of choice for monitoring
residues in fish.
Of the organochlorine pesticides, the only residues now com-
monly found in freshwater and marine fish, sometimes in concentrations
up to at least 0.1 mg/kg, are dieldrin, pp'-DDT, and its two metabolites
TOE and DOE, although hexachlorobenzene, alpha- and gamma-BHC may some-
times be detected. Marine fish also contain significant amounts of
PCBs, often up to 1 mg/kg in some organs and it seems likely that fresh-
water fish in heavily polluted areas will also contain PCBs.
1694.
Holden, A.V. 1975. The accumulation of oceanic contaminants
in marine mammals. Rapp. P. -v. Reun. Const. into Explor.
Mer 169:353-361.
Grey seals Halichoerus grypus, and common seals Phoca vitulina,
from the west, north and east coasts of Great Britain, which were also
analyzed for pesticide residues and PCBs, contained greatest concentra-
tions of Hg in liver. Mean concentration of Hg in seal liver, in mg/kg
wet wt, was 1.6 in seals 84-114 cm in length, 96 in seals 117-152 cm and
178 in those 155-254 cm. Mercury concentration for the three respective
size classes were 0.14, 0.29 and 0.34 mg/kg wet wt in brain, and 0.03,
0.06, 0.05 mg/kg in blubber. Mean zinc levels in seals, in mg/kg wet
wt, were: liver 54; muscle 34; heart 31; kidney 37; spleen 32; brain
26; and blubber 9. Average seal liver concentrations, in mg/kg wet wt,
were 14 for Cu, 8 for Pb and 1.2 for Cd.
1695.
Holden, A.V. and G. Topping. 1972. XIV - Occurrence of specific
pollutants in fish in the Forth and Tay Estuaries. Proc. Roy
Soc. Edin. B. 71(14):189-194.
Mean mercury contents of lobster Homarus vulgaris, from various
locations on the Scottish coast ranged from 0.21 to 0.54 mg/kg wet muscle.
Metal levels of 7 species of Scottish fish in mg/kg wet muscle, ranged
from 0.06 to 0.16 for Cd, <0.5 to 1.0 for Pb, 0.32 to 1.6 for Cu, and
1.7 to 14.7 for Zn. Organochlorine residues were also examined.
1696.
Hollifield, K.L. and R.V. Dimock, Jr. 1974. Interaction of
temperature and salinity on crab metabolism. Amer. Zool.
14:1259.
154
-------
Metabolism was measured for Pano eus herbstii acclimated to
10 C and 300/00, 10 C and 50/00, 23 C and 30 00, and 23 C and 50/00.
Measurements were made at experimental salinities of 40, 30, 15, and
50/00 at both 25 C and 10 C. Significant interaction between tempera-
ture and salinity occurred. For animals acclimated to 23 C and 300/00,
highest metabolic rates occurred at low experimental salinity at 25 C
test temperature. The same animals tested at 10 C had highest metab-
olism at high salinity. After low temperature acclimation, metabolism
was higher at low salinity under all experimental conditions. Tempera-
ture acclimation had the most consistent effect on metabolism at low
acclimation salinity and high test temperature. Q10 varied with salinity.
Sexual differences occurred only in animals acclimated to 23 C and 50/00
and tested at 25 C. Females exhibited significantly lower metabolic
rates than males under these conditions.
1697.
Holmes, A.D. and R. Remington. 1934. Arsenic content of
American cod liver oil. Ind. Eng. Chern. 26:573-574.
Twenty samples of crude, medicinal, American cod liver oils
were examined for arsenic. The samples represented typical oils from
the various American centers producing cod liver oil. Arsenic content
varied from 1.4 to 5.1 mg/kg with an average of 2.6 ! 0.13. These
values are materially higher than common fruits and vegetables, about
the same as American marine fish and shellfish, and decidedly lower than
crustaceans. Data were not available concerning the nutritional or
therapeutic value of arsenic by regular consumption of cod liver oil,
although it is believed to be present in a form of low or no toxicity.
1698.
Hoover, W.L., J.R. Melton, P.A. Howard and J.W. Bassett, Jr.
1974. Atomic absorption spectrometric determination of
arsenic. Jour. AOAC 57(1):18-21.
Two methods for As determination with sensitivities of 0.5
and 0.1 mg As/kg wet wt are described. Applied techniques yielded
values of 3.0 to 6.8 mg As/kg for fish muscle, and 6.1 to 6.4 for crab
muscle.
1699.
1971. The effect of marine pollutants
Marine Poll. Bull. 2:75-77.
Hopkins, R. and J.M. Kain.
on Laminarea hyperboria.
Two different techniques were used to determine toxic concen-
trations of mercury copper, zinc, herbicides, detergents and insecti-
cides, to ~. hyperborea. Culture experiments lasting 28 days ~n which
zoospores developed into gametophytes then sporophytes under glven con-
centrations of pollutants was one technique. Another used a respirometer,
155
-------
where the pollutant was added at 90 minutes and followed for 26 hours
in the dark. In culture experiments, the toxic concentration was the
lowest one tested in which plant growth differed from the control. For
Hg, Cu and Zn, these were 0.01, 0.05 and 0.25 mg/l, respectively. In
the respirometer approach the lethal concentrations were determined as
those which inhibit respiration; for Hg, Cu, and Zn, these concentra-
tions were 10, 100, and 1000 mg/l, respectively.
1700.
House, C.R. 1963. Osmotic regulation in the brackish water
teleost, Blennius pholis. Jour. Exp. BioI. 40:87-104.
In full strength seawater this species was calculated to
drink 0.62 g Na/kg fish/hr. Total flux of Na in !. pholis in 100% SW
was 2.3 g/l blood/hr; in both 40 and 10% SW this was 0.46. On the basis
of this and. other studies it was concluded that there 1s active outward
excretion of chloride ions in animals adapted to 150, 100 and 40% SW,
and active inward absorption of chloride ions in 10% SW and Na ions in
animals adapted to 40 and 10% SW.
1701.
Huckabee, J.W., C. Feldman, and Y. Talmi. 1974. Mercury con-
centrations in fish from the Great Smoky Mountains National
Park. Anal. Chim. Acta. 70:41-47.
Mean Hg concentrations of fish from 3 high altitude streams
in the Great Smoky Mountains, 20-25 km from nearest pollution source, in
mg/kg, were: rainbow trout Salmo gairdneri 0.036; brook trout Salvelinus
fontinalis, 0.018; banded sculpin Cottus carolinae 0.025; rosyside dace
Clinostomus funduloides 0.044; and stoneroller Campostoma anomalum 0.039.
There was no significant difference in Hg concentration among fish
analyzed whole, with gastrointestinal tract removed, or a strip of axial
musculature. There was a significant (p = >0.05) difference in Hg con-
centration among species in one stream and in 3 species from different
streams. Methyl-Hg constituted 93 I 2.6% of the total Hg. Results
indicate that all fish acquire the same tissue concentrations of Hg at
chronic low level exposure.
1702.
Huckabee, J.W. and N.A. Griffith. 1974. Toxicity of mercury and
selenium to the eggs of carp (Cyprinus carpio). Trans. Amer.
Fish. Soc. 103(4):822-825.
Carp eggs were exposed to trace amounts of Hg and Se to test
for effect on hatchability. Test concentrations of Hg as HgC12 and
2- , ,
Se03 as Se02, were 1, 2, 3, 4, and 5 mg/l each, and each possible
combination of these concentrations. No eggs hatched when incubated in
~4 mg/l Hg, but up to 5 mg/l Se032- had no effect on hatchability. Three
156
-------
mg/l was the lowest concentration of Hg that had
bility. When 1 mg/l concentrations were tested,
dropped from >99% to <20% when the elements were
respectively.
an effect on hatcha-
the percent hatch
alone and combined,
1703.
Hueck, H.J. and D.M.M. Adema. 1968.
tions in an artificial ecosystem.
copper toxicity towards ~algae and
wiss. Meeresunters. 17:188-199.
Toxicological investiga-
A progress report on
daphniae. Helgolander
Bioassay apparatus is described using algae, microcrustaceans
and fishes to simulate a food chain. Preliminary results with copper,
Chlorella pyrenoidosa, and Daphnia magna in an algae-crustacean two-stage
experiment are given. Continuous flow tests were more sensitive to D.
magna than static tests. Reproduction was the most sensitive parameter
measured with a concentration of 56 ug/l of Cu shown limiting for develop-
ment of D. magna. At a concentration of 1000 ug/l, development is
limited In ~. pyrenoidosa; accumulation factors for Cu are about 4000 to
5000 X. When fed with algae cultured in copper-containing media, D.
magna growth is inhibited at 560 ug/l Cu in the algal medium. D. magna
is therefore more sensitive to dissolved Cu than to Cu in food.- Taking
into account rate of feeding, provisional calculations suggest that
actual amount of Cu available to daphnids is higher via food than direct
absorption from medium.
1704.
Huggett, R.J., F.A. Cross and M.E. Bender. 1975. Distribution
of copper and zinc in oysters and sediments from three coastal-
plain estuaries. In Howell, F.G., J.B. Gentry and M.H. Smith
(eds.). Mineral Cycling in Southeastern Ecosystems. U.S.
Energy Res. Dev. Admin.: 224-238. Available as CONF-7405l3 from
NTIS, U.S. Dept. Comm., Springfield, VA 22161.
Oysters from the Newport River estuary, North Carolina, con-
tained 125 to 325 mg Zn/kg wet wt of soft parts and 2.2 to 6.2 mg Cu/kg.
For the Rappahannock River estuary, Virginia, oysters contained 275 to
425 mg Zn/kg wet wt and 3 to 29 for Cu. In all cases, higher metal con-
centrations occurred in animals living in lower-salinity waters. Concen-
tration levels in oysters were not directly related to concentrations in
sediments.
1705.
Huggins, A.K., D. Amrit, and C. Haworth. 1975. Biochemical
changes in crustaceans and other species associated with
alterations in environmental salinity. Biochem. Soc. Trans.
3:669-671.
157
-------
Using C-14 tracer, amount of various amino acids oxidized at
two salinities (850 and 340 mosmolal) in whole crab, Carcinus maenas,
was calculated. At the higher salinity, glutamate, glycine, and pro-
line had similar oxidation rates (0.020, 0.021, and 0.018 umol/h per g
wet wt, respectively). At the lower salinity, contribution of glycine
C to C02 produced increased nearly 5 X, to an oxidation rate of 0.099,
while glutamate and proline increased to only 0.037 and 0.035, respec-
tively. Thus glycine supplies additional oxidizable C during adapta-
tion to a decreased environmental salinity. Preliminary data with the
crabs Maia and Portunas suggests a similar mechanism, but this was not
observed for the euryhaline teleost Agonus cataphractus.
1706.
Hunter, W.R. 1949. The poisoning of Marinogammarus marinus
by cupric sulphate and mercuric chloride. Jour. Exp. BioI.
26:113-124.
Using behavioral criteria, mercury affected the marine
amphipod M. marinus at levels of 2.5 mg/l in seawater, and 0.5 mg/l in
distilled-water. In artificial seawater, copper had no effect at levels
<50 mg/l. Toxicities of Cu and Hg at concentrations of 5 mg/l were
increased by decreasing salinity. Cu levels from 0.2 to 2.5 mg/l in-
creased Hg toxicities, but 0.4 to 0.75 mg Hg/l did not effect CU toxi-
cities. In both artificial seawater and distilled water, oxygen con-
sumption was depressed by 25 mg Cull but not by 50 mg Cull.
1707.
Hutcheson, M.S. 1974. The effect of temperature and salinity
on cadmium uptake by the blue crab, Callinectes sapidus.
Chesapeake Science 15:237-241.
Adult crabs were exposed to various concentrations of cadmium
in seawater at different thermosaline regimes. Gill and hepatopancreas
were major sites of cadmium accumulation. Gill showed steady linear
increase of Cd with time; at 20 C, uptake increased with decreasing
salinity; at 5%0 S, uptake increased with increasing temperature.
Hi~hest concentration factors in gill were 6-8 times that of 10 mg/l
Cd + in water after 96 hours under regimes of 20 C, 200/00; 20 C,
30%0; and 10 C, 50/00. Mean Cd values (in mg/kg) after 96 hr in
respective regimes were approximately: 76, 55, and 70. Hepatopancreas
also accumulates Cd in linear fashion; at 5%0 S uptake rate increases
with increasing temperature. Maximum Cd levels at 20 C, 20%0 was
much higher after 96 hrs in hepatopancreas than ~illS (175 mg/kg Cd
~ 79). When crabs were removed from 10 mg/l Cd + water and placed in
Cd-free seawater, no loss of metal accumulation occurred within 96 hrs.
After 27 days of exposure to 0.2 mg/l Cd2+ at 20 C - 30%0, Cd con-
centrations (in mg/kg) were 3.4 in carapace, 54 in gills and 20 in
hepatopancreas.
158
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Crabs died in T-S regimes of 20 C, 200/00 (after 96 hrs) , 20 C,
50/00 (after 72 hrs), and 33 C, 50/00 (after 24 hrs). Concentrations of
cadmium in gills of live crabs at these times were 79, 83, and 79 mg/kg
Cd, respectively. This suggests a threshold level of approximately 80
mg/kg cadmium in gill. At low concentrations of Cd2+ in water (0.11
mg/l for 8 days and 0.2 mg/l for 27 days), no cadmium accumulated in
claw muscle.
1708.
Hutchinson, G.E.
The magnesium
significance.
28:90-108.
1932. Experimental studies in ecologie.
tolerance of Daphniidae and its ecological
Int. Revue Ges. Hydrobiol. u. Hydrograph.
I.
Magnesium tolerance levels, defined as Mg concentrations in
mg/l which prevent successful reproduction were: 0.24 for Daphnia magna,
0.03 for ~. ~homson~, 0.12 for ~. pulex, 0.03 to 0.06 for ~. longispina,
0.06 for Cerlodaphnla reticulata, and 0.18 for Moina macrocopa. For D.
pulex, D. magna and C. reticulata, LC-lOO (5 day) values for Zn were
<0.65 g7l. The implications of these findings to account for absence of
cladocerans in Lake Tanganyika is discussed.
1709.
Hutchinson, T.C., A Fedorenko, J. Fitchko, A. Kuja, J. Vanloon
and J. Lichwa. 1976. Movement and compartmentation of nickel
and copper in an aquatic ecosystem. In Nriagu, J.O. (ed.).
Environmental Biogeochemistry, Vol. 2:-Metals Transfer and
Ecological Mass Balances. Ann Arbor Sci. Publ., Ann Arbor,
Mich.: 565-585.
Nickel, copper and zinc were determined in water, sediments,
macrophytic vegetation, algal periphyton, crustaceans, molluscs, and
fish taken from rivers and reservoirs of the Sudbury, Ontario area, an
area where mining and smelting activities proliferate. Approximate
concentration factors for different ecosystem components for Ni, Cu and
Zn were: sediment, Ni 5300, Cu 12,000, and Zn 9700; algal periphyton,
Ni 19,600, Cu 17,600, and zinc 15,000; macrophytic vegetation (Poto-
mageton sp.), Ni 11,400, Cu 9000, and Zn 6500; zooplankton, Ni 643, Cu
3400, and Zn 15,700; clams, Ni 262, Cu 2,200, and Zn 21,500; benthos
(crayfish), Ni 929, Cu 39,100, and Zn 24,000; omnivorous fish (brown
bullhead), Ni 226, and Cu 149; and for carnivorous fish (yellow pickerel),
Ni 329 and Cu 156.
Metal concentrations in sediments reflected inputs from
industrial activity. Levels of Ni and Cu in water varied according to
input source and correlated well with levels in periphyton, zooplankton
and minnows, suggesting uptake. Metal concentrations of sediments corre-
lated significantly with concentrations in rooted macrophytes. Aquatic
159
-------
fauna showed selectivity in metal uptake with Ni excluded relative to Cu
and Zn in clams and crayfish. Fish had lowest metal levels implying
that while very large concentration factors exist for many parts of' the
ecosystem, food chain biomagnification apparently does not occur.
1710.
Hyvarinen, H. and T. Valtonen. 1973. Seasonal changes in the
liver mineral content of Coregonus nasus (Pallas), sensu
Svardson, in the Bay of Bothnia. Compo Biochem. Physiol.
45B:875-88l.
Copper content of adult whitefish liver was lowest during
summer and autumn in both sexes, but increased markedly during the
winter (mean 16 mg Cu/kg fresh wt). Zinc content appeared to be inde-
pendent of season or sex (highest average value =38 mg Zn/kg). For
magnesium, levels were highest in summer and lowest in winter; males
exhibited significantly lower zinc values than females; a similar
pattern was observed for calcium. Authors concluded that changes in
liver mineral content are associated with metal constituents of the
metal enzyme complexes or with changes in metalloenzyme concentrations.
1711.
Ichikawa, R. 1960. Strontium-calcium discrimination in the
rainbow trout. Rec. Oceanogr. Works Japan 5(2):120-131.
In lake water, trout uptake ra~io of Sr:Ca in muscle and bone
was 0.4 that of environmental levels. However, at levels of 1 to 12 mg
Sr/l (Sr:Ca ratios of 0.04 to 1.0), uptake ratios were 0.2 that of
medium. From dietary uptake, the Sr:Ca ratio was 0.7 that of food.
1712.
Ikuta, K. 1968. Studies on accumulation of heavy metals in
aquatic organisms - II. On accumulation of copper and zinc
in oysters. Bull. Jap. Soc. Sci. Fish. 34(2):112-116. (In
Japanese, English summary)
Oysters were transplanted from Urashiro Bay, a control region
with water concentrations of 0.5-2.3 ~g Cull and 5.7-37 ~g Zn/1, to
Akimizu Inlet with 1.0~6.4 ~g Cull and 8-42 ~g Zn/1. After 120 days
oysters contained 190 mg/kg wet wt Cu and 580 mg/kg wet wt Zn. Controls
in Urashiro Bay had metal levels, in mg/kg, of 25 for Cu and 200 for
Zn. Cu content in transplanted oysters increased exponentially, whereas
Zn increased in sigmoidally.
1713.
Ikuta, K. 1968. Studies on accumulation of heavy metals in
aquatic organisms. III. On accumulation of copper and zinc
160
-------
in the parts of oysters. Bull. Jap. Soc. Sci. Fish. 34(2):
117-122. (In Japanese, English abstract)
Zinc and copper in mantle, gill, labial palp, adductor muscle
and remainder were determined for clean oysters transplanted for 120 days
to an area where green oysters occur. Levels of copper increased expo-
nentially in some cases, reaching 65 mg Cu/kg wet wt in adductor muscle,
205 in mantle, 255 in gill, 1237 in labial palp, and 100 mg Cu/kg in
remainder. Exponential accumulation of zinc occurred in some instances,
reaching 250 mg/kg in adductor muscles, 800-900 in labial palp, mantle,
and gill, and 300 in remainder. In other instances zinc did not follow
any distinct pattern. Ratios of metal concentrations in parts of
oysters to levels in whole bodies for mantle, gill, and labial palp were
>1, but for adductor muscle and remainder; <1.
1714.
Ikuta, K. 1968. Studies on accumulation of heavy metals in
aquatic organisms. IV. On disappearance of abnormally accumu-
lated copper and zinc in oysters. Bull. Jap. Soc. Sci. Fish.
34(6):482-487.
Oysters Ostrea gigas, v:ith abnormally accumulated Cu and Zn
were transplanted into clean water to determine depuration rate. During
the 116 day study, Cu, in mg/kg wet wt, decreased in mantle from 286 to
14, in gill from 430 to 15, in labial palp from 264 to 18, in adductor
muscle from 58 to 5, in remainder from 214 to 13, and in whole body from
232 to 12. During the same period zinc decreased in mantle from 1072 to
95, in gill from 1270 to 171, in labial palp from 2178 to 112, in
adductor muscle from 221 to 37, in remainder from 1013 to 122, and in
whole body from 953 to 108. Accumulated Cu did not depurate until at
least 2 weeks post-transplantation. Zinc, however, began to depurate
immediately. Copper depuration rate is 2X that of zinc. Contents of
these metals and ratio of zinc to copper were normal when individuals
had grown 4X in weight (116 days).
1715.
Ikuta, K. 1972. Studies on green oyster. Bull. Fac. Agric.,
Miyazaki Univ. 19(1):116 pp. (In Japanese, English Abstract)
Through laboratory experimentation, the following formula was
derived to describe copper accumulation in oysters:
1 log Y-a' . 1 . .
og y = at b' (t~l), where y 1S the copper accumu at10n quant1ty,
Y is copper concentration in seawater, a is initial level of copper con-
tent, t is days of immersion, and a' and b' are constants of the standard.
izing line, and dependent on water temperature. Copper accumulation is
proportional to temperature with calculated values of copper being:
5.21 ug Cull at 15 C, 1.71 ug Cull at 20 C, and 0.44 ug Cull at 25 C in
161
-------
individual oysters. Accumulation also differs with salinities of coastal
and oceanic water; being greater in coastal waters having the same copper
concentrations as oceanic waters. Interaction of copper with other
metals under certain concentrations is recognized. It is suggested that
5 ug Cull should be adopted as the new water quality criterion (presently
set at 7.5 ug Cull), for at this level (including both ionic copper and
copper in food substances) green discoloration does not occur over long
time periods. The process of copper accumulation by oysters involves
absorption onto mucous sheets, transport across cell membrane to acido-
philic granules in epithelial cells for storage, and excretion of copper.
This process is probably common to other heavy metals with positive
polyvalent ions. All information obtained appears to represent a common
relationship between other genera of bivalves and heavy metals.
1716.
Imai, T. and M. Sakanoue. 1973. Content of plutonium, thorium
and protactinium in seawater and recent coral in the North
Pacific. Jour. Ocean. Soc. Japan 29:76-82.
Pu-239 content of North Pacific, East China Sea, and Japan Sea
surface waters ranged from 0.6 to 1.6 pCi/lOOO 1, with Pu-238/Pu-239
activities ratios of 0.2 to 0.7. Thorium-228/Thorium-232 activity
ratios for North Pacific waters varied between 7.6 and 30, whereas the
East China Sea ratio was 65. Contents of protactinium-23l are <6% of
that in equilibrium with its parent U-235. Plutonium isotopes have
concentrated in recent coral from Yoron Island with concentration factors
of 1 x 103 to 2 x 103.
1717.
Imanishi, N. 1959. Studies on the inorganic chemical constit-
uents of sea fishes. Records.Oceanog. Works Japan 3:135-139.
Cu, Pb, Sn, Fe, AI, Mn, Zn, Ca, Mg, Na, K, and Si were determined
spectrographically in ash samples from 8 species of deep water fish
caught at 200-300 m in the Bay of Tosa, Kochi prefecture, Japan.
1718.
Ingram, L.O. and E.L. Thurston. 1976.
cell division in Anacystis nidulans.
371.
Potassium requirement for
Jour. Bact. 125(1):369-
. ~. nidulans, an autotrophic blue-green bacterium, has a K
req~lrement of 0.7% of cellular dry wt. K starvation partially dis-
soclates growth from division, inducing 50% of population to form fila-
ments.
162
-------
1719.
Ireland, M.P. 1973. Result of fluvial zinc pollution on the
zinc content of littoral and sublittoral organisms in
Cardigan Bay, Wales. Environ. Poll. 4:27-35.
The distribution of fluvial zinc in seawater in 5 species of
littoral animals, one species of seaweed, and in two species of sub-
littoral animals, was studied at varying distances from Aberystwyth, a
source of zinc pollution. Zinc concentrations, in mg/g dry wt, in the
common mussel Mytilus edulis ranged from 0.25 to 0.77; in whelk Thais
lapillus, 0.91 to 1.98; in periwinkle Littorina littorea, 0.02 to 0.27;
in barnacle Balanus balanoides, 4.5 to 23.1; and in the anemone
Actinia equina, 0.16 to 0.60. Zinc content of littoral seaweed Fucus
vesiculosus ranged from 0.21 to 0.50 mg/g dry wt. Zinc concentrations
in the sublittoral sponge Halichondria panicea ranged from 0.08 to
0.15 mg/g dry, wt and in the sublittoral tunicate Botryllus schlosseri,
from 0.17 to 0.25 mg/g dry wt. Concentrations of Zn in F. vesciulosus
parallel that of seawater. Zinc concentrations in L. littorea and
!. lapillus are related to their diet. There is a site/species inter-
action in the filter feeders M. edulis and B. balanoides but Zn concen-
tration in B. balanoides is always at least-lOX higher than in M.
edulis. Zinc concentrations in the two sublittoral filter-feeders
(~. panicea and~. schlosseri) were significantly different at all
localities. Distribution of Zn is discussed in relation to tidal flow,
diet and species specificity.
1720.
Ishibashi, M., T. Fujinaga, F. Morii, Y. Kanchiku and F. Kamiyama.
1964. Chemical studies on the ocean (part 94) Chemical
studies on the seaweeds (19). Determination of zinc, copper,
lead, cadmium and nickel in seaweeds using dithizone extrac-
tion and polarographic method. Rec. Oceanogr. Works Japan
7(2):33-36.
Algae Eisenia bicyclis, contained Zn, Cu and Pb levels, in
mg/kg dry wt, of 112 to 127, 11 to 24, and 7 to 16, respectively.
Respective Ni and Cd levels in mg/kg dry wt, of 5 species of algae,
were 2.0 and 0.2 for VIva sp., 3.0 and 0.1 for Desmarestia viridis, 1.5
and 0.3 for Eisenia bICYClis, 2.2 and 0.2 for Gelidium sp., and 4.2 and
0.1 for Acanthopeltis japonica.
1721.
Ishibashi, M., T. Fujinaga, T. Yamamoto, T. Fujita, and K.
Watanabe. 1965. Zinc and iron in seaweeds. Jour. Chern.
Soc. Japan 86:728-733. (In Japanese)
Zinc and iron values in 58 species of aquatic plants, includ-
ing 8 species from freshwater, are presented. Zinc, in g/kg wet wt,
ranged from about 0.11 to 3.95 in marine species and 0.55 to 3.97 in
163
-------
freshwater groups. For iron, values ranged from 0.2 to 12.1 g/kg wet
wt for marine species, and 6.7 to 37.4 g/kg for freshwater flora.
1722.
Ishibashi, M. and T. Yamamoto. 1960. Inorganic constituents in
seaweeds. Rec. Oceanogr. Works Japan 5(2):55-62.
A total of 83 seaweed samples, comprising 44 species were
collected from Tomoga-Shima, Wakayama Pref., Japan throughout the year.
Metal content, in g/kg dry wt, ranged from 0.2 to 66.6 for Na, 0.3 to
34.3 for K, 5.6 to 42.1 for Ca, 0.3 to 44.3 for Mg, 0.2 to 2.8 for P,
0.07 to 3.41 for Fe and 0.000142 to 0.00253 for Cr. Authors concluded
that seaweeds contain elevated levels of Na, Mg and Fe when compared to
land plants. Brown seaweeds were high in K and Ca contents while green
seaweeds were high in Fe and Cr contents. There were extreme variations
in Fe and Mn content among species. Seaweeds with high Fe were also high
in Mn and Cr. Approximately half the species analyzed exhibited a
value of 3-7 in Fe/Mn atomic ratio. Fe/Cr atomic ratio also showed
considerable concentration of iron. The atomic ratio of K/Na is near
1 in all species. The Ca/Mg atomic ratio is below 2 except for
Oesmarestia viridis. Chromium is much more concentrated in seaweeds
than seawater.
1723.
Ishibashi, M., T. Yamamoto and T. Fujita. 1964. Chemical
on the ocean (Part. 93) Chemical studies on the seaweeds
Nickel content in seaweeds. Rec. Oceanogr. Works Japan
25-32.
studies
(18)
7:
Seaweeds collected from shore of Tomogashima, Wakayama Pref.,
Japan were analyzed for nickel. Among 78 samples representing 38
species, nickel ranged from 0.23 in Grateloupia turuturu to 10.90 mg/kg
dry wt in Enterrnorpha compressa. Total mean value of Ni content was
2.78 mg/kg dry wt; Ni content did not vary with season or habitat. Brown
seaweeds (Phaeophyceas) generally contain comparatively high Ni, but
some (Eisenia bicyclis, Sargassum gigantelifol1ium, Sargassum umtortile)
which have low iron, aluminum, manganese, chromium and cobalt are low
in Ni. Green seaweeds (Ch1orophycae) are high in nickel contents and
red seaweeds (Rodophycae) generally low. Nickel content of lirnnetic
weeds were higher than that of seaweeds.
1724.
Ishibashi, M., T. Yamamoto and F. Morii. 1962. Chemical studies
on the ocean (Parts 85) Chemical studies on the seaweeds (11)
Copper content in seaweeds. Rec. Oceanogr. Works Japan 6:
157-162.
164
-------
Copper in 66 samples of 40 species of seaweeds collected from
the coast of Tomogashima, Wakayama Pref., Japan, in mg/kg dry wt,
ranged from 6.1 to 26.4 in brown seaweeds (Phaeophycae); from 9.2 to
27.7 in green seaweeds (Chlorophycae); and from 7.0 to 26.7 in red
seaweeds (Rodophycae).
1725.
Ishikawa, M., T. Koyanagi and M. Saiki. 1976. Studies on the
chemical behaviour of l06Ru in seawater and its uptake by
marine organisms. I. Accumulation and excretion of l06Ru
by clam. Bull. Jap. Soc. Sci. Fish. 42(3):287-297.
Accumulation of Ru-l06 by Meretrix meretrix lusoria in the
form of crude Ru NO.Clx and Ru.Clx' or prepared forms which contained
higher radioactivity, reached equilibrium in about 2 weeks. Radio-
activity ratios (radioactivity of tissue/g wt + radioactivity of sea-
water/ml) for prepared Ru-l06.Clx after 20 days were 24 for mid gut
gland, 13 for gill, 4 for digestive tract, 30 for mantle, 2 for shell,
and 1 for foot and gonad. Loss of Ru-l06 was rapid for soft parts;
after 75 days depuration, percentage losses of Ru-l06 introduced as
prepared Ru.Clx were 48 for gill, 69 for mid gut gland, and 52 for
digestive tracts.
1726.
Jacobson, A.F. 1971. Effect of temperature upon the uptake of
144Ce by Chlamydomonas. Nuclear Sci. Abs. 55162:5427.
Uptake of Ce-144 by Chlaoydomonas, a unicellular green alga,
was positively correlated with temperature, time, and initial Ce-144
concentration; negatively correlated with biomass; and little affected
by cerium specific activity. Temperature and biomass showed the
strongest influence; interactions among variables also affected uptake.
1727.
Jampol, L.M. and F.H. Epstein. 1970. Sodium-potassium-
activated adenosine triphosphatase and osmotic regulation by
fishes. Amer. Jour. Physiol. 218:607-611.
Specific activity of Na-K-activated ATPase was high in gills
of saltwater teleosts and low in gills of elasmobranchs and freshwater
teleosts. Na-K-ATPase activity in gill filaments and intestinal mucosa
of freshwater eels Anguilla rostrata, doubled when adapted to seawater
for 2 to 3 weeks. Authors suggest that Na-K-ATPase activity varies
with Na transport in several organs of teleosts and elasmobranchs under
osmotic stress, and conclude that this enzyme plays an important role
in active transport of Na across epithelial membranes.
165
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1728.
Jangaard, P.M., L.W. Regier, F.G. Claggett, B.E. March and J.
Biely. 1974. Nutrient composition of experimentally pro-
duced meals from whole argentine, capelin, sand lance, and
from flounder and redfish filleting scrap. Jour. Fish. Res.
Bd. Canada 31:141-146.
Nutritional analyses, including protein, fat, ash, moisture,
minerals, vitamins, available lysine, amino acids, and protein digest-
ibility were conducted on meals produced from whole Atlantic argentines
Argentina silus, capelin Mallotus villosus, American sand lance
Ammodytes americanus and from filleting scrap from flounders Pleuro-
nectidae sp. and redfish Sebastes marinus. Whole fish meals appeared
nutritionally equal to good herring meal. Filleting scrap meals were
lower in protein content but nutritional values of the proteins were
equivalent to that of herring. '
Percentage metal content ranged between 1.8 and 8.8 for Ca,
0.13 and 0.24 for Mg, 1.0 and 1.3 for K, and 0.47 and 0.92 for Na.
Concentrations, in mg/kg, ranged from 42 to 199 for AI, 2.5 to 22 for
As, 1.6 to 3.9 for Ba, 5.3 to 17.5 for B, 0.13 to 0.34 for Cd, 1.5 to
23.7 for Cr; 0.05 to 0.18 for Co, 2.7 to 14.1 for Cu, 85 to 675 for Fe,
0.8 to 13.4 for Pb, 4.5 to 14.2 for Mn, 0.10 to 0.29 for Hg, 0.05 to
8.8 for Mo, 1.7 to 3.0 for Se, 90 to 416 for Sri and 74 to 142 for Zn.
1729.
Jarvenpaa, T., M. Tillander, and J.K. Miettinen. 1970. Methyl-
mercury: half-time of elimination in flounder, pike, and
eel. Suomen Kemistilehti B. 43:439-442.
Hg-203-labelled methylmercury, as the ionic form nitrate,
and as a protein-bound form, was applied perorally, and as the ionic
form, injected intramuscularly into flounder P1euronectes flesus, pike
Esox lucius, and eel Anguilla vulgaris. Both forms of methylmercury
produced similar elimination rates in flounder and pike: 640
to 780 days. However; 1M injection produced a half-time elimination
rate of 1,200 f 400 days in flounder. For eel, the proteinate given
perorally had a half-life of 910 days; the ionic form both perorally
and 1M = 1,030 days.
1730.
Jeffrey, R.G. and S.T. Zender. 1974. Ingested lead shot in
Washington waterfowl 1973-1974 hunting season. Washington
State Dept. Game, Tacoma, Wash.:1-9.
A total of 692 waterfowl gizzards were tested for ingested
lead shot in Washington; shot was found in 4%. Assuming a loss of
4 to 12% of birds ingesting shot, theoretical loss would range from
1.5 to 5.0 ducks per 1,000 and therefore appears insignificant.
166
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1731.
Jensen, A., B. Rystad and S. Melsom. 1976. Heavy metal toler-
ance of marine phytoplankton. II. Copper tolerance of
three species in dialysis and batch cultures. Jour. Exp.
Mar. BioI. Ecol. 22:249-256.
Reduction of growth rate was produced in Skelotonema costaturn,
Thalassiosira seudonana, and Phaeodactylurn tricornuturn2 via addition
of 10, 25, and 400 ~g 1 of Cu2+, -respectively. When Cu + was added at
levels of 400 and 700 ~g/l, cells of P. tricornuturn in dialysis culture
increased Cu content >200X over controls, with ratio of Cu to chlorophyll
in cells increasing l50X. All three diatom species showed marked in-
creases when a copper salt was added to batch cultures of algae. Two
clones of S. costaturn showed nearly identical sensitivity to Cu ions,
but differed markedly in zinc tolerance.
Jensen, S. and A. Jernelov. 1969. Biological methylation of
mercury in aquatic organisms. Nature 223:753-754.
Swedish lake bottom sediments can produce CH3Hg2+ from
HgC12' Over a 7 day period, samples of sediment produced the maximal
amount of CH3Hg+ (120 ~g/kg) when treated with 100 mg/kg HgC12' Dead
fish, Xiphophorus maculatus, weighing 5 g and containing 125 ~g CH3Hg+
converted up to 91 ~g to dimethyl mercury in 7 weeks. Authors suggest
that formation of the volatile CH3HgCH3 may be a factor in redistribu-
tion of Hg from aqueous industrial wastes.
1732.
1733.
Jernelov, A., L. Landner and T. Larsson. 1975. Swedish per-
spectives on mercury pollution. Jour. Water Poll. Control
Fed. 47(4):810-822.
Mercury interactions in aquatic environments emphasizing
Swedish contributions are reviewed. Processes examined include:
biological methylation of Hg; static and dynamic aspects of accumula-
tion in food chains including role of plankton, filter-feeding bottom
invertebrates, and fishes; restoration of Hg-contaminated bodies of
water; atmospheric transport; and degradation of methyl-Hg. A
bibliography of 52 articles is appended.
1734.
Johnson, D.L. 1972. Bacterial reduction of arsenate in sea-
water. Nature 240:44-45.
Bacterial cultures from Sargasso seawater and Narragansett
Bay (R.I.) water were grown in media with sodium arsenite added. As
bacterial populations entered the log phase of growth (about 8 h),
arsenate began to be replaced by arsenite. Total As remained constant
167
-------
with no accumulation br bacteria. Arsenate reduction rate, calculated
at 12 h, was about 10- 1 ~ mol/cell/min. Bacterial arsenate reduction
suggests that these processes can occur in open ocean and explain
observed arsenite conditions.
1735.
Johnson, D.L. and R.S. Braman. 1975. The speciation of arsenic
and the content of germanium and mercury in members of the
pelagic Sargassum community. Deep-Sea Res. 22:503-507.
Arsenic levels in mg/kg wet wt of various components of the
pelagic Sargassum community were: 4.2 to 19.5 for Sargassum fluitans
and~. filipendula; 5.5 to 6.5 for crab Portunas; 12.7 for shrimp;
3.6 for barnacles Lepas; and 2.6 for filefish. Average distribution
of chemical As species in members of Sargassum community was similar to
that of surface water: 15% as As3+, 85% as Ass+ and 1% as alkyl-As.
Germanium contents in mg/kg wet wt were: 0.003 to 0.032 for Sargassum;
0.002 to 0.025 for shrimp; up to 0.010 for Portunas; 0.006 for Lepas;
and 0.002 for filefish. Total mercury contents, in mg/kg wet wt, were:
0.01 to 0.07 for Sargassum; 0.03 to 0.09 for shrimp; <0.01 to 0.03 for
Portunas; 0.08 for Lepas; and <0.01 for filefish.
1736.
Jones, D., K. Ronald, D.M. Lavigne, R. Frank, M. Holdrinet and
J.F. Uthe. 1976. Organochlorine and mercury residues in the
harp seal (Pagophilus groenlandicus). Science Total Environ-
ment 5:181-195.
Seals, 3 to 14 days old, had total mercury levels in mg/kg
wet wt of 0.04 to 0.13 in brain, 0.09 to 0.48 in liver, and 0.04 to 0.34
in kidney. Levels did not differ between sexes. Starvation increased
Hg levels in muscle. In comparison with their respective pups, dams
had higher Hg levels in brain, liver and blood, with highest overall
values in liver (7.6 I 3.1 mg Hg/kg wet wt). DDT, dieldrin and PCB
levels were also examined.
1737.
Jones, E.B.G. and D.H. Jennings. 1964. The effect of salinity
on the growth of marine fungi in comparison with non-marine
species. Trans. Brit. Mycol. Soc. 47:619-625.
Of the 14 marine fungi studied, Lulworthia floridana was the
only species which showed a requirement for seawater, all others grow-
ing better at lower salinities. Growth of all non-marine fungi tested
was significantly less in seawater than distilled water. Authors
suggest that cation environment may affect vegetative reproduction and
nutrient uptake and utilization.
168
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1738.
Jones, J.R.E. 1937. The toxicity of dissolved metallic salts
to Polycelis nigra (Muller) and Gammarus pulex (L.). Jour.
Exp. BioI. 14:351-363.
For P. nigra, a planarian, threshold concentrations of indi-
vidual salts were: 0.20 N NaCl; 0.15 N NaN03; and 0.00003 N PbN03'
Survival time was 3 hrs for 0.00002 N HgC12 exposure. Toxic effects
of Hg, Cu and Zn salts at concentrations below isotonicity were due
almost entirely to the cation. At concentrations above isotonicity,
the anion and osmotic pressure of solution acted as additional lethal
factors. For nitrates and sulphates of these heavy metals, toxicity is
determined by the product of normality and electrical conductance ratio
at that normality. Author suggests that death in heavy metal salt
solutions is due to tissue fixation. Salts of the metals of the alkalis
and alkaline earths are comparatively harmless below isotonicity, with
the exception of salts with a toxic anion such as potassium chromate,
which is highly toxic at low concentrations. Death in hypertonic
solutions of these metals may be due to osmotic stress. For the
amphipod ~. pulex, exposure to increasing concentrations of copper
nitrate or copper sulphate resulted in rapid decrease in survival time
to 58 min at 5 x 10-4 N. Above 0.15 N concentrations, survival time
decreased further.
1739.
Jones, J.R.E. 1940. A further study of the relation between
toxicity and solution pressure, with Polycelis nigra as test
animal. Jour. Exp. BioI. 17:408-415.
Toxicity of salts of 18 metals to the planarian P. nigra was
determined by 48-h bioassays conducted at 15-18 C. The following
levels of toxicity, in mg/l, in increasing order, were observed: Sr
6600, Na 4370, Ca 2600, Mg 970, Mn 700, Pb 400, K 350, Al 110, Co 83,
Cr 75, Ni 45, As 40, Zn 30, Cd 2.7, Au 0.6, Cu 0.47, Hg 0.2, Ag 0.15.
The position of iron was uncertain, as toxicity of ferric chloride
solutions (>20 mg/l) appeared to be due to their acidity. Irregular
results were obtained with solutions of barium salts, which effect
excessive stimulation of musculature, inducing convulsive movements that
eventually result in rupture of body and extrusion of tissues.
There was a decided relationship between solution pressures
of metals and degree of toxicity of their salts, the general result
being very similar to that obtained earlier with Gasterosteus aculeatus.
This relationship suggests that degree of toxicity of ions is largely
determined by their affinity for their electrical charges, this
affinity determining the readiness with which they tend to abandon the
ionic state to enter into chemical combination with protoplasmic com-
pounds.
169
-------
1740.
Jones, J.R.E. 1942. The effect of ionic copper on the oxygen
consumption of Gammarus pulex and Polycelis nigra. Jour.
Exp. BioI. 18:153-161.
For the planarian £. nigra, immersion in 80 to 800 mg CUS04/l,
155 to 311 mg BaC12/l, 0.850 mg AgN03/l, or 1.28 mg HgC12/l, resulted
in a preliminary rise in respiratory rate accompanied by inhibition of
ciliary locomotion and increased muscular activity. Afterwards,
respiration dropped with distintegration observed at 60% of normal
oxygen consumption rate. An 8 mg CuS04/l solution did not inhibit
ciliary locomotion or stimulate muscular activity, but did produce a
decrease in oxygen consumption. Similar respiratory responses were
observed in Gammarus pulex, an amphipod, exposed to 16 and 32 mg CUS04/l
1741.
Jones, J.R.E. 1947. The oxygen consumption of Gasterosteus
aculeatus L. in toxic solutions. Jour. Exp. BioI. 23:298-311.
Stickleback respiration shows an initial increase and subse-
quent decline to death upon exposure to concentrations (in mg/l) of 13.6
to 54.2 HgC12' 0.16 CUS04, or 0.825 Pb(N03)2' As the respiration rate
declines, rate of operculate movement increases for l80-240/min, then
decreases when 02 intake reaches 38% of normal value. Author suggests
that metals cause an increase in blood C02 levels, stimulating opercular
movements while 02 intake continues to fall. Eventually, the fish be-
comes exhausted, respiratory movements fail, and death results.
1742.
Jones, L.H., N.V. Jones and A.J. Radlett. 1976. Some effects
of salinity on the toxicity of copper to the polychaete
Nereis diversicolor. Estuarine Coastal Marine Sci. 4:107-111.
Worms were collected from 2 stations in the Humber Estuary
in South-West England. Worms from Hessle, which has a salinity range of
7.0 to 15.00/00 and a surface sediment Cu level of 62-64 g Cu/kg dry wt,
had 96 hr LC-50's of 0.2, 0.44, 0.48 and 0.37 mg Cull at respective
salinities of 5.0, 10.0, 17.5 and 340/00. Worms from Skeffling, which
has a salinity range of 20.5 to 30.40/00 and a surface sediment Cu level
of 52 to 56 g Cu/kg dry wt had 96 hr LC-50's of 0.2, 0.45, 0.48 and
0.45 mg Cull in respective salinities of 5.0, 10.0, 17.5 and 34.00/00.
Authors suggest that the synergistic effect of increased copper toxicity
at high and low salinities is the important lethal factor rather than
amount of Cu accumulated.
1743.
Jones, M.B. 1975. Effects of copper on survival and osmoregula-
tion in marine and brackish water isopods (Crustacea). Proc.
9th Europ. Marine BioI. Symp.: 419-431.
170
-------
At salinities of 1 to 100% seawater (100% seawater = 340/00)
and temperatures of 5 and 10 C, a concentration of 10 mg Cull produced
mortalities >50% within 5 days among marine isopods Idotea baltica, I.
emarginata, !. neglecta, Euryd~ce pulchra, and brackish water species
Jaera stricto and J. nordmanni. Decreasing salinity was associated
with increased toxIcity. Mortalities did not reach 50% in full sea-
water with 1 mg Cull. Marine species were able to survive in 100% to
40% seawater, and brackish water forms from 100% to 1% seawater, by
maintaining hyperosmotic haemolymphs. But 1 mg Cull caused a reduction
of haemolymph osmotic pressure particularly in dilute salt solutions.
It was concluded that Cu acts synergistically with salinity; concentra-
tions of Cu which are sublethal at optimum conditions become increas-
ingly toxic as environmental stress is increased.
1744.
Jones, M.B. 1975. Synergistic effects of salinity, temperature
and heavy metals on mortality and osmoregulation in marine
and estuarine isopods (Crustacea). Marine Biology 30:13-20.
Marine isopods Idotea baltica, I. neglecta, I. emarginata and
Eurydice pulchra, as well as estuarine Jaera stricto and ~. nordmanni
had low mortalities in 100% SWat 5 C when exposed to 10 and 20 mg/l of
cadmium (3 CdS04.8H20), zinc (ZnS04 . 7H20) or lead (Pb(N03)2) for 120
hours. Decreased salinities or a temperature increase to 10 C reduced
LC-50 values. Cadmium, at levels of 20 mg/l, had no effect on osmo-
regulation of I. baltica and I. emarginata in 100 and 80% SWat 5 C,
but significantly lowered blood osmotic concentration of I. neglecta in
80% SW. Zinc, at levels of 20 mg/l did not alter haemolymph osmotic
concentration of I. neglecta in 100 and 80% SW, but did lower blood
osmotic concentration of I. baltica in 100% SW. Cd, Zn and mercury
(HgC12) also significantly altered osmoregulatory ability of J.
albifrons in dilute saline.
1745.
Kalk, M. 1963. Absorption of vanadium by tunicates.
198:1010-1011.
Nature
In Ascidia pygmaea, vanadium is absorbed by passive pharyngeal
permeability and by preferential linking of vanadyl ions from the sea
to sulphate groups in acid pharyngeal mucus. Neutralized mucus passes
by pinocytosis into blood plasma. Accumulation, reduction, and preci-
pitation of V takes place on membranes of cytoplasmic vacuoles, but not
at cell surface.
1746.
Kameda, K., M. Shimizu and Y. Hiyama. 1970. On the uptake of
65Zn and concentration factor of Zn in marine organisms. II.
171
-------
Changes in Zn and 65Zn concentration in rearing water.
Radiation Res. 11:44-52.
Jour.
Zn,in dust, contaminated water at a rate of 2.9 ug/hr/tank.
The presence of short-necked clams Tapes japonica produced an increase
in Zn of 2.0 and 3.1 ug/hr/tank, which is 25 to 30% of the estimated
Zn contamination values. This discrepancy is attributed to release of
insoluble Zn from, lams or a change-of Zn to insoluble state due to
excretes from clams. In another study, reduction in Zn-65 concentra-
tion in water corresponds to amount taken up by!. japonica.
1747.
Kamiya, M. and S. Utida. 1969. Sodium-potassium-activated
adenosine triphosphatase activity in gills of fresh-water,
marine and euryhaline teleosts. Compo Biochem. Physiol. 31:
671-674.
Activities of Na+-K+ ATPase in gills of stenohaline fish were
2 to 5X higher in marine species than freshwater species. Seawater
adaptation of euryhaline fish resulted in quadrupling of Na+-K+ ATPase
activities.
1748.
Kanazawa, T. and K. Kanazawa. 1969. Specific inhibitory effect
of copper on cellular division of Chlorella. Plant Cell
Physiol. 10:495-502.
Cellular division of the freshwater alga Chlorella ellipsoidea
was inhibited by addition of Cu2+ to the medium; inhibition was
especially marked at pH 6.3 in range 5.1 to 7.1. The lowest concen-
tration tested of 3 X 10-7 M Cu2+ (about 19 ug Cull) produced ~rowth
inhibition; the highest concentration tested of 3 X 10-6 M Cu2 (about
190 ug/l) completely suppressed growth.
1749.
Kania, H.J. and J. O'Hara. 1974. Behavioral alterations in a
simple predator-prey system due to sublethal exposure to
mercury. Trans. Amer. Fish. Soc. 103:134-136.
After 24-hr exposure to sublethal mercury concentrations of
0.1, 0.05, and 0.01 mg/l Hg++, the ability of mosquitofish Gambusia
affinis to avoid predation by bass Micropterus salmoides was impaired.
Fish exposed to 0.005 mg/l of Hg++ were not affected. Degree of effect
showed a positive correlation with mercury concentrations. Behavioral
alterations occurred when mean body concentrations were as low as 0.67
rng of Hg/kg wet wt of whole fish.
172
-------
1750.
Kayser, H. 1976. Waste-water assay with continuous algal
cultures: The effect of mercuric acetate on the growth of
some marine dinoflagellates. Marine Biology 36:61-72.
'Effect of mercuric acetate was studied with the dinoflagel-
lates Scrippsiella faeroense, Prorocentrum micans, and Gymnodinium
splendens. Impairment of growth rates, in vivo chlorophyll fluores-
cence, maximum cell densities and morphological changes were criteria
for assessing sublethal influences. Tests were made using batch and
continuous culture techniques. Addition of Hg at concentrations of
0.001 mg/l, reduced relative growth rates of S. faeroense. At 0.05
mg Hg/l, S. faeroense and P. micans populations recovered from initial
declines and showed new growth. Morphological variations were observed
in S. faeroense, which responded (even in sublethal concentrations) by
bursting it's thecae, releasing naked motile cells and forming vege-
tative resting stages.
1751.
Kazlauskene, a.p. and M.A. Shcherbina. 1975. Alteration in
the organic and mineral composition of the chyme in yearling
pond carp (Cyprinus carpio) following the addition of chalk
to the diet. Jour. Ichthyology 15:804-811.
Addition of 2 or 5% chalk to diet of carp resulted in a
decrease in protein and carbohydrate contents of chyme and an increase
in chyme levels of lipids and minerals, especially magnesium. Authors
suggest that Ca competes with Mg uptake in absorption processes of
alimentary tract.
1752.
Keckes, S., Z. Pucar, and L. Marazovic. 1966. The influence of
the physico-chemical form of l06Ru on its uptake by mussels
from sea water. In Aberg, B. and F.P. Hungate (eds.).
Radioecological Concentration Processes. Proc. Inter. Symp.
Stockholm, 1966, Pergamon Press, New York: 993-994.
Mussels Mytilus galloprovincialisconcentrated Ru-l06 by about
50 in soft parts and 4 in shell during 5 days of exposure to a Ru-l06
nitrate complex. Factors of 5 for soft parts and 1 for shell were
observed with a Ru-l06 chloride complex during a similar period.
1753.
Keeney, W.L., W.G. Breck, G.W. Vanloon and J.A. Page. 1976.
The determination of trace metals in Cladophora glomerata -
C. glomerata as a potential biological monitor. Water
Research 10:981-984.
173
-------
Metal levels, in mg/kg dry wt, of the alga Cladophora
collected from a remote island in Lake Ontario and from a shore site
near Kingston, Ontario, were respectively 8.2 and 23.7 for Zn, 1.4
and 3.9 for Cd, 12.2 and 9.5 for Pb, and 6.4 and 7.2 for Cu. In both
instances concentration factors were in the range 103 to 104.
1754.
Kelly, T.M., J.D. Jones, and G.R. Smith. 1975.
changes in mercury contamination in Michigan
(Stizostedion vitreum vitreum). Jour. Fish.
32:1745-1754.
Historical
walleyes
Res. Bd. Canada
Mercury concentrations in Michigan walleyes (teleosts) were
more variable among localities than between recent and historical
samples within localities. Mercury concentrations, in mg/kg wet
muscle, in walleyes of 280 rnm length collected between 1865 and 1936
vs 1971 were 0.17 vs 0.18 for Houghton Lake specimens, 0.143 vs 0.191
for Lakes Cadillac-and Mitchell, 0.21 vs 0.15 for Bear Lake, ~2l vs
0.25 for Saginaw Bay, 0.24 vs 0.30 for-rake Gogebic, and 0.43 vs 0~8
for Isle Royale. Recent waTfeyes of 307 rnm length taken from the
Western Basin of Lake Erie had a mean Hg level in muscle of 0.45
mg/kg, whereas specimens collected from 1865 to 1936 had 0.35 mg
Hg/kg muscle tissue.
Hg concentration in walleye muscle from recent and old museum
collections was positively correlated with age and size. Considerable
variation in concentration existed not only between geographic local-
ities, but within populations, and even within subsamples of the same
tissue.
1755.
Kennedy, V.S. 1976. Arsenic concentrations in some coexisting
marine organisms from Newfoundland and Labrador. Jour. Fish.
Res. Bd. Canada 33:1388-1393.
Inorganic arsenic concentrations in seawater and mud, and
total As concentrations in bodies of shrimp, zooplankton, and fish from
northern Newfoundland and southern Labrador were measured. For shrimp,
a positive relation existed between concentration and carapace length
for Pandalus borealis and ~. montagui and a negative relation for
Eualus macilentus; these contained mean As concentrations of 7.3-11.5,
7.4-10.8, and 6.7 mg/kg wet wt, respectively. There was no correlation
between concentrations in shrimp eggs and carapace length. Zoo-
plankton, hyperiids and gammarids contained more As at 2.6 and 6.6
mg/kg wet wt, respectively, than copepods and euphasiids at 1.4 and 1.8
mg/kg wet wt. In fish, concentrations in muscle of American plaice
Hippoglossoides platessoides at 4.4 mg As/kg wet wt, were higher than
those of redfish Sebastes marinus, Atlantic cod Gadus morhua, and
174
-------
turbot Rheinhardtius hippoglossoides, all of which had mean muscle
concentrations of 0.8 mg As/kg wet wt. There was no evidence of in-
creasing As concentrations through higher levels of the food chain.
1756.
Kennedy, W.A. and M.S. Smith. 1972. Sablefish culture-progress
in 1971. Fish. Res. Bd. Can. Tech. Rep. 309:15 p.
Sablefish Anoplopoma fimbria, reared and cultured in the
laboratory, were analyzed for Hg, along with fish used to feed sable-
fish. Sablefish fed a diet of 50% herring - 50% dogfish contained
0.57 mg Hg/kg after 12 months and 1.29 mg/kg after 28 months. For
24-month-old sablefish fed 62% herring and 29% chicken wastes, the
average Hg level was 0.46 mg/kg. Mean Hg level in mg/kg was 0.39 for
dogfish Squalus suckleyi, 0.05 for herring Clupea pallasii, 0.09 for
hake Merluccius productus, 0.04 for whiting Theragra chaleogrammus and
0.04 for arrowtooth flounder Atheresthes stomias. High levels of Hg
found in two lots of sablefish fed 50% dogfish was attributed to high
levels of Hg in dogfish.
1757.
Kerstetter, T.H., L.B. Kirschner and D.D. Rafuse. 1970. On the
mechanisms of sodium ion transport by the irrigated gills of
rainbow trout (Salmo gairdneri). Jour. Gen. Physiol. 56:
342-359.
Sodium uptake by trout gills obeyed a Michaelis-Menten rela-
tion, with a Km of 0.46 mM and proceeded unimpaired in absence of pene-
trating counterions; this could indicate existence of a coupled cation
exchange mechanism. Ammonia output was same as Na+ influx when external
Na+ concentration was 1 mM; this correlation did not hold at higher or
lower Na+ influxes. As Na+ influx increased, pH declined in irrigating
medium; authors suggest that exchanging cation is hydrogen. Aceta-
zolamide, a Na+ uptake inhibiter, also prevented downward pH shift.
Potential across gill was ~10 mv, body fluids positive, in NaCl solu-
tions up to 10 mM, and was little affected by changes in lower Na+
concentrations.
1758.
Ketchum, B.M.' and V.T. Bowen. 1958. Biological factors deter-
mining the distribution of radioisotopes in the sea. In
Proc. of Second Ann. U.N. Int. Conf. Peaceful Uses of Atom.
Energy - Vol. 18. Waste Treat. Environ. Aspect of Atomic
Energy, Geneva: 429-433.
Zn, and
copepod
Concentration factors (CF) for isotopes of Cs, Sr, Fe, Co,
Cd by various groups of marine biota are presented. CF for
Centropages sp. and Cs is 0.1 to 1; for Co it is 600. For the
175
-------
copepod Calanus sp. CF is 0.1 to 1 for Cs, 0.28 for Sr, 2.5 X 104 for
Fe, and 200 for Co. For squid Ommastrephes CF is 0.1 for Cd, 0.3 for
Sr, 104 for Fe, 200 for Co, 2 X 10~ for Zn, and 2 X 105 for Cs. For
the chaetognath Sagitta CF is 70 for Sr, 5 X 104 for Fe, and 104 for
Co. Other CF were 0.3 and 800 for Sr and Co in krill Euphausi~ and 60
for Co in the tunicate Salpa sp.
1759.
Khan, K.U. and Y. Hiyama. 1964. Mutual effect of Sr-Ca upon
their uptake by fish and freshwater plants. Records Oceanog.
Works Japan 7:107-122.
Six species of freshwater teleosts, molluscs and crustaceans,
6 species of freshwater algae and plants, and 3 species of marine fish
and shrimps .were reared in various concentrations of stable Ca and Sr
labeled by Sr-89 and Ca-45 to measure uPt~f through epithelial tissues.
Results fit exponential function y=a (I-e) where y was concentration
factor at time t and a,b were constants. In smaller sized fishes, the
concentration factor ranged between 30 and 40 (Cyprinus carpio, Oryzias
latipes); in large fishes the CF ranged between 5 and 10 (Misgurnus
anguil1icaudatus, Carassius auratus); in shrimps Xiphocardina compressa,
the CF was about 50. With exception of Spirogyra sp. and Myriophyllum
verticulatum, where CF ranged from 8 to 10, the CF in plants was 30 to
40. Strontium at 500 mg/1 was lethal for all fish. Uptake by animals
and plants was highest for both Ca-45 and Sr-89 in lowest solution of
Ca (1 mg/l) and Sr (1 mg/l), due to nutritional needs of these elements.
Goldfish subjected to chronic feeding of Ca-45 and Sr-89 reached
highest concentrations on 21st day.
1760.
Kharkar, D.P., J. Thomson, K.K. Turekian and W.O. Forster. 1976.
Uranium and thorium decay series nuclides in plankton from
the Caribbean. Limno1. Oceanog. 21:294-299.
Zooplankton, predominantly ca1anoids and cyc10poids, from the
Caribbean were analyzed for U-238, U-234, Th-232, Th-228, Ra-228,
Ra-226, Pb-2l0 and Po-210. Concentration factors in zooplankton rela-
tive to seawater (liters of SW eq. to 1 g plankton) were: 970 for
Po-2l0; 24 for Pb-210; 4.9 for Ra-226; 0.17 for U-238; and 20 for Th-228.
Pb-2l0 and Th-228 have similar concentration factors and are comparable
to reported fiber-scavenging experimental data on Pb-210 and Th-234.
Certain nuclides, such as Po-210, are concentrated more efficiently by
zooplankton but may be released rapidly to solutions in the mixed layer.
Actual flux of particles carrying radionuclides from mixed layer to
depth unidirectiona1ly cannot have the Po-210:Pb-210 ratio of bulk zoo-
plankton; thus, dominant transport agent for these nuclides from mixed
layer to depth cannot be unmodified zooplankton debris.
176
-------
1761.
Kiceniuk, J. and J.E. Phillips. 1974. Magnesium regulation in
mosquito larvae (Aedes campestris) living in waters of high
MgS04 content. Jour. Exp. BioI. 61:749-760.
Larvae of ~. campestris live in natural waters with seasonal
variations in magnesium content of 1 to more than 100 roM, while haemo-
lymph levels of Mg vary only from 1.5 to 4 roM. Field and laboratory
observations suggest an upper tolerance limit between 95 and 125 roM Mg.
Using observed mean drinking rates of 0.1 to 0.2 ul/h/mg (300% of total
body wt/day), rate of Mg excretion per larvae is 54 n mol/h and rate of
ingestion is 42 to 83 n mol/h, with ingested fluid and magnesium ions
being largely absorbed into haemolymph via midgut. Urinary concentra-
tions of Mg2+ ions was up to 2.8X greater than external media and up to
23X haemolymph. It is suggested that Mg is not excreted across the
general body surface; rather, malpighian tubules and hindgut are
largely responsible for Mg elimination from haemolymph.
1762.
Kifer, R.R. and W.L. Payne. 1968.
meal. Feedstuffs 31 Aug 68:32.
Selenium content of fish
Selenium contents in mg/kg, were determined for menhaden
(1.22 to 3.98), Peruvian anchovetta (1.05 to 1.71), and Norwegian
herring (1.73 to 3.43). Authors suggest that addition of 3 to 5% fish
meal to diets of chickens would meet their Se requirements of 0.05 to
0.1 mg/kg Se.
1763.
King, E.N. 1965. The oxygen consumption of intact crabs and
excised gills as a function of decreased salinity. Compo
Biochem. Physiol. 15:93-102.
Respiratory rate of whole crabs in 50% seawater compared to
that of normal seawater (S=360/00) decreased 50% in Maja verrucosa,
and 30% in Libinia emarginata, both stenohaline species, and increased
33% in Carcinus mediterraneus and 53% in Callinectes sapidus, both
euryhaline species. In excised gills under similar conditions, endo-
geneous respiratory rate increased 6% in Maja, 10% in Callinectes
collected in seawater (360/00), 30% in CaTIInectes collected in
brackish water (120/00) and did not change significantly in Carcinus.
Gills of Carcinus and Callinectes from both habitats showed a 2.5%
increase in water content on incubation in 50% seawater. In seawater,
gill respiration of brackish water Callinectes was significantly higher
than Callinectes from marine environments.
1764.
Kinne, O. 1964. The effects of temperature and salinity on
marine and brackish water animals. II. Salinity and
177
-------
temperature salinity combinations.
Ann. Rev. 2:281-339.
Oceanogr. Mar. BioI.
Literature on physiological responses of organisms to altered
salinities is reviewed with emphasis on total osmo-concentration,
relative proportion of internal solutes, ability to absorb and retain
dissolved gasses, and density and viscosity modifications. Salinity
factors may affect reproductive, developmental, and growth capabilities
of an organism. Ionic regulation mechanisms are discussed. Adapta-
tions for salinity stresses are examined in terms of genetic capabil-
ities. Combined effects of temperature and salinity are considered in
terms of metabolism and activity, reproduction, structure, and distri-
bution. Animals examined include coelenterates, echinoderms, annelids,
crustacea, molluscs, insects, sipunculids, elasmobranchs and fish. A
total of 382 references are listed.
1765.
Kirschner, L.B., L. Greenwald and T.H. Kerstetter. 1973.
Effect of amiloride on sodium transport across body sur-
faces of freshwater animals. Amer. Jour. Physiol. 224:832-
837.
Inhibition of Na influx
pipiens, and crayfish Procambarus
tively, occurred upon addition of
tion. Treatment had no effect on
in trout Salmo gairdneri, frog Rana
spp., by 79%, 46% and 90%, respec-
10-4 M amiloride to external solu-
efflux across body surface.
1766.
Kirschner, L.B., L. Greenwald, and M. Sanders. 1974.
mechanism of sodium extrusion across the irrigated
sea water-adapted rainbow trout (Salmo gairdneri).
Gen. Physiol. 64:148-165.
On the
gill of
Jour.
Sodium efflux across irrigated trout gill was rapid in sea-
water; but only about 25% the freshwater value. The difference corre-
lated with a change in the potential difference across gill (TEP); which
was about + 10 mV in SW, but 40 mV in FW. Both flux and electrical
data indicated that trout gills are permeable to a variety of cations
including Na+, K+, Mg2+, choline, and Tris. They are less permeable
to ~ions, with the ratio of permeability coefficients P~ :PK:PCl
estlmated as 1:10:0.3. The TEP was shown to be a diffus13n potential
determined by these permeabilities and the extant ionic gradients in
SW, FW, and other media. Na efflux appeared to be diffusive in all
experiments. A model is proposed which accounts for passive net dif-
fusion of Na+ and K+ across gill and dependence of TEP on external
concentrations. The question of whether there is an active component
to Na extrusion is still unresolved.
178
-------
1767.
Klass, E., D.W. Rowe and E.J. Massaro. 1974. The effect of
cadmium on population growth of the green alga Scenedesmus
quadracauda. Bull. Environ. Contamin. Toxicol. 12:442-445.
The freshwater algae ~. quadracauda was grown in Cd concen-
trations ranging from 0.0 to 610 ~g/l. Mean population size was not
affected below 6.1 ~g/l, but was inhibited at concentrations of Cd2+
of 6.1 ~g/l and above. Cd levels of 61 ~g/l and higher severely
inhibited growth. Enzyme inhibition is suggested to be a mechanism of
growth retardation. It was concluded that the 10 ~g Cd/l upper limit
for drinking water should be revised downward.
1768.
Klaunig, J., S. Koepp and M. McCormick. 1975. Acute toxicity
of a native murnrnichog population (Fundulus heteroclitus) to
mercury. Bull. Environ. Contamin. Toxicol. 14:534-536.
Murnrnichogs,estuarine cyprinodontiform teleosts, exposed to
0.86 mg HgC12/l for 96 h survived with no apparent deleterious effects.
Levels of 1.15 mg HgC12/l to the 96 h LC-50 of 2.0 mg HgC12/l pro-
duced the following among survivors: sluggish behavior, uncoordinated
swimming movements, and pronounced negative phototaxy. Increased
operculate movement and death within 24 h occurred during immersion
in 4.60 mg HgC12/l.
1769.
Kleerekoper, H., J.B. Waxman and J. Matis. 1973. Interaction
of temperature and copper ions as orienting stimuli in the
locomotor behavior of the goldfish (Carassius auratus). Jour.
Fish. Res. Bd. Canada 30:725-728.
Movements of single goldfish were monitored in a free choice
situation comprising zones of laboratory water, or water containing
0.010 mg Cull as CUC12, each at two temperatures, 21.1 I 0.1 and 21.5
I 0.1 C. Fish entered the Cu zone at 21.1 C significantly less fre-
quently and spent less time there per entry as compared to Cu-free
zone. The Cu zone at 21.5 C became significantly "attractive" to
fish in terms of both frequency of entry and time spent. Laboratory
water at 21.5 C was "attractive" to fish but became significantly more
so in presence of 0.010 mg Cu2+/l.
1770.
Klein, D.H. and E.D. Goldberg. 1970. Mercury in the marine
environment. Environ. Sci. Technol. 4:765-768.
Mercury levels in crabs, whelks, and scallops are several
orders of magnitude greater than comparable volumes of seawater.
Higher values of mercury are present in sediments near sewer outfalls
179
-------
as compared to similar deposits further removed; this was reflected
in mercury levels of benthic organisms.
1771.
Klemmer, H.W., C.S. Unninayer and W.I. Ukubo. 1976. Mercury
content of biota in coastal waters in Hawaii. Bull.
Environ. Contamin. Toxicol. 15:454-457.
! Total mercury in mg/kg wet wt in 58 different species of
fish, molluscs, crustaceans, and echinoderms, was determined. Con-
centrations ranged from undetectable «0.01 mg/kg) in 26% of samples
to 1.0 mg/kg in one sample. The overall mean value was 0.08 mg/kg.
For those organisms having a feeding habit in direct contact with
sediment, 0.022 mg Hg/kg was found in herbivores, 0.058 mg Hg/kg for
omnivores and 0.075 for carnivores. For organisms feeding above the
sediment-water interface, higher values were found in herbivores
(0.036). omnivores (0.070) and carnivores (0.080).
1772.
Knauer; G.A. 1970. The determination of magnesium, manganese,
iron, copper and zinc in marine shrimp. Analyst 93:476-480.
Mean metal content in pooled samples of two species of
penaeid shrimp, Penaeus aztecus and P. duorarum, were determined.
Values in mg/kg dry wt were 3520 for-Mg, 6.1 for Mn, 50 for Fe, 47
for Cu, and 62 for Zn.
1773.
Knauer, G.A. and J.H. Martin. 1973. Seasonal variations of
cadmium, copper, manganese, lead, and zinc in water and
phytoplankton in Monterey Bay, California. Limnol. Oceanogr.
18:597-604.
Mean (range) metal contents for surface water samples
collected over 1 year in Monterey Bay, in ~g/l, were: Cd 0.15 (0.02
to 4.7); Cu 1.3 (0.5 to 4.5); Mn 0.6 (0.3 to 3.5); Zn 6.5 (0.7 to 35);
and Pb 0.9 (0.2 to 2). Maximal values of phytoplankton metal contents,
in mg/kg dry wt, were: Cd 7, Cu 50, Mn 35, Zn 750, and Pb 40. Metal
levels in nearsho!e surface waters appeared to be more dependent upon
hydrographical fluctuations than biological factors, except for Cd,
which decreased during peak phytoplankton productivity. Most vari-
ability and highest concentrations of metals in phytoplankton occurred
during peak upwelling pulses. Phytoplankton metal levels appear to be
inversely related to biomass. For surface water between Hawaii and
Monterey, levels of Cu, Mn, and Zn were usually higher inshore than
offshore especially during periods of strong upwelling. Concentrations
of Cd and Pb were almost always an order of magnitude higher inshore.
180
-------
1774.
Knauss, H.J. and J.W. Porter. 1954. The absorption of inorganic
ions by Chlorella pyrenoidosa. Plant Physiol. 29:229-234.
Radiotracers were used to determine Ca, Fe, Mn, Zn, Cu, and
Sr in f. pyrenoidosa when nutrient concentration of element varied.
Absorption by algae was directly proportional to concentration of ele-
ment in nutrient solution. The percent of nutrient element removed by
cells ranged from 75 to 95% for Fe, 64 to 77 for Mn, 0.22 to 0.34 for
Ca, 0.61 to 0.79 for Sr, 15.6 to 39.6 for Cu, and 5.8 to 12.6% for Zn.
1775.
Kobayashi, J. 1971. Relation between the "i tai-i tai" disease
and the pollution of river water by cadmium from a mine. Adv.
Water Poll. Res. 1:1-32.
"Itai-itai" (ouch ouch) disease is an unusual chronic disease
affecting residents of the Jintsu River district in Toyama Prefecture,
Japan. Afflicted individuals had severe osteomalacia and suffered
intense pain. Since World War II about 200 cases have been discovered,
half of whom died, being most prevalent among older women. Post-mortem
analyses showed high residues of Cd, Zn and Pb in tissues of victims.
The cause of the disease was presumed associated with mine wastewater
containing heavy metals discharged into the drinking water supply
(Jintsu River). Associated with wastewater discharges was damage to
rice plants irrigated by the Jintsu River. There was a heavy accumu-
lation of Zn, Pb and especially Cd in patients' bones and internal organs,
soil, and plants. From these and other studies author concluded that
"itai-itai" disease was induced by cadmium in the wastewater from a
mine.
1776.
Kobayashi, N. 1971. Fertilized sea urchin eggs as an indicatory
material for marine pollution bioassay, preliminary experi-
ments. Publ. Seto Mar. BioI. Lab. 18(6):379-406.
As part of a larger investigation on marine water quality,
author investigated effects of various metals on sea urchin embryology.
All studies were conducted at 28 C with Anthocidaris crassispina in
static, raw seawater. Values bracketing the "no effect," "frank effect"
level, in mg/l were: 0.023-0.046 for Hg (as HgC12); 0.009-0.018 for
Hg (as phenyl mercuric acetate); 0.8-1.6 for Cd (as CdC1202 1/2H20);
0.6-1.2 for Ni (as NiC12°6H20); 0.065-0.13 for Zn (as ZnC12); 0.05-0.1
for Cu (asCuS0405H20); 17-170 for cobalt (as cobalt acetate); 6.6-13.2
for Mn (as MnC12°4H20); 4.2-8.4 for Cr+g (as CrClgo6H20); 1.1-2.2 for
Pb (as lead acetate); 2.1-4.2 for As (as AS20S); and 37-75 for B (as
HgBOg).
181
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1777.
Koblick, D.C. and C.D. Rufus. 1976.
calcium ions in osmoregulation in
Exp. Zool. 197:331-338.
The role of sodium and
Hydra littoralis. Jour.
Frequency of column contraction in Hydra as a measure of rate
of water elimination is maximal at 5 X 10-4 M Na+. This falls off
markedly at higher and lower concentrations, even though total medium
osmotic pressure is kept constant by replacement with K+. Reduction
in Ca2+ concentration causes a reduction in frequency of column con-
tractions. This reduction is half-maximal at about 4.8 X 10-4 M Ca2+.
Authors suggest that Na+ plays a regulatory role in the mechanism of
extrusion of water and salts from cells to the gastrovascular cavity.
1778.
Koch, H.J., J.C. Evans and E. Bergstrom. 1959. Sodium regula-
tion in the blood of parr and smolt stages of the Atlantic
salmon. Nature 184:283.
On abrupt transfer from fresh to seawater at the same tem-
perature, all 2 yr-old parr of Salmo salar died within 26 hrs. No
individuals in smolt stage, whether 1 or 2 yr old, died during the
same treatment. Upon transfer parr showed rising Na levels in blood;
smolt blood Na levels decreased to original level within 120 hrs.
1779.
Koczy, F.F. and H. Titze. 1958. Radium content of carbonate
shells. Jour. Mar. Res. 17:302-311.
Shells of 18 species of recent molluscs contained 0.359 X
10-10 to 3.58 X 10-10 g Ra/kg Ca. Exoskeleton of 4 species of recent
crustacea contained 2.0 X 10-10 to 8.1 X 10-10 g Ra/kg Ca. Fresh
phytoplankton contained 606 X 10-10 g Ra/kg Ca. It was estimated that
apparent half-life of Ra is one-third of natural decay constant due
to removal by biological processes.
1780.
Koeman, J.H., W.S.M. van de Ven, J.J.M. de Goeij, P.S. Tjioe and
J.L. van Haaften. 1975. Mercury and selenium in marine
mammals and birds. Science Total Environ. 3:279-287.
In marine mammals a 1:1 Hg/Se molecular increment ratio and
an almost perfect linear correlation between mercury and selenium was
found. Methylmercury, which tends to accumulate in fish and in food
chain more rapidly than other mercury compounds, comprised only a
minor portion of mercury in marine mammals, namely 2 to 14% in liver
a~d brain of adult seals. Due to these facts and that the Hg/Seratio
dlffers markedly in fish which make up diet of seals, it is proposed
that marine mammals are able to detoxify methylmercury by a specific
182
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chemical mechanism which involves Se. In fish-eating marine birds, the
Hg content is low compared to marine mammals, with no marked difference
between juvenile and adult birds. There was no statistical correlation
between Hg and Se in marine birds tested.
1781.
Koirtyohann, S.R., R. Meers and L.K. Graham. 1974. Mercury
levels in fishes from some Missouri lakes with and without
known mercury pollution. Environ. Research 8:1-11.
Mercurial fungicides used for golf greens maintenance can lead
to elevated levels of Hg in fish from lakes receiving greens drainage.
Largemouth bass Micropterus salmoides, was the most sensitive indicator
with Hg levels ranging from 1 to 7 mg/kg wet wt in fish taken from
lakes receiving drainage from treated greens. Mercury levels in other
fish species, in mg Hg/kg wet wt, ranged from 0.27 to 1.03 in green
sunfish Lepomis cyanellus, 0.37 to 1.11 in bluegill Lepomis macrochirus,
and 0.19 to 0.78 in channel catfish Ictalurus punctatus. Background
Hg levels in largemouth bass from impoundments in central Missouri are
0.1 to 1.2 mg/kg wet wt, depending on size and other factors. Many
lakes with no known source of Hg contamination produce bass which con-
tain significantly more than 0.5 mg/kg of Hg.
1782.
Koivusaari, J., I. Nuuja, R. Palokangas and M.-L. Hattula.
1976. Chlorinated hydrocarbons and total mercury in the
prey of the white tailed eagle (Haliaeetus albicilla L.) in
the Quarken Straits of the Gulf of Bothnia, Finland. Bull.
Environ. Contamin. Toxicol. 15:235-241.
Eagle populations have been dwindling and this appears to be
correlated with high concentrations of DOT, PCB and mercury (up to 26
mg/kg wet wt) in dead birds and addled eggs. Determination of PCB,
DOE, DOT and Hg in prey species of eagle showed Hg (in mg/kg wet wt)
in fish muscle ranged from 0.20 to 0.68; Hg in pectoral muscle of prey
birds ranged from 0.05 to 0.93.
1783.
Kolehmainen, S.E. 1972. The balances of Cs-137, stable cesium
and potassium of bluegill (Lepomis macrochirus Raf.) and
other fish in White Oak Lake. Health Physics 23:301-315.
Residues, uptake, and elimination rates of Cs-137, stable
Cs and K were determined over a 19 month period in bluegill and 6 other
fish species inhabiting a small radioactively-contaminated lake in
Oak Ridge, Tennessee. Cs-137 concentrations increased 4X in bluegills
over the weight range 1 to 70 g, but stable Cs concentration decreased
slightly with increasing fish size. In all species, concentrations of
183
-------
Cs-137 and stable Cs cycled seasonally with a minimum in summer and a
maximum in winter. Cs-137 concentration was highest in species feed-
ing on prey with high Cs-137 content. K concentrations dec~eased
slightly with increasing fish size, but did not fluctuate seasonally.
In bluegill the absorbed Cs-137 was eliminated by a two-component
exponential process. At 15 C, the rates were 0.09l2/day (fast com-
ponent) and 0.00370/day (slow component) in bluegill above 70 g. The
proportion of body burden eliminated by fast component was 37% after
a single feeding of food contaminated with Cs-137; at equilibrium,
proportion of body burden eliminated by fast component was only 2.3%.
Rates of elimination decreased with the increasing weight of bluegill.
There were no significant differences in rates of slow component be-
tween fish in equilibrium with Cs-137 intake and those receiving a
single feeding of Cs-137. K was eliminated at a single exponential
rate in bluegill: 0.019/day at 15 C. Intake rates of Cs-137, stable
Cs and K in bluegill were calculated on basis of seasonal changes in
body burden and elimination rates.
1784.
Komura, I., T. Funaba and K. Izaki. 1971. Mechanism of mercuric
chloride resistance in microorganisms. II. NADPH-dependent
reduction of mercuric chloride and vaporization of mercury
from mercuric chloride by a multiple drug resistant strain of
Escherichia coli. Jour. Biochem. 70:895-901.
Ability to vaporize a Hg-203 compound from Hg-203C12 was
demonstrated in crude cell-free extracts of a strain of E. coli which
had multiple drug resistance. NADPH was essential for vaporization,
while NADH had only a slight stimulating effect and NADP+ had no effect.
Oxidation of NADPH dependent on HgC12 was also demonstrated in crude
extracts, but HgC12-dependent NADH oxidation could be demonstrated only
when a partially purified enzyme preparation was used. It was suggested
that NADPH, and to a lesser extent NADH, act as electron donors for
enzymatic reduction of HgC12 prior to vaporization. This appears to be
a mechanism of resistance to HgC12 in E. coli strains having multiple
drug resistance. - ----
1785.
Komura, I. and K. Izaki. 1971. Mechanism of mercuric chloride
resistance in microorganisms. I. Vaporization of a mercury
compound from mercuric chloride by multiple drug resistant
strains of Escherichia coli. Jour. Biochem. 70:885-893.
Three strains of E. coli possessing multiple drug resistance
were resistant also to HgC12, though sensitive to Ni, Co, Cd and Zn.
As was true for resistance to chloramphenicol and tetracycline, the
HgC12 resistance could be transferred from a resistant strain of E.
coli to sensitive strains of ~. coli and Aerobacter aerogenes.
184
-------
Resistant strains could grow in 5.4 mg HgC12/l, whereas a sensitive
strain failed to grow in 2.7 mg HgC12/l. Cells of resistant strains
vaporized a form of radioactive Hg when incubated with Hg-203C12' while
cells of sensitive strain showed no such activity.
1786.
Kondo, I., T. Ishikawa and H. Nakahara. 1974. Mercury and
cadmium resistances mediated by the penicillinase plasmid in
Staphylococcus aureus. Jour. Bacteriol. 117(1):1-7.
Mercury resistance in S. aureus mediated by penicillinase
(Pc-ase) plasmid was based on changing the ion incorporated in the
cell into a somewhat innocuous form. This process was independent of
temperature and appeared controlled by an inducible enzyme. Killing
effect of Hg salts was not influenced by MgC12, CaC12, MnC12 and NaCl.
No vaporization of Hg was found in the case of Hg resistance in
staphylococci. Resistance to Cd ion was mediated by some protective
mechanism to retain the ion outside the cell. Pc-sensitive organisms
incorporated Cd ions into cells, whereas Pc-ase plasmid-carrying
organisms did not. Incorporation of Cd was temperature dependent and
did not take place at 4 C; Pc-sensitive organisms as well as Pc-resist-
ant organisms were resistant. Addition of CaC12 could eliminate kill-
ing effect of CdC12 with a dose-effective response.
1787.
Kopfler, F.C. and J. Mayer. 1967. Studies of trace metals in
shellfish. In Proc. Gulf and South Atlantic States Shell-
fish Sanitation Res. Conf.: 67-80.
Polarographic analyses of 136 oyster samples from South
Atlantic and Gulf Coast showed an average copper content of 19 mg/kg
wet wt with a range of 1-55 mg/kg; mean zinc content was 230 mg/kg
with a range of 24-820 mg/kg. At one sampling station cadmium was
1.12 mg/kg, chromium at trace levels, and lead undetectable. Zinc and
Cu levels at this station were 495 and 27 mg/kg wet wt, respectively.
Authors concluded that Cu content in oysters from these areas had not
increased significantly since 1932 values, and that no Cu and Zn levels
approached proposed interim guidelines of 100 Cu and 1500 Zn mg/kg
wet meats.
1788.
Kormondy, E.J. 1965. Uptake and loss of zinc-65 in the dragon-
fly Plathemis lydia. Lirnnol. Oceanogr. 10(3):427-433.
For early, middle, and late instar larvae of the dragonfly
exposed to concentrations of 0.005 to 0.5 ~ Ci Zn-65 C12/ml water, the
rate and amount of uptake were independent of temperature with
185
-------
equilibrium occurring in 24-48 hr. However, loss rate was significantly
greater at 10 C than at 20 and 30 C. Uptake and loss rates were inde-
pendent of body size (age), but amount concentrated was inversely
related to body size, the coefficient of accumulation being 68 in small
larvae and 28 in large larvae. Total uptake was directly proportional
to isotope availability in medium. Loss rates in field and laboratory
did not differ. Loss rate in dead animals was the same as in live
larvae: 95% of initial activity remained on the cast exuvium at molt-
ing and final metamorphosis. Uptake in dragonfly larvae occurs by sur-
face adsorption or cation exchange, thereby imposing constant use of
Zn-65 as an indicator of metabolic activity in energy flow studies.
But Odonata may effectively redistribute Zn, the bulk of which local-
izes in upper sediments.
1789.
Koryak, M., M.A. Shapiro and J.L. Sykora. 1972. Riffle zoo-
Qenthos in streams receiving acid mine drainage. Water
Research 6:1239-1247.
In stream localities immediately influenced by mine drain-
age, with pH's as low as 2.6, total acidity as high as 1130 mg/l as
CaC03, and average total iron up to 89 mg/l, the effect of acid mine
wastes on ecology and composition of benthic fauna is similar to
effect of organic pollution, i.e., high numbers of individuals com-
prised of a few species. In zones of active neutralization, where iron
hydroxides are deposited, species diversity slightly increases but bio-
mass is very low. The most numerous invertebrates in the stream sec-
tions exhibiting high acidity, low pH, and high Fe, are midge larvae,
especially Tendipes gr. riparius. Number of insect groups present
increases steadily with progressive neutralization until amphipods and
oligochaetes appear; indicating considerable improvement in water
quality. Supply of desirable benthic fish food (Tendipis sp.) is very
high in parts of stream where low pH, high acidity, and high ferrous
iron concentrations prevail. Unfortunately, fish cannot survive under
these conditions to utilize this abundant food supply. In less acidic
zones, where fish could possibly survive, deposition of ferric iron
drastically diminishes total biomass of benthic organisms and therefore
severely limits fish populations.
1790.
Kosta, L. and A.R. Byrne. 1969. Activation analysis for mer-
cury in biological samples at nanogram level. Talanta 16:
1297-1303.
Fish solubles contained between 68 and 76 nanograms Hg/g.
186
-------
1791.
Kramer, H.J. and B. Neidhart. 1975. The behavior of mercury in
the system water - fish. Bull. Environ. Contamin. Toxicol.
14:699-704.
At a mercury concentration of 1 mg/l, CH3HgCl was taken up
by fish 4X faster than Hg(N03)2 due to greater lipid solubility of
organic Hg. In the presence of complexing agents (10-7 mol/ml concen-
tration), accumulation rates decreased due to a screening effect by
complexing groups which allows only free Hg to enter cells. Tests
using CH3HgCl solutions of 0.1, r, 5, 10, and 20 mg Hg/l produced
higher accumulation (185, 1200, 4000, 9500, 17600 mg/kg, respectively,
after 10 days) and greater accumulation rates (17.4, 113, 400, 950,
1760 mg/kg-d, respectively) as Hg concentration increased. Release of
accumulated inorganic Hg occurs in a 2-step mechanism with a rapid
first step (T 1/2 = 4.2 d) and slow second step (T 1/2 = 67.7 d).
Accumulated organic Hg occurs in one slow step with a half life of 69
days. These results indicate that inorganic Hg is released l7X faster
than incorporated CH3HgCl, and that accumulated inorganic Hg is methyl-
ated in fish, then released in an identical manner as CH3HgCl.
1792.
Krasnov, E.V. and L.A. Pozdnyakova. 1975. Calcium-magnesium
ratios in the calcite of the shells of marine mollusks as a
criterion of specific and nonspecific reactions. Doklady
BioI. Sci. Proc. Acad. Sci. USSR 220:18-19.
Ca/Mg ratio of shells varied periodically with distance from
apex with limits of 110 to 470 for Mizuhopecten yessoensis and Swifto-
pecten swifti and 100 to 390 for Chlamys nipponensis. Ca/Mg ratios of
shells showed bimodal frequencies with maximal peaks of 150, 200, and
260 for C. nipponensis, M. yessoensis, and S. swifti, respectively, and
a secondary nonspecific peak of 280 to 330.- Paleoecological implica-
tions are discussed.
1793.
Krinsley, D. 1960. Trace elements in the tests of planktonic
foraminifera. Micropaleontology 6(3):297-300.
Planktonic foraminifera tests from Atlantic cores contained
12 to 82 mg/kg of MnO, 310 to 600 mg/kg of Ti02, 2700 to 6400 mg/kg of
A1203, 1700 to 3700 mg/kg of MgO, 1100 to 2100 mg/kg of SrO, 10 to 38
mg/kg of CuO and 20 to 30 mg/kg of NiO. Manganese concentrations in
planktonic foraminiferal tests appear to be related to location and
probably time. Copper is relatively constant with respect to geographic
location, with no apparent species effect. Sedimentary Mg is probably
superimposed on biogenic Mg in foraminiferal tests. Sr is relatively
stable from one core to another and is biogenic. Al and Ti are probably
sediment contaminants; little information is available on Ni.
187
-------
1794.
Krinsley, D. and R. Bieri. 1959. Changes in the chemical com-
position of pteropod shells after deposition on the sea floor.
Jour. Paleontology 33:682-684.
Modern planktonic pteropod shells contained metal levels, in
mg/kg, of 3 to 8 for AI, <8 to 20 for Cu, 110 to 360 for Mg, 950 to
1400 for Sr and 2 to 15 for Mn. Higher concentrations of AI, Mn and
Mg observed in shell? from sediment cores apparently result from uptake
after deposition. Both Cu and Sr levels were similar in planktonic
and core samples.
1795.
Kuhnert, P.M., B.R. Kuhnert, and R.B. Stokes. 1976. The effect
of in vivo chromium exposure on Na/K- and Mg-ATPase activity
in several tissues of the rainbow trout (Salmo gairdneri).
Bull. Environ. Contamin. Toxicol. 15:383-390.
After low-level chromium exposure of 2.5 mg Cr+6/l for 48
hrs, the mean tissue Cr levels in mg/kg wet wt increased from 0.22 to
2.16 in kidney, 0.18 to 0.58 in intestine, 0.11 to 0.54 in liver and
0.16 to 2.14 in gill. Sodium/potassium activated ATPase activity de-
creased after exposure for 48 hrs to Cr+6 in all tissues except gills.
Kidney was the only tissue showing a significant decrease in Na/K-
ATPase activity with 62% inhibition. A 50% reduction of intestinal
Na/K-ATPase was observed, but this was not statistically significant
at the 0.05 level. Changes noted in gill and liver were small and not
significant. Mg-ATPase activity was unaffected by accumulation of Cr
in tissue.
1796.
Kulikov, N.V., V.G. Kulikova and S.A. Lyubimova. 1972. The
movement of strontium-90 and cesium-137 along with fish eggs
during spawning season. Soviet Jour. Ecol. 2(4):296-299.
Radioactivity levels per kg wet wt in gravid female tench
Tinca tinea, and gravid female pike Esox lucius, minus stomachs and
intestines, were 0.21 X 10-9 and 0.2~10-~ ~ Ci for Sr-90, and 1.17
X 10-9 and 3.63 X 10-9 ~ Ci for Cs-137. For selected stable cations
these were 2.34 and 2.81 g for K, 4.55 and 6.33 g for Ca, and 2.13 and
8.21 g for Mg. Comparison of metal ratios of eggs to those of parent
gave selectivity coefficients for tench and pike, respectively, of 15.9
and 4.0 for Sr-90:Ca, 0.3 and 0.3 for Sr-90:Mg, 75.4 and 14.8 for
Mg:Ca, and 0.3 and 0.6 for Cs-137:K.
1797.
Kustin, K., K.V. Ladd and G.C. McLeod. 1975. Site and rate of
vanadium assimilation in the tunicate Ciona intestinalis.
Jour. Gen. Physiol. 65:315-328.
188
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Tunicates were reared in filtered seawater containing about
3.2 ug V/l. Using radioactive V-48 it was determined that vanadium is
not transported from seawater into the tunicate body via the tunic.
Site of V assimilation lies in the alimentary tract, with stnmach and
gut containing 510 and 257 mg/kg, respectively; other body parts con-
tained between 11 and 68 mg/kg. Rate of radiovanadium exchange is
first order with respect to V concentration over a 1000X increase in
V+5 above natural levels in seawater, and shows no saturation. V
accumulates in vanodocytes and forms a steady state concentration in
membranes of branchial net and gastrointestinal tract; with the latter
two possibly functioning as part of regulatory mechanism.
1798.
Kustin, K., D.S. Levine, G.C. McLeod and W.A. Curby. 1976. The
blood of Ascidia nigra: blood cell frequency distribution,
morphology, and the distribution and valence of vanadium in
living blood cells. BioI. Bull. 150:426-441.
Whole blood of ascidian A. nigra contained 51 mg V/l, present
partially as V3+. Green globular blood cells were primary V-bearers.
V occurred in all 5 layeTs of centrifugated blood cells. Authors
suggest that V may be present in more than one type of blood cell.
1799.
Kwapulinski, J., A. Buszman and G. Kwapulinska. 1976. A model
of the cumulation of 137Cs in the carp (Cyprinus carpio L.).
Acta Hydrobiol. 18:183-192.
An equation is presented to account for influence of Cs-137
in bottom sediments and from global fallout on Cs-137 content of carp;
results were comparable with published data on trout. Cs-137 content
in carp fry and second-year fish was weight dependent, with older fish
containing nearly 2X levels of fry.
1800.
Laarrnan, P.W., W.A. Willford, and J.R. Olson. 1976. Retention
of mercury in muscle of yellow perch (Perca flavescens) and
rock bass (Arnbloplites rupestris). Trans. Arner. Fish. Soc.
105:296-300.
Mercury-contaminated perch and bass were collected from Lake
St. Clair and stocked in two ponds. Twenty-six months later, mean
concentrations of total mercury in fillets had declined from 0.97 to
0.46 mg/kg in perch, and from 0.94 to 0.39 mg/kg in bass; mean weight
of the fish increased from 101 to 190 g in yellow perch and from 144
to 408 g in rock bass, during the same period. Reduction in mercury
concentrations was attributable to dilution by growth. Slight dis-
crepancies between theoretical and observed reduction of mercury
189
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concentrations suggest an
tissues to the muscle and
amounts of mercury during
initial redistribution of
a continued incorporation
growth.
residues from other
of background
1801.
Laevastu, T. and T.G. Thompson. 1956. The determination and
occurrence of nickel in seawater, marine organisms, and sedi-
ments. Jour. du Conseil 21:125-143.
Marine plankton samples from Puget Sound, Wash., contained
nickel levels ranging from 5.5 mg/kg dry wt (primarily diatoms) to 31
mg/kg dry wt (primarily copepods). Surface plankton showed concentra-
tion of Ni 2X that of deeper samples. Ni levels in fish muscle ranged
from 0.32 to 1.70 mg/kg dry wt. Razor clam Siliqua patula, contained
0.74 mg Ni/kg dry flesh. Calcareous skeletons of marine animals con-
tained from 0.31 to 0.46 mg Ni/kg. Water and sediments were also
examined.
1802.
Lahlou, B. and W.H. Sawyer. 1969. Sodium exchanges in the toad
fish, Opsanus tau, a euryhaline aglomerular teleost. Arner.
Jour. Physiol.~6(5):1273-l278.
Rate constants for Na turnover and total Na outflux rate in
toadfish were 15.6% and 805 ~Eq/hr per 100 g. Upon transfer to fresh-
water; Na outflux dropped by 90% immediately and then continued to
decrease for several days. Fish kept 4 to 11 days in freshwater re-
mained in negative Na balance. Euryhalinity of toadfish may be
explained in part by ability to reduce Na outflux instantaneously by
an "exchange diffusion," followed by a further slow reduction on
transfer to freshwater.
1803.
Lake, P.S. and V.J. Thorp. 1974. The gill lamellae of the
shrimp Paratya tasmaniensis (Atyidae: Crustacea). Normal
ultra structure and changes with low levels of cadmium.
Eighth Int. Congo Electron Microsc., Canberra, Australia,
Vol. II: 448-449.
f
Paratya exposed for 96 hrs to 0.03 and 0.05 mg/l of cadmium
(about one-tenth of the LC-50 (96 hr) level) exhibited accumulation of
granules (mean diameter of 470 AO) in some mitochondria, mitochondrial
degeneration, dilation of intercellular spaces, and a dilation of rough
endoplasmic reticular membranes. Effects were not as pronounced in
thin regions of cytoplasm or in other cell types.
190
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1804.
Lande, S.P. and S.I. Guttman. 1973. The effects of copper
sulfate on growth and mortality rate of Rana pipiens tad-
poles. Herpetologica 29:22-27. ----
Fertilized Rana pipiens eggs were not affected by copper
concentrations ranging from 0.04 to 1.56 mg/l Cu (as CuS04)' Tadpole
LC-50 (72 h) was 0.15 mg/l Cu; LC-lOO (72 h) was greater than 0.16
mg/l Cu and less than 1.25 mg/l Cu. Total mortality occurred within
4 days after hatching in concentrations of 0.31, 0.62 and 1.56 mg/l
Cu. Weights of tadpoles grown in 0.06 and 0.16 mg/l Cu were lower
than controls and those grown in 0.04 and 0.05 mg/l Cu. It appeared
that as the size of the tadpole increased, the survival time increased
such that the correlation coefficient (r) was +0.74 (P=>0.05).
1805.
Lansing, A.I. 1942. Some effects of hydrogen ion concentration,
total salt concentration, calcium and citrate on longevity
and fecundity of the rotifer. Jour. Exp. Zool. 91:195-211.
Experiments were conducted on 3 species of freshwater roti-
fers, Euchlanis triquetra, Rotifer vulgaris, and Proales sp. Fertility
and longevity of Euchlanis were increased in alkaline solutions com-
pared with solutions of pH 6.0 and 7.0. Solutions of pH 4.0 and 5.0
were toxic. Rotifer vulgaris deposited more eggs/d and had a longer
life span at a total salt concentration of 0.02% than 0.04%; Proales
had a shorter life span but deposited 2X number of eggs at 0.02% than
0.04%. Fertility of Proales was not appreciably altered in low and high
calcium concentrations; but life span was markedly increased in low Ca
solutions. Periodic immersion of Proales in sodium citrate results in
approximately a 50% increase in life span and an increase in average
number of eggs laid per day.
1806.
Larimer, J.L. and A.F. Riggs. 1964. Properties of hemocyanins -
I. The effect of calcium ions on the oxygen equilibrium of
crayfish hemocyanin. Compo Biochem. Physiol. 13:35-46.
Oxygen affinity of hemocyanin from crayfish Procambarus
simulans, is greatly decreased by dialysis between pH 6.5 and 8.0. This
effect is further reduced by addition of Ca2+ at 0.4 g/l, or Mg2+ at
1.28 g/l. Since Ca2+ concentration in crayfish blood changes during
molting, it is suggested that Ca2+ modifies the 02 transport function
of hemocyanin by changing degree of aggregation.
1807.
LaRock, P.A. and H.L. Ehrlich. 1975. Observations of bacterial
microcolonies on the surface of ferromanganese nodules from
191
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Blake Plateau by scanning electron microscopy.
Ecol. 2:84-96.
Microbial
Microcolonies of rod- and coccus-shaped bacteria were attached
by slime to the surface of ferromanganese nodules.
1808.
Larsson, A. 1975. Some biochemical effects of cadmium on fish.
In Koeman, J.H. and J.J.T.W.A. Strik (eds.). Sublethal
effects of toxic chemicals on aquatic animals. Elsevier Sci.
Publ. Co., Amsterdam: 3-13.
Exposure for 11 to 15 days to subacute levels of cadmium (1-10
mg Cd2+/l) caused blood anemia and hyperglycemia in teleosts. After
exposure for 15 days to 10 mg Cd2+/l, flounders (Pleuronectes flesus L.)
exhibited a decrease in hematocrit from 21% to 17%, a decrease in hemo-
globin, and an increase in blood glucose levels by 75%. Long-term ex-
posure of 4 and 9 weeks to sublethal cadmium levels of 0.005 to 0.500
mg Cd2+/l had similar effects. After 9 weeks exposure to 0.005 mg Cd/I,
hematocrit of P. flesus dropped from 22.1% to 16.0%, hemoglobin values
decreased from-6.l to 4.4 g/IOO ml, and blood glucose levels rose from
24.7 to 29.2 mg/IOO mI. In addition, cadmium seriously affected blood
plasma levels of potassium, calcium, magnesium and inorganic phosphate.
Observed effects of cadmium in fish are discussed in relation to cadmium
toxicosis in mammals, man included.
1809.
Laurie, R.D. and J.R.E. Jones. 1938. The faunistic recovery of
a lead-polluted river in North Cardiganshire Wales. Jour.
Animal Ecol. (Britain) 7: 272-286.
In the Lower Rheidol River, a total of 14 species of arthro-
pods were present between 1919 and 1921, during which Pb concentrations
were 0.2 to 0.5 mg/l water. Lower Pb contents of <0.02 mg/l, except
for occasional peaks of 0.4 mg/l, were accompanied by increased species
counts of 29 in 1922 and 103 in 1932. Sticklebacks Gasterosteus
aculeatus, which is one of the most sensitive species to lead in the
Rheidol, died after 14 days exposure to 0.1 mg Pb/l water, which was
maximum recorded Pb concentration in the Lower Rheidol for several
years prior to 1938. At the present concentration of 0.02 mg Pb/l,
fish could survive indefinitely, suggesting that Pb concentrations no
longer endanger fish. Trout Salmo trutta were abundant from 1932.
Authors concluded that river fauna had recovered fully from previous
Pb pollution.
192
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1810.
Lawrence, J.M. 1956. Preliminary results on the use of potassium
permanganate to counteract the effects of rotenone on fish.
Prog. Fish-Cult. 18(1): 15-21.
. Potassium permanganate counteracts toxic action of rotenone to
fish by oxidizing rotenone to a nontoxic form. When tap water was used
in aquaria, 0.05 mg/l rotenone was effectively detoxified by 2 mg/l
KMn04 over the temperature range 7 to 27 C. In field trials on ponds
and streams, concentrations of KMn04 ranging from 2.0 to 2.5 mg/l suc-
cessfully detoxified 0.05 mg/l rotenone. In aquaria at a temperature
of 27 C, LC-lOO (minimum concentration of KMn04 that killed all fish)
for bluegills was 3 mg/l; for largemouth bass this was 4 mg/l, and for
fathead minnows 5 mg/l. At 14.5 C, LC-lOO for bluegills and largemouth
bass was approximately 5 mg/l. Use of potassium permanganate apparently
had no harmful effects on waters treated but owing to its fungicidal
action may have beneficial effects on any fish present or those added
immediately to such treated waters.
1811.
Lay, B.A. 1971. Applications for potassium permanganate in fish
culture. Trans. Amer. Fish. Soc. 100(4):813-816.
By oxidizing organic and inorganic materials which consume
oxygen, potassium permanganate in amounts of 2-6 mg/l indirectly in-
creases soluble oxygen thereby preventing fish kills in culture ponds.
Diseases including fungi, some protozoans, parasitic copepods, and mono-
genetic trematodes, have been effectively controlled by KMn04' At con-
centrations of 2.0-2.5 mg/l, KMn04 will neutralize toxicity of 0.05 mg/l
rotenone, and 3.0 mg/l may detoxify 0.005 mg/l antimycin. Previous
toxicity studies have determined that LC-O (maximum concentration where
no fish killed) for catfish at 25 C is 9.1 mg/l for 1 hr and 3.2 mg/l
for 24 hr. The LC-lOO (all fish killed) for guppies is 20 mg/l; for
bluegills, walleyes, and sauger, the LC-lOO was 3 mg/l; for largemouth
bass, 4 mg/l; fathead minnow, 5 mg/l; and goldfish, 6 mg/l. KMn04 may
effectively control nuisance algae without harming fish.
1812.
Lebedeva, M.N. and A.I. Shtevneva. 1975. Heterotrophic micro-
flora fouling and its influence upon the corrosion of metals
in the oxygen and hydrosulphuric zones in the Black Sea.
Okeanology 15(4):649-654. (In Russian, English summary!
An aluminum alloy (Amg-6l) is more resistant to bacterial
fouling than steel (St. 3, Yu. 3). Fouling by heterotrophic microflora
in an oxygen-rich zone is 3 to l5X that in hydrosulphuric zone, with
maximum rates in autumn and minimum rates in winter.
193
-------
1813.
LeBlanc, P.J. and A.L. Jackson. 1973. Arsenic in marine fish
and invertebrates. Marine Poll. Bull. 4(6):88-90.
Background levels of arsenic in organisms near a proposed
mine site on the Pacific coast of Canada were determined. The highest
concentrations of arsenic (in mg/kg wet wt) in muscle or soft parts of
invertebrates was: 37.8 in Cancer magister (crab); 15.6 in Macoma sp.
and Clinocardium sp. (clams); 5.9 in Hexanchus griseus (shark); 5.6 in
Squalus acanthias (dogfish); 16.2 in Raja sp. (skate); 10.3 in Hydro-
lagus colliei (ratfish); <0.4 in Oncorhyncus sp. (salmon); <0.4 in
Salmo gairdneri (steelhead); 0.3 in Olphiodon elongatus (cod); 2.6 in
Sebastes sp. (rockfish); 0.8 in Hexagrammos sp. (greenling); and 11.5
in Psettichthys me1anostictus and Parophrys vetulus (sole). Author
concludes that arsenic accumulates in marine fishes and invertebrates
and may be a micronutrient.
1814.
Lee, G.F. and W. Wilson. 1974. Studies on the Ca, Mg, and Sr
content of freshwater clamshells. Wisconsin Acad. Sciences,
Arts and Letters 62:173-180.
Different laminar layers of Lampsilis siliquoidea rosacea
shell from 3 Wisconsin lakes had concentrations of 371-451 g Ca/kg,
33-216 ~g Sr/kg, and ~7-102 mg Mg/kg. .Ratio~ of Sr/Ca extended from
61 x 10 to 258 x 10 6; for Mg/Ca ratlos thlS was 115 x 10-6 to 431 x
10-6. In 3 different Wisconsin lakes shells contained 413 g Ca/kg of
shell, and exhibited slightly different Sr/Ca and Mg/Ca ratios; this
could be explained by differences in water content of Ca, Mg, and Sr.
1815.
Lem~e, J.C., J. Ancellin, and A. Vilquin. 1970. Contaminations
de crevettes roses (Leander serratus Pen.) au moyen du
caesium 137 par voie alimentaire. Radioprotection 6(2):133-
142. (English abstract)
Shrimps were fed mussels contaminated with Cs-137. A sharp
rise in contamination was noticed after each meal followed by partial
decontamination. Residual contamination was in the range of 15% of
diet activity. A comparison between the importance of contamination
from either diet or environment showed that the latter was higher.
1816.
Lett, P.F., G.J. Farmer and F.W.H. Beamish. 1976. Effect of
copper on some aspects of the bioenergetics of rainbow trout
(Salmo gairdneri). Jour. Fish. Res. Bd. Canada 33:1335-1342.
Initial response of trout exposed for 40 days to 0.0 to 0.3
mg Cull (the LC-50 value at 96 hr ranged from 0.25 to 0.68 mg/l) was
194
-------
cessation of feeding. Thereafter, food intake rates returned to con-
trol levels. Growth rate of trout exposed to 0.075 to 0.225 mg Cull was
initially depressed but approached control values after 40 days. During
this period, the lipid, protein, and moisture of fish exposed to Cu did
not change. Initial growth retardation was not attributable to inter-
ference with digestion.
1817.
Lewin, J. and C.H. Chen. 1976. Effects of boron deficiency on
the chemical composition of a marine diatom. Jour. Exp.
Botany 27:916-921.
Cells of the marine pennate diatom Cylindrotheca fusiformis,
multiplied in complete nutrient medium (containing 0.5 mg B/l) with a
generation time of 11 hr. In a boron-deficient culture medium (0.02 mg
B/l), generation time was 90 hr. Comparison of chemical compositions
of logarithmically growing cells of each culture condition showed that
in boron deficient cells, the concentration of protein, carbohydrates,
and RNA was depressed below control cells, that DNA showed no change,
and that lipids, phenolic compounds, and unaccounted-for organic frac-
tions all increased.
1818.
Lewis, G.B. and A.H. Seymour. 1965. Distribution of zinc-65 in
plankton from offshore waters of Washington and Oregon, 1961-
1963. Ocean Science Ocean Eng. 1965:956-964.
Distribution of zinc-65 in unsorted plankton consisting of
crustaceans, ctenophores and phytoplankton and collected within 220 km
of the Columbia River mouth, conformed to the general pattern of hori-
zontal distribution of Columbia River water. Zinc-65 was detected in
202 of 238 samples. The maximum value in picocuries per gram dry wt
was 1,300; arithmetic mean was 132; geometric mean 47. Zinc-65 values
showed seasonal changes and a close relationship with zinc-65 in river
water.
1819.
Lewis, M.L. 1976. Effects of low concentrations of manganous
sulfate on eggs and fry of rainbow trout. Prog. Fish-Cult.
38:63-65.
Groups of trout eggs exposed to 0, 1, 5, and 10 mg/l of
manganous sulfate for 29 days exhibited 7, 12, 22 and 30% mortality,
respectively. Most sensitive periods were at day 7 when eye pigments
appeared, and at hatching (day 29). In avoidance tests, fry were
unable to detect high (10 mg/l) levels of manganous sulfate.
195
-------
1820.
Lewis, S.D. and W.M. Lewis. 1971. The effect of zinc and
copper on the osmolality of blood serum of the channel cat-
fish, Ictalurus punctatus Rafinesque, and golden shiner,
Notemigonus crysoleucas Mitchi1l. Trans. Arner. Fish. Soc.
100 (4) : 639-643.
Exposure of fish to 2.5 and 5 mg/l Cu or 8.12 and 30 mg/l Zn
produced reductions in blood serum osmolality. Mortality occurred when
osmolality dropped below 230 mOsm (5.0 mg/l Cu for golden shiner, 2.5
mg/l Cu and 12 to 30 mg/l Zn for channel catfish). With Zn, osmotic
drop is principally re'lated to damage to head and gill areas of fish.
In presence of excess calcium there is no precipitation of mucus, no
respiratory distress, and no mortality. Addition of NaCl to water with
Cu or Zn also prevented distress symptoms and mortality? but caused
osmolality in fish to increase over levels of NaCl solution alone.
Authors suggest that heavy metals affect head or gill area of fish with
a subsequent drop in salt concentration of blood.
1821.
Lindahl, P.E. and E. Schwanbom. 1971. A method for the detec-
tion and quantitative estimation of sublethal poisoning in
living fish. Oikos 22:210-214.
Swimming ability of roach Leuciscus ruti1us, in a rotary flow-
ing water channel was used to evaluate sublethal poisoning. On accelera-
tion of the device from zero to the maximum number of revolutions per
minute (40 to 60 r.p.m.) the "critical r.p.m." is that which the fish
is unable to compensate for torque and forced to rotate. Exposure to
about 10 ~g/l of methylmercuric hydroxide (MMH) significantly decreases
the critical r.p.m. Decreases in critical r.p.m. of fish exposed to
MMH was linearly correlated to mercury residues per unit wet wt of
muscle.
1822.
Lindberg, E. and C. Harriss.
estuarine plant detritus.
1974. Mercury enrichment in
Marine Poll. Bull. 5:93-95.
Relative mercury concentrations are enriched by a factor of
10 in decomposition products of the red mangrove, Rhizophora mangle,
compared with living plant tissue. The mercury content of mangrove
detritus is 3 to 30 times higher than values reported for marine phyto-
plankton. It was concluded that detritus formation represents a
natural mechanism for mercury enrichment in estuarine food chains.
1823.
Lloyd, R. and D.W.M. Herbert. 1962. The effect of the environ-
ment on the toxicity of poisons to fish. Jour. Inst. Public
Health Eng. 61:132-145.
196
-------
Toxicities of monochloramine (as Cl), un-ionized ammonia,
copper sulphate, zinc sulphate, and anionic detergents are discussed
as functions of chemical and physical properties of the water. Increas-
ing temperature decreases survival times, perhaps due to metabolic rate
increases, but relation between survival time and temperature is not
the same for all fish species. For zinc, there is a threshold concen-
tration at which there is no temperature effect. Toxicity of metal
salts may be reduced in alkaline water by formation of an insoluble
basic salt, however, susceptibility of fish to ions remaining in solu-
tion can be reduced by increasing Ca content. For example, fish accli-
mated to different total water hardness levels then exposed to dilu-
tions of Zn, Pb, and Cu salts showed a linear relation between the
logarithm of threshold concentration and logarithm of total hardness.
Exposing fish to graded concentrations of Pb, Cu, or Zn sulphates at
different dissolved oxygen levels, none of which were low enough to be
lethal, showed that toxicities increase markedly with decreasing
dissolved 02 levels. Authors suggest that this increase in toxicity
may be due to increased water flow over gills as 02 content decreases.
Since gills are site of action or absorption for most toxins, this
increased water flow brings more poison into contact with fish. When
poisons were present in mixtures, it was found that the threshold for
the mixture was reached when the sum of the fractions reached unity.
1824.
Lock, R.A.C. 1975. Uptake of methylmercury by aquatic organisms
from water and food. In Koeman, J.H. and J.J.T.W.A. Strik
(eds.). Sublethal effects of toxic chemicals on aquatic
animals. Elsevier Sci. Publ. Co., Amsterdam: 61-79.
Accumulation and effects of high (1-40 mg/l) sublethal con-
centrations of methylmercury to freshwater green alga Chlamydomonas
reinhardtii, cladoceran Daphnia pulex, and rainbow trout Salmo
gairdneri were determined. Exposure to increased methylmercury concen-
trations resulted in a lengthened lag phase in algal cultures, with
mean generation times of 44, 48, 51 and 61 hrs for cultures grown at
0, 1, 5, and 10 mg Hg/l respectively. At 20 mg Hg/l, growth was severly
retarded; at 40 mg Hg/l cells died. Methylmercury levels in living and
killed C. reinhardtii were the same during the first 10 hrs, suggesting
that inYtial uptake is passive adsorption rather than active uptake.
In daphnia and trout, methylmercury uptake rate was higher from medium
than food, but percentage uptake of Hg was 5 to lOX higher from food.
In both species, uptake of Hg at concentrations below 1.0 mg Hg/l was
linearly related to methylmercury concentrations in medium. At higher
levels, however, uptake rate decreased. Author suggests that increased
mucus production at respiratory surfaces and gut epithelium may limit
Hg uptake. Since dissolved methylmercury in water is present in con-
centrations below 1 mg Hg/l and cannot account for levels found in
higher trophic level organisms, and since practically all methylmercury
197
-------
is complexed to organic matter, it was concluded that organisms accumu-
late most of their methylmercury burden from food.
1825.
Lockwood, A.P.M. and C.B.E. Inman. 1975. Diuresis in the
amphipod, Gammarus duebeni induced by methylmercury, D.D.T.,
lindane and fenithrothion. Compo Biochem. Physiol. 52C:
75-80.
Effect of lethal and sublethal concentrations of methylmercury
and other substances on rate of urine production in marine amphipods was
examined. In 100% seawater, methylmercury initiated diuresis at 56 ~g/l,
which is less than 30% of the LC-50 (96 hr) value. Water permeability,
total body water, blood K levels and urine/blood ratio for (Cr-5l)-EDTA
remained unchanged in amphipods exposed to 100 ~g/l methylmercuric
chloride, a concentration which induces diuresis. Sodium uptake in-
creased at this concentration. Mechanisms of toxicant-induced diuresis
and its ecological significance are discussed.
1826.
Lorz, H.W. and B.P. McPherson. 1976. Effects of copper or zinc
in fresh water on the adaptation to seawater and ATPase
activity and the effects of copper on migratory disposition
of coho salmon (Oncorhynchus kisutch). Jour. Fish. Res. Bd.
Canada 33:2023-2030.
Acute toxicity bioassays were conducted at water alkalinity
of 68 to 78, water hardness of 89 to 99 mg/l as CaC03, and at 10 to
12 C. The LC-50 (96 hr) value for Cu, as CUC12, for yearling salmon
decreased from 74 ~g/l in November to 60 ~g/l in Mayas fish became
smolts. The LC-50 (96 hr) value for Zn, as ZnC12, for yearling coho in
April was 4600 ~g/l.
Exposures for 144 hr to sublethal concentrations of Zn in
freshwater had little effect on enzyme activity of Na+, K+-activated
ATPase in gill microsomes or on survival of fish transferred to sea-
water. Acute and chronic exposures up to 4128 hr of yearling coho
salmon to 5 to 30 ~g Cull in freshwater had deleterious effects on gill
ATPase activity, survival in seawater, and on downstream migration
after fish were placed in a natural stream. More severe effects were
produced in chronic exposures than in 144 hr exposures on downstream
migration and survival in seawater, but not on gill ATPase. Effects of
Cu began to occur within 24 to 72 hr and were often maximized within
120 to 144 hr of exposure.
198
-------
1827.
Lovelace, F.E. and H.A. Podoliak.
active calcium by brook trout.
158.
1952. Absorption of radio-
Prog. Fish-Cult. 14(4):154-
Trout held in water containing 5000 c/m/ml of radioactive
calcium for 24 hr had radioactivity values, in ~ Ci/g wet tissue of
0.0338 for gills, 0.00942 for gastro-intestinal tract, and 0.01820 for
body residue. It was concluded that Ca absorption by trout from water
was primarily through gills.
1828.
Lowman, F.G., R.F- Palumbo and D.J. South. 1957. The occur-
rence and distribution of radioactive non-fission products
in plants and animals of the Pacific Proving Ground. Univ.
Washington Rept. UWFL-5l:6l pp. Available from Tech. Inf.
Ser. Ext., Oak Ridge, Tenn.
Isotopes contributing to total radioactivity in clam kidney
collected from Eniwetok Atoll in 1956 as % of radioactive output were:
Ru-l06-Rh-l06 0.7; Zr-95-Nb-95 0.2; Y-9l 2.6; Mn-54 2.2; Fe-55 73.5;
Fe-59 0.2; Co-57 9.6; Co-58 9.2; and Co-68 1.8. Isotopes contributing
to radioactivity of various fish liver samples were Mn-54 (0.5 to
6.4%), Fe-55 (15.2 to 95.3%), Fe-59 (0 to 0.1%), Co-57 (0.2 to 8.1%),
Co-58 (0 to 0.9%), Co-60 (0.8 to 7.2%), Zn-65 (3.1 to 58.1%). Mn-54,
Zn-65, Fe-59, Co-60, Co-58 and Co-57 were not found in 6 species of
algae sampled during the same year. Zn-65 was the predominant radio-
isotope in liver, muscle, gut, lung, liver and kidney of terns.
Authors conclude that non-fission radioisotopes Mn-54, Fe-55, Fe-59,
Co-57, Co-58, Co-60 and Zn-65 account for almost all radioactivity in
marine animals.
1829.
Lucu, C., O. Jelisavcic, S. Lucic and P. Strohal. 1969. Inter-
actions of 233pa with tissues of Mytilus galloprovincialis
and Carcinus mediterraneus. Marine Biology 2:103-104.
Contamination factors (c.f.) in mussels after 20 days in
Pa-233, were 2500 for byssus, 150 for shell, 100 to 200 for digestive
tract, ~60 for gills, ~15 for reproductive system and 'vlO for muscle.
In the crab, c.f. 's were 2500 in gills, <200 in skeleton and digestive
tract and 5 to 20 in reproductive system and muscle; hemolymph was
nearly uncontaminated. High contamination of digestive tract and gills
was directly related to feeding and filtration, respectively. High
values in byssus, skeleton, gills and digestive tract were due to sur-
face adsorption. Complexing by EDTA had no effect on degree of con-
tamination of either mussels or crabs.
199
-------
1830.
Lunde, G. 1967. Activation analysis of bromine, iodine, and
arsenic in oils from fishes, whales, phyto- and zooplankton
of marine and 1imnetic biotopes. Int. Revue ges. Hydrobio1.
52(2):265-279.
The method developed for an1ayzing Br, I, and As in oils was
based on neutron activation and measurement of induced radioactivity by
a y-spectrometer without any chemical treatment of oils. Results for
freshwater fish gave concentrations (in mg/kg) of 0.3 to 7.7 Br, <0.1
to 0.9 As, and 0.1 to 9.1 I. Saltwater fish contained 2.0 to 47.0 Br,
0.5 to 15.5 As, and 2.7 I. Oil from cod (Gadus morrhua) contained
levels of 3.7 to 59.6 Br, 0.7 to 26.0 As, and 5.4 to 60.4 I. Oil from
herring (C1upea harengus) had 0.7 to 24.0 Br; 3.1 to 14.3 As, and 1.2
to 5.1 I. Whale oil contained 0.5 to 5.6 Br and 0.6 to 2.8 As. Con-
centrations of 20 to 150 mg/kg Br, but no As or I were found in fresh-
water plankton (rotifers, diatoms, dinoflagellates, blue-green algae),
whereas saltwater plankton contained 10,900 to 15,870 mg/kg Br and no
As. Values indicate that nutrition is an important factor. Limnetic
organisms generally contained less Br, I, and As than marine organisms;
fishes from coastal areas and fiords had higher Br content in relation
to As than fishes from the open sea; and Br:As ratio was higher in liver
than in tissues. Results also support earlier assumptions that I and
As are present as organic compounds, and suggest that Br is also. No
sign of Br, I, or As was observed in oil samples extracted from terres-
trial plants and animals.
1831.
Lunde, G.
meal.
1968. Activation analysis of trace elements in fish-
Jour. Sci. Fd. Agric. 19:432-434.
Fishmea1s produced from herring Clupea harengus, mackerel
Scomber scomber, capelin Ma110tus vi11osus, and Norway pout Gadus
esmarki were analyzed by neutron activation for mercury, bromine,
arsenic, selenium, antimony, copper, cobalt, iron, zinc, molybdenum and
tungsten. The distribution of these elements in the solid and aqueous
phases in boiled fish used as raw material for fishmea1 was also studied.
Highest values recorded, in mg/kg, for press cake, N liquor,
and factory-produced fishmeal, were as follows:
Se
As
Sb
Co
Cu
Zn
Fe
press cake
2.7
4.5
0.061
0.17
11.2
86.0
23.0
N liquor
15.1
15.2
<0.01
0.28
17.2
6.7
4.4
fishmea1
5.3
19.1
0.20
0.82
4.1
180
106
200
-------
Hg
Mo
W
0.41
0.26
<0.005
<0.01
<0.05
<0.005
0.40
0.16
0.030
1832.
Lunde, G. 1968. Analysis of arsenic in marine oils by neutron
activation. Evidence of arseno organic compounds. Jour.
Amer. Oil Chern. Soc. 45:331-332.
The arsenic content of phospholipid fractions separated from
cod1iver oil (Gadus morrhua) and herring oil (C1upea harengus) was
analyzed by means of neutron activation. The fractions were separated
on a silicic acid column by chloroform/methanol mixtures as eluting
agents. Results indicate that the arsenic appears as arseno organic
compounds. Two such compounds were evident in herring oil. The
arsenic ~ontent in one fraction was about 3000 mg/kg. Author suggests
that it is the fish itself or other organisms contained in the food
intake of the fish which synthesizes these arseno organic compounds.
The arsenic in seawater (about 3 ug/1) appears mainly as the inorganic
anion.
1833.
Lunde, G. 1969.
marine fishes.
Water soluble arseno-organic compounds in
Nature 224:186-187.
When raw fish is boiled, arsenic is enriched in the water
soluble phase (N-1iquor). Using radioactive ion exchange, it was
determined that this As is present chiefly as one or more arseno-
organic compounds in which organic As does not exchange with inorganic
As. Arsenic levels in mg/kg dry wt in N-1iquor ranged in herring
C1upeus harengus from 5 to 21, in mackerel Scomber scomber it was 3.1,
and in cape1in Mal10tus vi110sus from 3 to 8.
1834.
Lunde, G. 1970. Analysis of arsenic and selenium in marine raw
materials. Jour. Sci. Food Agric. 21:242-247.
Arsenic and selenium were determined in various marine organ-
isms: cod Gadus morhua, herring C1upea harengus, mackerel Scomber
scomber, Norway haddock Sebastes marinus, lobster Homarus vulgaris,
mussel Myti1us edu1is, clam Pecten maximum, oyster Ostrea edu1is, squid
Ommastrephes sagittatus, and whale Ba1aenoptera physa1us. The analyses
were performed on both the raw material and the water-soluble phase
after boiling (the N liquor). An enrichment of arsenic is observed in
the N liquor, compared with the raw material. Results indicate that
selenium is also enriched in the N liquor from fish, but not from
invertebrates. Arsenic values, in mg/kg, in dehydrated raw material
ranged from 0.36 (whale meat) to 11.6 (clam); for selenium these values
201
-------
were <0.5 (oyster, whole meat) to 8.4 (cod skin). For N liquor, arsenic
values ranged from not detectable in various fish tissues to 37 mg/l for
cod liver; for selenium, values ranged from not detectable to 4.5 mg/l
for haddock fillets.
The N liquor and the water-soluble phase of the enzyme-
hydrolyzed presscake (the water-insoluble phase after boiling) were
fractionated by molecular gel filtration. Fractions from these elutions
were analyzed for arsenic and selenium. Selenium was present in the
fractions with a molecular weight above about 5000. Arsenic was con-
nected with the lower molecular weight fractions, and may be present as
more arseno-organic compounds.
1835.
Lunde, G. 1970. Analysis of trace elements in seaweed.
Sci. Food Agric. 21:416-418.
Jour.
Trace element composition of algae collected from two dif-
ferent localities in Norway was determined by neutron activation and
atomic absorption. One locale was characterized by a relatively strong
influence of river water and industrial waste; the other locale was free
from this type of contamination. For all species of algae regardless
of collection locale the following values were observed in mg metal per
kg dry wt: arsenic, 10-109; copper, 6-63; molybdenum, 0.3-5.8; manga-
nese, 4-164; zinc, 53-520; cobalt, 0.1-5.2; antimony, 0.05-2.5; sele-
nium, 0.04-0.24; and iron, 33-931. Considerable differences in content
of trace elements were found between the Laminariaceae and Fucaceae. In
one species of alga (Laminaria hyperborea) content of As, Sb, and Zn
were higher in Feb-April than Sep-Nov. Marine algae, when compared to
terrestrial plants, generally contained higher concentrations of Zn,
Cu, and especially As.
1836.
Lunde, G. 1972. The analysis of arsenic in the lipid phase
from marine and limnetic algae. Acta Chern. Scand. 26(7):
2642-2644.
Arsenic, in mg/kg, in freshwater algae was: Chlorella
pyrenoidosa 0.5; Osci.llatoria rubescens 0.4 and 0.5; and Phaeodactylum
tricornutum 4.8. For marine algae these were: Chlorella ovalis 0.7;
Phaeodactylum tricornutum 3.6; and Skeletonema costatum 1.3. Algae
were cultivated using enriched media containing 1-3 ug/l As. If this
value is accepted, then the enrichment coefficient is approximately
200 to 5000.
1837.
Lunde, G. 1972. Analysis of arsenic and bromine in marine and
terrestrial oils. Jour. Amer. Oil Chern. Soc. 49:44-47.
202
-------
Oils extracted from marine teleosts, molluscs, echinoderms,
crustaceans, seaweeds, seagulls, and terrestrial birds, mammals, and
plants were analyzed for arsenic and bromine content. Lipid-soluble
bromine and arseno organic compounds are characteristic components of
marine anim~l and plant oils. Bromine-containing compounds seem to be
relatively stable, but the arseno-containing compounds are not. On
saponification, some of the As and Br compounds were found in the fatty
acid fraction while others appeared in the water soluble fraction.
Arsenic values in oil ranged from 4.7 to 84 mg/kg for marine macro-
fauna, 5.7 to 221 for marine seaweeds, <0.2 for terrestrial birds,
animals, and plants, and 0.6 to 13.2 mg/kg for seagulls (3 spp.).
1838.
Lunde, G. 1973. Trace metal contents of fish meal and of the
lipid phase extracted from fish meal. Jour. Sci. Food
Agric. 24:413-419.
In fish meal produced industrially and in the laboratory
from mackerel Scomber scomber, herring Clupea harengus, Norway pout
Boreogadus esmarkii, and capelin Mallotus villosus, the following trace
elements were determined: Cd, Zn, Pb, Cu, Fe, and Co; and, in the
lipid phase extracted from the meals: Se, As, Br, Zn, Fe, and Cu.
Levels of zinc, lead and iron are higher in the industrially produced
meals (up to 639, 3.8 and 757 mg/kg, respectively) compared to those
produced in the laboratory (up to 62, 0.52 and 64 mg/kg, respectively).
Assuming that the zinc to cadmium ratio occurring naturally in seawater
is about 100 to one, then results suggest that Zn seems to be enriched
relative to Cd in the fish meal where ratios of 100 to 1000 were
observed, with Zn ranging between 38-639 mg/kg and Cd ranging between
0.02-0.96 mg/kg. Other trace metals anlayzed in industrial fish meal
were Cu (2.3-13.8 mg/kg) and Se (0.6-4.2 mg/kg). The ranges in concen-
trations (in mg/kg) of these elements from the lipid phase of factory
produced fish meal are: As 4.6-23.2, Br 8.1-18.5, Se 0.07-3.3, P
1600-22,310, Zn 1.1-54, Fe 2.6-67, and Co <0.02-0.21; organic lipid-
soluble selenium compounds do not decompose during the production of
fish meal.
1839.
Lunde, G. 1973. Separation and analysis
inorganic arsenic in marine organisms.
Agric. 24:1021-1027.
of organic-bound and
Jour. Sci. Food
A method for separation of stable arseno-organic compounds
from inorganic arsenic and subsequent determination of both forms of
As is described. Inorganic, organic, and total As values are given for
shrimp Pandalus borealis, mussel Mytilus edulis, mackerel Scomber
scombrus, haddock Melanogrammus aeglefinus, cod Gadus morhua, capelin
Mallotus villosus, tunny Thunnus thynnus, coalfish Pollachius virens,
203
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herring Clupea harengus, defatted enzyme hydrolyzed cod liver Gadus
morhua, seaweed Laminaria hyperborea, extract of herring, extract of
coalfish, and herring meal. Inorganic As values ranged from 0.7 (ex-
tract of coalfish) to 3.2 mg/kg dry wt (herring); organic As ranged
from 3.4 (herring) to 139 mg/kg dry (seaweed); and total As ranged
from 4.2 (herring) to 142 mg/kg dry (seaweed).
1840.
Lunde, G. 1973. The analysis of organically bound elements
(As, Se, Br) and phosphorus in raw, refined, bleached and
hydrogenated marine oils produced from fish of different
quality. Jour. Amer. Oil Chern. 50:26-28.
When raw fish deteriorated during storage, selenium and
phosphorus contents of oils increased (Se from ~0.05 mg/l to >0.20
mg/l in 13 days), whereas bromine and arsenic contents remained con-
stant. During refining, As and P disappear almost completely whereas
Se content decreased by two-thirds. In the hydrogenation step Se
disappears relatively rapidly (decreasing to <0.02 mg/l) and Br more
slowly. Respective ranges of Se and As in fresh fish oils, in mg/l
were: 0.02 to 0.09 (Se) and 5.3 to 6.5 (As) for herring; 0.05 (Se)
and 4.6 to 5.2 (As) for mackerel; 0.09 (Se) and 9.1 (As) for capelin.
1841.
Lunde, G. 1973. The synthesis of fat and water soluble arseno
organic compounds in marine and limnetic algae. Acta Chern.
Scand. 27(5):1586-1594.
Two green algae (Chlorella ovalis and Chlorella pyrenoidosa),
one blue green (Oscillatoria rubescence) and two diatoms (Phaeodactylum
tricornutum and Skeletonema costatum), grown in fresh or salt water
or both, synthesize fat soluble and water soluble arseno organic com-
pounds from inorganic As5+ or As3+. At arsenic concentrations up to
100 ug/l, P. tricornutum and C. ovalis convert As to arseno organic
compounds at rates inversely proportional to As concentration. Further
increases (up to 1 to 10 mg As/I) lead to a constant arseno organic
synthesis rate. Arsenic is accumulated by factors of 200 to 3000 in
algae. Acid treatment converted different arsenolipids into a water
soluble product apparently identical to an arseno organic compound
isolated from fat-free algal material from field collections. Algae
seem to be an important source of arseno organic compounds found in
higher marine organisms.
1842.
Lytle, T.F., J.S. Lytle, and P.L. Parker. 1973. A geochemical
study of a marsh environment. Gulf Research Rep. 4(2): 214-
232.
204
-------
, Marsh plants and sediments of Harbor Island, Texas, were
analyzed for hydrocarbons and trace metals. For 14 species of marsh
plants, metals in mg/kg dry wt ranged from 9 to 170 for Mn, 47 to 200
for Fe, 0.06 to 0.65 for Co, 0.2 to 2.6 for Ni, 1.0 to 9.4 for Cu, 3
to 50 for Zn, 0.3 to 2.5 for Mo, 0.07 to 0.74 for Cd, and 0.8 to 4.2
for Pb. In some cases marsh plants may serve as sources for trace
metal enrichment in the sediments, and in other instances (Mo) as an
active depleting agent.
1843.
MacCarthy, J.J. and G.W. Patterson. 1974. Effects of cation
levels of the nutrient medium on the biochemistry of Chlorella
I. Concentration series. Plant Physiol. 54:129-132.
Effects of varying levels of Mg2+, K+ and Ca2+ from deficiency
to toxicity levels on Chlorella sorokiniana were observed. At lowest
level of 0.01 meq/l MgZ+, growth rate was 4.7 doublings/day. Increas-
ing the Mg2+ level increased growth rate to a maximum of about 8.6
doublings/day; this was maintained until toxic level of 200 meq/l was
reached. The sufficiency value, or lowest concentration giving maximal
growth, was 0.08 meq/l. Cellular levels of Mg2+, K+, total N, total
fatty acids and unsaturated fatty acids were reduced under conditions
of Mg2+ deficiency. As Mg2+ concentration was raised, level of each
fraction increased and remained high until Mg2+ toxicity levels were
reached. Saturated fatty acids were reduced by increasing Mg2+ concen-
tration whereas total lipid levels were unaffected; cellular suffi-
ciency level of Mg2+ was 0.29% of dry wt. At lowest K+ level of 0.003
meq/l, growth rate was 4.8 doublings/day; increasing K+ levels were
accompanied by increasing growth rates until K+ sufficiency level of
0.10 meq/l was attained. At K+ toxicity of 499 meq/l, growth rate
declined sharply. Cellular levels of Mg2+, K+, total N, and unsaturated
fatty acids were low when K+ was deficient and increased with increasing
K+; cellular sufficiency concentration of K+ was 1.2% of dry wt. Ca2+
had no effect except at toxicity (100 meq/l).
1844.
Macfarlane, N.A.A. and J. Maetz.
salt load of the NaCl excretion
Platichthys flesus in seawater.
101-113. .
1975. Acute response to a
mechanisms of the gill of
Jour. Compo Physiol. 102:
Flounder adapted to seawater were injected IP with a 50% salt
content solution based on fish composition. Plasma Na+ increased from
3.9 to 4.3 g/l and plasma Cl- from 5.4 to 6.1 g/l. Cl- spaces in-
creased by 25% and Na+ space by 15%. In non-NaCl-loaded fish, branchial
Na+ exchange is about 2.5 to 3X faster than Cl- exchange. In response
to the load, Na+ efflux augmented slightly while Na- influx remained
unchanged. Both Cl- efflux and influx increased by 50 to 80%, the
205
-------
overall effect being an increase of net Cl- excretion rate. Gill
potential in SW was unaltered in salt-loaded fish. Transfer of non-
loaded fish into freshwater was followed by an instantaneous decline of
both Na+ and Cl- effluxes and reversal of gill potential. Addition of
K+ (final concentration 0.39 g/l) into FW (FWK) produced a 150% Na+
efflux increase, a 40% increase of Cl- efflux, and simultaneous de-
+ -
polarisation of gill potential. In loaded fish, Na and Cl effluxes
into FW were enhanced by about 100%. K-dependent Na+ efflux increased
by about 100%, K-dependent C.1- efflux by at least 400%, while potential
decreased in FWK.
Observed fluxes cannot be explained by Goldman equation in
terms of free diffusion of Na+ and K+ across gills along their electro-
chemical gradients. Authors suggest that salt loading induced a stimu-
lation of Cl- pump associated to a Na/K exchange carrier and to a Cl-
exchange diffusion process.
1845.
Mackay, N.J., R.J. Williams, J.L. Kacprzac, M.N. Kazacos, A.J.
Collins and E.H. Auty. 1975. Heavy metals in cultivated
oysters (Crassostrea commercialis = Saccostrea cucullata)
from the estuaries of New South Wales. Austral. Jour. Mar.
Freshwat. Res. 26:31-46.
Results of a survey of metal levels in the Sydney rock oyster
Crassostrea commercialis are reported. Concentrations of Cu, Zn, Cd,
Pb and As in oysters sampled from the 19 important production areas in
New South Wales were generally low, and in terms of the National Health
and Medical Research Council recommendations for these metals there was
little or no health risk to consumers. The concentration ranges
observed, in mg element per kg wet wt, extended from 3 to 48 for Cu;
80 to 665 for Zn; 0.1 to 1.0 for Cd; 0.3 to 1.3 for Pb and 0.3 to 3.4
for As. The N.H.M.R.C. recommends 30 mg/kg wet for Cu, 1000 for Zn,
2.0 for Cd, 2.0 for Pb and 1.14 for As as trioxide.
Evidence is presented which indicates that metal concentra-
tions decrease with increasing age and wet wt of oysters. In oysters
sampled from a single estuary, there is a gradient of increasing metal
concentration with increasing distance upstream from the sea. Pollution
may be the cause of the relatively high concentrations in oysters from
this estuary, but further work will be required to verify this. The
variability of metal concentrations in oysters is discussed, and a
sampling method is suggested for future monitoring of metals in this
species.
1846.
Maclean, F.I., O.J. Lucis, Z.Z. Shakh and E.R. Jansz. 1972.
The uptake and subcellular distribution of Cd and Zn in
206
-------
microorganisms.
31:699.
Fedn. Proc. Fedn. Amer. Soc. Exp. BioI.
Percentages of cadmium uptake by organisms grown in 1.79 mg
Cd-l09C12/l and Zn-65C12 were 9% for Escherichia coli, a bacterium; 98%
for Anacystis nidulans, a blue-green alga; 80% forlGhlorella sp., a
green alga; and 95% for Crithidia fasciculata, a trypanosomid flagellate
Red alga Chondrus crispus, after 24 hr incubation in seawater contain-
ing 1.79 mg Cd-l09C12/l, took up 85% of the isotope. Both Cd and Zn
were bound to macromolecules in Crithidia. About 65% of Cd and 35% of
Zn were associated with a component of 10-12 thousand molecular wt in
Anacystis.
1847.
Maetz, J. 1970. Mechanisms of salt and water transfer across
membranes in teleosts in relation to the aquatic environment.
In Benson, G.K. and J.G. Phillips (eds.). Memoirs of the
Society for Endicrinology. Hormones and the Environment 18:
1-29.
Teleost "effector-organs" of osmoregulation exhibit widely
different functions in maintaining osmotic constancy- Differences in
drinking rate are accompanied by modifications of intestinal water-
pumping efficiency. Parallel changes in ion-absorption capacity and
passive osmotic water permeability are responsible for: increased
solute-linked water flow, increased gradient against which absorption
is accomplished, and augmented molar ratio of salt absorbed. All of
these responses are characteristic of adaptation to higher salinities.
In gills, transfer from hypo- to hypertonic media is accompanied by an
increase of Na and Cl exchanges. Salt absorption pump is replaced by
a salt excretion pump with a different mechanism. Decreased passive
water permeability is observed during salt-water adaptation. All alter-
ations induced by external salinity changes involve cellular processes
such as cell division and differentiation, and molecular processes such
as protein synthesis, particularly of enzyme systems associated with
ion pumps and carriers.
1848.
Maetz, J. and P. Pic. 1975. New evidence for a Na/K and Na/Na
exchange carrier linked with the Cl- pump in the gill of
Mugil capito in sea water. Jour. Compo Physiol. 102(2):85-
100.
Na and Cl efflux and gill potential were recorded simul-
taneously in seawater (SW)-adapted mullet. After transfer of teleosts
to freshwater (FW), an instantaneous decline of the Na efflux was
observed, explained by reversal of gill potential which occurred simul-
taneously. Addition of increasing amounts of K or Na sulphate to FW
207
-------
was followed by a progressive depolarization and by a progressive
increase of Na efflux. K was far more efficient than Na in producing
these effects. The change in gill potential was not of sufficient
magnitude to explain observed increase of Na efflux. Transfer from
SW to FW also produced a decline of the Cl efflux. Addition of K to
FW enhanced not only the Na but also the Cl efflux. On the basis of
these and other studies with SCN authors conclude that the branchial
Cl pump is associated with Cl exchange diffusion mechanism and with a
Na/K exchange carrier insensitive to potential changes.
1849.
Mahrla, Z. 1975. Properties of Ca stimulated ATPase from the
sarcotubular fraction of the crayfish muscle. Physiol.
bohemoslov. 24:452.
Concentrations of 0.1 to 10 mM Ca2+, in absence of Mg2+ ions,
stimulated ATPase activity. Sepcific properties of this ATPase are
given. Ca2+ ions can be substituted for other divalent cations in the
sequence: Ca2+ = Mn2+ > C02+, Sr2+ > Ba2+, Ni2+.
1850.
Mallett, J.C. III. 1972. Environmental aspects of cardiac
regulation in the marine teleost Tautoga onitis (Linnaeus).
Ph.D. thesis, Univ. Rhode Island, Dept. Zool., Kingston,
R.I. 98 pp.
Cardiac regulation in tautogs was studied to determine effects
of temperature, salinity, dissolved oxygen (DO) and cadmium on the fish's
electrocardiogram (ECG). Cardiac rates from non-intoxicated fish were
determined at 6 combinations of temperature and salinity. Hypoxic-
induced bradycardia was noted in each instance with a regression of
heart rateAon DO following an asymptotic regression model of Y = A -
BRX where Y = estimated heart rate in beats per minute (BPM), A =
asymptotic or average maximum heart rate, B = Y intercept, R = instan-
taneous rate of cardiac increase and X = DO in mg/l. Initial cardiac
response to extremely high, lethal concentrations of Cd++ (400 mg/l)
was bradycardia; greatest inhibition (22 BPM) at 106 min post-exposure
gave way to a relative increase to 50 BPM at 280 min post-exposure
followed by a decline in rate to mortality. No histological damage to
gills was evident after 240 min exposure. Elevated and diphasic T-waves,
AV blockage and extrasystolic ventricular activity and progressive
dimunition of QRS amplitude were recorded from Cd++ intoxicated fish.
Cardiographic techniques as an aid in determination of water quality
criteria for teleosts are suggested.
208
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1851.
Mandelli, E.F. 1975. The effects of desalinization brines on
Crassostrea virginica (Gmelin). Water Research 9:287-295.
Effects of desalinization brines, diluted with seawater to
temperature and salinity levels 5 and 10% above fluctuating non-perturbed
environmental levels and characterized by 19 to 43 ~g Cull, were assessed
using juvenile and adult oysters in 60 day seasonal bioassays. Mor-
tality, in 42 ~g Cull tests, reached 70 and 100% for adults and juve-
niles, respectively, with greatest mortality occurring during spring and
summer. Lowest concentrations of brines tested resulted in decreased
growth and enhanced infection of the pathogenic fungus Labyrinthomyxa
marina, which augmented mortality. Gametogenesis was inhibited by
brine dilutions containing 19.2 to 43 ~g total Cull. Accumulation and
subsequent clean water depletion rates reached 6.94 and 3.95 mg Cu/kg/
day, respectively, for exposure to 19 to 43 ~g Cull.
1852.
March, G.L., T.M. John, B.A. McKeown, L. Sileo and J.C. George.
1976. The effects of lead poisoning on various plasma con-
stituents in the Canada goose. Jour. Wildlife Diseases 12:
14-19.
Plasma glucose, free fatty acid and uric acid levels were
measured in moribund lead-poisoned geese Branta canadensis. Lead level
in a pooled plasma sample of lead-poisoned birds was 2.9 mg/l vs 1.2
mg/l in controls. Plasma glucose levels were only slightly elevated
from 292 to 356 mg/IOO mI. Uric acid (15.9 mg/l) was significantly
higher than controls (6.2) and free fatty acids were significantly
lower (727 vs 449 ~eq/l). Altered plasma levels were attributed to
increased protein catabolism and perhaps renal disfunction. Plasma
level of growth hormone was unchanged while prolactin in experimentals
was unusually high; increased prolactin levels may reflect an effort to
stabilize free fatty acids.
1853.
Marchand, M. 1974. Considerations sur les formes
chimiques du cobalt, mangan~se, zinc, chrome et
eau de mer enriche ou non de mati~re organique.
into Explor. Mer 35(2):130-142.
physico-
fer dans une
Jour. Conseil
Using radioisotopes of Co, Mn, Zn, Cr and Fe as tracers,
various physico-chemical forms of the isotopes were determined in a
natural seawater and the same seawater enriched with marine algal organic
matter. In natural seawater, 3 'days after introduction of radionuclides,
manganese and zinc were mainly in soluble cationic forms (Mn2+, Zn2+).
Cobalt appeared in two soluble cationic forms (Co2+ and CoCl+); a
slight anionic or neutral fraction was detected which may correspond to
209
-------
complexes with the ligand Cl-(CoC142-, CoC13-, COC12)' Chromium,
adsorbed strongly to walls, was present as a soluble chromate (Cr042-).
Iron was usually found in a colloidal state; the occurrence of an
anionic or neutral fraction points to colloidal dispersion rather than
a truly soluble form. Addition of organic matter on physico-chemical
equilibrium of zinc, chromium and iron is demonstrated by formation of
anionic, neutral (iron and chromium) or cationic (zinc) organo-metallic
complexes. The action of organic matter is potentiated with increasing
insolubility of nuclides. Occurrence of Fe and Cr organic complexes is
less frequent at reduced pH.
1854.
Maren, T.H. 1962. Ionic composition of cerebrospinal fluid and
aqueous humor of the dogfish, Squalus acanthias. I. Normal
values. Compo Biochem. Physiol. 5:193-200.
Average Na levels of dogfish plasma, cerebrospinal fluid
(CSF), and aqueous humor, in mg/l, were 5870, 6230, and 6350, respec-
tively; for K these levels were 257, 304, and 293 mg/l for plasma, CSF
and aqueous humor. Comparison with patterns in other vertebrates was
made; the outstanding difference is the lack of K deficit in dogfish
CSF.
1855.
Maren, T.H. 1972. Bicarbonate formation in cerebrospinal
fluid: role in sodium transport and pH regulation. Amer.
Jour. Physiol. 222(4):885-899.
In dogfish Squalus acanthias, rate constant values for HC03,
Na+, and Cl- entry into cerebrospinal fluid (CSF) from plasma were 1.9.
0.19, and 0.14 hr-l, respectively. Composition of CSF as secreted had
same Na concentration as plasma, with HC03 much higher and Cl- lower than
plasma. Data suggest that HC03 reaches the CSF by hydroxylation of
gaseous C02 at the choroid plexus, and probably at glia. Movement of
HC03 has an important influence on movement of Na and fluid.
1856.
Maren, T.H., P. Wistrand, E.R. Swenson, and A.B.C. Talalay. 1974.
The rates of ion movement from plasma to aqueous humor in the
dogfish, Squalus acanthias. Invest. Ophthalmol. 14(9):662-673.
Aqueous humor dynamics were studied in dogfish using isotopi-
cally labeled inulin, Na-, C1-, and HC03. Fluid production was 100
u1/h, with a turnover rate constant of 0.4 hr-l which is about half
,
~hat of mammals. Na+ diffusion rates, in uM/h from plasma to aqueous
lS ~25 and from aqueous to vitreous. 420; secretion rate of Na+ from
plasma to aqueous is 25. Rates and concentrations are also given for
HCO- and C1-. Sodium and chloride secretion is masked by the diffusion
210
-------
process; neither ouab~in nor acetazolamide yield measurable effects on
accumulation of these isotopes. Analyses of data suggest that newly
formed aqueous has similar Na+ concentration to plasma, but is high in
HCO- and low in Cl-. This anion pattern resembles mammalian aqueous
humor, and cerebrospinal fluid and endolymph of other vertebrates.
These and other data suggest that constant features of formation of
these fluids in all phyla are sodium transport, and formation of HC03
from C02'
1857.
Marking, L.L. and T.D. Bills. 1975. Toxicity of potassium
permanganate to fish and its effectiveness for detoxifying
antimycin. Trans. Arner. Fish. Soc. 104(3):579-583.
Ten species of freshwater teleosts showed LC-50 (96 h) values
for potassium perrnanganate (KMn04) ranging from 0.75 mg/l with channel
catfish Ictalurus punctatus, to 3.6 mg/l with goldfish Carassius
auratus. Toxicity of KMn04 is greatest at low temperatures, increased
alkalinity, and elevated pH. KMn04 is effective in detoxification of
antimycin. Half-life for antimycin exposed to 1.0 mg/l of KMn04 at
12 C, is 10, 7, 8, and 11 minutes at pH's 6.5, 7.5, 8.5, and 9.5,
respectively.
1858.
Marks, G.W. 1938. The copper content and copper tolerance of
some species of mollusks of the southern California coast.
BioI. Bull. 75:224-237.
Copper levels in several species of mollusks was determined,
with emphasis on variations ~ttributable to age or size. In the snail
Helix aspersa, amount of copper per unit wt of tissue increases with
increase in size; the reverse was observed in the California sea mussel;
in octopus Polypus bimaculatus, Cu remains constant. Samples of Pacific
coast seawater contained 0.001 mg of copper per kg. Upper limits of
copper tolerance of a few species of marine mollusks, under laboratory
conditions for 30 days, is in the range 0.10 to 0.20 mg of added copper
per kg seawater. However; the clam Paphia staminea tolerates much
higher Cu concentrations.
1859.
Martin, J.H. 1969. Distribution of C, H, N, P, Fe, Mn, Zn,
Ca, Sr, and Sc in plankton samples collected off Panama
and Colombia. Bioscience 19:898-901.
Approximately 130 plankton samples of unknown species com-
position were collected on both sides of the Isthmus of Panama during
wet and dry seasons and analyzed for Fe, Mn, Zn, Sr, Ca, Sc, and Fe.
211
-------
Abundance and distribution of Fe and Sc is dependent on several factors
including settling or transport by bottom scouring currents of inorganic
particulate matter which has entered marine environment via runoff.
Abundance and distribution of Ca, Sr, and Zn is strongly dependent on
standing crop and species composition of phytoplankton and zooplankton.
1860.
Martin, J.H. and W.W. Broenkow. 1975. Cadmium in plankton:
elevated concentrations off Baja California. Science 190:
884-885.
Plankton, including diatoms and copepods, were collected in
the northeast Pacific Ocean and analyzed for cadmium. Concentrations
were generally low (2 to 5 mg Cd per kg dry wt) in all samples except
for those collected off Baja California where high values (10 to 20
mg/kg) were consistently found on two cruises. Authors suggest that
increased Cd concentrations found south of San Diego were due to
elevated Cd levels in seawater.
1861.
Martin, J.H., P.D. Elliot, V.C. Anderlini, D. Girvin, S.A.
Jacobs, R.W. Risebrough, R.L. Delong and W.G. Gilmartin.
1976. Mercury-selenium-bromine imbalance in premature
parturient California sea lions. Marine Biology, 35:91-104.
High premature birth rates were observed in sea lions
Zalophus californianus since 1968. Liver and kidney from 10 normal
parturient, and 10 premature parturient mothers and their pups were
analyzed for Hg, Se, Br, Cd, Ag, Cu, Fe, Zn, Mn, K, Na, Ca, and Mg.
Results showed that Hg, Se, Cd, and Br levels were significantly higher
in livers of normal mothers and that these elements were in balance
with each other; this was especially pronounced for Hg, Se, and Br. In
mothers with high concentrations of these elements (e.g. Hg greater
than 800 ~g/g dry wt), atomic ratios of approximately 1 Hg:l Se:l Br
were observed. Atomic Se:Hg ratios were also near unity in abnormal
mothers; however, Br concentrations were always severely depressed in
these individuals. Normal full-term pups had higher hepatic levels
of Hg and Se, and near-perfect 1:1 Se:Hg atomic ratios were almost
always observed. In contrast, liver from premature pups appeared to be
deficient in Hg, and consequently, elevated Se:Hg ratios were always
found. Premature pups had increased concentrations of Na, Ca, and Br.
Levels of these elements were correlated with their Se:Hg ratios.
Amounts of Mn and Cu were reduced in premature pups and negatively
correlated with Se:Hg ratios. It is suggested that balance between
elements is more important than the absolute concentration when possible
effects of toxic elements are considered. Bromine may be important in
detoxification process involving Se and Hg and perhaps Cd as well; i.e.,
all darns with Br in balance with Hg, Cd, and Se had normal pups, while
212
-------
those that lacked sufficient Br had a premature pup. The
whether Hg detoxifies Se is also raised. All normal pups
Se: Hg atomic -ratios of less than 2.2, whi Ie all premature
hibited reduced Hg amounts and Se:Hg ratios above 3.4.
question of
displayed
pups ex-
1862.
Martin, J.H. and A.R. Flegal. 1975. High copper concentrations
in squid livers in association with elevated levels of silver,
cadmium, and zinc. Marine Biology 30:51-55.
Livers from Loligo opalescens, Ommastrephes bartrami, and
Symplectoteuthis oualaniensis were analyzed for Ag, Cd, Cu, Zn, and
Fe. Mean concentrations, in mg/kg dry wt, in Loligo from central Cali-
fornia were Ag 25, Cu 5,350, Cd 85, Zn 247, and Fe 111. Using highest
copper concentration found (15,160), a concentration factor of 2.1
million was obtained. Mean concentrations in Loligo from southern
California (in area where silver input was high) were: Ag 45, Cu 8,370,
Cd 121, Zn 449, and Fe 87. O. bartrami from open ocean averaged 12 for
Ag, 195 for Cu, 287 for Cd, 163 for Zn, and 399 for Fe. S. oualaniensis,
from open ocean, contained means of: Ag 24, Cu 1,720, Cd-782, Zn 513,
and Fe 319.
1863.
Martin, D.F-, M.T. Doig and R.H. Pierce. 1971. Distribution of
naturally occurring chelators (humic acids) and selected
trace metals in some west coast Florida streams, 1968-1969.
Florida Dept. Nat. Res., Mar. Res. Lab., Prof. Pap. No. 12,
St. Petersburg, Fla.
Concentrations of humic acid, Fe, Mn, Cu and Zn from 14
coastal streams in western Florida were measured to establish relation,
if any, on incidence of red tide. Correlations between rainfall, humic
acids and heavy metals, particularly Fe, were examined and their sig-
nificance in development of blooms of Gymnodinium breve were discussed.
1864.
Martin, J.-L.M. 1973. Iron metabolism in Cancer irroratus
(crustacea decapoda) during the intermoult cycle, with
special reference to iron in the gills. Compo Biochem.
Physiol. 46A:123-l29.
During intermoult cycle of Cancer, iron shows little varia-
tion in exoskeleton, hepatopancreas, hypodeum, hemolymph, and muscle.
Storage cells for iron occur in the hepatopancreas. Gills accumulate
comparatively large quantities of iron, up to 500 mg/kg wet wt. This
accumulation occurs during stage C3 of the intermoult cycle and is
maximum in stage C4. Iron is not detectable in gill raphe, but forms
213
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a coating around the branchial lamallae.
old gill, will be rejected at ecdysis.
This coating, along with the
1865.
Martin, S.G. 1971. An analysis of the histopathologic effects
of copper sulfate on the Asiatic freshwater clam, Corbicula
fluminea (Muller). Ph.D. thesis, Univ. of Washington,
Seattle, Wash. 109 pp.
Effects of copper sulfate on clam histopathology, behavior
and tissue recovery potential, were investigated. Clams exposed to Cu
at >250 ~g/l for longer than 14 days began to show effects due to star-
vation; no clams pumped at >500 ~g/l. More than half the clams sub-
jected to 50 ~g/l and lower pumped actively throughout the experiment;
however, some were affected at Cu2+ levels of 12 ~g/l. At low level
exposures to Cu (12 to 50 ~g Cu2+/l) initial histopathological changes
observed were increase in mucous production of digestive tubules, then
hemocytic infiltration and increased mucocyte size in gills, followed
by fragmentation, necrosis and cell sloughing in mantle epithelium.
At 125 to 250 ~g Cu2+/l, gills were affected first, followed by diges-
tive tubules and collecting ducts. At >250 ~g Cu2+/l, digestive
tubules were first affected, followed by gill and mantle epithelium.
The most important histological responses to Cu ion were: partial or
complete necrosis in all tissues; hemocytic infiltration and diapedesis;
transformation of the mantle, collecting duct, and stomach epithelial
tissues; and increased mucous production by hypertrophic gill mucocytes.
Clam tissues exposed to relatively high Cu concentrations, accumulated
Cu in significant amounts by 7 days; those at medium concentration did
not accumulate significant amounts until 15 days. Copper ion accumu-
lations were observed in gill, mantle epithelium, digestive tubules,
and hemocytes. Capacity for tissue recovery was high in clams exposed
to 12 ~g/l, but incomplete or partial in those exposed to higher con-
centrations,mantle epithelium showed highest recovery potential.
Author states that optimal continuous dosage for Asiatic clam control
appears to be in the vicinity of 25 ~g Cu2+/l.
1866.
Massaro, E.3. 1974. Pharmacokinetics of toxic elements in
rainbow trout. u.S. Environ. Proto Agen. Rept. EPA-660/3-
74-027. 30 pp.
Hg-203 labelled methylmercury (MeHg) was administered intra-
gastrically in a single dose (0.5 mg Hg/kg = 0.3 ~Ci/kg) to rainbow
trout Salmo gairdneri of mean wt 250 g. Fish were sacrificed from
1.0 hr to 290 days postadministration. Mercury-203 was taken up
rapidly by blood, gill, spleen, liver, and kidney and more slowly by
muscle, brain, and lens. After 290 days blood, spleen, kidney, liver,
and lens had concentration factors (C.F. = tissue Hg conc/Hg dose x
214
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final tissue wt/initial tissue wt) of about 1.0. In general, C.F.'s
had dropped by at least 2/3 from their maxima except for muscle, brain,
and lens in which the C.F. 's remained at maxima; about 64% of the dose
still remained in the fish, with skeletal muscle--which comprised
about 55% of body weight--containing more than 40% of the residue.
Assuming MeHg excretion to be a first order process, there are at
least two rates of excretion: a rapid initial rate resulting in a
biological half-retention time (HRT) of about 200 days; and a slower,
subsequent rate yielding an HRT of more than 1000 days. The latter is
apparently governed by rate of release of MeHg from skeletal muscle.
Hemoglobin (Hb) is the main methylmercury (MeHg) transport
protein in trout blood. In vitro, MeHg is taken up rapidly in 3 min
by red blood cells. MeHglbinding in RBC is reversible in vitro as
demonstrated by efflux of Hg from RBC's suspended in protein solu-
tions. MeHg binding in RBC also is reversible in vivo as gel filtra-
tion chromatography of liver soluble proteins yielded identical elu-
tion profiles for MeHg administered as the free salt or bound in RBC's.
The number of reactive sulfhydryl (-SH) groups per molecule of Hb was
4, as determined by amperometric titration with MeHgCl. The reactive
-SH concentration in RBC was calculated to be at least 20 mM. A
mechanism for efflux of MeHg from RBC is proposed involving dissocia-
tion of MeHg from Hb; this was initiated by -SH groups outside RBC,
and migration of MeHg across membrane as MeHgCl.
1867.
Matsumoto, T., M. Satake, J. Yamamoto and S. Haruna. 1964.
the micro constituent elements in marine invertebrates.
Jour. Oceanogr. Soc. Japan 20(3):15-19. (In Japanese,
English Summary)
On
Whole organism metal levels, in mg/kg wet wt, in Octopus
were 39 for Cu, 106 for Zn, 4 for Cd, 1 for Pb, 37 for Fe and 4 for AI.
Squid Sepia, contained levels of 23 for Cu, 50 for Zn, 0.7 for Cd, 0.4
for Pb, 8 for Fe, and 1.7 for AI. Sea cucumber Holothuria and jelly-
fish Aurelia contained respective levels, in mg/kg wet wt, of 1.9 and
0.7 for Cu, 8.7 and 3.4 for Zn, 14.4 and 0.8 for Pb, 50 and 0.9 for Fe,
and 73 and 0.6 for AI; Aurelia contained 0.1 mg Cd/kg wet wt.
1868.
Mauchline, J. and W.L. Templeton. 1966. Strontium, calcium
and barium in marine organisms from the Irish Sea. Jour.
Cons. perm. into Explor. Mer. 30:161-170.
Strontium, calcium, and in some cases, barium concentrations
have been determined in 15 species of algae, 45 species of inverte-
brates and 6 species of fish from the Irish Sea. Algal Sr concentra-
tions in mg/kg wet wt, ranged from 0.12 to .0.22 in Chlorophyceae, 0.55
215
-------
to 1.20 in Phaeophyceae, and 0.02 to 6.40 in Rhodophyceae. Algal Ca
concentrations ranged from 15 to 33 in Chlorophyceae, 10 to 28 in
Phaeophyceae and 1.7 to 1800 in Rhodophyceae. Algal Ba levels were
from 0.09 to 0.44 in Chlorophyceae, 0.05 to 0.38 in Phaeophyceae and
0.05 to 0.36 in Rhodophyceae. Strontium content of invertebrates, in
mg/kg wet wt were: 0.31 in sponges; 3.0 to 3.6 in polyzoa; 0.02 to
1.4 in coelenterata; 2.1 in annelida; 0.97 to 17.0 in crustacea; 0.04
to 0.77 in mollusca; 2.3 to 8.8 in echinodermata; and 3.7 to 7.3 in
tunicata. Calcium levels were 59 in sponges, 434 to 522 in polyzoa,
1 to 206 in coelenterata, 306 in annelida, 197 to 1920 in crustacea,
5 to 232 in mollusca, 513 to 1458 in echinodermata and 7 to 32 in
tunicata. Barium concentrations were 0.22 for sponges, >0.2 for
polyzoa, >0.03 to 0.55 in coelenterata, 0.16 in annelida, >0.09 to
0.84 in crustacea, 0.02 to 0.1 in mollusca, 0.2 to 1.20 in echino-
dermata and 0.07 to 0.1 in tunicata. Strontium concentration in fish
bone ranged from 0.01 to 0.06 mg/kg wet wt. Calci~, in mg/kg wet wt,
for fish extended from 2 to 10 in flesh and 210 to 258 in bone.
1869.
May,D.R. and G.W. Brown, Jr. 1973. Allantoinase from
Eudistylia vancouveri (Polychaeta): Activation and inhi-
bition by heavy metals. In 1972 Research in Fisheries.
Ann. Rep. Fish., Univ. Wash., Seattle, Wash.: 66-67.
Marine polychaetes subjected to 7 x 10-5 M HgC12 (14 mg/l
Hg) exhibit 50% inhibition of allantoinase, a uricolytic enzyme;
allantoinase is activated 13 to 20% in presence of 2.5 x 10-8 M to
1 x 10-6 M HgC12' At 2.7 x 10-6 M CdC12 (0.3 mg/l Cd), enzyme was
inhibited 50%; but activation occurred at 2.5 x 10-8 M to 5 x 10-8 M
Cd+2. Metals concentrations causing 50% inhibition of allantoinase
were: 3.5 x 10-5 M Pb(N03)2 (7 mg/l Pb); 4.1 x 10-5 M ZnC12 (3 mg/l
Zn); and 7.8 x 10-5 M CuS04 (5 mg/l Cu). Low levels of these metals
also activated allantoinase. The enzyme is most sensitive to inhibi-
tion by metal ions in the order: Cd+2 > Pb+2 > Zn+2 > Hg+2 > Cu+2.
1870.
McBrien, D.C.H. and K.A. Hassall. 1965. Loss of cell potassium
by Chlorella vulgaris after contact with toxic amounts of
copper sulphate. Physiologia Plantarum 18:1059-1065.
Chlorella accumulated Cu from the medium with most of it
bound as divalent copper. When levels rose from 1.37 (controls) to
156 mg Cu/kg dry wt, K was released in excess of the number of
equivalents of Cu2+ entering cells. More Cu was bound under anaerobic
than under aerobic conditions; extra uptake was associated with but
not stoichiometrically related to increased loss of K. Authors sug-
gest that K is released due to a graded response of a barrier,
normally of low permeability, to increasing amounts of bound Cu.
216
-------
This increase in permeability is considered to be the primary toxic
effect of Cu. Cells which lost a considerable proportion of their
normal K were capable of subsequent growth.
McBrien, D.C.H. and K.A. Hassall. 1967. The effect of toxic
doses of copper upon respiration photosynthesis and growth
of Chlorella vulgaris. Physiologia Plantarum 20:113-117.
~. vulgaris cultures subjected to 200 mg Cu2+/l under
anaerobic conditions for two hrs, then exposed to anaerobic or aerobic
conditions for 2 hrs, exhibited suppressed respiration, and inhibited
photosynthesis and growth. A total of 8.2 mg Cu/kg dry wt algae was
determined. When experiment was conducted under aerobic conditions of
Cu uptake, and cells subsequently exposed for 2 hrs of oxygen-free
media, then respiratory inhibition is as marked as anaerobic uptake;
however, respiration eventually recovers because growth is not affected
as severely as when under anaerobic conditions. It is concluded that
extra copper absorbed under anaerobic conditions is directly or in-
directly responsible for the greatly increased toxicity to growth, and
that this copper is bound to sites not normally available under
aerobic conditions. Some aspects of the apparently unique toxic
effect of copper suggest that these extra sites are sulphydryl groups.
1871.
1872.
McCarty, L.S. and A.H. Houston. 1975. Effects of exposure to
sublethal levels of cadmium upon water-electrolyte status
in the goldfish (Carassius auratus). Jour. Fish BioI. 9:
11-19.
Goldfish exposed to 45 or 380 ~g Cd/l for 25 days showed
significant reduction of plasma chloride, and increased tissue K and
water contents. Specimens in 45 ~g Cd/l compensated for most of
initial Cd effect, and were characterized only by depressed plasma Na
levels. Exposure to 380 ~g Cd/l for 50 days produced depression of
plasma Na and Cl, and elevation of tissue Na and water content.
1873.
McDermott, D.J., G.V. Alexander, D.R. Young and A.J. Mearns.
1976. Metal contamination of flatfish around a large sub-
marine outfall. Jour. Water Poll. Contr. Fed. 48(8):1913-
1918.
Metal levels, in mg/kg dry wt of flesh, from Dover sole,
Microstomus pacificus from a California waste water outfall region and
a control region (Santa Barbara Channel) were, respectively: 0.2 and
0.1 for Ag; <3.0 and <3.0 for Cd; <0.2 and <0.2 for Cr; 0.6 and 0.5
217
-------
for Cu; <2.0
for Zn. Fin
in liver and
and <2.0 for Ni; 1.3 and <1.1 for Pb; and 39.4 and 38.0
erosion was associated with elevated Cr, Al and Fe levels
kidney and depressed Cd, Ti and Al in gonads and heart.
1874.
McFarren, E.F., J.E. Campbell and J.B. Engle. 1962. The
occurrence of copper and zinc in shellfish. In Jensen, E.D.
(ed.). Proc. 1961 Shellfish Sanitation Workshop, U.S.D.H.E.W.,
P.H.S. 1962:229-234.
A wide geographic variation in both Cu and Zn levels of East
Coast shellfish was noted. Zinc levels ranged from 310 mg/kg wet wt
in lower Chesapeake Bay to 4000 in upper Chesapeake Bay near Baltimore.
Oysters contained about 10 to 20X more Cu and 30 to 40X more Zn than
clams from the same or nearby areas, and about 200X more Cu and 90X
more Zn as mussels from the same area. Oysters with high Zn levels
were also high in Cu, although the converse was not apparent.
1875.
McHargue, J.S. 1924. The significance of the occurrence of
copper, manganese and zinc in shell-fish. Science 60:530.
The following concentrations, in mg/kg dry wt, of Cu, Fe,
Mn, and Zn were found in crustaceans and bivalve molluscs: crayfish
75 Cu, 896 Fe, 250 Mn, 320 Zn; mussel 12 Cu, 1325 Fe, 5424 Mn, 750 Zn;
clam 16 Cu, 711 Fe, 43 Mn, 1359 Zn; oyster 231 Cu, 208 Fe, 49 Mn,
4284 Zn; lobster (edible meat) 85 Cu, 54 Fe, 12 Mn~ 160 Zn; and crabs
(entire bodies) 68 Cu, 134 Fe, 16 Mn, 1216 Zn.
1876.
McHargue, J.S. 1927. The proportion and significance of
copper, iron, manganese and zinc in some mollusks and
crustaceans. Trans. Kentucky Acad. Sci. 2:46-52.
Respective copper, iron, manganese and zinc levels, in mg/kg
dry wt of shellfish were 12, 1325, 5424 and 750 for a mixed sample of
freshwater molluscs, Unio and Anodonta; 16, 711, 43, and 1359 for clam,
Venus mercenaria; 23, 208, 49 and 4284 for oysters; 85, 54, 12 and
160 for lobster, Homarus americanus, meat; and 68, 134, 16 and 1216
for whole crabs.
1877.
McInerney, J.E. 1964. Salinity preference: an orientation
mechanism in salmon migration. Jour. Fish. Res. Bd. Canada
21(5):995-1018.
Preference among fry of chum salmon Oncorhynchus keta, pink
salmon O. gorbuscha, chinook salmon O. tshawytscha, sockeye salmon
218
-------
0. nerka, and coho salmon 0. kisutch,
to saltwater of open ocean-salinity.
Pacific salmon use estuarine salinity
seaward migration.
gradually changed from freshwater
Author proposes that juvenile
gradients as directive cues in
1878.
McIntosh, A.W. and N.R. Kevern. 1974. Toxicity of copper to
zooplankton. Jour. Environ. Quality 3(2):166-170.
For the aquatic zooplankters Daphnia pulex, a cladoceran, and
Cyclops sp., a copepod, LC-50 (96 hr) values for copper sulfate, in mg
Cull, were 0.028 and >225.0, respectively. Addition of 0.75 mg Cull
as CuS04.5HzO to an outdoor pond resulted in a depression of cladoceran
and rotifer populations; within 4 weeks, both showed increasing numbers.
Addition of 0.75 mg Cull as copper sulfate to a second pond occurred
when cladoceran numbers were low; however, a combination of oxygen
depletion, HzS production and released Cu from large masses of decom-
posing Chara apparently suppressed rotifer; copepod, and cladoceran
populations. Treatment of 0.25 mg Cull to a third pond produced no
discernible effects on cladocera. Stomach analyses of green sunfish
Lepomis cyanellus, indicated that the fish shifted to alternate food
sources when cladocera disappeared from affected ponds.
1879.
McKim, J.M., G.F. Olson, G.W. Holcombe and E.P. Hunt. 1976.
Long-term effects of methylmercuric chloride on three
generations of brook trout (Salvelinus fontinalis): toxicity,
accumulation, distribution, and elimination. Jour. Fish. Res.
Bd. Canada 33:2726-2739.
During a l44-wk period, 3 generations of trout were exposed
continuously to mean water concentrations of methylmercuric chloride
(MMC) of 2.93, 0.93, 0.29, 0.09, 0.03 and <0.010 (control) ~g Hg/l.
During the fiTst 39 wks the highest concentration (2.9 ~g Hg/l) pro-
duced deformities and 88% mortality of first-generation adults. At an
MMC concentration of 0.93 ~g Hg/l, second-generation trout developed
deformities and all but one female died during the 108-wk exposure.
No significant effects on survival, growth, or reproduction of second-
generation trout were noted at any of the lower MMC concentrations.
No toxic symptoms were observed in the third generation at the 3 lowest
MMC concentrations. Maximum acceptable toxicant concentration (MATC)
for brook trout exposed to MMC in water with a hardness of 45 mgll
(as CaC03) and a pH of 7.5 fell between 0.93 and 0.29 ~g Hg/l, and
the application factor (MATC/96-h LC-50) lies between 0.004 and 0.013.
Accumulation rate of Hg by 8 selected tissues of first-generation trout
exposed to MMC was relatively rapid at all MMC concentrations tested.
The 2-wk tissue Hg:water Hg concentration factors ranged from 1 x 103
to 12 x 103, depending on tissue, whereas after 28-38 wks of exposure
219
-------
this parameter for both first- and second-generation trout ranged from
6.9 x 103 to 6.3 x 104. Blood, spleen, and kidney accumulated Hg most
rapidly and contained highest residues in both first- and second-
generation trout followed by liver, gill, brain, gonad, and muscle.
There was no significant elimination of Hg from the tissue of first-
or second-generation fish, yet a "steady state" (j1g Hg/g = constant)
was reached in all tissues after 20-28 wks of continuous water exposure.
Monomethylmercury made up 90-95% of the total Hg present in muscle.
Mean muscle residues in first-generation trout, dying after ]6-28 wks
of exposure to 2.93 j1g Hg/l and in second-generation trout, dying
after 64-100 wks of exposure to 0.93 j1g Hg/l, were 23.5 and 9.5 j1g
Hg/g, respectively.
1880.
McLean, R.O. 1974. The tolerance of Stigeoclonium tenue Klitz
to heavy metals in South Wales. Brit. Phycol. Jour. 9:91-95.
The distribution of Stigeoclonium tenue and Cladophora
glomerata in relation to metal pollution by Cu, Pb, Fe, Zn and Mn was
studied in 169 river stations in the spring months of 1972. Equal
tolerance to Cu, Pb and Zn was demonstrated in both algae, but Stigeo-
clonium showed greater tolerance to Fe, even in conditions of poor
nutrient status. Highest concentrations of various metals tolerated
by Stigeoclonium, in mg/l, were >9.98 for Fe, 0.02 for Cu, 0.20 for
Pb, >0.99 for Mn and 0.53 for Zn. For Cladophora these were 0.45 for
Fe, 0.02 for Cu, 0.22 for Pb, 0.85 for Mn, and 0.42 for Zn.
1881.
McLeay, D.J. 1975. Sensitivity of blood cell counts in juve-
nile coho salmon (Oncorhynchus kisutch) to stressors includ-
ing sublethal concentrations of pulpmill effluent and zinc.
Jour. Fish. Res. Bd. Canada 32:2357-2364.
Exposure to zinc concentrations of 0.50 to 1.20 mg/l for
24 hr significantly depressed mean white blood cell-thrombocyte counts
in salmon. Decreases were proportionate to Zn concentrations. Red
blood cell counts were unchanged.
1882.
McLeese, D.W. 1974. Toxicity of copper at two temperatures
and three salinities to the American lobster (Homarus
americanus). Jour. Fish. Res. Bd. Canada 31:1949-1952.
Time to 50% mortality from the lethal threshold 56 ug/l to
1000 ug/l copper, is longer at 5 than at 13 C. Within these concen-
trations similar effects were observed at salinities of 20 and 300/00.
220
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1883.
McLeod, G.C., K.V. Ladd, K. Kustin and D.L. Toppen. 1975.
Extraction of vanadium (V) from seawater by tunicates:
revision of concepts. Limnol. Oceanogr. 20:491-493.
a
Tunicates remove vanadium from the aqueous phase as monomeric
vanadate. As the seawater circulates through the tunicate, whether for
feeding or respiration, assimilation of vanadate may take place. The
time constant for extraction is inherently smaller than the pumping
time constant (which varies between 2 and 185 ml/h g wet wt), making
extraction out of seawater into tunicate's body the slow step in the
overall process. Inhibition of vanadium uptake by phosphate or arse-
nate may be the result of reaction with vanadate to form complexes, as
the product may not bind at all, or as well, to the appropriate site
on the tunicate. At phosphate levels naturally present in seawater
(~5 ~M) complex formation is relatively insignifican~.
1884.
McLerran, C.J. and C.W. Holmes. 1974. Deposition of zinc and
cadmium by marine bacteria in estuarine sediments. Limnol.
Oceanogr. 19:998-1001.
Mixed cultures of marine bacteria isolated from sediments of
Corpus Christi Harbor, Texas, were examined for their ability to assimi
late or precipitate radioactive zinc and cadmium from solution. Test
data indicate that during summer, when bacterial activity is at a
maximum, bacteria and their metabolic byproducts playa significant
role in removal of zinc and cadmium from seawater and their subsequent
deposition in marine sediments.
1885.
McLusky, D.S. and C.N.K. Phillips. 1975. Some effects of
copper on the polychaete Phyllodoce maculata. Estuarine
Coastal Mar. Sci. 3:103-108.
In 21 day tests, Cu was found to be toxic to P. maculata at
~0.08 mg/l, at which level mortality occurred in 9 days~ Authors sug-
gest that rate of Cu uptake is the lethal factor rather than amount of
Cu accumulated.
1886.
McNaughton, S.J., T.C. Folsom, T.Lee, F. Park, C. Price, D.
Roeder, J. Schmitz and C. Stockwell. 1974. Heavy metal
tolerance in Typha latifolia without the evolution of tol-
erant races. Ecology 55:1163-1165.
Clones of the broad-leaved cattail Typha latifolia, and soil
samples were obtained from the vicinity of a zinc smelter, and from a
control location. In the smelter location, soil zinc concentration was
221
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385 times higher (5000 mg/kg), cadmium content 37 times higher (73
mg/kg), and lead content 16 times higher (435 mg/kg). No evidence for
the evolution of heavy metal tolerance could be detected in which geno-
types from both locations were grown on both soils. Growth of genotypes
from both locations was inhibited on the heavy metal soil, but not to
the extent that would be expected from previous studies of heavy metal
effects.
1887-
Mendel, L.B. and H.C. Bradley. 1905. Experimental studies on
the physiology of the molluscs--second paper. Arner. J.
Physiol. 14:313-327.
Liver of Sycotypus canaliculatus, a marine gastropod, contains
Cu, Zn, Fe, Ca, Mg, and P- Total ash content of liver contains ~8% Cu
and ~15% Zn; on a dry wt basis this is about 1.2% Cu and 1.7% Zn. Cu
is uniformly distributed in gland cells and connective tissue, com-
prising 0.4% or ~3 mg/kg dry liver; it is more predominant in greenish
pigment cells, averaging ~3% or 8 mg/kg dry liver. Gland cells contain
about 2% or 15 mg/kg Zn; and connective tissue averages 1% or 3 mg/kg
Zn. Liver compounds are richer in these metals in certain cases than
the insoluble proteid combinations formed by precipitation of albumin
with metallic salts. Cu and Zn are probably obtained from the food of
Sycotypus, and retained in liver as reserve material for the processes
of haemopoiesis. Both Cu and Zn are present in combination in blood,
forming a respiratory proteid peculiar to this animal.
1888.
Mendel, L.B. and H.C. Bradley. 1906-1907. Experimental studies
on the physiology of the molluscs--third paper. Arner. J.
Physiol. 17:167-176.
. Extracts of foot muscle from Sycotypus canaliculatus, a
marIne gastropod, closely resembled those of other molluscs. Blood
proteins, however, differed in Cu and Zn. Blood analysis gave an
average of 0.474% Cu in ash, 0.043% Cu in tissue, 0.305% Zn in ash,
and 0.027% in tissue. Hemoglobin was present in some of the more
active tissues such as heart and pharynx muscle.
1889.
Meyer, O.K. 1962. Effects of mercuric ion on sodium movement
through the gills of gold fish. Federation Proc. 11:107-108.
Using radioactive Na, uptake of Na by gills was measured as
0.92 mg Na/lOO g fish/hr; loss of Na over same time period was 0.41.
When mercuric ion was added at a concentratin of 10-5 M, uptake of Na
was completely inhibited but loss of Na increased to 4.02 mg/lOO g
fish/hr. When Hg concentration was reduced to 10-6 M, active uptake
222
-------
was reduced by 25% while loss was increased by 43% over control rates.
Mercuric ions had no effect, even at 10-5 M concentrations, when a 40 g
fish received an intraperitoneal injection of 5 mg of 2-3 dithiopropanol.
1890.
Milanovich, F.P., R. Spies, M.S. Guram and E.E. Sykes. 1976.
Uptake of copper by the polychaete Cirriformia spirabrancha
in the presence of dissolved yellow organic matter of natural
origin. Estuar. Coast. Mar. Sci. 4:585-588.
At copper concentrations at or below 0.08 mg/l, polychaete
worms survived at least 20 days vs 34 in controls. At 0.10, 0.20 and
0.50 mg Cull, worms had an LT-50-of 16, 12 and 5 days, respectively.
Uptake of copper by ~. spirabrancha in 0.04 mg Cull was initially
linear until a plateau of approximately 50 mg/kg was reached in two
weeks. Tissue Cu content of ~. spirabrancha exposed to toxic levels
was not greater than those surviving indefinitely in 0.08 or 0.06 mg
Cull. Authors concluded that lethality is not related to total Cu
accumulated but to rate of uptake. Dissolved yellow organics, a
chemically and physically ill-defined aqueous extract of decaying plant
material, had no effect on uptake rate of Cu by worms in seawater media.
1891.
Miller, G.E., P.M. Grant, R. Kishore, F.J. Steinkruger, F.S.
Rowland and V.P. Guinn. 1972. Mercury concentrations in
museum specimens of tuna and swordfish. Science 175:1121-1122.
Mercury levels of museum specimens of seven tuna caught
between 1878 and 1909 and one swordfish were determined by neutron
activation analysis. The mean Hg concentration in museum specimens is
0.95 i 0.33 mg/kg dry wt, with a range from 0.53 to 1.51 mg/kg dry wt.
Corresponding mean Hg concentration for five recent tuna samples is
0.91 i 0.47 mg/kg dry wt, with values ranging from 0.44 to 1.53 mg/kg.
The mean Hg value of 1.36 i 0.31 mg/kg for the single swordfish speci-
men falls within range of values (0.94 to 5.1 mg/kg dry wt) found for
"modern" swordfish. These data support the contention that Hg levels
present in wide ranging ocean fish are not primarily the consequence
of man's pollution but rather of natural origin.
1892.
Mishima, J. and E.P. Odurn. 1963. Excretion rate of Zn65 by
Littorina irrorata in relation to temperature and body size.
Lirnno1. Oceanogr. 8:39-44.
Following a single ingested dose, elimination of Zn-65 in a
marine gastropod exhibited 2 exponential phases: an early rapid loss
phase for first 10 days and a much less rapid loss phase thereafter.
Biological half-life of the "assimilated pool" of second phase varied
223
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inversely with body size and directly with air temperature. Indivi-
duals in field excreted tracer more rapidly than those in laboratory.
Trends in relation to temperature paralleled expected rate of 02 con-
sumption. It is tentatively concluded that, after non-assimilated
tracer has been eliminated in the early phase, Zn-65 becomes suffi-
ciently bound to biomass so that whole body rate of excretion reflects
activity of individual. This technique may provide an index to long-
ter~ rate of metabolism in free living animals.
1893.
Mitchell, R. and I. Chet. 1975. Bacterial attack of corals in
polluted seawater. Microbial Ecol. 2:227-233.
Coral heads of genus Platigyra exposed to low concentrations
of crude oil, copper sulfate (100 mg/l), potassium phosphate, or dex-
trose were killed in periods of 5 to 10 days in aquarium studies. The
chemicals stimulated production of large quantities of mucus. In
aquaria treated with antibiotics to prevent microbial growth Platigyra
survived exposure to chemical dosages suggesting that microflora were
implicated in coral death. Subsequent studies showed that Desulfo-
vibrio and Beggiatoa, two species of predatory bacteria, were instru-
mental in destruction of stressed coral colonies.
1894.
Monahan, T.J. 1976. Lead inhibition of chlorophycean micro-
algae. Jour. Phycol. 12:358-362.
Under conditions in which phosphate was growth limiting at
pH 6.2, various species of freshwater algae, including Chlorella
pyrenoidosa, f. ellipsoidea, f. vulgaris, Scenedesmus sp., Sc.
obtusiusculus and Selenastrum capricornutum, first showed toxic effects
at 0.5 mg/l lead. Scenedesmus spp. and an Ankistrodesmus sp. were more
tolerant, with toxic effects at 1 mg/l Pb. At pH 8.0, Selenastrum
developed toxicity at 3 mg/l Pb, regardless of presence of phosphate.
When phosphate supply was growth-limiting, 6X more Pb (3 vs 0.5 mg/l)
was required to demonstrate toxicity with Selenastrum at pH 8.0 as
opposed to pH 6.2. Sc. obtusiusculus was inhibited at 0.5 mg/l in
phosphate-limiting medium and developed toxicity at 1 mg/l in media
containing phosphate.
1895.
Montgomery, H. 1930.
ular weight of the
of Loligo pealei.
The copper content and the minimal molec-
hemocyanins of Busycon canaliculatum and
BioI. Bull. 58:18-27.
Hemocyanin in the marine gastropods B. canaliculatum and B.
carica contained 2.4 g Cu/kg. For squid ~. pealei, hemocyanin con-
tained 2.5 g Cu/kg.
224
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1896.
Moore, M.N. and A.R.D. Stebbing. 1976. The quantitative cyto-
chemical effects of three metal ions on a lysosomal hydrolase
of a hydroid. Jour. Mar. BioI. Assn. U.K. 56:995-1005.
Effects of Cu2+, Cd2+, and Hg2+ on the cytochemical staining
reaction for lysosomal N-acetyl-B-D-glucosaminidase were determined and
related to inhibitory effects of these metals on colonial growth rate
of the hydroid Campanularia flexuosa. Cytochemical threshold concen-
trations of 1.2 to 1.9 ~g/l for CuLT, 40 to 75 ~g/l for Cd2+, and 0.17
~g/l for Hg2+, are comparable to known environmental levels and are
about lOX lower than those obtained by measuring colony growth rates.
Pretreatment of colonies with Cu2+ did not adapt its tolerance although
there was evidence of cumulative toxicity of Cu2+ and possible accumula-
tion in endodermal cell lysosomes. Toxicity of Cu2+ may be due to
decreasing stability of lysosomal membranes, thus increasing level of
free glucosaminidase activity.
1897.
Morisawa, M. and H. Mohri. 1974. Heavy metals and spermatozoan
motility. II. Turbidity changes induced by divalent cations
and adenosinetriphosphate in sea urchin sperm flagella.
Experim. Cell Res. 83:87-94
A marked increase in turbidity was caused when heavy metals,
such as Cd2+ and Zn2+, in relatively low concentrations were added to
suspensions of either intact fla~ella or axonemes isolated from sea
urchin spermatozoa. Mg2+ and Ca + were much less effective, while Na+
and K+ were without effect. The efficiency of divalent metal ions in
producing turbidity increase of suspensions showed the following order;
at 0.5 mM concentrations: Cd2+ > Cu2+ > Zn2+ > Fe2+ > Hg2+ > Ni2+ >
Co2+ > Mn2+ > Sr2+ > Ca2+ > Mg2+. The monovalent cations Na+ and K+
had little effect on turbidity even when concentrations were raised to
0.1 M. The turbidity increase was almost abolished by adding equivalent
amounts of EDTA or pyrophosphate. Addition of ATP to the metal-treated
suspensions of flagella also brought about a decrease in turbidity.
ADP was not as effective as ATP and little decrease was observed with
AMP. The same was true with other nucleoside phosphates. Within a
certain range of concentrations Cd2+ and Zn2+ caused fluctuations in
turbidity, which gradually decayed. ATP restored the fluctuations which
had once disappeared. The phenomenon could not be observed with samples
after long standing, heating, sonication or treatment with 8 M urea.
Similar results were obtained with suspensions of microtubules isolated
from the flagella. The observed changes in turbidity are discussed in
connection with flagellar movement.
1898.
Morris, R.J. 1971. Seasonal and environmental effects on the
lipid composition of Neomysis integer. Jour. Mar. BioI. Assn.
U.K. 51:21-31.
225
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Salinities between 5 and 300/00 did not influence fatty-
acid composition of this brackish water mysid.
1899.
Morris, O.P. and G. Russell. 1974. Inter-specific differences
in responses to copper by natural populations of Ectocarpus.
Brit. Phycol. Jour. 9:269-272.
The alga Ectocarpus siliculosus showed greater growth in sea-
water containing up to 0.5 mg Cull than E. fasciculatus, a different
species of the same genera collected from the same region. The greater
tolerance shown by E. siliculosus may result from immigration of Cu-
tolerant individuals from highly selective habitats nearby. Authors
suggest that E. siliculosus is a more variable species than ~. fascicu-
latus, and therefore more readily affected by natural selection.
1900.
Muller, A.A. and R. Mosley. 1976. Availability, uptake and
translocation of plutonium within biological systems: a
review of the significant literature. U.S. EPA Rept.
600/3-76-043. Off. Res. Dev., Envir. Monit. Support Lab.,
Las Vegas, Nev. 96 pp.
A selective literature review is presented on plutonium and
its cycling through biological systems, including algae, molluscs, fish
and annelids. Incorporation of particulates within aquatic bottom sedi-
ments may isolate Pu and prevent dissolution for long time periods, but
occasional violent agitation may cause Pu release and subsequent bio-
logical uptake. Concentrations are higher in animals associated with
sediment than water column. Food chain amplification has been observed
in mussels and starfish. A bibliography of 432 references is included.
1901.
Mullin, J.B. and J.P. Riley. 1956. The occurrence of cadmium
in seawater and in marine organisms and sediments. Jour.
Mar. Res. 15(2):103-122.
Mean cadmium concentration found in waters of the Irish Sea
and of the English Channel was 0.113 ug/l, with values ranging from
0.024 to 0.25 ug/1 depending upon station and season. Average copper
concentration in the Irish Sea was 13.7 ug/l with range of 8.7 to 17.3
ug/l. It is probable that variations are due to adsorption or utiliza-
tion of the elements by plankton outbursts or to adsorption by detritus.
Occurrence of cadmium in green, red, and brown algae, proto-
zoans, porifera, coelenterata, crustacea, molluscs, and echinoderms
(dried at 110 C) has been observed; concentrations varied between 0.134
(Laminaria digitata) to 16.4 mg/kg (Patella vulgata) and 37.9 mg/kg in
soft parts of Nucella lapillus. The distribution of Cd in various
226
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organs of Pecten maximus, Buccinum undatum, Chlamys opercularis, and
Porania pulvillus has been investigated: values in calcareous shells
are usually <0.02 mg/kg, muscle contains about 1.5 mg/kg, and high con-
centrations (up to 500 mg/kg) are found in digestive glands and renal
organs of molluscs. A representative selection of marine sediments
has been analyzed: mean Cd values for diatomaceous oozes is 0.39 mg/kg,
globigerina oozes 0.42; and radiolarian oozes 0.45. Two manganese
nodules contained 8.4 and 5.1 mg/kg of cadmium, respectively; thallium
(ca 2 mg/kg) was also detected in each case.
1902.
Mullins, L.J. 1950. Osmotic regulation in fish as studied with
radioisotopes. Acta phys. Scandinav. 21:303-314.
The drinking rate of sticklebacks Gasterosteus aculeatus upon
transfer from fresh to seawater was~4%of the body weight per hour.
This is equal to 350 mg Cl/kg/hr, 8 mg K/kg/hr and 230 mg Na/kg/hr.
Permeation of gill membrane by Na-24, K-42, Br-82, and P-32 was measured
in freshwater. For Na-24, exchange rate was equal to~l% of total amount
present in body/hr, or ~14 mg/kg/hr. For K-42 in fresh and seawater,
exchange rates were 6 and 12 mg/kg/hr, respectively. If one considers
that exchange proceeds only with extracellular space K, the rate is
about equal to that for Na.
1903.
Murphy. T.P. and D.R.S. Lean. 1976. Blue-green algae: Their
excretion of iron-selective chelators enables them to dominate
other algae. Science 192:900-902.
The ability of blue-green algae to suppress other algae during
blue-green algal blooms may be determined by the availability of iron.
Iron deprivation induces production of hydroxamate chelators, which
appears to be the suppressant agent. In field studies, periods of nitro-
gen fixation coincided with rapid uptake of Fe-55, supplied as FeC13'
There was no change in flux of iron from sediments. When Fe was not in
high demand, blue-green algae comprised about 30% of the phytoplankton
biomass. During periods of rapid Fe uptake, blue-green algae increased
to >90% of phytoplankton biomass. In 2 weeks, these blooms were followed
by 65% and 50% reductions each in phytoplankton biomass. To test the
hypothesis that blue-green algal suppression of other algae may have
been mediated by hydroxamate siderochromes, ultrafiltration experiments
were conducted. These showed that microbes produced an organic compound
with molecular weight of about 1000 capable of solubilizing iron.
Colorimetric assay showed that bound hydroxymates were present only
during periods of rapid Fe-55 uptake. Effects of the hydroxamate che-
late of axenic Anabaena flos-aquae on Scenedesmus basiliensis included
marked growth inhibition; authors concluded that the hydroxamate chelate
and not a toxin was responsible.
227
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1904.
Myslik, G. and T.C. Hutchinson. 1971. Algal strains resistant
to heavy metals from isolates of lakes in the Sudbury smelt-
ing region. Amer. Jour. Botany 58:483. (Abstract)
In laboratory tests, nickel and copper were highly toxic to
laboratory algal strains at levels present in many lakes of the Sudbury
smelting region; Ni and Cu showed synergistic effects. Isolates from
sparse algal flora in some heavily polluted lakes indicated a high
tolerance to normally toxic levels of these metals.
1905.
Nagy, J. and G. Denes. 1976. Iron-requiring mutant of Esche-
richia coli carrying a deletion on the aro G - nad A region
of the chromosome. Jour. Bacteriol. 128:490-491.
A mutant of E. coli K-12 carrying a deletion in the aro G -
nad A region of the genome requires a high concentration of Fe for
growth. After 4 hrs, growth at 50 ~M FeS04 is about 5X greater than
growth at 1 ~M FeS04' This mutant shows a growth response to citrate
and is chromium sensitive. Addition of 0.1 mM CrC13 decreases growth
by 50% after 4 hrs. Authors suggest that deletion mutant lost a gene
between aro G and nad A which is a component of the enterochelin-
dependent iron transport system.
1906.
Nakamura, M. 1974. Experimental studies on the accumulation of
cadmium in the fish body (Tribolodon). Jap. Jour. Public
Health 21:321-327. (In Japanese, English summary)
Tribolodon fry were reared in water containing 0.005, 0.01,
and 0.05 mg Cd/I, and in Cd-free water. Death corresponded with mass
and age of fry. Fish began to die on the 385th day in 0.01 mg Cd/l
with 68% of these deformed, and on the 4l3th day in 0.005 mg Cd/l with
65% deformed. Accumulation of Cd increased with mass and age of fish,
reaching 18 mg/kg in 0.05 and 0.01 mg Cd/I, and 11 mg/kg in 0.005 mg
Cd/I. Liver and kidney had highest values of Cd (55 mg/kg, compared to
2.7 mg/kg for control) while flesh had lowest levels (1.5 mg/kg, com-
pared to 0.6 for control). Growth differences were apparent between
experimental and control fish over the 27 month test period, with
inferior growth occurring even in 0.005 mg Cd/I. Author concludes that
Cd hinders bone growth.
1907.
Nakatani, R.E. 1966. Biological response of rainbow trout
(Salmo gairdneri) ingesting zinc-65. In Disposal of Radio-
active Wastes into Seas, Oceans, and Surface Waters. Int.
Atom. Ener. Agen., Vienna, Austria: 809-823.
228
-------
Trout were force fed Zn-65 at 2-3% of average body wt daily.
After a single dose fish rapidly excrete Zn-65 for several days, pri-
marily through gastrointestinal tract and gills. Highest 'Zn-65 con-
centrations were in gill, G.I. tract and bone. G.I. tract contained
30-50% of body burden after both chronic and single feeding. Little
Zn-65 was excreted in urine. Trout fed 0.01, 0.1 and 1.0 ~Ci Zn-65/g
fish daily for 17 weeks did not differ significantly from controls.
Growth of Zn-65 fed fish exceeded controls with no mortalities. Fish
fed 10 ~Ci Zn-65/g fish for 10 weeks exhibited no anomalies in blood
hematocrit, hemoglobin or erythrocytes; however, leucopenia was indi-
cated. Histopathological evidence of tissue damage was observed only
in gill filaments. Because trout with 10,000X greater burden of Zn-65
than river fish showed no detrimental effects, authors concluded that
Columbia River fish populations are not adversely affected by present
levels of Zn-65 contamination.
1908.
Negilski, D.S. 1976. Acute toxicity of zinc, cadmium and
chromium to the marine fishes, yellow-eye mullet (Aldri-
chetta forsteri C. & V.) and small-mouthed hardyhead
(Atherinasoma microstoma Whitley). Austral. Jour. Mar.
Freshwater Res. 27:137-149.
For juvenile mullet in static tests, the acute incipient
lethal level for Zn, the LC-50 (168 h) level for Cd, and LC-50's (96 h)
levels for Cr3+ and Cr6+ were 9, 16, 53 and 24 mg/l, respectively.
Highest metal levels, in mg/l, that did not cause death were 5, 10 and
13.5 mg/l for Zn, Cd and Cr, respectively. For pre-adult hardyhead,
the acute incipient lethal level for Zn and Cd LC-50 (168 h) were 33
and 21 mg/l, respectively. In continuous-flow tests with mullet, acute
incipient lethal level for Zn, Cd LC-50 (120 h), and Cr6+ LC-50 (96 h)
were 12, 14 and 31 mg/l, respectively. Symptoms produced by Zn poison-
ing included fin erosion, impaired swimming ability, dark color, and
surfacing behavior. For hardyhead, incipient lethal levels for Zn and
Cr and LC-50 (168 h) value for Cd were 37, 36 and 15 mg/l, respectively
Toxicity of Zn to mullet appeared to increase with temperature.
1909.
Nehring, R.B. 1976. Aquatic insects as biological monitors of
heavy metal pollution. Bull. Envir. Contamin. Toxicol. 15:
147-154.
LC-50 (14 d) values for mayfly Ephemerella grandis, in mg/l,
were: 0.18 to 0.20 for Cu; 3.5 for Pb; <0.001 for Ag; and >9.2 for Zn.
Stonefly Pteronarcys californica had LC-50 (14 d) values of 10.1 to
13.9 for Cu; >19.2 for Pb; 0.004 to 0.009 for Ag; and >13.9 for Zn.
Insects were more tolerant to metals screened than fish. Insects con-
centrated metals in relative proportion to occurrence of metal in the
229
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stream by some predictable, reproducible factor. These data, together
with field tests, indicate that aquatic insects may be effective bio-
logical monitors of heavy metal pollution where fish-kills are involved.
Nelson, D.A., A. Calabrese, B.A. Nelson, J.R. MacInnes and D.R.
Wenzloff. 1976. Biological effects of heavy metals on
juvenile bay scallops, Argopecten irradians, in short-term
exposures. Bull. Environ. Contamin. Toxicol. 16(3):275-282.
LC-50 (96 h) values for tests conducted at 250/00 salinity
and 20 C for scallops were 0.033 mg/l of silver; 0.089 mg/l of mercury,
1.48 mg/l of cadmium, and 3.49 mg/l of arsenic. Scallops exposed to
0.94 mg Cd/lor 0.022 mg Ag/l for 96 hr exhibited respective oxygen
consumption rates that were 12.9% and 14.7% higher than controls.
After exposure for 96 hr to 0.01 mg/l of Ag, 0.75 mg/l of Cd, 0.04
mg/l of Hg or 2.0 mg/l of As, whole juvenile scallops contained, in
mg/kg wet wt, 3.1 Ag, 49.4 Cd, 48.9 Hg, or 29.2 As, respectively.
1910.
1911.
Nelson, D.J. 1962. Clams as indicators of strontium-90.
Science 137(3523):38-39.
Analysis of specific activities of Sr-90 in shells of fresh-
water clams (Unionidae) showed that Sr-90 released to the Tennessee
River system remained in solution and that concentrations to a distance
of 800 km from the release site can be predicted on basis of dilution
of contaminated White Oak Creek water by uncontaminated Clinch-
Tennessee River water. Strontium content of 190 shells representing
15 species ranged from 150 to 550 mg/kg and varied with species, age
within species, and shell growth rate. Average concentration factor
(Sr/gm shell:Sr/ml water) for Sr in shells immediately downstream from
White Oak Creek was 4.8 x 103 which is in good agreement with 6.5 x
103, based on monitoring data for water.
1912.
Nelson, D.J., J.W. Gooch, N.A. Griffith and S.A. Rucker. 1971.
White Oak Lake Studies. In Oak Ridge Nat. Lab. Ecol. Sci.
Div. Ann. Prog. Rep. ORNL~634, Avail. from NTIS, U.S. Dept.
Comm., Springfield, VA: 104-106.
Food habits and accumulation of Cs-137, Co-60, Ru-l06, Sb-125,
and Zn-65 in shad Dorosoma cepedianum, goldfish Carassius auratus, and
bluegill Lepomis macrochirus from White Oak Lake, Tennessee, were
studied over a period of 14 months. Of 272 fish analyzed Ru-l06 was
found in 42 specimens, Sb-125 in 15, and Zn-65 in 13. Cesium-137 con-
centrations in all three species followed a seasonal cycle with minimum
concentrations in summer and higher concentrations in winter. Shad had
230
-------
the highest Cs-137 concentration with 49.2 pCi/g fresh wt, then gold-
fish with 23.6, and bluegill with 19.2 (water=0.16 pCi/ml). Low con-
centrations in bluegill are probably due to inclusion of sediments in
digestive tracts of chironomid larvae, and this in turn could interfere
with absorption of Cs-137 from food. The preponderance of ingested
algae from which Cs-137 was readily assimilated accounted for higher
Cs-137 concentrations in goldfish. Piscivorous food habits of shad
explains their high Cs-137 concentration if "trophic level effect" con-
cept is applied. In water with Co-60 content of 0.095 pCi/ml, gold-
fish contained more Co-60 (4.6 pCi/g fresh wt) than shad (2.9 pCi/g
fresh wt) or bluegill (2.4 pCi/g fresh wt) and were also the species
which ingested more algae. Bluegills and shad are essentially carni-
vores and have lower Co-60 concentrations, suggesting that Co-60
obtains its maximum concentrations in primary producers.
1913.
Nelson, D.L. and E.P. Kennedy. 1971. Magnesium transport in
Escherichia coli. Jour. BioI. Chern. 246(9):3042-3049.
Energy-dependent transport of Mg2+ into bacteria, E. coli,
was inhibited by 590 ~g Co2+/l. Co2+ substituted for Mg2+ in promoting
efflux of cellular Mg2+. Accumulation of Co2+ was energy dependent;
maximum rate and extent of Co2+ uptake were similar to those of Mg2+,
although affinity for Co2+ was one-tenth that for Mg2+. Co2+ uptake
was inhibited by 240 ~g Mg2+/l. Intracellular Mg2+ exchanged readily
with external Mg2+, but Co2+ within cells did not easily exchange with
Mg2+ or Co2+ in medium. Ex~osure to a low level of Co2+ in absence of
Mg2+ killed cells, but Mg + protected against lethal effect of Co2+.
Conditions which prevented Co2+ uptake, such as low temperature, or
deprivation of an energy source, reduced lethality of Co2+. A mutant
selected for resistance to Co2+ had a decreased capacity to transport
both Co2+ and Mg2+. Authors concluded that Co2+ is transported into
cells of ~. coli by the same system responsible for Mg2+ transport.
1914.
Nelson, J.D., Jr. and R.R. Colwell. 1975. The ecology of
mercury-resistant bacteria in Chesapeake Bay. Microbiol.
Ecology 1:191-218.
Total ambient mercury concentrations in sediment (7-860 ~g/kg)
and in water (0.07-0.49 ~g/l) and numbers of mercury resistant, aerobic
heterotrophic bacteria at 6 locations in Chesapeake Bay were monitored
over a 17 month period. Mercury resistance expressed as proportion of
total, viable, aerobic, heterotrophic bacterial population reached a
reproducible maximum in spring and was positively correlated with dis-
solved oxygen concentration and with sediment Hg concentration and
negatively correlated with water turbidity. A relation between Hg
resistance and metabolic capability for reduction of mercuric ion (Hg+2)
231
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to the metallic state (HgO) was established by surveying a number of
HgC12-resistant cultures. The reaction was also observed in micro-
organisms isolated by differential centrifugation of water and sediment
samples. Hg+2 exhibited an average half-life of 12.5 days in presence
of approximately 105 organisms/mI. HgC12 or phenylmercuric acetate
(PMA) at levels as low as 1.2 ~g/l inhibited a measurable portion of
the total population. Cultures resistant to 6 mg/l of HgC12 and 3 mg/l
PMA were classified into 8 generic categories. Pseudomonas spp. were
the most numerous of those bacteria capable of metabolizing both com-
pounds; however; PMA was more toxic and more selective for Pseudomonas.
The Hg-resistant generic distribution was distinct from that of total
bacterial generic distribution and differed between water and sediment,
positionally and seasonally. Proportion of nonglucose-utilizing mercury-
resistant Pseudomonas spp. was found to be positively correlated with
total bacterial Hg resistance. It is concluded that numbers of Hg-
resistant bacteria as established by plate count can serve as a valid
index of in situ Hg2+ metabolism.
1915.
Nelson, J.S. 1968. Salinity tolerance of brook sticklebacks,
Culaea inconstans, freshwater ninespine sticklebacks,
Pungitius pungitius, and freshwater fourspine sticklebacks,
Apeltes quadracus. Canad. Jour. 2001. 46:663-667.
The salinity tolerance of Culaea, Pungitius, and Apeltes was
studied at 8, 12, 16, and 20 C. Results were compared with the toler-
ance of Pimephales promelas, Notemigonus crysoleucas, and Umbra limi
by increasing salinity in steps of 10% seawater (3.50/00) at regular
intervals. Culaea had a sig~ificantly lower salinity tolerance than
Pungitius and Apeltes but had a significantly higher salinity tolerance
than Pimephales, Netemigonus, and Umbra. Culaea recovered when returned
to freshwater after an abrupt transfer to 100% seawater for 1.75 hr or
less. In Culaea, temperature had an effect on salinity tolerance but
neither light duration nor acclimation in 20% seawater had any measur-
able effect. Apeltes had a significantly higher salinity tolerance
than Pungitius at 8 C but not at 16 C. At 16 C most feeding and fanning
activity ceased at 60, 80, and 110% seawater, in Culaea, Pungitius, and
Apeltes, respectively. In the Gasterosteidae the order of decreasing
salinity tolerance and increasing utilization of the freshwater habitat
is: Spinachia, Apeltes, Gasterosteus, Pungitius, and Culaea. Bio-
geography of these species is discussed.
1916.
Nelson, V.A. and A.H. Seymour. 1972. Oyster research with
radionuclides. A review of selected literature. Proc. Natl.
Shellfish Assoc. 62:89-94.
232
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Zn-65 concentrations of 10-4 Ci/l will produce harmful
effects on oyster larvae. Biological half-lives (time for half of
substance to leave body due to biological processes) for Zn-65 in
adult Paoific oysters Crassostrea gigas, was 250 days for first 23
days of study, 160 days during four month spawning season, and 970 days
during remainder of year (winter).
Uses of radionuclides in oyster research from previous
studies are also discussed. These include depuration studies, radio-
nuclides as metabolic tracers, determination of filtration and feeding
rates using radionuclide-tagged algae, determination of shell forma-
tion and growth rate, radionuclides as a field tag, trace element
determination by activation analysis, and genetic studies using
radiation-increased mutation rates.
1917.
Nelson, V.A. and A.H. Seymour. 1976. Amchitka radiobiological
program progress report January 1975 to December 1975.
NVO-269-27, Univ. Washington, Lab. Radiation Ecol., Seattle,
Wash. 47 pp.
Radioactivity levels attributable to Be-7, K-40, Zr-95, Nb-95,
Ru-l03-l06, Sb-125, Cs-137, Ce-144, and Eu-155 were determined for
marine teleosts, sponges, and algae; for freshwater teleosts, alga,
mosses, higher plants; and for terrestrial groups. It is part of a
program started in 1970 to provide a continuing documentation of radio-
nuclides, both naturally occurring and man-made, in biological and
environmental samples from Amchitka and environs. Unexpected combina-
tions or concentrations of radionuclides would indicate presence of
newly-added radionuclides to the environment, presumably from fresh
fallout, nuclear-powered vessels, or from nuclear detonations at
Amchitka Island.
1918.
Nevissi, A. and W.R. Schell. 1975. 210po and 239pu - 240pu in
biological and water samples from the Bikini and Eniwetok
atolls. Nature 255(5506):321-323.
Measurements of radioactivity in water and biological samples
from Bikini and Eniwetok lagoons indicate that although samples were
collected from the most plutonium-polluted waters of the world, vallles
of the naturally produced radionuclide, polonium-2l0,were usually
greater by up to 100X than those for plutonium-239 and 240, both of which
are produced by nuclear detonations. For fishes, Po-2l0 activity is
highest in bone, decreasing in order in liver, viscera and muscle. Al-
though bone and liver have been reported as major repositories for
plutonium, the Pu content of the single bone samples reported was at the
detection limit of 0.001 d/m/g wet wt. The high concentrations of
233
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Po-2l0, Pu-239 and Pu-240 in viscera and viscera minus liver (convict
surgeon fish), together with the fact that algae in diet of these
species concentrates those radionuclides from seawater, seems to
support the idea that both radionuclides enter the fish through the
food chain. Highest Pu-239 and Pu-240 contents in water column were
found in areas where the highest activity of those radionuclides occurred
in sediments, as reported for Bikini. The highest Po-2l0 concentration
was found outside the lagoon in deep ocean waters. One possible explana-
tion could be that biological uptake results in a shorter resident time
of Po-2l0 - Pb-2l0 in the lagoon. The concentration of Pb-2l0 in the
particulate phase, (>0.3 ~m in size) was less than 10% of the total;
the concentrations of Pu-239 and Pu-240 in the particulate phase varied
from 2 to 60% of the total depending on collection site. The overall
result indicates that inside the lagoon the radioactivity values of
plutonium were more variable than those of Po-2l0. All specimens
measured exhibited concentration factors for Po-2l0 up to 100X greater
than those for Pu-239,-240 with the exception of samples of turtle
liver and surgeon fish viscera. Authors concluded that plutonium radio-
activity is only a fraction of the natural polonium radioactivity, and
that a greater radiation dose to marine organisms of Bikini and Eni-
wetok lagoons would be received from Po-2l0 than from plutonium-239 and
-240.
1919.
Newton, L. 1944. Pollution of the rivers of West Wales by lead
and zinc mine effluent. Ann. Appl. BioI. Brit. 31:1-11.
Studies on effects of lead and zinc on plant and animal life
of Cardiganshire streams showed that Zn had greater impact on plants
than Pb. The greater toxicity of zinc is a primary cause of the scarcity
of vegetation on mine detritus and in rivers. Maximum non-lethal con-
centrations of Zn, in mg/kg, were: 0.2 for pond snail Limnaea pereger,
and freshwater limpet Ancylastrum fluviatile; 0.3 for freshwater shrimp
Gammarus pulex; 0.2 to 0.5 for mayfly nymph Chloeon simile; 30.0 for
planarian Polycelis nigra; and 500.0 for water-boatman, stonefly nymph,
dragonfly larvae, and trichopteran larvae. Ranunculus aquatilus (an
aquatic flowering plant) was very sensitive to Pb or Zn pollution, and
first to disappear when traces of Pb or Zn were present. Fish mortality
was not due primarily to fragments of lead grit which caused clogging
and inflammation of the gills, but rather to formation of an adsorption
complex of heavy metals upon the gills plus an excess secretion of
mucus; together these caused suffocation following acute respiratory
distress.
1920.
Nielsen, E.S. and H.B. Laursen. 1976. Effect of CuS04 on the
photosynthetic rate of phytoplankton in four Danish Lakes.
Oikos 27:239-242.
234
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Photosynthetic rate of phytoplankton in water samples from
four lakes was altered by the addition of CuS04' Cu had its maximum
adverse effect on photosynthesis at concentrations of 125 ~g/l and
higher. Among factors which influenced toxic action of Cu2+, were:
taxonomic composition of phytoplankton (blue-greens were most sensi-
tive); biomass; humus content of water; temperature; and pH. Although
addition of 25 ~g/l Cu in three of the lakes decreased photosynthesis
considerably, in the fourth lake--a brown-water lake--an increase
occurred. In the brown-water lake, humus bound Cu2+ so effectively
that it was probably present in very low concentrations in the water.
1921.
Nielson, E.S. and S. Wium-Andersen. 1972. Influence of copper
on photosynthesis of diatoms, with special reference to an
afternoon depression. Verh. Internat. Verein. Limnol. 18:
78-83.
The addition of 3 or 6 ~g Cull to cultures of Nitzschia
palea reduced photosynthesis to levels as low as 65% and 10%, respec-
tively, of Cu-free control values. Susceptibility to Cu was highest
during darkness in a light-dark regimen of 12:12. These results suggest
alternative explanations for previous work using water contaminated with
up to 3 ~g Cull.
1922.
Niimi, A.J. and Q.N. LaHam. 1975. Selenium toxicity on the
early life stages of zebrafish (Brachydanio rerio). Jour.
Fish. Res. Bd. Canada 32:803-806.
Embryos at four stages of development, and newly-hatched
larvae of zebrafish were exposed to selenium concentrations of 0.5, 1,
3, 5, and 10 mg/l in freshwater to establish toxic levels at different
stages. Embryo mortality was negligible at all concentrations. Follow-
ing hatching, mortality among larvae sharply increased at concentrations
of 3 mg/l or greater, regardless of embryonic stage when exposed; over
90% of larvae died within 10 days of hatching in most cases. The
mortality rate for larvae exposed to selenium after hatching was
slightly less.
1923.
Noel-Lambert, F. 1976. Distribution of cadmium, zinc and copper
in the mussel, Mytilus edulis. Existence of cadmium-binding
proteins similar to metallothioneins. Experientia 32:324-325.
In mussels, Zn and Cu are principally associated with high
molecular wt proteins. The same distribution is observed for Cd in un-
treated mussels. But in chronically Cd-intoxicated animals (90 day
exposure to 5 ~g Cd/I), the metal is principally bound to low molecular
235
-------
wt proteins synthesized by mussels and quite similar to metallothioneins
of vertebrates.
1924.
Norstrom, R.J., A.E. McKinnon, and A.S.W. DeFreitas. 1976. A
bioenergetics-based model for pollutant accumulation by fish.
Simulation of PCB and methylmercury residue levels in Ottawa
R'ver yellow perch (Perca flavescens). Jour. Fish. Res. Bd.
Canada 33:248-267.
A pollutant accumulation model based on pollutant biokinetics
coupled to fish energetics was formulated to predict concentrations of
PCBs and methylmercury in tissues of yellow perch. Metabolic rate ex-
pression includes a growth-dependent term for estimating the contribu-
tion to metabolism of seasonal and annual growth in each age-class.
Uptake of pollutant from food is based on caloric requirements for
respiration and growth coupled to concentration of pollutant in food
and its dietary assimilation efficiency. Uptake of pollutant from water
is based on flow of water past the gills for respiration, concentration
of pollutant in water and efficiency of its assimilation by gills.
Pollutant clearance, related to body wt raised to the power of -.58, is
independent of metabolic rate. Under steady state conditions of chronic
exposure, predicted ratio of uptake to clearance is roughly constant at
all weights, and the slope of a curve of log pollutant concentration in
tissues vs log body wt can be used to establish the exponent of body wt
for clearance.
1925.
Noshkin, V.E., R.J. Eagle and K.M. Wong. 1976.
in Kwajalein lagoon. Nature 262:745-748.
Plutonium levels
Plutonium-239,-240 levels in fish (primarily mullet, surgeon
fish and goatfish species) from Kwajalein and Enewetak Atolls are not
significantly different. This suggests that Kwajalein Atoll contains
significantly more environmental plutonium than expected from worldwide
fallout levels alone, although no plutonium levels greater than fallout
concentrations have been detected in lagoon water. High levels in the
fish have not been explained and raise questions concerning validity
of concentration factors.
1926.
Noshkin, V.E., Jr. and C. Gatrousis.
239pu in Atlantic marine samples.
Letters 22:111-117.
1974. Fallout 240pu and
Earth and Planetary Science
Mass spectrometric analyses of low levels of global fallout
plutonium separated from Atlantic marine samples have differentiated
fallout Pu-239 and Pu-240 in aquatic samples for the first time.
236
-------
Results show no single characteristic Pu-240/Pu-239 ratio in marine
samples; the observed range is from 0.11 to 0.27 on an atom basis;
sediment cores ranged from 0.11 at 4810 m to 0.27 at 4920 m; Sargassum
had a 0.20 ratio, plankton a 0.24 ratio, and salps a 0.21 ratio. There
are indications that differences exist in the chemical or physical form
of plutonium from atmospheric fallout in Atlantic surface water and that
selective concentration in surface organisms is occurring. No single
Pu-240/Pu-239 value is found in pelagic sediments collected from dif-
ferent depths and locations. Discounting sources other than fallout,
our results show that the plutonium deposited at any given time since
atmospheric testing began may have carried a unique Pu-240/Pu-239 tag.
This label may be useful to trace fallout plutonium through biogeo-
chemical cycles.
1927.
Noshkin, V.E., K.M. Wong, R.J. Eagle and C. Gatrousis. 1975.
Transuranics and other radionuc1ides in Bikini Lagoon: Con-
centration data retrieved from aged coral sections. Limno1.
Oceanogr. 20(5):729-742.
X-radiography and autoradiography of thin vertical sections
were used to estimate growth rate of Favites virens from Bikini Lagoon.
Discrete bands of radioactivity were identifiable with specific nuclear
test series (1954, 1956, 1958). The coral growth rate of 8.0 mm/year
is in good agreement with rate derived from the "seasonal" alternating
light and dark bands on X-radiographs. With these bands as growth rate
indicators, the coral was sectioned into yearly increments and analyzed
to reconstruct variations in concentration of transuranics (Am-241,
Pu-238,-239.-240,-241) and other radionuc1ides (Sr-90, Y-90, Cs-137,
Rh-102m, Sb-125, Eu-155, Bi-207, Co-60. Po-210, Pb-210) in the marine
environment at Bikini since 1954. From concentration data retained in
this indicator species, exchange rate of radionuc1ides between lagoon
and open ocean is computed to be longer than exchange rates based on
physical circulation data. There is no constant ratio of plutonium
isotopes in the coral growth sections. The Pu-240:Pu-239 activity
ratios in coral average 0.77; this ratio decreasing in each post-test
year to 72% of its test year value, and in 1960 increasing to 20% over
the post-test series year. The average Pu-238:Pu-239, Pu-240 ratio was
0.040 for 1969-1972. This suggests that redistributions of the several
plutonium isotopes in the environment may be governed by different bio-
geochemical processes.
Stable strontium in coral averaged 8.94 mg/g. The concentra-
tion factors for Pu-239 -240 and Sr-90 in Bikini coral are 2.7 x 103
and 1.1 x 103, respecti~e1Y, These values are very similar to water
concentration values, indicating that coral species take up Sr-90 and
Pu-239,-240 in proportion to environmental concentrations.
237
-------
The following activity ratios were found in recent coral sec-
tions: Am-24l:Eu-155, 0.83; Co-60:Eu-155, 4.4; and Bi-207:Eu-155, 1.0.
The concentration of Po-2l0 (Pb-2l0) in coral from 1966-1971 was 0.20
pCi/g. There was a small but definite increase during test years, which
correlates with an increase in artificial radionuclides. This contra-
dicts previous arguments that no Pb-2l0 has resulted from weapons test-
ing.
1928.
Nuorteva, P. and E. Hasanen. 1975. Bioaccumulation of mercury
in Myoxocephalus quadricornis (L.) (Teleostei, Cottidae) in
an unpolluted area of the Baltic. Ann. Zool. Fennici 12:
247-254.
In the unpolluted Bromary area of the Baltic, mean mercury
content was 0.03 mg/kg wet wt for invertebrates, 0.10 mg/kg in flesh of
fishes that feed on invertebrates, 0.29 mg/kg in flesh of piscivorous
fishes, and 0.35 mg/kg in flesh of fish-eating migratory birds. Mer-
cury content of the stenothermal fish Myoxocephalus quadricornis in-
creased with size to a maximum value of 0.47 mg/kg. Observations from
an area moderately polluted with mercury showed a notably accelerated
accumulation of mercury, which was evident from the increased slope of
the regression line of mercury content on body size. This and earlier
observations indicate that the balanced natural condition of mercury
circulation is characterized by regression coefficients near zero.
Mercury contents of other invertebrate-eating fishes living in the same
environment at Bromary were below the suggested maximum background
level of 0.2 mg/kg. The exceptionally strong bioaccumulation of mer-
cury in M. quadricornis is probably a result of its feeding on mysida-
ceans which have a higher mercury content (0.06-0.09 mg/kg) than other
invertebrates (0.01-0.03 mg/kg). The transfer of such peak concentra-
tions along the food chain is possible only in oligotrophic conditions,
where there are relatively few species and each predator has a limited
spectrum of prey animals.
1929.
Nuorteva, P. E. Hasanen, and S.-L. Nuorteva. 1975. The effec-
tiveness of the Finnish anti-mercury measurements in the
moderately polluted area of Hameenkyro. Ymparisto ja Terveys
6(8):611-635. (English summary)
Measures were taken in 1967 to end Hg pollution and reduce the
population's intake of Hg in Finland. Four to 8 years later (1971-1975)
Hg content of fish, in mg/kg, from waters above source of pollution
ranged from 0.19 to 0.42. At locations going increasingly downstream
from source, ranges of Hg concentrations decreased from 0.95 to about
0.59 mg/kg. Decrease of Hg content in pikes from 1971 to 1975 averaged
0.2 mg/kg/yr. An average of 12.9 mg/kg Hg was found in hair of persons
238
-------
consuming fish. Persons eating little or no fish had 1.5 to 2.6 mg/kg
Hg in their hair; the current tolerance limit is 6 mg/kg.
Blowflies (sarcophagous flies of family Calliphoridae) were
tested for possible value as indicators of degree of Hg contamination
in the environment. Hg content of flies rises in positive correlation
to mercury content of feeding substrates, but has only a 2 day half-
life in flies. This decreases considerably when flies turn to a carbo-
hydrate diet before period of egg development.
1930.
Oglesby, L.M. and A.C. Bannister. 1959. Sodium and potassium
in salt-water fish. Jour. Amer. Dietet. Assoc. 35:1163-1164.
Sodium content in 9 species of Gulf Coast saltwater fishes
ranged from 468 to 1,012 mg/kg wet wt whole fish with an average of
661 mg/kg. Potassium content ranged from 1,911 to 3,230 mg/kg wet wt
whole fish with an average of 2,411. These values are comparable to
fish from other geographical areas and are suitable for use in sodium-
restricted diets.
1931.
Ogura, K. 1959. Midgut gland cells accumulating iron or copper
in the crayfish, Procambarus clarkii. Annotationes
Zoologicae Japonenses. 32:133-142.
Accumulation of ferric iron and copper under natural condi-
tions was detected in midgut gland. Both metals appeared in a particu-
lar type of acinus cells, being contained in various size granules.
Besides iron or copper-containing cells, a few other types of cells
were distinguished in acinus epithelium. Excretion of metal-containing
granules was markedly promoted by removal of eyestalks.
1932.
Oguri, M. 1976.
rainbow trout.
On the enlarged liver in "cobalt" variant of
Bull. Jap. Soc. Sci. Fish. 42(8):823-830.
Trout from high cobalt environments were characterized by
corpulent body structures and enlarged livers. Liver in fish weighing
40 to 60 g contained elevated glycogen levels; liver of larger trout
contained abundant fat droplets. It was concluded that liver enlarge-
ment in trout from high cobalt waters was induced by accumulation of
glycogen and fat resulting from organ malfunction.
1933.
Ohmomo, Y.. H. Suzuki, M. Sumiya and M. Saiki. 1972~ Studies
on accumulation, excretion and distribution of iodine-131
and cadmium-115m in freshwater fish and marine fish. Jour.
Rad. Res. 13:3-4. (Abstract)
239
-------
High accumulation of cadmium-115m in kidney was noted in the
freshwater teleost Cyprinus carpio; in the marine fish Gire1la punctata,
highest enrichment was in digestive tract. High excretion range of
cadmium-115m from gill was recognized for both Cyprinus and Girella.
The longest-lived component of cadmium-115m in freshwater fish had a
biological half-life of about 58 days.
1934.
Okubo, K. and T. Okubo. 1962. Study on the bioassay method for
the evaluation of water pollution - II Use of the fertilized
eggs of sea urchins and bivalves. Bull. Tokai Reg. Fish. Res.
Lab. 32: 131-140. (In Japanese, English summary)
Concentrations of metals salts, which grossly affect larval
development (no effect on development) of sea urchin Anthocidaris, sea
urchin Hemicentratus, mussel Mytilus, and oyster Crassostrea, in 24 hr
at 20-27 C were determined. Concentrations in mg metal!l for Cu were
0.1 (0.032), 0.032 (0.01), 0.1 (0.032) and 0.1 (0.032); for Hg this
was 0.032 (0.01) for all 4 species; for Fe, 10 (3.2). n.d., 32 (10), and
n.d.; for Mn 32 (10), n.d., 32 (10) and n.d.; for Zn 0.32 (0.1), n.d.,
1.0 (0.32) and 3.2 (1.0); and for Cr 10 (3.2), >1.0, 10 (3.2) and n.d.,
respectively. LC-50 (24 h) values, in mg!l for brine shrimp Artemia,
were 0.68 to 2.5 for Cu, 21 to 50 for Hg, 1570 to 2880 for Mn, 160 to
275 for Zn and 40 for Cr. LC-50 -(24 h) values, in mg/l, for crabs
Sesarma, were 5.2 to 6.0 for Cu, 0.06 for Hg, 500 for Mn, 6.2 for Zn and
56 for Cr. Respective levels of no effect for barnacle Balanus adults
and nauplii, respectively, were, in mg/l: 3.2 and 3.2 for Cu; 0.32 and
0.1 for Hg; 100 and 100 for Mn; 32 and 3.2 for Zn; and 3.2 and n.d. for
Cr. Authors concluded that larval stages were more sensitive to metal
pollutants than previously examined adult forms.
1935.
Olafson, R.W. and J.A.J. Thompson. 1974. Isolation of heavy
metal binding proteins from marine vertebrates. Marine
Biology 28:83-86.
Cadmium binding proteins have been isolated from liver homo-
genates of the Atlantic grey seal Halichoerus grypus, the Pacific fur
seal Callorhinus arsinup, and copper rock fish Sebastodes caurinus.
Rock fish showed an increase in hepatic cadmium binding protein upon
administration of CdC12. The apparent molecular weights of the iso-
lated proteins were 9000 for grey seal, 10,000 for fur seal, and 11,000
for fish.
1936.
Olson, G.F., 0.1. Mount, V.M. Snarski and T.W. Thorslund. 1975.
Mercury residues in fathead minnows, Pimephales promelas
240
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Rafinesque, chronically exposed to methylmercury in'water.
Bull. Environ. Contamin. Toxicol. 14(2):129-134.
Minnows were continuously exposed to methylmercury water con-
centrations of 0.018, 0.036, 0.063, 0.114, and 0.247 ug/l. After 48
weeks exposure total mercury residues in whole fish were 1.47, 2.50,
4.48, 7.06, and 10.90 mg Hg/kg tissue (wet wt). Concentration factors
for lowest and highest water concentrations were 8.2 x 104 and 4.4 x
104, respectively. Control fish living in water with concentrations of
mercury less than 0.01 ug/l contained 0.21 mg/kg total body residue.
These body concentrations are the result of continuous water exposure
and probable intake from a portion of the food eaten.
1937.
Olson, K.R. and R.C. Harrel. 1973. Effect of salinity on acute
toxicity of mercury, copper, and chromium for Rangia cuneata
(Pelecypoda, Mactridae). Contrib. Mar. Sci. 17:9-13.
The 48, 72, and 96 hr LC-50's for mercury, copper, and
chromium were determined for a brackish water clam at salinities of
<10/00, 5.50/00, and 220/00. All ions were more toxic in freshwater
than in more saline waters requiring 6.3 mg/l Hg, 0.78 mg/l Cu, and
0.96 mg/l Cr for a 48 hr LC-50. At 5.50/00, 48 hr LC-50's were 40.0
mg/l Hg, 16.0 mg/l Cu, and 66.0 mg/l Cr; and at 220/00, 48 hr LC-50's
were 17.0 mg/l Hg, 14.7 mg/l Cu, and 86.0 mg/l Cr. Seventy-two and
96 hr LC-50's followed similar trends.
1938.
Ophel, I.L. and J.M. Judd. 1967. Skeletal distribution of
strontium and calcium and strontium/calcium ratios in several
species of fish. In Lenihan, J.M.A. (ed.). Strontium
metabolism. Academic Press: 103-109.
Sr and Ca contents of bony and calcified structures of perch
Perca flavescens, from Perch Lake, Canada, and Lake Huron and redhorse
sucker Moxostoma areolum from Lake Huron were determined. The Ca
content in mg/g ash wt, was uniform in different bony tissues of the
same fish; this ranged from 362 to 372 in Perch Lake perch, 364 to 371
in Lake Huron perch and 327 to 367 in Lake Huron suckers. Each species
had a characteristic Sr content: values in mg/kg ash wt ranged from
373 to 413 in Perch Lake perch, 272 to 312 in Lake Huron perch and 321
to 389 in Lake Huron sucker. Differences in Sr content in bone of perch
from the two lakes reflect differences in Sr/Ca ratios of lake waters.
Observed strontium/calcium ratios (Sr/Ca in fish bone to Sr/Ca in lake
water) in Perch Lake perch was 0.21. In Lake Huron fish, these ratios
were for perch 0.19, redhorse sucker 0.23, longnose sucker Catostomus
catostomus 0.23, gizzard shad Dorosoma cepedianum 0,24, and carp
Cyprinus carpio 0.66. Authors concluded that high observed ratio in
241
-------
carp is due in part to its diet of aquatic plants which do not discrimi-
nate against Sr.
1939.
Oporowska, K. 1976. Investigations on the content of copper in
the ponds of some regions of Poland. Acta Hydrobiol. 18(2):
139-152.
Cu and Zn levels in fish from eleven Polish ponds were deter-
mined. Cu levels in gills, in mg/kg wet wt, ranged from 2.5 (tench) to
11.7 (German carp). Zn in gill ranged from 4.8 (tench) to 44.0 (carp).
For liver, Cu levels extended from 5.2 (pike) to 18.5 (carp); Zn range
was 6.0 (pike) to 29.5 (carp). In flesh, Cu content ranged from 1.2
(carp) to 1.7 (tench); for Zn this was 1.1 (pike) to 4.2 (carp). Copper
in water column for all ponds ranged from 1-490 ~g/l; for bottom sedi-
ments this was 8-535 mg/kg dry wt. High Cu in water and sediments was
reflected in high Cu content of fish gills.
1940.
Orvini, E., T.E. Gills and P.D. LaFleur. 1974. Method for
determination of selenium, arsenic, zinc, cadmium, and mer-
cury in environmental matrices by neutron activation analysis.
Anal. Chern. 46:1294-1297.
Average concentrations, in mg/kg wet wt, for albacore tuna
flesh were: Se 3.3, As 4.6, Zn 13.4, Cd 0.06, and Hg 1.03.
1941.
Oshida, P.S., A.J. Mearns, D.J. Reish and C.S. Word. 1976.
effects of hexavalent and trivalent chromium on Neanthes
arenaceodentata (Polychaeta: Annelida). S. Calif. Coastal
Water Research Project, 1500 E. Imperial Hwy., El Segundo,
Calif., TM 225. 58 pp.
The
Lethal and sublethal effects of Cr+3 and Cr+6 upon marine
polychaetes were evaluated. For hexavalent chromium, as K2Cr207, the
LC-50 (96 hr) and LC-50 (168 hr) value ranges were 2.2 to 4.3, and 1.44
to 1.89 mg Cr+6/l. In a long-term (3 generations, 440 days) experiment
with Cr+6, reproduction ceased at 0.10 mg/l and brood size decreased at
levels of 0.0125 mg/l and above. Worms exposed to 0.05 mg/l Cr+6 in
the long-term experiment had tissue concentrations of 6.20 to 81.7
mg/Cr kg wet wt, which is more than lOX greater than controls (0.486
to 1.55 mg/wet kg) exposed to <0.001 mg/l total Cr. In experiments
with trivalent chromium (as CrC13), in which worms were exposed to a
precipitated form of Cr+3, there was <5% mortality at 12.5 mg/l during
a period of 168 hr. Worms that lived in Cr+3 precipitate during a
long-term (2 generations, 293 days) experiment showed no adverse effects
or abnormal behavior. Thus, although Cr+6 reduces brood sizes at
242
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relatively low seawater concentrations (0.0125 mg/l), Cr+3 as a pre-
cipitate in seawater had no detrimental effects on worms at concentra-
tions of'50.4 mg/l. A literature review of Cr in the environment
,
wastewater and invertebrates, as well as effects of selected trace
metals on polychaetes, is presented.
1942.
Oshida, P.
duction
1500 E.
and D.J. Reish. 1975. Effects of chromium on repro-
in polychaetes. So. Calif. Coastal Water Res. Proj.,
Imperial Hwy., El Segundo, Calif. Ann. Report: 55-60.
Hexavalent and trivalent chromium effects on Nereis arenaceo-
dentata at various concentration levels were determined. At 20 C,
lethal levels of Cr+6 were 2.22 to 4.30 mg/l in 4 days, from 1.44 to
1.89 in 7 days, 0.78 in 14 days, and 0.2 mg/l in 56 days. The lowest
level inhibiting tube building was 0.079 mg/l in 14 days. For Cr+3, no
significant mortality occurred at 0.195 to 12.5 mg/l levels over a 3
week period; total die-off occurred at 50 mg/l within 24 hr, probably
from extremely low pH (4.5). Inhibition of egg laying occurred at 0.1
and 0.2 mg/l Cr+6; abnormal behavior occurred only at 0.2 mg/l level.
Presence of Cr+6 caused reduction in mean brood size from 305 in con-
trols to 150 at 0.0125 mg/l, 137 at 0.025 mg/l, and to 78 at 0.050 mg/l.
Relative mean times required to spawn were longer in controls (117 d)
and 0.05 mg/l (121 d) than in 2 intermediate concentrations of 0.0125
mg/l (107 d) and 0.025 mg/l (90 d). Reduced spawning time implies a
net increase in number of generations per year and therefore larger
populations for animals exposed to intermediate Cr concentrations.
Trivalent Cr showed no significant mortality prior to spawning or
abnormal behavior. Data suggest that pure trivalent Cr in seawater
forms a precipitate that is not toxic to N. arenaceodentata.
1943.
Osterberg, C. 1962. Fallout radionuclides in euphausiids.
Science 138:529-530.
Euphausia pacifica, collected off the western U.S. coast,
contained up to 618 pCi Zr-95-Nb-95, 180 pCi Ce-14l, and 30 pCi Ru-l03
per g dry wt. Values were highly variable both temporally and spatially.
1944.
Osterberg, C., A.G. Carey and H. Curl. 1963. Acceleration of
sinking rates of radionuclides in the ocean. Nature, London
200:1276-1277.
Sea cucumbers Paelopatides sp. collected from a depth of 2800
m contained Ce-14l-l44 Zr-95-Nb-95 and K-40 in amounts similar to those
,
of Stichopus californicus, a sea cucumber from 200 m. Amounts of Zn-65
in Paelopatides was lower than that of Stich opus. Sea anemones and
243
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worms from 2800 m also contained Zr-95-Nb-95. Authors suggest that
short (7-12 d) downward transit times of Zr-95-Nb-95 and Ge-14l-l44 are
due to incorporation of unassimilated radionuclides in fecal pellets of
copepods, euphasiids, salps and pteropods.
1945.
Osterberg, C., L. Small and L. Hubbard. 1963. Radioactivity in
large marine plankton as a function of surface area. Nature,
London 197:883-884.
Euphausia pacifica of mean length 20 mm were compared with
copepods Calanus cristatus, averaging about 9-10 mm in content of K-40,
Zn-65, Zr-95-Nb-95, Ru-l03-l06, Cr-Sl and Ce-14l. Total radioactivity
per gram dry wt was greater in euphasiids despite their smaller surface
area per unit wt. A second experiment comparing large adult ~. pacifica
with small adults and juveniles showed that radioactivity, with excep-
tion of Cr-Sl, was not greater in small euphasiids, which exhibited
greater surface area per unit wt ratios and indicates that factors other
than surface area are important. The exception of Cr-5l may be sig-
nificant due to particle size of Cr. A comparison of radioactivity in
the transparent outer body of pelagic tunicates Salpa sp., with internal
"nucleus" which contains digestive tract, showed higher concentrations
in nucleus. Zirconium-95-niobium-95, and cerium-l4l which are particu-
late in seawater were most strongly concentrated in the "nucleus" while
zinc-65 and potassium-40, which are in ionic form show markedly smaller
concentration ratios.
1946.
Ottolenghi, p, 1975. The reversible delipidation of a solu-
bilized sodium-pIus-potassium ion-dependent adenosine triphos-
phatase from the salt gland of the spiny dogfish. Biochem.
Jour. 151:61-66.
A microsomal fraction rich in Na+, K+-ATPase and correspond-
ing K+-dependent p-nitrophenyl phosphatase from rectal salt gland of
spiny dogfish Squalus acanthias, was solubilized by treatment with
deoxycholate at high ionic strength. On gel filtration, the ATPase
apoenzyme could be separated in apparently soluble form, from the
tissue-fraction phospholipids and was almost free of enzymic activity.
On mixing the apoenzyme with an activator, a large proportion of the
original enzymic activity was obtained. Specific activities of the
re-activated enzyme were somewhat higher than in the material before
gel filtration: values of 1300-1450 uM and 250-290 uM/h per mg of pro-
tein were obtained for the hydrolysis of ATP and of p-nitropheny1 phos-
phate,respective1y. The activity was inhibitib1e by ouabain.
244
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1947.
Overnell, J. 1975. The effect of heavy metals on photosynthesis
and loss of cell potassium in two species of marine algae,
Dunaliella tertiolecta and Phaeodactylum tricornutum. Marine
Biology 29:99-103.
For ~. tertiolecta, Cu-induced K release occurred at marginally
lower concentrations than did inhibition of photosynthesis; the primary
toxic effect of Cu being an increase in permeability of the cell. Mer-
cury and thallium appear to be transported through the outer membrane of
cell to chloroplast where photosynthesis is inactivated at concentrations
causing no damage to cell membrane, as reflected in K leakage. Methyl
Hg had a very limited effect on K leakage, suggesting a very selective
action on the membrane. Methyl Hg caused complete inhibition of oxygen
evolution at low levels (~l x 10- M). P. tricornutum was particularly
sensitive to external K concentrations. -At Hg or Cu concentrations
above 10-5 M, light-induced respiration occurred. This may be due to
decomposition of chloroplast lamellae, with subsequent liberation of
chlorophyll forms capable of promoting photosynthesized oxidation of
reducible substrates present in cells. Both algal species were insensi-
tive to Cd, Pb and Zn.
1948.
Palermo, T. 1971. Analysis of fish tissue for mercury content.
State of Mass. Div. Fish Game, Proj. F-35-R-3, Job III-I. 10 pp
A total of 59 fish collected between July 1970 and March 1971
from 11 freshwater streams and 16 ponds in Massachusetts were analyzed
for total mercury. Stream-caught fish (n=24) contained between 0.03 and
0.99 mg Hg/kg wet wt muscle, with 33% at 0r above the FDA level of 0.5
mg/kg. Pond-caught fish (n=35) contained between 0.05 and 1.36 mg Hg/kg
wet wt muscle, with 40% at or above the established 0.5 mg/kg level.
Most fish containing more than 0.5 mg Hg/kg wet wt were predators, i.e.
walleye, largemouth bass, smallmouth bass, and chain pickerel. A total
of 22 trout (brook, brown and rainbow) from 4 hatcheries were also
analyzed for mercury. Concentrations of Hg in catchable-size hatchery
trout ranged from 0.00 to 0.10 mg/kg wet wt muscle.
1949.
Parrish, K.M. and R.A. Carr. 1976. Transport of mercury through
a laboratory two-level marine food chain. Marine Poll. Bull
7(5):90-91.
Algae Croomonas salina, grown in 164 ~g Hg/l for 48 hrs, accumu-
lated 1400 mg Hg/kg dry wt. Copepods Acartia tonsa, fed contaminated ~.
salina for 5 days showed no impairment of egg laying, nor retention of
Hg in tissues, eggs or feces. Eggs of an exposed female developed to
the copepodite IV stage with no apparent ill effects.
245
-------
1950.
Parry, G. 1954. Ionic regulation in the palaemonid prawn
Palaemon (=Leander) serratus. Jour. Exp. BioI. 31:601-613.
Blood and urine of Palaemon serratus were analyzed for Na, K,
Ca, Mg, Cl, and S04 during immersion in 50, 100 and 120% seawater. In
100% SW concentrations, expressed as percentages of concentrations in
medium, were: Na, K and Cl, 85%; Ca, 105%; Mg, 20%; S04, 10%. In 50%
SW the corresponding figures were: Na and Cl, 105%; K, 120%; Ca, 200%;
Mg, 20%; S04, 10%. In 120% SW these values were: Na, K and Cl, 85%;
Ca, 115%; Mg, 30%; S04, 20%. Concentrations of Na, K and Ca in urine
are always slightly «20%) less than concentrations in blood; Cl level
is slightly greater in urine than blood (10-20%) and concentrations of
Mg and S04 are very much greater, by factors of up to 7 times. Relative
concentrations of ions in blood and urine do not change substantially
with changes in external medium. The antennal gland, although it plays
no part in purely osmotic regulation, is partly responsible for main-
taining low blood concentrations of Mg and S04.
1951.
Parry, G. 1957. Osmoregulation in some freshwater prawns.
Jour. Exp. BioI. 34:417-423.
The salt concentration in blood and urine of Palaemonetes
antennarius, a freshwater prawn, was different than the brackish water
P. varians and Palaemon longirostus. Contrary to freshwater crayfish
which produce dilute urines, P. antennarius produces urine isosmotic
with blood at the rapid rate of 2% body wt/hr. When held in distilled
water these prawns lost salt at a rate of 2.21 uM/g/hr; upon return to
natural (very dilute) medium, an uptake rate of 2.56 uM/g/hr was observed,
It is probable that under natural conditions there is a constant absorp-
tion of ions to compensate for osmotic inflow of water and loss of salts
through antennal glands.
1952.
Parry, G. and W.T.W. Potts. 1965. Sodium balance in the fresh-
water prawn, Palaemonetes antennarius. Jour. Exp. BioI. 42:
415-421.
Sodium content of P. antennarius and rates of influx and efflux
in freshwater and other media are described. The greater part of efflux
is due to loss in urine. Loss varies from 3.5 mM-Na/kg animal/hr (79.5
mg Na/kg/hr) to 4.3 mM/kg/hr (98.9 mg/kg/hr) depending on media. Rate
of influx depends on salt load of the animal: salt-deficient animals
have a higher uptake rate than equilibrated animals; salt-loaded animals
have lower rates of uptake. Influx rate declines rapidly at external
salinity <0.5 mM/l, while efflux remains almost constant. This could
indicate a threshold effect and may be important in determining distribu-
tion of P. antennarius
246
-------
1953.
Pasanen, S. and P. Koskela. 1974. Seasonal changes in calcium,
magnesium, copper and zinc content in the liver of the common
frog, Rana temporaria L. Compo Biochem. Physiol. 48A:27-36.
In Finland, values in frog liver for Ca, Mg, Cu and Zn per unit
wt are lowest during winter and highest during spring and summer, partly
as a result of seasonal changes in-wt and water content of liver. The
total Ca, Mg, and Zn figures are highest during summer and autumn due to
feeding and rapid metabolism. Total copper remains practically constant
throughout the year in liver of males, but in females there is a clear
spring maximum connected with egg-laying. Sex differences are found in
dry wt liver Ca and Mg content during summer, apparently due to ovary
development. Highest values recorded, in mg/kg dry wt, were 315 for Ca,
749 for Mg, 845 for Cu, and 91 for Zn. On a wet wt basis these were 75
for Ca, 180 for Mg, 207 for Cu, and 25 for Zn.
1954.
Patel, B. and G.R. Doshi.
as indicator of 54Mn.
1971. Lamellidens marginalis (Lamarck)
Arch. Oceanogr. Limnol. 17:27-42.
During radioecological studies in Bombay, the freshwater
mussel L. marginalis concentrated high amounts of Mn-54 deposited through
fallout~ and stable manganese from its environment. Teleosts (Labeo
rohita, Cyprinus carpio, Tilapia mossambica) from the lake contained
background levels of Mn-54. Of the various tissues of mussel, labial
palp showed maximum concentration of stable (9872 mg/kg) and radioactive
("'9000 pcMn-54/kg) manganese, follm'led by gill, mantle fold, visceral
sac, adductor muscle and foot. Concentration factors, in mg/k~ wet wt,
were determined for Mn (1122 x 102), Zn (258 x 102),Fe (4 x 10 ), Cu
(16 x 102), Sr (32 x 102) and Ca (16 x 102). Distribution of Mn, Ca,
and Sr in various parts of shell are also given.
1955.
Patel, B. and A.K. Ganguly. 1968. Concept of acute and chronic
tissue concentration of elements in radioecology. Symp. on
Mollusca, Marine BioI. Assn. India, Vol. 2:446-455.
Using data from previous studies, authors differentiate two
types of concentration and concentration factors encountered in radio-
ecological studies: one obtained under natural environmental condi-
tions; and another under controlled laboratory conditions and using the
Chronic Concentration (CC) , Chronic Concentration Factor (CCf), Acute
Concentration (AC), and Acute Concentration Factor (ACf).
For metabolically significant trace elements, such as Zn, Mn,
Fe, Co, etc., which form parts of enzymes systems, CCf's are consistently
higher than ACf's in all marine organisms studied. Curves of uptake and
elimination rates for these elements by shellfish are always steeper for
uptake than initial loss rates. Elements with chemical properties
247
-------
similar to the previous ones, but whose metabolic functions/importance
are not known, such as Ce, Sr, etc., have ACf's and CCf's which are often
the same in, soft tissues; rate of uptake depending on relative concen-
tration of chemically similar elements in the medium. CCf's of Sr are
higher than ACf's in skeletons of invertebrates and fish, possibly due
to fixation of minerals in the non-metabolic zone of skeletal system.
Uptake and elimination rate curves for these elements have both steep
uptake and initial elimination rates, with slopes very close to one
another. For elements which are metabolically not significant, such as
Cr, U, Pu, etc., AC's and CC's depend on concentration of element in
medium. In general, CCf's are higher than ACf's for both Cr and U.
Definite conclusions on Pu cannot be drawn as equilibrium with Pu may
not be attained in the orgamism's lifetime. These elements show a lower
initial rate of absorption than elimination in uptake-elimination rate
curves. Organisms, in general, concentrate significantly higher amounts
of isotopes under chronic exposure conditions than acute exposure. Life-
time exposure to a radioisotope under natural conditions eventually
results in CCf's of the same value as those obtained with stable iso-
topes in the environment.
1956.
Patel, B., C.D. Mulay, and A.K. Ganguly. 1975. Radioecology of
Bombay Harbour--a tidal estuary. Estuarine Coast. Marine
Sci. 3:13-42.
Low level liquid radioactive wastes from nuclear facilities
at Bhabha Atomic Research Centre, Bombay, are released into Bombay
Harbour after monitoring and dilution. Interactions of gamma-emitting
fission product nuclides, especially cesium-137, with sedimentary parti-
cles and biota were studied during 1968-71. Cesium-137 is first
scavenged by sedimentary particles, followed by cerium-144 and ruthenium-
106. Zirconium/niobium-95, though present in the effluent, was not
sorbed. Cs-137 was distributed throughout the harbor, whereas Ce and
Ru deposition were limited to a few stations off Trombay coast. Maxi-
mum deposition of Cs-137 activity was around the discharge zone off
Trombay; it decreased significantly with distance, the concentration
being 100X lower towards the harbor mouth. Over the period of surveil-
lance there was about 2-3X increase in accumulation of radioactivity by
bed material, though total radioactivity in effluent discharge had in-
creased 5X. Maximum deposition of activity was found in the upper 5 cm
layer of sediment column; decreasing thereafter either intermittently
or exponentially with depth. The sorption sequence of Cs-137, Ce-144
and Ru-106 was explained in terms of sorption rate, mineral structure,
and physicochemical parameters controlling diffusion mechanisms.
The occurrence of artificial radioactivity in fish and shell-
fish of economic importance in 1965 before regular discharge began was
below the detection limit. Anlaysis since then showed accumulation of
Cs-137 only. Other nuclides, Ce-144, Ru-106 and Zr/Nb-95, were not
248
-------
detected except in the ark-shell bivalve Anadara granosa, which showed
specific accumulation of Cs, Ce, and Ru nuclides but no~ Zr/Nb-95,
although this nuclide was present in the effluent. A. granosa was there-
fore used as an indicator to detect contamination due to cerium and
ruthenium radionuclides. Lamellibranchs and crustaceans, in general,
were the most effective integrators of Cs-137. In these benthic sEecies,
concentration factors (Cf's) for the nuclide varied from 102 to 10 ;
pelagic species were poor integrators of Cs-137 (Cf's: 10-50). Monthly
variation in concentration of Cs-137 in ~. granosa, Placenta placenta
(bivalve), Scylla serrata (crab), and Periopthalmus sp. (fish) could be
related to variation in amount of activity released. Maximum concen-
tration of Cs-137 occurred in muscle tissues of different species.
Radiation dose from contaminated environments to benthic communities was
far below limits required to produce detectable radiation damage. Radi-
ation dose to fishermen, both internally through the consumption of
contaminated marine products and externally through fishing over the
contaminated bed, was also well below permissible dose limits.
1957.
Patrick, F.M. and M. Loutit. 1976. Passage of metals in
effluents, through bacteria to higher organisms. Water
Research 10:333-335.
Bacteria were most abundant in river sediments receiving
effluents from various sources. Sediment isolates contained metal
levels, in mg/kg dry wt, of 2973 for Cr, 1512 for Cu, 456 for Mn, 2664
for Fe, 1881 for Pb, and 1127 for Zn when grown in 2 mg of each metal/l
for 7 days at 28 C. Tubificid worms of genera Tubifex and Limnodrilus,
from stream sediments contained concentrations, in mg/kg dry wt, of 19
for Cr, 81 for Cu, 113 for Mn, 1286 for Fe, 151 for Pb, and 530 for Zn.
Worms fed bacterial cells grown in 2 mg/l of each metal contained levels,
in mg/kg dry wt, of 30 for Cr, 621 for Cu, 25 for Mn, 1944 for Fe, 568
for Pb, and 868 for Zn.
1958.
Peakall, D.B., D.S. Miller and W.B. Kinter. 1975. Blood cal-
cium levels and the mechanism of DOE-induced eggshell thin-
ning. Environ. Pollut. 9:289-294.
Ring doves Streptopelia risoria, a~d white Peki~ d~cks Anas
platyrhynchos, fed DOE, exhibited 35% and 20~ eggshell thlnnlng,
respectively; blood calcium levels remained constant at 20 and 46 mg %,
respectively. Blood calcium levels, although constant in ring doves,
are more variable in ducks, decreasing to 18 mg % when not laying.
Results from these studies are consistent with those mechanisms of DOE
action involving inhibition of shell gland function, but not with those
involving decreased calcium supply to the gland.
249
-------
1959.
Pe1ati, L.T. and C. Triu1zi. 1972. The radioactivity of some
plankton and sea water samples collected during the 1960-1968
period. Rapp. Comm. into Mer Medit. 20:735-737.
Gross beta radioactivity in plankton, including activity con-
tributed by Ce-144, Pm-147, Eu-155, Zr-95, Sb-125, and Mn-54, was
measured from the North Adriatic and Ligurian-Tyrrhenian Seas during
1960-1968. Highest values were reached in 1963 and these approximated
the trends of fallout debris; in 1968 the same values of 1961 were
reached. Comparison of Sr-90 values in seawater and plankton samples
for North Adriatic and Ligurian-Tyrrhenian Seas showed that Sr-90 con-
tamination of seawater is higher in the Adriatic while Sr-90 contamina-
tion of plankton is always higher in Ligurian-Tyrrhenian Sea. Concen-
tration factors for plankton samples are lOX more for Ligurian-Tyrrhenian
plankton than Adriatic plankton; this was attributed to presence of the
protozoan Acantharia, as specific strontium accumulators.
1960.
Penot, M. and C. Videau. 1975. Absorption du 86Rb et du 99Mo
par deux algues marines: Le Laminaria digitata et 1e Fucus
serratus. Z. Pf1anzenphysio1. Bd. 76 (Supp1)~285-293.
During exposure for 2 hrs in seawater containing rubidium-86
at 15 C, Fucus accumulated the equivalent of 1.7 mg/kg Rb dry wt; for
Laminaria this was 1.0. Similar studies with mo1ybdenum-99 showed
Laminaria with 0.5 mg/kg Mo dry wt, but only 0.1 mg/kg in Fucus during
an identical exposure interval. Temperature affects uptake of Rb by
Laminaria; Rb content at 15 C was twice that at 0 C in 2 hr. Fucus
accumulated 2X more Mo at 15 than 0 C in 5Y2 hrs. Rb uptake by Fucus
was reduced by half in 5 hrs with 10-3 M dinitrophenol; a similar pattern
was observed with Mo uptake by Laminaria and 10-5 M KCN. Increasing
light intensity (lux) enhances Rb uptake in both species; however, light
intensity did not effect Mo uptake by either in 5 hrs.
1961.
Penrose, W.R. 1975. Biosynthesis of organic arsenic compounds
in brown trout (Sa1mo trutta). Jour. Fish. Res. Bd. Canada
32:2385-2390.
Radioactive inbrganic arsenic was administered to trout orally
and by intramuscular injection. After oral administration of 1 ~g As as
arsenic acid, As concentrations in ~g/kg, in blood, muscle and liver
tissues after 4.5 hr were, respectively, 0.20, 0.18 and 1.08; after
24 hr, these were 0.37, 2.03 and 1.42. Uptake of orally administered As
was accompanied by conversion to a nonanionic form, which was also found
in gastro-intestina1 contents. Following 1M injection of 1 ~g As as
arsenic acid, As concentrations after 4.5 hr, in ~g/kg in blood, muscle
and liver tissues of trout were 6.67, 1.10 and 2.80, respectively; after
250
-------
48 hr, these were 0.13, 1.37 and 0.76. Injected As appeared in tissues
in inorganic form and was only slowly converted to organic form; mean-
while, large amounts of inorganic and organic As occurred in bile.
Author maintains that findings are consistent with biosynthesis of
organic As compound within gastro-intestina1 tract.
1962.
Penrose, W.R., R. Black and M.J. Hayward. 1975. Limited arsenic
dispersion in seawater; sediments, and biota near a continuous
source. Jour. Fish. Res. Bd. Canada 32:1275-1281.
Moreton's Harbor, Newfoundland, has been exposed to arsenic-
bearing drainage and leaching from a stibnite mine for at least 38 years.
Sediments contained 2600 mg As/kg at point of input, 847 mg/kg 34 m
offshore and 11.0 mg As/kg 65 m offshore. Inorganic As levels in sea-
water were 5.3, 4.1, 2.4 and 0.2 ~g/l at distances of 0, 34, 147 and 186
m, respectively. Sea urchin Strongylocentrotus droebachiensis gonads
contained As levels, in mg/kg, of 6.0, 5.6, 3.8 and 1.9 at distances of
0, 35, 57 and 189 m from input source. Respective As levels, in mg/kg,
of marine organisms collected at source of As input, and from control
sites 5 or 300 km distant, were 5.3 and 1.6 for mussel Mytilus edulis
(minus shell); 11.5 and 4.0 for snail Littorina littorea (minus shell);
17.2 and 12.1 for algae Fucus sp.; 17.2 and 9.8 for algae Ascophyllum
nodosum; and 0.8 and 0.4 for blenny (fish) muscle. Lobsters Homarus
americanus, collected at input site, contained 3.8 and 7.6 mg As/kg.
1963.
Pentreath, R.J. 1971. The metabolism of radio nuclides. In
Marine Radioecology, Proc. Second ENEA Seminar, Hamburg:--
97-126.
Author reviews radionuclide metabolism processes in freshwater
and marine biota, including effects of temperature and salinity on up-
take, retention, excretion, tissue distribution and storage, subcellular
distribution, enzyme utilization and dynamics of cellular exchange.
Specific examples are given with isotopes of Ce, Cs, Ca, Sr, Zn, Ru, Nb,
K, Y, Fe, Mn, and Co in algae, crustacea, teleosts, molluscs, annelids,
and elasmobranchs.
1964.
Pentreath R.J. 1973. The accumulation from seawater of
,
54Mn, 58Co and 59Fe by the thornback ray, Raja c1avata
Jour. Exp. Mar. BioI. Eco1. 12:327-334.
65Zn
,
L.
Respective Zn, Mn and Fe concentrations, in mg/kg wet wt, of
thornback rays, were 4.7, 0.16 and 105 for whole blood; 9.4, 0.27, and
29 for heart; 15.9, 0.32 and 109 for spleen; 17.1, 1.45 and 62 for liver;
11.3, 1.95 and 33 for kidney; 10.9, 0.37 and 9 for gonad; 14.8, 0.82 and
251
-------
13 for gut; 11.1, 1.47 and 24 for gill filaments; 12.3, 2.73 and 9 for
skin; 4.8, 0.29 and 2 for muscle; 19.3, 9.12 and 5 for cartilage; 8.5,
1.07 and 34 for rectal glan~ and 10.1, 0.41 and 10 for brain and nerve
cord, giving whole body levels of 9.6 (Zn), 2.4 (Mn), and 9.4 (Fe).
After 90 days, whole body concentration factors were 20, 5, 3 and 1 for
Fe-59, Zn-65, Co-58 and Mn-54, respectively.
1965.
Pentreath, R.J. 1976. Some further studies on the accumulation
and retention of Zn-65 and Mn-54 by the plaice, Pleuronectes
platessa L. Jour. Exp. Mar. BioI. Ecol. 21:179-189.
Previous studies have determined that direct absorption of
Zn-65 and Mn-54 plays a minor role in accumulation of these metals.
Therefore tests were made to determine whether accumulation occurred
via food or by absorption from water using eggs and larvae of a marine
flatfish. Accumulation by embryo was negligible; larval accumulation
rate of Zn-65, at 15 ~g/l of Zn, represented an intake of 7.2 ng/g/day;
for Mn-54, at 2 ~g/l, this was 0.86 ng/g/day. Concentrations within 7
g fish (~200 days after hatching) were 6.6 ~g/g wet in muscle and 39.2
~g/g wet in bone for Zn; and 40 ~g/g wet in bone for Mn. It appears
that food constitutes the major pathway for accumulation. Stable element
analyses of liver, muscle, and bone samples from fish of differing
weights and ages show that concentrations in adult fish remain fairly
constant: Zn values varied by only a factor of 3 in muscle and 2 in
bone (the largest components); Mn varied by a factor of 4.4 in bone; and
Fe varying by 4, 7, and 20 in bone, liver, and muscle, respectively.
On this basis it has previously been estimated that biological half-
times of these metals via food should be shorter than those observed
after accumulation from labelled water. Experiments using radioactively-
labelled Nereis diversicolor, gave effective half-times of 60 days for
Zn-65 and 35 days for Mn-54, supporting this view.
1966.
Pentreath, R.J. 1976. The accumulation of organic mercury from
seawater by the plaice, Pleuronectes platessa L. Jour. Exp.
Mar. BioI. Ecol. 24:121-132.
Accumulation of organic Hg from seawater by flatfish eggs,
larvae, and adults was determined using CH3 Hg-203 Cl. Eggs increasingly
accumulated the isotope, attaining a concentration factor of 465 after
12 days. Larvae rapidly accumulated Hg also with a CF of 2000 after 8
days. In young fish, whole body CF increased with time reaching a
maximum of 600 after 64 days. Highest concentration factors were in
blood, spleen and kidney. Muscle had the largest accumulation of CH3
Hg-203 Cl with 64% of total uptake. The biological half-time of CH3
Hg-203 Cl at 275 days is greater than inorganic Hg.
252
-------
1967.
Pentreath, R.J. 1976. The accumulation of mercury from food by
the 'plaice, P1euronectes p1atessa L. Jour. Exp. Mar. Biol.
Eco1. 25:51-65.
Flatfish were fed Hg-203C12 and CH3Hg-203Cl labelled Nereis
diversico10r worms. After 5 days only 3-5% of the initial inorganic
Hg dose was retained compared to 80-85% of CH3Hg-203Cl. The methyl form
of Hg was more rapidly assimilated. Three days post-exposure, 53-88%
of the initial dose remained in gut lumen of fish fed inorganic Hg; less
than 3% remained in gut of those fed organic Hg. In CH3Hg-203Cl-fed
plaice, Hg-203 accumulated in liver and kidney to a greater extent than
the inorganic form. Mean biological half-times for elimination of
Hg-203C12 and CH3Hg-203Cl were 32.9 and 163.0 days, respectively. Using
a simplified model of accumulation of methylmercury from food, concen-
trations of Hg in fish at different ages were calculated in relation to
basic physiological factors and dietary intakes. Solutions of this
model showed that a considerable range of concentrations of methyl-
mercury can be attained by individual fish depending on diet and rela-
tive weightings of parameters.
1968.
Pentreath, R.J. and M.B. Lovett. 1976. Occurrence of plutonium
and americium in plaice from the north-eastern Irish Sea.
Nature 262:814-816.
Adult flatfish, Pleuronectes platessa, collected during 1975
from the NE Irish Sea near the Windscale nuclear reprocessing plant were
analyzed radiologically for americium and plutonium. In February,
highest concentrations of Pu were in kidney, followed by liver, gut,
bone, gill, skin and muscle. In August, highest Pu concentrations were
in gill followed by gut, kidney, liver, skin, bone and muscle. Concen-
trations of Am-24l were, in general, higher than those reported for Pu.
In February, highest Am-241 concentrations were in liver, followed by
kidney, gill, gut, bone, skin and muscle. In August, the highest Am-24l
concentration was in gill, then gut, kidney, liver; bone, skin and muscle
The overall Am-24l levels were lower in August than February which might
reflect a decreased discharge rate of Am-24l. Data emphasizes that very
low and comparatively safe levels of Pu and Am are present in edible
portions of plaice, even from areas most liable to contamination.
1969.
Persoone, G. and G. Uyttersprot. 1975. The influence of inor-
ganic and organic pollutants on the rate of reproduction of
a marine hypotrichous ciliate: Euplotes vannus Muller. Rev.
Intern. Oceanogr. Med. 37-38:125-151.
Effects of Pb, Cu, Cd, Zn, and Hg ions, five pesticides, and
a PCB on reproduction of a marine protozoa are given. There was no
253
-------
effect of any metal at concentrations of 0.1 mg/l. Total Inhibition of
reproduction occurred in 100 mg/l of Pb, Zn, or Cd; 10 mg/l of Cu; or
1 mg/l of Hg. Organochlorine pesticides and PCB were all less toxic
than metals; 10 mg/l reduced reproduction rate by only 10%. When com-
pared to metal concentrations in the environment, only sediments con-
tained lethal levels (up to 926 mg/l Zn, 280 mg/l Pb, 221 mg/l Cu, and
1.24 mg/l Hg).
1970.
Peters, A.W. and 0. Burres. 1909. Studies on enzymes. II. The
diastatic enzyme of Paramoecium in relation to the killing
concentration of copper sulphate. Jour. BioI. Chern. 6:65-73.
Death of Paramoecia occurred within 20 seconds in the range
17.5 x 10-8 to 30 x 10-~ gm mol. per cc of copper sulphate (about 12 to
25 mg/Cu/l). A positive correlation was demonstrated between concentra-
tion of CuS04.5H20 that killed instantly and that concentration which
markedly inhibits the action of diastase.
1971.
Peterson, R.H. 1976. Temperature selection of juvenile Atlantic
salmon (Salmo salar) as influenced by various toxic substances.
Jour. Fish. Res. Bd. Canada 33:1722-1730.
Preferred temperature for salmon in a horizontal temperature
gradient was unaltered by metal salt levels, in mg/l, up to 0.03 for
CuS04 (~0.012 mg Cull), 0.39 for ZnS04 (~0.158 mg Zn/l), or 0.002 for
CdS04 (~O.OOI mg Cd/I).
1972.
Phelps, O.K., G. Telek and R.L. Lapan, Jr. 1975. Assessment of
heavy metal distribution within the food web. In Pearson and
Frangipane (eds.). Marine Pollution and MarinelWaste Dis-
posal. Pergamon Press, New York: 341-348
Chromium levels in sediments, water and biota were determined
in samples collected from Narragansett Bay, R.I. Highest levels were
in sediments (range 56.7-320.0 mg/kg dry wt) followed by seston (88.8-
211.0 mg/kg dry wt), phytoplankton (41.3-73.3), a polychaete annelid
(23.8-38.0), quahaug clam (3.3-24.7), winter flounder «2.2 mg Cr/kg dry
wt in selected tissues), and water column «0.005-0.032 mg/l). Authors
concluded that chromium accumulation above the primary producing level
of the food web is directly associated with food and feeding rather than
direct uptake from water column. It was suggested that chromium levels
in particle-feeding benthic organisms reflected those of polluted
reservoirs such as dredge spoil disposal sites.
254
-------
Phillips, A.H. 1917. Analytical search for metals in Tortugas
marine organisms. In Papers Dept. Mar. BioI. Carnegie Inst.
Washington, Publ. 251, xi:9l-93.
1973.
Maximum metal contents of marine organisms collected from the
Dry Tortugas, in g/kg dry wt, were:
Cu
Molluscs
Fasciolaria gigantea
(liver) :
Cassis sp.
(liver) :
3.7
0.10
Strombus bitubercalatus
(soft parts):
~. gigas
(liver):
(soft parts):
Fulgur perversus
(soft parts):
Aplysia sp.
(whole animal):
(liver):
0.03
0.04
0.13
0.035
0.15
0.11
Crustacea
Palinurus sp.
(blood) :
(liver):
Arachnoidea
Limulus polyphemus
(liver & gonads):
(blood) :
0.7
1.1
0.17
0.85
Echinodermata
Holothuria bermudiana
(muscle) :
(intestines) :
0.0
0.02
ZnO
0.6
0.10
0.07
0.38
0.255
0.39
0.08
0.10
0.0
0.2
0.67
0.07
0.22
0.065
Fe
1.0
0.5
0.56
2.0
0.965
0.57
0.435
0.62
0.86
0.285
0.27
0.29
0.29
0.01
MnO
0.01
0.008
0.055
0.22
0.11
0.008
0.01
0.0
0.07
0.0008
0.005
0.042
trace
trace
Tunicata
Ciona atra
(whole animal): 0.015 0.030 1.18 0.01
In addition, Fasciolara contained 0.003 g Pb Oz/kg dry wt.
1974.
Phillips, J.H. 1976. The common mussel Mytilus edulis as an
indicator of pollution by zinc, cadmium, lead and copper. I.
255
-------
effects of environmental variables on uptake of metals.
Marine Biology 38:59-69.
Mussels from 3 locations in Port Phillip Bay, Australia,
showed spatial and seasonal variations in metal content of whole soft
parts; for all locations, content in mg/kg wet wt, ranged from 19.3 to
60.1 for Zn, 0.2 to 1.3 for Cd, and 0.61 to 0.98 for Cu. Near fresh-
water metal inputs, Zn, Cd and Pb levels in mussels declined with depth;
when runoff was seasonally less, no variation was found. When subjected
to a mixture of 400 ~g Zn, 40 ~g Cd, 20 ~g Pb and 20 ~g Cu per liter at
temperatures of 10 and 18 C, a salinity decrease from 350/00 to 15%0
did not affect net uptake of Zn by mussels, but Cd uptake increased and
Pb uptake decreased. At these salinities, a temperature decrease from
18 to 10 C had no effect on net Zn or Pb uptakes; uptake of Cd was un-
affected by low temperature at 350/00, but decreased at 150/00. When
exposed to combinations of Zn, Cd, Pb and Cu at levels, in ~g/l, of
o to 400 for Zn, 0 to 40 for Cd, 0 to 20 for Pb and 0 to 20 for Cu, the
presence of other 3 metals had no effect on individual net uptake of
Zn, Cd or Pb. However net uptake of Cu was extremely erratic and was
affected by salinity, temperature, as well as presence of other metals.
1975.
Phillips, J.H. 1976. The common mussel Mytilus
indicator of pollution by zinc, cadmium, lead
relationship of metals in the mussel to those
industry. Marine Biology 38:71-80.
edulis as an
and copper. II.
discharged by
Mean metal levels in mg/kg wet soft tissue of mussels from
Port Phillip Bay and Western Port Bay, Victoria, Australia, ranged from
16.4 to 97.1 for Zn, 0.20 to 18.16 for Cd, n.d. to 10.02 for Pb, and
n.d. to 1.45 for Cu. Author concluded that mussels act as efficient
time-integrated indicators of Zn, Cd, and Pb over a wide variety of
environmental conditions. Cu levels were highly variable, and it was
suggested that alternative organisms be used as Cu indicators.
1976.
Pic, P. and J. Maetz. 1975. Differences de potentiel trans-
branchial et flux ioniques chez Mugil capito adapte a l'eau
de mer. Importance de l'ion Ca++. C.R. Acad. Sc. Paris 280
(Ser. 0):983-986.
The trans-branchial potential results primarily from diffusion
of Na+ and K+ along the length of their concentration gradient, and
secondarily by a Cl-pump mechanism. Ca++ ions modulate the relative
permeability of cations and Cl-.
256
-------
1977.
Pic, P., N. Mayer-Gostan and J. Maetz. 1975. Branchial effects
of epinephrine in the seawater-adapted mullet. II. Na+ and
Cl- extrusion. Amer. Jour. Physiol. 228(2):441-447.
Injection of epinephrine into Mugil capito adapted to sea-
water is followed by a 40-60% inhibition of Na and Cl effluxes. Simul-
taneously Na influx is decreased by 30%, the overall result being a
reduction of net Na extrusion rate by gill. Na influx change is in
part explained by a 75-80% decrease of oral ingestion of seawater. This
branchial adrenergic response is sensitive to a-blockade by phentolamine
and to1azo1ine and insensitive to B-blockade by propranolol. Both a-
blockers are ineffective when injected alone. Propranolol injected
alone mimics epinephrine while simultaneous injection of phentolamine
blocks response to propranolol. Rapid transfer experiments suggest that
epinephrine inhibits the branchial Cl pump and its associated Na/K
exchange mechanism. Leak pathway for these ions remains insensitive to
epinephrine.
1978.
Pilkey, O.H. and H.G. Goodell. 1963. Trace elements in recent
mollusk shells. Limnol. Oceanogr. 8(2):137-148.
In 7 species of marine mollusks collected from much of their
present range, metal contents of shells in mg/kg dry wt ranged from 0
to 438 for Mn, 3 to 1059 for Fe, 123 to 3114 for Mg, 3 to 48 for Ba and
1540 to 4097 for Sr. Differences in environmental salinity below 250/00
caused greater changes in shell composition than temperature differences.
Several significant correlations between shell composition and environ-
mental parameters were observed, but authors considered these to be too
weak for paleoecological determinations.
1979.
Pi1lai, V.K. 1956. Chemical studies on Indian seaweeds. I.
Mineral constituents. Proc. Indian Acad. Sci. 44(1)Sec. B:
3-29.
Seasonal variations in 11 species of algae were determined for
Na, K, Ca, Mg, Fe, Cu, Mn, B, Mo and Zn. K and Ca are absorbed more
efficiently than Mg, with intensity dependent on algal type. Distinct
minima in Na, K, Ca, and Mg were found between August and September, with
amounts increasing from December to June. Fe content is lowest in
Chlorophyceae and highest in Phaeophyceae. The maximum Fe value was 504
mg/kg dry wt in Padina australis. Cu was generally low in content with
no seasonal correlations and a maximum value of 12.0 mg/kg in Acanthophora
spicifera. Mn and B showed wide variations in species with minimum
values in April and maximum in August; highest values w~re in agar-
containing Rhodophycoeae. Mo has maximum values in August with a maximum
value of 0.24 mg/kg dry wt in Graci1aria 1ichenoides. Average Zn content
257
-------
varies between 10 and 80 mg/kg dry wt with minimum values in Chloro-
phyceae and maximum values in Rhodophyceae. No seasonal variations
in Zn content were found.
1980.
Porter, K.R. and D.E. Hakanson. 1976.
to embryonic and larval boreal toads
Copeia 2:327-331.
Toxicity of mine drainage
(Bufonidae: Bufo boreas).
Bioassays were conducted with a Colorado mine drainage waste
using zygotes and larvae of toads. Toads tolerated between 0.06% drain-
age (containing 0.16 mg Fe/I, 0.023 mg Zn/l, and 0.002 mg Cull at pH of
5.0) and 1.2% drainage (with 3 mg Fe/I, 0.5 mg Zn/l, 0.044 mg Cull and
pH of 4.0). Incipient lethal levels, in mg/l, for individual components
were: 20 to 30 for Fe, 0.1 to .05 for Zn, and 0.02 to 0.044 for Cu.
Incipient lethal acidity fell within the range pH 3.1 to 4.0.
1981.
Portmann, J.E. 1972. The levels of certain metals in fish from
coastal waters around England and Wales. Aquaculture 1:91-96.
Mean concentrations in mg/kg wet wt of metals found in cod
muscle from inshore habitats were: Cd 0.12, Cu 0.47, Cr <0.50, Hg 0.26,
Pb <0.50, Zn 4.35; from the North Sea these were: Cd 0.18, Cu 0.65,
Cr <0.50, Hg 0.10, Pb <0.50, Zn 5.16; and from distant waters: Cd <0.05,
Cu 1.00, Cr <0.50, Hg 0.09, Pb <0.50, Zn 4.70. Mean concentrations in
plaice from coastal waters were: Cd 0.07, Cu 0.85, Cr <0.50, Hg 0.25,
Pb 0.54, Zn 5.36; from North Sea: Cd 0.12, Cu 0.85, Cr <0.50, Hg 0.08,
Pb <0.50, Zn 5.70; and from distant waters: Cd 0.05, Cu 1.50, Cr <0.50,
Hg 0.05, Pb <0.50, Zn 6.60.
1982.
Portmann, J.E. and J.P. Riley. 1964. Determination of arsenic
in seawater, marine plants and silicate and carbonate sedi-
ments. Anal. Chim. Acta 31:509-519.
Seawater contained 2.0 I 0.02 ~g As/I; Fucus serratus and red
clay contained 1.67 I 0.03 and 6.6 I 0.17 mg As/kg dry wt, respectively.
1983.
Potts, W.T.W. and F.B. Eddy. 1973. Gill potentials and sodium
fluxes in the flounder, Platichthys flesus. Jour. Compo
Physiol. 87:29-48. -------
The potential between blood plasma and external medium of a
euryhaline flounder is largely dependent on external concentration of
sodium and acts as a diffusion potential; permeability to Ca, Mg, and
S04 is very low. Changes of potential account for the apparent "Na
258
-------
exchange diffusion effect" observed in Na fluxes following changes in
external medium and the slight dependence of Na efflux on external sea-
water K concentration. Average plasma concentrations of seawater-adapted
flounder were 4.4 and 0.17 g/l for Na and K, respectively.
1984.
Potts, W.T.W. and D.H. Evans. 1967. Sodium and chloride balance
in the killifish Fundulus heteroclitus. BioI. Bull. 133:411-425
Measurements of influx and efflux rates of Na, plus efflux
rates of Cl and Br ions in this euryhaline teleost were made in seawater,
40% seawater and freshwater. The relationship between active influx, f,
and external concentration, M, is given by:
M
f = fmax [M+CJ
where C is concentration at which f = Y2 f and is a measure of
affinity of carrier molecule to ion; with ~aIower C indicating a lower
concentration in which an animal can survive. In Fundulus, C ~ 2 rnMNa/l.
In freshwater crustacea C can be as low as 0.2 (Astacus) or 0.1 rnM/l
(Potamon), indicating that Fundulus is not as well adapted to freshwater
as these crustaceans.
The most important single change during adaptation to fresh-
water is a reduction of permeability. Normal fish adapted to freshwater,
or placed in freshwater for a short period (i.e., 15 min) maintain low
permeability for many hours after return to seawater. This rapid, but
not instantaneous adaptation and slow reversal suggests that permeability
is controlled by a hormone released in response to freshwater, falling
blood concentration, or both.
1985.
Potts, W.T.W., M.A. Foster and J.W. Stather. 1970. Salt and
water balance in salmon smolts. Jour. Exp. BioI. 52:553-564.
Respective sodium contents of smolting salmon adapted to fresh-
water and seawater were 690 and 1030 mg/kg wet wt. Total Na flux in
freshwater and seawater adapted animals were 368 and 2967 mg/kg fish/day.
Na flux rates, in mg/kg/hr, for smolts adapted to seawater and fresh-
water; respectively, were 36 and 0 for drinking influx, 87 and 16 for
influx through body wall, <0.23 and 0.46 for urine loss and 124 and 15
for extra renal loss. On immediate transfer from seawater to dilute
seawater or to freshwater, influxes decline rapidly; on transfer from
freshwater to seawater, restoration of fluxes occurs slowly.
1986.
Potts, W.T.W. and G. Parry. 1964.
the prawn, Palaemonetes varians.
Sodium and chloride balance in
Jour. Exp. BioI. 41:591-601.
259
-------
For P. varians in an isosmotic medium (~230/00), exchange of
Na+ and Cl- took place by passive diffusion with fluxes, in g/k~ animal/
hr, of 1.7 and 0.7 for Na+ and Cl-, respectively. At 350/00 Na was
removed extrarenally at a rate of 3.5 g/kg animal/hr; Cl- passively
diffused outward at a rate of 1.8 g/kg animal/hr. Increased ion fluxes
may be associated with maintenance of water balance by water-swallowing.
At OJ%o, Cl- was actively absorbed at a rate of 1.0 g/kg
animal/hr; which resulted in inward diffusion of Na+ at a rate of 414
g/kg animal/hr. Some active Na+ uptake also occurred. In seawater
<0.70/00, equilibrium could not be maintained.
1987.
Pouvreau, B. and J.-C. Amiard. 1974. Etude experimentale de
l'accumulation de l'argent 110 m chez divers organismes
marins. Comm. a l'Energie Atomique-France, Rept. CEA-R-457l.
19 pp.
Concentration factors (cf) were determined for Ag-llOm in
coastal marine .organisms, some of which are marine products of commerce;
results were similar to those measured in situ for the stable element.
Tests were conducted at 15 C in static seawater containing initial con-
centrations of 3.33 uCi Ag 110m/I. Cf values for three species of algae
ranged between 1600 and 2800 after 38 days; for bivalve mollusc flesh
these were 500-32,000 (especially high in oyster after 160 days); for
gastropod molluscs, cf values were 1100-3000; for 3 species of whole
decapod crustaceans cf values were 75-4000; and for a teleost 40, after
98 days. Many tissues were not in equilibrium at the end of their
respective exposure periods, including all species of algae, flesh of
bivalve molluscs, whole fish, and fish viscera.
1988.
Powers, E.B. 1920, Influence of temperature and concentration
on the toxicity of salts to fishes. Ecology 1:95-112.
Goldfish were tested at various concentrations of lithium
chloride (0.046 N to 0.488 N) and 5 temperatures between 4 and 34.8 C.
Toxicity increased with both concentration and temperature; survival
time decreased from 1411 min (0.058 N, 4 C) to 7 min (0.372 N, 34.8 C).
Toxicity of ammonium ,chloride to goldfish, bluntnose minnow (Pimephales
notatus) and minnows (Notropis blennius) increased with temperature.
Temperature effect on toxicity of LiC12 and NH3Cl did not follow van't
Hoff's rule at extreme temperatures. QIO also did not meet van't Hoff's
rule except at high temperatures. Relative toxic activities of LiC12
at different temperatures to goldfish follow closely the square root of
relative standard metabolism of vertebrates; therefore, LiC12 may attack
some intermediary substance of metabolism.
260
-------
1989.
Pratt, D.R., J.S. Bradshaw and B. West. 1972. Arsenic and
selenium analyses in fish. Utah Acad. Arts Sciences Proc.
Part 1, 49:23-26.
A procedure for analysis of arsenic and selenium in freshwater
fishes is described. Values obtained for As (in ug/kg wet wt) were:
bass 35-172, carp 55-210, catfish 79-298, sucker 62-253, and trout 69-
149. For selenium these were: bass 375-1265, carp 328-1896, catfish
387-2659, sucker 444-1522, and trout 397-792.
1990.
Preston, A., J.W.R. Dutton and B.R. Harvey. 1968. Detection,
estimation, and radiological significance of silver-110m in
oysters in the Irish Sea and the Blackwater Estuary. Nature
218:689-690.
Oysters Ostrea edu1is from Blackwater Estuary adjacent to a
nuclear power station contained in pCi/g wet wt: 0.79 Fe-55; 0.35
Co-60; 43.1 Zn-65; 0.38 Ag-110m; and 0.17 Cs-137. Irish Sea oysters
had concentrations. in pCi/g wet wt, of: ~5 Ce-144; 15 Ru-106; ~2
Zr-95/Nb-95; 2.3 Ag-110m; 2.4 Zn-65; and 3.5 K-40. Silver-110m is 3.3X
more radiotoxic than Zn-65, but this difference is almost offset by
the greater concentration factor for zinc in oyster flesh. Although
Zn-65 in effluent is almost 50X greater than Ag-I10m (4.44 vs 0.070),
the two nuclides are of almost equal importance per curie released.
1991.
Preston, A., D.F. Jeffries, J.W.R. Dutton, B.R. Harvey and A.K.
Steele. 1972. British isles coastal waters: the concen-
trations of selected heavy metals in sea water, suspended
matter and biological indicators--a pilot survey. Environ.
Pollut. 3:69-82.
Highest concentrations of metals in seawater from the eastern
Irish Sea, in ug/l, were: Zn 7.1, Fe 11.9, Mn 6.1, Cu 1.7, Ni 2.6,
Pb 1.6, Ag 0.08, and Cd 0.46. Metal concentrations were also determined
for bladder wrack Fucus vesicu1osus, 1averweed Porphyra umbi1ica1is, and
limpets (soft parts) Patella vu1gata. The highest concentrations found,
in order respectively, were in mg/kg dry wt: Zn 171, 66, 158; Fe 249,
387, 2450; Mn 99, 29,42; Cu 10.1, 11.5, 14.4; Ni 6.7, 2.2, 7.3; Pb 4.0,
3.1, 7.9; Ag 0.35, 0.13, 2.1; and Cd 1.4, 0.35, 13.1. Little change
was found in metals levels of Fucus during 10 years prior to 1970
samples. Concentration factors are also given, showing a high reconcen-
tration of Fe, Ag and Cd in flesh of Patella. Fucus appears to be a
good indicator species for Zn, Fe, Mn, and Ag. In general, proportions
of metals associated with suspended matter remain fairly constant with
respect to variations of total concentrations in either time or space.
261
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1992.
Prytherch, H.F. 1931. The role of copper in the setting and
metamorphosis of the oyster. Science 73(1894):429-431.
Laboratory studies demonstrated that concentrations of copper
in the range 0.02-0.04 mg/l initiated almost immediately a positive
setting reaction of oyster larvae; no such effect was observed with com-
pounds of tin, iron, zinc, lead, aluminum, manganese, and silver. In
river water copper was present in amounts varying from 0.2-1.25 mg/l
and is apparently the specific element essential for oyster attachment,
metamorphosis, and survival. Highest set of spat in Milford Harbor,
Connecticut, occurred when copper content of the water ranged from 0.15
to 0.50 mg/l; setting ceased when copper content dropped below 0.01 mg/l.
Author states that because copper plays an important role in oyster
respiratory processes, its presence would naturally enhance release of
cells necessary for setting and metamorphosis. Author cautions that at
slightly higher concentrations (presumably >1.25 mg/l) copper quickly
produces cytolysis and death of oyster larvae.
1993.
Prytherch, H.F. 1934. The role of copper in the setting, meta-
morphosis, and distribution of the American oyster, Ostrea
virginica. Ecological Monographs 4(1):47-107.
The stimulus for setting of oyster larvae has been traced to
surface and underground waters flowing into inshore coastal areas, and
specifically to presence of minute amounts of copper in these waters.
The duration of the setting process varied in waters of different
salinities and reached its optimum or shortest interval in salt concen-
trations of 16-18.60/00 when setting is completed in from 12-19 minutes.
Under natural conditions the setting of oyster larvae was most pro-
nounced at the stage of tide when copper content of water was highest,
and within a range of from 0.05 to 0.6 mg of copper per liter. Within
this range the intensity of setting or number of individuals correspond-
ing to copper stimulation was directly proportional to the amount of
copper present. The oyster larva receives the stimulus for setting
through ingestion of copper in the form of a colloidal precipitate and
reacts to its presence after an 'average latent period of 4 minutes and
20 seconds.
Copper is highly toxic to the larva when the concentration is
in excess of that found in natural waters, and gradually produces cytol-
ysis of the tissues and death of the organism. The metamorphosis of the
attached larva and its development are dependent upon the ingestion of
additional amounts of copper. The horizontal and vertical distribution
of oysters in different coastal regions can be correlated with the
copper content, salinity of the water, and the variations in these
factors under different hydrographical and tidal conditions. The loca-
tion of the most prolific areas for setting and seed oyster production
262
-------
is determined largely by the degree of interaction between fresh water
and sea water and particularly by the amount of copper supplied by the
former.
1994.
Pugh, P.R. 1975. Variations in the biochemical composition of
the diatoms Coscinodiscus eccentricus with culture age and
salinity. Marine Biology 33:195-205.
Marine diatoms were grown at 20, 25, 30 and 350/00. Changes
in carbohydrate, protein, silicon and pigment concentrations of cells
throughout the growth cycle were monitored. Carbohydrates and pigments
showed no salinity dependence, whereas protein and silicon concentration
did. At the start, dry wt % silica contents were 30, 32, 30, and 31%
in 20, 25, 30, and 350/00 S, respectively; whereas at the end these
values were 16, 15, 13, and 11%, respectively. Changes in frustular
thickness were also calculated.
1995.
Raeder, M.G. and E. Snekvik. 1949.
fish and other aquatic organisms.
Selskab. 21(25):102-104.
Mercury determinations in
Kongl. Norske Vidensk.
Mercury concentrations in fish fillets were 136 to 166 ~g/kg
in Anarrhichas lupus, and 75 ~g/kg in Salmo alpinus.
1996.
Raeder, M.G. and E. Snekvik.
other aquatic organisms.
21(25):105-109.
1949. Mercury contents of fish and
Kongl. Norske Vidensk. Selskab.
Mercury, in ug Hg/kg, of freshwater organisms was: 142 for
Gasterosteus pungitis, a stickleback; 167 for Anguilla vulgaris, an eel;
94-136 for Salmo trutta, a trout; 100-138 for Salmo alpinus; 288 for
Limnea, a snail; 89 for Perca fluviatilis, a perch; 77 for Lota Iota,
the turbot (fish); and 76 for Coregonus lavaretus, a whitefish. Marine
organisms studied, and their concentrations (in ug Hg/kg) were: Gadus
morrhua, codfish, 44 in liver to 180 in soft roe; Cancer pagurus, crab,
60 in shells and 62 in pulpy parts; and Pandalus borealis, shrimp, 51
in pulpy parts to 114 in shells and head. It was concluded that inter-
species differences were due to variations in food and feeding habitat,
with primary Hg intake via digestive tract rather than gills.
1997.
Ramamoorthy, S. and D.J. Kusher. 1975. Binding of mercuric and
other heavy metal ions by microbial growth media. Microbial
Ecol. 2:162-176.
263
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Addition of 20 mg/l of Hg2+, Pb2+, or Cu2+ to widely used
bacterial growth media resulted in binding of all but 80 ug/l of each
metal. Cd2+ did not bind as completely as Hg2+, Pb2+, or Cu2+. Authors
state that ions either enter bacterial cells as organic complexes, or
bacteria successfully compete with growth media for bound ions.
1998.
Rana, B.C. and H.D. Kumar. 1974. The toxicity of zinc to
Chlorella vulgaris and Plectonema boryanum and its protection
by phosphate. Phykos 13:60-66.
Relatively high concentrations of phosphate, but not nitrate,
improves growth of 2 species of freshwater algae and also protects
against increased zinc toxicity to a certain limit. In low concentra-
tions, nitrate also stimulates growth but fails to protect C. vulgaris
against toxicity caused by high zinc content. Phosphate protection
against zinc signifies a possible ecological role of phosphate in
eutrophic habitats in reducing toxicity of metal ions, thereby encourag-
ing growth of sewage organisms. Authors conclude that phosphate ions
may complex with zinc to produce a non-ionic product of low biological
activity-
1999.
Rana, B.C. and H.D. Kumar. 1974. Effects of toxic waste and
waste water components on algae. Phykos 13:67-83.
Several species of freshwater algae were exposed to effluents
of a zinc smelter. Anacystis nidulans, Oscillatoria sp. and Nodularia
spumigena were most sensitive and failed to grow at any pH tested.
Chlorella vulgaris survived in effluent at pH 5.0 with improved growth
as pH rose to 8.0; Scenedesmus sp. was similar to Chlorella while
Plectonema boryanum grew only in effluent at pH 8.0. Respective 10-day
LC-50 values in mg/l, for Zn2+ and CuS04, were 1.0 and 0.4 for Anacystis
nidulans, 0.5 and 0.5 for Oscillatoria sp., 0.4 and 0.4 for Anthrospira
jenneri, 10.0 and 4.0 for Plectonema boryanum, 0.7 and 0.5 for Nodularia
spumigena, 5.0 and 2.5 for Chlorella vulgaris and 5.0 and 4.0 for
Scenedesmus sp.
2000.
Rancitelli, L.A., W.A. Haller, and J.A. Cooper. 1968. Trace
element variations in silver salmon and king salmon muscle
tissue. Rapport Americain BNWL-7l5 Part 2:42-47.
For silver salmon, average metal contents from white, cheek,
and red muscle tissue, in mg/kg freeze dried tissue, ranged from 920 to
3380 for Na, 9600 to 16,800 for K, 3.6 to 5.6 for Rb, 0.056 to 0.105 for
Cs, 7.6 to 40.0 for Fe, 12 to 50 for Zn, 0.73 to 0.98 for Se, 0.2 to
264
-------
0.6 for Hg, 0.006 to 0.014 for Co, 0.00003 to 0.00009 for Sc, 0.0002 to
0.0004 for Sb, and <0.001 for Ag. Average liver values, in mg/kg freeze
dried wt, were 3000 for Na, 18,000 for K, 7.2 for Rb, 0.047 for Cs, 270
for Fe, 95 for Zn, 3.8 for Se, 0.3 for Hg, 0.17 for Co, 0.0002 for Sc,
0.17 for Ag, and 0.0008 for Sb. A correlation between K, Rb, and Cs
exists, as well as a correlation between Na and Zn. The ratio Rb:K in
muscle tissue is similar to that of seawater, while Cs:K shows a 10-fold
increase over that of seawater. Average metal concentrations, in mg/kg
freeze dried wt, of Alaskan king salmon red muscle were 1600 for Na,
13,000 for K, 3 for Rb, 0.12 for Cs, 15 for Fe, 22 for Zn, 1.6 for Se,
0.8 for Hg, 11 for Co, 0.0002 for Sc, <0.001 for Ag, and 0.0009 for Sb.
2001.
Rancitelli, L.A., C.E. Jenkins and W.A. Haller. 1967.
element content and the specific activity of several
nuclides in silver salmon liver. Rapport Americain,
715, Part 2:47-52.
Trace
radio-
BNWL-
Concentrations of metals in mature salmon livers from Washing-
ton State, in mg/kg freeze-dried tissue, were: 3000 for Na, 18,000 for
K, 6.6 for Rb, 0.047 for Cs, 95 for Zn, 270 for Fe, 0.17 for Co, <0.02
for Cr, 0.17 for Ag, 0.001 for Sb, <0.0002 for Sc, 3.8 for Se, and 0.3
for Hg. Specific radioactivities of K-40 and Cs-137 in salmon liver
are similar to those in seawater, but Co-60 and Zn-65 are higher; these
differences may be due to contact with the Columbia River where high
concentrations of Zn-65 and Co-60 are present.
2002.
Rathsack, R. and K. Lohs. 1969. Zur aufnahme van kupferver-
bindungen durch Chlorella pyrenoidosa. Studia Biophys.
Berlin 13(4):209-215. (In German, English summary)
In range of 0.64 to 640.0 ug Cull, the Cu complex of tri-
ethanolamine was more toxic and taken up more rapidly by ChIarella than
CuS04' Permeation rate of Cu complex to algae appeared higher despite
its greater stability.
2003.
Ratkowsky, D.A., T.G. Dix, and K.C. Wilson. 1975. Mercury in
fish in the Derwent Estuary, Tasmania and its relation to the
position of the fish in the food chain. Australian Jour. Mar.
Freshwater Res. 26:223-231.
Total mercury concentrations are reported for 258 individual~
representing 16 species of finfish from the Derwent Estuary, Tasmania.
Hg concentrations in muscle varied between 0 and 2.0 mg/kg in a school
shark Galeorhinus australis. Ralphs Bay contained a higher percentage
of fish with Hg concentrations in excess of Tasmanian Food Regulation
265
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limit of 0.5 mg/kg than any other area of the Estuary. Approximately
51% of individual piscivorous fish had Hg concentrations >0.5 mg/kg; by
contrast, 24% of invertebrate predators and only 7% of individual herbi-
vores had Hg concentrations >0.5 mg/kg.
2004.
Read, L.J. 1971. Chemical constituents of body
of the holocephalan Hydrolagus collei. Compo
Physiol. 39A:185-l92.
fluids and urine
Biochem.
Levels of Na, K, Mg, Ca and other substances were determined
in serum, cranial fluid and urine of ratfish. Levels of urea and
trimethylamine oxide are lower, and Na and Cl higher in ratfish body
fluids than elasmobranchs. However, similarities in electrolyte distri-
bution with elasmobranchs suggest a similar pattern of 'renal and possibly
extrarenal function.
2005.
Reed, J.R. 1975. Uptake and elimination of radiotungsten in
black bullheads. In Howell, F.G., J.B. Gentry and M.H. Smith
(eds.). Mineral Cycling in Southeastern Ecosystems. U.S.
Energy Res. Dev. Admin.: 435-444. Available as CONF-7405l3
from NTIS, U.S. Dept. Comm. Springfield, VA 22161.
Catfish Ictalurus melas, took up radiotungsten from food and
water with a plateau in whole-body activity after immersion for 4 days
at 14 C. Fish accumulating W-187 from water had a single exponential
component of elimination with a biological half-life of 2.75 days. Fish
dosed in a single feeding lost activity at two rates; one component had
a half-life of 14 hr and the other 6 days. After 8 days, flesh, gills,
bone and gut together contained 78.6% of total activity. Bone had
longest half-life (8.0 days) of examined tissues and contained 69.8%
of whole-body activity after 16 days of elimination.
2006.
Reese, M.J. 1937. The microflora of the non-calcareous streams
Rheidol and ~1elindwr with special reference to water pollution
from lead mines in Cardiganshire. Jour. Ecol. 25:385-407.
Collections of microflora in the Rheidol and Melindwr Rivers
above and below sources of pollution from lead mines, show that micro-
and macroflora abundance was greater in unpolluted (upstream) sections
than polluted downstream areas. This difference in growth was present
at all seasons and with all water level variations. Author suggests
that this may not be due to lead itself, but to presence of silt
derived from mines and deposited on stream bed.
266
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2007.
Regier, L.W., P.M. Jangaard, H.E. Power, B.E. March
1974. Composition and nutritive characteristics
Canadian white fish meals. Jour. Fish. Res. Bd.
201-204.
and J. Biely.
of Atlantic
Canada 31:
Whitefish meals from plants in eastern Canada, were analyzed
for proximate composition, minerals, vitamins, amino acids, available
lysine, and pepsin digestibility. ~he composite samples were similar
in chemical composition with respect to both macro- and micronutrients.
In vitro pepsin digestibility was 95-96% and chemically estimated avail-
able lysine 6.5-6.9 g/16 g N, or 87-96% of the total lysine present.
Mineral analyses yielded average values of (%): 5.4 Ca, 0.18 Mg, 1.0
K, 1.1 Na, and (mg/kg): 123.0 AI, 2.5 Ba, 13.0 B, 9.6 Cr, 6.4 Cu, 85.0
Fe, 9.R Mn, 0.24 Hg, 2.0 Se, >200.0 Sr, and 64.0 Zn.
2008.
Rehwoldt, R. and D. Karimian-Teherani. 1976. Uptake and effect
of cadmium on zebrafish. Bull. Environ. Contamin. Toxicol.
15:442-446.
Uptake of cadmium over a 6 month period by the freshwater
Brachydanio rerio, fed a daily diet containing 10 mg Cd/kg as Cd
(CH3COO)2, was recorded and compared to controls. Cadmium uptake in-
creased rapidly, then slowed with a plateau after approx. 3 months.
Maximum Cd concentration attained in females was 12.7 mg/kg dry wt; for
males this was 5.1 mg/kg dry wt. Coloration and markings of Cd-fed fish
became less defined. After 30 days, the monthly total of eggs declined.
Residue analysis of offspring yielded no detectable amounts of Cd, indi-
cating that Cd is retained by parents and not transferred to the Fl'
2009.
Rehwoldt, R., D. Karimian-Teherani and H. Altmann. 1975.
Measurement and distribution of various heavy metals in the
Danube River and Danube Canal aquatic communities in the
vicinity of Vienna, Austria. Science Total Envir. 3:341-348.
Mud, water, algae and fish collected over a ten-month period
were analyzed by neutron activation for Cr, Co, Sb, Zn, Sc, and Fe.
Metal content of algal samples measured in mg/kg dry wt were: 8 to 12
for Co; 12 to 20 for Cr; 6006 to 7124 for Fe; 6 to 8 for Zn; 2 to 6 for
Sb; and 2 to 9 for Sc. Metal content of whole homogenated carp or white-
fish, in mg/kg dry wt, collected from the river were: Co, 0.31; Cr,
0.50; Fe, 14; Zn, 7.0; and Sc, 0.029. Values for those fish found in
the Canal were: Co, 0.24; Cr, 0.48; Fe, 16; Zn, 7.6; and Sc, 0.030; Sb
was not detectable in all fish samples.
267
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2010.
Rehwoldt, R., D. Karimian-Teherani and H. Altmann. 1976.
Distribution of selected metals in tissue samples of carp,
Cyprinus carpio. Bull. Environ. Contamin. Toxicol. 15:374-
577.
Gill content of Co, Cr; Fe, Zn, La and Sc, in carp ~. carpio,
resemble that of suspended solids. This may be due to filtering func-
tion of gills with resultant high concentrations of metals adhering to
particles imbedded on gill surfaces and not in tissue itself. Metals
tested also appear to concentrate in viscera. Concentrations in liver,
in mg/kg dry wt, were 0.07 for Co, 0.21 for Cr, 19.3 for Fe, 7.0 for
Zn, 0.44 for La, and 0.20 for Sc. In kidney, metal content was 0.03
for Co, 0.08 for Cr, 2.4 for Fe, 8.4 for Zn, 0.03 for La, 0.05 for Sc.
In contrast to the other metals. La and Sc tended to concentrate in
bone, at 1.1 and 0.6 mg/kg dry wt, respectively. Co also accumulated
in bone tissue at 0.06 mg/kg dry wt.
2011.
Reichle, D.E., P.B. Dunaway and D.J. Nelson. 1970. Turnover
and concentration of radionuclides in food chains. Nuclear
Safety 11:43-55.
Accumulation and retention of radionuclides (Ca, Sr, K, Cs,
Na, Co, Zn, Mn, Ru, Fe, Ra, Zn, Sc, As, Cu, Cr, and Ce) by terrestrial
and aquatic organisms, including algae, hizher plants, crustaceans,
insects, molluscs, amphibians, fish and reptiles are reviewed. Data
are presented for use in environmental models and correlation with
species characteristics, such as body size, that allow estimation of
absolute values for many different animal groups based on existing
knowledge.
2012.
Reinert, R.E., L.J. Stone and W.A. Willford. 1974. Effect of
temperature on accumulation of methylmercuric chloride and
p,p'DDT by rainbow trout (Salmo gairdneri). Jour. Fish. Res.
Bd. Canada 31:1649-1652.
Yearling trout exposed to methylmercuric chloride at concen-
trations of 0.234-0.263 ug/l for 12 weeks at 5, 10, and 15 C accumulated
1.19, 1.71, and 1.96 mg/kg, respectively. Trout exposed to p,p'DDT at
concentrations of 0.133-0.776 ug/l accumulated 3.76 (5 C), 5.93 (10 C),
and 6.82 mg/kg (15 C). Concentrations of mercury accumulated were
significantly different (P <0.01) at each of the three temperatures;
concentrations of DDT were significantly different at 5 vs 10 C and
5 vs 15 C.
268
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2013.
Reinhart, K. and T.O. Myers. 1975. Eye and tentacle abnormal-
ities in embryos of the Atlantic oyster drill, Urosalpinx
cinera. Chesapeake Sci. 16(4):286-288.
Multiple development of eyes and cephalic tentacles
in 2.7% of ~. cinera embryos exposed to 0.01 mg Hg/l as HgC12
24 days. Abnormalities occurred in 0.4% of control animals.
animals had 1 to 3 tentacles and 1 to 6 eyes.
occurred
for 3 to
Abnormal
2014.
Reish, O.J., J.M. Martin, F.M. Piltz and J.Q. Word. 1976.
effect of heavy metals on laboratory populations of two
chaetes with comparisons to the water quality conditions
standards in southern California marine waters. Water
Research 10:299-302.
The
poly-
and
Toxicities of salts of Cd, Cr+6, Cu, Pb, Hg, and Zn were deter.
mined for two species of polychaete annelids in seawater. Respective
LC-50's (96 h) and LC-50's (28 d), in mg/l, for Neanthes arenaceodentata
adults (juveniles) were: 12.0 (12.5) and 3.0 (3.0) for Cd; >1.0 (>1.0)
and 0.55 (0.7) for Cr+6; 0.3 (0.3) and 0.25 (0.14) for Cu; >10.0 (>7.5)
and 3.2 (2.5) for Pb; 0.022 (0.1) and 0.017 (0.09) for Hg; and 1.8 (0.9)
and 1.4 (0.9) for Zn. Respective LC-50's (96 h) and LC-50's (28 d), in
mg/l, for Capitella capitata adults (trocophores) were: 7.5 (0.22) and
0.7 for Cd; 5.0 (8.0) and 0.28 for Cr+6; 0.2 (0.18) and 0.2 for Cu; 6.8
(1.2) and 1.0 for Pb; <0.1 (0.014) and 0.1 for Hg; and 3.5 (1.7) and
1.25 for Zn. Results were compared to water quality standards for dis-
charges in the State of California. Amounts of Cu and Zn present in
two Los Angeles County sewage outfalls exceeded the LC-50 (28 d) values
of both species of polychaetes.
2015.
Renfro, J.L., B. Schmidt-Neilson, O. Miller, O. Benos and J.
Allen. 1974. Methyl mercury and inorganic mercury: uptake,
distribution, and effect on osmoregulatory mechanisms in
fishes. In Vernberg, F.J. and W.B. Vernberg (eds.). Pollu-
tion and Physiology of Marine Organisms, Academic Press, N.Y.:
101-122.
Sodium-depleted killifish Fundulus heteroclitus, could not
take up Na in mercury-free water after exposure to 0.125 mg HgC12/1 for
24 hrs. Fish exposed to 0.125 mg methyl-Hg/Cl for 24 hrs began to take
up Na after 30 min, eventually reaching levels obtained in control
groups. Neither Hg treatment increased gross Na efflux. Uptake of
Hg-203C12 occurs rapidly in killifish gills, with gradual increase in
liver and kidney, reaching 90% and 70% of gill concentration, respec-
tively, after 72 hr. Gills also take up CH3Hg-203Cl rapidly, but liver
concentration reaches 189% that of gills in 48 hrs, and kidney
269
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concentration reaches 293% of gill content in 72 hrs. C-Hg bond appears
to break soon after methyl-HgCl uptake.
Urinary bladders from winter flounder Pseudopleuronectes
americanus, showed decreased net Na transport without recovery when ex-
posed to 108 mg HgC12/l, but an immediate reduction of Na reabsorption
followed by recovered ability after 30-60 min when exposed to 100 mg
CH3HgCl/1. Na-K-ATPase activity was totally inhibited by 10.8 mg
HgC12/1 and 80% inhibited by 12.5 mg methyl-HgCl/l.
Eels Anguilla rostrata, exhibited mean values of 0.618 and
1.28 mg Hg/kg muscle when kept for 1 month in salt and freshwater;
respectively; intracellular K decreased with Hg accumulation in muscle.
2016.
Renfro, W.C., S.W. Fowler, M. Heyraud and J. LaRosa. 1975.
Relative importance of food and water in long-term zinc-65
accumulation by marine biota. Jour. Fish. Res. Bd. Canada
32:1339-1345.
Shrimp, crabs, and fish were maintained for 3 months in a
Zn-65-labelled simulated ecosystem in which individuals were allowed to
accumulate radiotracer either directly from water or from a combined
food and water pathway. Shrimp and crabs receiving Zn-65 from the food-
water milieu did not attain significantly higher Zn-65 body burdens
than those that accumulated the isotope from water only. For fish,
food pathway accounted for only 2.5 times more Zn-65 than that accumu-
lated directly from water. Specific activity measurements of both
organisms and water as well as comparisons of radioactive concentration
factors with those based on stable element measurements indicated that
Zn-65 in organisms had not reached equilibrium with isotope in water,
even though net Zn-65 accumulation in shrimp and crabs had ceased by
the end of the experiment. It was concluded that there are zinc pools
within adult organisms that exchange only slowly, if at all, with zinc
atoms available in the organisms' food or surrounding water. Hence,
aquatic organisms such as those used in this study can most likely
achieve true isotopic equilibrium only after living significant por-
tions of their actively growing life stages in a radioactive environ-
ment.
2017.
Renzoni, A. and E. Bacci. 1976. Bodily distribution, accumula-
tion and excretion of mercury in a freshwater mussel. Bull.
Environ. Contamin. Toxicol. 15:366-373.
Total mercury values of Unio elongatulus from the Paglia
River in central Italy, an area of mercury mining and processing, never
exceeded 0.2 mg/kg with a mean of 0.12 mg/kg. In whole soft parts of
small individuals, Hg concentration ranges from 0.192 to 0.385 mg/kg
270
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(mean 0.280 mg/kg). Mercury distribution was analyzed in large mussels:
digestive gland showed highest level of 1.403 mg/kg; gills and gonads
were next with 1.259 and 1.232 mg/kg, respectively. Mantle, foot and
adductor muscle had lower mean Hg concentrations of 0.866, 0.855 and
0.818 mg/kg, respectively. Mercury biological half-life ranged from
15 to 35 days in digestive gland, gills and gonads to about 60 days
for foot abductor muscle and mantle.
2018.
Rice, T.R. 1956. The accumulation and exchange of strontium by
marine planktonic algae. Limnol. Oceanogr. 1:123-138.
Of 12 species of planktonic algae grown in medium containing
Sr-89 and Sr-90, only Carteria and Thoracomonas accumulated Sr-90. '
Other species took up Y-90, the radioactive daughter of.Sr-90. Removal
of Y-90 from medium by Carteria was due to surface adsorption, whereas
Sr-90 was taken into cells. Sr uptake was correlated with division rate
and medium concentration of Sr, but was not influenced by high Cu levels.
Carteria could not divide in absence of Ca; Sr could not be substituted
for Ca in Carteria metabolism. Nitzschia closterium concentrated Sr
l7X over seawater. Concentration factor for Sr in Carteria, though
greater than that for Nitzschia, was variable, and influenced by rate
of cell division, age of culture, and initial pH of medium. Radio-
active Sr was not lost from Carteria unless medium contained a chelat-
ing compound. Some 10ss of radioactive Sr occurred when cells were
filter washed with several different types of solutions.
2019.
Rice, T.R. 1965. The role of plants and animals in the cycling
of radionuclides in the marine environment. Health Physics
11:953-964.
The capacity of organisms (algae, fish, crustaceans, molluscs)
to concentrate and cycle in the marine environment radionuclides, such
as Cs, Sr, Sb, Te, Mo, Ru, Ce, Zr, Y, Nb, P, Zn, Mn, K, and Pr is
reviewed. The level to which an isotope is concentrated by an organism
varies with species, season, geographical location and other factors
imperfectly understood. Biota plays an important role in radionuclide
cycling through metabolism when living, and through decomposition after
death. The availability of radionuclides to marine organisms is depend-
ent on its physical state, dissolved or particulate. These materials
can: remain in solution or suspension; precipitate and settle on the
bottom; or be accumulated by plants and animals. Each radionuclide takes
a characteristic route and has its own rate of movement from component
to component, water sediment or biota, before attaining equilibrium.
For an organism to be of significance in marine cycling of radionuclides,
it must accumulate and retain it, and constitute a portion of a food
chain. Organism obtains radionuclides by absorption, adsorption and
271
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ingestion and loses them via excretion and decomposition. Sediments
accumulate radionuclides through physical processes of exchange and
adsorption, with water acting as transport medium between biota and
sediments.
2020.
Rice, T.R., J.P. Baptist, F.A. Cross and T.W. Duke. 1972.
Potential hazards from radioactive pollution of the estuary.
In Ruivo, M. (ed.). Marine Pollution and Sea Life. Fishing
Trading News (Books) Ltd., London: 272-276.
This report summarizes results of many studies on effects of
radioactive wastes upon marine estuary systems. One study followed
movement of Zn-65 added to a closed, and to an open system. After 100
days, >95% of Zn-65 and stable Zn was in sediment of each pond. Analysis
of specific activity in components of ecosystem indicated that exchange
of Zn between sediment and water dominated cycling and controlled dis-
tribution of Zn-65.
Uptake of Co-60, -57, -58, Zn-65, Sr-85, Cs-137 and Ce-144
was determined in the copepod Tigriopus ca1ifornicus: concentration
factors varied from <2 for Sr-85 to >500 for Ce-144 after 48 hrs. In
another experiment, food was a more important source of Zn-65 than
water for brine shrimp Artemia salina. Carnivorous fish excreted par-
ticulate radionuclides: 99% of Ce-144 pipetted directly into stomachs
of croakers Micropogon undu1atus, was excreted in 24 hrs. An experi-
ment was conducted to measure uptake of Zn-65 from seawater by phyto-
plankton (Chlamydomonas), zooplankton (Artemia salina), postlarval
croakers (Micropogon undulatus) and killifish (Fundulus heteroc1itus).
Zinc-65 was readily transferred through the food chain to the fourth
trophic level. Postlarval fish took up Zn-65 rapidly during the first
few days, but uptake rate soon decreased and Zn-65 content remained
more or less constant. Radioactivity in killifish continued to increase
throughout. With daily feeding, 3.8% of Zn-65 concentration in phyto-
plankton reached fourth trophic level; with alternate day feeding, this
was 1.1%. The fourth trophic level Zn-65 concentrations were 1.4 and
9.7%, respectively, of third trophic level concentrations.
In a final study, effects of low-level chronic irradiation on
division rate of phytoplankton was studied. Nitzschia closterium cells
were grown at an initial culture of 2 million cells and 14.3 uCi of
CS-137/l of medium. After 26 weeks the Cs-137 was increased to 143.0
uCi/l; during a 56 week period, cells grown in Cs-137 medium divided'
426X, and controls 427X.
2021.
Roberts, D. and C. Maguire.
sediment and meiofauna.
1976. Interactions of lead with
Marine Poll. Bull. 7:211-213.
272
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Concentrations of lead up to 10 ug/l are readily sorbed onto
sediments by physical rather than biotic processes. Harpacticoid cope-
pods and Turbellaria appear to be the most sensitive faunal groups in
surface sand meiofauna when subjected to lead contamination; other taxa
including flatworms, nematodes and ostracOdS showed no effects at con-
centrations up to 1000 ug/l Pb. In sub-surface sand (7-15 cm depth),
nematodes were the most sensitive group.
2022.
Roberts, T.M., P.B. Heppleston and R.D. Roberts. 1976.
bution of heavy metals in tissues of the common seal.
Poll. Bull. 7:194-196.
Distri-
Marine
Lead, cadmium and mercury content of soft tissues and bone
were determined for the common seal Phoca vitulina,taken from coasts of
East Anglia and West of Scotland. Lead levels were low in all tissues,
with greatest mean accumulations of 4.0 and 3.5 mg/kg wet wt in claw and
rib, respectively. Cadmium levels were also low but tended to accumu-
late with age in liver and kidney of West Scotland seals reaching levels
of 1.1 and 1.9 mg/kg wet wt, respectively. Movement of lead and cadmium
across the placenta was not significant. Total Hg levels up to 110
mg/kg wet wt were found in liver tissue of seals from both areas but
much lower concentrations occurred in all other tissues analyzed. Com-
parison with results of other workers suggests that rate of Hg accumula-
tion in liver of seals increases in the order: Canadian Arctic and
Atlantic coast < West Scotland < East Anglia < Netherlands coast.
Accumulation of mercury in kidney and spleen of older seals lends sup-
port to hypothesis that protective demethylation and retention process
in liver may begin to leak mercury to other tissues at the high concen-
trations which have been recorded in the liver of older seals, and at
high dose rates which have been used in toxicological experiments.
2023. Robertson, D.E. 1967. Trace elements in marine organisms.
Rapport Americain BNWL 481-2:56-59.
Using neutron activation analysis, the following metal concen-
trations, in mg/kg ash, were obtained:
Ag Sb Co Sc Zn
-
Squid 8.1 0.46 0.93 0.010 710
Lantern fish 4.4 0.83 0.22 0.009 210
Rat-tail fish <1 2.5 0.56 0.16 270
Saury <1 1.6 0.38 0.006 410
Euphausiid <1 1.9 0.63 0.016 430
Sabel eel <1 <0.2 0.14 0.045 180
Seawater 4xlO-5 3xlO-3 5xlO-4 lxlO-6 lxlO-2
273
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Enrichment factors as high as 1 to 2 x 104 for Ag were ob-
served in squid and lantern fish, while rat-tail fish concentrated
scandium by a factor of 1.6 x 104. Co and Zn were concentrated to a
somewhat lesser extent, while Sb was not significantly accumulated.
2024.
Robertson, D.E., L.A. Rancitelli, J.C. Langford and R.W. Perkins.
1972. Battelle-Northwest contribution to the IDOE base-line
study. Battelle Pacific Northwest Laboratories, Richland,
Washington, 99352. 46 pp.
Baseline concentrations of Ag, As, Ca, Cd, Co, Cr, Cs, Cu,
Eu, Fe, Hf, Hg, K, Na, Pb, Rb, Sb, Sc, Se, Sr, Ta, Tb, Th, and Zn were
measured in sediments and marine organisms, including penguins, seals,
crustaceans, fishes, molluscs, algae and echinoderms. High arsenic
levels were found in long-fin cod and rattail muscle tissues (540 and
190 mg/kg dry wt, respectively), taken off the Oregon Coast. Arsenic
levels in all organisms were significantly higher than values reported
previously. Mercury concentrations in Pacific coastal organisms were
below the tolerance level in edible seafood of 0.5 mg/kg wet wt tissue,
except in muscle, liver and kidney tissues of the same rattail fish
containing high As levels. Mercury concentrations in salmon were all
relatively low (0.1 to 0.4 mg/kg dry wt)- Lead concentrations in Pacific
coastal organisms never exceeded the detection limit of 2 to 3 mg/kg
dry wt tissue. Cadmium levels in muscle tissue of various organisms
never exceeded 1 mg/kg (dry wt), but a very high concentration of 38
mg/kg Cd (dry wt) was found in rattail kidney tissue. Several whole
organisms contained Cd levels ranging between 1 to 5 mg/kg (dry wt),
which indicates that Cd is concentrated in internal organs of some marine
animals. Copper concentrations show variation within species, while Zn
concentrations are constant, suggesting definite physiological require-
ments. Significant variations in concentration of other elements, in-
cluding Se and Co were also evident.
Concentrations of Hg, Cd, Se, Sb, and Fe were observed in
liver tissue of seal and penguin specimens obtained from the Antarctic.
Mercury concentrations as high as 70 to 120 mg/kg ~ry wt) were observed
in seal liver tissue, and a Cd concentration of about 90 mg/kg was found
in liver of an Adelie penguin. High levels of these trace metals are
possibly accumulated by natural processes, since man's additions of
trace metal pollution in this region is almost non-existent.
2025.
Robertson, J.D. 1949. Ionic regulation in some marine inverte-
brates. Jour. Exp. BioI. 26:182-200.
Body fluids of representatives from five invertebrate phyla
were analyzed for ionic composition before and after dialysis in col-
lodion sacs against samples of ambient seawater. Mesogloeal tissue
274
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fluid of coelenterate Aurelia aurelia showed the following composition,
expressed as % of concentration in dialysed fluid: 99 for Na, 106 for
K, 96 for Ca, 97 for Mg, 104 for Cl, and 47 for S04. Regulation seems
to be brought about by elimination of S04 and accumulation of K by
epithelia bounding the mesogloea, with resultant alteration of remain-
ing ions in conformity with osmotic equilibrium between Aurelia and
seawater. In echinoderms only K was regulated, values in perivisceral
fluid did not exceed 111%, with higher values in ambulacral fluid. Poly-
chaetes regulated K (up to 126%) and sometimes reduced 804 (92%). Regu-
lation extended to all ions in decapod crustacea. In 6 species the
range was 104 to 113% for Na, 77 to 128% for K, 108 to 131% for Ca, 14
to 97% for Mg, 98 to 104% for Cl and 23 to 99% for S04. In the series
Lithodes, Cancer, Carcinus, Palinurus, Nephrops and Homarus, Mg fell
from 97 to 14%, roughly in accordance with increase of activity. Anten-
nary glands eliminated Mg,804, and sometimes Ca from blood, but con-
served other ions. '
Lamellibranchs and gastropods accumulated K and Ca, and
eliminated 804 to a small degree. Range of values in 6 species was 97
to 101% for Na, 107 to 155% for K, 103 to 112% for Ca, 97 to 103% for
Mg, 99 to 101% for Cl, and 87 to 102% for S04. Considerable ionic regu-
lation existed in cephalopods, ranges were 95 to 98% for Na, 152 to 219%
for K, 94 to 107% for Ca, 102 to 103% for Mg, 101 to 104% for Cl, and
29 to 81% for 804. In Eledone cirrosa and Sepia officinalis, differen-
tial excretion by renal organs was important. 804 and Na were eliminated
in quantities greater than in plasma ultrafiltrate, tending to lower
these values, whereas other ions were excreted in proportions below
those of an ultrafiltrate, tending to elevate their blood concentrations.
Ratio of equivalents Na + K/Ca + Mg in body fluids remained at seawater
figure of 3.8 in Aurelia, echinoderms, annelid worms, and lamellibranchs,
but decreased in gastropods and cephalopods to 3.5. In decapod crustacea,
owing principally to reduction of Mg, it increased from 3.8 in Lithodes
to 9 and 12 in Palinura and Astacura spp.
2026.
Robinson, K.M. and M.R. Wells. 1975. Retention of a single oral
dose of cadmium in tissues of the softshell turtle, Trionyx
spinifer. Bull. Environ. Contamin. Toxicol. 14(6):750-752.
Turtles fed orally with 2 mg Cd (as cadmium acetate) retained
9.43% of total Cd fed after 48 hrs and 4.02% after 96 hrs. Liver re-
tained the most Cd in both instances. Concentrations, in mg Cd/kg wet
wt after 48 hrs ranged from 3.45 in kidney to 20.7 in small intestine;
after 96 hrs values ranged from 1.23 in stomach to 5.91 in liver. Fe-
male turtles taken from a river with high metal pollution contained Cd
levels ranging from 0.19 mg/kg in small intestine to 9.87 mg/kg in
kidneys. Results indicate that Cd found in effluent from treatment
plants serving plating industries has little effect on health of turtles.
275
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Rocca, E. 1969. Copper distribution in Octopus vulgaris Lam.
hepatopancreas. Compo Biochem. Physiol. 28:67-82.
Octopus hepatopancreas contained 4880 I 2549 mg copper/kg dry
wt. all Cu was in the cuprous state. Ninety-six percent of Cu was bound
, 0
to substances with a molecular wt (M.W.) >1500 and 50-60~ to substances
with a M.W. between 5000 and 30,000; only 10% was bound to substances
with a M.W. of 70,000.
2027.
2028.
Roeder, M. and R.H. Roeder. 1966. Effect of iron on the growth
rate of fishes. Jour. Nutrition 90:86-90.
Addition of up to 7.4 mg FeS04/l enhanced growth of green
swordtail Xiphophorus helleri; with platyfish ~. maculatus,growth was
unaffected at FeS04 levels < 3.7 mg/l although addition of 7.4 mg
FeS04/1 enhanced growth. FeS04 additions reduced mortality from hatch-
ing to maturity phases. Hematocrits from both species, plus a hybrid,
helleri x macu1atus, were significantly higher upon treatment with 3.7
or 7.4 mg FeS04/1. Addition of 7.4 mg ferric nitrate/l had no effect.
Effectiveness of Fe addition diminished as sexual maturity approached.
2029.
Roesijadi, G., S.R. Petrocelli, J.W. Anderson, B.J. Presley and
R. Sims. 1974. Survival and chloride ion regulation of the
porcelain crab Petrolisthes armatus exposed to mercury.
Marine Biology 27:213-217.
Acute toxicity of mercury, as HgC12' was determined at 7. 14,
21, 28 and 35%0 S. LC-50 (96 hr) values for P. armatus were 50 to
64 wg Hg/1 depending on test salinities. Lower-salinities decreased
time to death of mercury-exposed crabs due to a greater inflow of water
and therefore pollutant. Differences in survival after 96 hr due to
salinity were not statistically significant. Blood chloride concentra-
tions were hyper at low salinities and hypochloride at high salinities
by acclimated crabs. The salinity isochloride to blood was 220/00 S.
Transfer of crabs from 15%0 S to salinities ranging from 7 to 350/00 S
resulted in new steady-state chloride levels within 12 hr. Exposure to
50 wg Hg/l did not alter chloride ion regulation of either acclimated
crabs or crabs adjusting to new salinities.
2030.
Rose, W.C. and M. Bodansky. 1920. Biochemical studies on
marine organisms. I. The occurrence of copper. Jour. BioI.
Chern. 44:99-112.
Whole body Cu in mg/kg wet wt was 1.5 for jelly fish (Aurelia);
2.5 for Portuguese man-of-war (Physalia); 0.0 for clams; 5.8 for crabs;
276
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3.5 for torpedo ray; and 5.2 for sting ray. Analysis of 20 teleosts
from 12 species yielded an average of 2.5 mg Cu/kg wet wt. Oysters
contained Cu concentrations in mg/kg wet wt, of 35 in mantle, 34 in
digestive gland, 18 in adductor muscle, and 40 in remainder (including
gills), giving a total value of 34; 12.2% of Cu in oysters was in a
diffusible form. In shrimp, Cu concentrations in mg/kg wet wt, were
7.3 and 2.4 for exoskeleton (including heads and tails), and meats,
respectively.
2031.
Rosenthal, H. and M. Fonds. 1973. Biological observations
during rearing experiments with the garfish Belone belone.
Marine Biology 21:203-218.
Embryology and early life history aspects are described, and
also survival, ability to withstand thermal stresses, and swimmir!g
stamina. Observations on approximate high or low lethal levels of
salinity after gradual adaptation indicate that young fish between 2
and 3.5 cm die when salinity falls below 2 to 30/00 or increases beyond
550/00.
2032.
Rosenthal, H. and K.R. Sperling. 1974. Effects of cadmium on
development and survival of herring eggs. In Blaxter, J.H.S.
(ed.). The Early Life History of Fish. Springer-Verlag:
383-396.
Herring eggs were incubated at 0.01, 1.0, 5.0 and 10.0 mg/l
of cadmium, and in different test solutions containing mixtures of
cadmium-EDTA, cadmium-zinc, and cadmium-ascorbic acid. Incubation time
was reduced up to 103 hrs with increasing Cd concentration. Percentage
of viable hatch was 16.3%, 82.7%, and 93.0% in 1.0, 0.1 mg/l Cd and
controls, respectively. At concentrations of 5 and 10 mg/l Cd, only a
few larvae hatched and those were small with long yolk sacs. Increas-
ing Cd levels caused decreases in diameter of eyes and otic capsules;
10 mg/l Cd produced some larvae with no otic capsules. This effect was
diminished in the presence of Zn and EDTA, resulting in larger larvae
with larger otic capsules and higher percentage viable hatch. Uptake
of Cd by herring eggs was rapid, reaching a stable level some hours
after the beginning of exposure. At 5.0 mg/l, Cd concentration in
whole eggs reached 18 mg/kg. Immediately before hatching, Cd levels
dropped considerably, with hatched larvae containing virtually no cad-
mium. Eggs incubated in Cd-EDTA mixtures took up negligible amounts of
Cd until the chelating capacity of EDTA was fully utilized. In the
Cd-Zn (20 ~g/l Zn2+) study there was rapid uptake initially with quick
loss during incubation. Primary site of cadmium uptake was at egg
capsule surface, reaching 85 mg/kg in chorion when incubated in 5 mg/l
Cd solutions. This produces a change in the physico-chemical
277
-------
properties of chorion, resulting in shortened incu~at~on time, lower.
percentag,e viable hatch, and sma~ler larva~.. The 10nl~ form of cadmlUID
in seawater is important for actl0n of tOX1Clty mechanlsms.
Ross, I.S. and K.M. Old. 1973. Mercuric chloride resistance of
Pyrenophora avenae. Trans. Brit. Mycol. Soc. 60:293-300.
Isolates of the fungi P. avenae from naturally infested seed
which had not been exposed to mercury compounds were found to be either
resistant or sensitive to HgC12' Isolates surviving on not more than
50 mg HgC12/kg were considered sensitive and those surviving on ~75
mg/kg were regarded as resistant. Ultrathin sections of mycelium
treated with 100 mg HgC12/kg prior to fixation with potassium perman-
ganate did not show electron-transparent areas; the nuclear envelope
had a more rounded appearance than those not treated with HgC12 suggest-
ing that nucleus is a binding site of HgC12' Nuclei of resistant iso-
lates treated with 50 mg HgC12/kg were similar to untreated mycelium,
but nuclei of sensitive isolates similarly treated with Hg more nearly
resembled those of mycelium treated with 100 mg HgC12/kg. Authors con-
cluded that Hg was toxic to nuclei of sensitive isolates but not resis-
tant isolates. No correlation was evident between the production of
red pigment (a mixture of 1,4,5,8-tetrahydroxyanthraquinones and capable
of chelating Hg), and resistance to HgC12'
2033.
2034.
Ross, I.S. and K.M. Old. 1973. Thiol compounds and resistance
of Pyrenophora avenae to mercury. Trans. Brit. Mycol. Soc.
60:301-310.
Approximately equal quantities of non-protein thiol compounds
were detected in both sensitive and resistant strains of P. avenae to
mercury. Since this could be due to problems in extracting and deter-
mining thiol content, thiol reagents were used to inactivate intra-
cellular thiols. Resistance of mycelium and conidia to Hg was reduced
by treatment with iodoacetic acid. Oxidation of thiols within conidia
by diamide also greatly reduced resistance. It was suggested that a
pool of thiol compounds within the cells is responsible for Hg
resistance.
2035.
Rothstein, A. 1959. Cell membrane as site of action of heavy
metals. Federation Proc. Fed. Amer. Soc. Exp. BioI. 18:1026-
1038.
Topics discussed included role of cell membranes in primary
reactions with environmental metals; role of physiologically inert cyto-
plasmic substances that bind with and affect toxicity of metals;
278
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symptoms of membrane vs cytoplasmic toxicity; and the chain of events
between chemical interaction and physiological result. Examples are
presented of action of Hg, U, Mn, K, Mo, Na, and Ca, on cell membranes
of mammals, bacteria and yeasts.
2036.
Rucker, J.B. and J.W. Valentine. 1961. Salinity response of
trace element concentration in Crassostrea virginica.
Nature 190:1099-1100.
Shells of oysters collected between Massachusetts and Texas
were analyzed for trace metal content to determine correlations between
elemental concentrations and ambient thermosaline regimes. Salinities
ranged from 13.3 to 30.40/00 and metal content ranged from 1964 to 2744
mg/kg for Mg, 1142 to 1648 mg/kg for Sr, 21 to 227 for Mn, and 2064 to
3264 for Na. No significant correlation with temperature was demon-
strable and neither Sr, Mg, B nor Cu were related to either temperature
or salinity. Significant correlations between elemental concentrations
and salinity were demonstrated for Mn and for Na. If individual Sr and
Mg concentrations are combined and correlated with salinity the coeffi-
cient is significant; significant correlation of Mg, Mg plus Sr, Mn and
Na with salinity was demonstrated.
2037.
Ruesink, R.G. and L.L. Smith, Jr. 1975. The relationship of the
96-hour LCso to the lethal threshold concentration of hexa-
valent chromium, phenol, and sodium pentachlorophenate for
fathead minnows (Pimephales promelas Rafinesque). Trans. Amer.
Fish. Soc. 104(3):567-570.
Short-term bioassays were conducted using adult minnows vs
Cr+6, phenol, and sodium pentachlorophenate at 15 C and 25 C. LC-SQ
(96 hr) values for Cr were 52 mg/l at 15 C and 37 mg/l at 25 C; a
similar pattern was observed at 48 hrs. The lethal threshold concentra-
tion was not a constant multiple of the LC-50 (96 hr) value for any
toxicants examined.
2038.
Rummel, W., H.-J. Bielig, W. Forth, K. Pfleger, W. Rudiger and
E. Seifen. 1967. Absorption and accumulation of vanadium by
tunicates. Protides BioI. Fluids Proc. Colloq. Bruges 14:
205-210.
Accumulation of vanadjum in blood cells (1.2 to 1.8 ~g V/mg
dry wt) of Ciona intestinalis is preceded by a specific absorption
process. The site of absorption is the one-layer epithelium of the
branchial net. The absorption of V is a biochemical process which is
highly temperature-dependent (increasing with rising temperature) and
279
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which is inhibited by ouabain, an inhibitor of the membrane ATPase sys-
tem. Phosphate and arsenate were shown to inhibit V absorption, whereas
chromate, niobate, molybdate and iron were incapable. V can be bound
by blood plasma of C. intestinalis
2039.
Ruohtula M. and J.K. Miettinen. 1975. Retention and excretion
of 203Hg-labelled methylmercury in rainbow trout. Oikos 26:
385-390.
Elimination of Me-Hg-203 by whole trout Salmo gairdneri,
followed a bi-exponential equation. Biological half-time of Me-Hg at
16-19 C varied from 202 to 516 days depending on retained dose and water
temperature. At 16-19 C, it was 204 d with a retained dose of 3 ug Hg/kg
and 348 d with a retained dose of 0.06 mg Hg/kg. At 0.5-4 C retained
doses of 0.05-0.10 took 516 d for half-time excretion. Ionic Me-Hg
absorbed via gills was excreted faster (TB 1/2 = 268 d) than ionic Me-Hg
administered per os (TB 1/2 = 320 d) or injected intramuscularly (TB
1/2 = 319 d) and this is attributed to an increase in protein-bound
mercury.
2040.
Russel, G. and O.P. Morris. 1970. Copper tolerance in the
marine fouling alga Ectocarpus siliculosus. Nature 228:288-
289.
Differential responses to dissolved copper by a brown alga
E. siliculosus, may be associated with habitats from which populations
were taken. Five-week bioassays utilizing different concentrations of
Cu as CuC12, showed that E. siliculosus from an uncontaminated rocky
shore had a critical toxicant concentration (concentration at which
there is no increase or decrease in plant volume) of 0.05 mg Cull. Two
populations from hulls of different ocean-going freighters treated with
copper-based antifouling bottom preparations had critical toxicant con-
centrations of 0.5 mg Cull each.
2041.
Russell, G. and O.P. Morris. 1972. Ship-fouling as an evolu-
tionary proc~ss. Proc. 3rd Int. Congress on Marine Corrosion
and Fouling, Wash. D.C., Oct. 2-9:719-730.
Populations of Ectocarpus siliculosus, a brown alga, collected
from ship hulls and Cu-contaminated regions, were more Cu resistant than
populations from uncontaminated rocky shores. Cu tolerance arose by
spontaneous mutation from an otherwise Cu-sensitive strain, thereby
producing plants of high potential fouling ability. Cu tolerance
heritability was established by culture of successive generations.
280
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2042.
Russell, P. 1955. Inactivation of phenyl mercuric acetate in
groundwood pulp by a mercury-resistant strain of Penicillium
roqueforti Thorn. Nature 176(4493):1123-1124.
A mercury resistant strain of ~. roqueforti absorbed phenyl
mercuric acetate from nutrient media and reduced the concentration of
biologically active Hg to nil, allowing invasion by other non-tolerant
bacterial species.
2043.
Ruthven, J.A. and J. Cairns, Jr. 1973. Response of fresh-.water
protozoan artificial communities to metals. Jour. Protozoal.
20:127-135.
An artificial freshwater protozoan community was subjected to
different concentrations of Zn and Cu in a test system through which
pond water flowed continuously. Although percent survival of colonizing
species exposed to Cu or Zn fluctuated greatly at each concentration,
the range of toxicity for each compound allowed comparison of protozoa
with other organisms with respect to resistance to heavy metal toxicity.
Individual protozoan species also were exposed for 3 hr to Zn, Cu, Cr,
phenol, Pb, Mn, Co, HN03, acetic acid, AI, Sn, and HCl to derive time
to death curves. Protozoa tested appeared to be more resistant than
Daphnia to phenol, K2Cr207, and Cu; however, some species were more sen-
sitive than Daphnia to Zn, nitric acid, and HCl. This suggests that
sensitivity of protozoa to toxicants may be either more or less than
that of macroinvertebrates and that information does not suffice to pre-
dict sensitivity. Moreover, the relative sensitivity of protozoa to
various toxicants will not always be the same, i.e. species X may be
twice as tolerant to a toxicant as species Y but its relative sensitivity
may be quite different for another toxicant. Concentrations of selected
metals salts lethal (or tolerated) by 13 protozoan species, in mg/l metal,
ranged as follows: Cr+6, 160 to 5000 (>18 to 1000); Cu, 0.056 to 500
(0.024 to 18.0); Pb, 56 to >1000 (5.6 to 1000); Mn, 3.2 to >32 (0.65 to
3.2); Zn, 5.6 to >1000 (0.56 to 5000); Co, >2500 to >5000 (1000 to 2500);
AI, 2.4 to >1000 (1.0 to 1000); Sn, 10 to 32 (7.5).
2044.
Ryder, J.A. 1881(1882).
color of the oyster.
Notes on the breeding, food, and green
Bull. U.S. Fish Comm. 1:403-419.
A brief account of the natural history and cultivation of
oysters, as known at that time, is given. Speculation is made as to
source of green coloration found in some oysters; proposed causes in-
clude spores of green algae Ulva; the green microscopic plant Navicula
ostrearia; algous parasites or diatoms collecting in the animal tissues
(but was found to be green blood cells); and that "blood cells imbibing
the color from the tinged nutritive juices transuded through the walls
281
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of the alimentary canal acquired the color of the food which has been
dissolved by the digestive fluids." That copper could be the causative
agent was totally discredited for the quantity of copper ~eeded to pro-
duce green organs would "without a doubt be as fatally pOlsonous to the
oyster as to a human being."
2045.
Ryndina, D.O. 1973. Extraction of strontium-90 from seawater
by some high molecular weight compounds of brown algae.
Hydrobiological Jour. 9:16-20.
Data on accumulation and fixation of Sr-90 by live, killed,
and decomposing Cystoseira barbata thalli are presented; changes in
content of alginic acids and quantity of metals released during detritus
formation following acid digestion are shown. There is a 3 to 5X de-
crease in Sr-90 accumulation in C. barbata upon decomposition and
detritus formation; this does not significantly reduce content of
alginic acids in detritus. Metals equivalent to concentration of
alginic acids were extracted from C. barbata when treated with dilute
HC1. Increased HCl concentrations-sharply altered this relationship
with no significant decomposition of alginic acids occurring in such
treatment. Between 81 and 91% of Sr-90 in C. barbata was bound to com-
pounds possessing ion-exchange properties or capable of dissolving when
treated with weak HC1.
2046.
Ryndina, D.O. and G.G. Polikarpov. 1974. Role of Cystoseira
barbata (Good et Wood) AG. polysaccharides in the extraction
of some radionuclides from seawater. Hydrobiological Jour.
10(5):61-65.
Removal of fucoidan from Cystoseira barbata did not affect up-
take of Mn-54, Y-9l, or Ce-144 by decomposing alga. However, fucoidan
may act to concentrate Ca-45 and Sr-90 and stimulate Sr-90 fixation by
alginic acids. Sharp decrease in Sr-90 build-up factors in decomposing
Cystoseira may be due to decrease in sorption properties of its indi-
vidual polysaccharides, especially alginic acids, following changes in
pH of intracellular fluids. Cystoseira alginic acids and algulose
participate in concentration of Y-9l and Ce-144 from seawater.
2047.
Sabodash, V.M. 1974. Survival rate of grass carp larvae after
exposure to zinc sulfate. Hydrobiological Jour. 10:77-80.
At water hardness of 4.4 to 4.9 meq/l, mean percent survival
of carp larvae (Ctenopharyngdon idella) during exposure for 25 days to
zinc sulphate water levels of 0.05, 0.5, and 5.0 mg/l was higher than
controls (64.2,69.5 and 61.6, respectively, compared to 58.7%). At
282
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this hardness, addition of zinc salts at 0.05 and 0.5 mg/l also improved
size of larvae. Variability of length and weight and number of indi-
viduals lagging in development and growth were less than in control.
The 5.0 mg/l concentration adversely affected larval size and weight.
Addition of Zn salts to water with hardness of 8.2 to 8.7 meq increased
25 day surviyal rate to 71.2%, 80.7% and 69% at concentrations of 0.05,
0.5 and 5.0 mg/l, respectively, as compared to 65.0% in the control.
Differences in responses to Zn salts in water of varying hardness sug-
gest that Zn ions have a more stimulatory effect in water with a high
calcium content. Zinc has a selective effect in zones affecting calci-
fication of bony tissue.
2048.
Sadolin, E. 1928. The occurrence of arsenic in fish. Dansk.
Tids. Farmoci. 2:186-200. (In Danish, English summary)
In 2 analyses of codfish muscle tissue, values of 0.4 and 0.8
mg As/kg were determined. Liver contained 0.7 and 3.2 mg As/kg; and
cod-liver oil between 3.0 and 4.5 mg As/kg. Attempts were made to con-
centrate the oil-soluble arsenic compounds. From 6700 cc cod-liver oil
containing 26 mg As, a 2 cc extract was obtained containing 2 mg As.
The oil-containing muscular tissue from an eel was extracted whereby
all arsenic was removed from tissue and 0.6 mg As/kg was found in oil.
Similar experiments with herring showed a content of 2.0 mg As/kg in
muscle tissue and 9.0 mg As/kg in oil.
2049.
Saenko, G.N., M.D. Koryakova, V.F. Makienko and I.G. Dobrosmyslova.
1976. Concentration of polyvalent metals by seaweeds in
Vostok Bay, Sea of Japan. Marine Biology 34:169-176.
Spectrophotometric methods were used to measure contents of
Ti, V, Cr, Mn, Fe, Co, Ni, Cu, Mo and Zn in 16 species of red, brown,
and green seaweeds and 2 species of higher water plants collected from
intertidal and sublittoral zones of Vostok Bay, Sea of Japan. Some
species displayed capability for increased accumulation of selected
groups of several metals. Ptilota filicina concentrates Ti, V, Mn, Fe,
Ni, Cu, Zn, and Mo; Polysiphonia japonica Ti, V, Mn, Fe, Zn, Mo, and Cr;
Rhodomela larix Ti, V, Mn, Fe, Ni, Zn, and Cr; Agarum cribrosum Ti, V,
Mn, Fe, Ni, Zn, and Cr; VIvaria splendens Ti, V, Mn, Fe, Ni, and Cu;
VIva fenestrata Mn, Fe, Ni, and Cu; Enteromorpha prolifera Mn, Co, Zn,
Mo, and Cr; Codium yessoensis V, Mn, Fe, Zn, and Cr; Zostera asiatica
Ti, Mn, Ni, and Mo; Phyllospadix iwatensis Ti, V, Mn, Fe, and Zn. The
contents of the metals studied in seawater and the accumultion coeffi-
cients were also determined. The variation range is extremely high
both for the seaweed species and metals investigated. Maximum coeffi-
cients were noted for the following: Mn, 1.8x 105; Ti, 4.4 x 104;
Fe, 2.4 x 104; and Cr, 1.2 x 106.
283
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2050.
Saiki, M. and T. Mori. 1955. Studies on the distribution of
administered radioactive zinc in the tissues o~ fishes I.
Bull. Jap. Soc. Sci. Fish. 21(8):945-949.
Radioactivity levels in c/m/g of tissue of clam Meretrix
following immersion for 3 days in seawater containing 200,000 c/m/l
Zn-65 were: gill, 500; viscera without liver, 270; mantle, 260; liver,
250; adductor muscle and siphon, 170; and foot, 130. After 22 days in
water containing 45,000 c/m/l Zn-65, carp Cyprinus contained 285 c/m/l
in gill, 50 in skin and caudal fin, 65 in scales, 5 in vertebrae, 27 in
intestine, 2 in gall-bladder, 26 in hepatopancreas, 299 in kidney, 57
in heart and 3 in muscle.
Respective radioactivity values, in c/m/g raw tissue of carp
45 to 48 hrs after intramuscular injection of 5,000 c/m Zn-65, 12,000
c/m Sr-90 or 27,000 c/m Cs-137, were 1180 (Zn), 163 (Sr), and 2,200
(Cs) for kidney; 251, 44, and 427 for hepatopancreas; 173, 0, and
2,325 for heart; 121, 14 and 510 for intestine; 119, 352 and 756 for
gill; 87, 1349, and 522 for scale; 86, 569, and 832 for caudal fin; 51,
0, and 669 for gall bladder; 31, 60, and 349 for skin; 29, 137, and 301
for vertebra; and 9 (Zn) , 20 (Sr), and 130 (Cs) for muscle.
2051.
Saiki, M., S. Okano and T. Mori. 1955. Studies on the radio-
active material in the radiologically contaminated fishes
caught at the Pacific Ocean in 1954. Bull. Jap. Soc. Sci.
Fish. 20(10):902-906. (In Japanese, English abstract)
Highest concentrations of radioactivity were found in viscera,
particularly spleen, kidney and liver, with decreasing amounts in heart,
gill, intestine, and reproductive organs; very little was detected in
muscles and bone. Some radioactive material could be removed from raw
meat with water or 0.5% EDTA-Na solution. Active substances in fish
were chiefly composed of the radioisotopes of AI, Fe, Zn, Co, and Ni;
relatively little Sr or Ca was detected.
2052.
Saliba, L.J. and M. Ahsanullah. 1973. Acclimation and tolerance
of Artemia salina and Ophryotrocha labronica to copper sul-
phate. Marine Biology 23:297-302.
Brine shrimp A. salina and polychaete O. labronica were
acclimated in seawater with copper sulphate at concentrations of 0.1,
0.05, and 0.025 mg Cu2+/l, for 3 and 2 generations, respectively. Adults
and larvae of A. salina showed a greater tolerance to 1 mg Cu2+/l after
acclimation compared to controls of the same age, although this tolerance
diminished in successive generations. The acclimation effect was less
marked in O. labronica. In both species, tolerance to concentrations
>10 mg Cu2~/l was not enhanced. Growth-rate inhibition and an adverse
284
-------
effect on reproduction was observed for both species, in some instances
in direct relationship to the acclimation concentration. For A. salina,
authors suggest that a certain tolerance to Cu may be acquired-through
exposure to low concentrations.
2053.
Saliba, L.J. and R.M. Krzyz. 1976. Effects of heavy metals on
hatching of brine-shrimp eggs. Marine Poll. Bull. 7:181-182.
Addition of Cu, Fe, and Zn (as sulphates) caused decreased
hatch of brine-shrimp Artemia salina eggs with increasing concentrations.
With Pb (as acetate), decrease in hatch remained constant. Taking con-
current seawater controls as 100%, percentage hatch after 3 days exposure
to 5 mgll metal were: Cu, 15%; Pb, 65%; Fe, 46%; and Zn, 15%.
2054.
Saliba, L.J. and R.M. Krzyz. 1976. Acclimation and tolerance
of Artemia salina to copper salts. Marine Biology 38:231-238.
Brine shrimp were acclimated in seawater with cupric chloride,
acetate, carbonate, and sulphate, each at concentrations of 0.1, 0.05,
and 0.025 mg Cull. When compared to controls, growth inhibition was
observed in all four compounds generally in direct relation to concen-
tration. Growth was least in sulphate, and increased progressively in
chloride, acetate and carbonate, in that order. No inhibition was ob-
served in carbonate at 0.025 mg Cull. In toxicity tests, 2-week old
larvae from each solution were exposed to concentrations of 10, 7.5, 5,
2.5 and 1 mg Cull of the same compounds, together with unacclimated
larvae of the same age. Similar tests were held with 6-week old adults
acclimated in: 0.1 mg Cull (chloride, acetate and sulphate) using the
same concentrations; and in 0.5 mg Cull (carbonate), using 150, 125, 100,
75, and 50 mg Cull. Toxicity to unacclimated larvae and adults differed
with compounds, carbonate being the least toxic, followed by sulphate,
chloride and acetate in increasing order. Larvae acclimated in chloride
(0.025 mg Cull) and sulphate (0.1 and 0.5 mg Cull) showed an increased
tolerance to 1 and 2.5 mg Cull compared to untreated controls; tolerance
was not enhanced from 5 mg Cull upwards. In both compounds, adults
acclimated in 0.1 mg Cull showed increased tolerance to concentrations
between 1 and 7.5 mg Cull compared to controls. Larval mortality in
carbonate was below 50% in all test solutions; adults acclimated at 0.5
mg Cull showed an increased tolerance to 50 mg Cull compared to con-
trols. Considerable precipitation occurred with high levels of this
compound, thus affecting the "final" concentrations. No acclimation
effect was observed in acetate for either larvae or adults. It is sug-
gested that in A. salina, copper toxicity depends on the particular form
of the metal, and that this difference is manifested in growth inhibition
and in potential acquisition of increased tolerance through exposure to
low concentrations.
285
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2055.
Saltman, P. and H. Boroughs. 1960. The accumulation of zinc by
fish liver slices. Arch. Biochem. Biophys. 86:169-174.
Zinc can be accumulated by Tetraodon hispidus liver cells
against an apparent seven-fold concentrat~on gradient ~ia ~ passi~e
mechanism not directly coupled to metabolIc energy. KInetIc studIes
suggest that this process consists of a first-order ~or~tion.of ~n to
binding sites on or within the cell. Although the bIndIng sIte IS not
specifically characterized, it is profoundly altered by changes in tem-
perature, pH, and chemical environment.
2056.
Sandholm, M. 1973. Biological aspects of selenium: Uptake of
selenium by SH-groups and different organic materials in the
ecosystem. Thesis, Dept. Medicine, ColI. Veterinary Medicine,
Helsinki, Finland. 35 pp.
Although soils and plants in Finland were generally low in
selenium, high levels of Se in plants are associated with poisoning of
livestock. An important natural source of selenium may be fish which
in turn obtain Se from plankton. Phytoplankton such as Scenedismus
dimorphus, actively take up selenomethionine; zooplankton absorb sele-
nite directly from the water. In animals, selenite is metabolized by
erythrocytes, bound by carrier proteins associated with plasma albumin,
and then transported through the body. Selenite is bound to plasma
albumin using reduced glutathione. The active form of Se may be the
selenide located in non-haem-iron proteins.
The beneficial action of selenite may be due to its effect on
the enzyme glutathione peroxidase. Glutathione is necessary in maintain-
ing erythrocyte GSH, preventing oxidative damage. When erythrocytes
were incubated in selenite,Se was fluxed into cells within 1-2 minutes
and thereafter pumped out by a GSH dependent system. Se induced electron
flow from higher energy states to lower levels, thereby decreasing sulf-
hydryls and increasing oxygen consumption. When toxic amounts of Se
were introduced, Se in cell proteins and organelles normally present in
small amounts became disorganized with electrons transferred in an
uncontrolled way towards oxygen. The "charge transfer" capacity of Se
may be enhanced by hypervalent bonding. Se is excreted by urinary,
faecal, and respiratory routes.
2057.
Sandifer, P.A., J.S. Hopkins and T.I.J. Smith. 1975. Observa-
tions on salinity tolerance and osmoregulation in laboratory-
reared Macrobrachium rosenbergii post-larval (Crustacea:
Caridea). Aquaculture 6:103-114.
The tolerance of post-larval prawns to gradual and rapid in-
creases in salinity was determined. Mortalities occurred at salinities
286
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around 25%0 and increased rapidly at levels ~300/00 in both cases.
However, acclimation substantially increased survival time at 350/00.
Freezing point depressions of blood were measured from laboratory-
reared post-larvae and juveniles exposed to various salinities from
freshwater to approximately 350/00. Blood concentration was hyper-
osmotic to medium at salinities from freshwater to about 17-180/00 and
hypoosmotic at higher salinities. Post-larvae maintained a nearly con-
stant blood concentration over a wide range of external salinities
(freshwater to about 27-300/00). Osmoregulatory mechanisms failed at
salinities ~300/00, and thereafter blood concentration paralleled that
of medium. Blood concentrations of juvenile shrimp grown for 5 months
at salinities from freshwater to about 150/00 closely resembled those
of post-larvae.
The osmoregulatory performance of young M. rosenbergii is
generally similar to that of other brackish water animals, but in their
ability to hyperosmoregulate effectively in freshwater they more closely
resemble freshwater species. It is suggested that ~. rosenbergii may
be able to conserve salt in dilute media by producing blood-hypoosmotic
urine. A stress symptom often preceded death of post-larvae in high
salinities; animals changed gradually from nearly transparent to opaque
white and then died, usually within a day or so.
2058.
Sandow, A. and A. Isaacson. 1966. Topochemical factors in
potentiation of contraction by heavy metal cations. Jour.
Gen. Physiol. 49:937-961.
Low concentrations (about 0.5 mM) of Zn2+, Be2+, Ba2+, Cd2+,
Ni2+, Cu2+, pt4+, and 0.5 urn of UO~+, potentiate the twitch of frog sar-
torius and toe muscles by prolonging the active state of contraction.
Magnesium, Ca2+, and Hg2+ decrease contraction, and Sr2+ has variable
effects. The degree of potentiation is a roughly S-shaped function of
p (meta12+), suggesting that each metal binds to a ligand of the muscle
fiber, representative aRparent affinity constants being: UO~+, 5 x 106;
Zn2+, 2.8 x 105; and Cd +, 2 x 104. UO~+ potentiation effects are
rapidly reversed by P04, and Zn2+ and Cd2+ effects by EDTA, P04, and
cysteine. The rapidity of these reversals by nonpenetrating EDTA and
P04, and the fact that heavy metal ions evidently potentiate by prolong-
ing the action potential, indicate that metal potentiators exert their
primary action at readily accessible (i.e., plasma and T tubular) mem-
brane sites. Relatively slow kinetics-or-development of potentiation,
and even slower reversa~ of it in pure Ringer's solution, indicate that
metal ions are bound to connective tissue, as well as to muscle fibers,
to the amount of 1.0 uM/g for Zn, and 100 times that for UO~+. The
binding effects at the readily accessible membrane sites evidently im-
pairs delayed rectification and thus modifies the action potential and
excitation-contraction coupling so as to cause potentiation; this does
287
-------
not occur with anions such as NOs. SH is excluded, and P04 and imidazole
are possibilities, as the membrane ligand binding the potentiating metal
ions.
2059.
Sano, K. and H. Mohri. 1976.
magnesium ions in seawater.
Fertilization of sea urchins needs
Science 192:1339-1340.
When sea urchin eggs were inseminated in seawater free of
magnesium, the fertilization rate was very low. Spermatozoa that had
been treated with egg jelly to induce the acrosome reaction also failed
to fertilize eggs in Mg-free seawater. These results indicate that Mg
is indispensable for some process or processes at fertilization, such as
membrane fusion or sperm penetration.
2060.
Sappington, C.W. 1969. The acute toxicity of zinc to cutthroat
trout (Salmo clarki). M.S. Thesis, University of Idaho
Graduate School. 25 pp.
In static water with a hardness of 23.9 mg/l as CaC03, and pH
7, LC-50 (24, 48 and 96 hr) values of zinc, for trout, were 0.62, 0.27
and 0.09 mg/l, respectively. In a recirculating, flowing-water bioassay,
the LC-50 (24 hr) value of Zn was 0.42 mg/l.
2061.
Sarata, U. 1938. Studies in the biochemistry of copper. XXX.
Seasonal changes in the amount and distribution of copper in
tissues of the cultivated bull-frog. Japan. Jour. Med. Soc.
4:65-69.
Blood copper was highest at the end of winter, substantially
lower in the spring, increases somewhat with egg laying, and lowest in
the fall. Water balance and changes associated with breeding were con-
sidered the most probable causes. A similar pattern, but of reduced
magnitude, was established for liver (the primary storage organ for Cu).
Fat contained reduced levels of copper (by half) during spring and
breeding seasons. Eggs contained comparatively high levels of copper.
2062.
Sargent, D.F- and C.P.S. Taylor. 1972. The effect of cupric
and fluoride ions on the respiration of Chlorella. Canadian
Jour. Bot. 50:905-907.
Respiration of the alga ~. pyrenoidosa was not decreased by
760 mg Fil or 512 mg Cu2+/l, but simultaneous addition of both stopped
oxygen uptake. Authors conclude that Cu alone does not inhibit a dis-
similation pathway distinct from glycolysis.
288
-------
2063.
Sarot, D.A. and A. Perlmutter. 1976. The toxicity of zinc to
the immune response of the zebrafish, Brachydanio rerio,
injected with viral and bacterial antigens. Trans. Amer.
Fish. Soc. 105:456-459.
Zebrafish were injected with antigens prepared from infec-
tious pancreatic necrosis virus (IPNV) or from the bacterium Proteus
vulgaris. Zinc, present at 0.3 mg/l (l/lOth the 96 hr LC-50 value)
appeared to suppress the immune response against ~. vulgaris but not
against IPNV. Two weeks after second injection, IPNV-injected fish pro-
duced antibody titers of 32 in both zinc-treated and non-zinc-treated
groups, but ~. vulgaris-injected fish produced antibody titers of 128
and 32 in non-zinc-treated groups and 0 in zinc-treated groups.
2064.
Sastry, V.W. and Y.M. Bhatt. 1965. Zinc content of some marine
bivalves and barnacles from Bombay Shores. Jour. Indian Chern.
Soc. 42:121-122.
The following mean zinc concentrations, in mg/kg wet wt, were
found in samples collected from Bo~oay coast: 11 for clam Katelysia
marmorata, 14 for clam Meretrix meretrix, 11 for mussel Mytilus viridis,
254 for rock-oyster Crassostrea cucullata, 203 for backwater oyster C.
madrasensis, and 71 for barnacle Balanus amphitrite communis.
2065.
Sato, S., Y. Miyata and S. Kunitomi. 1976. Physical properties
of "narutowakame" and its alginate and metal contents. Bull.
Jap. Soc. Sci. Fish. 42(3):337-341.
Water soluble alginate derived from brown seaweed, Undaria
pinnatifida, contained elemental levels up to 40 mg/kg for Na and K, 20
for Ca and 30 for Mg. Each element decreased to <10 mg/kg upon ash-
treatment, an important step in processing of "narutowakame," a Japanese
food substance. Residues contained levels, in mg/kg, of ~25 for Na and
K and up to 250 for Ca and 200 for Mg. Ash-treatment increased Ca levels
to 700 mg/kg, but did not affect other elements. From tensile strength
studies, authors concluded that hardness of "narutowakame" is due to
formation of water insoluble Ca alginates during ash-treatment.
2066.
Saward, D., A. Stirling and G. Topping. 1975. Experimental
studies on the effects of copper on a marine food chain.
Marine Biology 29:351-356.
Copper at levels of 10, 30, and 100 ug Cull were applied to a
marine food chain consisting of phytoplankton, the clam Tellina tenuis,
and juvenile flatfish Pleuronectes platessa. Accumulations were dose-
289
-------
dependent and in no case was a plateau concentration reached. Most of
the added dose was taken up by sand; accumulations in clam shell were
negligible. However, high levels were found in clam flesh, where con-
centrations after 100 days were 50, 270, 470, and 1100 mg Cui kg dry
flesh for added dose concentrations of 0, 10, 30, and 100 ~g Cull,
respectively. There was no accumulation of Cu in fish muscle, but
accumulations in viscera after 100 days were 30, 71, 147, and 567 mg
Cu/kg dry flesh for dose concentrations of 0, 10, 30, and 100 ~g Cull,
respectively. All doses reduced both standing crop and rate of photo-
synthesis per unit of chlorophyll a. All dose concentrations adversely
affected clam condition, with effect most marked during deposition of
winter reserves. Siphons of Tellina, which are important food items
for Pleuronectes, showed a weight decrease when exposed to 30 and 100
~g Cull. For fish, all Cu doses resulted in reduced growth, but there
was no significant change in condition or biochemical composition. How-
ever, ash weight of fish exposed to copper was significantly higher
than controls.
2067.
Sayler, G.S., J.D. Nelson, Jr. and R.R. Colwell. 1975. Role
of bacteria in bioaccumulation of mercury in the oyster
Crassostrea virginica. Applied Microbiol. 30(1):91-96.
Uptake of Hg-203 by oysters held under control conditions was
compared with that of Hg-203 uptake by oysters under similar conditions
except that Hg-accumulating and Hg-metabolizing species of Pseudomonas
were added to the test oysters. After 4 days in seawater containing 10
ug of Hg-203 C12/l, oysters without bacteria contained 4 ug Hg/kg wet
wt in mantle fluid, 200 in mantle, 647 in gills, 216 in viscera, and
56 in adductor muscle, with a total content of 201 ug Hg/kg wt tissue.
Oysters with a Hg-reducing strain of Pseudomonas accumulated 9 ug Hg/kg
wt tissue in mantle fluid, 511 in mantle, 1747 in gills, 463 in viscera,
133 in adductor muscle, and 312 in whole oyster. Oysters held with a
Hg-accumulating strain of Pseudomonas contained 12 ug Hg/kg wt tissue
in mantle fluid, 405 in mantle, 2850 in gills, 335 in viscera, 161 in
adductor muscle, and 463 in whole oyster. The major portion of Hg-203
in water was associated with microparticulate fraction corresponding to
a rise in total viable tount of Pseudomonas. Authors concluded that
whole oyster accumulation of mercury was more than doubled in presence
of Hg-resistant bacteria.
2068.
Schell, W.R. and R.L. Watters. 1975. Plutonium in aqueous
systems. Health Physics 29:589-597.
A review of current knowledge of plutonium in aquatic environ-
ments is presented. Limited data indicate that low environmental levels
are present. Concentration factors are highest in plankton, and decrease
290
-------
with increasing organism complexity. Recent studies of water; sediment,
algae, fish, molluscs, echinoderms, crustacea, and detritus at Bikini
and Eniwetok Atolls indicate that Pu exists in the particulate, soluble,
and colloidal physical-chemical states. Radioplutonium species, even
16 years post-initial contamination, are still being injected into water
column from sediments, indicating an active biogeochemical cycle. Con-
centrations of plutonium in vertebrates and invertebrates measured at
Eniwetok were low and ranged from 0.001 to 0.2 pCi/g wet in fish muscle.
2069.
Scott, D.M. and C.W. Major. 1972. The effect of copper (II) on
survival, respiration, and heart rate in the common blue
mussel, Mytilus edulis. BioI. Bull. 143:679-688.
After 7 days, 55% of mussels held in 0.2 mg/l of Cu2+ (initial
concentration) died; only 5% were dead at 0.1 mg/l of Cu2+; controls
exhibited 1% mortality over the same time period. At 10 mg/l of Cu2+,
valves were closed immediately after addition of copper and remained
closed for at least 15 hours, at which time this portion of the study
was discontinued. At 1.0 mg/l of Cu2+, mussels shut down for about 15
minutes; afterwards, valves were opened and rate of oxygen consumption
was 184 ~l/hr; approximately 90 minutes after copper addition there was
a sudden increase in respiration until rate a~proached that of controls
(578 ~l of oxygen per hr). At 0.5 mg/l of Cu + there was no initial
shutdown, but a recovery similar to that of 1.0 mg/l was observed. At
0.3 mg/l there was neither a shutdown or recovery. At 0.2 mg/l of Cu2+
the change in respiration over 2 hours at 10 C was not significantly
different from controls. No change in heart beat rate from controls
was noted at 0.2 mg/l of Cu2+, blrt at higher concentrations a general
dose response is clearly apparent within one hour. It is suggested
that organically bound Cu does not provide toxic levels of free Cu.
Some organisms will be damaged by free Cu on initial binding, as this
is considered the toxic step. But members of the food chain may accu-
mulate extraordinary levels of organically bound copper without apparent
effect. Authors conclude that free copper and not total copper in a
marine ecosystem is probably the pertinent parameter of toxicity.
2070.
Scott, D.P. 1974.
relation to age,
fishes from Clay
31: 1723-1729.
Mercury concentration of white muscle in
growth, and condition in four species of
Lake, Ontario. Jour. Fish. Res. Bd. Canada
Studies of walleye Stizostedion vitreum, northern pike Esox
lucius, white sucker Catostomus commersoni, and lake whitefish Coregonus
clupeaformis from each of 4 areas of a highly Hg-contaminated lake
showed that larger fish have greater white muscle Hg concentration with-
in species and within populations. Older fish and faster-growing fish
291
-------
were generally more contaminated, while rela~ivelY heavier ~is~ were
less contaminated, subject to the above specIes-areas restrIctIons.
Statistical analyses indicated profound within-species differences
between samples from all areas. There was no correlation between these
differences and sediment Hg values. There are significant interactions
between age and growth, and age ~nd condition.
2071.
Scott, R.
algae.
1954. A study of caesium accumulation by marine
Proc. 2nd Radioisotope Conf. 1:373-380.
Fucus vesiculosus accumulated Cs-134 by a concentration factor
(C.F. = counts per g dry wt/counts per g seawater) of 50 in 45 days
when maintained in natural and artificial seawater. Exclusion of K and
an equivalent addition of Na resulted in a CF of 200 in 25 days. Cs-134
uptake by Rhodymenia palmata was light dependent, but no region of the
visible spectrum was disproportionately effective in promoting uptake.
Treatment of ~. palmata with 0.001 M sodium azide, 0.001 M potassium
cyanide or C02 exclusion, resulted in diminution or cessation of Cs-134
uptake. A lethal dosage of 0.001 M dinitrophenol resulted in total
Cs-134 release. Healthy~. palmata, which had absorbed Cs-134, lost no
radioactive material over several weeks when transferred to natural sea-
water. For R. palmata, highest concentrations occurred in stipo-frondal
zone. In Laminaria digitata uniform radioactivity per unit area was
found from stipo-frondal zone to tip.
2072.
Severy, H.W. 1923.
marine animals.
The occurrence of copper and zinc in certain
Jour. BioI. Chern. 55:79-92.
Crustaceans, molluscs, teleosts, echinoderms, coelenterates,
and marine mammals (16 species in all) were analyzed for Cu and Zn.
Highest concentration of copper in any sample was 19.6 mg/kg wet wt in
shrimps and the lowest was <0.00 mg/kg in shell of mussel, and spleen
and liver of sea lion. All other copper values ranged between 0.56 and
4.0 mg/kg. Zinc was present in all samples with values ranging from
2.11 mg/kg in sea urchin to 64.9 mg/kg in oyster (zinc content of Cali-
fornia oyster is much lower than Eastern oyster). Marine mammals (sea
lion, whale) do not carry copper to any extent; copper in the sea food
eaten does not appear to be accumulative; zinc was present in all
tissu~s examined, but amount is less than for oysters. Copper is pre-
~ent In lower forms of sea animals as an oxygen carrier in place of the
Iron of mammals; environment does not seem to change the sea lion and
whale in this respect. The function of the zinc had not been clearly
worked out.
292
-------
2073.
Seymour, A.H. 1966. Accumulation and loss of zinc-65 by oysters
in a natural environment. Proc. Symp. Disposal Radioactive
Wastes into Seas, Oceans and Surface Waters. Int. Atom. Ener.
Agen., Vienna, 16-20 May 1966: 605-619.
Accumulation and loss of Zn-65 by oysters was determined by
cross-transplanting Crassostrea gigas from/to Puget Sound or Hood Canal,
where Zn-65 is virtually absent, to/from Willapa Bay, which contains
from 0.0036 to 0.012 mg/l Zn, or 85X levels of Puget Sound. For the
first 60 days after transfer, accumulation of Zn-65 ranged from 0.5 to
2 pCi/g(dry)/day; after 200 days the rate decreased to 0.25 pCi/g(dry)/
day. Seasonal and annual differences in accumulation immediately after
transfer were evident; accumulation rates generally decreased from
spring to fall and from 1963 to 1965. Steady-state condition was not
reached until after 500 days. Rate of loss was relatively constant at
0.55%/day. The effective and biological half-lives were estimated to
be 125 and 255 days, respectively. Willapa Bay oysters concentrated
Zn by a factor of 1.5 x 104, using a wet-dry ratio of 6.0 and Zn values
of 515 mg/kg(dry) for oysters and 7.37 ~g/l for seawater.
2074.
Shaw, H.M., R.L. Saunders and H.C. Hall. 1975. Environmental
salinity: its failure to inf~uence growth of atlantic salmon
(Salmo salar) parr. Jour. Fish. Res. Bd. Canada 32:1821-1824.
Instantaneous growth rates and food conversion efficiencies
of salmon parr fed daily rations of 0 to 2.9% of dry body wt were
similar at salinities of 0.1, 10 and 20%0. Maintenance ration was
slightly more in 20%0 than in 10%0 (salinity isomotic with blood)
or 0.1%0 (freshwater).
2075.
Shaw, T.L. and V.M. Brown.
copper to rainbow trout.
1974. The toxicity of some forms of
Water Research 8:377-382.
The LC-50 (24 hr) of total Cu, present as Cu2+ and CuC03, at
pH 7.3-7.5, ranges from 0.07 to 0.25 mg Cu2+/l at an alkalinity of
100 mg CaC03/l and from 1.15 to 2.08 mg Cu2+/l at an alkalinity of 250
mg CaC03/l. Addition of neutralized NTA (nitrilotriacetic acid) to
cupric copper produces an NTA-copper complex, which was tested for
toxicity. In 8-day bioassays, 0.5 mg/l total copper (=0.03 mg/l free
cupric ion, 0.47 mg Cu2+/l as copper carbonate, and no Cu2+ as NTA-Cu
complex) produced 50% mortality; 4.0 mg/l total copper (=0.01 mg/l free
cupric ion, 0.16 mg Cu2+/l as copper carbonate, and 3.83 mg Cu2+fl as
NTA-Cu complex) produced no deaths; 5.5 mg/l total copper (=0.03 mg/l
free cupric ion, 0.47 mg Cu2+/l as copper carbonate, 5.0 mg Cu2+/l as
NTA-Cu complex) produced 90% mortality. Authors concluded that the
2~
-------
total concentration of soluble Cu and hence toxicity can be determined,
except when highly toxic organocopper compounds are present.
2076.
Shealy, M.H. and P.A. Sandifer. 1975. Effects of mercury on
survival and development of the larval grass shrimp,
Palaemonetes vulgaris. Marine Biology 33:7-16.
For grass shrimp, 56 ug Hg/l was toxic to all larvae within
24 hrs; below 5.6 ug Hg/l no lethal effect occurred within 48 hrs.
LC-50's (48 hr) for fed and unfed larvae were 15.6 and 10.0 ug Hg/l,
respectively. Latent effects of larval exposure for 48 hrs to sub-
lethal mercury concentrations included: reduced survival to postlarval
stage, delayed molting, extended development time, increased numbers of
larval instars, and morphological deformities.
2077.
Sherwood, M.J. 1975. Toxicity of chromium to fish. Ann. Rep.
S. Calif. Coas. Water Res. Proj. El Segundo, Calif. :61-62.
For speckled sanddab Citharichthys stigmaeus, the LC-50 (96
hr) value for hexavalent chromium was 31.0 mg/l. The LC-50 (21 day) was
5.4 mg Cr+6/l. Estimates for median effective concentrations (EC-50)
for a feeding response for 4, 14 and 21 days were 15.0, 3.7 and 2.2
mg Cr+6/l, respectively.
2078.
Shin, E.-B. and P.A. Krenkel.
biomethylation mechanisms.
48(3):473-501.
1976. Mercury uptake by fish and
Jour. Water Poll. Contr. Fed.
Factors affecting methylmercury accumulation by teleosts
included: chemical Hg species; type and number of microorganisms
present; sorption characteristics of sediments; temperature; and
chloride ion concentration. No discernible effect on uptake was evi-
dent by adding organics. Demethylation of methyl-Hg occurred in sedi-
ments with highest methylation rate at pH 7-
Shulman, J., I.L. Brisbin and W. Knox. 1961. Effect of tempera-
ture, salinity, and food intake on the excretion of Zn65 in
small marine fish. BioI. Bull. 121(2):378.
At 20 C and 35%0 salinity, the biological half-life (TbY2)
of Zn-65, administered via Venus meat soaked in Zn-65C12, was 13 days
for Menidia menidia as compared with 58 days for Fundulus heteroclitus;
the metabolic rate of Fundulus is about 2X that of Menidia. For
Fundulus, TbY2 was 75 days at 10 C and 35 days at 30 C, suggesting an
2079.
2~
-------
inverse relationship of environmental temperature and excretion rate.
A preliminary experiment showed that Fundulus's TbY2 was the same at
8 and 350/00 salinity, indicating that gill salt excretion at high
salinity does not materially increase Zn exchange.
Over a l7-day geriod, Zn-65 tagged specimens of Tautogolabrus
adspersus at 20 C and 35 /00 salinity exhibited a Tb~ of 44 days at
food levels varying from 153 to 58 cal/g fish/day. TbY2 of one speci-
men of T. adspersus which was starved for the l7-day period was 59 days.
2080.
Shultz, C.D., D. Crear, J.E. Pearson, J.B. Rivers and J.W.
Hylin. 1976. Total and organic mercury in Pacific blue
marlin. Bull. Environ. Contamin. Toxicol. 15:230-234.
Nineteen marlin Makaira nigricons caught off the Kona side
of Hawaii were analyzed for total mercury and organic mercury (methyl-
mercury). Mean total mercury in mg/kg wet wt was 6.3 for liver, 2.0
for muscle, 0.5 for central nervous tissue, and 0.3 for gonads. Mean
organic mercury in mg/kg wet wt was 0.4 for muscle, 0.2 for liver;
0.09 for central nervous tissue, and 0.07 for gonads. Authors state
that the unusually high total to organic mercury ratio of 35:1 in liver
may be a physiological mechanism to reduce Hg content by transforming
organic mercury to its less toxic and more easily excretable inorganic
form. Since all marlin were captured near an active volcano, and pre-
vious studies have shown greater biological levels of Hg near areas of
high geothermal activity, it was possible that Hg in these marlin may be
from natural causes.
2081.
Shuster, C.N., Jr. and B.H. Pringle. 1968. Effects of trace
metals on estuarine molluscs. Proc. First Mid-Atl. Indus.
Waste Conf., 13-15 Nov. 1967: 285-304. Available from Dept.
Civil Engineering, Univ. Delaware, Newark, Del.
American eastern oyster Crassostrea virginica, northern qua-
hog Mercenaria mercenaria, and softshell clam Mya arenaria, collected
from productive commercial shellfish beds from Maine through N. Carolina,
contained the follow~ng metals contents in mg/kg wet wt of soft parts:
oyster quahaug clam
180-4120 11-40 9-28
7-517 1-16 1.2-90
31-238 9-83 49-1710
0.14-15 0.7-29 0.1-29
0.10-7.8 0.10-0.73 0.10-0.90
0.10-2.30 0.10-7.5 0.10-10.2
0.04-3.40 0.19-5.8 0.10-5
0.08-1.80 0.10-2.4 0.10-2.3
0.06-0.20 0.10-0.20 0.10-0.20
Zn
Cu
Fe
Mn
Cd
Pb
Cr
Ni
Co
295
-------
A rise in metal content of oysters during the past 35 years was noted.
Laboratory exposure studies of 20 weeks duration in flowing
seawater showed at 20 weeks the following cumulative percentage mortali-
ties, and total metal accumulations in mg/kg wet wt, during immersion
in various concentrations of Cd, Cu, Co, Zn, or Pb:
Test concentration Oyster Quahaug
(mg/l) % deaths (residue) % deaths (residue)
Cd 0.1 32 (121) 3 (7)
0.2 45 (96) 38 (15)
Cu 0.025 3 (630) 91 (2.2)
0.05 6 (1060) 93 (3.6)
Co 0.05 5 (6) 0 (-)
0.1 2 (11) 1 (-)
Zn 0.1 2 (1524) 0 (-)
0.2 1 (2671) 0 (17)
Pb 0.2 1 (328) 0 (70)
Cd-exposed oysters showed inhibition of shell growth when com-
pared to those exposed to Cu, Cr, or Zn. Quahaugs exposed to Zn
exhibited a deep purple shell color.
2082.
Sick, L.V. and H.L. Windom. 1975. Effects of environmental levels
of mercury and cadmium on rates of metal uptake and growth
physiology of selected genera of marine phytoplankton. In
Howell, F.G., J.B. Gentry, M.H. Smith (eds.). Mineral cycling
in southeastern ecosystems. U.S. Energy. Res. Dev. Admin.:
239-249. Avail. as CONF-7405l3 from NTIS, U.S. Dept. Comm.
Springfield, VA 22161.
Rates of Hg-203 and Cd-l09 uptake by algae were dependent on
stable metal concentration, exposure time and algal species. Concentra-
tions of Hg-203 uptake above 40 ug Hg2+/l did not increase rates of up-
take. Rates of Cd-l09 uptake were 10 to 100X lower than Hg-203 and were
directly proportional to metal added between 20 and 80 ug/l. Nitzischia
exhibited higher uptake for both Hg and Cd than Carteria or Dunaliella
and this may be due to its greater surface area. Concentrations of
stable Hg2+ between 30 and 350 ug/l significantly depressed algal growth.
2083.
Simmons, M.A. and A.W. Knight. 1975. Respiratory response of
Neomysis intermedia (Crustacea: Mysidacea) to changes in
salinity, temperature and season. Compo Biochem. Physiol.
50A:18l-l93.
296
-------
Neomysis respiration generally decreased as salinity increased
from 1 to 70% seawater, with smaller mysids experiencing a greater
change in respiration than larger ones. Respiratory response to tem-
perature was weight dependent with larger mysids experiencing a greater
change in respiration with temperature increase than smaller mysids.
Seasonal temperature acclimation was apparent only at 6 C. Seasonal
modification of respiration appeared to be related to changes in level
of reproduction and type of available food.
2084.
Sinley, J.R., J.P. Goettl, Jr. and P.H. Davies. 1974. The
effects of zinc on rainbow trout (Salmo gairdneri) in hard
and soft water. Bull. Environ. Contamin. Toxicol. 12:193-201.
LC-50 (96 hr) values for juvenile trout in hard water (330
mg/l as CaC03) and soft water (25 mg/l as CaC03) at 15 C were 7210 and
430 ~g/l zinc as zinc sulphate, respectively. Bioassays with eyed eggs
produced an LC-50 value of 2720 ~g Zn/l in soft water; suggesting that
this is one of the more resistant stages. The maximum allowable toxi-
cant concentration (MATC) for trout after 21 months exposure in hard
water fell between 640 ~g Zn/l (6.4% mortality) and 320 ~g Zn/l (no
zinc-caused mortalities); growth rates and ovarian development were the
same for all zinc concentrations tested. The MATC for trout after 21
months exposure in soft water ranged between 260 ~g Zn/l (6.9% mortality),
and 140 ~g Zn/l (no deaths). Chronic toxicity of zinc to trout was
dependent upon the life cycle stage at which exposure began. Fish not
exposed to zinc as zygotes may be up to 4X more susceptible than those
subjected initially to zinc as zygotes.
2085.
Skei, J.M., M. Saunders and N.B. Price.
ton from a polluted Norwegian fjord.
34-35.
1976. Mercury in plank-
Marine Poll. Bull. 7:
Plankton of mixed composition were collected from Sorfj~rden
and Hardangerfj~rden on west coast of Norway and analyzed for total Hg
by atomic absorption. Five methods of decomposing the samples were
tested, showing no significant variations in recovery of Hg. Levels
ranged from 0.52 to 25.21 mg Hg/kg dry wt. Maximum values were found
in southern part of Sorfj~rden where three industrial companies are
located, one of which discharged 3 kg Hg/day into fjord waters in 1972.
Two samples contained larger portions of zooplankton than anticipated
and showed lower Hg content than expected. This lower Hg concentration
in zooplankton as compared to phytoplankton suggests a lack of food
chain amplification in lower trophic levels.
297
-------
Skerfring, S., K. Hansson and J. Lindstem. 1970. Chromo7ome
'breakage in humans exposed to methyl mercury through flsh
consumption. Arch. Environ. Health 21:133-139.
Chromosome analysis was performed on cells from lymphocyte
cultures from 9 subjects with increased levels of mercury in their red
blood cells (21 to 370 m~g/g) and in 4 healthy controls (mercury levels
2 to 40X lower). The elevated mercury levels were likely to have ori-
ginated from dietary fish containing 1 to 7 mg/kg wet wt of methyl-
mercury. A statistically significant rank correlation was found between
frequency of cells with chromosome breaks and mercury concentration.
2086.
2087.
Skidmore, J.F. 1966. Resistance to zinc sulphate of zebrafish
(Brachydanio rerio) embryos after removal or rupture of the
outer egg membrane. Jour. Fish. Res. Bd. Canada 23:1037-1041.
Fifteen and 25-hr-old zebrafish embryos with the outer egg
membrane ruptured survived longer in a solution of zinc sulphate (20
mg/l Zn) than embryos of the same ages with the membrane intact. Forty-
two-hr embryos with the membrane completely removed survived in 4 concen-
trations of zinc sulphate (2.5, 5, 10, and 20 mg/l Zn) at least as long
as 42-hr embryos with the membrane entire. The high resistance of
zebrafish embryos to zinc was therefore not owing to protection by the
membrane. On the contrary the presence of the membrane lowered resis-
tance. This result was probably due to formation of opaque material
enclosed by the outer egg membrane of zinc-poisoned, unruptured eggs.
The action of this material in reducing survival is unknown.
2088.
Slater, J.V. 1961. Comparative accumulation of radioactive
zinc in young rainbow, cutthroat and brook trout. Copeia
1961:158-161.
Analysis of comparative accumulation rate of Zn-65 at a con-
centration of 0.1 ~Ci/ml in 7 to 8 month old trout showed greatest
accumulation in brook trout Salvelinus fontinalis, at 37 x 10-3 counts/
min/mg dry wt between 24 and 48 hrs of exposure. Uptake by cutthroat
trout Salmo clarki, was 34 x 10-3 c/m/mg dry wt; for rainbow trout
Salmo gairdnerii, this was 24 x 10-3c/m/mg dry wt. In rainbow and cut-
throat, gill filaments accumulated greatest amount of isotope, with
operculum, tail and ventral body wall having respectively smaller accumu-
lations. The ion uptake in cutthroat gill was almost twice that of rain-
bow gill.
298
-------
2089.
Small, L.F. and S.W. Fowler. 1973. Turnover and vertical trans-
port of zinc by the euphausiid Meganyctiphanes norvegica in
the Ligurian Sea. Marine Biology 18:284-290.
Participatory turnover time is defined as the time required
to cycle an element in a system through a given material in that system.
The participatory turnover time of ionic zinc by the adult ~. norvegica
population in the Ligurian Sea ranged between 498 and 1243 years, depend-
ing upon available food and considering food chain as the only route for
zinc accumulation. A total impact turnover time was calculated as the
sum of participatory turnover time for live individuals plus time re-
quired for dead euphausiids to lose 90% of their zinc to water. Car-
casses lost zinc to water at a slower rate than either feces or molts,
and so established the maximum loss time for all particulate excretion
products. Nevertheless, total-impact turnover time for zinc did not
differ significantly from the participatory turnover time. The net ver-
tical transport of zinc by M. norvegica from sea surface to any speci-
fied depth can be calculated as sum of dissolved zinc excreted below the
depth plus concentrations of zinc left in feces, molts, and carcasses
after sinking to specified depth. Carcasses sink fastest and lose the
smallest fraction of zinc during descent; fecal pellets sink slowest and
lose the greatest fraction of their zinc; molts are intermediate. Feces
represents the major route for delivering zinc to the Ligurian Sea
bottom (2500 m), because concentration of the element in pellets is much
higher (41-117 mg Zn/kg dry wt daily) than carcasses (up to 0.55) or
molts (up to 1.35). Excretion of dissolved zinc into the water at the
vertical migration depth of the living population during daylight hours
was also inconsequential. Feces zinc represented over 80% of the total
zinc transported to the sea floor if only marginal food supplies were
available to the euphausiids, and over 90% if food was in sufficient
supply. M. norvegica can effect a net transport of about 98% of its
body zinc concentration below 500 m daily in conditions of sufficient
food supply and assuming that no released products are eaten during
descent. If the food supply in the Ligurian Sea is considered only
marginal throughout the year; M. norvegica can still effect a daily net
transport below 500 m of about 36% of its body concentration, and about
6% of its body concentration will reach 2500 m daily.
2090.
Small, L.F., S. Keckes, and S.W. Fowler. 1974. Excretion of
different forms of zinc by the prawn, Palaemon serratus
(Pennant). Limnol. Oceanog. 19(5):789-793.
Fresh specimens of Palaemon serratus (300-1,600 mg wet wt),
were collected from the upper Adriatic Sea and used to determine excre-
tion rates of zinc in "zinc-free" water by anodic stripping polarographic
techniques. Weight-specific excretion of total zinc varied reciprocally
with body wt, in a log-log relationship. Weight-specific excretion of
299
-------
ionic-particulate zinc appeared gre~test in short ter~ (1-3 hr) experi-
ments, while weight-specific excretl0n.of comp1exed Zlnc appeared
greatest in longer term (4-5 hr) experlments; how~ver, authors ~oncede
the possibility that ionic-particulate zinc and d1sso1~ed ?rga~lc com-
pounds may be excreted separately with subsequent comblnatlon ln water
to yield zinc complex.
2091.
Smith, A.L., R.H. Green and A. Lutz. 1975.
by freshwater clams (family Unionidae).
Canada 32:1297-1303.
Uptake of mercury
Jour. Fish. Res. Bd.
Mercury concentrations were measured in water, sediments and
3 species of clams from lakes with and without reported Hg contamination.
Elevated mercury levels in clams were associated with elevated mercury
levels in water and sediments. For example, Anodonta grandis from Clay
Lake, Ontario, where Hg levels were comparatively high, i.e., 0.2 ~g/l
in water column and 0.10 mg Hg/kg in wet sediment, exhibited Hg levels,
in mg/kg wet wt. of 0.47 in mantle, 0.51 in gill, 0.83 in adductor muscle,
0.78 in liver, 0.62 in foot, 0.65 in visceral mass and 0.08 in decalci-
fied shell, giving a whole clam value of 0.18. Clams from Minnedosa
Lake, which had lower Hg levels of 0.01 ~g/l in water column and 0.01
mg/kg in wet sediment exhibited lower Hg levels, in mg/kg wet wt, of
0.05 in foot, 0.07 in gill and 0.06 in liver, giving a whole clam value
of 0.01.
Uncontaminated clams were exposed to 3 Hg compounds at 1, 10,
50, and 100 ~g Hg/l for up to 3 weeks in the laboratory. Clams concen-
trated Hg in the order methylmercuric chloride> phenylmercuric acetate
> mercuric chloride. Over a range of 1.0 to 100 ~g Hg/l, Hg uptake
rates were related to environmental levels; temperatures of 10 and 20 C
produced essentially identical elimination rates. Distribution among
organs depended on compound to which clams had been exposed. Of the 3
Hg species tested, only methylmercuric chloride was concentrated exten-
sively in foot muscle. Transfer of methylmercuric chloride among organs
apparently continued after exposure to compound had ended.
2092.
Smith, B.P., E.rHejtmancik and B.J. Camp. 1976.
of cadmium on Ictalurus punctatus (catfish).
Contamin. Toxico1. 15(3):271-277.
Acute effects
Bull. Environ.
Catfish exposed to ~800 ~g Cd/l for 3 weeks showed concentra-
tion factors from 2 to 12 in liver, and 5 to 41 in kidney, with greatest
magnification occurring at 50 ~g Cd/I. Hematological constituents such
as serum transaminase, serum triglycerides, albumin:g1obulin ratio, and
serum Na and Mg were not significantly altered by this Cd treatment.
300
-------
2093.
Smith, D.C.W. 1956. The role of the endocrine organs in the
salinity tolerance of trout. Mem. Soc. Endocrinol. 5:83-101.
In brown trout Salmo trutta,both thyroid activity and salinity
tolerance peaked in the spring, but only salinity tolerance peaked in
autumn; no correlation between the two was evident. Mature fish had a
lower salinity tolerance than immature, but there was no difference in
thyroid activity. Trout subjected to increasing salinity showed a fall
in thyroid activity. Injection of thyroxine generally raised salinity
tolerance; doses required were above the physiological level. Adminis-
tration of thiourea and thiouracil reduced salinity tolerance.
Posterior-pituitary extracts, testosterone propionate, chorionic gonado-
trophin, thyrotrophin, ACTH and adrenocortical extracts had no signifi-
cant effect on salinity tolerance; anterior-pituitary extracts and
growth hormone raised salinity tolerance; threshold for growth hormone
is below 30 ~g/lO g fish/week--probably a physiological dose.
2094.
Smith, D.H. 1967. R factors mediate resistance to mercury.
nickel, and cobalt. Science 156:1114-1116.
Clinical isolates and laboratory stocks of Escherichia coli
and Salmonella bacteria were studied for resistance to AI, Cd, Cr; Co,
Cu, Pb, Hg, Ni, Ag and Tl. Eleven clinical isolates carrying R factors
were resistant to Hg. Resistance was mediated by a previously unde-
fined R-factor gene, phenotypically expressed within 2 to 4 minutes
after entry into sensitive bacteria. Fourteen strains, 12 infected
with R factors, were resistant to Co and Ni, but these resistances were
mediated by R-factor genes in only two strains; separate R-factor genes
mediated resistances to Ni and Co. Results indicate that genetic com-
position of R factors is greater than originally defined.
2095.
Smith, E.J. and J.L. Sykora. 1976. Early developmental effects
of lime-neutralized iron hydroxide suspensions on brook trout
and coho salmon. Trans. Amer. Fish. Soc. 105:308-312.
Effects of lime-neutralized iron hydroxide suspensions on eggs
and alevins of brook trout Salvelinus fontinalis, and coho salmon
Oncorhynchus kisutch, were interpreted from data on hatchability, sur-
vival, and growth in 5 test concentrations from 0.75 to 10.5 mg Fe/I,
and controls. Growth of 90 day-old coho salmon alevins was reduced in
water containing 1.27 mg Fe/l of lime-neutralized suspended iron, where-
as hatchability was unaffected in highest concentration tested of 10.5
mg Fe/I. Concentration of 10.5 mg Fe/l had no measurable effect on
hatchability, survival and growth of brook trout alevins. Safe upper
limit of lime-neutralized suspended iron for coho salmon alevins lies
between 0.97 and 1.27 mg Fe/I.
301
-------
2096.
Smith, M.W. 1935. The use of copper sulphate for eradicating
the predatory fish population of a lake. Trans. Amer. Fish.
Soc. 65:101-114.
Copper sulphate was added to a Nova Scotia lake in August,
1934, in sufficient quantity to yield a concentration of 3.06 mg/l.
Phytoplankton were decimated and continued to be scarce for almost a
year. Rooted, submerged, and emergent vegetation appeared little
affected. Zooplanktonic forms were drastically reduced in number. All
clams and snails were killed; insect abundance was reduced. Fish mor-
talities were high, with most dead individuals found in shallow water.
Author suggests that death in fish was due to precipitation of mucus on
gills, leading to suffocation.
2097.
Smith, P.G. 1969. The ionic relations of Artemia salina (L.).
II. Fluxes of sodium, chloride, and water. Jour. Exp.
BioI. 51:739-757.
Effects of different external media (including lithium,
choline, and benzenesulphonate) on sodium and chloride efflux in brine
shrimp Artemia salina, were observed in animals acclimatized to sea-
water. In seawater, both sodium and chloride fluxes across epithelium
are a~proximatelY 7 x 10-15 M/cm2/sec (or 1.6 x 10-10 and 2.5 x 10-10
mg/cm /sec, respectively). Sodium efflux drops markedly in sodium-free
media, and chloride efflux falls in chloride-free media; the two effects
are independent and not due to changes in external osmolarity. De-
creases in Na efflux can be explained by changes in electrical potential
difference and diffusional permeability; exchange diffusion of sodium
does not occur.
Approximately 70% of the chloride efflux (22 x 10-13 M/sec)
is due to exchange diffusion (12 x 10-13 M/sec), while the remainder is
primarily due to active transport (9.0 x 10-13 M/sec). The plot of ion
efflux against external concentration, fitted by a Michaelis-Menten
equation, does not constitute evidence for presence of exchange diffu-
sion; graphs of similar shape can be obtained if flux is simply diffu-
sional. Drinking rate, determined from rate of uptake of I-13l-poly-
vinylpyrrolidone is 2.0% body wt/hr. or 20 ml/kg/hr. Diffusional
influx of water is 24 x 10-13 l/sec.
2098.
Solbe, J.F. de L.G. and V.A. Cooper. 1976. Studies on the
toxicity of copper sulphate to stone loach Noemacheilus
barbatulus (L.) in hard w.ater. Water Research 10:523-527.
The LC-50 (63 day) value of copper sulphate to N. barbatulus
was about 0.25 mg Cull in water of total hardness 249 mg/! as CaC03;
302
-------
larger fish survived longer. At concentrations >0.29 mg Cull, fish took
shelter less frequently during daylight hours. Noemachei1us surviving
0.12 mg Cull for 64 days depurated Cu when placed in clean water for 7
days: gill" muscle, eye and vertebrae lost significant amounts of Cu
during this period. Tissue levels of Cu, in mg/kg dry wt, in fish
killed by 0.76 mg Cull were 18 in eye, 164 in gill, 8 in muscle, 7 in
vertebrae and 115 in liver, compared to control levels of 19, 26, 5, 3
and 53, respectively.
2099.
Sorensen, E.M.B. 1976. Toxicity and accumulation of arsenic in
green sunfish, Lepomis cyanellus, exposed to arsenate in
water. Bull. Environ. Contarnin. Toxicol. 15:756-761.
Time for 50% death (LT-50) for green sunfish L. cyanel1us
immersed in 100, 500 or 1000 mg/l arsenic as sodium arsenate was 46, 17
and 12 hrs, respectively. When cumulative percent mortality was ob-
served against 3 size classes, no variation was observed in 500 and 1000
mg/l As levels. The smallest fish exposed to 100 mg/l As died at a more
rapid rate than the other 2 size classes. LT-50 values for small, inter-
mediate and large fish exposed to 100 mg/l As are 39, 55 and 73 hr,
respectively. LC-50 values for 12, 18, 24 and 48 hr were 1000, 350,
175 and 150 mg/l As, respectively. Arsenic accumulation increased with
increasing As exposure levels. Mean As accumulation was 33, 541, and
581 mg/kg for As exposure levels of 100, 500 and 1000 mg/l, respectively.
No correlation was observed with As accumulation and fish total length,
wet wt, dry wt, or condition.
2100.
Spaargaren, D.H. 1972. Osmoregulation in the prawns Palaemon
serratus and Lysmata seticaudata from the Bay of Naples.
Netherlands Jour. of Sea Res. 5:416-436.
Measurement of blood osmotic concentrations reveal P. serratus
to be strongly regulating and L. seticaudata to have a high degree of
osmoconforrnity. Both species were equally capable of regulating the
electrolyte concentrations in tissues; non-electrolyte concentrations
in cells followed changes in blood osmolarity. A strong influence of
temperature on osmotic concentrations of blood and homogenate of P.
serratus is evident; in blood this is due to changes in electrolyte
concentration; in homogenate by alteration of non-electrolyte concentra-
tion. In L. seticaudata, total osmotic concentrations are practically
independent of temperature. Urine excretion does not play an important
role in water and salt regulation of either species. Gross extra-renal
efflux of electrolytes is greatest at normal salinities for these species
Permeability is actively controlled, with decreases at supranormal
salinities. For both prawn species transfer to lower salinities results
within a few hours in decrease of blood concentrations. During this
303
-------
osmotic adaptation a strong increase of blood non-electrolytes occurs
within 10 minutes. These are probably liberated from the tissues.
Results are compared with osmoregulatory patterns and migrational be-
havior of two shrimps in the North Sea and the Wadden Sea, Crangon
crangon and C. allmanni, which have been indicated incapable of surviv-
ing high salTnities and temperatures to which Palaemon serratus and
Lysmata seticaudata are exposed in the Bay of Naples.
2101.
Spangler, W.J., J.L. Spigarelli, J.M. Rose, R.S. Flippin and
H.H. Miller. 1973. Degradation of methylmercury by bacteria
isolated from environmental samples. Appl. Microb. 25:488-
493.
Of 207 bacterial cultures isolated from fish and sediment from
Lake St. Clair, Michigan, 30 isolates were positive for aerobic demethyl-
ation without adaptation to methylmercury. Of the 30 positive isolates,
22 were facultative anaerobes, and 21 of these were capable of anaerobic
demethy1ation. Two of the isolates were gram-positive cocci, two gram-
positive rods, and the remainder gram-negative rods with characteristics
typical of Pseudomonas. Although methylmercury degradation was com-
plete in most cases, Some inorganic Hg formed was not volatilized and
is presumed bound to cells. All positive isolates were tolerant to at
least 0.5 ~g of methylmercury per ml with increasing volatilization at
increasing concentration until threshold value is reached. Results
indicate that demethYlating species are prevalent in the environment and
may be important in suppressing methylmercury content of sediments.
2102.
Spehar, R.L. 1976. Cadmium and zinc toxicity to flagfish,
Jordanel1a floridae. Jour. Fish. Res. Bd. Canada 33:1939-1945.
The LC-50 (96 hr) values for Cd to juvenile flagfish was
2,500 ~g/l; for Zn this was 1,500 ~g/l. In chronic tests, reproduction
was the most sensitive indicator of Cd toxicity and was inhibited at 8.1
~g/l. Fish exposed tc 1.7 ~g/l and above accumulated significantly
greater amounts of Cd than controls. In Zn tests, survival of larvae
(not exposed as embryos) and growth of females were the most sensitive
measure of Zn toxicity; these were reduced at respective concentrations
of 85 and 51 ~g/l. Significant uptake of Zn occurred in fish exposed
to 47 ~g/l and above. The lowest Cd and Zn concentrations causing ad-
verse effects to f1agfish were similar to those affecting other fresh-
water fish species.
2103.
Spinelli, J. and C. Mahnken. 1976. Effect of diets containing
dogfish (Squalus acanthias) meal on the mercury content and
304
-------
growth of pen-reared coho salmon (Oncorhynchus kisutch).
Jour. Fish. Res. Bd. Canada 33:1771-1778.
Use of dogfish meal containing 1.4 to 2.3 mg total Hg/kg,
including' 1.1 to 1.9 mg Hg/kg as methyl-Hg, as a complete replacement
for low Hg fish rations led to salmon muscle Hg levels ~0.5 mg/kg, the
U.S. FDA tolerance level, in 240 days. Muscle Hg levels did not rise
above 0.5 mg/kg when dogfish meal replaced <50% of fish meal portion.
Chelating agents in dehydrated orange peel or polygalacturonic acid-
cellulose complexes did not prevent deposition in either muscle or
liver tissues of salmon.
2104.
Stebbing, A.R.D. 1976. The effects of low metal levels on a
clonal hydroid. Jour. Mar. BioI. Assn. U.K. 56:977-994.
Concentrations, in ug/l, which depressed growth rate of the
colonial marine hydroid Campanularia flexuosa over an 11 day period
were: 1.6 to 1.7 for HgL~; 10 to 13 for CUL+; and 110 to 280 for Cd2+.
Growth stimulation was observed at 1 ug/l for Cu between days 7 and 11;
1 ug/l of Hg produced a similar effect between days 3 and 7.
2105.
Stenner, R.D. and G. Nickless. 1974. Absorption of cadmium,
copper and zinc by dog whelks in the Bristol Channel. Nature
247:198-199.
Mean metal levels in mg/kg dry flesh of whelks ~. lapillus,
transplanted from Beer, Dorset, to Bristol Channel rose from 36 to 211
for Cd, 70 to 170 for Cu and 345 to 2530 for Zn in 5 months. Levels
of local specimens in mg/kg dry flesh were 780 for Cd, 905 for Cu and
2900 for Zn. Limpets Patella sp. similarly transplanted showed a rise
of mean metal concentrations in mg/kg dry flesh of 11 to 220 for Cd,
7 to 30 for Cu, and 91 to 340 for Zn in 8 months.
2106.
Stenner, R.D. and G. Nickless. 1974. Distribution of some
heavy metals in organisms in Hardangerfjord and Skjerstad-
fjord, Norway. Water, Air, and Soil Poll. 3:279-291.
Near Adda, West Norway, metal-bearing waters enter the Sor-
fjord, a tributary of the Hardangerfjord. Unusually high concentrations
of Cd, Pb, and Zn are present in marine life over considerable length
of the fjord. Marine life near Adda also contained concentrations of
Hg higher than normal. At Fauske, North Norway, marine organisms con-
tain high concentrations of Cu, but this contamination is confined to a
small area of the Skjerstadfjord system.
305
-------
Highest metal concentrations for all organisms collected over
the entire region, in mg/kg dry wt, were:
Cd Cu Zn Pb ~ Ni Mn
-
Algae 20 170 2370 1200 1.2
Crustacea 8.8 94 275 31
Echinoderms 18 18 1500 460
Molluscs 140 190 2900 3100 0.6
Fish flesh 0.7 4 45 14 0.6
Sediments (mg/kg) 1.5 18 64 66
Water (ug/l) 85 77 3560 27 5.6 16.9
2107.
Stenner, R.D. and G. Nickless. 1975. Heavy metals in organisms
of the Atlantic coast of S.W. Spain and Portugal. Marine
Poll. Bull. 6:89-92.
Very high concentrations of copper, lead, zinc, and to a
lesser extent mercury, are present in the estuary of the Rio Tinto in
Southwest Spain. At the mouth of the estuary, concentrations fall very
sharply towards natural levels of these metals in organisms living in
this part of the Atlantic.
Highest values observed in mg metal/kg dry wt in flesh from
edible molluscs and crustaceans were: 32 for Cd, 205 for Cu, 516 for
Pb, 280 for Zn, and 0.03 for Hg. For fish flesh this was 3.2 for Cd,
8 for Cu, 7 for Pb, 132 for Zn, and 0.79 for Hg. Highest values re-
corded for cadmium in mg/kg dry wt were 7.4 for algae, 12.1 for barna-
cles, 16.0 for gastropods, 4.1 in sediments, and 6 (ng/l) for water.
For Cu, highest values recorded were 26 mg/kg dry wt in algae (except
Zostera which was 1350), 26 for molluscs, up to 600 in barnacles, up
to 1400 in sediments, and up to 107 (ng/l) in water. Highest Zn values
were 320 mg/kg dry wt for molluscs, 145 for algae (exception Zostera
1480), up to 3300 in barnacles, 3100 in sediments, and up to 525 (ng/l)
in water. For Pb, highest values determined were 22 for algae (except
Zostera which was 1800 mg/kg dry wt), up to 1600 in sediments, and up
to 38 (ng/l) in water. Highest Ni and Mn levels in water (ng/l) were
10.8 and 108, respectively.
2108.
Stephenson, R.R. and D. Taylor. 1975. The influence of EDTA on
the mortality and burrowing activity of the clam (Venerupis
decussata) exposed to sublethal concentrations of copper.
Bull. Environ. Contamin. Toxicol. 14(3):304-308.
Clams were exposed to copper concentrations (in mg/l) of 0.1
Cu, 0.01 Cu, 0.1 Cu plus 1.0 mg/l EDTA, and 0.01 Cu plus 1.0 mg/l EDTA
for 75 days; controls were exposed to seawater or seawater plus 1.0
306
-------
mg/l EDTA. The EDTA plus Cu group, and the controls exhibited about 2%
death. All Venerupis exposed to 0.1 mg/l Cu died within 50 days; the
0.01 mg/l Cu group had deaths between the 30th and 9lst days only.
Control populations and those exposed to EDTA showed no inhibition of
burrowing; but those exposed to copper alone showed a significant de-
cline. Normal burrowing was regained within 30 days when exposure to
0.01 mg/l Cu ceased.
2109.
Stevenson, R.A. and S.L. Ufret. 1966. Iron, manganese and
nickel in skeletons and food of the sea urchins Tripneustes
esculentus and Echinometra lucunter. Limnol. Oceanogr. 11(1):
11-17.
Levels of Fe, Ni, and Mn in skeletons of 2 species of sea
urchins from two collection sites were determined. Levels in mg/kg dry
wt of T. esculentus and E. lucunter from Punta Higuero, Puerto Rico,
were 81 and 38 for Fe, 14 and 21 for Mn, and 35 and 52 for Ni, respec-
tively. In urchins from La Parguera, PR, levels were 53 and 35 for Fe,
13 and 20 for Mn and 35 and 49 for Ni. For the marine angiosperm
Thalassia testudinum, the main food source of T. esculentus at La
Parguera, levels were 250, 49, and 20 mg/kg dry wt for Fe, Mn and Ni,
respectively. Padina gYIDnospora, the principle forage alga of !.
esculentus at Punta Higuero, contained 4100, 99 and 27 mg/kg dry wt of
Fe, Mn, and Ni, respectively, but these higher levels were not reflected
in urchin.
2110.
Stewart, J. and M. Schulz-Baldes. 1976. Long term lead
lation in abalone (Haliotis spp.) fed on lead-treated
algae (Egregia laevigata). Marine Biology 36:19-24.
accumu-
brown
The amount of lead accumulated in body of a grazing mollusc
by transfer from its algal food was assessed in laboratory experiments
and compared with amounts found in naturally occurring molluscs and
seaweed. Near La Jolla, California, where concentration of Pb in sea-
water is probably less than 0.08 ~g/l and most of the naturally occur-
ring Egregia laevigata contains less than 0.4 mg Pb/kg wet wt, the total
body masses without shells of juvenile abalone Haliotis rufescens fed
on this seaweed for 3 to 6 months showed similar concentrations. When
~. laevigata is placed for 1 to 6 days in seawater with a Pb concentra-
tion of 0.1 or 1.0 mg/l, both seaweed and abalone accumulate propor-
tionately larger amounts of Pb. After 6 months, young abalone fed on
~. laevigata pretreated with 1.0 mg Pb/l accumulated up to 21 mg Pb/kg
wet wt. This amount of Pb had no apparent consequences on growth or
activity of molluscs. Analyses of 6 different organs from adult abalone
showed that Pb was selectively concentrated in digestive gland. In the
307
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foot (muscle tissue), which is the part normally consumed by humans,
only negligible amounts were found.
2111.
Stickle, W.B. and T.W. Howey. 1975. Effects of tidal fluctua-
tions of salinity on hemolymph composition of the southern
oyster drill, Thais laemastoma. Marine Biology 33:309-322.
Amplitude of hemolymph osmolality and ion fluctuation in
oyster drills during laboratory simulated tidal fluctuations of,salinity
(30-10-300/00 S, 20-10-200/00 S, or 10-5-100/00 S) was directly related
to the amplitude of ambient salinity fluctuation and inversely related
to rate of fluctuation. Rate of hemolymph osmolality and ion change was
directly related to rate of ambient salinity change. Dilution of sea-
water with simulated Mississippi River water instead of deionized water
resulted in a reduced amplitude of fluctuation of hemolymph osmolality
and ion concentration. Most hemolymph osmolality fluctuation was due
to solute movement; less than 22% was due to shifts in body water.
Hemolymph, Na+and Cl- levels changed similarly throughout all experi-
ments except the 10-5-100/00 S-simulated river-water experiment in which
Cl- changed much less than Na. Hemolymph ninhydrin-positive substance
(NPS) levels cycled inversely with ambient salinity during 30-10-300/00
and 20-10-20%0 S diurnal and 30-10-300/00 semidiurnal experiments,
but did not change during 10-5-100/00 S deionized water or simulated
river-water experiment. Snails fed for most of the 2-week 20-10-20%0
S diurnal cycle fluctuation experiment and, with no deaths recorded.
Drills were hyperosmotic to ambient water at all but two isosmotic
sampling periods. Hemolymph NPS levels tended to be higher during low-
salinity slack water than high-salinity slack water. Even small fluc-
tuations of ambient salinity result in fluctuations of hemolymph
osmolality and ionic composition which may affect rate functions within
the zone of capacity adaptation.
2112.
Stickney, R.R., H.L. Windom, D.B. White and F.E. Taylor. 1975.
Heavy-metal concentrations in selected Georgia estuarine
organisms with comparative food-habit data. In Howell, F.G.,
J.B. Gentry and M.H. Smith (eds.). Mineral Cycling in
Southeastern Ecosystems. U.S. Energy Res. Dev. Admin.: 257-
267. Available as CONF-7405l3 from NTIS, U.S. Dept. Comm.,
Springfield, VA 22161.
Mean metal levels in mg/kg dry muscle of 11 species of
estuarine fishes ranged from 0.02 to 0.22 for Cd, 0.9 to 5.2 for Cu,
0.01 to 0.16 for Pb, 0.10 to 2.74 for Hg and 21 to 51 for Zn. Mean
metal levels in mg/kg dry tissue of various parts of 12 species of
crustacea which serve as food organisms, ranged from 0.01 to 0.40. for
Cd, 13 to 74 for Cu, 0.03 to 0.94 for Pb, 0.06 to 1.57 for Hg and 55 to
308
-------
290 for Zn. No positive correlation between metal levels and food
habits of fish existed, although high Hg levels in oyster toad fish
Opsanus ~ appeared to be associated with elevated Hg levels in crabs,
its major food source. Cu and Zn were commonly higher in invertebrates
than fish predators. Authors conclude that trace metal contents in
organisms of different trophic levels depend more on physiological
processes within each organism than on metal content of food.
2113.
Stiefel, R.C. 1974. Mercury as a factor in the fisheries enVl-
ronment. Ohio Dept. Natur. Res., Div. of Wildlife. 45 pp.
Analyses of total mercury concentration in 40 species of
freshwater fish from 195 locations throughout Ohio indicate that while
there is some mercury in nearly every fish tested, there are only a few
species of fishes from a limited number of locations throughout the
state that contain excessive concentrations of mercury. Only 128 of
the 1537 samples analyzed contained mercury in concentrations above
0.5 mg/kg; and fully one-third of these samples were collected from
one river basin and at one other location in the state. The species of
fishes that contain high mercury concentrations and the highest Hg level
found in them, are: longnose gar Lepisosteus osseus (1.10 mg/kg Hg);
northern pike Esox lucius (0.98 mg/kg); channel catfish Ictalurus punc-
tatus (0.93 mg?Kg); flathead catfish Pylodictis olivaris (1.04 mg/kg);
white bass Morone chrysops (1.52 mg/kg); rockbass Ambloplites rupastris
(1.33 mg/kg); smallmouth bass Micropterus dolomieut (1.00 mg/kg);
spotted bass ~. punctulatus (1.19 mg/kg); largemouth bass ~. salmoides
(1.00 mg/kg); and walleye Stizostedio~ vitreum (0.59 mg/kg). The
majority of these were greater than 25 cm in length and very high in
the food chain, with diets including the smaller species of fish. Based
on these results, it is concluded that mercury contamination is not a
serious problem in the fisheries environment in the State of Ohio.
2114.
Stiff, M.J. 1971. Copper/bicarbonate equilibria in solutions
of bicarbonate ion at concentrations similar to those found
in natural water. Water Research 5:171-176.
The equilibrium constant for reaction between cupric and
bicarbonate ions resulting in formation of the soluble complex species
CuC03' was determined by means of a cupric ion selective electrode. If
cupric ion were the toxic form of Cu, and copper carbonate complex was
relatively non-toxic, this could account for differences observed in
copper toxicity to fish in hard and soft waters. Differences in toxic-
ity would not be related to water hardness ~~ but to differences
in alkalinity which it accompanies.
309
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2115.
Stokes, P.M., T.C. Hutchinson and K. Krauter. 1973. Heavy-metal
tolerance in algae isolated from contaminated lakes near
Sudbury, Ontario. Canad. Jour. Bot. 51:2155-2168.
Algal isolates of Chlorella and Scenedesmus from two lakes in
the smelting region of Sudbury, Ontario, were the test species. Copper
and nickel content, in mgll, for the two lakes were Cu 0.52-0.74, and
Ni 2.7-3.2 in Baby Lake and Cu 0.10-0.13 and Ni 2.5 in Boucher Lake.
Growth, as determined by cell numbers was tested under control condi-
tions in defined media with nutrient conditions, pH, copper, and nickel
concentrations used as variables.
Lake Scenedesmus were especially metal tolerant. Cell division
was active at 0.4 mg Cull whereas the laboratory strain (control) was
killed at 0.1 mg Cull. Tolerance to Ni was more pronounced with con-
tinued growth at 1.5 mg Ni/l compared to 0.25 mg Ni/l for laboratory
strains. Lake Chlorella was less tolerant than lake Scenedesmus to Cu,
ceasing cell division at 0.15 mg Cull. Laboratory Chlorella died at
concentrations above 0.04 mg Cull. Pattern of response also differed
between lake isolates and lab strains in that the latter showed a thresh-
old effect, with inhibition and death above a certain critical metal
level, but little inhibition below this level. The lake strains showed
a gradual reduction in growth with increasing metal level. In cultures
that very high levels of Cu prevented cell division, cells of lake
strains were comparatively large and contents distorted, but these were
able to resume normal appearance and division in media containing less
Cu.
2116.
Strik, J.J.T.W.A., H.H. de Iongh, J.W.A. van Rijn van Alkemade
and T.P. Wuite. 1975. Toxicity of chromium (VI) in fish,
with special reference to organoweights, liver and plasma
enzyme activities, blood parameters and histological alter-
ations. In Koeman, J.H. and J.J.T.W.A. Strik (eds.). Sub-
lethal effects of toxic chemicals on aquatic animals.
Elsevier Sci. Publ. Co., Amsterdam: 31-41.
Rainbow trout Salmo gairdnerii, exposed to 10 mgll Cr+6 for
14-22 days, showed decreased activity and food intake after 5 days, with
25% mortality by the 15th day. Intestines of treated trout contained
swollen blood vessels. Chromium-treated trout when compared to con-
trols exhibited increased hematocrit, increased hemoglobin, decreased
blood Na+ content, a higher incidence of swollen salt cells and slime
cells, gill damage, and severe necrosis of kidney tubules.
Roach Rutilus rutilus (teleost) were exposed for 32 days to
0, 0.1, 1.0 or 10 mgll of Cr+b. Roach in 10 mgll group showed decreased
activity and food intake. There was no difference among groups in
weights of liver, kidney and gonad, or in various blood parameters
310
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(hematocrit, hemoglobin, RBC, WBC) or various liver homogenate enzymes
(glutamate-pyruvate-transaminase and glucose-6-phosphate-dehydrogenase).
Glutamate-oxaloacetate-transaminase activity in liver homogenate of
roach exposed to 10 mg/l decreased when compared to controls. Blood
glucose content of roach exposed to 10 mg Cr+6/l differed (P<0.005) from
1 mg Cr/l group and (P
-------
Oysters (n=50 per sample) from Whitstable collected in 1921
examined by the wet combustion process contained 3.5-3.7 mg As (as
AS406) kg wet wt; this is 2.5X the maximum limit suggested by the Royal
Commission on Arsenical Poisoning for arsenic in food substances
generally. On the other hand, more than 3 to 12 dozen oysters would
have to be consumed to exceed a (then) medicinal dose of arsenic.
Content of As, Zn, Pb, Cu, and Sn in healthy and diseased
oysters was determined. In general, As content was low or absent in
both groups, and this may be associated with the comparatively high
copper content of healthy oysters (up to 970 mg Cu/kg wet wt). Values
for Zn and Sn were as high as 1360 and 40 mg/kg wet wt, respectively;
Pb was never detectable in any samples. One sample of 53 oysters was
dark blue in color; on analysis these showed abnormally high levels of
Cu (3300 mg/kg wet wt), Zn (2100), and Sn (220)--or about 0.5% Zn and
Cu.
2119.
Stutzenberger, F.J. and E.O. Bennet. 1965. Sensitivity of mixed
populations of Staphylococcus aureus and Escherichia coli to
mercurials. Applied Microb. 13:570-574.
S. aureus exhibited higher resistance to merbromin and mer-
curic chloride in presence of E. coli. This protective effect was
attributed to production of extracellular glutathione and hydrogen sul-
fide and to an unequal distribution of inhibitor between the two species.
S. aureus did not significantly influence the resistance of E. coli to
mercurials. - -
2120.
Styron, C.E., T.M. Hagan, D.R. Campbell, J. Harvin, N.K. Whitten-
burg, G.A. Baughman, M.E. Bransford, W.H. Saunders, D.C.
Williams, C. Woodle, N.K. Dixon and C.R. McNeill. 1976.
Effects of temperature and salinity on growth and uptake of
Zn-65 and Cs-137 for six marine algae. Jour. Mar. BioI. Assn.
U.K. 56:13-20.
Population growth and concentration factors for Zn-65 and
Cs-137 have been measured for Achnanthes brevipes, Carteria sp.,
Chlamydomonas sp., Dunaliella salina, Nannochloris atomus, and Phaeo-
dactylum tricornutum subjected to factorial combinations of 8 tempera-
tures (6-40 C) and 10 salinities (3.5-44.00/00). Regression coeffi-
cients were calculated for pOlynomial models describing response sur-
faces for growth and radionuclide concentration. Salinity was more
important than temperature in describing population growth for Carteria,
Dunaliella, Nannochloris and Phaeodactylum. No independent variable was
consistently of primary importance in describing Cs-137 concentration
factors, while temperature accounted for more variation in Zn-65
312
-------
concentration factors than salinity or population growth in all algae
except Dunaliella. 'Concentration factors for Zn-65 were uniformly higher
than Cs-137 concentration factors.
2121.
Sugiura, K., S. Sato, M. Goto and Y. Kurihara. 1976. Toxicity
assessment using an aquatic microcosm. Chemosphere 5(2):113-
118.
Changes in freshwater community structure, productivity, and
respiration were analyzed following addition of Cu ions. The aquatic
microcosm consisted of 5 or more species of bacteria; the ciliate,
Cyclidium; rotifers, Philodina and Lepadella; a species of aquatic oligo-
chaete; green algae, Chlorella and Scenedesmus; and blue green algae.
When Cuwas added at beginning of cultivation, organism density differed
from controls at 0.3 mg/l. When added at a stationary stage (25th day)
effects on organism density were observed at 0.9 mg/l. Differences in
concentration at which decline in densities occur may be due to increased
output of bacterial metabolities, which form complexes with Cu ions.
These complexes inhibit growth and accelerate mortality of Cyclidium and
ChI orella to a greater extent than Cu ions alone. Gross production, total
respiration and net production measurements show that even when density
of organisms in the system are the same as controls, toxicity can be
assessed.
2122.
Sullivan, G. and A.L. Buikema, Jr. 1972.
on the toxicity of zinc sulfate to the
(Bdelloidea, Bdelloida, Philodinidae).
104.
The effect of hardness
rotifer Philodina sp.
The ASB Bull. 19(2):
Toxicity of zinc sulfate to Philodina sp.in water with a total
hardness of 280 mg/l produced an LC-50 (24 h) >100 mg/1 at pH 6.9 and
23 C. By contrast, toxicity of zinc sulfate in deionized water was con-
siderably greater; the LC-50 (24 h) being <1 mg/1 at pH 6.5 and 23 C.
2123.
Sullivan, G.W., A.L. Buikema and J. Cairns. 1973. Acute bio-
assays for the assessment of heavy metal pollution using the
freshwater littoral rotifer, Philodina sp. Virginia Jour. Sci.
24:120. (Abstract)
LC-50 (96 hr) values at 20 C for Philodina were in mg!l:
3.1 for K2Cr207, 0.1 for CdS04, 0.4 for CUS04, 0.7 for HgC12, 1.3 for
ZnS04, and 40.8 for PbC12'
313
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2124.
Summers, A.a. and E. Lewis. 1973. Volatilization of mercuric
chloride by mercury-resistant plasmid-bearing strains of
Escherichia coli, Staphylococcus aureus, and Pseudomonas
aeruginosa. Jour. Bact. 113:1070-1072.
Strains of E. coli, S. aureus and P. aeruginosa were examined
for ability to volatilize Hg-203 added as HgC12, and to convert added
Hg-203C12 to a chloroform soluble form. Strains carrying independently
isolated plasmids with genes determining resistance to Hg will convert
HgC12 to a volatile form of Hg which is soluble in organic solvents.
This form of Hg is very likely metallic Hg, rather than an alkyl mercury
compound.
2125.
Summers, A.a. and S. Silver. 1972. Mercury resistance in a
plasmid-bearing strain of Escherichia coli. J. Bacteriol.
112: 1228-1236.
A strain of E. coli carrying genes determining mercury resist-
- - 0
ance on a naturally occurring resistance transfer factor converts 95?o
of 10-5M Hg2+ (chloride) to metallic mercury at a rate of 4 to 5 nmoles
of Hg2+ per min per 108 cells. The metallic mercury is rapidly elimi-
nated from the culture medium as mercury vapor. Volatilizing activity is
temperature dependent, has a heat sensitivity characteristic of enzymatic
catalysis, and is inducible by mercuric chloride. Ag+ and Au3+ are
markedly inhibitory of mercury volatilization.
2126.
Sumner, A.K., J.G. Saha and Y.W. Lee. 1972. Mercury residues
in fish from Saskatchewan waters with and without known
sources of pollution - 1970. Pesticides Monit. Jour. 6:122-126.
Mercury concentrations in dorsal muscle from goldeye, longnose
sucker, pike, sauger, and perch taken from the Saskatchewan River system
ranged from 0.18 to 8.88 mg/kg wet wt. This river receives industrial
and municipal wastes containing Hg. Mercury levels were higher (0.18 to
8.88 mg/kg wet wt) in fish caught downstream from a chlor-alkali plant,
with highest average Hg concentration found in goldeye (2.05 mg/kg wet
wt) and pike (4.80 mg/kg wet wt) collected several kilometers downstream
from the chlor-alkali plant. Fish from an upstream site but contaminated
with municipal or other types of industrial wastes average 0.67 mg Hg/kg
wet wt. Levels in pike, perch, and walleye collected from four lakes
without any known source of Hg pollution ranged from 0.11 to 1.13 mg
Hg/kg wet wt. Authors suggest that these high Hg levels are probably
of natural origin and related to Hg content of sedimentary bedrock.
314
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2127.
Sunda, W. and R.R.L. Guillard. 1976. The relationship between
cupric ion activity and the toxicity of copper to phytoplankton.
Jour. Marine Res. 34(4):511-529.
Culture experiments with the estuarine diatom Thalassiosira
pseudonana in highly chelated seawater media demonstrate that growth rate
inhibition and copper content of cells are altered independently of total
copper concentration through varying chelator concentration and pH.
Cellular copper content of 3 to 4 day old cultures followed a hyperbolic
relation with cupric ion activity. Copper inhibited growth rate at acti-
vities above 0.002 ~g/cell, with growth ceasing at values above 0.32 ~g/
cell. However, the relation between growth rate inhibition and cupric
ion activity was not a simple hyperbolic function. In experiments with
the estuarine green alga Nannochloris atomus, growth rate inhibition also
was related to cupric ion activity with partial growth rate inhibition
occurring in the activity range 0.003 to 0.128 ~g/cell. Calculated esti-
mates of cupric ion activity in seawater indicate that natural activity
levels can be inhibitory to these phytoplankton depending on pH and the
degree of copper complexation by natural organic ligands.
2128.
Sutton, D.L., L.W. Weldon and R.D. Blackburn. 1970. Effect of
diquat on uptake of copper in aquatic plants. Weed Science
18:703-707.
Combinations of copper sulfate pentahydrate (CSP) at 1.0 mg/kg
dry wt Cu plus 0.1 to 2.0 mg/kg of the herbicide diquat resulted in
higher accumulations of Cu in hydrilla (Hydrilla verticillata), egeria
(Egeria densa) and southern naiad (Najas guadalupensis) when compared to
plants receiving CSP only. Contact period greater than 24 hr was neces-
sary before highest amounts of Cu were detected in plants treated with
CSP and diquat. Water samples taken from outdoor plastic pools, 7 days
after treatment with CSP at 1.0 mg Cu/kg dry wt, plus 1.0 mg/kg dry wt
of diquat, contained 25% less Cu than pools treated with Cu alone.
Samples of hydrilla and southern naiad removed 7 days after treatment
with CSP and diquat contained 77 and 38% more Cu, respectively, than
samples treated with CSP alone.
2129.
Svansson, A. 1975. Physical and chemical oceanography of the
Skagerrak and the Kattegat. I. Open sea conditions. Fishery
Bd. of Sweden, Institute of Marine Research, Goteborg, Sweden,
Rept. No.1. 88 pp.
Mercury concentrations, (y) in mg/kg wet wt, are given in rela-
tion to fish wt, (x) in kg; for herring it was y ; 0.22 x+ 0.023;
flounder y = 0.073 x+ 0.06; plaice y = 0.063 x+ 0.050 for North Sea, but
0.025 mg/kg lower for the Kattegat; porbeagle Lamna nasus, y = 0.05 x, and
315
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cod y = 0.025 x+ 0.17. Concentrations (in ~g/kg wet wt) of cadmium
ranged from 0.02 to 0.5; lead O.l.to 3.0; zlnc.3 to 17; and copper 0.6
to 3.6; zinc and copper values, glven for herrlng, were somewhat lower
than those for cod and plaice.
2130.
Swader, J.A. and W.-Y. Chan. 1975. Citric acid enhancement of
copper solubility and toxicity in bicarbonate solutions.
Pesticide Biochem. Physiol. 5:405-411.
Toxicity of cupric ions to algal growth during the first 2 days
of incubation was increased by the presence of citric acid in the growth
medium (number of cells decreased from 1.27 x 10-6 ml with CuS04 to 1.12
x 10-6 ml with CUS04 plus citric acid). No adverse effects of citric
acid on cupric sulfate as an algicide were detected. Sulfhydryls were
oxidized in presence of cupric ions to disulfides with one mole of oxygen
taken up for every 4 moles sulfhydryls oxidized. In bicarbonate solu-
tions, this reaction was stimulated by addition of citric acid. Citric
acid influence on copper sOlubility and cupric ion toxicity was not due
to a pH effect.
2131.
Swain, R. and P.S. Lake. 1974. The fenestra dorsalis of Allana-
spides (Crustacea: Syncarida)--cytological changes in response
to elevated NaCl levels. 8th Internat. Congress on Electron
Microscopy. Canberra, Australia, Vol. 11:246-247.
Changes in transport tissue of a fresh water crustacea were
studied by transferring animals from natural water (Na = 0.17 meq/l) to
similar water with added NaCl (Na = 4.36 meq/l), and observing changes
in fenestra dorsalis after 1, 5, 10, 20, and 30 days. Final condition
after 30 days is a pronounced reduction in surface area of both apical
and basal transport systems and a much less efficient arrangement for
water/ion movement.
2132.
Sykora, J.L., E.J. Smith, M.A. Shapiro and M. Synak. 1972.
Chronic effect of ferric hydroxide on certain species of
aquatic animals. 4th Symposium on Coal Mine Drainage Research,
Mellon Institute, Apr. 26-27, 1972, Pittsburgh, Penna.: 347-
369.
Growth data of juvenile brook trout Salvelinus fontinalis kept
for a full generation in 50, 25, 12, 6 mg Fe/l and control, showed a
definite trend toward slower growth with increasing concentration of
suspended ferric hydroxide; growth was greatest in the 6 mg Fe/l group
and controls. Brook trout egg production decreased at high iron concen-
trations. This may reflect the importance of Fe as an inorganic nutrient,
316
-------
although at high levels excessive turbidity occurs which impairs visi-
bility and feeding.
Fathead minnows Pimephales promelas were tested one year in
concentrations of 50, 25, 12, 6, 3, 1.5 mg Fe/I, and control; these
showed a decrease in growth and increase in mortality with increasing
concentrations of Fe. Mortality was highest in 50 mg Fe/l (exceeding
50%) and also high in 25 and 12 mg Fe/I. The highest concentration of
suspended iron which does not seem to affect survival and growth of
fathead minnows was <12 mg Fe/I. However; spawning took place in 25
mg Fe/I, as well as in 1.5 mg Fe/I. Except for control and 50 mg Fe/I,
on which there was no apparent effect, hatchability decreased as sus-
pended Fe concentration decreased, with a 50% rise from 1.5 mg Fe/l to
control. The only significant variable is the size of ferric hydroxide
particles. Generally, the number of smaller particles decreases with
higher concentrations. Smaller particles in low concentrations of sus-
pended Fe may have clogged egg pores, resulting in low hatchability.
Gammarus minus (amphipod) and Cheumatopsyche (caddisfly)
larvae were tested in the following two sets of concentrations: 100,
50,25, 12,6, 3 and 20, 10,5,2.5, 1.75,0.80 mg Fe/I. Tests con-
ducted with invertebrates show low susceptibility of Cheumatopsyche
larvae to suspended ferric hydroxide, with adults emerging at the highest
concentration tested of 20 mg Fe/I. Studies on Gammarus minus show a
higher toxic effect of ferric hydroxide, especially to younger animals.
The safe concentration for reproduction and growth of this species seems
to be <3 mg Fe/I.
Results suggest that suspended iron produces high turbidities
at high concentrations which interferes with feeding of teleosts and
that low concentrations exert deleterious effects on the more sus-
ceptible eggs and hatched fry.
2133.
Sykora, J.L., E.J. Smith, M. Synak and M.A. Shapiro. 1975. Some
observations on spawning of brook trout (Salvelinus fontinalis,
Mitchell) in lime neutralized iron hydroxide suspensions.
Water Research 9:451-458.
Long-term effect of lime neutralized suspended iron at concen-
trations of 50, 25, 12, 6, 3, and a mg Fe/Ion brook trout growth, sur-
vival, spawning, fecundity, and egg viability were assessed. Results of
a 2 year study show low survival of maturing fish at concentration of
>12 mg Fe/l and a decline in egg production at >12 mg/l due mainly to
high winter mortality (40%) prior to spawning. Egg hatchability was un-
affected at concentrations between 0.75 and 12 mg Fe/I. Safe levels of
lime neutralized iron hydroxide suspensions for brook trout in an en-
closed, intermittent-flow testing system lie between 7.5 and 12.5 mg
Fe/I.
317
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2134.
Tagatz, M.E. 1971. Osmoregulatory ability of blue crabs in
different temperature-salinity combinations. Chesapeake Sci.
12(1):14-17.
At salinities of 1.7, 17 and 340/00 and temperatures of 10, 20
and 30 C, salinity alone and salinity-temperature interactions affected
total osmotic concentrations of blood for all life stages of blue crab;
temperature alone did not affect response parameters. Ovigerous females
did not regulate as well as mature females or adult males at 1.7 or
170/00 salinities. At almost all temperature-salinity combinations,
however, differences in osmoregulatory ability of adult males and mature
females were not significant. Differences in osmoregulatory capabilities
are probably related to differences in distribution of lifestages and
sexes.
2135.
Talbot, V.W., R.J. Magee and M. Hussain. 1976. Cadmium in Port
Phillip Bay mussels. Marine Poll. Bull. 7(5):84-86.
Cadmium levels, in mg/kg dry wt, ranged from 2 to 63 for
mussels Mytilus edulis, and 36 to 174 for oysters Ostreidae angasi.
Some values were in excess of the approximately 10 mg/kg dry wt (2 mg/kg
wet wt) standard set by the Australian National Health and Medical Re-
search Council.
2136.
Tartar, V. 1957. Reactions of Stentor coeruleus to certain
substances added to the medium. Experim. Cell Res. 13:317-332.
The comparatively large protozoan ciliate S. coeruleus reacts
in specific and selective ways to compounds of sodium, lithium, mag-
nesium, calcium, potassium and other chemicals. The major finding was
that every chemical tested except ethyl alcohol caused stentors to shed
the peristome within 20 minutes either in solution or upon return to
culture fluid. Only in the case of ammonium acetate and NiS04 did all
the animals, which cast off the peristome, fail to recover from treat-
ment and regenerate a new set of feeding organelles when returned to
normal medium. The effect was not attributable to ionic, viscosity,
osmotic, or hydrogen ion effects.
2137.
Taylor, D.O. and T.J. Bright. 1973. The distribution of heavy
metals in reef-dwelling groupers in the Gulf of Mexico and
Bahama Islands. Rept. TAMU-SG-73-208, Dept. Ocean., Texas
A&M University, College Sta., Texas. 249 pp.
Groupers of family Serranidae from the Gulf of Mexico and
Carribean were analyzed for Hg, As, Cd, Pb, Cu, and Zn. Mean muscle
318
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concentration of Hg, in mg/kg wet wt, ranged from 0.15 to 0.81 in
Epinephalus striatus, 0.17 to 0.38 in Mycteroperca tigris, 0.41 to 0.60
in E. cruentatus, and 0.13 to 0.50 in M. phenax. For As these were 9.09
for-~. striatus, 1.66 for M. tigris, 1~82 for ~. phenax, and 1.36 for
E. guttatus; for Cd these were 0.02 for E. striatus, 0.02 for M. tigris,
0.018 for M. phenax, and 0.024 for ~. guttatus. Mean muscle concentra-
tions of Pb (Cu) were 0.09 (0.31) for E. striatus, 0.06 (0.25) for M.
tigris, 0.152 for ~. guttatus, and 0.29 (0.23) for ~. phenax. Mean-
muscle concentrations for Zn were 4.03 for E. striatus, 3.70 for M.
tigris, and 3.17 for M. phenax. Correlation between concentrations of
heavy metals and growth factors indicated differences between members of
same species as well as interspecific differences. Hg and Zn increase
with age and size in certain groupers where As shows no correlation.
Interspecific differences reflect possible variations in feeding habits
and metabolism; therefore, extrapolation from one species to another is
invalid as is lumping species to represent a trophic level. High levels
of arsenic in reef organisms which include crustacea, mollusks, echino-
derms, polychaetes, porifera, algae, and other fish, appear to be related
to substitution of arsenate for phosphate in biological systems. It is
suggested that low phosphate reef waters can produce high magnification
of arsenic by reef organisms.
2138.
Templeton, W.L. and V.M. Brown. 1964. The relationship between
the concentrations of calcium, strontium and strontium-90 in
wild brown trout, Salmo trutta L. and the concentrations of the
stable elements in some waters of the United Kingdom, and the
implications in radiological health studies. Int. Jour. Air
Water Poll. 8:49-75.
Respective Ca (Sr) concentrations in g/kg wet wt of trout
tissues ranged from 45 to 80 (0.03 to 0.47) for bone; and 0.042 to 0.29
(0.00006 to 0.001) for muscle. Ca levels in bone and muscle were inde-
pendent of water content while tissues levels were inversely related to
Sr and Ca concentrations of water. In both bone and muscle, discrimina-
tion against Sr relative to Ca occurred. Trout and other species of
freshwater fish contained 0.04 to 2.87 atoms Sr per 1000 atoms Ca.
Aquatic higher plants (algae) had atoms Sr/lOOO atoms Ca ratios of 0.66
to 5.2 (0.41 to 1.9). Sr/Ca ratio in fish and plants reflected Sr/Ca
ratio of water. Accumulation factors for Sr in brown trout ranged from
3.2 x 104 in bone and 80 in muscle for waters of low Ca concentration,
to 280 in bone and 1.0 in muscle tissue in high Ca waters. For Sr-90,
degree of accumulation and relationship with Ca concentration of water
is comparable with that of stable Sr.
2139.
Thibaud, Y. 1971. Teneur en mercure dans quelques poissons de
consommation courante. Sciences et Peche, Bull. Inst. Peches
marit. 209:1-10.
319
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Total mercury, in mg/kg wet flesh, was determined for various
species of edible marine teleosts. Values were, in general, well below
0.33 mg/kg. However, some albacore tuna Neothunnus albaco:a contained
up to 1.80 mg Hg/kg in white muscle, and up to 2.11 mg/kg In red muscle.
2140.
Thibaud, J.
francais.
1973. Teneur en mercure dans les moules du littoral
Science et Peche, Bull. Inst. Peches marit. 221:1-6.
Two species of mussels, Mytilus edulis
collected from various stations along the entire
December 1971 and October 1972 contained between
mercury per kg wet wt.
and ~. galloprovincialis,
French coast between
0.02 and 0.31 mg total
2141.
Thomas, A. 1915. Effects of certain metallic salts upon fishes.
Trans. Amer. Fish. Soc. 44:120-124.
After 48 hr in 30 mg Cull as CUS04, killifish Fundulus hetero-
clitus contained 0.0035% Cu on a dry wt basis; all fish died by 96 hr.
CuClz was more toxic than CUS04 in a similar period. Tests with nickel
chloride, ferric-ammonium-citrate and potassium dichromate showed that
none were toxic at the highest concentration examined of 200 mg/l.
Cobalt chloride, manganese chloride and zinc sulphate were also non-toxic
at these levels, but mercuric chloride, cadmium nitrate and sodium arse-
nate were fatal at this concentration. Fundulus were present in an
isolated nearly-freshwater pond which received salt water only during
storms every two or three years. These fish were more sensitive to
metals: mortalities occurred within 12 hrs at 3 mg/l lead nitrate; with-
in 36 hrs at 14 mg/l aluminum sulphate; and within 5 days at 7 mg/l
aluminum sulphate. Zinc sulphate was fatal within 48 hrs at 10 mg/l,
but was non-toxic in seawater. Copper sulphate was fatal within 10 hrs
at 4 mg/l; cadmium nitrate within 36 hr at 6 mg/l; nickel and cobalt
chloride were lethal within 5 days at 16 mg/l and manganese chloride
lethal in 6 days at 12 mg/l.
2142.
Thomas, A.E. 1975. Marking channel catfish with silver nitrate.
Prog. Fish-Cult. 37(4):250-252.
A preparation of 75% silver nitrate and 25%
was used to mark channel catfish Ictalurus punctatus.
from cauterization of skin by caustic action of Ag N03
permanent. KN03 sterilizes the mark area and prevents
potassium nitrate
A pale mark results
and is relatively
infection.
2143.
Thomas, W.H. and A.N. Dodson.
synthesis by germanic acid:
1974. Inhibition of diatom photo-
separation of diatom productivity
320
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from total marlne primary productivity.
11-19.
Marine Biology 27:
Germanic acid inhibited photosynthetic 14C02 uptake in marine
diatoms, but inhibition was incomplete at concentrations of 20 mg Ge/l
during 24 hr incubation. The decrease in photosynthesis due to Ge(OH)4
was independent of growth stage of the culture. At 0.5 and 1.0 mg Ge/l,
degree of inhibition was dependent on concentration of Si(OH)4 in the
medium. At 5 and 10 mg Ge/l, inhibition was not affected by Si(OH)4
concentrations as high as those found in the sea (120 ~g-atoms Sill).
The effect of Ge(OH)4 on photosynthesis is specific for diatoms; other
marine phytoplankters were not inhibited. In mixed cultures of diatoms
and marine flagellates, the reduction in 14C02 fixation upon addition of
Ge(OH)4 was used to calculate proportion of diatom photosynthesis to
total photosynthesis; calculated proportions agreed well with actual pro-
portions. Inhibition by Ge(OH)4 was also used to estimate percent of
diatom photosynthesis in a natural marine community, and this was compared
with the diatom portion of the crop. Diatom photosynthesis was higher
than expected from crop figures, although both diatom photosynthesis and
diatom numbers were low.
2144.
Thompson, J.A.J., J.C. Davis and R.E. Drew. 1976. Toxicity,
uptake and survey studies of boron in the marine environment.
Water Research 10:869-875.
Little is known about toxicity and biomagnification to aquatic
life posed by borate discharges from British Columbia ground wood pulp
mills. Bioassays with underyearling coho salmon Onchorhynchus kisutch
produced LC-50 (283 h) values of boron, as sodium metaborate, of 113.0
and 12.2 mg/l in fresh and saltwater, respectively. The disparity
between freshwater and saltwater boron toxicity to coho is not under-
stood at this time. Average B levels, in mg/kg wet wt, of sockeye salmon
O. nerka in normal seawater were 0.6 for gills, 0.7 for liver; 0.6 for
kidney, 0.5 for muscle and 1.5 for bone. After 3 weeks exposure of sock-
eyes to 10 mg B/l, tissue levels in mg B/kg wet wt were 5.6 for gills,
5.2 for liver, 7.3 for kidney, 3.8 for muscle, and 10.5 for bone. Oysters
show no bioaccumulative potential or prolonged retention of boron follow-
ing cessation of dosage. Mean B levels in mg/kg wet wt of various
British Columbia marine bivalves, were: 3.8 for butter clam Saxidomus
giganteus; 2.3 for little neck clams Protothaca staminea and Venerupis
japonica; 3.5 for oysters Ostrea lurida and Crassostrea gigas; 3.0 for
razor clam Siliqua patula; 4.5 for mussel Mytilus californianus; 3.5 for
bay mussel M. edulis; 2.0 for cockle Clinocardium nuttalli; 3.0 for clam
Mya arenaria; 1.6 for horse clam Schizothoerus capax; 1.3 for octopus
Polypus bimaculatus; and 1.8 for crab Cancer magister.
Authors aver that at the present level of industrial discharge
of boron (~l mg B/l) there is no hazard to salmonoids or oysters.
321
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2145.
Thompson, T.G. and T.J. Chow. 1955. The strontium-calcium atom
ratio in carbonate-secreting marine organisms. Deep-Sea
Research 3(Suppl):20-39.
Strontium and calcium levels in 250 species of carbonate-
secreting marine organisms including algae, protozoa, porifera, coelen-
terata, platyhelminthes, annelida, phoronidea, crustacea, mollusca, bryo-
zoa, brachiopoda, echinodermata, and tunicata were determined. Sr-Ca
atom ratio in calcareous portions ranged from 1.0 to 11 x 10-3. With the
exception of nudibranchs and corals, the atom ratio in marine organisms
was less than seawater (8.9 x 10-3). Sr-Ca atom ratios in marine organ-
isms appeared to be constant in accordance with their phylogenetic
classification. Similar types of marine organisms living under differ-
ent environmental conditions from arctic to tropical oceans, showed con-
stant Sr-Ca atom ratios. Variations in salinity and temperature of sea-
water apparently did not influence the Sr-Ca atom ratio in calcareous
shells.
Mineralogical properties of calcium carbonate in marine organ-
isms demonstrated a definite correlation with occurrence of Sr. Marine
organisms containing calcium carbonate as aragonite had Sr-Ca atom ratios
greater than calcite. Samples of deep-sea sediments and Globigerina
ooze showed Sr-Ca atom ratios of 1.94 x 10-3 and 1.49 x 10-j, respectively.
Limestone depo~its which ori~inated from ma:ine orga~isms had smallest
Sr-Ca atom ratlo (0.63 x 10- ) of all materlals examlned. Apparently,
matrix of calcareous deposits of marine origin has lost Sr during geo-
logical time.
2146.
Thomson, A.J., J.R. Sargent and J.M. Owen. 1975. Effect of
environmental changes on the lipid composition and (Na++K+)-
dependent adenosine triphosphate in the gills of the eel,
Anguilla anguilla. Biochem. Soc. Trans. 3:668.
Changes in lipid unsaturation and Arrhenius-plot discontinuity
+ +
of (Na +K )-dependent ATPase appear to result from changes in tempera-
ture but not salinity during migration of eels from fresh to seawater.
2147.
Thorp, V.J. and P.S. Lake. 1973. Pollution of a Tasmanian river
by mine effluents. II Distribution of macroinvertebrates.
Int. Revue ges. Hydrobiol. 58:885-892.
The distribution and abundance of macroinvertebrates were
studied in the South Esk River, Tasmania, which was impacted by cadmium
and zinc wastes from mining operations. Groups most intolerant of Cd-Zn
pollution were the crustacea, mollusca and annelida. Highly tolerant
groups included aquatic hemiptera and arachnida, and larvae of leptocerid
322
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trichopterans. A drop in species diversity and biomass occurred after
floods in winter; this may be due to pulses of cadmium and zinc dis-
charged into the river and to increased molar action of the unstable
substrate. One station at which no living organisms were found in
summer or winter exhibited anomalously high levels of zinc (3.52 8.0
mg/l), cadmium (0.24 - 0.44 mg/l), copper (0.04 - 0.12 mg/l), manganese
(0.97 - 4.7 mg/l), potassium (1.5 - 1.85 mg/l), calcium (6.0 17.6 mg/l),
and magnesium (5.14 - 13.9 mg/l).
2148.
Thrower, 8.J. and I.J. Eustace. 1973. Heavy metal accumulation
in oysters grown in Tasmanian waters. Food Tech. in Australia
25:546-553.
Abnormally high concentrations of zinc, cadmium, and copper
were found in oysters Crassostrea gigas and Ostrea angasi grown in the
Derwent and Tamar Estuaries. Individual oysters contained concentrations
of zinc, cadmium, and copper as high as 21,000, 63, and 450 mg/kg wet wt,
respectively. High concentrations of Zn and Cd in oysters from an area
in the Derwent Estuary probably caused symptoms of nausea and vomiting
experienced by some people after eating them. Oysters growing in areas
where heavy metal pollution was expected to be minimal, showed levels of
accumulation of zinc, cadmium, and copper up to 4000, 7.8, and 100 mg/kg
wet wt, respectively. These were similar to levels reported from other
parts of the world. None of the oysters examined complied with current
food regulations (viz 40 mg/kg wet wt for Zn, 5.5 for Cd, and 30 for Cu).
2149.
Thrower, 8.J. and I.J. Eustace. 1973. Heavy metals in Tasmanian
oysters in 1972. Austral. Fisher. 32(Oct. 1973):7-10.
Oysters accumulate certain toxic heavy metals if traces of
these are present in surrounding waters; sites for commercial leases must
be chosen with a full awareness of this possiblity. An exploratory
survey of oysters from Tasmanian waters demonstrated unusual concentra-
tions of cadmium, copper, and zinc in some oysters taken from leases
close to Hobart and Launceston. Highest concentrations of Cu, Cd, and
Zn determined in Tasmanian oysters were 123, 19, and 7670 mg/kg wet wt,
respectively. The upper limits permitted by Tasmanian food regulations
are, on a mg/kg wet wt basis, 30 for Cu, 5.5 for Cd, and 40 for Zn.
2150.
Thurberg, F.P" W.D. Cable, M.A. Dawson, J.R. MacInnes and D.R.
Wenzloff. 1975. Respiratory response of larval, juvenile
and adult surf clams, 8pisula solidissima, to silver. ~
Cech, J.J., Jr., D.W. Bridges and D.B. Horton (eds.). Respir-
ation of Marine Organisms. TRIGOM Publ. S. Portland, Me.:
41-52.
323
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Respiratory response of various life stages of surf clams
during exposure to sublethal concentratios of silver (0.005 to 0.100
mg/l) was measured. When larvae reached length of 150 ~, those exposed
to 0.05 mg Ag/l respired at rate of 12.5 ~1 02/hr/1000 larvae; control
value was 9.4. Juveniles respired at a significantly higher rate than
controls at 0.010 and 0.020 mg Ag/1, but not at 0.005 mg Ag/1. Adults
respired significantly higher than controls at 0.050 and 0.100 mg Ag/1
but not at 0.010 mg Ag/1. Mean silver concentration, in mg/kg wet wt,
for clam body minus gills was 0.0£ for controls, 1.01 for the 0.010 mg
Ag/1 group, 2.23 for 0.050 mg Ag/1 and 2.00 for 0.100 mg Ag/1. For
gills, mean Ag concentration in mg/kg wet wt was <0.63 for controls,
5.73 for 0.010 mg Ag/1, 8.72 for 0.050 mg Ag/1, and 8.52 for 0.100 mg
Ag/1. Valve movements of 8 control clams and 8 clams during exposure
for 96 hrs to 0.050 mg Ag/1 were recorded: exposed animals averaged
24.6 movements or partial closures per hour, while controls averaged
12.0.
2151.
Thurberg, F.P., A. Calabrese and M.A. Dawson. 1974. Effects of
silver on oxygen consumption of bivalves at various salinities.
In Vernberg, F.J. and W.B. Vernberg (eds.). Pollution and
Physiology of Marine Organisms. Academic Press, New York:
67-78.
Oxygen consumption of American oysters Crassostrea virginica
at 25 and 150/00 salinity was 1.1 and 1.15 ~l 02/hr/mg, respectively.
This increased to 1.3 and 1.7 ~l 02/hr/mg during exposure for 96 hrs to
1.0 mg silver/I; silver did not affect 02 consumption at 350/00. Oxygen
consumption rates of quahaugs Mercenaria mercenaria, held at 25 and
350/00 salinity increased from 1.2 to 1.6 ~1 02/hr/mg during exposure to
1.0 mg Ag/l for 96 hrs; silver did not affect oxygen consumption rate
of quahaug held at 15%0. Mussels Mytilus edulis exhibited increases
from 1.2 and 1.8 to 2.0 and 3.0 ~l 02/hr/mg at salinities of 25 and
15%0, respectively, during exposure to 1.0 mg Ag/1 for 96 hrs. At 25
and 35%0 salinities, soft-shelled clams Mya arenaria died at 1.0 mg
Ag/1; Mya held at 15%0 increased respiration rates from 1.6 to 3.2 ~l
02/hr/mg upon identical Ag addition. Ag concentrations of 0.1 mg/l
increased consumption rates for all species showing significant rate
changes at 1.0 mg Ag/l.
Lamellibranchs collected within 1.6 km of Milford Harbor, Con-
necticut showed the following Ag concentrations in mg/kg wet wt: 6.1 in
body, 5.9 in gills of ~. virginica; 0.4 in body, 1.6 in gills of M.
mercenaria; 0.2 in whole M. edu1is; and 0.3 in whole M. arenaria.- Dur-
ing 96 hr exposure to 1.0-mg Ag/l, silver content increased to 14.9 in
body and 33:9 in gills of ~. virginica; 1.0 in body and 6.9 in gills of
~. mercenarla; and 5.2 in whole M. edu1is.
324
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2152.
Tingle, L.E., W.A. Pavlat and LL. Cameron. 1973. Sublethal
cytotoxic effects of mercuric chloride on the ciliate Tetra-
hymena pyriformis. Jour. Protozool. 20(2):301-304.
Behavior and ultrastructure of !. pyriformis was assessed
after exposure to dosages of 0.25 mg/l and 0.50 mg/l HgC12, which is 8
and 16% respectively of the LC-50 (96 hr) concentration. The lower
dosage caused no abnormal changes in cell motility, contractile vacuole
activity or cell shape. Higher dosage caused reduced cell motility and
increased activity of contractile vacuole. Seventy-five percent of
cells in higher dosage had swollen and distorted mitochondria; 70% had
membraneous swirls inside the outer membrane of pellicle; macronucleus
had condensed chromatin, with chromatin bodies moved or displaced from
nuclear envelope. At the lower HgC12 dosage, extensive changes involv-
ing mitochondria occurred after I-hr exposure; these were repaired after
24 hrs of exposure indicating adaption to toxicant. Authors attempt to
apply findings and cytotoxic evidence to define a "safe" concentration
of HgC12.
2153.
Tolkach, V.V., V.V. Gromov and V.I. Spitsyn. 1975. An investi-
gation of absorption of 137Cs by krill. Doklady BioI. Sci.
Proc. Acad. Sci. USSR 220:11-13.
From 15 to 20% of Cs-137 (initial dosage 1 m Ci) was absorbed
in 1.5 days by these Antarctic crustaceans when added to 8.6 to 30.9 g
krill/l of seawater. Mean coefficient of accumulation for small krill
was 324 per wt of heat-dried krill and 9 per dry wt; for large krill it
was 103 per wt of heat-dried krill and S per dry wt. Cs-137 entrapment
was proportional to volume of krill alimentary organs.
2154.
Tompkins, T. and D.W. Blinn. 1976. The effect of mercury on the
growth rate of Fragilaria crotonensis Kitton and Asterionella
formosa Hass. Hydrobiologia 49:111-116.
Effects of Hg (N03)2 and HgClz on two species of freshwater
planktonic diatoms showed that growth of Fragilaria was totally inhibited
at 0.1 mg/l and that a 4 day increase in lag phase occurred together
with a 2-4X reduction in growth rate at 0.05 mg/l. Asterionella showed
a gradual increase in lag phase and reduction in growth rate with in-
creasing concentrations of Hg up to 0.25 mg/l. Asterionella growth was
totally inhibited at 0.5 mg/l. Hg salts in cultures of both species
with soil extract additives were significantly less toxic. Cultures of
~. formosa deviated from the typical 8-16 celled stellate colony at sub-
lethal concentrations to form large cylindrical stacks composed of 25 to
30 colonies.
325
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2155.
Tonomura, K., K. Maeda, F. Futai, T. Nakagami and M. Yamada.
1968. Stimulative vaporization of phenylmercuric acetate by
mercury-resistant bacteria. Nature, London 217:644-646.
An experiment was conducted in which a large amount of phenyl-
mercuric acetate (PMA) was absorbed by mercury-resistant bacteria.
Using Hg-203 labelled PMA, it was found that cell-bound radioactivity
disappeared rapidly from culture before onset of growth. Free PMA
rarely disappeared from solution under the same conditions. When organ-
isms were incubated directly with Hg-203 labelled PMA, disappearance of
radioactivity from the culture was also observed. PMA may be bound to
bacterial surfaces and then biologically stimulated to initiate vaporiza-
tion of Hg. Vaporization was not stimulated by heated cells, disrupted
cells or cells treated with acetone or toluene. Vaporization was
inhibited at PMA concentrations greater than 150 mg!l and enhanced by
cells pre-incubated with PMA. Authors suggest two mechanisms of vapor-
ization. One in which it is stimulated by a gaseous substance evolved
from bacterial surface on which PMA is bound. The second is a chemical
conversion of PMA to a substance more volatile than P~~.
2156.
Topping, G. 1973. Heavy metals in shellfish from Scottish waters.
Aquaculture 1:379-384.
Concentrations of Cu, Zn, Pb and Cd in edible tissues of
shellfish taken from Scottish coastal waters were determined. Lead in
mg metal per kg wet wt ranged from <0.2 to 5.5 in mussel Mytilus edulis;
<0.1 to 2.8 in periwinkle Littorina littorea; <0.1 to 1.0 in scallop
Pecten maximus; <0.2 to 0.5 in spiny lobster Nephrops norvegicus; <0.4
in lobster Homarus vulgaris; and <0.8 in crab Cancer pagurus. Cadmium
ranged from 0.1 to 2.0 in mussel, 0.03 to 0.05 in periwinkle, 5.1 to
23.0 in scallop, <0.03 to 0.1 in spiny lobster; <0.03 to 0.09 in lobster
and 3.6 to 13.0 in crab; highest values were in kidney and liver of
scallop, lobster and crab. Copper ranged from 0.5 to 5.0 in mussel, 6.2
to 20.0 in periwinkle, 0.4 to 0.9 in scallop, 2.1 to 11.3 in spiny lobster,
6.2 to 13.2 in lobster and 8.0 to 125.0 in crab; highest Cu values were
in kidney and liver of individual shellfish. Zinc was lowest in spiny
lobster at 8.5 to 12.2 and highest in crab at 21.3 to 34.5. Zinc ranged
from 12.5 to 82.5 in mussel, 6.6 to 20.2 in periwinkle, 19.1 to 45.5 in
scallop and 13.8 to 16.7 in lobster. Zn concentration in all shellfish
examined was higher than Pb, Cu or Cd concentration. It was concluded
that variations in metals content observed were attributable to natural
effects rather than anthropogenic perturbations.
2157.
Towle, D.W. 1974. Equivalence of gill Na+ + K+ - ATPases from
blue crabs acclimated to high and low salinity. Amer. Zool.
14:1259.
326
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Male blue crabs Callinectes sapidus were acclimated to salini-
ties of 34 and 50/00. Microsomal preparations of gills from these animals
had Na+ + K+ -ATPase activities of 1.29 and 2.33 ~moles P./mg protein/min,
respectively, implicating Na+ + K+ -ATPase in the previou~ly recognized
ability of crab to regulate hyperosmotically in dilute seawater. The
possibility of two unique Na+ + K+ -ATPases was discounted by comparing
properties of enzymes isolated from crabs acclimated to two different
salinities. Enzymes from both sources were highly sensitive to ouabain
and required either K+ or NH4+ as well as Na+. Sodium-dependent phos-
phorylation of both enzymes by labelled ATP-32 was blocked by K+ or NH4+'
Polyacrylamide gel electrophoresis of SDS-solubilized P-32 labelled Na+
+ K+ -ATPases showed one band of radioactivity in each case. This phos-
phorylated protein had an apparent molecular weight of 100-105,000 and
represented over 30% of the total microsomal membrane protein in each
preparation.
2158.
Townsley. S.J. 1954. Studies on copper in mollusks, with parti-
cular reference to Busycon canaliculatum Linnaeus. Ph.D.
Thesis. Yale Univ., New Haven, Ct. 126 pp.
Average levels of copper, in mg/kg wet wt, of channeled whelks
were: gut 248; liver 146; kidney 76; pancreas 76; buccal mass 44; gill
40; gonad 21; heart 16; and foot 8. Similar Cu distributions were found
in Nassa obsoleta and Littorina littorea though kidneys had less and
pancreas more Cu than Busycon organs. Cu values in mg/kg wet wt ranged
from 35 to 83 for blood, 67 to 137 for hemocyanin, and 3 to 40 for super-
natant in Busycon. Cu was histochemically demonstrated only in green pig-
ment granules of cells of connective tissue surrounding and invading gut,
liver, pancreas and gonad. Accumulation of Cu-64 by other organs in
quantities not ascribable to activity of included blood demonstrated that
Cu was not due to occluded blood. Cu was either in a more soluble form
removed in histological preparation, or more strongly bound chemically
than Cu of pigment cells and thus incapable of histochemical detection.
Kidney. gill, heart, gonad and possibly buccal mass had rapid Cu turn-
over rates; turnover may be associated with Cu enzymes present. Relative
activity of gut indicated involvement in Cu excretion; pancreas and liver
had low apparent Cu metabolisms and stored any Cu accumulated. Injected
Cu-64 circulated to tissues in combination both with hemocyanin and
smaller molecules of the supernatant fraction. Cu was transferred from
blood to tissues within 24 hrs after injection, although subsequently
returned to blood or excreted. Injected Cu-64 exchanged with Cu already
present in blood fractions. It is suggested that Cu-64 may exchange with
Cu at active sites on hemocyanin molecules or become bound to smaller
supernatant fraction molecules. Cu in hemocyanin was in equilibrium
with that of supernatant fraction. Only 4-8% resynthesis of hemocyanin
occurred by 24 hrs after animals were bled. Failure of Cu-64 activity of
blood to drop at 24 hrs in bled animals indicated that less Cu-64 was
327
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transferred to tissues and utilized in synthesis of new hemocyanin
units.
2159.
Tripp, M. and R.C. Harriss. 1976. Role of mangrove vegetation
in mercury cycling in the Florida everglades. In Nriagu, J.D.
(ed.). Environmental Biogeochemistry. Vol. 2. Metals Trans-
fer and Ecological Mass Balances. Ann Arbor Sci. Publ., Ann
Arbor, Mich.: 489-497.
Field studies on mercury accumulation by detrital mangrove
leaves Rhizophora mangle showed a lOX Hg enrichment of decomposing man-
grove material during initial submergence and leaching by water, and
during transition from leached leaf tissue to fine-grained particulate
organic sediment. Samples collected during periods of low freshwater
discharge, i.e. during periods of high salinity in mangrove environment,
exhibited higher Hg concentrations in most tissue and sediment samples
relative to samples collected during the wet season and from mangroves
exposed to low salinities, i.e. 1 to 120/00. Tannin concentrations in
mangroves decreased about lOX when leaves were subjected to subaqueous
leaching, in an inverse relationship to Hg. A laboratory experiment
designed to simulate decomposition of mangrove leaves under controlled
conditions showed that Hg content of decomposing mangrove leaves in-
creased from 90 nannograms/g dry wt in fresh leaves to 120-140 nannograms/g
dry wt in tissue leached for 15 days. Tannin content of leaves decreased
from 115 mg/g to 78 mg/g, simulating changes in natural system. This
supports a model that attributes initial Hg enrichment to loss of soluble
cellular materials which ~re low in Hg with a consequent relative increase
in Hg per unit wt of tissue in cell fractions resistant to decomposition.
Approximately 10-11% of tissue Hg is associated with cellular fluids and
components which are released during breakdown of cells. About 90% of
total leaf Hg is concentrated in cell wall materials which are not readily
degraded. It was stated that cell wall may be the primary site for
deposition of non-essential trace metals.
2160.
Trollope, D.R. and B. Evans. 1976. Concentrations of copper, iron,
lead, nickel and zinc in freshwater algal blooms. Environ.
Pollution 11:109-116.
Algae were collected from areas adjacent, near, or distant from
zinc smelting wastes in the lower Swansea Valley in Wales. Algae showed
decreasing zinc concentration with increasing distance from probable zinc
sources. Copper concentrations in adjacent and distant waters were
similar, but mean Cu, Fe, Ni and Pb values in near waters were about 2X
those in adjacent waters. Majority of algal blooms were filamentous and
all were Chlorophyta except two. Seven adjacent blooms contained very
high Zn and Pb compared with seven distant blooms, mean values being 25X
328
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greater. With one exception, metal levels were adjacent> near> distant
The exception was Ni where high mean value for near algae was due to high
value in the Cyanophyte Oscillatoria. Mean concentration factors for Zn
were higher at distant> adjacent> near, whereas Cu, Fe, and Pb were
adjacent> near> distant and Ni was near> adjacent> distant. For the
three groups, mean metal concentrations were ordered Fe > Zn > Pb > Cu >
Ni. For individual water masses there were: Fe > Zn > Ni, Pb > Cu in
distant areas; Zn > Ni > Pb > Fe >-Cu in near; and, Zn > Pb > Fe > Ni >
Cu in adjacent waters.
2161.
Truchot, J.P. 1973. Fixation et transport de l'oxygene par Ie
sang de Carcinus maenas: variations en rapport avec diverses
conditions de temperature et de salinite. Netherlands Jour.
Sea Res. 7:482-495. (In French, English summary)
Increased temperature and decreased salinity diminished 02-
affinity of blood respiratory pigment in crabs. Increased temperature
resulted in PSG, the partial pressure of 02 at half saturation, by simple
thermodynamic effect and by control of blood pH at lower values. De-
creasing salinity resulted in blood dilution, augmenting the PSG' In
vivo compensations occurred which maintained PSG between 7 and 12 torr.
These compensations were related to rise of blood pH accompanying the
decrease of salinity. PSG showed a significant decrease at temperatures
above 20 C and this may be due to ion exchange between internal and
ambient media.
2162.
Tsubaki, T., T. Sato, K. Kondo, K. Shirakawa, K. Kanbayashi,
K. Hirota, K. Yamada and 1. Murone. 1967. Outbreak of intoxi-
cation by organic mercury compound in Niigata Prefecture. An
epidemiological and clinical study. Jap. Jour. Med. 6(3):132-
133.
A second outbreak of organic mercury compound intoxication
among inhabitants along the Agano River, Japan, occurred between August
1964 and July 1965. Symptoms included numbness, hearing difficulties,
cerebellar ataxia, speech disturbances, visual field constriction and
disturbance of gait. Levels of Hg in hair of villagers correalted with
amount of Agano River fish eaten.
2163.
Tsuruga, H.
to fish.
Japanese,
1963. Tissue distribution of mercury orally glven
Bull. Japan. Soc. Sci. Fish. 29(5):403-406. (In
English summary)
Freshwater (carp) and marine (conger eel) teleosts were fed
mussels and clams labelled with Hg-203Cl. Previous studies indicated
329
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that mussel will concentrate mercury by a factor of 660 in 4 days and
clam 190X in 8 days from seawater containing 0.05 mg Hg/l. Similar
patterns were observed among carp fed mussel for 17 days and eels fed
clams for up to 19 days. Hg concentrated in fish kidney, gill, liver,
and bone; content in muscle was low (0.03 to 0.5 mg/kg). This study
does not support the high mercury content found in fish from (the
mercury-impacted) Minamata Bay; however, the form in which the mercury
was administered in the present study (inorganic) was probably differ-
ent from the chemical species encountered by Minamata Bay fish and shell.
fish (organic).
2164.
Turekian, K.K. and R.L. Armstrong. 1960. Magnesium, strontium,
and barium concentrations and calcite-aragonite ratios of some
recent molluscan shells. Jour. Marine Res. 18(3):133-151.
Aragonitic shells of pelecypods contained 53 to 320 mg/kg of
Mg, 1000 to <5000 of Sr; and 4 to 41 of Ba. For Pecten, shells were
80 to 100% calcite containing 440 to 4700 mg/kg of Mg, 660 to 1200 of
Sr, and 6 to 12 of Ba. Gastropods contained Mg, Sr, and Ba levels of
38 to 4300 mg/kg (Mg), 860 to 2700 (Sr), and 4 to 15 (Ba). Percent cal-
cite content ranged from a to 75%. Authors suggest that simple ionic
size may control incorporation of trace alkaline-earths in shells.
2165.
Turekian, K.K., J.K. Cochran, D.P. Kharkar, R.M. Cerrato, J.R.
Vaisnys, H.L. Sanders, J.F. Grassle and J.A. Allen. 1975.
Slow growth rate of a deep-sea clam determined by 228Ra
chronology. Proc. Nat. Acad. Sci. U.S.A. 72(7):2829-2832.
The age of a deep-sea clam, Tindaria callistiformis, from 3800
m depth has been determined by Ra-228 (6.7 year half-life) chronology of
separated size fractions of a captured population. Assuming growth laws
for shallow water bivalves hold for deep water forms, a length of 8.4 mm
is attained in about 100 years implying that gonad development begins at
age 50-60 years (4 mm). Shells of this size fraction show about 100
regularly spaced bands, indicating that the growth feature may be an
annual one.
2166.
Tyler, P.A. and R.T. Buckney. 1973. Pollution of a Tasmanian
river by mine effluents. I. Chemical evidence. Int. Rev.
Ges. Hydrobiol. 58:873-883.
Discharge of sulfuric acid, Zn, Cd, Cu, Pb, Fe and Mn in
either dissolved or particulate form from tin and wolfram mines has led
to destruction of normal biota in two creeks in North-East Tasmania.
Brown trout Salmo trutta were unable to survive, and benthic algae were
uncommon. Creek water was unsuitable for domestic or agricultural use.
330
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2167.
Ueda, T., R. Nakamura and Y. Suzuki. 1976. Comparison of 115 m
Cd accumulation from sediments and seawater by polychaete
worms. Bull. Japan. Soc. Sci. Fish. 42:299-306.
Deposit-feeding marine worms Nereis japonica dire~tly in con-
tact with Cd-115m sediments accumulated 6X more Cd-115m than worms not
in contact with Cd-115m sediments during an 8 day period. Dividing the
concentration factor of 22 (from seawater) by 0.12 (the value of Cd-115m
accumulation by direct contact from sediments), an assumed biological
factor of 200 for sediments is obtained. This suggests that sediments
and seawater would affect worm residues equally when level of Cd-115m in
sediments is 200X higher than seawater, and seawater levels decrease by
dilution and diffusion. Distribution of Cd-115m in seawater, sediments
and alga were examined using a theoretical mathematical mode; it was
determined that activity ratios of Cd-115m were 9 for sediments and 21
for alga, which was similar to 22 for worms.
2168.
Ui, J. 1971. Mercury pollution of sea and fresh water its
accumulation into water biomass. Rev. Intern. Oceanogr. Med.
22-23:79-128.
Histories of mercury poisoning cases in Japan are examined.
Article also reviews past research on methyl-Hg, including role of fish
and bacteria in coastal environments of Italy, Germany, Sweden, Finland,
Canada, U.S.A. and Holland.
2169.
Ukeles, R. 1962. Growth of pure cultures of marine phytoplankton
in the presence of toxicants. Appl. Microbiol. 10:532-537.
Effects of 17 toxicants, which included organic phosphates,
phenolics, oils, iodophor, chlorinated hydrocarbons, carbamates, urea
derivatives and Lignasin (ethyl mercury phosphate), on the growth of
Monochrysis lutheri, Dunaliella euchlora, Chlorella sp., Protococcus sp.,
and Phaeodactylum tricornutum were studied. Lignasin was the most toxic
compound; 0.06 mg/l was lethal to all species; the only concentration
tested which did not cause drastic inhibition of growth was 0.0006 mg/l.
2170.
Ulrikson, G.U., D.J. Nelson and N.A. Griffith. 1971. The effect
of temperature on elimination rates of Cs-137 in bluegill
(Lepomis macrochirus). In Oak Ridge Nat. Lab. Ecol. Sci. Div.
Ann. Prog. Rep., ORNL-4634:l06-l07. Available from NTIS, U.S.
Dept. Comm., Springfield, Va.
Experimental data support the theory that there is a doubling
in rate of Cs-137 elimination with each 10 C increase in temperature.
Small fish eliminated Cs-137 more rapidly than large fish.
331
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2171.
Updegraff, K.F. and J.L. Sykora. 1976. Avoidance of lime-
neutralized iron hydroxide solutions by coho salmon in the
laboratory. Environ. Sci. Technol. 10:51-54.
Salmon Oncorhynchus kisutch raised in clean water showed no
avoidance of suspended lime-neutralized iron hydroxide suspensions con-
taining up to 1.20 mg Fe/I. Higher concentrations produced increased
avoidance until a definite avoidance reaction was observed at 4.25-
,
6.45 mg Fe/I. Adaptation is possible: fish exposed for several months
to different iron hydroxide concentrations showed responses almost
identical to those of controls.
2172 .
Ussing, H.H. 1947. Interpretation of the exchange of radio-
sodium in isolated muscle. Nature 160:262-263.
Isolated frog sartorii muscle were equilibrated with radio-
sodium. Exchange of Na in muscle fibers with outside medium occurred
at more than 150 cal/kg/hr. Several possible mechanisms which allow
for exchange of sodium ions without consumption of energy are discussed.
2173.
Uthe, J.F. and E.G. Bligh. 1971. Preliminary survey of heavy
metal contamination of Canadian freshwater fish. Jour. Fish.
Res. Bd. Canada 28:786-788.
For lake whitefish Coregonus clupeaformis, northern pike Esox
lucius, rainbow smelt Osmerus mordax, and yellow perch Perca flavescens,
collected from non-industrialized and heavily industralized freshwater
regions of Canada, muscle residues in mg/kg wet wt, were: <0.5 for Pb;
<0.2 for Ni; 0.5 to 1.28 for Cu; 0.0022 to 0.0043 for Sb; ~0.05 for Cd;
11 to 20 for Zn; <1 to 3 for U; 0.02 to 3.16 for Mn; 0.17 to 0.38 for
Se; <0.017 to 0.035 for Cr; and 0.55 to 5.43 for Sn. For most of these
elements, residues did not differ significantly between regions. Arsenic
and Hg levels ranged from 0.05 to 0.70 mg/kg wet wt, with highest values
observed in the industrial area.
2174.
Vaczi, L., M. Fodor; H. Milch and A. Rethy - 1962. Studies on the
mercuric chloride resistance of Staphylococcus aureus. Acta
Microbiologica 9:81-87.
Of 409 S. aureus strains 34% were sensitive, and 66% resistant
to mercuric chloride. Incidence of HgC12-resistant cultures among anti-
biotic sensitive staphylococci was 20%; among strains resistant to peni-
cillin or more than one antibiotic this was 70%. HgC12-resistant
organisms occurred chiefly among phage group I and untypable strains;
they were especially common among "epidemic" strains of phage group I,
332
-------
and among cultures resistant to 4-6 antibiotics. A 30X difference in
HgC12 sensitivity and a 2X difference in merthiolate sensitivity was
found among the strains. Sulfhydryl content of HgC12 resistant organ-
isms was only 1.5X greater than that of sensitive bacterjq. A 2X dif-
ference was found between the p-chlor mercuric benzoate binding capacity
of HgC12 sensitive vs resistant bacteria. Differences in HgC12 resist-
ance of staphylococcal strains might be due to differences in chemical
structure of cell surface.
2175.
Vaituzis, Z., J.D. Nelson, Jr., L.W. Wan and R.R. Colwell. 1975.
Effects of mercuric chloride on growth and morphology of
selected strains of mercury-resistant bacteria. Appl. Micro-
bioI. 29(2):275-286.
Mercury resistance was dependent upon ability to volatize
mercury from medium and upon amount of mercury accumulated by cells.
Most cultures which adapt to growth in presence of HgC12' exhibit exten-
sive morphological abnormalities. Significant effects include delay in
onset of growth and cell division, and numerous structural irregularities
associated with cell wall and cytoplasmic membrane synthesis and function.
Detailed analysis of adaptation process and resulting effects on mor-
phology was performed on an Enterobacter Spa During the period preced-
ing active multiplication, selection for mercury-resistant mutants occurred
It was also demonstrated that growth commenced only at a specific thresh-
old concentration of 1.1 ug/ml Hg2+.
2176.
Valiela, I., M.D. Banus and J.M. Teal. 1974. Response of salt
marsh bivalves to enrichment with metal-containing sewage
sludge and retention of lead, zinc and cadmium by marsh sedi-
ments. Environ. Pollut. 7:149-157.
Growth in clam Mercenaria mercenaria, and oyster Crassostrea
virginica in tidal creeks of salt marshes on the NW Atlantic coast, was
not affected by experimental additions of metal-containing sewage sludge
and urea fertilizers to salt marsh plots. Modiolus demissus, a mussel
inhabiting the marsh surface, grew better under the same fertilizer
treatments. All 3 species of shellfish showed no increases in lead or
zinc contents, but all showed increased cadmium contents related to
sludge fertilizer treatments. Increases in Zn, and particularly Cd, but
not Pb, were detected in creek bottom detritus downstream from the plots.
Surface sediments of marsh plots show significant accumulation of all 3
metals. The calculation of input-output budgets shows that Pb was
tTapped in sediments with virtually no losses to deeper waters. Zinc and
Cd also accumulated in sediments but there is some transport away from
salt marsh surface, especially with cadmium. Highest concentrations of
metals recorded in clam in mg/kg dry wt were: 3.5 for Pb, 298 for Zn,
333
-------
and 2.18 for Cd. For oyster these were <1,12,675, and 9.45 for Pb, Zn,
and Cd, respectively. For mussel it was 3.2 for Pb, 52 for Zn, and
7.13 for Cd.
2177.
Vanderploeg, H.A., R.S. Booth and F.H. Clark. 1975. A specific-
activity and concentration model applied to cesium movement in
an oligotrophic lake. In Howell, F.G., J.B. Gentry, and M.H.
Smith (eds.). Mineral cycling in southeastern ecosystems.
U.S. Energy Res. Dev. Admin.: 142-165. Avail. as CONF-7405l3
from NTIS, U.S. Dept. Comm., Springfield, Va. 22161.
A linear systems-analysis model was derived to simulate time-
dependent dynamics of specific-activity and concentration of radio-
nuclides in aquatic systems. Transfer coefficients were determined for
movement of Cs-137 in water, sediments, interstitial water, algae,
insect larvae, and fish of three trophic types in an oligotrophic lake.
Simulations with a model that ignored sediment-water interactions pre-
dicted much higher Cs-137 activities in water and biota than in the com-
plete model. Comparing predicted Cs-137 concentrations with reported
concentrations in biota of an experimentally contaminated lake indicated
that derived transfer coefficients are adequate.
2178.
van Someren, V.D. 1937. A preliminary investigation into the
causes of scale absorption in salmon (Salmo salar Linne).
Fish. Bd. Scotland Salmon Fish. No. 2:1-12.
During migration, serum Ca level in female salmon rose from
20 to 40 mg%; at spawning it dropped to 12 mg%. Serum Ca in male salmon
remained at 16 mg% until spawning, when it also fell to 11 mg%. Varia-
tions in serum Ca was independent of weight, length, condition, and
degree of scale absorption; authors suggest that it is a secondary
phenomenon incidental to pituitary activity and growth of gonads. Blood
Ca was probably not derived from the scales. Major cause of scale
absorption is attributed to potential mineral deficiency during migra-
tion fast. In male salmon, absorption is probably accentuated by a
demand for Ca necessary for development of secondary sexual character-
istics.
2179.
Velimirov, B. and E.L. Bohm. 1976. Calcium and magnesium car-
bonate concentrations in different growth regions of gorgonians.
Marine Biology 35:269-275.
Four abundant gorgonian (coelenterate) species from SW Cape of
Good Hope.waters, Eunicella papillosa, ~. alba, ~. tricoronata, and
Lophogorgla flamea were analyzed for Ca and Mg. Total mineral content
334
-------
in peripheral tissues, excluding axial skeleton, expressed as sum of
CaC03 and MgC03 on a dry wt basis ranged between 65 and 83%. Mineral
content varied in different growth regions; all specimens showed a
higher degree of mineralization at the base than at branch tips. MgC03
concentration varied with genus and species and ranged between 9 and 11
mol %. Variation of MgC03 concentration within different growth regions
of the same species was small, and generally did not exceed 0.8 mol %.
From branch to stem, CaC03 and total mineral content increased. The
CaC03:MgC03 ratios in different growth regions of all species indicated
that composition of mesoskeleton with regard to relative concentration
of CaC03 and MgC03 is constant throughout animal. Mineralogically,
mesoskeleton consists of high magnesian calcite as identified by X-ray
diffraction. The MgC03 data in gorgonian samples from cold Atlantic
Ocean and warmer Indian Ocean show a linear relationship between water
temperature.
2180.
Vernberg, W.B., P.J. DeCoursey and J. O'Hara.
environmental factor effects on physiology
fiddler crab, Dca pugilator. In Vernberg,
Vernberg (eds.~ Pollution an~physiology
Academic Press, Inc., New York: 381-425.
1974. Multiple
and behavior of the
F.J. and W.B.
of marine organisms.
Effects of cadmium and mercury salts on Dca depend on many
factors including stage of life cycle, sex, thermaTlhistory, and environ-
mental regime. The two metals do not necessarily affect Uca in the
same manner. Larvae are several orders of magnitude more-sensitive to
mercury than adult stages, and adult males are more sensitive to mercury
than females. Mercury is most toxic at low temperatures and low salinity.
Warm-acclimated animals (summer animals) are less tolerant of Hg at low
temperatures than cold-acclimated (winter) ones, and concentrations of Hg
that are sublethal under optimum conditions of temperature and salinity
become lethal with suboptimal thermosaline regimes. Distribution of Hg
in crab tissues is dependent on environmental regime, but total body
burden is not. Adult crabs are also less sensitive to cadmium poisoning
than larvae, but there were no observed differences in mortalities be-
tween males and females. Cadmium is most toxic at high temperature and
low salinity, and both the distribution and total body burden of cadmium
is dependent upon environmental conditions. Although there are major
differences in uptake and accumulation of Hg and Cd, it is stated that
with both elements death is probably related to accumulation of metal in
gills with an associated breakdown in osmoregulation or respirating
functions.
2181.
Vijayamadhavan, K.T. and T. Iwai. 1975. Histochemical
vations on the permeation of heavy metals into taste
goldfish. Bull. Jap. Soc. Sci. Fish. 41:631-639.
obser-
buds of
335
-------
Taste buds located in palatal organs of goldfishCarassius
auratus were exposed for 3, 10, 15, 30, and 60 minutes to 10-~M solutions
of mercuric chloride, copper sulphate and zinc chloride (24 mg/l, 16 mg/l
and 10 mg/l solutions, respectively), and 10-3M solutions of copper sul-
phate, zinc chloride and lead nitrate (160 mg/l, 100 mg/l and 269 mg/l
solutions, respectively). Rate of metal-permeation into taste cells
varied with metal, concentration of metallic ions in medium, and dura-
tion of exposure. In terms of permeation rate the sequence of metals
was found to be Hg, Cu, Zn, and Pb. Hg damaged not o~ly taste buds but
entire epithelial layers within 30 min; Cu effects were more or less
confined to taste buds. Both Hg and Cu caused vacuolation at the bases
of taste buds. Pb affected mucous cells more than taste buds. Results
suggest that histological damage is associated with and preceded b4
metal-permeation. During the early phase of exposure, Hg, Cu (10- M),
and Zn (10-3M) selectively permeated certain taste bud cells.
2182.
Vink, G.J. 1972. Koper in vis (copper in fish).
27:493-496. (In Dutch, English summary)
TNO Nieuws
Copper levels in muscle of young flatfish collected in Dutch
coastal waters ranged from 1.3 to 6.7 mg/kg dry wt. Age, condition, and
location of collection were all significant factors affecting Cu residues.
2183.
Vinogradova, Z.A. and V.V. Koual'skiy. 1962. Elemental composi-
tion of the Black Sea plankton. Doklady Acad. Sci. U.S.S.R.
Earth Sci. Sec. 147:217-219.
Respective maximum concentrations of elements, in g/kg ash wt,
of 1) diatoms, 2) copepods, 3) chaetognaths (Sagitta), and the 4) cteno-
phore (Pleurobranchia pileus) were: beryllium 0.003, 0.003, nd (not
detected), and nd, respectively; for lead 3, 0.15, 1.5 and 0.04; tin 0.1,
0.07, 0.4 and 0.02; gallium 0.02, 0.04, 0.01 and nd; molybdenum nd, 0.05,
nd, and nd; lithium 0.15, 0.4, 0.5 and 0.6; copper 100, 15, 30 and 0.3;
silver 0.03, 0.03, 0.06 and 0.004; nickel 0.15, 0.2, 0.3 and 0.05; cobalt
0.015, 0.015, nd and nd; zirconium 0.05, 0.07, 0.05 and nd; chromium
0.08, 0.07, 0.08 and 0.01; for vanadium 0.06, 0.07, 0.02 and nd;
manganese 0.3, 0.5, 0.8, and 0.02; iron 8, 40, 100 and 5; aluminum 4,
>30, 7 and 0.5; zinc 5, 4, 20 and 0.9; titanium 20, 0.7, 0.5 and 0.03;
strontium 15, 1.5, 1.5 and 1.0; barium 30, 2, 1.5 and 0.06; sodium 20,
30, 30 and >30; calcium >100, 70, 35 and 15; and magnesium 10, 30, 100
and 70. Sharp differences were evident between individual species in a
taxon.
336
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2184.
Vorob'yev, V.I. and V.F. Zaystev. 1975. Dynamics of some trace
elements in organs and tissues of the rudd. Hydrobiological
Jour. 11(2):57-60.
Concentrations are listed of Fe, Cu and Al in organs and
tissues of rudd Scardinius erythrophthalmus, a teleost from the Volga
delta. The order of Fe accumulation by organ and tissues is: kidney>
gill fringe> spleen> liver> scales> swim bladder> muscle. In all
organs except gill fringe, Fe accumulation was significantly higher in
males. The order of Cu accumulation is: liver> scales> spleen>
kidney> gill fringe> swim bladder> muscle. For AI, this was: kidney
> scales> gill fringe> spleen> liver> swim bladder> muscle.
Seasonal and sex-associated differences are discussed.
2185.
Vostal, J. 1972. Transport and
nature and possible routes of
J. Vostal (eds.). Mercury in
Press: 15-27.
transformation of mercury in
exposure. In Friberg, L.T. and
the marine environment. CRC
Concentrations, chemical species, sources, and biological
half-life of mercury in various species of fish, aquatic mammals, and
fish-eating birds from different geographical areas are reviewed.
2186.
Voyer, R.A. 1975. Effect of dissolved oxygen concentration on
the acute toxicity of cadmium to the mummichog, Fundulus
heteroclitus (L.) at various salinities. Trans. Amer. Fish.
Soc. 104:129-134.
Fish acclimated to test salinities ranging between 10 and 32%0
were subjected to dissolved oxygen levels between 4 mg/l and saturation.
Re~ardless of salinity and oxygen regimen, mean LC-50 (96 hr) values for
Cd + ranged between 52 and 92 mg/l.
2187.
Voyer, R.A., P.P. Yevich and C.A.
and toxicological responses of
clitus (L.),to combinations of
oxygen in a freshwater. Water
Barszcz. 1975. Histological
the mummichog, Fundulus hetero-
levels of cadmium and dissolved
Research 9:1069-1074.
LC-50 (96 hr) values for the mummichog, aeuryhaline estuarine
teleost, in freshwater ranged upward from 1.3 to about 3.0 mg cadmium/l
at 2.3 and 8.5 mg dissolved oxygen (00)/1, respectively. Mortality data
showed factors examined were interdependent and that Cd x DO and Cd x
time interactions were significant (P <0.01). No histopathology was
evident at 3 mg Cd/I. Mummichogs exposed to 25 mg Cd/l at 20 C and 8.5
mg 00/1 showed no histopathology after 5.5 hrs; at 6.5 hrs necrosis,
337
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mucosal sloughing of gills, and damage in nasal passage and buccal cavity
tissues were evident.
2188.
Waldichuk, M. 1974. Some biological concerns in heavy metals
pollution. In Vernberg, F.J. and W.B. Vernberg (eds.).
Pollution an~Physiology of Marine Organisms. Academic Press,
New York: 1-57.
Current research on toxicity, bioaccumulation, and physiologi-
cal effects of selected heavy metals on marine biota is reviewed. Ele-
ments discussed include AI, Sb, As, Ba, Be, Bi, Cd, Cr, Co, Cu, Fe, Pb,
Mn, Hg, Mo, Ni, Rb, Ag, Te, Th, Ti, U, V. and Zn, with special reference
to stimulatory concentrations for algae, bioconcentration by fish and
macroinvertebrates, and toxicity to crustaceans, mollu~cs, and fish. A
list of 118 references is appended.
2189.
Walker, G., P.S. Rainbow, P. Foster and D.J. Crisp. 1975.
Barnacles: possible indicators of zinc pollution? Marine
Biology 30:57-65.
Three species of barnacles (Balanus balanoides, Elminius
modestus, Lepas anatifera) from several different sites accumulated zinc
at levels from 138 to 3438 mg Zn/kg wet wt. Seventy-five to 88% of total
Zn in barnacles was in soft tissues with 45 to 65% of total Zn in
organism associated with gut and associated parenchyma. Zinc accumulated
in gut was in the form of discrete concentrically layered granules,
mainly within parenchyma cells which surround the gut; these granules
probably are an insoluble Zn salt. Concentration factors for tissues
associated with gut remained relatively constant for barnacles from dif-
ferent localities at 0.71 to 1.5 x 106 g Zn/g dry wt x g Zn/g seawater
and suggests that gut Zn levels conform closely to environmental Zn levels.
2190.
Walker, G., P.S. Rainbow, P. Foster and D.L. Holland. 1975.
phosphate granules in tissue surrounding the midgut of the
barnacle Balanus balanoides. Marine Biology 33:161-166.
Zinc
Chemical composition of inorganic granules found in parenchyma
cells surrounding the midgut of adult barnacles was found to be 38% Zn,
48% P04-P, 5% Ca, 1% Fe, 1% Cu, 4% Mg, and 2% K. Results indicate that
most trace metals entering barnacles are excreted except Zn, which pri-
marily accumulates as insoluble zinc phosphate granules. These may be
the end product of a detoxification process.
338
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2191.
Walker, G.C. and D.J.D. Nicholas. 1961. An iron requirement for
a dissimilatory nitrate reductase in Neurospora crassa.
Nature 198:141-142.
Neuros~ora grown at low oxygen tensions dissimilates nitrate.
Under these condltions nitrate reductase is dependent on Fe and Mo for
maximum activity. Deficiencies of either Fe or Mo at the 2-day stage of
growth reduced nitrase reductase activity to 21% and 61% of normal acti-
vity. After 5 days growth, only Mo deficiency depressed nitrate reduc-
tase activity (by 43%). Enzyme activity at 5 days growth was not
affected by Fe deficiency. Lack of Cu, Mn, or Zn did not decrease
nitrate reductase activity at any stage of growth.
2192.
Walker, J.B.
Chlorella.
and zinc.
1954. Inorganic micronutrient requirements of
II. Quantitative requirements for iron, manganese
Arch. Biochem. Biophys. 53:1-8.
Quantitative inorganic micronutrient requirements of Chlorella
pyrenoidosa for Fe, Mn, and Zn were determined by obtaining plots of
yield versus amount of added micronutrient in media devoid of added
chelating agents. For growth of one g of dried Chlorella, a minimum of
approximately 30 ~g Fe, 2.5 ~g Mn, and 4.5 ~g Zn are required under the
test conditions. In presence of ethylenediaminetetraacetic acid (EDTA),
much larger quantities of all required micronutrients except Fe must be
supplied for a defined yield; Fe requirement is same in presence or
absence of EDTA. In absence of EDTA, Fe added in form of potassium ferri.
cyanide was up to 2X as effective for growth per unit Fe as was iron in
form of ferrous sulfate; this advantage was most marked in alkaline solu-
tions. Both iron sources were equally effective in presence of EDTA.
2193.
Walker, J.D. and R.R. Colwell.
and petroleum degradation.
1974. Mercury-resistant bacteria
Appl. Microbiol. 27(1):285-287.
Concentration of Hg in water and sediment, and in oil extracted
from water and sediment, was determined for samples collected in Colgate
Creek, located in Baltimore Harbor of Chesapeake Bay. Bacterial popula-
tions of samples studied had maximum tolerances of 4 to 60 mg HgCl/l and
can degrade oil, suggesting that these bacteria are significant factors
in oil degradation in Colgate Creek. Concentration of Hg in sediment
oil was 2795 mg/kg, and 2960 mg/kg in water-borne oil; by contrast, an
oil-free sediment contained 0.67 mg Hg/kg and oil-free water <0.01 mg
Hg/kg.
339
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2194.
Wallen, I.E., W.C. Greer and R. Lasater. 1957.
Gambusia affinis of certain pure chemicals in
Jour. Sewage Industrial Wastes 29(6):695-711.
Toxicity to
turbid waters.
Toxicities to mosquito fish of 86 chemicals commonly found in
oil refinery wastes were determined in turbid pond water. LC-50's (96 h)
in mg/l for some metal compounds were: 133 for A1C13; 1,640 for BaC12;
75 for CUS04; 74 for FeC13; 240 for Pb(N03)2; 16,500 for MgC12; 920 for
KCl' and 17 550 for NaCl. Effects of various soil suspensions were also
, ,
examined.
2195.
Wangersky, P.J. and O. Joensuu. 1964. Strontium, magnesium and
manganese in fossil foraminiferal carbonates. Jour. Geology
72:477-483.
Deep sea foraminiferal cores from the Caribbean and Atlantic
Ocean were analyzed for Sr, Mg and Mn. Concentration of Sr was uniform
in all cores. The distribution of Mg was more variable both within and
between cores. In all 3 cores there are direct correlations between Mn
and depth, implying a shift of Mn into the coarse fraction from some
other phase of the sediment.
2196.
Ward, A. and R.G. Wetzel. 1975. Sodium: some effects on blue-
green algal growth. Jour. Phycol. 11:357-363.
Anabaena cylindrica with no Na+, suffered from decreased rates
of acetylene reduction, l~C assimilation, excretion of organic C as well
as lower concentrations of chlorophyll a and particulate organic C when
compared to cultures supplied with 5, 10, and 50 mg Na+/l. Na-deficient
algae released extrace1lularly a higher percentage of previously fixed C
as organic C. No differences in any parameter measured were demonstrable
among cultures grown with 5, 10, and 50 mg Na+/l. Nitrate concentrations
of 20 mg NO;/l resulted in decreased rates of acetylene reduction and
heterocyst numbers in Na-sufficient and Na-deficient cultures; however,
decreased cellular Na content at high NO; levels occurred only in N
deficient cultures. Higher percentages of excreted organic C occurred
with increasing NO; concentrations in Na deficient cultures. Addition
of 5 mg Na/l to natural bluegreen populations resulted in increased C
fixation, but addition of 50, 100 or 200 mg Na/l elicited no res~onse.
Since Na concentrations of SW Michigan lake water at ca. 5 mg Na /1 was
sufficient for growth, Na is not assumed to be limiting under most
natural conditions.
2197.
Ward, E.E. 1966. Uptake of plutonium by the lobster, Homarus
vulgaris. Nature (London) 209:625-626.
340
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Lobsters were held in aerated, filtered seawater at 9-12 C
containing 6.5 x 10-2 ~Ci/l of plutonium-239 for up to 220 days. When
lobsters molt, the soft shell, gills, hepatopancreas and flesh contained
relatively less Pu-239 than normal animals, while cast shell has ~2X
that of shell of intermoult lobster; calcifying shells rapidly accumu-
lated Pu-239. The calcified skeleton (43% total wt of lobster) contains
89% of total Pu; whereas hepatopancreas has 4.6%; and flesh (28.7% total
body wt) contains only 1.2%. Concentration factor for lobster flesh is
3, which is equal to cf of fish Sarda lineolata.
2198.
Waterman, A.J. 1937. Effect of salts of heavy metals on develop-
ment of the sea urchin, Arbacia punctulata. BioI. Bull. 73:
401-420.
The following concentrations of metals, as chlorides, prevented
gastrulation when embryos were exposed during blastula stage: Ni 90.7
mg/l; Al 30.4 mg/l; Cd 92 mg/l; Cu 1.57 mg/l; Zn 2.4 mg/l; Zn (as sul-
phate) 2.03 mg/l; Zn (as acetate) 1.84 mg/l; and Hg 0.092 mg/l. Few
gastrula developed at 14.9 mg/l Pb. No effect occurred at 8.8 mg/l Fe,
the highest concentration tested. All controls developed to the young
plutei stage during the same 13.5-17 hr test period.
2199.
Watling, H.R. and R.J. Watling. 1976. Trace metals in oysters
from Knysna Estuary. Marine Poll. Bull. 7(3):45-48.
Metal residues in Crassostrea gigas cultured in a South African
estuary, in mg/kg dry tissue, were: Zn 396; Cd 3.7; Cu 32; Fe 128; Mn
16; Ni 1.6; and Ag 1.9. For C. margaritacea these values were: Zn 886;
Cd 2.5; Fe 57; Mn 2; Ni 1.6; and Ag 2.6. Ostrea edulis had concentrations,
in mg/kg dry tissue, of: Zn 660; Cd 3.1; Cu 38; Fe 167; Mn 6; Ni 1.7;
and Ag 6.4. Logarithmic regression coefficients relating Zn, Cd, Cu, or
Fe contents (ug) to dry tissue (g) for the 3 oyster species ranged from
0.415 to 1.064, with most values <1.0. It was the intent of this study
to create a baseline for comparison with future effects of industrial
growth.
2200.
Watling, H.R. and R.J. Watling. 1976. Trace metals in Choro-
mytilus meridionalis. Marine Poll. Bull. 7(5):91-94.
Oysters Crassostrea gigas, from a bay and lagoon on the SW
African coast had metal levels in mg/kg dry tissue of 424 for Zn, 9 for
Cd, 33 for Cu, 1 for Pb, 12 for Mn, 1 for Ni, 1 for Co, and 4 for Bi.
Mean sediment levels in mg/kg were 8.7 for Zn, 0.7 for Cd, 3.3 for Cu,
17 for Pb, 12 for Mn, 6 for Ni and 3 for Co. Ranges of mean metal
levels in mg/kg dry tissue of mussels Choromytilus meridionalis collected
341
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from 3 sites were 73 to 113 for Zn, 1 to 8 for Cd, 7 to 14 for Cu, 2 to
5 for Pb 9 to 11 for Mn, 2 to 3 for Ni, 2 to 3 for Co, and 5 to 6 for
Bi. Met~l concentrations were negatively correlated with size. Females
had higher Cu, Mn and Zn residues, but lower Pb and Bi than males of
comparable size. Cu and Mn levels, and Pb and Bi contents were corre-
lated and all 4 were correlated with Zn. In mussels, concentrations of
Fe, A~ and Cr were 60, 0.3 and 1.4 mg/kg dry wt, respectively.
2201.
Watson, T.A. and B.A. McKeown. 1976. The activity of ~5-3S
hydroxysteroid dehydrogenase enzyme in the interrenal tissue
of rainbow trout (Salmo gairdneri Richardson) exposed to
sublethal concentrations of zinc. Bull. Environ. Contamin.
Toxicol. 16(2):173-181.
Effects of exposure of adult trout for 50 days to 3 sublethal
concentrations of zinc (0.248, 0.528 and 1.14 mg/l) on ~5-3S-hydroxy-
steroid dehydrogenase (65-3SHSDH) enzyme activity in the head kidney
tissue was investigated. Zinc-exposed trout showed a greater degree of
65-3SHSDH activity compared to controls. Increase in enzyme activity is
associated with stimulation of pituitary-interrenal axis by zinc stress.
2202.
Webb, D.A. 1939. Observations on the blood of certain ascidians,
with special reference to the biochemistry of vanadium. Jour.
Exp. BioI. 16:499-523.
Vanadium chromogen in blood of several species of Ascidians was
examined. Vanadium, in g/kg organic dry wt, was 0.4 for Cion~ 1.1 to 1.8
for Ascidia, 0.04 for Dendrodoa and <0.02 for Botryllus, Botrylloides,
Tethyum and Microcosmus. Vanadium chromogen is not a protein or porphy-
rin, but may be an association of V with a straight chain complex of
pyrrol rings. Seawater concentrations are calculated to be sufficient
for V uptake. It is concluded that presence of V is a primitive charac-
ter which has been lost in more specialized families.
2203.
Wedemeyer, G. 1968. Uptake and distribution of Zn65 in the coho
salmon egg' (Oncorhynchus kisutch). Compo Biochem. Physiol.
26:271-279.
Zinc-65 uptake and accumulation was strongly pH dependent in
chorion of intact egg. In isolated chorion it was constant at 6 x 10-3
wM/g over pH range 2-9. Zinc uptake was inhibited by Cu2+ in range 0-2
mg/l Cu2+ but facilitated above 2 mg/l. Malachite green, an azo dye,
increased Zn permeability especially at concentrations above 1 mg/l.
Zinc uptake also increased with increasing temperature. About 70% of
total accumulated zinc was bound to chorion; about 26% was in perivitelline
342
-------
fluid, 2% in yolk, and about 1% in embryo. Temperature, pH, inhibitor and
kinetic studies indicated that Zn uptake involves physicochemical sorp-
tion to chorion together with passive diffusion into yolk and embryo.
2204.
Weigel, H.P. 1976. Atomabsorptionsmessungen von Blei, Cadmium,
Kupfer, Eisen und Zink im Seston der Ostsee. Helgolander wiss.
Meersunters. 28:206-216. (In German, English summary)
Seston samples from 23 stations between Kiel Bight and Finnish
Bay in the Baltic Sea, were analyzed for Pb, Cd, Cu, Fe and Zn. Mean
values in mg/kg wet wt were: Pb, 123; Cd, 6; Zn, 733; Cu, 61; and Fe,
3535. In contrast to trace metal analyses for offshore seston, values
for Pb and Cd in the Baltic Sea are very high and values of Zn, Cu and
Fe, apart from local influences, agree well.
2205.
Weis, J.S. 1976. Effects of mercury, cadmium, and lead salts on
regeneration and ecdysis in the fiddler crab, Uca pugilator.
U.S. Dept. Commerce, Nat. Ocean. Atmos. Admin., Fish. Bull.
74(2):464-467.
Autotomized fiddler crabs were placed in solutions of 0.1 or
1.0 mg/l Pb2+, Hg2+ or Cd2+ for up to 28 days. Retardation of regenera-
tion was a specific effect of Cd at both 0.1 and 1.0 mg/l with no deaths
occurring. At 0.1 mg/l, Hg was neither toxic nor had any effect on
growth of limb buds. But at 1.0 mg/l Hg caused almost total inhibition
of limb growth and was toxic to 60% of crabs. Mercury inhibition of
regeneration is probably associated with its toxic properties. Lead had
no effect on regeneration rate at levels examined. Crabs exposed for
2 wks to 0.1 mg/l of Hg contained 0.026 mg Hg/kg whole wet crab; those
subjected to 0.1 mg/l of Cd contained 0.50 mg Cd/kg; and those exposed
to 0.1 mg/l of Pb absorbed 2.04 mg Pb/kg.
2206.
Weis, P. and J.S. Weis. 1976. Effects of heavy metals on fin
regeneration in the killifish, Fundulus heteroclitus. Bull.
Environ. Contamin. Toxicol. 16:197-201.
Regeneration of amputated lower half of killifish caudal fin
was observed during exposure to Hg, Pb or Cd salts at 25 C and 300/00
salinity. One mg/l Hg was lethal to all fish within 1 week. At 0.1
mg/l Hg, all died within 1.5 weeks. Fish in 0.1 mg/l Pb regenerated at
slightly faster rates than controls. At all three doses of Cd (0.01,
0.1, and 1.0 mg/l), fin regeneration was retarded but effect was not
correlated with dose. Cadmium affected initial healing and blastema
formation; however, growth rates of experimentals and controls were
equal.
343
-------
2207.
Weiss, R.E., P.L. Blackwelder and K.M. Wilbur. 1976. Effects
of calcium, strontium and magnesium on the coccolithophorid
Cricosphaera (Hymenomonas) carterae. II. Cell division.
Marine Biology 34:17-22.
Effects of deficiencies of Ca and Mg, and Sr enrichment on cell
division in alga were studied. Cell growth was reduced at 0.04 g Call
and absent at 0.02 g Call and lower. Addition of Sr to media deficient
in Ca enabled cells to divide, the effect increasing with Sr concentra-
tion. When 0.4 g Sr/l was added to media containing 0.004 g Call, rate
of division and final cell concentration were comparable to controls
(0.4 g Call); Sr was 20X more effective in this respect than Ca. Rate
of growth was also examined at various Mg concentrations: cell division
was absent, or nearly so, in Mg concentrations below 0.001 g/l; cell size
increased progressively as Mg concentration decreased. However, low
protein concentrations were evident in absence of Mg. In media lacking
Mg, cells exhibited changes in ultrastructure including rounding-up and
apparent fragmentation of chloroplasts, and increase in vacuole size.
Number of mitochondria per cell section increased 2.9X in absence of Mg
while total cross-sectional area remained the same, indicating fragmen-
tation.
2208.
Welander, A.D., K. Bonham, R.F. Palumbo, S.P. Gessel, F.G. Lowman,
W.B. Jackson, R. McClin and G.B. Lewis. 1967. Bikini-
Eniwetok studies 1964: Part II. Radiobiological studies.
Univ. Washington Lab Radiation Ecology, Seattle, Wash. UWFL -
93:164 pp. + Appendix.
Eniwetok and Bikini Atolls, in the west central Pacific, were
the site of approximately 60 nuclear or atomic explosions between 1946 and
1958. They were visited in 1964, to identify and document kinds and
conditions of organisms present on reefs and islands. Bird populations
consisted of 6 species of shorebirds which fed primarily on molluscs,
crustaceans and insects found in and on the beaches and islands, and 7
species of seabirds which fed upon small fishes and squid. Shorebirds
contained (in p Ci/g dry wt) Mn-54, Co-60 and Cs-137 in amounts of 0.074,
48 and 350, respectively. Seabirds had 2.5, 6.0 and 0 p Ci/g dry wt of
Mn-54, Co-60 and Cs-137, respectively. Shorebirds contained the highest
amounts of Cs-137 in muscle tissue (200 p Ci/g dry wt at Eniwetok and
630 p Ci/g dry wt at Bikini). Liver, kidney, gut and skin had lower,
but comparatively high amounts of Cs-137, with bones containing the lowest
amount. No Cs-137 was found in detectable amounts in any organs of sea-
birds. Highest amounts of radioactivity in seabirds were in liver and
kidney, mostly Mn-54 and Co-60.
Cobalt-60 at concentrations up to 200 p Ci/g dry wt, was the
primary radionuclide found in plankton samples. Other radionuclides in
344
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relative order of abundance are Ru-106, Co-57, Sb-125, Bi-207, Mn-54
and Cs-137. Zn-65 was not detected in any plankton samples. Cobalt-60
was the most abundant radionuc1ide and the only one found in all plankton
samples. Algae contained in decreasing magnitude of activity: Ce-144,
Co-60, Ru-106, Bi-207, Mn-54, Cs-137 and Sb-125. Cerium-144 was the most
dominant radionuc1ide. Filamentous, vesicular, or succulent types of
algae appeared to have higher concentrations of radioactivity than
coralline types. Radioactivity levels in echinoderms, sponges, coelen-
terates and other invertebrate samples varied with locality and species
but insufficient to be hazardous to these populations. Especially high
concentrations of Co-60 (up to 66,000 p Ci/g dry wt) and Co-57 (up to
11,000 p Ci/g dry wt) were noted in clams. Cesium-137 was noted at
2,000 p Ci/g dry wt in land crabs. Radioactivity of crabs was higher in
terrestrial than in the more aquatic species, whereas the opposite was
true in the weeks following detonations. Invertebrate life exists in
approximately the same abundance as before the testing, except within a
0.5 mile radius of the large detonations. Even in these areas, the
reduction in invertebrate life resulted primarily from mechanical rather
than radioactive causes. Radionuclide content of fish, given as the
higher average of the two atolls in p Ci/g dry wt were: 24 for Co-60,
2.9 for Mn-54, 1.2 for Cs-137 and Zn-65, 1.1 for Co-57, 2.0 for Bi-207,
and 0.038 for Ru-l06. No Sb-125 was found.
Comparison of radioactivity in various organs or tissues of
fish, showed that highest values of Co-60 were in liver or viscera which
included entire alimentary tract, gonads, air-bladder and spleen); smaller
amounts were in "remainder" (which included some bone, muscle, skin, gills,
kidney, and nervous tissue); lowest values were in the skin, muscle, and
bone. Biogeographical distributions of radionuclides are given and their
implications discussed.
2209.
Wells, H.W. 1961. The fauna of oyster beds, with special
reference to the salinity factor. Ecol. Monog. 31(3):239-266.
In the Beaufort, N.C. area between 1955-1956 distribution of
oyster associates was compared with physical factors, particularly
salinity. Three hundred and three species representing annelids,
bryozoans, coelenterates, crustaceans, echinoderms, teleosts, insects,
platyhelminthes, protozoans, and molluscs were collected. Number of
species declined upstream and bore a direct relationship to salinity con-
ditions. Mortalities due to hurricanes and the subsequent recovery of
oyster beds were followed. Twenty species were tested in the laboratory
for tolerances to low salinities; ranking of their salinity death points
was compared with their distribution in the Newport River. Only 2 species
showed wide deviations from distribution expected on basis of their
salinity death points. It is concluded that a great majority of the
species of the oyster bed community are limited in their upstream pene-
tration by salinity.
345
-------
2210.
Westernhagen, H.V. 1974. Incubation of garpike eggs (Belone
belone Linne) under controlled temperature and salinity con-
ditions. Jour. Marine BioI. Assn. U.K. 54:625-634.
Hatching rate of larvae from artificially fert~lized eggs was
maximal at 18 C and salinities between 15 and 33%0. Minimum tempera-
ture and salinity for viable larvae production was 12 C and 10%0.
2211.
Westernhagen, H.V. and V. Dethlefsen. 1975. Combined effects of
cadmium and salinity on development and survival of flounder
eggs. Jour. Marine BioI. Assn. U.K. 55:945-957.
Eggs of Baltic flounder Pleuronectes flesus were incubated in
cadmium-contaminated seawater (0, 0.1, 0.5, 1.0, 2.0, 3.0, 5.0 mg/l) at
4 salinities (16, 25, 32, 42%0). Cd concentrations of 1.0 mg/l and
above caused the chorion of eggs to become soft and to burst on removal
from water. Effects of Cd on embryonic survival and viable hatch were
not dependent on salinity of incubating water but showed a straight
salinity dependence with survival being 40 to 50% for 25 and 42%0, and
15 to 20% at 32 and 160/00, compared to 80-90% in controls. At all
salinities, hatching rates and viable hatch were not adversely affected
by Cd concentrations of up to 1.0 mg/l; 2.0, 3.0 and 5.0 mg/l of Cd
caused marked decrease in hatching rates and viable hatch. Mean total
length, eye and otic capsule diameter did not appear to be adversely
affected by increasing cadmium concentrations in rearing medium. Highest
malformation rates (bent and crippled larvae) were obtained at 3.0 and
5.0 mg/l and at 16%0 S. Cd concentrations in mg/kg dry wt of eggs in
5.0 mg/l Cd were: 45 for 42%0, 60 for 32%0, 65 for 25%0 (fertili-
zation occurred), 87 for 25%0 (no fertilization), and 90 for 16%0.
Other Cd concentrations showed a similar trend: uptake increasing with
decreasing salinity.
2212.
Westernhagen, H.V., V. Dethlefsen and H. Rosenthal. 1975.
bined effects of cadmium and salinity on development and
survival of garpike eggs. Helgolander wiss. Meeresunters
27:268-282.
Com-
Eggs of Baltic Sea garpike Belone belone were incubated in
normal and Cd-contaminated seawater (0.05, 0.1, 0.5, 1.0, 2.0, 5.0 mg/l)
at 15%0, 250/00, and 35%0 Sand 15 C. Embryonic heart beat and
frequency of pectoral fin movements in prelarvae was greatly depressed
at Cd concentrations >0.5 mg/l. Embryonic survival and viable hatch
were unaffected in Cd concentrations of 1.0 and 0.5 mg/l, respectively.
At high Cd concentrations (2.0 and 5.0 mg/l) there was greater embry-
onic survival and viable hatch at comparatively high salinities. Cadmium
content of eggs was generally higher in lower salinities than in more
346
-------
saline water at comparable cadmium concentrations. Accumulation factors
of Cd in eggs were inversely proportional to the ambient Cd concentration.
Highest accumulation factors of more than 40 were recorded a~ 0.05 mg/l
Cd. At high cadmium concentrations accumulation factors were about 5.
2213.
Westernhagen, H.V.,
bined effects of
vival of herring
433.
H. Rosenthal and K.-R. Sperling. 1974. Com-
cadmium and salinity on development and sur-
eggs. Helgolander wiss. Meeresunters. 26:416-
Eggs of autumn spawning Baltic herring Clupea harengus were
incubated in Cd-contaminated water (0, 0.1, 0.5, 1.0, 5.0 mg/l) at 5%0,
16%0, 250/00 and 32%0 S. Effects of Cd on embryonic survival were
salinity dependent with deleterious effects of Cd and developing herring
embryos more pronounced in brackish water than seawater. Embryonic
activity as a measure of viability decreased in Cd concentrations with
decreasing salinity, with most pronounced effect of Cd at 5%0 S. Egg
diameter was never altered by Cd content of incubation water. In all
salinities incubation time was shortened with increased Cd content of
medium. At 5, 16, and 25%0 S and 0, 0.1, 0.5 and 1.0 mg Cd/I, hatch-
ing rate was not significantly altered by Cd. High hatching rates of 85
to 99% occurred in all salinity-Cd combinations. At Cd levels of 5.0
mg/l, there was. greater survival of embryos at salinities of 32 and 25%0
than at 16 and 5%0. Percentage viable hatch was unaffected at 32, 25
and 16%0 S and 0, 0.1, and 0.5 mg Cd/I. At 5%0 only 1% viable hatch
occurred at 0.5 mg/l; in 16%0, 61% viable hatch occurred at 1.0 mg/l
Cd. No viable larvae were obtained in any salinity at 5.0 mg/l Cd. In
all salinities mean total length decreased with increasing Cd concentra-
tion. Relative decrease in mean total length was minimum at 32%0 S.
At all 4 salinities, yolk sac volumes of newly hatched larvae increased
with increased Cd concentrations, probably due to declining embryo
activity. Cd concentrations (in ~g Cd/egg) of eggs in 5.0 mg/l Cd were:
0.013 for 32%0, 0.019 for 25%0, 0.04 for 16%0 and between 0.057 and
0.038 for 50/00. In general Cd content of eggs at any given Cd concen-
tration increased with decreasing salinity.
2214.
Wettern, V.M., D.W. Lorch and A. Weber. 1976. Die wirkung von
blei und mangan auf die grUnalge Pediastrum tetras in
axenischer kult~r. I. Speicherungsraten und beeinflussung
des wachstums. Arch. Hydrobiol. 77(3):267-276. (In German,
English summary)
Over the range 0 to 1.0 mg Mn/l, Mn concentration of axenic
freshwater algae cultures correlated linearly with ambient Mn level.
Maximum concentration factor was 73. All Mn concentrations stimulated
growth. Addition of Zn had no influence on growth but promoted Mn uptake.
347
-------
About 15% of bound Mn could be desorbed by a 10-3 M EDTA-solution. Pb
was accumulated only in small amounts; uptake was independent of solu-
tion concentration; Pb concentrations of 0 to 1.5 mg/l had no influence
on algal growth.
2215.
Whitfield, P.H. and A.G. Lewis. 1976. Control of the biological
availability of trace metals to a calanoid copepod in a
coastal fjord. Estuarine Coastal Marine Sci. 4:255-266.
Organic material present in natural waters and in sediments
alters availability of Zn, Mn, and Cu to prefeeding stages of Euchaeta
japonica. In the laboratory, survival decreased with a decrease in
amount of u.v. photo-oxidizable material. Replacement of the material
with a known chelating agent (EDTA) increased survival. Comparison of
survival in untreated water with that in different EDTA concentrations
provided an EDTA equivalent value and this was used to indicate the
natural complexing ability of water. An EDTA equivalent value was also
obtained for saltwater extracts of bottom sediments. Natural complexing
ability of deep water increased after a major intrusion of deep water
and decreased with increasing residence time. Complexing ability of
saltwater extractable material in bottom sediments appears to be depend-
ent upon nearsurface productivity.
2216.
Wieser, W. 1967. Conquering terra firma: The copper problem
from the isopod's point of view. Helgol. wiss. Meeresunters
15:282-293.
In marine isopods and amphipods, water flow maintained via
ciliary or muscular movements provides >6X copper needed. Food there-
fore contributes little to copper supply. Extraction of copper from
primary vegetable matter by intertidal species is difficult and possible
only at high Cu concentrations. Author suggests that microorganisms
will liberate Cu from its natural tightly bound state in decaying algae.
The amount of copper stored in hepatopancreas increases with increasing
dependence of the species on the terrestrial environment; intertidal
species exhibit intermediate Cu values. Copper is more strictly rele-
gated to storage cells of the hepatopancreas in terrestrial isopods
than in marine or intertidal isopod species. But in marine forms,
copper seems to be able to move more freely in an easily dissociable
state between storage cells and other cells of the hepatopancreas.
2217.
Willard, J.T. 1908. On the occurrence of copper in oysters.
Jour. Amer. Chern. Soc. 30:902-904.
348
-------
Two samples of oysters suspected of causing illness were
examine~ for copper. They contained 2110 and 3020 mg Cu/kg dry wt,
respectIvely. A total of 34 samples of fresh and canned oysters were
then tested; these contained between 50 and 1700 mg Cu/kg dry wt.
Author concludes that Cu is normally found in oysters but not in levels
as high as those of original samples.
2218.
Williams, L.G. 1970. Concentration of 85strontium and 137cesium
from water solutions by Cladqphora and Pithophora. Jour.
Phycol. 6:314-316.
The alga Pithophora accumulated Sr-85 and Cs-137 by respective
equilibrium concentration factors of 2106 and 1816 when 0.1 mg Ca and
0.1 mg K/l were also present; c.f. were 853 and 1514 in 30.1 mg Ca and
0.1 mg K/l; 2314 and 600 in 1.0 mg Ca and 30.0 mg K/l; and 1713 and 513
in 30 mg Ca and 30 mg K/l. Corresponding concentration factors for
another alga, Cladophora, were comparable.
2219.
Wilson, K.W. and P.M. Connor. 1971. The use of a continuous
flow apparatus in the study of longer-term toxicity of heavy
metals. Int. Coun. Explor. Sea. C.M. 1971/E8:343-347.
Newly-molted brown shrimp Crangon crangon were more vulnerable
to Cd and Hg than unmolted animals; smaller individuals were more sensi-
tive. LC-50 (48 h) values for Hg or Cd was 5 mg/l; after 1500 hr tests,
both metals were toxic at 0.005 and 0.05 mg/l, respectively.
2220.
Windom, H., W. Gardner, J. Stephens and F. Taylor. 1976. The role
of methylmercury production in the transfer of mercury in a
salt marsh ecosystem. Estuar. Coast. Mar. Sci. 4:579-583.
A salt marsh estuary near Brunswick, Georgia, which received
discharges of approximately one kg of inorganic Hg daily for 6 years, was
studied in order to evaluate occurrence and production of methylmercury.
The methyl form was not detected «1 ng/g) in marsh sediments or in the
dominant Spartina alterniflora vegetation, although the inorganic form
was present in amounts up to 1.47 mg/kg dry wt, with variation due to
distance from Hg source and Spartina plant part. Significant levels of
methylmercury were present in primary consumers Littorina irrorata, and
Uca sp. with concentrations up to 0.61 and 0.40 mg/kg dry wt, respectively
Assuming that these molluscs and crustaceans accumulated a significant
percentage of methylmercury produced in the salt marsh ecosystem, then
annual production is estimated at 50 mg/kg of total Hg in the upper 5 cm
of sediment column.
349
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2221.
Winner, R.W. 1976. Toxicity of copper to daphnids in reconsti-
tuted and natural waters. U.S. Environ. Protect. Agen. Rept.
EPA-600: 3-76-051, USEPA, Congdon Blvd., Duluth, Minn. 69 pp.
Toxicity of copper was compared for Daphnia magna cultured in
reconstituted versus pond water and fed on trout-pellet vs vitamin-
enriched algal foods. Effects of chronic Cu stress were highly variable
when tested in reconstituted waters, and this was attributed to vari-
ability in quality of distilled water used. Vitamin enriched algal food
proved excellent for maintenance of 6 species of Daphnia (Q. magna, Q.
ambigua, D. parvula, D. pulex, Q. pulicaria and Q. galeate-mendotae),
while animals reared on trout-granule food exhibited reduced longevity
and greater sensitivity to Cu. The two largest species, Q. magna and Q.
pulex, had 72 hr LC-50's of 0.086 mg Cu/l while the two smallest species,
Q. parvula and Q. ambigua, had 72 hr LC-50's of 0.072 and 0.067 mg Cu/l.
Acute toxicity of chromium was tested and the following 72 hr LC-50's,
in mg Cr/l, were: D. ambigua, 7.7; D. magna, 42.1; D. galeata, 65.6; and
Q. pulicaria, 110.8~ Maximum allowable toxicant concentration (MATC) was
estimated to be 0.04 mg Cu/l for D. magna, D. ambigua, D. parvula and
Q. pulex in pond water-algal system when longevity was used as a
criterion, and 0.01 mg Cu/l for D. magna tested in the trout-granule-pond-
water system. MATC based on longevity was estimated to fall between
0.050 and 0.075 mg Cu/l for Q. magna tested in unaerated, standard water
and between 0.015 and 0.020 mg Cu/l in aerated standard water. Repro-
ductive response to chronic Cu stress was more variable than longevity.
D. magna did not exhibit reduction in mean brood size at any Cu concen-
tration that reproduction occurred; a rise in reproduction rate was
observed at concentrations of 0.06 mg Cu/l and lower. No stimulatory
effects of Cu on brood sizes in D. pulex, D. parvula, or D. ambigua were
observed. D. pulex exhibited a significant reduction in mean brood size
at 0.08 mg/!, D. parvula at 0.06 mg/l and D. ambigua at 0.04 mg/l. D.
parvula, Q. pulex and Q. ambigua all exhibited restrictions in instan-
taneous rate of population growth (r) at Cu concentrations greater than
0.04 mg/l. Because of stimulatory effect of Cu on brood size in D. magna,
r did not decline in this species until chronic Cu stress exceeded O~
mg/l. Application factors for D. magna, D. pulex, D. parvula and D.
ambigua were 0.47, 0.57, 0.62 and 0.59, respectively.
2222.
Winner, R.W. and M.P. Farrell. 1976. Acute and chronic toxicity
of copper to four species of Daphnia. Jour. Fish. Res. Bd.
Canada 33:1685-1691.
Respective LC-50 (72 hr) levels of copper in ~g/l were 86.5,
86.0, 72.0 and 67.7 for Daphnia magna, D. pulex, D. parvula and D.
ambigua. Survival of all species was affected at->40 ~g Cu/l. Instan-
taneous rate of population growth (r) decreased at concentrations >60 ~g
Cu/l for Q. magna and >40 ~g Cu/l for other species. A decrease in brood
350
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size was observed at Cu levels >40 ~gjl for D. ambigua and >60 ~gjl for
Q. pulex and Q. parvula. Reproduction of Q.-magna was inhibited at Cu
levels >80 ~gjl due to death of prereproductive females. All species of
daphnids studied did not differ in susceptibility to chronic Cu stress.
2223.
Wlodek, S. 1966. The behavior of 137Cs in freshwater
with particular reference to the reactions of plant
to contamination. In Radioecological Concentration
Proc. Inter. Symp. ,:Stockholm, Apr. 25-29, Pergamon
897-912.
reservoirs,
communities
Processes.
Press, N.Y.:
Distribution of radiocesium in the ecological system due to
radioactive fallout contamination was calculated to be 7% in water, 91%
in sediments, and 3% in plants. In laboratory tank experiments the
presence of filamentous algae, predominantly Ulothrix, and Nasturtium,
both of which present large total surface areas to water, caused Cs-137,
which normally attains low levels rapidly, to remain high in water for
2 weeks. Strong sediment contamination occurred within 24 hrs, with up-
take of Cs increasing with organic content of sediments. When 3 levels
of contamination were studied (4 uCijl, 0.43 uCijl, and 0.046 uCijl),
activity levels in water and in plants were proportional; therefore,
levels of activity in plants may be used to characterize contamination
in the environment. Distribution of Cs in plants was not uniform, with
younger portions generally containing less Cs than older parts. Cs con-
tamination was not found to affect biomass production of plants. Studies
showed that water tends to give up its Cs quite rapidly to other parts
of the ecosystem. Except for Ulothrix, which retained >60% Cs for a
short period, plants generally playa modest part in Cs-137 accumulation,
with bottom sediments being dominant receptors. Secondary contamination
of water may occur due to strong agitation of plants, sudden changes of
water level in reservoir, gentle agitation of bottom sediments, or death
of plants. Results indicate that plants cannot be used to decontaminate
waters, but can be used as bioindicators for contamination if previous
histories and ecological conditions are considered.
2224.
Wolfe, D.A. 1970. Zinc enzymes in Crassostrea virginica.
Fish. Res. Bd. Canada 27:59-69.
Jour.
Nearly all the zinc in oysters is bound either to soluble high-
molecular weight proteins or to structural cellular components such as
cell membranes. Oyster alkaline phosphatase is a zinc metalloenzyme, as
indicated by in vitro inhibition studies with various metal-binding
agents. Dialysis of soluble tissue extracts at pH 7-9 removes up to 96%
of the total Zn without effect on alkaline phosphatase. If alkaline
phosphatase is considered representative of the metabolic functions of Zn
in oysters, most Zn accumulated by oysters must be superfluous to the
animal's requirements.
351
-------
2225.
Wolfe, D.A. 1974. The cycling of zinc in the
estuary, North Carolina. In Vernberg, F.J.
(eds.). Pollution and Physiology of Marine
Press, New York: 79-99.
Newport River
and W.B. Vernberg
Organisms, Academic
A model was constructed for Zn flux that provides for primary
production by phytoplankton and Spartina, conversion of part of this pro-
duction to detritus by heterotrophic microorganisms, direct consumption
of part of the phytoplankton production by zooplankton and herbivorous
macrobiota, and consumption of detritus either directly or indirectly
after microbial assimilation. The role of juvenile fish in the summer
cycle of Zn within the estuary was estimated by this model to be: 1065
g/day ingested, 56 g/day assimilated, and 1009 g/day defecated. These
figures are based on 3 fish species (menhaden, spot, and pinfish) which
compose >40% of total nekton and epibenthic macrofaunal biomass in the
estuary. A test of the hypothesis: only 10% detrital Zn is ultimately
assimilated by microbiota and meiofauna thereby becoming available to
macrofauna, was attempted through analysis of Zostera, benthic algae,
and detritus for Zn. Mean values obtained were 84 mg/g dry wt (Zostera),
33 to 120 mg/g dry wt (algae), and 49 mg/g dry wt (detritus); results
were inconclusive. Wolfe's model indicates that Zn is highly conserved
and recycled approximately l6X per year. It also suggests that Zn occurs
in more than one physicochemical form, with the form involved in bio-
logical cycling being distinct from that involved in sediment-water
exchange. Additional flushing of dissolved and suspended Zn in the water
column exerted little effect on biological fluxes around phytoplankton
and detritus.
If the estuary is considered a closed system, turnover can be
expressed as the fraction of exchangeable sediment Zn which is cycled
annually through biota of the system. If the system extends to a depth
of 1 m into sediments (the depth of Spartina root penetration). annual
phytoplankton and Spartina incorporation of Zn (60.5 mg Zn/m2 yr) would
produce a turnover of about 0.8% per year. Thus, at least 100 years would
be required to equilibrate any additions of Zn with the large reservoir
represented by the deep sediment compartment. Surface sediments, how-
ever, are probably involved in a more rapid dynamic equilibrium with
metals dissolved in the overlying and interstitial waters, due to a con-
stant resuspension of fine silt, clays, and detritus, and to burrowing
activities in the upper several cm of sediments. Turnover of Zn in the
system can also be discussed as an open system, in terms of proportion
of total Zn in the annual biological cycle which is exported annually
from the system. Thus, the combination of commercial catch (0.19 mg
Zn/m2 yr), emigration of macrofauna (0.10) and flushing of zooplankton
(0.011) and phytoplankton (0.3) accounts for ~l% of total Zn incorporated
annually by primary producers Spartina and phytoplankton (60.5 mg Zn/m2
yr). This same estimate of biological export represents ~1/6 of annual
import in runoff from the watershed. Both considerations support the
352
-------
conclusion that the Newport River estuary
for Zn and approaches a closed system for
metal.
has a great retentive capacity
biological cycling of this
2226.
Wood, J.M., F.S. Kennedy and C.G. Rosen. 1968. Synthesis of
methylmercury compounds by extracts of a methanogenic bacterium.
Nature 220:173-174.
Transfer of methyl groups from methylcobalamine to Hg2+ occurs
naturally in mild reducing conditions. Anaerobic extracts of a methano-
genic bacterium culture from canal mud at Delft, Holland, enhance this
process, providing Me-Hg for incorporation into aquatic environments.
2227.
Woodhead, D.S. 1973. Levels of radioactivity in the marine
environment and the dose commitment to marine organisms. In
Radioactive Contamination of the Marine Environment, IAEA-5m-
158/31, Vienna: 499-525.
Published data on levels of radioactive elements, Sb, Cs, Co,
Eu, Fe, Pb, Mn, Ni, Nb, Pm, Po, Pu, K, R~~ Rb, Ag, Sr; Th, U, Y, Zn,
and Zr, in seawater, the sea bed and marine biota from natural sources,
fallout and waste disposal operations are reviewed. As a starting point
for calculations of dose-rates to marine organisms data have several
deficiencies. A complete set of data for all isotopes (natural and
artificial) is not available for either a single species or even for
groups of organisms. To calculate dose-rates, simple models have been
employed to represent phytoplankton, zooplankton, mollusca, crustacea,
and fish. Little known information on differential distributions within
organisms and the prescription of standard volumes to each group present
serious limitations. Within these limitations results of calculations
show that, in a global context, dose-rates to marine biota from artifi-
cial radionuclides are of same order as those from natural background
sources, and weapons-test fallout is the major contributor. Practice
of marine disposal of radioactive waste leads to locally high dose-rates,
but in population or global terms, dose-rate contribution is and will
probably remain negligible.
~
2228.
Wort, D.J. 1955. The seasonal variation in chemical composition
of Macrocystis integrifolia and Nereocystis luetkeana in
British Columbia coastal waters. Canadian Jour. Botany 33:
323-340.
Two species of seaweeds collected from Port Hardy and Van-
couver, B.C. between October 1949 and September 1951 were analyzed for
various inorganic and organic chemical species. Two year averages of
353
-------
copper; zinc, and iron in mg/kg dry wt (range), were: Macrocystis:
Cu-fronds 59 (14-243), stipes 22 (4-87); Zn-fronds 97 (14-335). stipes
21 (10-34); Fe-fronds 562 (100-3250), stipes 125 (30-400). Nereocystis:
Cu-fronds 46 (3-140), stipes 29 (7-70); Zn-fronds 424 (90-2800), stipes
74 (7-310); Fe-fronds 153 (4-420), stipes 124 (30-360).
2229.
Wright, D.A. 1976. Heavy metals in animals from the north east
coast. Marine Poll. Bull. 7(2):36-38.
Cadmium, zinc, copper and nickel levels in mg/kg wet wt in
muscle of fish collected from the Northumberland coast of England ranged
from 0.12 to 1.44 for Cd, 1.9 to 119.0 for Zn, 0.5 to 4.6 for Cu and 0.5
to 7.2 for Ni. Concentrations for gill, axial skeleton, skin, stomach
wall, liver, fat body, kidney and gonad levels were also presented.
Whole body metal levels in mg/kg wet wt for crustaceans ranged from 0.98
to 2.80 for Cd, 23.7 to 28.9 for Zn, 6.8 to 10.9 for Cu, and 6.5 to 9.8
for Ni. Values for selected crustacean tissues were also presented.
2230.
Wurtz, C.B. 1962. Zinc effects on fresh-water molluscs.
Nautilus 76(2):53-61.
One year after mine water discharge leading to 10 mg/l peaks
of Total Heavy Metals (THM = Zn, Pb, Cu), molluscs were absent in a 19
km stretch of the NW Miramichi River, although levels below 1 mg THM/l
prevailed at that time. However; macroinvertebrates representing 77
species and several phyla were present.
In laboratory studies adult pond snails Physa heterostropha
exhibit LC-50 (48 hr) values of 3.62 mg Zn/l and 0.069 mg Cull at water
hardness of 100 mg Ca C03/l, but 1.11 mg Zn/l at hardness of 20 mg Ca
C03/l; juveniles were more sensitive to Zn than adults. Young Physa
were about 3X more sensitive to Zn at 11 C than 32 C. Ramshorn snails
Helisoma campanulatum exhibit an LC-50 (96 hr) value of 1.27 mg Zn/l at
22 C in hard water; however. unlike Physa, resistance was greater at
11 C. Helisoma, as was true for Physa, were more sensitive to Zn in
softwater (20 mg Ca C03/l).
2231.
Yamamoto, T., T. Yamaoka, T. Fujita and C. Isoda. 1971.. Chemical
studies on the seaweeds (26) Boron content of seaweeds. Rec.
Oceanogr. Works Japan 11(1):7-13.
Boron content of 52 samples of 41 species of seaweeds from
Wakayama Pref., Japan ranged from 16 to 319 mg/kg dry wt, with an
average of 106 mg/kg. For ash, the range was 231 to 3038 mg B/kg with
an average of 762.
354
-------
2232.
Yamamoto, Y., T. Fujita and M. Ishibashi. 1970. Chemical
studies on the seaweeds (25) Vanadium and titanium contents
in seaweeds. Rec. Oceanogr. Works Japan 10(2):125-135.
Average vanadium levels in mg/kg dry wt of brown, green, and
red seaweeds, and limnetic weeds, were 3.1, 3.4, 2.8 and 1.1, respec-
tively- For titanium these were 33.9. 40.9. 21.8 and 38.1, respectively
2233.
Yamanaka, S. and K. Ueda.
by man-made pollution.
(4):409-414.
1975. High ethylmercury in river fish
Bull. Environ. Contamin. Toxicol. 14
During heavy industrial ethylmercury pollution of the Jinzu
River in 1969, ayu (Plecoglossus altivelis) and dace (Tribodon
hakonensis) contained, respectively, 2.33 and 2.01 mg/kg ethyl-Hg and
2.72 and 4.65 mg/kg total Hg. In 1970, after ethyl-Hg input had ceased,
ayu, which has a one year life cycle, had ethyl-Hg and total Hg concen-
trations of 0.2 and 0.3 mg/kg, respectively. However, dace, which lives
for several years, did not drop to control levels until four years
later; indicating a long biological half-life for Hg. Methylmercury
levels in both species did not exceed 0.3 mg/kg during the 1969-1973
study period. Differences in contamination of fish with Hg from man-
made and geological sources are discussed.
2234.
Yoshimura, A., H. Tada, M. Sakai, T. Harada and K. Oishi. 1976.
Distribution of inorganic constituents of Kombu blade - III
Inorganic constituents of acceleratedly cultured ma-kombu at
various growth stages. Bull. Jap. Soc. Sci. Fish. 42:661-664.
(In Japanese, English summary)
The algae Laminaria japonica, in accelerated culture near
Hakodate, Japan was analyzed for inorganic constituents. More than 70%
of the ash consisted of Cl-, K+ and Na+; these remained relatively con-
stant during the study (April-July 1968). Nutrient ions such as Fe3+,
A13+, Ca2+, and Mg2+ increased in June and decreased in July; Mn2+
decreased steadily; Cu2+ increased after decreasin~ in May. Grou~s,
according to concentration factors, are: A13+, Cu +, Fe3+ and Mn +
(2 x 105 - 104); Si02 (2 x 102); K+, Ca2+ (70-10); and Mg2+, Cl-, and
Na+ (2.3-1.6).
2235.
Yoshinari, T.
by chitin.
chemistry.
Balances.
and V. Subramanian. 1976. Adsorption of metals
In Nriagu, J.D. (ed.). Environmental Biogeo-
Vol. 2. Metals Transfer and Ecological Mass
Ann Arbor Sci. Publ., Ann Arbor; Mich.: 541-555.
355
-------
Granular chitin was prepared from lobster shells and tested
for adsorption of metals. Chitin absorbed 40 to 60% of metals in
distilled water solution in 183 hrs, with accumulation independent of
initial concentration of metals in the 1 to 16 mg/l range. Ca2+
initially taken up by chitin was released back to solution after 40 hr;
pH of the solution decreased with increasing Ca retention by chitin
suggesting that Ca2+ and H+ may interchange positions. Uptake rates of
metals in 0.2 M, 0.4 M, and 0.6 M NaCl solutions were also determined.
Initial concentrations of Mg2+ and Ni2+ had little effect on adsorption
rates. As ionic strength decreased, amount of Mg2+ and Ni2+ adsorbed
decreased linearly. Ca behaves similarly when initial Ca2+ concentra-
tion is 1 mg/l. Adsorption of Zn, Pb, Co, Cu, Mn and Fe is less depend-
ent on variation of ionic strengths in the medium. Adsorption of a
mixture of metals showed that a steady state was reached in 9 hrs with
the following selectivity sequence in uptake of metals by chitin in
double distilled water: Zn > Ni > Co > Cu > Pb. After 50 hrs, the
following sorption sequence was recognized for metal uptake by chitin in
double distilled water: Ni > Zn > Co > Cu > Pb > Fe = Mn > Mg > Ca.
The general mechanism for chitin-metal complexation is discussed.
2236.
Young, D.R. 1974. Cadmium and mercury in the
Bight. Summary of findings, 1971 to 1973.
Water Res. Proj., 1500 E. Imperial Highway,
16 pp.
southern California
So. Calif. Coastal
El Segundo, Calif.
The Southern California Bight was monitored for mercury,
cadmium, and DOT. Digestive glands of mussels Mytilus californianus
contained Cd residues of 5.7 to 29 mg/kg dry wt, which were similar to
levels found in specimens from sparsely populated islands offshore and
indicating little regional contamination. Dover sole Microstomus
pacificus trawled from the bight, had liver concentrations in mg/kg dry
wt of 0.58 to 0.19 for Cd, and 0.11 to 0.19 for Hg, which are natural
levels and again indicate no accumulation. Sediments and anthropogenic
sources were also examined for Hg, Cd, and DOT contents.
2237.
Young, D.R. and D.J. McDermott. 1975. Trace metals in harbor
mussels. Ann. Rep. S. Calif. Coast. Water Res. Proj., E1
Segundo, Calif., June 30: 139-142.
Highest values recorded of selected metals in digestive gland
of mussels Mytilus edulis from intertidal zones of San Diego Harbor and
adjacent coastline, in mg/kg wet wt, were: 77.0 Cu; 7.4 Cr; 6.0 Ni; and
185.0 Zn. For gonads, maximum levels were 23.0 Cu; 3.0 Cr; 2.6 Ni; and
183.0 Zn. For muscle this was 53.0 Cu; 11.0 Cr; 14.0 Ni; and 172.0 Zn.
Remainder contained upper values of 34.0 Cu, 3.4 Cr, 2.6 Ni, and 244.0
Zn. Cu and Zn levels in harbor mussels were about 9 and 3X greater,
356
-------
respectively, than coastal specimens; Cr and Ni levels were the same
regardless of collection locale.
2238.
Young, E.G. and W.M. Langille. 1958. The occurrence of inorganic
elements in marine algae of the Atlantic provinces of Canada.
Canadian Jour. Botany 36:301-310.
Concentrations in mg/kg dry wt of various elements in 11
species of green, red and brown algae, ranged from: 16,300 to 47,200
for Na; 23,100 to 71,100 for K; 2,500 to 24,000 for Ca; 0.3 to >2.0 for
Ni; 0.09 to 6.25 for Co; 0.23 to 1.36 for Mo; 35 to 97 for Zn; 6 to 62
for Cu; 20 to 50 for Mn; and 2 to 58 for As. Chondrus crispus contained
8 mg Pb/kg dry wt. Thorough washing with tap water lowered content of
ash, Na, K, and Si, but did not affect concentrations of other elements.
No seasonal variation was detectable in concentration of trace elements
in~. cris~us. Differences in concentration were observed between frond
and stipe In two species of Laminaria.
2239.
Young, M.L. 1975. The transfer of 65Zn and 59Fe along a Fucus
serratus (L.) ~ Littorina obtusata (L.) food chain. Jour.
Mar. BioI. Assn. U.K. 55:583-610.
Zinc-65 was rapidly accumulated by F. serratus. The concentra-
tion factor (c.f.) of 10,768 had not stabilized at day 40, and remained
high when algae were transferred to unlabelled seawater. Concentration
of zinc in F. serratus is the result of a process of accumulation through-
out the life of the plant. Iron-59 reached an equilibrium c.f. of 2000-
2500 after 70 d. Some exchange of Fe-59 between labelled algae and sea-
water was observed, but it appears that Fe concentrations in F. serratus
are largely dependent on age of tissue, as is the case for Zn~
In the laboratory, neither metal was accumulated up the food
chain. The chain appears to be more important than direct uptake from
water for accumulation of zinc and Zn-65, and iron and Fe-55 by L.
obtusata. Results show that the food chain accounts for 60% of Zn-65
accumulation with an input of 1.1 ug Zn/g tissue/day to total tissue
concentration of 46.7 ug Zn/g, and 42% of Fe-59 with an input of 0.91 ug
Fe/g tissue/day to total tissue concentration of 34.6 ug/g. L. obtusata
reacted similarly to Zn and Fe ingested in food, including similar rate
of excretion from L. obtusata tissues.
Environmental samples of seaweeds gave Zn c.f. of 3600-9700 for
Ascophyllum nodosum, 5200 to 12300 for ~. serratus, and 4700 to 11300 for
F. vesiculosus; c.f. varied with collection locale and with season in the
case of Fucus sp. Analysis of environmental samples of l. obtusata
indicated that it possesses some ability to regulate concentration of Zn
in its tissues against changes in Zn content of food. This results in
357
-------
accumulation of Zn up the food chain when Zn content of food is low. L.
obtusata from four sites contained up to lOX greater Fe residues than -
observed in the laboratory, possibly due to contamination by fine par-
ticulate matter trapped in the mantle cavity; no relation between Fe con-
centrations in L. obtusata and Fe in food was observed. The relevance
of the results to radioecology and heavy metal pollution studies is
discussed.
2240.
Zaroogian, G.E. and S. Cheer. 1976. Cadmium accumulation by the
American oyster, Crassostrea virginica. Nature 261:408-410.
Oysters in their third year were immersed in flowing raw sea-
water containing 5 ~g of Cd2+/1 (range 4.7-5.3 ~g/l), as CdC12 . 2~2
H20, for 40 weeks (November 1973 to August 1974). Whole body content of
cadmium increased progressively from 2.72 mg/kg wet wt ,at start to 13.57
mg/kg wet wt after 40 weeks, a concentration considered potentially harm-
ful to human health. Most of the increase occurred between weeks 28 and
40 when water temperatures ranged between 16.4 and 22.6 C. Control
oysters held in seawater containing 0.1-0.2 ~g Cd/1 for the 40 week study
always exhibited whole body residues between 1.69 and 2.81 ~g Cd/kg wet
wt.
2241.
Zeitoun, I.H., D.E. U11rey, J.E. Ha1ver, P.I. Tack and W.T. Magee.
1974. Influence of salinity on protein requirements of coho
salmon (Oncorhynchus kisutch) smo1ts. Jour. Fish. Res. Bd.
Canada 31:1145-1148.
Six purified diets ranging from 30 to 55% protein were fed for
10 weeks to duplicate groups of coho salmon smo1ts maintained at 10 or
20%0 salinity. Results demonstrated minimum protein requirements did
not differ for fish at either salinity, and that weight gain and protein
retention plateaued after 40% dietary protein was attained.
2242.
Zeitoun, I.H., D.E. U11rey and P.I. Tack. 1974. Effects of water
salinity and dietary protein levels on total serum protein and
hematocrit of rainbow trout (Sa1mo gairdneri) fingerlings.
Jour. Fish. Res. Bd. Canada 31:1133-1134.
Seven separate diets ranging from 30 to 60% protein in 5%
increments were fed for 10 weeks to trout maintained at 10 and 20%0
salinity. Water salinity and dietary protein concentration did not
significantly influence total serum protein. Hematocrit increased sub-
stantially with salinity (35.3% for fish at 100/00 and 39.1% for those
at 20%0), but different levels of dietary protein did not affect this
parameter.
358
-------
2243.
Zeitoun, I.H., D.E. Ullrey, W.G. Bergen and W.T. Magee. 1976.
Mineral metabolism during the ontogenesis of rainbow trout
(Salmo gairdneri). Jour. Fish. Res. Bd. Canada 33:2587-2591.
Unfertilized oocytes and post yolk-absorption-stage larva of
trout contained respective metal levels, in g/kg dry wt of: 0.9 and
<0.01 for Ca; 1.4 and <0.05 for Mg; 3.4 and <0.01 for Na; 4.5 and <0.01
for K; 0.0761 and <0.00001 for Fe; 0.013 and <0.00001 for Cu; and 0.061
and <0.00005 for Zn. Derivation of-Ca, Na, K, Fe, and Zn from water
environment at post yolk absorption was estimated to be at least 70, 76,
45, 68, and 2~ respectively. All Cu in larva could have been derived
from unfertilized oocyte.
2244.
Zitko, V. 1975. Toxicity and pollution potential of thallium.
Science Total Environ. 4:185-192.
Although world production of thallium amounts to 10 to 12
tons/yr, up to 48 t/yr of thallium may be present in wastes from zinc
production in Canada alone. Atlantic salmon are relatively sensitive
to Tl: the LC-50 value is 0.03 mg Tl/l. The following lethal doses in
mg/l for thallium have been reported: 10 to 15 for rainbow trout, 60 for
perch, 40 to 60 for roach (fish), 0.4 for tadpole, 2-4 for Daphnia. and
4 for Gammarus. Growth inhibition occurs at levels of 20, 390 and 200
mg/l for Azotobacter, Proteus mirabilis, and Aspergillus ni,er, respec-
tively. LC-50's of fish for other metals include 0.2 mg Hg 1 for
stickleback. 0.09 mg ethylmercury/l for rainbow trout, 1.4 to 19 mg Cd/l
for fathead minnow, 0.8 to 1.3 mg Pb/l for rainbow trout, 0.05 to 0.5 mg
Cull for minnow and salmon, and 0.6 to 10 mg Zn/l for minnow and salmon.
In Atlantic salmon, thallium had an accumulation coefficient (tissue
conc mg/kg wet wt: water conc mg/l) of 130 in muscle, 170 in liver and
480 in gills. Combined effects with other naturally occurring chemicals,
antidotes and sources of thallium pollution are discussed.
2245.
Zitko, V. and W.V. Carson. 1975. Accumulation of thallium in
clams and mussels. Bull. Environ. Contamin. Toxicol. 14(5):
530-533.
Clams Mya arenaria accumulated up to 6.03 and 12.45 mg/kg dry
wt of thallium during exposure for 88 days to 50 and 100 ~g/l Tl, respec-
tively. After depuration for 30 days, thallium levels were <0.5 mg/kg
dry wt. Mussels Mytilus edulis accumulated up to 4.26 and 6.33 mg Tl/kg
dry wt during exposure for 40 days to 50 and 100 ~g Tl/l, respectively.
Thallium levels in mussels fell to <0.5 mg/kg 7 days after termination
of exposure. Thallium levels in controls of both species were always
<0.5 mg/kg dry wt. It was concluded that thallium is not an environ-
mental danger to aquatic molluscs.
359
-------
2246.
Zitko, V. and W.G. Carson. 1976.
water hardness on the lethality
Chem~sphere 5(5):299-303.
A mechanism of the effects of
of heavy metals to fish.
In flowing water bioassays with juvenile Atlantic salmon Salmo
salar, toxicity of Zn is slightly decreased by increased concentrations
of Ca and considerably decreased by Mg; but Mg and Ca do not affect bio-
cidal properties of Cu and Cd. Authors stated that competition for
active sites between Mg and Zn could account for effects of water hard-
ness on Zn toxicity to fish. Mechanism of effects of hardness on toxi-
city of relatively weakly bound toxic cations, such as Be and Ni may be
similar. The competition does not playa significant role in cases of
very strongly bound cations, such as Cu and possibly Hg, or those acting
on specific target sites, of which cadmium may be an example..
360
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SECTION III
INDEX
Three indices are presented: INDEX-METALS, INDEX-TAXA, and INDEX-
AUTHORS. Each index encompasses this volume and the two preceding
vol~es in this series, namely, Eisler, R. 1973. Annotated bibli-
ography on biological effects of metals in aquatic environments
(No. 1-567). U.S. Environmental Protection Agency Report R3-73-007:
287 pp.; Eisler, R. and M. Wapner. 1975. Second annotated bibliog-
raphy on biological effects of metals in aquatic environments (No.
568-1292). U.S. Environmental Protection Agency Report 600/3-75-008:
400 pp.
361
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INDEX - METALS
ACTINIUM
Algae: 1016
Crustacea: 1016
Fish: 1016
Insecta: 1016
ALUMINUM
Algae: 535, 792, 992, 1130, 1289, 1405, 1425, 1498, 1499, 1503,
1522, 1669, 2183, 2188, 2234
Annelida: 535
Bacteria: 535, 1173, 1425, 1486, 1812, 2094
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 2183
Coelenterata: 535, 1131, 1392, 1503, 1867
Crustacea: 409, 428, 506, 535, 546, 626, 992, 1063, 1289, 1425,
1498, 1499, 1503, 1520, 2043, 2183, 2188
Ctenophora: 2183
Echinodermata: '535, 1131, 1503, 1867, 2198
Fish: 18, 142, 156, 409, 428, 452, 506, 535, 754, 761, 795, 796,
898, 940, 945, 1235, 1465, 1520, 1628, 1717, 1728, 1873,
2007, 2051, 2141, 2184, 2188, 2194
Higher Plants: 535, 570
Insecta: 1283, 1284, 1558
Miscellaneous: 505
Mollusca: 216, 428, 506, 535, 649, 670, 1106, 1162, 1486, 1503,
1794, 1867, 1993, 2188
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 535, 1503
Protozoa: 535, 1503, 1793, 2043
Sediments: 1486
Tunicata: 535
AMERICIUM
Annelida: 1354
Coelenterata: 1927
Fish: 1968
362
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ANTIMONY
Algae: 483, 535, 541, 851, 932, 951, 1038, 1208, 1234, 1425, 1522,
1627, 1676, 1835, 1917, 1959, 2009, 2019, 2024, 2117, 2188,
2208, 2227
Aves: 541, 851, 1038, 1676, 2024, 2208
Bacteria: 535, 842, 1177. 1425
Brachiopoda: 535
Bryazoa: 535
Bryophyta: 1038, 1676, 1917
Coelenterata: 535, 851, 1627, 1676, 1927, 2208
Crustacea: 13, 535, 541, 851, 952, 1038, 1039, 1210, 1234, 1384,
1425, 1627, 1676, 1959, 2019, 2024, 2117, 2188, 2208,
2227
Echinodermata: 535, 1038, 1676, 2024, 2208
E1asmobranchii: 1627
Fish: 274, 334, 535, 541, 851, 940, 951, 952, 1038, 1210, 1234, 1465,
1676, 1831, 1912, 1917, 2000, 2001, 2009, 2019, 2023, 2024,
2117, 2173, 2188, 2227
Higher Plants: 535, 541, 1038, 1676, 1835, 1917
Mammalia: 541, 851, 933, 1038, 1676, 2024
Mollusca: 466, 535, 541, 638, 951, 1038, 1039, 1224, 1234, 1384,
1627, 1676, 2019. 2023, 2024, 2117, 2118, 2188, 2208, 2227
Phoronidea: 535
Plankton: 466, 1959
Porifera: 535, 1038,
Protozoa: 535, 1627,
Sediments: 466, 541,
Tunicata: 535, 1627
1627, 1676, 1917, 2208
1957
951, 2117
ARSENIC
535, 632, 706, 735, 748, 815,
1400, 1407, 1411, 1425, 1455,
1522, 1604, 1605, 1627, 1631,
1839, 1841, 1962, 1982, 2011,
Algae: 37, 42, 338, 420,
1203, 1208, 1382,
1499, 1500, 1518,
1835, 1836, 1837,
2188, 2238
Amphibia: 2011
Annelida: 535, 1238, 1382, 1436, 2137
Aves: 1382, 1386, 1518, 2024
Bacteria: 535, 571, 657, 1282, 1400, 1425, 1486, 1734
Brachiopoda: 535
Bryazoa: 535, 1382
Chaetognatha: 1408
Coelenterata: 535, 1097, 1382, 1386, 1400, 1627, 1631
363
951, 959,
1462, 1498,
1735, 1830,
2024, 2137,
-------
Crustacea: 12, 92, 342, 520,
1039, 1203, 1249,
1411, 1425, 1455,
1525, 1552, 1604,
1755, 1813, 1834,
2188
Echinodermata: 535, 1238, 1382, 1386, 1631, 1776, 1837, 1962, 2024,
2137
E1asmobranchii: 1386, 1627, 1813
Fish: 37, 42, 70, 142, 166, 205, 245, 274, 334, 342, 520, 531, 535,
735, 748, 815, 951, 952, 977, 979, 1067, 1203, 1257, 1269,
1347, 1382, 1386, 1400, 1407, 1408, 1455, 1462, 1465, 1500,
1508, 1518, 1550, 1552, 1596, 1604, 1605, 1647, 1697, 1698,
1728, 1735, 1755, 1813, 1830, 1831, 1832, 1833, 1834, 1837,
1838, 1839, 1840, 1940, 1961, 1962, 1989, 2011, 2024, 2048,
2099, 2137, 2141, 2173, 2188
Fungi: 735
Higher Plants:
535, 626, 632, 706, 735, 952,
1347, 1382, 1386, 1400, 1407,
1462, 1493, 1494, 1498, 1499,
1605, 1627, 1647, 1697, 1698,
1837, 1839, 1962, 2011, 2024,
1408,
1518,
1735,
2137;
531, 535, 748, 1118, 1203, 1382, 1697, 1830, 1835,
1837, 2011
Insecta: 1203, 1518, 1550, 2011
Mammalia: 581, 933, 1382, 1385, 1386, 1462, 1494, 1500, 1550, 1596,
1830, 1834, 1837, 2024
Mollusca: 338, 456, 534, 535, 670, 951,
1386, 1407, 1455, 1462, 1487,
1604, 1605, 1627, 1631, 1685,
1839, 1845, 1910, 1962, 2011,
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 535, 1238, 1386, 1518, 1627, 2137
Protozoa: 535, 1203, 1627
Reptilia: 2011
Rotifera: 706, 1830
Sediments: 951, 1486, 1962, 1982
Tunicata: 535, 1627, 1883, 2038
982, 1039, 1238, 1347, 1382,
1493, 1500, 1525, 1596,
1697, 1813, 1834, 1837,
2024, 2118, 2137, 2188
BARIUM
Algae: 56, 228, 628, 992, 1112, 1130, 1208, 1425, 1498, 1518, 1522,
1627, 1669, 1868, 2183, 2188
Amphibia: 897, 2058
Annelida: 535, 1868
Aves: 1518
Bacteria: 535, 571, 1425
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 2183
Coelenterata: 535, 965, 1392, 1627, 1868
364
-------
Crustacea: 13, 360, 535, 626, 992, 1039, 1425, 1498, 1518, 1627,
1740, 1849. 1868, 2183, 2188
Ctenophora: 2183
Echinodermata: 535, 1868
Elasmobranchii: 1627, 1868
Fish: 56, 142, 156, 245, 273, 360, 450, 535, 754, 797, 898, 940,
945, 1218, 1235. 1465, 1518, 1628, 1728, 1868, 2007, 2188,
2194
Higher Plants: 535
Insecta: 797, 1518, 1558
Mammalia: 202, 797
Miscellaneous: 392
Mollusca: 535, 557, 769, 1039. 1106, 1563, 1627, 1868, 1978, 2188
Phoronidea: 535
Platyhelminthes: 1739, 1740
Porifera: 535, 1518, 1627, 1868
Protozoa: 535, 1627
Tunicata: 535, 1627, 1868
BERYLLIUM
Algae: 535, 1038, 1130. 1208, 1498, 1499, 1522, 1676, 1917, 2183,
2188
Amphibia: 138, 2058
Annelida: 535
Aves: 1038, 1676
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
Bryophyta: 1038, 1676, 1917
Chaetognatha: 2183
Coelenterata: 535, 1676
Crustacea: 535, 1038, 1498, 1499. 1676, 2183, 2188
Ctenophora: 2183
Echinodermata: 535, 1038, 1676
Fish: 156, 271, 512, 535, 751, 754, 940, 1038, 1101, 1182, 1183,
1676, 1917, 2188, 2246
Higher Plants: 535, 1038, 1676, 1917
Mammalia: 1038, 1676
Mollusca: 535, 1038, 1101, 1676, 2188
Phoronidea: 535
Porifera: 535, 1038, 1676, 1917
Protozoa: 535
Tunicata: 535
BIS~lliTH
Algae:
535, 541, 1016, 1130, 1208, 1498, 1522, 1627, 2188, 2208
365
-------
Annelida: 535
Aves: 541, 2208
Bacteria: 535, 842
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535, 1627, 1927, 2208
Crustacea: 535, 541, 1016, 1498, 1627, 2188, 2208
Echinodermata: 535, 2208
E1asmobranchii: 1627
Fish: 535, 541, 940, 1016, 2188
Higher Plants: 535, 541
Insecta: 1016
Mammalia: 541
Mollusca: 65, 535, 541, 1627, 2188, 2200, 2208
Phoronidea: 535
Porifera: 535, 1627, 2208
Protozoa: 535, 1627
Soils: 541
Tunicata: 535, 1627
BORON
Algae: 983, 1330, 1498, 1522, 1643,
Coelenterata: 965
Crustacea: 1039, 1498, 1520, 2144
Echinodermata: 1776
Fish: 1520, 1628, 1728, 2007, 2144
Higher Plants: 570
Mollusca: 1039, 2036, 2144
1817, 1979, 2231
CADMIUM
Algae: 242, 269, 486, 535, 632, 648, 683, 802, 833, 862, 873, 951,
959, 992, 1025, 1110, 1296, 1349, 1381, 1382, 1411, 1425,
1445, 1448, 1449, 1492, 1498, 1499, 1522, 1579, 1627, 1672,
1720, 1754, 1767. 1773, 1846, 1860, 1901, 1947, 1991, 2024,
2082, 2106, 2107, 2137, 2166, 2167, 2188
Amphibia: 897, 1171, 2058, 2244
Annelida: 155, 468, 535, 648, 653, 873, 994, 1121, 1305, 1382, 1428,
1436, 1869, 2014, 2137, 2147, 2167
Aves: 995, 1382, 2024
Bacteria: 535, 571, 1425, 1448, 1449, 1472, 1486, 1606, 1785, 1786,
1846, 1884, 1997, 2094, 2244
Brachiopoda: 535
Bryazoa: 535, 648, 1382
Bryophyta: 873
Chaetognatha: 1408, 1758
Coelenterata: 535, 904, 1131, 1382, 1627, 1867. 1896, 1901, 2104
366
-------
Crustacea: 13, 92, 155, 468, 535, 626, 632, 648, 755, 759, 789, 837,
862, 952, 991, 992, 995, 1039, 1050, 1051, 1075, 1084,
1104, 1171, 1212, 1213, 1249, 1296, 1305, 1350, 1359,
1360, 1382, 1408, 1411, 1425, 1428, 1448, 1498, 1499,
1509, 1627, 1632, 1647. 1695, 1707, 1744, 1758, 1803,
1860, 1901, 2024, 2106, 2107, 2112, 2137, 2147, 2156,
2180, 2188, 2205, 2219, 2229, 2244
Echinodermata: 155, 535, 862, 1131, 1305, 1382, 1564, 1776, 1867,
1897, 1901, 2024, 2106, 2137, 2198
E1asmobranchii: 1227, 1564, 1627
Fish: .35, 106, 142, 155, 156, 191, 242, 271, 334, 363, 407, 441,
468, 507, 535, 616, 627, 640, 648, 678, 682, 745, 746, 751,
752, 753, 754, 755, 759, 802, 808, 837, 843, 844, 862, 873,
887, 898, 913, 940, 950, 951, 952, 972, 977, 979, 994, 995,
1002, 1020, 1021, 1092, 1093, 1104, 1121, 1122, 1138, 1151,
1171, 1218, 1227, 1235, 1269. 1322, 1328, 1346, 1367, 1372,
1382, 1408, 1427, 1440, 1448, 1449, 1453, 1459, 1465, 1564,
1613, 1647, 1662, 1684, 1695, 1728, 1808, 1838, 1850, 1872,
1873, 1906, 1908, 1933, 1935, 1940, 1971, 1981, 2008, 2024,
2032, 2092, 2102, 2106, 2107, 2112, 2129, 2137, 2141, 2166,
2173, 2186, 2187, 2188, 2206, 2211, 2212, 2213, 2229, 2236,
2244, 2246
Fungi: 1157, 1449
Higher Plants: 535, 681, 802, 873, 950, 995, 1382, 1454, 1539, 1775,
1842, 1886, 2107
537, 802, 1121, 1212, 1283, 1284, 1360, 1617, 1662,
Insecta: 468,
2147
Mammalia: 202, 279, 581, 933, 1382, 1439, 1694, 1775, 1808, 1861,
1935, 2022, 2024
Miscellaneous: 392
Mollusca: 155, 221, 242, 426, 475, 477, 535, 559. 560, 638, 639,
649, 670, 731, 755, 770, 789, 821, 862, 873, 875, 951,
982, 989, 994, 1023, 1039, 1084, 1104, 1115, 1121, 1162,
1305, 1321, 1382, 1415, 1445, 1448, 1486, 1564, 1589,
1591,1592,1627,1646,1758,1787,1845,1862,1867,
1901, 1910, 1923, 1974, 1975, 1991, 2024, 2081, 2105,
2106, 2107, 2135, 2137, 2147, 2148, 2149, 2156, 2176,
2188, 2199. 2200, 2236, 2240
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 535, 1627, 1901, 2137
Protozoa: 535, 679, 1171, 1448, 1449, 1627, 1846, 1901, 1969
Reptilia: 2026
Rotifera: 1440, 2123
Sediments: 478, 731, 787, 873, 950, 951, 995, 1445, 1486, 1901,
1969, 1991, 2106, 2107, 2236
Seston: 2204
Tunicata: 535, 1564, 1627, 1758
367
-------
CALC IUM
Algae: 37, 193, 269, 298, 381, 503, 535, 549, 602, 648, 674, 694,
737, 792, 846, 880, 978, 983, 992, 1070, 1071, 1102, 1110,
1112, 1250, 1399, 1402, 1406, 1437, 1449, 1464, 1498, 1499,
1522, 1532, 1599, 1627, 1673, 1722, 1759, 1774, 1779, 1843,
1859, 1868, 1963, 1979, 2011, 2024, 2046, 2065, 2138, 2145.
2183, 2207, 2218, 2234, 2238
Amphibia: 184, 317, 608, 897, 1535, 1953, 2011, 2058
Annelida: 115, 535, 648, 900. 1464, 1868, 1963, 2025, 2145, 2147
Aves: 1958, 2024
Bacteria and yeasts: 204, 535, 971, 1102, 1449, 1786, 2035
Brachiopoda: 535, 2145
Bryazoa: 535, 648, 2145
Chaetognatha: 1599. 2183
Coelenterata: 535, 965. 1131, 1319, 1392, 1464, 1478, 1599, 1627,
1777, 1868, 2025, 2145, 2179
Crustacea: 13. 31, 115, 299, 301, 381, 461, 467, 535, 602, 626, 645,
648, 674, 716, 737, 739, 749, 798, 806, 812, 829, 830,
991, 992, 1102, 1350, 1369, 1384, 1437, 1464, 1498, 1499,
1510, 1511, 1520, 1535, 1581, 1599. 1627, 1638, 1639,
1640, 1641, 1642, 1663, 1759, 1779, 1806, 1849, 1859.
1868, 1950, 1963, 2011, 2024, 2025, 2145, 2147, 2183,
2235
Ctenophora: 2183
Echinodermata: 530, 535, 872, 1131, 1464, 1868, 1897, 2024, 2025,
2145
E1asmobranchii: 153, 1531, 1569, 1627, 1868, 1963, 2004
Fish: 1, 2, 4, 7, 11, 22, 37, 69, 80, 95. 115, 128, 142, 156, 157,
184, 251, 262, 282, 301, 309, 356, 371, 380, 381, 443, 444,
445, 449, 459, 525, 528, 535, 648, 658, 664, 674, 737, 749,
754, 798, 806, 876, 898, 912, 940, 950, 980, 1054, 1071, 1094,
1119, 1197, 1198, 1199, 1221, 1228, 1235, 1302, 1306, 1314,
1369, 1378, 1379, 1437, 1449, 1465, 1497, 1520, 1534, 1535,
1569, 1576, 1628, 1633, 1650, 1651, 1652, 1662, 1684, 1710,
1711, 1717, 1728, 1751, 1759, 1796, 1808, 1820, 1827, 1868,
1938, 1954, 1976, 2004, 2007, 2011, 2024, 2047, 2051, 2138,
2178, 2243, 2246
Fungi: 1449
Higher Plants:
535, 570, 737, 880, 950, 1070, 1201, 1369, 1523,
1722, 1759, 1938, 2011, 2138
Insecta: 115, 602, 1283, 1535, 1558, 1617, 1662, 2011, 2147
Mammalia: 202, 1808, 1861, 2024, 2035
Miscellaneous: 392
Mollusca: 32, 33, 61, 65, 66, 115, 158,
674, 700, 749, 769, 806, 832,
1237, 1341, 1342, 1369, 1384,
1627, 1637, 1639, 1759, 1779,
368
184, 204, 530, 535, 629.
1033, 1078, 1106, 1162,
1437, 1444, 1464, 1535,
1792, 1814, 1868, 1887,
-------
Mollusca (cont.):
Phoronidea: 535,
Plankton: 1859
Platyhelminthes: 1535, 1739, 2145
Porifera: 535, 1464, 1627, 1868, 2145
Protozoa: 535, 1000, 1361, 1449, 1464,
Reptilia: 2011
Rotifera: 1805
Sediments: 184, 950, 1369
Tunicata: 535, 1599, 1627, 1868, 2145
1954,
2190
2145
1963, 2011, 2024, 2025, 2145, 2147, 2164
1599, 1627, 2136, 2145
CERIUM
Algae: 17, 28, 215, 323, 333, 383, 413, 415, 439, 440, 483, 535,
539,541,555,582,583,585,586,602,851,862,1029,1038,
1100, 1128, 1164, 1425, 1437, 1498, 1518, 1522, 1540, 1612,
1726, 1917, 1955, 1959, 1963, 2011, 2019, 2020, 2046, 2208
Amphibia: 2011
Annelida: 535, 583, 1088, 1944, 1963
Aves: 541, 851, 928, 1038, 1518, 2208
Bacteria: 535, 1425
Brachiopoda: 535
Bryazoa: 535
Bryophyta: 1038, 1917
Coelenterata: 535, 586, 851, 1944, 1955, 2208
Crustacea: 28, 111, 124, 265, 299, 413, 439, 471, 535, 539, 541,
582, 583, 586, 600, 790, 791, 850, 851, 862, 955, 1038,
1100, 1128, 1164, 1331, 1369, 1425, 1437, 1498, 1518,
1612, 1943, 1945, 1955, 1956, 1959, 1963, 2011, 2019,
2020, 2208
Detritus: 110, 111, 393, 415
Echinodermata: 535, 862, 1038, 1944, 1955, 2208
E1asmobranchii: 353, 1963
Fish: 28, 106, 207, 270, 323, 383, 439, 449, 471, 531, 535, 541,
582, 583, 586, 636, 851, 862, 928, 1038, 1083, 1088, 1156,
1164, 1369, 1437, 1465, 1518, 1540, 1612, 1917, 1955, 1956,
2011, 2019, 2020
Higher Plants: 413, 535, 541, 555, 1038, 1369, 1612, 1917, 2011
Insecta: 1518, 1558, 1617. 2011
Mammalia: 541, 851, 1038, 1956
Mollusca: 28, 190, 224, 383, 425, 439, 457, 466, 535, 539, 541,
582, 583, 586, 600, 862, 955, 1029, 1038, 1156, 1164,
1224, 1369, 1437, 1612, 1955, 1956, 1963, 1990, 2011,
2019, 2208
Phoronidea: 535
Plankton: 466, 1959
Porifera: 333, 535, 1038, 1518, 1917, 2208
369
-------
Protozoa:
Reptilia:
Sediments;
Tunicata:
413, 535, 1959
2011
466, 541, 1369, 1956
535, 1945
CESIUM
Algae: 28, 29, 53, 211, 222, 223, 242, 261, 300, 310, 383, 399, 413,
415, 532, 535, 541, 548, 555, 582, 583, 586, 762, 818, 840,
851, 862, 932, 1016, 1029, 1038, 1071, 1116, 1234, 1336,
1413, 1437, 1446, 1470, 1498, 1518, 1522, 1540, 1612, 1676,
1917. 1963, 2011, 2019. 2020, 2024, 2071, 2120, 2177, 2208,
2218, 2223, 2227
Amphibia: 19, 184, 399. 2011
Annelida: 83, 535, 583, 1088, 1442, 1963
Aves: 541, 851, 1038, 1518, 1676, 2024, 2208
Bacteria: 532, 535
Brachiopoda: 535
Bryazoa: 535, 1545
Bryophyta: 1038, 1676, 1917
Chaetognatha: 1758
Coelenterata: 83, 535, 586, 851, 1442, 1676, 1927, 2208
Crustacea: 28, 52, 82, 83, 84, 86, 261, 264, 265, 300, 306, 314,
361, 413, 498, 532, 535, 541, 582, 583, 586, 600, 762,
791, 831, 850, 851, 862, 955, 1016, 1038, 1039, 1116,
1210, 1234, 1350, 1369, 1413, 1437, 1438, 1442, 1446,
1470, 1498, 1518, 1612, 1676, 1758, 1815, 1956, 1963,
2011, 2019, 2020, 2024, 2153, 2208, 2227
Detritus: 393, 413, 415
Echinodermata: 83, 261, 535, 862, 1038, 1413, 1442, 1676, 2024, 2208
Elasmobranchii: 353, 890, 1085, 1442, 1963
Fish: 19, 28, 41, 52, 79, 156, 169, 170, 176, 184, 208, 222, 225,
226, 227, 242, 261, 264, 270, 273, 300, 305, 306, 310, 314,
315, 324, 361, 371, 372, 373, 374, 383, 386, 399, 400, 449,
450, 535, 540, 541, 582, 583, 586, 636, 754, 762, 793, 805,
831, 851, 853, 862, 865, 884, 890, 915, 940, 1016, 1035, 1038,
1055, 1071, 1083, 1085, 1088, 1156, 1194, 1210, 1234, 1235,
1343, 1369, 1413, 1437, 1442, 1446, 1465, 1470, 1518, 1540,
1557. 1612, 1628, 1676, 1783, 1796, 1799, 1912, 1917, 1956,
2000, 2001, 2011, 2019, 2020, 2024, 2050, 2170, 2177, 2227
Higher Plants: 19, 306, 310, 399, 400, 413, 535, 541, 555, 568, 587,
818, 1038, 1369, 1424, 1612, 1676, 1917, 2011, 2223
Insecta: 587, 1016, 1518, 1558, 1617, 2011, 2177
Mammalia: 310, 541, 851, 1038, 1148, 1676, 1956, 2024
Miscellaneous: 358
Mollusca: 28, 52, 79. 83, 84, 184, 190, 194,
413, 425, 535, 541, 557, 582, 583,
957, 1029, 1038, 1039, 1078, 1156,
370
224, 242, 261, 361, 383,
586, 600, 838, 862, 955,
1234, 1277, 1278, 1332,
-------
Mollusca (cont.):
1369, 1413, 1437, 1442, 1446, 1470, 1612, 1676,
1758, 1956, 1963, 1990, 2011, 2019, 2024, 2050,
2208, 2227
Phoronidea: 535
Porifera: 535. 1038, 1518, 1676, 1917, 2208
Protozoa: 83. 415. 535
Reptilia: 2011
Sediments: 79, 184. 399. 541, 762, 818, 1277, 1369, 1956
Tunicata: 83, 535, 1758
CHROM IUM
Algae: 40. 383. 394. 526. 535, 539. 597, 632, 648, 683, 702, 788,
792. 932. 992, 1025, 1043, 1105, 1130. 1208, 1234, 1264,
1382. 1425. 1448. 1449, 1481, 1498, 1518. 1522, 1579, 1602,
1603. 1627, 1645. 1657, 1722. 1723, 1853, 1955. 1972, 2009,
2011, 2024. 2049. 2183, 2188
Amphibia: 1535. 2011
Annelida: 114. 434, 502. 535. 648, 994. 1081, 1121, 1382, 1603,
1941, 1942, 1957, 1972. 2014
Aves: 1382. 1518. 2024
Bacteria: 535. 571. 842. 1173, 1425, 1448, 1449, 1486, 1905, 1957,
2094
Brachiopoda: 535
Bryazoa: 535. 648. 1382
Chaetognatha: 2183
Coelenterata: 535, 965. 1131, 1382. 1392, 1627. 1955
Crustacea: 13. 40. 91, 124, 319, 409, 434, 453. 506,
597, 626. 632. 648. 702. 992. 1039, 1081.
1234. 1350. 1382, 1384. 1425. 1448, 1498,
1535. 1594, 1602. 1603. 1627, 1645. 1647,
1934. 1945. 1955. 2011. 2024, 2043, 2183.
Ctenophora: 2183
Echinodermata: 535. 1131. 1382, 1602. 1603, 1776, 1934, 1955. 2024
E1asmobranchii: 1627
Fish: 1, 19, 93. 94, 95. 98. 106, 142. 156. 185, 205. 241, 245,
273. 303. 334. 383, 394. 403. 407. 409. 460. 506, 529, 535,
538. 539. 591. 597. 605. 640, 648, 663, 665. 754, 799, 856,
898. 930. 940. 944. 950. 977. 994. 1021, 1069. 1121, 1122,
1178. 1210. 1219, 1234. 1235, 1299. 1300, 1371, 1382, 1440,
1448, 1449. 1465. 1518. 1535, 1602. 1603, 1628, 1645, 1647.
1728, 1795. 1873, 1908, 1955, 1972. 1981, 2001, 2007, 2009,
2010. 2011. 2024, 2037. 2077. 2116. 2141, 2173, 2188
Fungi: 1449
Higher Plants: 535. 788. 950, 1382. 1603, 1722. 1723, 2011, 2049
Insecta: 502. 537. 1121. 1283. 1284, 1518. 1535, 1558, 1617, 2011
Mammalia: 597. 788. 1382, 2024
Miscellaneous: 64
526, 535. 539,
1210, 1211,
1509, 1518.
1738, 1825,
2188, 2221
371
-------
Mollusca: 93, 224, 383, 394, 426, 475, 506, 535, 539, 598, 638, 649,
670, 705, 770, 821, 944, 994, 1037, 1039, 1105, 1121,
1162, 1224, 1234, 1309, 1321, 1382, 1384, 1448, 1450,
1486, 1535, 1589, 1591, 1602, 1603, 1627, 1645, 1787,
1934, 1937, 1955, 1972, 2011, 2024, 2081, 2188, 2200,
2237
Phoronidea: 535
Platyhelminthes: 1535, 1738, 1739
Porifera: 535, 1518, 1627
Protozoa: 535, 1448, 1449, 1627, 2043
Reptilia: 2011
Rotifera: 1440, 2123
Sediments: 950, 1486, 1972
Tunicata: 526, 535, 1457, 1627, 1945, 2038
COBALT
Algae: 193, 223, 224, 242, 261, 269, 333, 383, 471, 472, 541, 583,
628, 632, 648, 683, 792, 840, 849, 851, 885, 932, 973, 974,
975, ~83, 992, 1029, 1038, 1128, 1130, 1164, 1208, 1209, 1234,
1317, 1402, 1425, 1437, 1470, 1483, 1498, 1499, 1518, 1522,
1627, 1643, 1654, 1657, 1676, 1723, 1828, 1835, 1853, 1955,
1963, 2009, 2011, 2020, 2024, 2049, 2183, 2188, 2208, 2227,
2238
Amphibia: 79, 184, 260, 1171, 2011
Annelida: 468, 535, 579, 583, 648, 994, 1222, 1963
Aves: 541, 851, 928, 974, 1038, 1518, 1676, 1828, 2024, 2208
Bacteria: 535, 842, 1425, 1486, 1606, 1785, 1913, 2094, 2226
Brachiopoda: 535
Bryazoa: 232, 535, 648
Bryophyta: 1038, 1676
Chaetognatha: 312, 313, 1758, 2183
Coelenterata: 312, 535, 851, 965, 1131, 1627, 1676, 1927, 1955, 2208
Crustacea: 13, 91, 261, 312, 313, 468, 471, 507, 535, 541, 554, 561,
579, 583, 626, 632, 648, 784, 851, 973, 974, 975, 991,
992, 1038, 1039, 1075, 1128, 1164, 1171, 1174, 1210, 1234,
1286, 1315, 1316, 1317, 1318, 1350, 1384, 1425, 1437
1470, 1498, 1499, 1518, 1583, 1590, 1627, 1663, 1676,
1758, 1849, 1955, 1963, 2011, 2020, 2024, 2043, 2183,
2188, 2208, 2227, 2235
Ctenophora: 2183
Echinodermata: 261, 535, 1038, 1131, 1676, 1776, 1897, 1955, 2024,
2208
E1asmobranchii: 1627, 1963, 1964
Fish: 79, 106, 142, 156, 184, 242, 261, 273, 334, 376, 383, 386, 468,
471, 472, 473, 507, 521, 535, 541, 579, 583, 605, 616, 636,
648, 751, 754, 784, 851, 853, 861, 865, 898, 928, 940, 950,
973, 974, 977, 994, 1038, 1057, 1083, 1147, 1164, 1171, 1209,
372
-------
Fish (cont.): 1210,
1676,
2001,
2188,
Fungi: 1157, 1674
Higher Plants: 535, 541, 568, 849, 885, 950, 1038, 1057, 1676, 1723,
"1835, 1842, 2011, 2049
Insecta: 468, 537, 1283, 1284, 1518, 1558, 1617, 2011
Mammalia: 278,279,541,851,1038,1209,1317,1676,2024
Miscellaneous: 392
Mollusca: 79, 184, 194, 224, 242, 261, 312, 383, 426, 535, 541, 561,
583, 623, 649, 784, 838, 974, 975, 994, 1023, 1029, 1038,
1039, 1077, 1078, 1086, 1135, 1162, 1164,,1174, 1175, 1209,
1224, 1234. 1236, 1259. 1286, 1317, 1318, 1341, 1342, 1384
1437, 1470, 1486, 1563, 1589, 1591, 1627, 1676, 1758, 1828,
1955, 1963, 1990, 2011, 2023, 2024, 2081, 2188, 22vO, 2208,
2227
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 333, 535, 1038, 1518, 1627, 1676, 2208
Protozoa: 535, 679. 1171, 1627, 2043
Reptilia: 2011
Rotifera: 1440
Sediments: 79, 184, 541, 849, 950, 1486
Tunicata: 312,313,535,1174,1627,1758
1218,
1728,
2009.
2227
1234, 1235, 1437, 1440, 1465, 1470, 1518,
1828, 1831, 1838, 1912, 1932, 1955, 2000,
2010, 2011, 2020, 2023, 2024, 2051, 2141,
COPPER
Algae: 42, 48, 122, 132, 134, 173, 175, 228, 256, 269, 332, 338, 339.
345, 346, 394, 420, 446, 486, 521, 535, 583, 597, 632, 641,
648, 651, 683, 720, 732, 735, 736, 741, 748. 757, 777, 781,
803, 804, 814, 833, 841, 871, 961, 983, 992, 999, 1024, 1025,
1040, 1041, 1042, 1043, 1110, 1130, 1134, 1139, 1153, 1207,
1208, 1247, 1250, 1263, 1264, 1275, 1285, 1288, 1289, 1296,
1349, 1373, 1381, 1382, 1389, 1411, 1420, 1425, 1448, 1449.
1460, 1481, 1498, 1499, 1503, 1518, 1522, 1579. 1627, 1643,
1655, 1657, 1669. 1670, 1671, 1672, 1699, 1703, 1709, 1720,
1724, 1731, 1748, 1754, 1773, 1774, 1835, 1863, 1870, 1871,
1880, 1899, 1904, 1920, 1921, 1947, 1979, 1991, 1999, 2002,
2011, 2024, 2040, 2041, 2049, 2062, 2066, 2096, 2106, 2107,
2115, 2121, 2127, 2128, 2130, 2137, 2160, 2166, 2183, 2188,
2228, 2234, 2238
Amphibia: 138, 175, 804, 841, 897, 903, 1171, 1356, 1573, 1804. 1953,
1980, 2011, 2058, 2061, 2244
Annelida: 405, 434, 502, 535, 553, 583, 648, 650, 994, 1081, 1121,
1382, 1428, 1436, 1742, 1869. 1885, 1890, 1957, 2014, 2052,
2121, 2137, 2147
Arachnoidea: 1344, 1973
373
-------
Aves: 1356,
Bacteria and
1382, 1518, 1556, 2024
yeasts: 290, 497, 535, 571, 572, 657, 757, 780, 804,
971, 1098, 1099, 1173, 1220, 1425, 1448, 1449,
1486, 1555, 1556, 1606, 1893, 1957, 1997, 2094,
2121, 2244
Bibliography: 1397
Brachiopoda: 535
Bryazoa: 232, 357, 535, 553, 648, 1382
Chaetognatha: 1408, 2183
Coelenterata: 535, 904, 965, 1131, 1382, 1392, 1503, 1556, 1627,
1867, 1893, 1896, 2030, 2072, 2104
Crustacea: 13, 25, 50, 51, 60, 85, 91, 119, 122, 171, 254, 255, 256,
343, 344, 378, 409, 412, 421, 429, 434, 499, 507, 509,
535, 546, 553, 583, 596, 597, 625, 626, 631, 632, 647,
648, 695, 699, 732, 735, 736, 741, 759, 804, 841, 881A,
954, 961, 962, 991, 992, 1039, 1075, 1081, 1117, 1134,
1139, 1153, 1171, 1210, 1213, 1285, 1289, 1296, 1344,
1347, 1348, 1350, 1360, 1382, 1408, 1411, 1419, 1425,
1428, 1429, 1448, 1498, 1499, 1503, 1509, 1518, 1520,
1525, 1556, 1578, 1583, 1618, 1622, 1627, 1647, 1695,
1703, 1706, 1709, 1738, 1740, 1743, 1772, 1875, 1876,
1878, 1882, 1931, 1934, 1973, 2011, 2024, 2030, 2043,
2052, 2053, 2054, 2072, 2096, 2106, 2107, 2112, 2137,
2147, 2156, 2183, 2188, 2215, 2216, 2221, 2222, 2229,
2235, 2244
Ctenophora: 2183
Echinodermata: 71, 485, 487, 535, 1022, 1131, 1287, 1344, 1382, 1479,
1503, 1564, 1678, 1776, 1867, 1897, 1934, 1973, 2024,
2072, 2106, 2137, 2198
E1asmobranchii: 1356, 1564, 1627, 2030
Fish: 2, 18, 20, 30, 42, 48, 76, 77, 93, 106, 108, 128, 134, 142,
143, 156, 175, 203, 231, 236, 245, 271, 282, 325, 328, 329,
330, 334, 340, 343, 344, 345, 363, 365, 375, 378, 394, 407,
409, 410, 411, 454, 484, 488, 489, 492, 493, 494, 495, 504,
509, 521, 527, 535, 536, 544, 564, 583, 597, 616, 622, 627,
640, 643, 646, 648, 664, 665, 672, 678, 682, 693, 708, 732,
735, 740, 745, 748, 751, 752, 754, 759, 804, 807, 841, 887,
898, 899, 913, 922, 923, 940, 945, 950, 956, 964, 977, 979,
984, 994, 1003, 1004, 1005, 1020, 1021, 1049, 1059, 1064,
1092, 1098, 1099, 1120, 1121, 1122, 1134, 1139, 1147, 1170,
1171, 1178, 1188, 1195, 1210, 1215, 1235, 1268, 1269, 1291,
1307, 1322, 1328, 1346, 1347, 1356, 1370, 1373, 1382, 1395,
1427, 1430, 1431, 1432, 1440, 1448, 1449, 1465, 1469, 1495,
1518, 1520, 1530, 1554, 1555, 1556, 1564, 1577, 1578, 1613,
1625, 1628, 1647, 1662, 1666, 1683, 1690, 1695, 1709, 1710,
1717, 1728, 1741, 1769, 1816, 1820, 1823, 1826, 1831, 1873,
1878, 1939, 1954, 1971, 1981, 2007, 2011, 2024, 2030, 2066,
2072, 2075, 2096, 2098, 2106, 2107, 2112, 2114, 2129, 2137,
374
-------
Fish (cont.): 2141, 2166, 2173, 2181, 2182, 2184, 2188, 2194, 2229,
2243, 2244, 2246
Fungi: '735, 736, 1157, 1449, 1556, 1674, 1686, 1851, 2191
Higher Plants: 38, 175, 535, 570, 619, 650, 748, 950, 1134, 1382,
1461, 1539, 1556, 1578, 1709, 1835, 1842, 1878, 2011,
2049, 2096, 2107, 2128
Insecta: 171, 175, 410, 492, 493, 502, 537, 804, 1121, 1283, 1284,
1360, 1518, 1578, 1625, 1662, 1909, 2011, 2096, 2147
Mammalia: 202, 278, 597, 1356, 1382, 1556, 1694, 2024, 2072
Miscellaneous: 10, 64, 89, 289, 1373
Mollusca: 44, 72, 108, 133, 175, 187, 197, 220, 221, 240, 244, 338,
377, 394, 396, 405, 421, 426, 475, 477, 504, 509, 535,
552, 553, 558, 559. 583, 598, 610, 620, 638, 642, 649,
670, 695, 699, 700, 728, 731, 742, 770, 804, 821, 857,
875, 935, 954, 982, 989, 994, 1039, 1078, 1115, 1117,
1121, 1136, 1137, 1139, 1162, 1196, 1272, 1301, 1309,
1321, 1326, 1344, 1347, 1382, 1390, 1391, 1415, 1416,
1419, 1448, 1486, 1501, 1503, 1525, 1537, 1549, 1556,
1563, 1564, 1578, 1589, 1591, 1592, 1609, 1610, 1620,
1627, 1646, 1685, 1704, 1709, 1712, 1713, 1714, 1715,
1787, 1794, 1845, 1851, 1858, 1862, 1865, 1867, 1874,
1875, 1876, 1887, 1888, 1895, 1923, 1934, 1937, 1954,
1973, 1974, 1975, 1991, 1992, 1993, 2011, 2024, 2027,
2030, 2036, 2044, 2066, 2069, 2072, 2081, 2096, 2105,
2106, 2107, 2108, 2118, 2137, 2147, 2148, 2149, 2156,
2158, 2188, 2190, 2199, 2200, 2217, 2230, 2237
Phoronidea: 535
Platyhelminthes: 1738, 1739, 1740
Porifera: 535, 1503, 1518, 1627, 2137
Protozoa: 535, 662, 956, 1171, 1254, 1448, 1449, 1503, 1627, 1635,
1793, 1969, 1970, 2043, 2121
1356, 2011
1440, 1878, 2121, 2123
48, 339, 477, 731, 950, 1373, 1486, 1709, 1969, 1991,
2066, 2106, 2107, 2215
Seston: 2204
Tunicata: 535, 1564, 1627, 1973
Reptilia:
Rotifera:
Sediments:
DYSPROSIUM
Algae: 1498, 1522
Crustacea: 1498
ERBIUM
Algae: 1498, 1522
Crustacea: 1498
375
-------
EUROP IUM
Algae: 851, 1038, 1498, 1522, 1917, 1959, 2024, 2227
Aves: 851, 1038, 2024
Bryophyta: 1038, 1917
Coelenterata: 851, 1927
Crustacea: 466, 851, 1038, 1498, 1959, 2024, 2227
Echinodermata: 1038, 2024
Fish: 273, 851, 1038, 1917, 2024, 2227
Higher Plants: 1038, 1917
Insecta: 1558
Mammalia: 851, 1038, 2024
Mollusca: 466, 1038, 1224, 2024, 2227
Plankton: 466, 1959
Porifera: 1038, 1917
Protozoa: 1959
Sediments: 466
GADOLINIUM
Algae: 1498, 1522
Crustacea: 1498
GALL IUM
Algae: 535, 983, 1130, 1498, 1503, 1627, 2183
Annelida: 535
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 2183
Coelenterata: 535, 1503, 1627
Crustacea: 535, 1039, 1498, 1503, 1520, 1627, 2183
Ctenophora: 2183
Echinodermata: 535, 1503
E1asmobranchii: 1627
Fish: 535, 1520
Higher Plants: 535
Mollusca: 535, 1039, 1503, 1627
Phoronidea: 535
Porifera: 535, 1503, 1627
Protozoa: 535, 1503, 1627
Tunicata: 535, 1627
GERMANIUM
Algae: 535, 601, 957A, 1498, 1627, 1735, 2143
Annelida: 535
376
-------
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535, 1627
Crustacea: 535, 1039. 1498,
Echinodermata: 535
E1asmobranchii: 1627
Fish: 535, 1735
Higher Plants: 535
Mollusca: 535, 1039. 1627
Phoronidea: 535
Porifera: 535. 1627
Protozoa: 535, 1627
Tunicata: 535, 1627
1627, 1735
GOLD
Algae: 535, 932, 1208, 1604, 1605, 1627. 1669
Annelida: 535
Bacteria: 535, 2125
Brachiopoda: 535
Bryazoa:. 535
Coelenterata: 535, 1627
Crustacea: 146, 535, 626, 1039, 1604, 1605, 1627
Echinodermata: 535
Elasmobranchii: 1627
Fish: 146, 156, 334, 535, 754, 898, 1465, 1604, 1605, 1683
Higher Plants: 535
Mammalia: 202, 1861
Mollusca: 146, 425. 535, 1039, 1604, 1605, 1627
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 535, 1627
Protozoa: 535, 1627
Sediments: 146
Tunicata: 535, 1627
HAFNIUM
Algae: 1498, 2024
Aves: 2024
Crustacea: 1498, 2024
Echinodermata: 2024
Fish: 1465, 2024
Mammalia: 2024
Mollusca: 2024
377
-------
HOLMIUM
Algae:
1522
I~IUM
Algae:
Fish:
1130, 1522
605, 940, 1465
IRIDIUM
Fish:
940
IRON
Algae: 48, 130, 132, 193, 223, 242, 261, 269, 420, 471, 513, 521,
535, 541, 550, 583, 628, 632, 648, 651, 683, 696, 721, 741,
781, 802, 840, 885, 932, 958, 973, 974, 983, 992, 1029, 1040,
1130, 1134, 1234, 1264, 1373, 1405, 1449, 1498, 1499. 1503,
1518, 1522, 1548, 1579, 1601, 1603, 1626. 1627, 1657, 1669,
1721, 1722, 1723, 1774, 1828, 1835, 1853, 1859, 1863, 1880,
1903, 1955, 1963, 1979, 1991, 2009, 2011, 2024, 2049, 2109.
2160, 2166, 2183, 2188, 2192, 2227, 2228, 2234, 2239
Amphibia: 1535, 1980, 2011
Annelida: 115, 404, 405, 535, 583, 648, 707, 1428, 1601, 1603, 1789,
1957, 1963
Arachnoidea: 1344, 1973
Aves: 541, 928, 974, 1518, 1556, 1575, 1828, 2024
Bacteria and yeasts: 535, 921, 1099, 1177, 1220, 1426, 1449, 1556,
1606, 1807, 1812, 1905, 1957
Brachiopoda: 535
Bryazoa: 535, 648
Chaetognatha: 313, 1408, 1601, 1758, 2183
Coelenterata: 535, 965, 1131, 1392, 1503, 1556, 1627, 1867, 1955
Crustacea: 13, 60, 91, 115, 161, 261, 313, 390, 409, 453, 471, 506,
535, 541, 546, 583, 625, 626, 631, 632, 648, 741, 798
921, 973, 974, 991, 992, 1117, 1134, 1210, 1234, 1249,
1331, 1344, 1360, 1384, 1408, 1419, 1428, 1498, 1499,
1503, 1509. 1518, 1520, 1525, 1535. 1556, 1583, 1590,
1601, 1603, 1618, 1627, 1758, 1772, 1789, 1859, 1864,
1875, 1876, 1931, 1934, 1955, 1963, 1973, 2011, 2024,
2053, 2132, 2183. 2188, 2227, 2235
Ctenophora: 2183
Echinodermata: 261, 535, 1022, 1131, 1344, 1503, 1603, 1867, 1897,
1934, 1955, 1973, 2024, 2109, 2198
E1asmobranchii: 153, 1627, 1963, 1964
378
-------
Fish: 3, 18, 24, 26, 48, 90, 106, 1l5, 129, 142, 156, 161, 168, 213,
242, 261, 272, 273, 386, 390, 409, 41l, 433, 452, 471, 500,
506, 521, 535, 538, 541, 551, 583, 605, 615, 636, 640, 648,
678, 708, 754, 798, 802, 853, 861, 878, 879, 921, 928, 940,
945, 950, 973, 974, 979, 1021, 1099, 1l34, 1l86, 1205, 1210,
1217, 1234, 1235, 1279, 1373, 1408, 1423, 1427, 1449, 1465,
1518, 1520, 1535, 1556, 1603, 1628, 1662, 1717, 1728, 1789,
1828, 1831, 1838, 1873, 1954, 1955, 2000, 2001, 2007, 2009,
2010, 2011, 2024, 2028, 2051, 2095, 2132, 2133, 2141, 2166,
2171, 2184, 2188, 2194, 2227, 2243
Fungi: 921, 1449, 1556, 1674, 1686, 2191
Higher Plants: 535, 541, 570, 802, 885, 921, 950, 1134, 1187, 1279,
1523, 1556, 1603, 1721, 1722, 1723, 1835, 1842, 2011,
2049, 2109
Insecta: 115, 537, 802, 1283, 1284, 1360, 1518, 1535, 1558, 1617,
1662, 1789. 2011, 2132
Mammalia: 541, 615, 1556, 1861, 2024
Miscellaneous: 24, 1373
Mollusca: 14, 115, 158, 242, 243, 261, 313, 321, 390, 404, 405, 426,
506, 535, 541, 583, 638, 649, 863, 864, 921, 974, 1029,
1078, 1086, 1111, 1117, 1135, 1136, 1162, 1224, 1234,
1272, 1274, 1279, 1344, 1384, 1415, 1419, 1503, 1525,
1535, 1556, 1580, 1589, 1591, 1592, 1601, 1603, 1609,
1616, 1620, 1627, 1677, 1758, 1828, 1862, 1867, 1875,
1876, 1887, 1934, 1954, 1955, 1963, 1973, 1978, 1990,
1991, 1993, 2011, 2024, 2081, 2188, 2190, 2199, 2200,
2227, 2239
Phoronidea: 535
Plankton: 131, 1859
Platyhelminthes: 1535, 1739
Porifera: 535, 1503, 1518, 1627
Protozoa: 535, 1449, 1503, 1627
Reptilia: 201l
Rotifera: 1572
Sediments: 48, 541, 707, 950, 1373, 1991
Seston: 2204
Tunicata: 43, 313, 535, 1204, 1457, 1601, 1627, 1758, 1973, 2038
LANTHANUM
Algae: 535, 1425, 1498, 1499, 1518, 1522, 1532
Annelida: 535
Aves: 1518
Bacteria: 535, 1425
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535
Crustacea: 360, 535, 1425, 1498, 1499, 1518
379
-------
Echinodermata: 535
Fish: 334, 360, 535,
Higher Plants: 535
Insecta: 1518, 1558
Mollusca: 535, 557,
Phoronidea: 535
Porifera: 535, 1518
Protozoa: 535
Tunicata: 535
940, 1465, 1518) 2010
1224, 1341
LEAD
Algae: 228, 269, 420, 583, 597, 628, 632, 648, 651, 683, 741, 802,
803, 804, 833, 990, 992, 1043, 1130, 1160, 1168, 1208, 1263,
1264, 1275, 1296, 1381, 1382, 1407, 1425, 1445, 1449, 1455,
1481, 1498, 1499, 1522, 1579, 1627, 1669, 1672, 1679, 1680,
1720, 1754, 1773, 1880, 1894, 1947, 1991, 2006, 2024, 2106,
2107, 2110, 2137, 2160, 2166, 2183, 2188, 2214, 2227, 2238
Amphibia: 58, 138, 260, 293, 804, 822, 1171, 2244
Annelida: 545, 583, 648, 994, 1081, 1382, 1428, 1436, 1869, 1957,
2014, 2021, 2137
Arachnoidea: 1809, 1973
Aves: 118, 259, 995, 1358, 1374, 1382, 1575, 1730, 1852, 2024
Bacteria: 290, 571, 804, 842, 1177, 1425, 1449, 1486, 1957, 1997,
2094, 2244
Bibliography: 673
Bryazoa: 232, 648, 1382
Chaetognatha: 2183
Coelenterata: 904,965,1018,1019,1131,1382,1392,1529,1627,
1867, 1927
Crustacea: 13, 92, 161, 343, 344, 378, 409, 546, 583, 597, 612, 626,
632,648, 717, 741, 759, 782, 798, 804, 837, 881A, 991,
992, 995, 1039, 1075, 1081, 1104, 1154, 1168, 1171, 1249,
1296,1350,1360,1368,1382,1407,1425,1428,1429,
1455, 1498, 1499, 1520, 1525, 1627, 1647, 1695, 1738,
1744, 1760, 1809, 1919, 1973, 2021, 2024, 2043, 2053,
2106, 2107, 2112, 2137, 2156, 2183, 2188, 2205, 2227,
2235, 2244
Ctenophora: 2183
Echinodermata: 1131,1382,1479,1776,1867,1973,2024,2106,2137,
2198
E1asmobranchii: 1627
Fish: 2, 104, 105, 123, 139, 142, 156, 161, 209, 212, 248, 271, 282,
286,295, 328, 330, 343, 344, 378,403,407,409.501,517,
542,577,583,591,595,597,612,616,617,640,648,678,
717, 723, 754, 759, 798, 800, 802, 804, 837, 843, 860, 887,
898, 940, 945, 950, 979, 994, 995, 1031, 1066, 1104, 1154,
1171, 1178, 1235, 1257, 1298, 1322, 1346, 1382, 1407, 1440,
380
-------
Fish (cont.): 1449,
1628,
1838,
2129,
2244
Fungi: 567, 1449
Higher Plants: 802, 950, 995, 1345, 1382, 1539, 1775, 1842, 1886,
1919, 2107
Insecta: 537, 802, 804, 1360, 1625, 1662, 1809, 1909, 1919
Mammalia: 202, 248, 278, 279, 581, 597, 617, 635, 1168, 1382, 1694,
1775, 2022, 2024
Miscellaneous: 52, 89, 104, 392
Mollusca: 137, 248, 426,583, 598, 612,
742, 770, 804, 821, 845, 989.
1160, 1162, 1309, 1321, 1382,
1474, 1486, 1501, 1525, 1549,
1787, 1809, 1845, 1867, 1919.
1993, 2024, 2081, 2106, 2107,
2176, 2188, 2200, 2227
Nematoda: 2021
Platyhelminthes: 1738, 1739, 1809.1919.2021
Porifera: 1627, 2137
Protozoa: 679,823,1171, 1254, 1449, 1627, 1634, 1635, 1969,2043
Reptilia: 74, 1918
Rotifera: 1440, 2123
Sediments: 787, 950, 995, 1154, 1345, 1445, 1486, 1969, 1991, 2106,
2107
Seston: 2204
Tunicata: 1627, 1973
1455,
1647,
1873,
2137,
1458,
1662,
1918,
2166,
1473,
1695,
1919,
2173,
1512,
1717,
1981,
2181,
1517,
1728,
2024,
2188,
1520,
1741,
2106,
2194,
1607,
1809.
2107,
2206,
1625,
1823,
2112,
2227,
638, 639, 649, 670, 671,
994, 1039, 1104, 1158, 1159,
1407, 1415, 1445, 1455,
1589, 1591, 1627, 1646,
1973,1974,1975,1991,
2110, 2118, 2137, 2156,
LITHIUM
Algae: 535, 628, 1425, 1449, 1498, 1522, 2183
Amphibia: 608
Annelida: 535, 994, 1442
Bacteria: 535, 1425, 1449
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 2183
Coelenterata: 535, 965, 1442
Crustacea: 13, 31, 535, 1425, 1442, 1498, 2183
Ctenophora: 2183
Echinodermata: 535, 1442
E1asmobranchii: 1442
Fish: 142, 156, 535, 754. 940, 945, 994, 1442, 1449, 1988
Fungi: 1449
Higher Plants: 535
Mollusca: 32, 61, 535, 629, 769, 957, 994, 1442
381
-------
Phoronidea: 535
Porifera: 535
Protozoa: 535,
Tunicata: 535
1449, 2136
LUTETIUM
Algae:
Fish:
1522
1465
MAGNES IUM
Algae: 269, 602, 648, 694, 846, 880,
1449, 1464, 1498, 1499, 1522,
1722, 1843, 1979, 2065, 2183,
Amphibia: 184, 897, 1535, 1953, 2058
Annelida: 115, 648, 900, 1464, 2025, 2147
Bacteria: 971, 1449, 1486, 1786, 1913
Bryazoa: 648, 1545
Chaetognatha: 1599, 2183
Coelenterata: 1131, 1319, 1392, 1464, 1599, 1627, 2025, 2179
Crustacea: 13, 115, 461, 602, 626, 631, 648, 716, 749, 798, 806,
812, 829, 830, 991, 992, 1210, 1350, 1464, 1498, 1499,
1510, 1511, 1520, 1535, 1581, 1599, 1627, 1639, 1708,
1772, 1806, 1849, 1950, 2025, 2147, 2183, 2235
Ctenophora: 2183
Echinodermata: 870, 1131, 1464, 1897, 2025, 2059
E1asmobranchii: 153,263,1531,1569,1627,2004
Fish: 7,80, 115, 128, 142, 152, 156, 157, 184,213,258,356,380,
621, 648, 725, 749, 754, 798, 806, 870, 876, 888, 889, 898,
920, 940, 950, 980, 981, 1054, 1094, 1103, 1197, 1210, 1228,
1235, 1306, 1449, 1465, 1497, 1520, 1534, 1535, 1569, 1628,
1633, 1650, 1651, 1652, 1662, 1710, 1717, 1728, 1751, 1766,
1795, 1796, 1808, 1983, 2004, 2007, 2092, 2194, 2243, 2246
Fungi: 1449, 1514
Higher Plants: 570, 880, 950, 1201, 1722
Insecta: 115, 602, 1283, 1284, 1535, 1662, 1761, 2147
Miscellaneous: 392
Mammalia: 1808,. 1861
Mollusca: 61, 115, 158, 184, 558,
1162, 1237, 1272, 1444,
1792, 1794, 1814, 1887,
2190
Platyhelminthes:
Porifera: 1464,
Protozoa: 1361,
Sediments: 184,
Tunicata: 1599,
978, 992, 1399, 1406, 1420,
1574, 1598, 1599, 1627, 1669,
2207, 2234
629, 700, 749, 769, 806, 1106,
1464, 1486, 1535, 1627, 1639,
1978, 2025, 2036, 2147, 2164,
1535, 1739
1627
1449, 1464,
950, 1486
1627
1599, 1627, 1793, 2136, 2195
382
-------
MANGANESE
Algae: 17, 223, 224, 228, 261, 333, 383, 471, 483, 539, 541, 550,
555, 583, 628, 632, 651, 683, 763, 777, 785, 802, 804, 840,
849, 851, 973, 983, 992, 1038, 1100, 1130, 1134, 1139, 1164,
1208, 1234, 1264, 1437, 1498, 1499, 1518, 1522, 1579, 1601,
1627, 1655, 1657, 1669, 1722, 1723, 1773, 1774, 1811, 1828,
1835, 1853, 1859, 1863, 1880, 1955, 1959, 1963, 1979, 1991,
2011, 2019, 2046, 2049, 2106, 2107, 2109, 2166, 2183, 2188,
2192, 2208, 2214, 2227, 2234, 2238
Amphibia: 804, 1171, 2011
Annelida: 468, 583, 652, 688, 707, 1601, 1957, 1963, 1965, 2147
Arachnoidea: 1973
Aves: 541, 851, 928,
Bacteria and yeasts:
1038, 1518, 1828, 2208
657, 804, 842, 921, 1544, 1619,,1664, 1786,
1807, 1957, 2035
Bryazoa: 232
Bryophyta: 1038
Chaetognatha: 1601, 2183
Coelenterata: 851, 965, 1131, 1392, 1627, 1955, 2208
Crustacea: 13, 88, 91, 161, 261, 314, 337, 466, 468, 471, 539, 541,
561, 583, 626, 632, 785, 804, 820, 851, 881A, 921, 973,
991, 992, 1038, 1039, 1075, 1100, 1134, 1139, 1164, 1171,
1211, 1234, 1286, 1360, 1437, 1498, 1499, 1509, 1518,
1583, 1590, 1601, 1627, 1772, 1811, 1849. 1859, 1875,
1876, 1934, 1955, 1959, 1963, 1973, 2011, 2019, 2043,
2106,2107,2147,2183,2188,2208,2215,2227,2235
Ctenophora: 2183
Echinodermata: 261, 1038, 1131, 1287, 1564, 1776, 1897, 1934, 1955,
1973, 2106, 2109, 2208
E1asmobranchii: 1564, 1627, 1963, 1964
Fish: 2, 106, 142, 156, 161, 207, 209, 261, 273, 314, 315, 337, 383,
398, 403, 457, 468, 471, 521, 538, 539, 541, 583, 636, 640,
708, 710, 754, 756, 785, 802, 804, 851, 865, 898, 921, 928,
940, 950, 973, 1038, 1083, 1087, 1134, 1139, 1147, 1156, 1164,
1171, 1217, 1234, 1235, 1279. 1295, 1395, 1427, 1437, 1465,
1518, 1564, 1628, 1662, 1684, 1717, 1728, 1810, 1811, 1819.
1828, 1857, 1954, 1955, 1965, 2007, 2011, 2019, 2106, 2107,
2141, 2166, 2173, 2188, 2227
Fungi: 921, 1157, 1674, 1811, 2191
Higher Plants: 541, 555, 570, 802, 849. 921, 950, 1038, 1134, 1279,
1722, 1723, 1835, 1842, 2011, 2049, 2107, 2109
Insecta: 337, 468, 756, 802, 804, 1283, 1284, 1360, 1518, 1558, 1662,
2011, 2147
Mammalia: 202, 278, 279, 541, 851, 1038, 1861, 2035
Miscellaneous: 392
383
-------
Mollusca: 100, 189. 219. 223, 261, 355,
557, 561, 583, 623, 638, 639,
769, 785, 804, 811, 821, 921,
1078, 1086, 1139, 1155, 1156,
1286, 1341, 1342, 1437, 1564,
1608, 1609, 1627, 1794, 1828,
1955, 1963, 1973, 1978, 1991,
2081, 2106, 2107, 2147, ~188,
Plankton: 466, 1859, 1959
Platyhelminthes: 1739, 1811
Porifera: 333, 1038, 1518, 1627, 2208
Protozoa: 1171, 1627, 1793, 1811, 1959, 2043, 2195
Reptilia: 2011
Sediments: 466, 541, 707, 731, 849, 950, 1991, 2106, 2107, 2215
Tunicata: 688, 1457, 1564, 1601, 1627, 1973
383, 426, 466, 539, 541,
649, 670, 688, 731, 738,
1023, 1038, 1039, 1076,
1162, 1164, 1234, 1279,
1589, 1591, 1592, 1601,
1875, 1876, 1934, 1954,
1993, 2011, 2019, 2036,
2199, 2200, 2208, 2227
MERCURY
Algae: 269, 535, 597, 768, 802, 833,
927, 932, 949, 951, 992, 996,
1208, 1247, 1264, 1381, 1382,
1448, 1449, 1481, 1482, 1498,
1527, 1571, 1597, 1598, 1624,
1699, 1735, 1750, 1822, 1824,
2106, 2107, 2137, 2154, 2169,
Amphibia: 1171, 2058, 2244
Annelida: 535, 553, 873, 1121, 1334, 1382, 1428, 1527, 1869, 1967,
2014, 2137
Aves: 276, 543, 569, 764, 771, 771A, 772, 824, 896, 905, 906, 924,
934, 995, 1073, 1074, 1080, 1185, 1189, 1241, 1242, 1324,
1340, 1375, 1380, 1382, 1527, 1611, 1780, 1782, 1928, 2024,
2185
Bacteria and yeasts:
834, 835, 839, 873, 874, 896,
997, 1043, 1047, 1096, 1166,
1409, 1410, 1411, 1425, 1441,
1499, 1506, 1515, 1516, 1522,
1643, 1648, 1667, 1669, 1672,
1947, 1949, 2024, 2082, 2085,
2188
Bibliography: 21,
Brachiopoda: 535
Bryazoa: 535, 553, 1382, 1527
Bryophyta: 873
Coelenterata: 535, 904, 1382, 1896, 2104
Crustacea: 13, 92, 119, 120, 121, 218, 342, 421, 429, 468, 507, 509.
535, 553, 597, 626, 695, 699, 704, 729, 759, 767, 794,
854, 874, 899A, 927, 949, 952, 992, 995, 1012, 1013, 1075,
1096, 1104, 1117, 1125, 1163, 1171, 1189, 1210, 1240,
447, 535, 571, 572, 618, 727,
1011, 1036, 1132, 1190, 1282,
1425, 1433, 1448, 1449, 1485,
1527, 1555, 1606, 1733, 1784,
1997, 2035, 2042, 2067, 2078,
2124, 2125, 2155, 2168, 2174,
2244
592, 724, 750, 937, 1165, 1179
779, 892, 893,
1338, 1383, 1394,
1486, 1487, 1490,
1785, 1786, 1914,
2094, 2101, 2119,
2175, 2193, 2226,
384
-------
Crustacea (cant.): 1242, 1243, 1244,
1348, 1350, 1382,
1482, 1498, 1499,
1585, 1614, 1636,
1706, 1733, 1735,
1824, 1825, 1928,
2076, 2085, 2106,
2205, 2219. 2220,
Echinodermata: 485, 535, 1287, 1382,
2106, 2137, 2198
E1asmobranchii: 686, 687, 786, 1227, 1614, 1648, 1756, 2003, 2103
Fish: 2, 11, 21, 36, 49, 57, 63, 116, 142, 160, 180, 218, 230, 241,
249, 266, 267, 268, 271, 273, 275, 276, 277, 283, 316, 342,
352, 375, 442, 447, 448, 468, 507, 509, 535, 543, 556, 569.
578, 590. 597, 606, 613, 630, 634, 654, 672, 678, 686, 692,
708,711, 727,730, 733, 739, 753, 759. 760, 765, 766, 767,
768, 771, 772, 773, 774, 794, 801, 802, 813, 816, 817, 824,
825,827,828,843,847,873.874,887,892,893, 894, 895,
898, 899, 902, 906, 908, 913, 914. 916, 917, 924, 927, 929
934, 936, 940, 943, 945, 947, 949, 951, 952, 966, 967, 979,
985,995,996,1001,1002,1006,1010,1011,1012,1013,1014,
1021, 1045, 1046, 1052, 1053, 1080, 1091, 1096, 1104, 1121,
1122, 1125, 1132, 1133, 1139, 1140, 1144, 1145, 1146, 1161,
1163, 1171, 1180, 1188, 1189. 1206, 1210, 1~23, 1227, 1233,
1235,1253,1257,1258,1260,1261,1267,1269,1292,1307,
1310, 1324, 1325, 1327, 1328, 1329, 1333, 1334, 1335, 1337,
1340, 1346, 1375, 1376, 1382, 1396, 1427, 1440, 1447, 1448,
1449, 1453, 1465, 1480, 1482, 1502, 1504, 1521, 1527, 1543,
1555,1561,1562,1568,1593,1596,1611,1613,1614,1615,
1621, 1647, 1648, 1666, 1667, 1675, 1683, 1692, 1693, 1695,
1701, 1702, 1728, 1729, 1732, 1733, 1735, 1741, 1749. 1753,
1756, 1768, 1771, 1781, 1782, 1790, 1791, 1800, 1821, 1824,
1831, 1866, 1879, 1889, 1891, 1924, 1928, 1929. 1936, 1940,
1948,1966,1967,1981,1995,1996,2000,2001,2003,2007,
2012, 2015, 2024, 2039, 2070, 2078, 2080, 2086, 2103, 2106,
2107, 2112, 2113, 2126, 2129, 2137, 2139, 2141, 2162, 2163,
2168, 2173, 2181, 2185, 2188, 2206, 2233, 2236, 2244, 2246
Fungi: 1157, 1449, 2033, 2034
Higher Plants: 218, 535, 543, 734, 768, 771, 802, 854, 873, 874,
893, 936, 995, 1271, 1382, 1447, 1454, 1527, 1614,
1667, 1822, 2107, 2159, 2220
Insecta: 192,468,537,765,802,1046,1121,1334,1527,1558,
1617, 1928, 1929
Mammalia: 202, 266, 278, 279, 302, 316, 569, 580, 581, 590, 597,
809, 810, 810A, 827, 896, 908, 924, 933, 936, 963, 967,
1011, 1012, 1080. 1096, 1144, 1163, 1180, 1214,
1382,1396,1439,1504,1527,1561,1596,1611,1692,1694,
1736, 1780, 1861, 1929. 2022, 2024, 2035, 2086, 2162, 2185
1248,1267,1270,
1384, 1411, 1425,
1509, 1521, 1527,
1647, 1648, 1667,
1738, 1740, 1744,
1934, 1949. 1996,
2107, 2112, 2137,
2244
1771, 1776, 1897,
1327, 1334,
1428, 1448,
1536, 1542,
1692, 1695,
1770, 1771,
2024, 2029,
2180, 2188,
1934, 2024,
385
-------
Miscellaneous: 392
Mollusca: 266, 267, 302, 316, 352, 421, 509, 535, 553, 590, 598,
670, 671, 695, 699, 712, 731, 742, 767, 768, 770, 772,
867, 873, 874, 877, 882, 883, 894, 896, 908, 925, 934,
935, 949, 951, 989, 996, 1012, 1013, 1104, 1117, 1121,
1125, 1163, 1166, 1206, 1226, 1232, 1321, 1327, 1334,
1382, 1384, 1443, 1448, 1486, 1487, 1501, 1502, 1505,
1506, 1527, 1533, 1580, 1585, 1596, 1648, 1692, 1733,
1770, 1771, 1910, 1934, 1937, 1996, 2013, 2017, 2024,
2067, 2091, 2106, 2107, 2137, 2140, 2163, 2188, 2220,
2236
Phoronidea: 535
Platyhelminthes: 1738, 1739, 1740
Porifera: 535, 2137
Protozoa: 535, 679, 823, 1171, 1448, 1449, 1634, 1635, 1969, 2152
Rotifera: 1440, 2123
Sediments: 218, 230, 267, 731, 787, 873,
1096, 1190, 1253, 1486, 1527,
1770, 1969, 2070, 2078, 2106,
Tunicata: 535
MISCELLANEOUS
Algae: 1901
Bibliography: 1547, 1629
Coelenterata: 1901
Crustacea: 1901
Echinodermata: 1901
Mollusca: 1901
Porifera: 1901
Protozoa: 1901
Sediments: 1901
MOLYBDENUM
Algae: 535, 628, 683, 737, 983, 992,
1499, 1522, 1604, 1605, 1627,
2183, 2188, 2238
Annelida: 535
Bacteria and yeasts: 535, 1425, 2035
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 2183
Coelenterata: 535, 1392, 1627
Crustacea: 535, 737, 992, 1039, 1176,
1627, 2019, 2183, 2188
Ctenophora: 2183
Echinodermata: 535
386
892, 943, 951, 995, 1011,
1543, 1562, 1732, 1733,
2107, 2236
1176, 1208, 1250, 1425, 1498,
1835, 1960, 1979, 2019, 2049,
1425, 1498, 1499, 1604, 1605,
-------
E1asmobranchii: 1627
Fish: 535,737,940,950, 1176, 1219, 1255, 1465, 1604, 1605, 1628,
1728, 1831, 2019, 2188
Fungi: 1674, 2191
Higher Plants: 535, 737, 950, 1835, 1842, 2049
Insecta: 1283, 1284
Mammalia: 2035
Mollusca: 535, 638, 1039, 1176, 1604, 1605, 1627, 2019, 2188
Phoronidea: 535
Porifera: 535, 1627
Protozoa: 535, 698, 1627
Sediments: 950
Tunicata: 535, 1457, 1627,2038
NEODYMIUM
Algae: 535, 1498, 1499, 1522
Annelida: 535
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535
Crustacea: 535, 1498, 1499
Echinodermata: 535
Fish: 535
Higher Plants: 535
Insecta: 1558
Mollusca: 535
Phoronidea: 535
Porifera: 535
Protozoa: 535
Tunicata: 535
NEPTUN IUM
Algae: 788, 1518
Aves: 1518
Crustacea: 1518
Fish: 1518 ,
Higher Plants: 788
Insecta: 1518
Mammalia: 788
Porifera: 1518
NICKEL
Algae:
228, 269, 486, 535, 628, 648,
1130, 1208, 1382, 1425, 1449.
1627, 1643, 1657, 1669, 1709,
2049, 2106, 2107, 2109, 2115,
683, 741, 792, 992, 1025, 1043,
1481, 1498, 1499, 1522, 1579,
1720, 1723, 1801, 1904, 1991,
2160, 2183, 2188, 2227, 2238
387
-------
APlphibia: 260, 897, 1171, 2058
Annelida: 468, 535, 648, 994, 1121, 1382
Aves: 1382
Bacteria: 535, 571, 819, 1173, 1177, 1425, 1449, 1785, 2094
Brachiopoda: 535
Bryazoa: 232, 535, 648, 1382
Chaetognatha: 2183
Coelenterata:. 535,965,1131,1382,1392,1627
Crustacea: 12, 91, 161, 343, 344, 378, 409, 428, 468, 507, 535, 626,
648, 741, 991, 992, 1039, 1075, 1117, 1171, 1350, 1360,
1382, 1425, 1498, 1499, 1509, 1627, 1647, 1709, 1801,
1849, 2106, 2107, 2183, 2188, 2227, 2229, 2235
Ctenophora: 2183
Echinodermata: 535, 1131, 1382, 1776, 1897,2106,2109,2198
Elasmobranchii: 1627
Fish: 2,77, 106, 128, 141, 143, 156, 161,343,344,375,378, .407,
409, 468, 507, 521, 535, 591, 640, 643, 648, 751, 754, 898,
940, 950, 994, 1092, 1120, 1121, 1122, 1170, 1171, 1218, 1235,
1346, 1382, 1440, 1449, 1628, 1647, 1709, 1801, 1873, 2051,
2106, 2107, 2141, 2173, 2188, 2227, 2229
Fungi: 1157, 1449, 1674
Higher Plants: 535, 950, 1382, 1709, 1723, 1842, 2049, 2107, 2109
Insecta: 468,537,1121,1283,1284,1360
Mammalia: 1382
Miscellaneous: 64, 392
Mollusca: 46, 421, 426, 535, 638,
1039, 1078, 1117, 1121,
1415, 1589. 1591, 1627,
2188, 2199, 2200, 2227,
Phoronidea: 535
Platyhelminthes: 1739
Porifera: 535, 1627
Protozoa: 535, 1171, 1449, 1627, 1793, 2136
Rotifera: 1440
Sediments: 46, 731, 950, 1709, 1991, 2106, 2107
Tunicata: 535, 1627
649, 670, 671, 731, 994, 1023,
1162, 1309, 1321, 1341, 1342, 1382,
1709, 1801, 1991, 2081, 2106, 2107,
2237
NIOBIUr.1
Algae: 102, 178, 214, 333, 383, 483,
1208,1437,1498,1518,1522,
1963, 2019, 2227
Annelida: 535, 1088, 1944, 1963
Aves: 1038, 1518, 1676, 1828
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
Bryophyta: 1038, 1676, 1917
535, 539, 555, 1029, 1038, 1166,
1540, 1612, 1676, 1828, 1917.
388
-------
Coelenterata: 535, 1676, 1944
Crustacea: 102, Ill, 466, 535, 539, 1038, 1437, 1498, 1518, 1612,
1676, 1943, 1945, 1956, 1963, 2019. 2227
Detritus: 110, III
Echinodermata: 535, 1038, 1676, 1944
Elasmobranchii: 353, 1963
Fish: 383, 535, 539, 605, 940, 103R, 1088, 1437, 1518, 1540,
1612, 1676, 1828, 1917, 1956, 2019, 2227
Higher Plants: 535, 555, 1038, 1612, 1676, 1917
Insecta: 1518
~1ammalia: 1038, 1676, 1956
Mollusca: 190, 383, 466, 535, 539, 557, 1029, 1038, 1166,
1437, 1456, 1612, 1676, 1828, 1956, 1963, 1990,
2019, 2227
Phoronidea: 535
Plankton: 466
Porifera: 333, 535, 1038, 1518, 1676, 1917
Proto:oa: 535
Sediments: 466, 1956
Tuniclta: 535,1456,1457,1945,2038
PALLADIU~1
Algae: 1627
Crustacea: 1627
Coelenterata: 1627
Elasmobranchii: 1627
Fish: 692, 940
~1011usca: 1627
Porifera: 1627
Proto:oa: 1627
Tunicata: 1627
PLATINUM
Amphibia: 2058
Crustacea: 626
Fish: 940, 1683
PLUTONIUH
Algae: 150, 516, 541, 1095, 1134, 1281, 1293,
1900, 1926, 1955, 2068, 2227
Annelida: 676, 1293, 1353, 1354, 1587, 1900
Aves: 1293
1653, 1654,
389
-------
Coelenterata: 1293, 1716, 1927, 1955
Crustacea: 541, 782, 1044, 1095, 1134, 1293, 1587, 1658, 1955,
2068, 2197, 2227
Detritus: 2068
Echinodermata: 1293, 1900, 1955, 2068
E1asmobranchii: 1280
Fish: 150, 516, 541, 636, 865, 1044, 1095, 1134, 1293, 1658,
1900, 1918, 1925, 1955, 1968, 2068, 2197, 2227
Higher Plants: 541, 1095, 1134
Mammalia: 541, 1044, 1293
Mollusca: 541, 676, 1044, 1095, 1280, 1293, 1587, 1900, 1955,
2068, 2227
1926, 2068
1918
150. 541, 1293, 1900, 1926. 2068
1926
Plankton:
Reptilia:
Sediments:
Tunicata:
POLONIUM
Algae: 1168, 1281, 1496, 2227
Coelenterata: 1927
Crustacea: 612, 782. 1154. 1168, 1466,
Fish: 5, 209, 248. 612, 616, 617, 866,
Mammalia: 248. 617. 1168
Mollusca: 248, 612. 2227
Reptilia: 1918
Sediments: 1154
1682, 1760, 2227
1154, 1918, 2227
POTASSIUM
Algae: 333. 535, 547. 548, 549. 602,
1038, 1041, 1164, 1290, 1406,
1599, 1643. 1676, 1722, 1811,
1963, 1979, 2011. 2019. 2024,
2238
Amphibia: 184, 317. 608, 1418, 1668. 2011
Annelida: 83, 115. 535, 868, 900, 1442, 1944, 1963, 2025, 2147
Aves: 928. 1038, 1676, 2024
Bacteria and yeasts: 535. 1068, 1173, 1718, 1893. 2035
Brachiopoda: 535
Bryazoa: 535. 1545
Bryophyta: 1038. 1676, 1917
Chaetognatha: 1599
Coelenterata: 83. 535. 1131, 1319, 1442, 1599, 1676, 1893,
1944. 2025
694. 737, 846, 880, 992,
1437, 1498. 1499, 1522,
1843. 1870. 1917, 1947.
2065, 2218, 2227, 2234,
390
-------
Crustacea: 13, 82, 83, 84, 86, 115, 167,
561, 602, 626, 645, 716, 737,
1164, 1210, 1294, 1369, 1437,
1510, 1511, 1567, 1581, 1599,
1945, 1950, 1963, 2011, 2019,
2227
Echinodermata: 83, 535, 1038, 1131, 1442, 1676, 1897, 1944, 2024,
2025
E1asmobranchii: 153, 263, 296, 1442, 1531, 1569, 1727, 1854, 1963,
2004
Fish: 1, 2, 7, 70, 80, 115, 142, 152, 156, 157, 184, 199, 200, 207,
213, 227, 245, 251, 258, 273, 306, 314, 315, 341, 356, 370,
372, 450, 460, 528, 535, 540, 547, 658, 714, 725, 737, 749,
754, 869, 876, 888, 889, 898, 915, 928, 940, 950, 964, 980,
986, 988, 1027, 1038, 1053, 1054, 1083, 1094, 1164, 1197, 1198,
1199, 1210, 1228, 1229, 1235, 1303, 1304, 1357, 1369, 1423,
1437, 1442, 1465, 1560, 1565, 1566, 1569, 1576, 1628, 1633,
1644, 1650, 1651, 1652, 1676, 1717, 1727, 1728, 1747, 1766,
1783, 1795, 1796, 1808, 1810, 1811, 1826, 1844, 1848, 1857,
1872, 1902, 1917, 1930, 1946, 1976, 1977, 1983, 2000, 2001,
2004, 2007, 2011, 2019, 2024, 2142, 2146, 2194, 2227, 2243
Fungi: 1811
Higher Plants:
306, 314, 461, 466, 535,
749, 829, 830, 992, 1038,
1438, 1442, 1498, 1499,
1663, 1676, 1811, 1825,
2024, 2025, 2147, 2157,
306, 535, 570, 737, 880, 950, 1038, 1201, 1369, 1676,
1722, 1917, 2011
Insecta: 115, 602, 1558, 2011, 2147
Mammalia: 1038, 1676, 1808, 1861, 2024, 2035
Miscellaneous: 289
Mollusca: 33, 34, 83, 84, 115, 158, 184, 318, 466, 535, 561, 700,
749, 769, 881, 957, 1038, 1076, 1106, 1162, 1164, 1341,
1342, 1369, 1437, 1442, 1676, 1687, 1963, 1990, 2011,
2019, 2024, 2025, 2147, 2190, 2227
Phoronidea: 535
Plankton: 466
Platyhelminthes: 1739, 1811
Porifera: 333, 535, 1038, 1676, 1917
Protozoa: 83, 535, 1599, 1811, 2136
Reptilia: 2011
Rotifera: 1805, 2123
Sediments: 466, 950, 1369
Tunicata: 83, 535, 1599, 1945
PRASEODYMIUM
Algae: 333, 439,
Annelida: 535
Bacteria: 535
Brachiopoda: 535
Bryazoa: 535
535, 1498, 1522, 2019
391
-------
Coelenterata: 535
Crustacea: 439, 466, 535, 850, 1498, 2019
Detri tus: 110
Echinodermata: 535
Fish: 439, 535, 2019
Higher Plants: 535
Mollusca: 439, 466, 535, 2019
Phoronidea: 535
Plankton: 466
Porifera: 333, 535
Protozoa: 535
Sediments: 466
Tunicata: 535
PROMETHIUM
Algae: 17, 555, 1959, 2227
Annelida: 688
Crustacea: 466, 1959, 2227
Fish: 2227
Higher Plants: 555
Mollusca: 466, 688, 2227
Plankton: 466, 1959
Protozoa: 1959
Sediments: 466
Tunicata: 688
PROTACTINIUM
Coelenterata: 1716
Crustacea: 1829
Mollusca: 1829
RADIUM
Algae: 151, 350, 401, 476, 588, 747, 1627, 1779. 2011, 2227
Amphibia: 2011
Aves: 928
Coelenterata: 1018,1019.1529,1627
Crustacea: 350, 466, 1627, 1760, 1779, 2011, 2227
Elasmobranchii: 1627
Fish: 248, 273, 326, 350. 391, 401, 588, 928, 2011, 2227
Higher Plants: 391, 401, 2011
Insecta: 391, 588, 2011
Mammalia: 248, 401
Mollusca: 65, 248, 466, 1627, 1779. 2011, 2165, 2227
Plankton: 466
Porifera: 1627
392
-------
Protozoa:
Reptilia:
Sediments:
Tunicata:
1627
2011
350,
1627
391, 466
RHEN IUM
Algae: 555, 1604, 1605
Crustacea: 1604, 1605
Fish: 334, 940, 1604, 1605
Higher Plants: 555
Mollusca: 1604, 1605
RHOD IUM
Algae: 17. 333, 599, 1029, 1828
Annelida: 599
Aves: 1828
Coelenterata: 1927
Detritus: 110
Fish: 599, 1219, 1828
Higher Plants: 599
Insecta: 599
Mammalia: 599
Mollusca: 599, 1029, 1828
Porifera: 333
RUBIDIUM
Algae: 193, 310, 535, 628, 932, 1425, 1498, 1522, 1960, 2024, 2188
2227
Annelida: 535, 1442
Aves: 2024
Bacteria: 535, 1425
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535, 1442
Crustacea: 535, 1039, 1384, 1425, 1442, 1498, 2024, 2188, 2227
Echinodermata: 535, 1442, 2024
E1asmobranchii: 1442
Fish: 156, 334, 535, 754, 940, 1442, 1465, 1628, 2000, 2001, 2024,
2188, 2227
Higher Plants: 535
Insecta: 1558
Mammalia: 2024
Mollusca: 535, 957, 1039, 1384, 1442, 2024, 2188, 2227
Phoronidea: 535
Porifera: 535
393
-------
Protozoa:
Tunicata:
535
535
RUTHENIUM
Porifera:
Reptilia:
Sediments:
Tunicata:
Algae: 17, 28, 53, 150, 214, 281, 483, 539, 541,
583, 584, 585, 586, 599, 851, 1029, 1038,
1320, 1413, 1437, 1518, 1532, 1540, 1612,
1676, 1828, 1917, 1963, 2011, 2019, 2208
Amphibia: 2011
Annelida: 583, 599, 919, 1088, 1963
Aves: 541, 851, 1038, 1518, 1676, 1828, 2208
Bryophyta: 1038, 1676, 1917
Coelenterata: 586, 851, 1320, 1659, 1676, 2208
Crustacea: 28, 53, 111, 265, 539, 541, 582, 583, 586, 600, 851, 907,
955, 1038, 1100, 1134, 1320, 1331, 1369, 1413, 1437,
1518, 1612, 1659, 1676, 1943, 1945, 1956, 1963, 2011,
2019, 2208
Detritus: 110, 111, 393
Echinodermata: 1038, 1413, 1676, 2208
E1asmobranchii: 353, 1963
Fish: 28, 53, 150, 281, 310, 539, 541, 547, 582, 583, 586, 599, 636,
851, 861, 919, 940, 1038, 1088, 1134, 1156, 1209, 1320, 1369,
1413, 1437, 1518, 1540, 1612, 1676, 1828, 1912, 1917, 1956,
2011, 2019
Higher Plants: 310, 541, 555, 599, 1038, 1134, 1369, 1612, 1676,
1917, 2011
599, 1518, 1617, 2011
310, 541, 599, 851, 1038, 1209, 1676, 1956
28, 53, 190, 281, 457, 539, 541, 557, 565, 582, 583, 586,
599, 600, 886, 911, 955, 1029, 1038, 1156, 1209, 1320,
1369, 1413, 1437, 1612, 1659, 1676, 1725, 1752, 1828,
1956, 1963, 1990, 2011, 2019, 2208
333, 584, 1038, 1518, 1676, 1917, 2208
2011
73,150,281,541,551,1369,1956
584, 1320, 1945
547, 551, 555,582,
1100, 1134, 1209,
1653, 1654, 1659,
Insecta:
Mammalia:
Mollusca:
SALINITY
Algae: 9, 462, 624,
2120, 2145
Annelida: 652, 900,
Bacteria: 297, 701,
Brachiopoda: 2145
Bryazoa: 2145, 2209
Coelenterata: 1764,
848, 1048, 1108, 1289, 1290, 1477, 1963, 1994,
1351, 1742, 1764, 1963, 2145, 2209
826, 1068, 1383, 1486
2145, 2209
394
-------
Crustacea: 148, 461, 506, 511, 523, 593, 607, 625, 715, 716, 718,
719, 791, 830, 855, 899A, 938, 942, 1007, 1008, 1090,
1150, 1245, 1265, 1289, 1393, 1412, 1475, 1477, 1491,
1526, 1528, 1559, 1623, 1656, 1696, 1705, 1706, 1707,
1743, 1763, 1764, 1825, 1898, 1951, 1952, 1963, 1984,
1986, 2029, 2057, 2083, 2097, 2100, 2131, 2134, 2145,
2157, 2161, 2209
Echinodermata: 578, 1764, 2145, 2209
E1asmobranchii: 1764, 1963
Fish: 7,8, 15,23,57,59, 103, 112, 117, 144, 177, 199,200,201,
237,246,247,251,252,253,307,341,356,388,389,422,
462, 470, 507, 510, 518, 573, 574, 575, 576, 609, 611, 621,
658, 689, 690, 691, 744, 753, 858, 926, 939, 948, 953, 976,
980, 986, 1009, 1103, 1113, 1114, 1126, 1127, 1143, 1169,
1178, 1200, 1225, 1231, 1297, 1300, 1303, 1304, 1306, 1308,
1398, 1401, 1467, 1468, 1477, 1488, 1489, 1519, 1524, 1546,
1560, 1576, 1649, 1661, 1691, 1700, 1705, 1764, 1766, 1778,
1802, 1844, 1847, 1848, 1850, 1857, 1877, 1915, 1983, 1984,
1985, 2031, 2074, 2093, 2146, 2186, 2209, 2210, 2211, 2212,
2213, 2241, 2242
Fungi: 1157, 1513, 1737, 1851
Higher Plants: 1187, 1477, 2159
Insecta: 1661, 1764, 2209
Miscellaneous: 289
Mollusca: 148, 367, 518, 594, 659, 680,
1277, 1278, 1313, 1355, 1403,
1570,1660,1691,1715,1764,
2111, 2145, 2151, 2209
Phoronidea: 2145
Platyhelminthes: 1351, 2145, 2209
Porifera: 2145
Protozoa: 2145, 2209
Reptilia: 743
Rotifera: 1805
Sediments: 1277, 1486
Siponcu1oidea: 764
Tunicata: 2145
SAMARIUM
Algae: 535, 1498, 1522
Annelida: 404, 405, 535
Bacteria: 535
Brachiopoda: 535
Bryaz oa: 535
Coelenterata: 535
Crustacea: 535, 1499
Echinodermata: 535
395
968, 969, 970, 1152, 1237,
1422, 1452, 1486, 1538,
1851, 1963, 1978, 1992,
-------
Fish: 535, 1465
Higher Plants: 535
Mollusca: 404, 405,
Phoronidea: 535
Porifera: 535
Protozoa: 535
Tunicata: 535
535, 1224
SCANDIUM
Algae: 932, 1166, 1498, 1499, 1518, 1522, 1859, 2009, 2011, 2024
Amphibia: 2011
Annelida: 404, 405
Aves: 1518, 2024
Coelenterata: 965
Crustacea: 124, 1384, 1498, 1499, 1518, 1859, 2011, 2024
Echinodermata: 2024
Fish: 273, 1465, 1518, 2000, 2001, 2009, 2010, 2011, 2023, 2024
Higher Plants: 2011
Insecta: 1518, 1558, 2011
Mammalia: 2024
Mollusca: 404, 405, 1166, 1224, 1384, 2011, 2023, 2024
Plankton: 1859
Porifera: 1518
Reptilia: 2011
SELENIUM
Mollusca:
Plankton:
Sediments:
Algae: 684, 702, 941, 1149, 1425, 1498, 1522, 1835, 2024, 2056
Aves: 1611, 1762, 1780, 2024
Bacteria: 1220, 1425, 1463
Crustacea: 702, 1149, 1384, 1425, 1498, 1584, 1585, 1586, 1834, 2024
Echinodermata: 2024
Fish: 334, 827, 940, 979, 1065, 1149, 1257, 1352, 1465, 1551, 1596,
1611, 1702, 1728, 1762, 1831, 1834, 1838, 1840, 1922, 1940,
1989, 2000, 2001, 2007, 2024, 2056, 2173
Fungi: 1463
Higher Plants: 1262, 1835, 2056
Insecta: 1558
Mammalia: 827, 933, 1262, 1352, 1596, 1611, 1780, 1834, 1861, 2024,
2056
1077, 1224, 1384, 1585, 1586, 1596, 1834, 2024
2056
1262
SILICON
Algae:
535, 601, 694, 848, 918, 957A, 959, 960, 978, 983, 992, 999,
1043, 1061, 1062, 1405, 1498, 1499, 1599. 1994, 2143, 2234
396
-------
Annelida: 535
Bacteria: 535, 1173
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 1599
Coelenterata: 535, 965, 1392, 1599
Crustacea: 535, 992, 1498, 1499, 1599
Echinodermata: 535
Fish: 309, 535, 1465, 1628, 1717
Higher Plants: 535
Mollusca: 535
Phoronidea: 535
Porifera: 535
Protozoa: 535, 1599
Tunicata: 535, 1599
SILVER
Algae: 228, 269, 535, 628, 648, 778, 833, 992, 1130, 1164, 1208,
1264, 1288, 1411, 1425, 1498, 1499, 1627, 1645, 1669. 1987,
1991, 2024, 2183, 2188, 2227
Amphibia: 1171
Anne1i4a: 535, 648, 1312, 1436
Aves: 2024
Bacteria: 535, 571, 572, 1173, 1425, 1486, 1606, 2094, 2125
Brachiopoda: 535
Bryazoa: 535, 648
Chaetognatha: 2183
Coelenterata: 535,1131,1312,1392,1627
Crustacea: 535, 614, 648, 695, 783, 784, 992, 1039, 1075, 1164, 1171,
1312, 1315, 1360, 1384, 1411, 1425, 1498, 1499, 1627,
1645, 1647, 1740, 1987, 2024, 2183, 2188, 2227
Ctenophora: 2183
Echinodermata: 485, 535, 1131, 1312, 2024
E1asmobranchii: 1627
Fish: 142, 143, 156, 241, 271, 273,
754, 783, 784, 865, 887, 898,
1311, 1440, 1613, 1625, 1628,
2000, 2001, 2023, 2024, 2142,
Higher Plants: 535, 1312
Insecta: 1360, 1625, 1909
Mammalia: 202, 783, 1861, 2024
Miscellaneous: 392, 563
Mollusca: 221, 535, 638, 639, 649, 670, 671, 695, 742, 783, 784, 821,
982, 1039, 1162, 1164, 1272, 1309, 1312, 1321, 1384, 1486,
1589,1627,1645,1646,1862,1910.1987,1990,1991,1993,
2023, 2024, 2150, 2151, 2188, 2199, 2200, 2227
Phoronidea: 535
386, 535, 616, 648, 692, 697,
940, 945, 1164, 1171, 1218, 1235,
1645, 1647, 1683, 1873, 1987,
2188, 2227
397
-------
Platyhelminthes: 1312, 1739, 1740
Porifera: 535, 1627
Protozoa: 535, 1171, 1627
Rotifera: 1440
Sediments: 1486, 1991
Tunicata: 535, 1627
SODIUM
Algae: 535, 602, 694, 846, 848, 983, 992, 1406, 1498, 1499, 1522,
1599, 1722, 1979, 2011, 2024, 2065, 2183, 2196, 2234, 2238
Amphibia: 184, 317, 1418, 1668, 1765, 2011, 2172
Annelida: 115, 535, 868, 900, 1442, 2025
Aves: 2024
Bacteria and yeasts: 535, 971, 1068, 1383, 1786, 2035
Brachiopoda: 535
Bryazoa: 535, 1382
Chaetognatha: 1599, 2183
Coelenterata: 535, 1131, 1319, 1442, 1599. 1777, 2025
Crustacea: 12, 13, 31, 84, 113, 115, 264, 336, 423, 461, 535, 602,
626, 645, 716, 749, 798, 820, 829, 830, 992, 1210, 1294,
1442, 1498, 1499, 1510, 1511, 1567, 1581, 1594, 1599,
1738, 1765, 1825, 1950, 1951, 1984, 1986, 2011, 2024,
2025, 2097, 2131, 2157, 2183
Ctenophora: 2183
Echinodermata: 535, 1131, 1442, 1897, 2024, 2025
E1asmobranchii: 153,263, 1377, 1442, 1531, 1569, 1727, 1854,1855,
1856, 2004
Fish: 1, 2, 7, 15, 80, 99. 108, 113, 115, 123, 128, 142, 152, 156,
157, 162, 163, 164, 165, 184, 199, 200, 213, 225, 239, 245,
251, 258, 264, 273, 307, 341, 356, 452, 528, 535, 621, 658,
714, 725, 749, 754, 798, 869, 876, 888, 889, 898, 915, 920,
940, 950, 980, 981, 986, 987, 988, 1026, 1027, 1053, 1054,
1094, 1103, 1143, 1169, 1197, 1198, 1199. 1210, 1228, 1229,
1230, 1235, 1299, 1300, 1303, 1304, 1306, 1357, 1401, 1423,
1442, 1465, 1488, 1489, 1519, 1560, 1565, 1566, 1569, 1576,
1628, 1633, 1644, 1650, 1651, 1652, 1683, 1700, 1717, 1727,
1728, 1747, 1757, 1765, 1766, 1778, 1795, 1802, 1820, 1826,
1844, 1847, 1848, 1872, 1889, 1902, 1930, 1946, 1976, 1977,
1983, 1984, 1985, 2000, 2001, 2004, 2007, 2011, 2015, 2024,
2092, 2116, 2146, 2194, 2243
Fungi: 1514
Higher Plants: 535, 570, 950, 1201, 1722, 2011
Insecta: 115, 602, 1558, 2011
Mammalia: 1861, 2024, 2035
Mollusca: 32, 33, 34, 61, 84, 108, 115, 158, 184, 367, 535, 629, 700,
749, 769, 957, 1106, 1162, 1196, 1341, 1442, 1444, 1687,
2011, 2024, 2025, 2036
398
-------
Phoronidea: 535
Platyhelminthes: 1738, 1739
Porifera: 535
Protozoa: 535, 1361, 1599, 2136
Reptilia: 149, 2011
Sediments: 184, 950
Tunicata: 535, 1599
STRONTIUM
Algae: 6, 53, 150, 188, 215, 222, 223, 224, 242, 261, 298, 310, 347,
380, 381, 387, 413, 414, 415, 417, 439, 522, 532, 535, 541,
547, 566, 628, 648, 674, 683, 703, 818, 840, 851, 862, 901,
992, 1015, 1016, 1038, 1070, 1071, 1100, 1102, 1112, 1116,
1130, 1139, 1208, 1209, 1234, 1250, 1399, 1406, 1413, 1425,
1437, 1470, 1498, 1518, 1522, 1540, 1612, 1627, 1673, 1676,
1759, 1774, 1859, 1868, 1955, 1959, 1963, 2011, 2018, 2019,
2020, 2024, 2045, 2046, 2138, 2145, 2183, 2207, 2218, 2227
Amphibia: 79, 184, 335, 897, 2011
Annelida: 370, 535, 648, 1595, 1868, 1963, 2145
Aves: 347, 541, 851, 928, 1038, 1518, 1676, 2024
Bacteria: 322, 532, 535, 1102, 1425
Brachiopoda: 535, 2145
Bryazoa: 232, 535, 648, 2145
Bryophyta: 6, 310, 414, 1038, 1676
Chaetognatha: 1758, 2183
Coelenterata: 413, 414, 535, 851, 931, 965, 1019, 1131, 1319, 1392,
1627, 1676, 1868, 1927, 1955, 2145
Crustacea: 13, 53, 107, 188, 261, 264, 291, 299, 348, 358, 360, 380,
381, 413, 414, 439, 466, 467, 532, 535, 541, 589, 626,
648, 674, 749, 812, 850, 851, 862, 991, 992, 993, 1016,
1038, 1039, 1100, 1102, 1116, 1139. 1234. 1315, 1350,
1369, 1413, 1425, 1437, 1470, 1498, 1518, 1612, 1627,
1676, 1758, 1759, 1849, 1859. 1868, 1955, 1959. 1963,
2011, 2019, 2020, 2024, 2145, 2183, 2227
Ctenophora: 2183
Detritus: 6, 393, 413, 415
Echinodermata: 188, 261, 535, 862, 1038, 1131, 1413, 1676, 1868,
1897, 1955, 2024, 2145
E1asmobranchii: 353, 1627, 1868, 1963
Fish: 4, 16, 53, 67, 68, 69, 75, 79, 80, 142, 150, 156, 169, 170,
184, 188, 222, 242, 261, 262, 264, 310, 349, 359, 360, 368,
371, 379, 380, 381, 403, 435, 439. 443, 444, 445, 449, 450,
455, 458, 459, 474, 514, 524, 525, 535, 541, 547, 589, 603,
605, 616, 633, 636, 648, 674, 677, 749, 754, 851, 862, 898,
928, 940, 1016, 1030, 1034, 1038, 1055, 1056, 1058, 1071, 1139,
1172, 1209, 1216, 1217, 1221, 1234, 1235, 1239, 1302, 1314,
1369, 1378, 1379, 1413, 1414, 1437, 1465, 1470, 1518, 1540,
399
-------
Reptilia:
Sediments:
Tunicata:
Fish (cont.): 1612, 1628, 1676, 1711, 1728, 1759, 1796, 1868, 1938,
1954, 1955, 2007, 2011, 2019, 2020, 2024, 2050, 2051,
2138, 2227
Higher P'1ants: 347, 522, 535, 541, 568, 589, 818, 901, 1038, 1056,
1058, 1070, 1201, 1369, 1612, 1676, 1759. 1938, 2011,
2138
Insecta: 370, 1016, 1518, 1617, 2011
Mammalia: 202, 310, 347, 541, 851, 1038, 1056, 1148, 1209, 1676,
2024
Miscellaneous: 358
Mollusca: 14, 53, 65, 66, 79, 184, 188, 190, 196, 224, 242, 261,
347, 370, 385, 387, 413, 414, 417, 439, 466, 535, 541,
674, 749, 862, 1033, 1037, 1038, 1039, 1078, 1107, 1139,
1162, 1209, 1234, 1239, 1332, 1369, 1413, 1437, 1470,
1595, 1612, 1627, 1676, 1758, 1759, 1794, 1814, 1868,
1911, 1954, 1955, 1963, 1978, 2011, 2019, 2024, 2036,
2050, 2145, 2164, 2227
Phoronidea: 535, 2145
Phytoplankton: 322
Plankton: 466, 1859, 1959
Platyhelminthes: 1739, 2145
Porifera: 535, 1038, 1518, 1627, 1676, 1868, 2145
Protozoa: 413, 414, 466, 535, 1000, 1361, 1627, 1793, 1959. 2145,
2195
2011
73,79,150,184,466,541,818,901,1369
535, 1627, 1758, 1868, 2145
TANTALUM
Algae: 1208, 2024
Aves: 2024
Crustacea: 2024
Echinodermata: 2024
Fish: 940, 1465, 2024
Insecta: 1558
Mammalia: 2024
Mollusca: 2024
Tunicata: 1457
TECHNETIUM
Algae: 1653, 1654
Sediments: 73
TELLURIUM
Algae:
1522, 2019, 2188
400
-------
Crustacea: 265, 2019, 2188
Fish: 940, 2019, 2188
Mollusca: 2019, 2188
TERBIUM
Algae: 1522, 2024
Aves: 2024
Crustacea: 2024
Echinodermata: 2024
Fish: 2024
Mammalia: 2024
Mollusca: 2024
THALLIUM
Algae: 535, 1522, 1627, 1947
Amphibia: 138, 2244
Annelida: 535
Aves: 995
Bacteria: 535, 2094, 2244
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535, 1627
Crustacea: 369, 535, 995, 1627, 2244
Echinodermata: 535
E1asmobranchii: 1627
Fish: 156, 273, 369. 535, 754, 940, 995, 1683, 2244
Higher Plants: 535, 995
Mollusca: 535, 1627, 2245
Phoronidea: 535
Porifera: 535, 1627
Protozoa: 535, 1627
Sediments: 995
Tunicata: 535, 1627
THORIUM
Algae: 151, 747, 932, 1016, 1202, 1425, 1522, 2024, 2188, 2227
Aves: 2024
Amphibia: 138
Bacteria: 1425
Coelenterata: 1529, 1716
Crustacea: 1016, 1425, 1760, 2024, 2188, 2227
Echinodermata: 2024
Fish: 334, 401, 940, 977, 1016, 1465, 2024, 2188, 2227
Higher Plants: 401
Insecta: 1016, 1558
401
-------
Mammalia:
Mollusca:
401, 2024
1224, 2024, 2165, 2188, 2227
THULIUM
Algae:
1522
TIN
Algae: 535, 628, 1130, 1208, 1498, 1499, 1522, 1627, 2166, 2183
Annelida: 535
Bacteria: 535, 1606
Brachiopoda: 535
Bryazoa: 232, 535
Chaetognatha: 2183
Coelenterata: 535, 1131, 1627
Crustacea: 13, 92, 409, 506, 535, 626, 1039, 1498, 1499, 1525, 1627,
2043, 2183
Ctenophora: 2183
Echinodermata: 535, 1131
E1asmobranchii: 1627
Fish: 106, 142, 294, 403, 409, 535, 775, 940, 1218, 1219, 1465,
1717, 2166, 2173
Higher Plants: 535
Mollusca: 535, 1039, 1077, 1525, 1563, 1627, 1993, 2118
Phoronidea: 535
Porifera: 535, 1627
Protozoa: 535, 1627, 2043
Tunicata: 535, 1627
TITANIUM
Algae: 535, 628, 792, 992, 1130, 1208, 1425, 1484, 1498, 1499, 1522,
1627, 1657, 2049, 2183, 2188, 2232
Annelida: 535
Bacteria: 535, 1425
Brachiopoda: 535
Bryazoa: 535
Chaetognatha: 7183
Coelenterata: 535, 965, 1392, 1627
Crustacea: 535, 992, 1039, 1425, 1498, 1499, 1520, 1627, 2183, 2188
Ctenophora: 2183
Echinodermata: 535
E1asmobranchii: 1627
Fish: 403, 535, 940, 1465, 1520, 1628, 1873, 2188
Higher Plants: 535, 2049, 2232
Mollusca: 535, 1039, 1627, 2188
Phoronidea: 535
402
-------
Porifera:
Protozoa:
Tunicata:
535, 1627
535, 1627, 1793
535, 1457, 1627
TUNGSTEN
Algae: 535, 792, 1208, 1425, 1522, 1604, 1605, 2166
Annelida: 535
Bacteria: 535, 1425
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535
Crustacea: 535, 1425, 1604, 1605
Echinodermata: 535
Fish: 535, 1465, 1604, 1605, 1831, 2005, 2166
Higher Plants: 535
Mollusca: 535, 1604, 1605
Phoronidea: 535
Porifera: 535
Protozoa: 535
Tunicata: 535, 1457
URANIUM
Algae: 151, 308, 588, 747, 788, 932, 1016, 1425, 1522, 1955, 2188,
2227
Amphibia: 2058
Bacteria and yeasts: 206, 427, 1032, 1425, 2035
Coelenterata: 965, 1716, 1955
Crustacea: 1016, 1017, 1425, 1760, 1955,2188,2227
Echinodermata: 1955
Fish: 27, 308, 334, 512, 588, 945, 977, 1016, 1017, 1465, 1955,
1683, 2173, 2188, 2227
Higher Plants: 788, 1017
Insecta: 588, 1016
Mammalia: 788, 2035
Miscellaneous: 392
Mollusca: 1017, 1955, 2188, 2227
Protozoa: 1032
VANADIUM
Algae: 535, 628, 683, 788, 792, 983,
1604, 1605, 1657, 1627, 2049,
Annelida: 535
Aves: 1556
Bacteria and yeasts: 535, 1556
Brachiopoda: 535
992, 1130, 1208, 1498, 1522,
2183, 2188, 2232
403
-------
Bryazoa: 232, 535
Chaetognatha: 2183
Coelenterata: 535, 1392, 1556, 1627
Crustacea: 535, 992, 1039, 1498, 1556, 1604, 1605, 1627, 2183, 2188
Ctenophora: 2183
Echinodermata: 535
E1asmobranchii: 1627
Fish: 106, 403, 535, 940, 1218, 1465, 1556, 1604, 1605, 1628, 2188
Fungi: 1556
Higher Plants: 535, 788, 1556, 2049, 2232
Insecta: 1558
Mammalia: 788, 1556
Mollusca: 535, 638, 639, 1039, 1107, 1456, 1556, 1604, 1605, 1627,
2188
Phoronidea: 535
Porifera: 535, 1627
Protozoa: 535, 1627
Tunicata: 535, 1204, 1456, 1457, 1476, 1553, 1627, 1630, 1745, 1797,
1798, 1883, 2038, 2202
YTTERBIUM
Algae: 1498, 1522
Crustacea: 1498
Fish: 1465
YTTR IUM
Algae: 215, 387, 439, 535, 703, 1246, 1413, 1498, 1522, 1540, 1627,
1828, 1963, 2018, 2019, 2046, 2227
Amphibia: 335
Annelida: 535, 1595, 1963
Aves: 1828
Bacteria: 322, 535
Brachiopoda: 535
Bryazoa: 535
Coelenterata: 535, 1627, 1927
Crustacea: 299, 439. 466, 535, 1413, 1498, 1627, 1963, 2019, 2227
Echinodermata: 535, 1413
E1asmobranchii: 1627, 1963
Fish: 22, 68, 75, 273, 368, 439, 474, 514, 525, 535, 1030, 1413, 1414,
1540, 1828, 2019, 2227
Higher Plants: 535
Insecta: 192
Mollusca: 387, 439, 466, 535, 1037, 1413, 1595, 1627, 1828, 1963,
2019, 2227
Phoronidea: 535
Phytoplankton: 322
404
-------
Plankton:
Porifera:
Protozoa:
Sediments:
Tunicata:
466
535, 1627
535, 1627
466
535. 1627
ZINC
Algae: '40, 47, 48, 53, 54, 87, 102, 127, 193, 210, 211, 222, 224,
242, 269, 345, 354, 383, 394, 419, 420, 436, 471, 486, 521,
532, 535, 539, 550, 583, 597, 602, 628, 632, 648, 651, 683,
702, 709, 713, 722, 781, 785, 802, 803, 804, 840, 849, 851,
862, 891, 932, 951, 973, 983, 992, 999, 1025, 1038, 1043,
1072, 1110, 1123, 1129, 1130, 1134, 1139, 1164, 1166, 1208,
1209, 1234, 1256, 1263, 1264, 1266, 1275, 1296, 1323, 1339.
1349, 1373, 1382, 1407, 1413, 1420, 1425, 1437, 1445, 1448,
1449, 1470, 1471, 1481, 1483, 1492, 1498, 1499, 1518, 1522,
1579, 1600, 1627, 1643, 1645, 1669, 1672, 1699. 1709, 1719.
1720, 1721, 1731, 1754, 1773, 1774, 1818, 1828, 1835, 1846,
1853, 1859, 1863, 1880, 1947, 1955, 1963, 1979, 1991, 1998,
1999, 2009, 2011, 2019. 2020, 2024, 2049, 2106, 2107, 2120,
2137, 2160, 2166, 2183, 2188, 2192, 2208, 2214, 2225, 2227,
2228, 2238, 2239
Amphibia: 79, 138, 184, 804, 1171, 1535, 1953, 1980, 2011, 2058,
2244
Annelida: 217, 284, 404, 405, 535, 545, 553, 583, 648, 650, 653,
676, 707, 726, 994, 1121, 1124, 1273, 1305, 1382, 1428,
1436, 1681, 1869, 1944, 1957, 1963, 1965, 2014, 2137,
2147
Arachnoidea: 1973
Aves: 836, 851, 1038, 1382, 1387, 1518, 1556, 1828, 2024, 2208
Bacteria and yeasts: 419, 532, 535, 571, 572, 804, 1098, 1266, 1425,
1448, 1449, 1486, 1555, 1556, 1785, 1846, 1884,
1957, 2063, 2244
Brachiopoda: 535
Bryazoa: 232, 535, 553, 648, 1382
Bryophyta: 284, 1038
Chaetognatha: 313, 1408, 1758, 2183
Coelenterata: 526, 535, 851, 904, 965, 1131, 1382, 1556, 1600, 1627,
1719. 1818, 1867, 1944, 1955, 2072, 2208
Crustacea: 13, 40, 53, 60, 80, 92, 102, 124, 125, 145, 147, 148,
181, 182, 183, 284, 313, 314, 343, 344. 360, 378, 382,
397, 409, 421, 471, 506, 507, 508, 532, 535. 539, 546,
553, 561, 583, 597, 602, 625, 626, 631, 632, 647, 648,
675, 695, 699, 702, 713, 749, 759, 785, 789, 791, 804,
837, 851, 862, 881A, 946, 952, 973, 991, 992, 1038, 1060,
1075, 1089. 1117, 1123, 1129, 1134, 1139, 1164, 1171,
1184, 1211, 1212, 1234, 1249. 1256, 1273, 1286, 1296,
405
-------
Crustacea (cont.):
1305, 1331, 1350, 1360, 1368,
1407, 1408, 1413, 1419, 1425,
1437, 1448, 1470, 1498, 1499,
1581, 1582, 1583, 1588, 1590,
1647, 1681, 1695, 1708, 1709,
1758, 1772, 1818, 1859, 1875,
1945, 1955, 1963, 1973, 2011,
2024, 2043, 2053, 2064, 2072,
2107, 2112, 2137, 2147, 2156,
2208, 2215, 2227, 2229, 2235,
1382, 1384, 1388,
1428, 1434, 1435,
1518, 1535, 1556,
1600, 1627, 1645,
1719, 1738, 1744,
1876, 1919, 1934,
2016, 2019, 2020,
2089, 2090, 2106,
2183, 2188, 2189,
2244
Ctenophora: 2183
Detritus: 286, 2227
Echinodermata: 101, 291, 384, 485, 533, 535,
1131, 1287, 1305, 1382, 1413,
1897, 1934, 1944, 1955, 1973,
2198, 2208
E1asmobranchii: 153, 1564, 1627, 1963, 1964
Fish: 3, 18, 19, 20, 40, 48, 53, 62, 76, 77, 78, 79, 81, 93, 94, 95,
97, 98, 106, 108, 109, 123, 128, 142, 152, 154, 156, 157, 179,
184, 198,203,205,207,209,217,222,229,233,234,238,
241,242,250,273,282,284,287,288,292,314,315,327,
328, 329, 330, 334, 343, 344, 345, 360, 362, 378, 38~, 394,
398, 406, 407, 408, 409, 411, 412, 430, 431, 432, 436, 437,
438, 454, 463, 464, 471, 479, 480, 481, 482, 487, 488, 489,
490, 491, 492, 493, 494, 495, 496, 504, 507, 521, 535, 539,
540, 564, 583, 597, 604, 605, 640, 643, 644, 648, 655, 656,
660, 661, 663, 664, 665, 666, 667, 668, 669, 675, 678, 682,
685, 697, 708, 713, 745, 749, 751, 752, 754, 758, 759, 785,
802, 804, 827, 837, 843, 851, 859, 862, 865, 887, 898, 899,
940, 950, 951, 952, 973, 977, 979, 994, 998, 1021, 1028, 1035,
1038, 1082, 1083, 1087, 1092, 1098, 1109, 1120, 1121, 1122,
1123, 1129, 1134, 1139, 1141, 1142, 1147, 1156, 1164, 1171,
1178, 1181, 1188, 1191, 1192, 1193, 1195, 1209, 1217, 1218,
1234, 1235, 1251, 1252, 1269, 1279, 1295, 1322, 1346, 1362,
1363, 1364, 1365, 1366, 1373, 1382, 1387, 1404, 1407, 1408,
1413, 1421, 1427, 1431, 1437, 1440, 1448, 1449, 1451, 1465,
1470, 1471, 1518, 1535, 1541, 1554, 1555, 1556, 1564, 1577,
1613, 1625, 1628, 1645, 1647, 1662, 1665, 1683, 1684, 1688,
1689, 1690, 1695, 1709, 1710, 1717, 1728, 1820, 1823, 1826,
1828, 1831, 1838, 1873, 1881, 1907, 1908, 1912, 1919, 1939,
1940, 1954, 1955, 1965, 1971, 1981, 2000, 2001, 2007, 2009,
2010, 2011, 2016, 2019, 2020, 2023, 2024, 2032, 2047, 2050,
2051, 2055, 2060, 2063, 2072, 2079, 2084, 2087, 2088, 2102,
2106, 2107, 2112, 2129, 2137, 2141, 2166, 2173, 2181, 2188,
2201, 2203, 2225, 2227, 2229, 2243, 2244, 2246
Fungi: 1079, 1157, 1266, 1449, 1556, 1674, 1686, 2191
675, 862, 1022, 1038,
1479, 1564, 1776, 1867,
2024, 2072, 2106, 2137,
406
-------
Higher Plants: 19, 284, 418, 419, 437, 535, 570, 619, 650, 802, 849,
950, 1038, 1123, 1129, 1134, 1273, 1279, 1382, 1454,
1556, 1709, 1721, 1775, 1835, 1842, 1886, 1919, 2011,
2049, 2107, 2225
Insecta: 217, 284, 286, 410, 493, 537, 602, 802, 804, 1121, 1212,
1273, 1283, 1284, 1360, 1518, 1535, 1558, 1617, 1625, 1662,
1788, 1909, 1919, 2011, 2147
Mammalia: 202, 597, 758, 827, 851, 933, 1038, 1129, 1209, 1382, 1387,
1556, 1694, 1775, 1861, 2024, 2072
Miscellaneous: 89, 127, 392, 1373
Mollusca: 53, 62, 79, 93, 108, 135, 136, 145, 146, 147, 148, 158,
172, 174, 184, 194, 217, 219, 220, 223, 224, 242, 284, 313,
354, 383, 394, 395, 404, 405, 421, 424, 425, 426, 451, 457,
475, 477, 504, 506, 524, 533, 535, 539, 553, 557, 559, 560,
561, 562, 583, 598, 623, 637, 638, 639, 642, 649, 670, 671,
675, 676, 695, 699, 700, 705, 731, 738, 742, 749, 758, 770,
776, 785, 789, 804, 821, 857, 862, 875, 909, 910, 935, 946,
951, 982, 994, 1037, 1038, 1076, 1086, 1107, 1115, 1117,
1121, 1129, 1135, 1136, 1139, 1156, 1162, 1164, 1166, 1167,
1209, 1234, 1236, 1256, 1272, 1276, 1279, 1286, 1305, 1309,
1321, 1382, 1384, 1388, 1407, 1413, 1415, 1416, 1417, 1419,
1437, 1445, 1448, 1450, 1470, 1471, 1486, 1507, 1535, 1537,
1549, 1556, 1563, 1564, 1589, 1591, 1592, 1609, 1627, 1645,
1646, 1681, 1685, 1704, 1709, 1712, 1713, 1714, 1719, 1746,
1758, 1787, 1828, 1845, 1862, 1867, 1874, 1875, 1876, 1887,
1888, 1892, 1916, 1919, 1923, 1934, 1954, 1955, 1963, 1973,
1974, 1975, 1990, 1991, 1993, 2011, 2019, 2023, 2024, 2050,
2064, 2072, 2073, 2081, 2105, 2106, 2107, 2118, 2137, 2147,
2148, 2149, 2156, 2176, 2188, 2190, 2199, 2200, 2208, 2224,
2227, 2230, 2237, 2239
Phoronidea: 535
Plankton: 1860
Platyhelminthes: 284, 1535, 1738, 1739, 1919
Porifera: 535, 1038, 1518, 1627, 1719, 2137, 2208
Protozoa: 535, 622, 679, 823, 1171, 1254, 1448, 1449, 1627, 1634,
1846, 1969, 2043
2011
1440, 2122, 2123
48, 79, 101, 147, 184, 217, 418, 419, 437, 477, 707, 731,
787, 849; 950, 951, 1373, 1445, 1486, 1709, 1969, 1991,
2106, 2107, 2215
Seston: 2204
Tunicata: 313, 382, 535, 1564, 1600, 1627, 1719, 1758, 1945, 1973
Reptilia:
Rotifera:
Sediments:
ZIRCONIUM
Algae:
102, 178, 193, 214, 310, 333, 483, 539, 555, 582, 585, 851,
852, 1029, 1038, 1166, 1208, 1437, 1484, 1498, 1499, 1518,
407
-------
Algae (cont.): 1522, 1540. 1612, 1627, 1676, 1828, 1917, 1959.
2019, 2183, 2227
Annelida: 1088, 1944
Aves: 851, 1038, 1518, 1676, 1828
Bryophyta: 1038, 1676, 1917
Chaetognatha: 2183
Coelenterata: 851, 1627, 1676, 1944
Crustacea: 102, 111, 360, 466, 539, 582, 851, 1038, 1369, 1437,
1498, 1499, 1518, 1612, 1627, 1676, 1943, 1945, 1956,
1959, 2019, 2183, 2227
Ctenophora: 2183
Detri tus: 110, 111
Echinodermata: 1038, 1676, 1944
E1asmobranchii: 353, 1627
Fish: 310, 360, 383, 539, 582, 851,
1518, 1540, 1612, 1628, 1676,
Higher Plants: 310, 555, 852, 1038,
Insecta: 1518, 1558, 1617
Mammalia: 310, 851, 852, 1038, 1676, 1956
Mollusca: 190, 194, 383, 466, 539. 557, 582, 1029, 1038, 1166, 1369,
1437, 1612, 1627, 1676, 1828, 1956, 1990, 2019. 2227
466, 1959
333, 1038, 1518, 1627, 1676, 1917
1627, 1959
466, 1369. 1956
1457, 1564, 1627, 1945
940, 1038, 1088, 1369, 1437,
1828, 1917, 1956, 2019, 2227
1369. 1612, 1676, 1917
Plankton:
Porifera:
Protozoa:
Sediments:
Tunicata:
408
-------
INDEX - TAXA
ALGAE
Actinium: 1016
Aluminum: 535, 792, 992, 1130, 1289, 1405, 1425, 1498, 1499, 1503,
1522, 1669, 2183, 2188, 2234
Antimony: 483, 535, 541, 851, 932, 951, 1038, 1208, 1234, 1425,
1522, 1627, 1676, 1835, 1917, 1959, 2009, 2019, 2024.
2117, 2188, 2208, 2227
Arsenic: 42, 338, 420, 535, 632,
1208, 1382, 1400, 1407,
1500, 1518, 1522, 1604,
1836, 1837, 1839, 1841,
2238
Barium: 56, 228, 535, 628, 992, 1112, 1130, 1208, 1425, 1498, 1518,
1522, 1627, 1669, 1868, 2183, 2188
Beryllium: 535, 1038, 1130, 1208, 1498, 1499. 1522, 1676, 1917,
2183, 2188
Bismuth: 535, 541, 1016, 1130, 1208, 1498, 1522, 2188, 2208
Boron: 983, 1330, 1498, 1522, 1627, 1643, 1817, 1979, 2231
Cadmium: 242, 262, 486, 535, 632, 648, 683, 802, 833, 862, 873, 951,
959, 992, 1025, 1110, 1296, 1349, 1381, 1382, 1425, 1445,
1448, 1449, 1492, 1498, 1499, 1522, 1579, 1627, 1672, 1720,
1753, 1767, 1773, 1846, 1860, 1901, 1947, 1991, 2024, 2082,
2106, 2107, 2137, 2166, 2167, 2188
Calcium: 193, 269, 298, 380, 381, 503, 602, 648, 674, 694, 737, 792,
846, 880, 978, 983, 992, 1070, 1071, 1102, 1110, 1112, 1250,
1399, 1402, 1406, 1437, 1449, 1464, 1498, 1499, 1522, 1532,
1599, 1627, 1673, 1722, 1759, 1774, 1779, 1843, 1859. 1868,
1963, 1979, 2011, 2024, 2046, 2065, 2138, 2145, 2183, 2207,
2218, 2234, 2238
Cerium: 17, 28, 214, 215, 323, 333, 383, 413, 414, 415, 439, 440,
471, 483, 535, 539, 541, 555, 582, 583, 585, 586, 851, 862,
1029, 1038, 1100, 1128, 1164, 1425, 1437, 1498, 1518, 1522,
1540, 1612, 1726, 1917, 1955, 1959, 1963, 2011, 2019, 2020,
2046, 2208
Cesium: 28, 29, 53, 211, 222, 223, 224, 242, 261, 300, 310, 383, 399,
413,414,415,532,535,541,548,549,555,582,583,586,
762, 818, 840, 851, 862, 932, 1016, 1029, 1038, 1071, 1116,
1234, 1336, 1413, 1437, 1446, 1470, 1498, 1518, 1522, 1540,
1612, 1676, 1917, 1963, 2011, 2019, 2020, 2024, 2071, 2120,
2177, 2208, 2218, 2223, 2227
Chromium: 40, 383, 394, 526, 539,597,632,648,683, 702, 788, 792,
932, 992, 1025, 1043, 1105, 1130, 1208, 1234, 1264, 1382,
1425, 1448, 1449, 1481, 1498, 1518, 1522, 1579, 1602, 1603,
1627, 1645, 1657, 1722, 1723, 1853, 1955, 1972, 2009, 2011,
2024, 2049, 2183, 2188
706, 735, 748, 815, 951, 959, 1203,
1411, 1425, 1455, 1462, 1498, 1499,
1605, 1627, 1631, 1735, 1830, 1835,
1962, 1982, 2011, 2024, 2137, 2188,
409
-------
Cobalt: 193, 223, 224, 242, 261, 269, 333, 383, 446, 471, 472, 535,
541, 583, 632, 648, 683, 792, 840, 849, 851, 855, 932, 973,
974, 975, 983, 992, 1029, 1038, 1128, 1130, 1164, 1208,
1209, 1234, 1317, 1402, 1425, 1437, 1470, 1483, 1498, 1499,
1518, 1522, 1627, 1643, 1654, 1657, 1676, 1723, 1828, 1835,
1853, 1955, 1963, 2009, 2011, 2020, 2024, 2049, 2183, 2188,
2208, 2227, 2238
Copper: 42, 48, 122, 132, 134, 173, 175, 228, 256, 269, 332, 338,
339, 345, 346, 351, 394, 420, 486, 521, 535, 583, 597, 628,
632, 641, 648, 651, 683, 720, 732, 735, 736, 741, 748, 757,
777, 781, 803, 804, 814, 833, 841, 871, 961, 983, 991, 992,
999, 1024, 1025, 1040, 1041, 1042, 1043, 1110, 1130, 1134,
1139, 1153, 1207, 1208, 1247, 1250, 1263, 1264, 1275, 1285,
1288, 1289, 1296, 1349, 1373, 1381, 1382, 1389, 1397, 1411,
1420, 1425, 1448, 1449, 1460, 1481, 1498, 1499, 1503, 1518,
1522, 1579, 1627, 1643, 1655, 1657, 1669, 1670, 1671, 1672,
1699, 1703, 1709, 1720, 1724, 1731, 1748, 1753, 1773, 1774,
1835, 1863, 1870, 1871, 1880, 1899, 1904, 1920, 1921, 1947,
1979, 1991, 1999, 2002, 2011, 2024, 2040, 2041, 2049, 2062,
2066, 2096, 2106, 2107, 2115, 2121, 2127, 2128, 2130, 2137,
2160, 2166, 2183, 2188, 2228, 2234, 2238
Dysprosium: 1498, 1522
Erbium: 1498, 1522
Europium: 851, 1038, 1498, 1522, 1917, 1959, 2024, 2227
Gadolinium: 1498, 1522
Gallium: 535, 983, 1130, 1498, 1503, 1627, 2183
Germanium: 535, 601, 957A, 1498, 1627, 1735, 2143
Gold: 535, 932, 1208, 1604, 1605, 1627, 1669
Hafnium: 1498, 2024
Holmium: 1522
Indium: 1130, 1522
Iron: 30, 48, 132, 193, 223, 224, 242, 261, 262, 471, 513, 521,
535, 541, 550, 551, 583, 628, 632, 648, 651, 683, 696, 707,
721, 741, 781, 802, 840, 885, 932, 958, 973, 974, 983, 992,
1029, 1040, 1130, 1134, 1234, 1264, 1373, 1405, 1449, 1498,
1499, 1503, 1518, 1522, 1548, 1579, 1601, 1603, 1626, 1627,
1657, 1669, 1721, 1722, 1723, 1774, 1828, 1835, 1853, 1859,
1863, 1880, 1903, 1955, 1963, 1979, 1991, 2009, 2011, 2024,
2049, 2109, 2160, 2166, 2183, 2188, 2192, 2227, 2228, 2234,
2239
Lanthanum: 535, 1425, 1498, 1499, 1518, 1522, 1532
Lead: 228, 269, 420, 583, 597, 628, 632, 648, 651, 683, 741, 802,
803, 804, 833, 990, 992, 1043, 1130. 1160, 1168, 1208. 1263,
1264, 1275, 1296, 1381, 1382, 1407, 1425, 1445, 1449, 1455,
1481, 1498, 1499, 1522, 1579, 1627, 1669, 1672, 1679, 1680,
1720, 1753, 1773, 1880, 1894, 1947, 1991, 2006, 2024, 2106,
2107, 2110, 2137, 2160, 2166, 2183, 2188, 2214, 2227, 2238
410
-------
Lithium:
Lutetium:
Magnesium:
535, 628, 1425, 1449, 1498, 1522, 2183
1522
269, 602, 648, 694, 846, 880, 978, 992, 1399, 1406, 1420,
1449, 1464, 1498, 1499, 1522, 1574, 1598, 1599, 1627,
1669, 1722, 1843, 1979, 2065, 2183, 2207, 2234
Manganese: 17, 223, 224, 228, 261, 333, 383, 471, 483, 539, 541,
550, 555, 583, 628, 632, 651, 683, 707, 763, 777, 785
802, 804, 840, 849, 851, 973, 983, 992, 1038, 1100, 1130,
1134, 1139, 1164, 1208, 1234, 1264, 1437, 1498, 1499,
1518, 1522, 1579, 1601, 1627, 1655, 1657, 1669, 1722,
1723, 1773, 1774, 1811, 1828, 1835, 1853, 1859, 1863,
1880, 1955, 1959, 1963, 1979, 1991, 2011, 2019, 2046,
2049, 2106, 2107, 2109, 2166, 2183, 2188, 2192, 2208,
2214, 2227, 2234, 2238
Mercury: 269, 535, 597, 768, 802, 833, 834, 835, 839, 873, 874, 896,
927, 932, 949, 951, 992, 996, 997, 1043, 1047, 1096, 1166,
1208, 1247, 1264, 1381, 1382, 1409, 1410, 1411, 1425, 1441,
1448, 1449, 1481, 1482, 1498, 1499, 1506, 1515, 1516, 1522,
1527, 1571, 1597, 1598, 1624, 1643, 1648, 1667, 1669, 1672,
1699, 1735, 1750, 1822, 1824, 1928, 1947, 1949, 2024, 2082,
2085, 2106, 2107, 2137, 2154, 2169, 2188
Molybdenum: 535, 628, 683, 737, 983, 992, 1176, 1208, 1250, 1425,
1498, 1499, 1522, 1604, 1605, 1627, 1835, 1960, 1979,
2019, 2049, 2183, 2188, 2238
Neodymium: 535, 1498, 1499, 1522
Neptunium: 788, 1518
Nickel: 228, 269, 486, 535, 628, 648,
1043, 1130, 1208, 1382, 1425,
1579, 1627, 1643, 1657, 1669,
1991, 2049, 2106, 2107, 2109,
2238
Niobium: 102, 178, 214, 215, 333, 483, 535, 539, 555, 1029, 1038,
1166, 1208, 1437, 1498, 1518, 1522, 1540, 1612, 1676, 1828,
1917, 1963, 2019, 2227
Plutonium: 150, 516, 541, 1095, 1134, 1281, 1293, 1653, 1654, 1900,
1926, 1955, 2068, 2227
Polonium: 1168, 1281, 1496, 2227
Potassium: 333, 535, 547, 548, 549, 602,
1038, 1041, 1164, 1290, 1406,
1599, 1643, 1676, 1722, 1811,
1963, 1979, 2011, 2019. 2024,
2238
Praseodymium: 333, 439, 535, 1498, 1522, 1627, 2019
Promethium: 17, 555, 1959, 2227
Radium: 151, 350, 401, 476, 588, 747, 1627, 1779, 2011, 2227
Rhenium: 555, 1604, 1605
Rhodium: 17, 333, 599, 1029, 1828
683, 741, 792, 992, 1025,
1449, 1481, 1498, 1499, 1522,
1709, 1720, 1723, 1801, 1904
2115, 2160, 2183, 2188, 2227,
694, 737, 846, 880, 992,
1437, 1498, 1499, 1522,
1843, 1870, 1917, 1947,
2065, 2218, 2227, 2234,
411
-------
Rubidium: 193, 535, 628, 932, 1425, 1498, 1522, 1960, 2024, 2188,
2227
Ruthenium: 17, 28, 53, 150, 214, 281, 310, 333, 483, 539, 541, 547,
551, 555, 582, 583, 584, 585, 586, 599, 851, 1029, 1038,
1100, 1134, 1209, 1320, 1413, 1437, 1518, 1532, 1540,
1612, 1653, 1654, 1659, 1676, 1828, 1917, 1963, 2011,
2019, 2208
Salinity: 9, 462, 624, 848, 1048, 1108, 1289, 1290, 1477, 1963,
1994, 2120, 2145
535, 1498, 1522
932, 1166, 1498, 1499, 1518, 1522, 1859, 2009, 2011, 2024
684, 702, 941, 1149, 1425, 1498, 1522, 1835, 2024
535, 601, 694, 848, 918, 957A, 959, 960, 978, 983, 992,
999, 1043, 1061, 1062, 1405, 1498, 1499, 1599, 1994, 2143,
2234
Silver: 228, 269, 535, 628, 648, 778, 833, 992, 1130, 1164, 1208,
1264, 1288, 1411, 1425, 1498, 1499, 1627, 1645, 1669, 1987,
1991, 2024, 2183, 2188, 2227
Sodium: 535, 602, 694, 846, 848, 983, 992, 1406, 1498, 1499, 1522,
1599, 1722, 1979, 2011, 2024, 2065, 2183, 2196, 2234, 2238
Strontium: 6, 53, 150, 188, 214, 222, 223, 224, 242, 261, 298, 310,
380, 381, 387, 413, 414, 415, 417, 439, 522, 532, 535,
541, 547, 566, 628, 648, 674, 683, 703, 818, 840, 851,
862, 901, 992, 1015, 1016, 1038, 1070, 1071, 1100, 1102,
1112, 1116, 1130, 1139, 1208, 1209, 1234, 1250, 1399,
1406, 1413, 1425, 1437, 1470, 1498, 1518, 1522, 1540,
1612, 1627, 1673, 1676, 1759, 1774, 1859, 1868, 1955,
1959, 1963, 2011, 2018, 2019, 2020, 2024, 2045, 2046,
2138, 2145, 2183, 2207, 2218, 2227
Tantalum: 1208, 2024
Technetium: 1653, 1654
Terbium: 1522, 2024
Tellurium: 1522, 2019, 2188
Thallium: 535, 1522, 1627, 1947
Thorium: 151, 401, 747, 932, 1016, 1202, 1425, 1522, 2024, 2188,
2227
Thulium: 1522
Tin: 535, 628, 77~, 1130, 1208, 1498, 1499, 1522, 1627, 2166, 2183
Titanium: 535, 628, 792, 992, 1130, 1208, 1425, 1484, 1498, 1499,
1522, 1627, 1657, 2049, 2183, 2188, 2232
Tungsten: 535, 792, 1208, 1425, 1522, 1604, 1605, 2166
Uranium: 151, 308, 588, 747, 788, 932, 1016, 1425, 1522, 1955, 2188,
2227
Vanadium: 535, 628, 683, 788, 792, 983, 992, 1130, 1208, 1498, 1522,
1604, 1605, 1627, 1657, 2049, 2183, 2188, 2232
Ytterbium: 1498, 1522
Yttrium: 215, 387, 439, 535, 703, 1246, 1413, 1498, 1522, 1540, 1627,
1828, 1963, 2018, 2019, 2046, 2227
Samarium:
Scandium:
Selenium:
Silicon:
412
-------
Zinc: 47, 53, 54, 87, 102, 127, 210, 211, 222, 223, 224, 242, 269,
345, 354, 383, 394, 419, 436, 471, 486, 521, 532, 535, 539,
550, 583, 597, 602, 628, 632, 648, 651, 683, 702, 707, 709,
713, 722, 781, 785, 802, 803, 804, 840, 849, 851, 862, 891,
932, 951, 973, 983, 992, 999, 1025, 1038, 1043, 1072, 1110,
1123, 1129, 1130, 1134, 1139, 1164, 1166, 1208, 1209, 1234,
1256, 1263, 1264, 1266, 1275, 1296, 1323, 1339, 1349, 1373,
1382, 1407, 1413, 1420, 1425, 1437, 1445, 1448, 1449, 1470,
1471, 1481, 1483, 1492, 1498, 1499, 1518, 1522, 1579, 1600,
1627, 1643, 1645, 1669, 1672, 1699, 1709, 1719, 1720, 1721,
1731, 1753, 1773, 1774, 1818, 1828, 1835, 1846, 1853, 1859,
1863, 1880, 1947, 1955, 1963, 1979, 1991, 1998, 1999, 2009,
2011, 2019. 2020, 2024, 2049, 2106, 2107, 2120, 2137, 2160,
2166, 2183, 2188, 2192, 2208, 2214, 2225, 2227, 2228, 2238,
2239
Zirconium:
102, 193, 214, 215, 310, 333, 383, 483, 539, 555, 582,
585, 851, 852, 1029, 1038, 1166, 1208, 1437, 1484, 1498,
1499, 1518, 1522, 1540, 1612, 1627, 1676, 1828, 1917,
1959, 2019, 2183, 2227
AMPHIBIA
Arsenic: 2011
Barium: 897, 2058
Beryllium: 138, 2058
Cadmium: 897. 1171, 2058, 2244
Calcium: 317, 608, 897, 1535, 1953, 2011, 2058
Cerium: 2011
Cesium: 79, 399, 2011
Chromium: 1535, 2011
Cobalt: 79, 260, 1171, 2011
Copper: 138, 175, 804, 841, 897, 903, 1171, 1356, 1397, 1573, 1804,
1953, 1980, 2011, 2058, 2061, 2244
Iron: 1535, 1980, 2011
Lead: 58, 138, 260, 293, 804, 822, 1171, 2244
Lithium: 608
Magnesium: 897, 1535, 1953, 2058
Manganese: 804, 1171, 2011
Mercury: 1171, 2058, 2244
Nickel: 260, 897, 1171, 2058
Platinum: 2058
Potassium: 317, 608, 1418, 1668, 2011
Radium: 2011
Ruthenium: 2011
Scandium: 2011
Silver: 1171
Sodium: 317, 1418, 1668, 1765, 2011, 2172
Strontium: 79, 335, 897, 2011
413
-------
Thallium: 138, 2244
Thorium: 138
Yttrium: 335
Uranium: 2058
Zinc: 79, 138, 804, 1171, 1535, 1953, 1980, 2011, 2058, 2244
ANNELIDA
Aluminum: 535
Americium: 1354
Antimony: 535
Arsenic: 535, 1238, 1382, 1436, 2137
Barium: 535, 1868
Beryllium: 535
Bismuth: 535
Cadmium: 155, 468, 535, 648, 653, 873, 994, 1121, 1305, 1382, 1428,
1436, 1869, 2014, 2137, 2147, 2167
Calcium: 115, 535, 648, 900, 1464, 1868, 1963, 2025, 2145, 2147
Cerium: 535, 583, 1088, 1944, 1963
Cesium: 84, 535, 583, 1088, 1442, 1963
Chromium: 114, 434, 502, 535, 648, 994, 1081, 1121, 1382, 1603,
1941, 1942, 1957, 1972, 2014
Cobalt: 468, 535, 579, 583, 648, 994, 1222, 1963
Copper: 405, 434, 502, 535, 553, 583, 648, 650, 994, 1081, 1121,
1382, 1428, 1436, 1742, 1869, 1885, 1890, 1957, 2014, 2052,
2121, 2137, 2147
Gallium: 535
Germanium: 535
Gold: 535
Iron: 115, 404, 405, 535, 583, 648, 707, 1428, 1601, 1603, 1789,
1957, 1963
Lanthanum: 535
Lead: 545, 583, 648, 994, 1081, 1382, 1428, 1436, 1869, 1957, 2014,
2021, 2137
Lithium: 535, 994, 1442
Magnesium: 115, 648, 900, 1464, 2025, 2147
Manganese: 468, 583, 652, 688, 707, 1601, 1957, 1963, 1965, 2147
Mercury: 468, 535, 553, 873, 1121, 1334, 1382, 1428, 1527, 1869,
1967, 2014, 2137
Molybdenum: 535
Neodymium: 535
Nickel: 468, 535, 648, 994, 1121, 1382
Niobium: 535, 1088, 1944, 1963
Plutonium: 676, 1293, 1353, 1354, 1587, 1900
Potassium: 84, 115, 535, 868, 900, 1442, 1944, 1963, 2025, 2147
Praseodymium: 535
Promethium: 688
Rhodium: 599
414
-------
Rubidium: 535, 1442
Ruthenium: 583, 599, 919, 1088, 1963
Salinity: 652, 900, 1351, 1742, 1764, 1963, 2145, 2209
Samarium: 404, 405, 535
Scandium:. 404, 405
Silicon: 535
Silver: 535, 648, 1312, 1436
Sodium: 115, 535, 868, 900, 1442, 2025
Strontium: 370, 535, 648, 1595, 1868, 1963, 2145
Thallium: 535
Tin: 535
Titanium: 535
Tungsten: 535
Vanadium: 535
Yttrium: 535, 1595, 1963
Zinc: 283, 404, 405, 535, 545, 553, 583, 648, 650, 653, 676, 707,
726, 994, 1121, 1124, 1273, 1305, 1382, 1428, 1436, 1681,
1869, 1944, 1957, 1963, 1965, 2014, 2137, 2147
Zirconium: 1088, 1944
ARACHNOIDEA
Copper: 1344, 1973
Iron: 1344, 1973
Lead: 1809, 1973
Manganese: 1973
Zinc: 1973
AVES
Antimony: 541, 851, 1038, 1676, 2024, 2208
Arsenic: 1382, 1386, 1518, 2024
Barium: 1518
Beryllium: 1038, 1676
Bismuth: 541, 2208
Cadmium: 995, 1382, 2024
Calcium: 1958, 2024
Cerium: 541, 851, 928, 1038, 1518, 2208
Cesium: 541, 851, 1038, 1518, 1676, 2024, 2208
Chromium: 1382, 1518, 2024
Cobalt: 541, 851, 928, 974, 1038, 1518, 1676, 1828, 2024, 2208
Copper: 1356, 1382, 1518, 1556, 2024
Europium: 851, 1038, 2024
Hafnium: 2024
Iron: 541, 928, 974, 1518, 1556, 1575, 1828, 2024
Lanthanum: 1518
Lead: 118, 259, 995, 1358, 1374, 1382, 1575, 1730, 1852, 2024
Manganese: 541, 851, 928, 1038, 1518, 1828, 2208
415
-------
Mercury: 276, 543, 569, 764, 771, 771A, 772, 824, 896, 905, 906,
924, 934, 995, 1073, 1074, 1080, 1185, 1189, 1241, 1242,
1324, 1340, 1375, 1380, 1382, 1527, 1611, 1780, 1782,
1928, 2024, 2185
Neptunium: 1518
Nickel: 1382
Niobium: 1038, 1518, 1676, 1828
Plutonium: 541, 1293
Potassium: 928, 1038, 1676, 2024
Radium: 928
Rhodium: 1828
Rubidium: 2024
Ruthenium: 541,
Scandium: 1518,
Selenium: 1611,
Silver: 2024
Sodium: 2024
Strontium: 541, 851, 928, 1038, 1518, 1676, 2024
Tantalum: 2024
Terbium: 2024
Thallium: 995
Thorium: 2024
Vanadium: 1556
Yttrium: 1828
Zinc: 836, 851, 1038, 1382, 1387, 1518, 1556, 1828, 2024, 2208
Zirconium: 851, 1038, 1518, 1676, 1828
851, 1038, 1518, 1676, 1828, 2208
2024
1762,1780,2024
BACTERIA AND YEASTS
Aluminum: 535, 1173, 1425, 1486, 1812, 2094
Antimony: 535, 842, 1177, 1425
Arsenic: 535, 571, 657, 1282, 1400, 1425, 1486, 1734
Barium: 535, 571, 1425
Beryllium: 535
Bismuth: 535, 842
Cadmium: 535, 571, 1425, 1448, 1449, 1472, 1486, 1606, 1785, 1786,
1846, 1884, 1997, 2094, 2244
Calcium: 204, 535, 971, 1102, 1449, 1786, 2035
Cerium: 535, 1425
Cesium: 532, 535
Chromium: 535, 571, 842, 1173, 1425, 1448, 1449, 1486, 1905, 1957,
2094
Cobalt: 535, 842, 1425, 1486, 1606, 1785, 1913, 2094, 2226
Copper: 290, 497, 535, 571, 572, 657, 757, 780, 804, 971, 1098,
1099, 1173, 1220, 1425, 1448, 1449, 1486, 1555, 1556, 1606,
1893, 1957, 1997, 2094, 2121, 2244
Gallium: 535
Germanium: 535
416
-------
Gold: 535, 2125
Iron: 535, 921, 1099, 1177, 1220, 1426, 1449, 1556, 1606, 1807,
1812, 1905, 1957
Lanthanum: 535, 1425
Lead: 290, 571, 804, 842, 1177, 1425, 1449, 1486, 1957, 1997, 2094,
2244
Lithium: 535, 1425, 1449
Magnesium: 971, 1449, 1486, 1786, 1913
Manganese: 657, 804, 842, 921, 1544, 1619, 1664, 1786, 1807, 1957,
2035
Mercury: 447, 535, 571, 572, 618, 727,
1011, 1036, 1132, 1190, 1282,
1448, 1449, 1485, 1486, 1487,
1784, 1785, 1786, 1914, 1997,
2101, 2119. 2124, 2125, 2155,
2244
Molybdenum: 535, 1425, 2035
Neodymium: 535
Nickel: 535, 571, 819, 1173, 1177, 1425, 1449, 1785, 2094
Niobium: 535
Potassium: 535, 1068, 1173, 1718, 1893, 2035
Praseodymium: 535
Rubidium: 535, 1425
Salinity: 297, 701, 826, 1068, 1383, 1486
Samariuni: 535
Selenium: 1220, 1425, 1463
Silicon: 535, 1173
Silver: 535, 571, 572, 1173, 1425, 1486, 1606, 2094, 2125
Sodium: 535, 971, 1068, 1383, 1786, 2035
Strontium: 322, 532, 535, 1102, 1425
Thallium: 535, 2094, 2244
Thorium: 1425
Tin: 535, 1606
Titanium: 535, 1425
Tungsten: 535, 1425
Uranium: 206, 427, 1032, 1425, 2035
Vanadium: 535, 1556
Yttrium: 322, 535
Zinc: 419, 532, 535, 571, 572, 804, 1098, 1266, 1425, 1448, 1449,
1486, 1555, ,1556, 1785, 1846, 1884, 1957, 2063, 2244
779, 892, 893,
1338, 1383, 1394,
1490, 1527, 1555,
2035, 2042, 2067,
2168, 2174, 2175,
1425,
1606,
2078,
2193,
1433,
1773,
2094,
2226,
BIBLIOGRAPHY
Copper: 1397
Lead: 673
Mercury: 592,
Miscellaneous:
Mollusca: 45,
937
366, 724, 750, 1165, 1179, 1547, 1629
56
417
-------
BRACHIOPODA
Al uminum: 535
Antimony: 535
Arsenic: 535
Barium: 535
Beryllium: 535
Bismuth: 535
Cadmium: 535
Calcium: 535, 2145
Cerium: 535
Cesium: 535
Chromium: 535
Cobalt: 535
Copper: 535
Gallium: 535
Germanium: 535
Gold: 535
Iron: 535
Lanthanum: 535
Lithium: 535
Mercury: 535
Molybdenum: 535
Neodymium: 535
Nickrl: 535
Niobium: 535
Potassium: 535
Praseodymium: 535
Rubidium: 535
Salinity: 2145
Samarium: 535
Silicon: 535
Silver: 535
Sodium: 535
Strontium: 535, 2145
Thallium: 535
Tin: 535
Titanium: 535
Tungsten: 535
Vanadium: 535
Yttrium: 535
Zinc: 535
BRYAZOA
Aluminum:
Antimony:
Arsenic:
535
535
535, 1382
418
-------
Barium: 535
Beryllium: 535
Bismuth: 535
Cadmium: 535, 648, 1382
Calcium: 535, 648, 2145
Cerium: 535
Cesium: 535, 1545
Chromium: 535, 648, 1382
Cobalt: 232, 535, 648
Copper: 232, 357, 535, 553, 648, 1382
Gallium: 535
Germanium: 535
Gold: 535
Iron: 535, 648
Lanthanum: 535
Lead: 232, 648, 1382
Li thium: 535
Magnesium: 648, 1545
Manganese: 232
Mercury: 535, 553, 1382, 1527
Molybdenum: 535
Neodymium: 535
Nickel: 535, 648, 1382
Niobium: 535
Potassium: 535, 1545
Praseodymium: 535
Rubidium: 535
Salinity: 2145, 2209
Samarium: 535
Silicon: 535
Silver: 535, 648
Sodium: 535
Strontium: 232, 535, 648, 2145
Thallium: 535
Tin: 232, 535
Titanium: 535
Tungsten: 535
Vanadium: 232, 535
Yttrium: 535
Zinc: 232, 535, 553, 648, 1382
BRYOPHYTA
Antimony: 1038, 1676, 1917
Beryllium: 1038, 1676, 1917
Cadmium: 873
Cerium: 1038, 1917
Cesium: 1038, 1676, 1917
419
-------
Cobalt: 1038, 1676
Europium: 1038,1917
Manganese: 1038
Mercury: 873
Niobium: 1038, 1676, 1917
Potassium: 1038, 1676, 1917
Ruthenium: 1038, 1676, 1917
Strontium: 6, 310, 414, 1038, 1676
Zinc: 284, 1038
Zirconium: 1038, 1676, 1917
CHAETOGNATHA
Aluminum: 2183
Arsenic: 1408
Barium: 2183
Beryllium: 2183
Cadmium: 1408, 1758
Calcium: 1599, 2183
Cesium: 1758
Chromium: 2183
Cobalt: 1758, 2183
Copper: 1408, 2183
Gallium: 2183
Iron: 313, 1408, 1601, 1758, 2183
Lead: 2183
Lithium: 2183
Magnesium: 1599. 2183
Manganese: 1601, 2183
Molybdenum: 2183
Nickel: 2183
Potassium: 1599
Silicon: 1599
Silver: 2183
Sodium: 1599, 2183
Strontium: 1758, 2183
Tin: 2183
Titanium: 2183
Vanadium: 2183
Zinc: 313, 1408, 1758, 2183
Zirconium: 2183
CRUSTACEA
Actinium:
Aluminum:
1016
409, 428, 506, 535, 546, 626, 992, 1063, 1289, 1425, 1498,
1499, 1503, 1520, 2043, 2183, 2188
420
-------
Antimony: 13, 535, 541, 851, 952, 1038, 1039, 1210, 1234, 1384,
1425, 1627, 1676, 1959, 2019, 2024, 2117, 2188, 2208,
2227
Arsenic: 12, 92, 342, 520, 535, 626, 632, 706, 735, 952,
1249, 1347, 1382, 1386, 1400, 1407, 1408, 1411,
1462, 1493, 1462, 1493, 1494, 1498, 1499, 1518,
1604, 1605, 1627, 1647, 1697, 1698, 1735, 1755,
1837, 1839, 1962, 2011, 2024, 2137, 2188
Barium: 13, 360, 535, 626, 992, 1039, 1425, 1498, 1518, 1627, 1740,
1849, 1868, 2183, 2188
Beryllium: 535, 1038, 1498, 1499, 1676, 2183, 2188
Bismuth: 535, 541, 1016, 1498, 2188, 2208
Boron: 1039, 1498, 1520, 1627, 2144
Cadmium: 13, 92, 155, 468, 535, 626, 632, 648, 755, 759, 789, 837,
862, 952, 991, 992, 995, 1039, 1050, 1051, 1075, 1084,
1104, 1171, 1212, 1213, 1249, 1296, 1305, 1350, 1359, 1360,
1382, 1408, 1425, 1428, 1448, 1498, 1499, 1509, 1627, 1632,
1647, 1695, 1707, 1744, 1758, 1803, 1860, 1901, 2024, 2106,
2107, 2112, 2137, 2147, 2156, 2180, 2188, 2205, 2219, 2229,
2244
Calcium: 13, 31, 115, 299, 301, 381, 461, 467, 535, 602, 626, 645,
648, 674, 716, 737, 749, 798, 806, 812, 829, 830, 991, 992,
1102, 1350, 1369, 1384, 1437, 1464, 1498, 1499, 1510, 1511,
1520, 1535, 1581, 1599, 1627, 1638, 1639, 1640, 1641, 1642,
1663, 1759, 1779, 1806, 1849, 1859, 1868, 1950, 1963, 2011,
2024, 2025, 2145, 2147, 2183, 2235
Cerium: 28, Ill, 124, 265, 299, 413, 471, 535, 539, 541, 582, 583,
586, 600, 790, 791, 850, 851, 862, 955, 1038, 1100, 1128,
1164, 1331, 1350, 1369, 1425, 1437, 1498, 1518, 1612, 1943,
1945, 1955, 1956, 1959, 1963, 2011, 2019, 2020, 2208
Cesium: 28, 52, 82, 83, 84, 86, 261, 264, 265, 300, 306, 314, 361,
413, 498, 532, 535, 541, 582, 583, 586, 600, 762, 791, 831,
850, 851, 862, 955, 1016, 1038, 1039, 1116, 1210, 1234,
1350, 1369, 1413, 1437, 1438, 1442, 1446, 1470, 1498, 1518,
1612, 1676, 1758, 1815, 1956, 1963, 2011, 2019, 2020, 2024,
2153, 2208, 2227
Chromium: 13, 40, 91, 124, 319, 409, 434, 453, 506, 526, 535, 539,
597, 626, 632, 648, 702, 992, 1039, 1081, 1210, 1211,
1234, 1350, 1382, 1384, 1425, 1448, 1498, 1509, 1518,
1535, 1594, 1602, 1603, 1627, 1645, 1647, 1738, 1825,
1934, 1945, 1955, 2011, 2024, 2043, 2183, 2188, 2221
Cobalt: 13, 91, 261, 312, 313, 468, 471, 507, 535, 541, 554, 561,
579, 583, 626, 632, 648, 784, 851, 973, 974, 975, 991, 992,
1038, 1039, 1075, 1128, 1164, 1171, 1174, 1210, 1234, 1286,
1315, 1316, 1317, 1318, 1350, 1384, 1425, 1437, 1470, 1498,
1499, 1518, 1583, 1590, 1627, 1663, 1676, 1758, 1849, 1955,
1963, 2011, 2020, 2024, 2043, 2183, 2188, 2208, 2227, 2235
1039,
1425,
1525,
1813,
1203,
1455,
1552,
1834,
421
-------
Copper: 13, 25, 50, 51, 60, 85, 91, 119, 122, 171, 254, 255, 256,
343, 344, 378, 409, 412, 421, 429, 434, 499, 507, 509, 535,
546, 553, 583, 596, 597, 625, 626, 631, 632, 647, 648, 695,
699, 704, 732, 735, 736, 741, 759, 804, 841, 881A, 954,
961, 962, 991, 992, 1039, 1075, 1081, 1117, 1134, 1139,
1153, 1171, 1210, 1213, 1285, 1289, 1296, 1344, 1347, 1348,
1350, 1360, 1382, 1397, 1408, 1411, 1419, 1425, 1428, 1429,
1448, 1498, 1499, 1503, 1509, 1518, 1520, 1525, 1556, 1578,
1583, 1618, 1622, 1627, 1647, 1695, 1703, 1706, 1709, 1738,
1740, 1743, 1772, 1875, 1876, 1878, 1882, 1931, 1934, 1973,
2011, 2024, 2030, 2043, 2052, 2053, 2054, 2072, 2096, 2106,
2107, 2112, 2137, 2147, 2156, 2183, 2188, 2215, 2216, 2221,
2222, 2229, 2235, 2244
Dysprosium: 1498
Erbium: 1498
Europium: 466, 851, 1038, 1498, 1959, 2024, 2227
Gadolinium: 1498
Gallium: 535, 1039, 1498, 1503, 1520, 1627, 2183
Germanium: 535, 1039, 1498, 1627, 1735
Gold: 146, 535, 626, 1039, 1604, 1605, 1627
Hafnium: 1498, 2024
Iron: 13, 60, 91, 115, 161, 261, 313, 390, 409, 453, 471, 506, 535,
541, 546, 583, 625, 626, 631, 632, 648, 741, 798, 921, 973,
974, 991, 992, 1117, 1134, 1210, 1234, 1249, 1331, 1344, 1360,
1384, 1408, 1419. 1428, 1498, 1499, 1503, 1509, 1518, 1520,
1525, 1535, 1556, 1583, 1590, 1601, 1603, 1618, 1627. 1758,
1772, 1789, 1859, 1864, 1875, 1876, 1931, 1934, 1955, 1963,
1973, 2011, 2024, 2053, 2132, 2183, 2188, 2227, 2235
Lanthanum: 360, 535, 1425, 1498, 1499, 1518
Lead: 13, 92, 161, 343, 344, 378, 409, 546, 583, 597, 612, 626, 632,
648, 717, 741, 759, 782, 798, 804, 837, 881A, 991, 992, 995,
1039, 1075, 1081, 1104, 1154, 1168, 1171, 1249, 1296, 1350,
1360, 1368, 1382, 1407, 1425, 1428, 1429, 1455, 1498, 1499,
1520, 1525, 1627, 1647, 1695, 1738, 1744, 1760, 1809, 1919,
1973, 2021, 2024, 2043, 2053, 2106, 2107, 2112, 2137, 2156,
2183, 2188, 2205, 2227, 2235, 2244
Lithium: 13, 31, 535, 1425, 1442, 1498, 2183
Magnesium: 13, 115, 461, 602, 626, 631, 648, 716, 749, 798, 806,
812, 829, 839, 991, 992, 1210, 1350, 1464, 1498, 1499,
1510, 1511, 1520, 1535, 1581, 1599, 1627, 1639, 1708,
1772, 1806, 1849, 1950, 2025, 2147, 2183, 2235
Manganese: 13, 88, 91, 161, 261, 314, 337, 466, 468, 471, 539. 541,
561, 583, 626, 632, 785, 804, 820, 851, 881A, 921, 973,
991, 992, 1038, 1039, 1075, 1100, 1134, 1139, 1164, 1171,
1211, 1234, 1286, 1360, 1437, 1498, 1499, 1509, 1518,
1583, 1590, 1601, 1627, 1772, 1811, 1849, 1859, 1875,
1876, 1934, 1955. 1959, 1963, 1973, 2011, 2019, 2043,
2106, 2107, 2147, 2183, 2188, 2208, 2215, 2227, 2235
422
-------
Mercury: 13, 92, 119, 120, 121, 218, 342, 421, 429, 468, 507, 509,
535, 553, 597, 626, 695, 699, 704, 729, 759, 767, 794, 854,
874, 899A, 927, 949, 952, 992, 995, 1012, 1013, 1075, 1096,
1104, 1117, 1125. 1163, 1171, 1189. 1210, 1240, 1242, 1243,
1244, 1248, 1267, 1270, 1327, 1334, 1348, 1350, 1382, 1384,
1411, 1425, 1428, 1448, 1482, 1498, 1499, 1509. 1521, 1527,
1536, 1542, 1585, 1614, 1636, 1647, 1648, 1667, 1692, 1695,
1706, 1733, 1735, 1738, 1740, 1744, 1770, 1771, 1824, 1825,
1928, 1934, 1949, 1996, 2024, 2029. 2076, 2085, 2106, 2107,
2112, 2137, 2180, 2188, 2205, 2219, 2220, 2244
Molybdenum: 535, 737, 992, 1039, 1176, 1425, 1498, 1499, 1604, 1605,
1627, 2019, 2183, 2188
Neodymium: 535, 1498, 1499
Neptunium: 1518
Nickel: 12, 91, 161, 343, 344, 378, 409, 428, 468, 507,535, 626,
648, 741, 991, 992, 1039, 1075, 1117, 1171, 1350, 1360,
1382, 1425, 1498, 1499, 1509, 1627, 1647, 1709, 1801, 1849,
2106, 2107, 2183, 2188, 2227, 2229, 2235
Niobium: 102, 111, 466, 535, 539, 1038, 1437, 1498, 1518, 1612,
1676, 1943, 1945, 1956, 1963, 2019, 2227
Platinum: 626
Plutonium: 541, 782, 1044, 1095, 1134, 1293, 1587, 1658, 1955, 2068,
2197, 2227
Polonium: 612, 782, 1154, 1168, 1466, 1682, 1760, 2227
Potassium: 13, 82, 83, 84, 86, 115, 167, 306, 314, 461, 466, 535,
561, 602, 626, 645, 716, 737, 749, 829, 830, 992, 1038,
1164, 1210, 1294, 1369. 1437, 1438, 1442, 1498, 1499,
1510, 1511, 1567, 1581, 1599, 1663, 1676, 1811, 1825,
1945, 1950. 1963, 2011, 2019. 2024, 2025, 2147, 2157,
2227
Praseodymium: 439, 466, 535, 850, 1498, 1627, 2019
Promethium: 466, 1959. 2227
Protactinium: 1829
Radium: 350, 466, 1627, 1760, 1779, 2011, 2227
Rhenium: 1604, 1605,
Rubidium: 535, 1039, 1384, 1425, 1442, 1498, 2024, 2188, 2227
Ruthenium: 28, 53, 111, 265, 539, 541, 582, 583, 586, 600, 851,
907, 955, 1038, 1100, 1134, 1320, 1331, 1369, 1413, 1437,
1518, 1612, 1659. 1676, 1943, 1945, 1956, 1963, 2011,
2019, 2208
Salinity: 148, 461, 506, 511, 523, 593, 607, 625, 715, 716, 718,
719, 791, 830, 855, 899A, 938, 942, 1007, 1008, 1090,
1150, 1245, 1265. 1289, 1393, 1412, 1475, 1477, 1491,
1526, 1528, 1559. 1623, 1656, 1696, 1705, 1706, 1707,
1743, 1763, 1764. 1825, 1898, 1951, 1952, 1963, 1984,
1986, 2029. 2057, 2083, 2097, 2100, 2131, 2134, 2145,
2157, 2161, 2209
423
-------
535, 1498
124, 1384, 1498, 1499, 1518, 1859, 2011, 2024
702, 1149, 1384, 1425, 1498, 1584, 1585, 1586, 1834, 2024
535, 992, 1498, 1499, 1599
535, 614, 648, 694, 783, 784, 992, 1039, 1075, 1164, 1171,
1312, 1315, 1360, 1384, 1411, 1425, 1498, 1499, 1627, 1645,
1647, 1740, 1987, 2024, 2183, 2188, 2227
Sodium: 12, 13, 31, 84, 113, 115, 264, 336, 423, 461, 535, 602, 626,
645, 716, 749, 798, 8~0, 829, 830, 992, 1210, 1294, 1442,
1498, 1499, 1510, 1511, 1567, 1581, 1594, 1599, 1738, 1765,
1825, 1950, 1951, 1984, 1986, 2011, 2024, 2025, 2097, 2131,
2157, 2183
Strontium: 13, 53, 107, 188, 261, 264, 291, 299, 348, 358, 360, 380,
381, 413, 414, 439, 466, 467, 532, 535, 541, 589, 626,
648, 674, 749, 812, 850, 851, 862, 991, 992, 993, 1016,
1038, 1039, 1100, 1102, 1116, 1139, 1234, 1315, 1350,
1369, 1413, 1425, 1437, 1470, 1498, 1518, 1612, 1627,
1676, 1758, 1759, 1849, 1859, 1868, 1955, 1959, 1963,
2011, 2019, 2020, 2024, 2145, 2183, 2227
Tantalum: 2024
Terbium: 2024
Tellurium: 265, 2019, 2188
Thallium: 369, 535, 995, 1627, 2244
Thorium: 1016, 1425, 1760, 2024, 2188, 2227
Tin: 13, 92, 409. 506, 535, 626, 1039, 1498, 1499, 1525, 1627, 2043,
2183
Titanium: 535, 992, 1039, 1425, 1498, 1499, 1520, 1627, 2183, 2188
Tungsten: 535, 1425, 1604, 1605
Uranium: 1016, 1017, 1425, 1760, 1955, 2188, 2227
Vanadium: 535, 992, 1039, 1498, 1556, 1604, 1605, 1627, 2183, 2188
Ytterbium: 1498
Yttrium: 299,439,466, 535, 1413, 1498, 1627, 1963, 2019, 2227
Zinc: 13, 40, 53, 60, 80, 92, 102, 124, 125, 145, 147, 148, 181,
182, 183, 284, 313, 314, 343, 344, 360, 378, 382, 397, 409,
421, 471, 506, 507, 508, 532, 535, 539, 546, 553, 561, 583,
597, 602, 625, 626, 631, 632, 647, 648, 675, 694, 699, 702,
713, 749, 759. 785, 789, 791, 804, 837, 851, 862, 881A, 946,
952, 973, 991, 992, 1038, 1060, 1075, 1089, 1117, 1123, 1129,
1134, 1139, 1164, 1171, 1184, 1211, 1212, 1234, 1249, 1256,
1273, 1286, 1296, 1305, 1331, 1350, 1360, 1368, 1382, 1384,
1388, 1407, 1408, 1413, 1419, 1425, 1428, 1434, 1435, 1437,
1448, 1470, 1498, 1499, 1518, 1535, 1556, 1581, 1582, 1583,
1588, 1590, 1600, 1627, 1645, 1647, 1681, 1695, 1708, 1709,
1719, 1738, 1744, 1758, 1772, 1818, 1859, 1875, 1876, 1919,
1934, 1945, 1955, 1963, 1973, 2011, 2016, 2019, 2020, 2024,
2043, 2053, 2064, 2072, 2089, 2090, 2106, 2107, 2112, 2137,
2147, 2156, 2183, 2188, 2189, 2208, 2215, 2227, 2229, 2235,
2244
Samarium:
Scandium:
Selenium:
Silicon:
Silver:
424
-------
Zirconium:
102, 111, 360, 466, 539, 582, 851, 1038, 1369, 1437, 1498,
1499, 1518, 1612, 1627, 1676, 1943, 1945, 1956, 1959,
2019, 2183, 2227
CTENOPHORA
Aluminum: 2183
Barium: 2183
Beryllium: 2183
Calcium: 2183
Chromium: 2183
Cobalt: 2183
Copper: 2183
Gallium: 2183
Iron: 2183
Lead: 2183
Lithium: 2183
Magnesium: 2183
Manganese: 2183
Molybdenum: 2183
Nickel: 2183
Silver: 2183
Sodium: 2183
Strontium: 2183
Tin: 2183
Titanium: 2183
Vanadium: 2183
Zinc: 2183
Zirconium: 2183
COELENTERATA
Aluminum: 535, 1131, 1392, 1503, 1867
Americium: 1927
Antimony: 535, 851, 1627, 1676, 1927, 2208
Arsenic: 535, 1097, 1382, 1386, 1400, 1627, 1631
Barium: 535, 965, 1392, 1627, 1868
Beryllium: 535, 1676
Bismuth: 535, 1927, 2208
Boron: 965, 1627
Cadmium: 535, 904, 1131, 1382, 1627, 1867, 1896, 1901, 2104
Calcium: 535, 965, 1131, 1319, 1392, 1464, 1478, 1599, 1627, 1777,
1868, 2025, 2145, 2179
Cerium: 535, 586, 851, 1944, 1955, 2208
Cesium: 83, 535, 586, 851, 1442, 1676, 1927, 2208
Chromium: 535, 965, 1131, 1382, 1392, 1627, 1955
Cobalt: 312, 535, 851, 965, 1131, 1627, 1676, 1927, 1955, 2208
425
-------
Copper: 535, 904, 965, 1131, 1382, 1392, 1503, 1556, 1627, 1867,
1893, 1896, 2030, 2072, 2104
Europium: 851, 1927
Gallium: 535, 1503, 1627
Germanium: 535, 1627
Gold: 535, 1627
Iron: 535, 965, 1131, 1392, 1503, 1556, 1627, 1867, 1955
Lanthanum: 535
Lead: 904, 965, 1018, 1019, 1131, 1382, 1392, 1529, 1627, 1867, 1927,
Lithium: 535, 965, 1442
Magnesium: 1131, 1319, 1392, 1464, 1599, 1627, 2025, 2179
Manganese: 851, 965, 1131, 1392, 1627, 1955, 2208
Mercury: 535, 904, 1382, 1896, 2104
Molybdenum: 535, 1392, 1627
Neodymium: 535
Nickel: 535, 965, 1131, 1382, 1392, 1627
Niobium: 535, 1676, 1944
Plutonium: 1293, 1716, 1927, 1955
Polonium: 1927
Potassium: 535, 1131, 1319, 1442, 1599, 1676, 1893, 1944, 2025
Praseodymium: 535, 1627
Protactinium: 1716
Radium: 1018, 1019, 1529, 1627
Rhodium: 1927
Rubidium: 535, 1442
Ruthenium: 586, 851, 1320, 1659, 1676, 2208
Salinity: 1764, 2145, 2209
Samarium: 535
Scandium: 965
Silicon: 535, 965, 1392, 1599
Silver: 535, 1131, 1312, 1392, 1627
Sodium: 535, 1131, 1319, 1442, 1599, 1777, 2025
Strontium: 413, 414, 535, 851, 931, 965, 1019, 1131, 1319, 1392
1627, 1676, 1868, 1927, 1955, 2145
Thallium: 535, 1627
Thorium: 1529, 1716
Tin: 535, 1131, 1627
Titanium: 535, 965, 1392, 1627
Tungsten: 535
Uranium: 965, 1716, 1955
Vanadium: 535, 1392, 1556, 1627
Yttrium: 535, 1627, 1927
Zinc: 535, 851, 904, 965, 1131, 1382, 1556, 1600, 1627, 1719, 1818,
1867. 1944, 1955, 2072, 2208
Zirconium: 851, 1627, 1676, 1944
426
-------
DETRIWS
Cerium: 110, 111, 393. 415
Cesium: 393, 413, 415
Niobium: 110, 111
Plutonium: 2068
Praseodymium: 535
Rhodium: 110
Ruthenium: 110, 111, 393
Strontium: 6, 393, 413, 415
Zinc: 286, 2225
Zirconium: 110, 111
ECHINODERMATA
Aluminum: 535. 1131, 1503, 1867, 2198
Antimony: 535, 1038, 1386, 1676, 2024. 2208
Arsenic: 535, 1238, 1382, 1386, 1631, 1776, 1837, 1962, 2024, 2137
Barium: 535, 1868
Beryllium: 535, 1038, 1676
Bismuth: 535, 2208
Boron: 1776
Cadmium: 155, 535, 862, 1131, 1305, 1382, 1564, 1776, 1867, 1897,
1901, 2024, 2106, 2137, 2198
Calcium: 530, 535. 872, 1131, 1464, 1868, 1897, 2024, 2025, 2145
Cerium: 535, 862, 1038, 1944, 1955, 2208
Cesium: 83, 261, 535, 862, 1038, 1413, 1442, 1676, 2024, 2208
Chromium: 535, 1131, 1382, 1602, 1603, 1776, 1934, 1955, 2024
Cobalt: 261, 535, 1038, 1131, 1676, 1776, 1897, 1955, 2024, 2208
Copper: 71, 485, 487, 535, 1022, 1131, 1287, 1344, 1382, 1397, 1479,
1503, 1564, 1678, 1776, 1867, 1897, 1934, 1973, 2024, 2072,
2106, 2137, 2198
Europium: 1038, 2024
Gallium: 535, 1503
Germanium: 535
Gold: 535
Hafnium: 2024
Iron: 261, 535, 1022, 1131, 1344, 1503, 1603, 1867, 1897, 1934,
1955, 1973, 2024, 2109. 2198
Lanthanum: 535 r
Lead: 1131, 1382, 1479. 1776, 1867, 1973, 2024, 2106, 2137, 2198
Lithium: 535, 1442
Magnesium: 870, 1131, 1464, 1897, 2025, 2059
Manganese: 261, 1038, 1131, 1287, 1564, 1776, 1897, 1934, 1955,
1973, 2106, 2109, 2208
Mercury: 485, 535, 1287, 1382, 1614, 1771, 1776, 1897, 1934, 2024,
2106, 2137, 2198
Molybdenum: 535
427
-------
Neodymium: 535
Nickel: 535, 1131, 1382, 1776, 1897, 2106, 2109, 2198
Niobium: 535, 1038, 1676, 1944
Potassium: 83, 535, 1038, 1131, 1442, 1676, 1897, 1944, 2024, 2025
Plutonium: 1293, 1900, 1955, 2068
Praseodymium: 535
Rubidium: 535, 1442, 2024
Ruthenium: 1038, 1413, 1676, 2208
Salinity: 518, 1764, 2145, 2209
Samarium: 535
Scandium: 2024
Selenium: 2024
Si licon: 535
Silver: 485, 535, 1131, 1312, 2024
Sodium: 535, 1131, 1442, 1897, 2024, 2025
Strontium: 188, 261, 535, 862, 1038, 1131, 1413, 1676, 1868, 1897,
1955, 2024, 2145
Tantalum: 2024
Terbium: 2024
Thallium: 535
Thorium: 2024
Tin: 535, 1131
Titanium: 535
Tungsten: 535
Uranium: 1955
Vanadium: 535
Yttrium: 535, 1413
Zinc: 101, 291, 384, 485, 533, 535,
1305, 1382, 1413, 1479, 1564,
1955, 1973, 2024, 2072, 2106,
Zirconium: 1038, 1676, 1944
675, 862, 1022, 1038, 1131, 1287,
1776, 1867, 1897, 1934, 1944,
2137, 2198, 2208
ELASMOBRANCHI I
Antimony: 1627
Arsenic: 1386, 1627, 1813
Barium: 1627, 1868
Boron: 1627
Cadmium: 1227, 1564, 1627
Calcium: 153, 1531, 1569, 1627, 1868, 1963, 2004
Cerium: 353, 1963
Cesium: 353, 890, 1085, 1442, 1963
Chromium: 1627
Cobalt: 1627, 1963, 1964
Copper: 1356, 1564, 1627, 2030
Gallium: 1627
Germanium: 1627
Gold: 1627
428
-------
Iron: 153, 1627, 1963, 1964
Lead: 1627
Lithium: 1442
Magnesium: 153, 263, 1531, 1569, 1627, 2004
Manganese: 1564, 1627, 1963, 1964
Mercury: 686,687,786, 1227, 1614, 1648, 1756, 2003, 2103
Molybdenum: 1627
Nickel: 1627
Niobium: 353, 1963
Plutonium: 1280
Potassium: 153, 263, 296, 1442, 1531, 1569, 1727, 1854, 1963, 2004
Praseodymium: 1627
Radium: 1627
Rubidium: 1442
Ruthenium: 353, 1963
Salinity: 1764, 1963
Silver: 1627
Sodium: 153, 263, 1377, 1442, 1531, 1569. 1727, 1854, 1855, 1856,
2004
Strontium: 353, 1627, 1868, 1963
Thallium: 1627
Tin: 1627
Titanium: 1627
Vanadium: 1627
Yttrium: 1627, 1963
Zinc: 153, 1564, 1627, 1963, 1964
Zirconium: 353, 1627
FISH
Actinium: 1016
Aluminum: 18, 142, 156, 409, 428, 452, 506, 535, 754, 761, 795, 796,
898, 940, 945, 1235, 1465, 1520, 1628, 1717, 1728, 1873,
2007, 2051, 2141, 2184, 2188, 2194
Americium: 1968
Antimony: 274, 334, 535, 541, 851, 940, 951, 952, 1038, 1210, 1234,
1465, 1676, 1831, 1912, 1917, 2000, 2001, 2009, 2019, 2023,
2024, 2117, 2173, 2188, 2227
Arsenic: 37, 42, 70, 142, 166, 205, 245, 274, 334, 342, 520, 531,
535,735, 748, 815,951,952,977,979, 1067, 1203, 1257,
1269, 1347, 1382, 1386, 1400, 1407, 1408, 1455, 1462, 1465,
1500, 1508, 1518, 1550, 1552, 1596, 1604, 1605, 1647, 1697,
1698, 1728, 1735, 1755, 1813, 1830, 1831, 1832, 1833, 1834,
1837, 1838, 1839, 1840, 1940, 1961, 1962, 1989, 2011, 2024,
2048, 2099, 2137, 2141, 2173, 2188
Barium: 56, 142, 156, 245, 273, 360, 450, 535, 754, 797, 898, 940,
945, 1218, 1235, 1465, 1518, 1628, 1728, 1868, 2007, 2188,
2194
429
-------
Beryllium: 156, 271, 512, 535, 751, 754, 940, 1038, 1101, 1182,
1183. 1676. 1917. 2188, 2246
Bismuth: 535, 541, 940, 1016, 2188
Boron: 1520, 1628, 1728, 2007, 2144
Cadmium: 35, 106, 142, 155, 156, 191, 242, 271, 334, 363, 407, 441,
468, 507, 535, 616, 627, 640, 648, 678, 682, 745, 746, 751,
752, 753, 754, 755, 759, 802, 808, 837, 843, 844, 862, 873,
887, 898, 913, 940, 950, 951, 952, 972, 977, 979, 994, 995,
1002, 1020, 1021, 1092, 1093, 1104, 1121, 1122, 1138, 1151,
1171, 1218, 1227, 1235, 1269, 1322, 1328, 1346, 1367, 1372,
1382, 1408, 1427, 1440, 1448, 1449, 1453, 1459, 1465, 1564,
1613, 1647, 1662, 1684, 1695, 1728, 1808, 1838, 1850, 1872,
1873, 1906, 1908, 1933, 1935, 1940, 1971, 1981, 2008, 2024,
2032, 2092, 2102, 2106, 2107, 2112, 2129, 2137, 2141, 2166,
2173, 2186, 2187, 2188, 2206, 2211, 2212, 2213, 2229, 2236,
2244, 2246
Calcium: 1, 2, 4, 7, 11, 22, 37, 69, 80, 95, 115, 128, 142, 156,
157, 184, 251, 262, 282, 301, 309, 356, 371, 380, 381, 443,
444, 445, 449, 459. 525, 528, 535, 648, 658, 664, 674, 737,
749, 754, 798, 806, 876, 898, 912, 940, 950, 980, 1054,
1071, 1094, 1119, 1197, 1198, 1199, 1221, 1228, 1235. 1302,
1306, 1314, 1369, 1378, 1379. 1437, 1449. 1465, 1497, 1520,
1534, 1535, 1569, 1576, 1628, 1633, 1650, 1651, 1652, 1662,
1684, 1710, 1711, 1717, 1728, 1751, 1759. 1796, 1808, 1820,
1827, 1868, 1938, 1954, 1976, 2004, 2007, 2011, 2024, 2047,
2051, 2138, 2178, 2243, 2246
Cerium: 28, 106, 207, 270, 323, 383, 439, 449, 471, 535, 539. 541,
582, 583, 586, 636, 851, 862, 928, 1038, 1083, 1088, 1156,
1164, 1369, 1437, 1465, 1518, 1540, 1612, 1917, 1955, 1956,
2011, 2019, 2020,
Cesium: 19, 28, 41, 52, 79, 156, 169.
226, 227, 242, 261, 264, 270,
315, 324, 361, 371, 372, 373,
450, 535. 540, 541, 582, 583,
831, 851, 853, 862, 865, 884,
1038, 1055, 1071, 1083, 1085,
1235, 1343, 1369, 1413, 1437,
1540, 1557, 1612, 1628, 1676,
1956, 2000, 2001, 2011, 2019,
2227
Chromium: 1, 19, 93, 94, 95, 98, 106, 142, 156, 185, 205, 241, 245,
273, 303, 334, 383, 394, 403, 407, 409. 460, 506, 529, 535,
538, 539, 591, 597, 605, 640, 648, 663, 665, 754, 799, 856,
898, 930, 940, 944, 950, 977, 994, 1021, 1069, 1121, 1122,
1178, 1210, 1219, 1234, 1235, 1299. 1300, 1371, 1382, 1440,
1448, 1449, 1465, 1518, 1535, 1602, 1603, 1628, 1645, 1647,
1728, 1795, 1873, 1908, 1955, 1972, 1981, 2001, 2007, 2009,
2010, 2011, 2024, 2037, 2077, 2116, 2141, 2173, 2188
170, 176, 184, 208, 222, 225,
273, 300, 305, 306, 310, 314,
374, 383, 386, 399, 400, 449.
586, 636, 754, 762, 793, 805,
890, 915, 940, 1016, 1035,
1088, 1156, 1194, 1210, 1234,
1442, 1446, 1465, 1470, 1518,
1783, 1796, 1799, 1912, 1917,
2020, 2024, 2050, 2170, 2177,
430
-------
Cobalt: 79, 106, 142, 156, 184, 242, 261, 273, 334, 376, 383, 386,
468, 471, 472, 473, 507, 521, 535, 541, 579, 583, 605, 616,
636, 648, 751, 754, 784, 851, 853, 861, 865, 898, 928, 940,
950, 973, 974, 977, 994, 1038, 1057, 1083, 1147, 1164,
1171, 1209, 1210, 1218, 1234, 1235, 1437, 1440, 1465, 1470,
1518, 1676, 1728, 1828, 1831, 1838, 1912, 1932, 1955, 2000,
2001, 2009, 2010, 2011, 2020, 2023, 2024, 2051, 2141, 2188,
2227
Copper: 2, 18, 20, 30, 42, 48, 76, 77, 93, 106, 108, 128, 134, 142,
143, 156, 175, 203, 231, 236, 245, 271, 282, 325, 328, 329,
330, 334, 340, 343, 344, 345, 363, 365, 375, 378, 394, 407,
409, 410, 411, 454, 484, 488, 489, 492, 493, 494, 495, 504,
509, 521, 527, 535, 536, 544, 564, 583, 597,616, 622, 627,
640, 643, 646, 648, 664, 665, 672, 678, 682, 693, 708, 732,
735, 740, 745, 748, 751, 752, 754, 759, 804, 807, 841, 887,
898, 899, 913, 922, 923, 940, 945, 950, 956, 964, 977, 979,
984, 994, 1003, 1004, 1005, 1006, 1020, 1021, 1049, 1059,
1064, 1092, 1098, 1099, 1120, 1121, 1122, 1134, 1139, 1147,
1170, 1171, 1178, 1188, 1195, 1210, 1215, 1235, 1268, 1269,
1291, 1307, 1322, 1328, 1346, 1347, 1356, 1370, 1373, 1382,
1395, 1397, 1408, 1427, 1430, 1431, 1432, 1440, 1448, 1449,
1465, 1469, 1495, 1518, 1520, 1530, 1554, 1555, 1556, 1564,
1577, 1578, 1613, 1625, 1628, 1647, 1662, 1666, 1683, 1690,
1695, 1709, 1710, 1717, 1728, 1741, 1769, 1816, 1820, 1823,
1826, 1831, 1873, 1878, 1939, 1954, 1971, 1981, 2007, 2011,
2024, 2030, 2066, 2072, 2075, 2096, 2098, 2106, 2107, 2112,
2114, 2129, 2137, 2141, 2166, 2173, 2181, 2182, 2184, 2188,
2194, 2229, 2243, 2244, 2246
Europium: 273, 851, 1038, 1917, 2024, 2227
Gallium: 535, 1520
Germanium: 535, 1735
Gold: 146, 156, 334, 535, 754, 898, 1465, 1604, 1605, 1683
Hafnium: 1465, 2024
Indium: 605, 940, 1465
Iridium: 940
Iron: 3, 18, 24, 26, 48, 90, 106, 115, 129, 142, 156, 161, 168, 213,
242, 261, 272, 273, 386, 390, 409, 411, 433, 452, 471, 500,
506, 521, 535, 538, 541, 551, 583, 605, 615, 636, 640, 648,
678, 708, 754, 798, 802, 853, 861, 878, 879, 921, 928, 940,
945, 950, 973, 974, 979, 1021, 1099, 1134, 1186, 1205, 1210,
1217, 1234, 1235, 1279, 1373, 1408, 1423, 1427, 1449, 1465,
1518, 1520, 1535, 1556, 1603, 1628, 1662, 1717, 1728, 1789,
1828, 1831, 1838, 1873, 1954, 1955, 2000, 2001, 2007, 2009,
2010, 2011, 2024, 2028, 2051, 2095, 2132, 2133, 2141, 2166,
2171, 2184, 2188, 2194, 2227, 2243
Lanthanum: 334, 360, 535, 940, 1465, 1518, 2010
431
-------
Lead: 2, 104, 105, 123, 139, 140, 142, 156, 161, 209, 212, 248, 271,
282, 286, 295, 328, 330, 343, 344, 378, 403, 407, 409, 501,
517, 542, 577, 583, 591, 595, 597, 612, 616, 617, 640, 648,
678, 717, 723, 754, 759, 798, 800, 802, 804, 837, 843, 860,
887, 898, 940, 945, 950, 979, 994, 995, 1031, 1066, 1104,
1154, 1171, 1178, 1235, 1257, 1298, 1322, 1346, 1382, 1407,
1440, 1449, 1455, 1458, 1473, 1512, 1517, 1520, 1607, 1625,
1628, 1647, 1662, 1695, 1717, 1728, 1741, 1809, 1823, 1838,
1873, 1918, 1919, 1981, 2024, 2106, 2107, 2112, 2129, 2137,
2166, 2173, 2181, 2188, 2194, 2206, 2227, 2244
Lithium: 142, 156, 535, 754, 940, 945, 994, 1442, 1449, 1988
Lutetium: 1465
Magnesium: 7, 80, 115, 128, 142, 152, 156, 157, 184, 213, 258, 356,
380, 621, 648, 725, 749, 754, 798, 806, 876, 888, 889,
898, 920, 940, 950, 980, 981, 1054, 1094, 1103, 1197,
1210, 1228, 1235, 1306, 1449, 1465, 1497, 1520, 1534,
1535, 1569, 1628, 1633, 1650, 1651, 1652, 1662, 1710,
1717, 1728, 1751, 1766, 1795, 1796, 1808, 1983, 2004,
2007, 2092, 2194; 2243, 2246
Manganese: 2, 106, 142, 156, 161, 207, 209, 261, 273, 314, 315, 337,
383, 398, 403, 457, 468, 471, 521, 538, 539, 541, 583,
636, 640, 708, 710, 754, 756, 785, 802, 804, 851, 865,
898, 921, 928, 940, 950, 973, 1038, 1083, 1087, 1134,
1139, 1147, 1156, 1164, 1171, 1217, 1234, 1235, 1279,
1295, 1395, 1427, 1437, 1465, 1518, 1564, 1628, 1662,
1684, 1717, 1728, 1810, 1811, 1819, 1828, 1857, 1954,
1955, 1965, 2007, 2011, 2019, 2106, 2107, 2141, 2166,
2173, 2188, 2227
Mercury: 2, 11, 21, 36, 49, 57, 63, 142, 160, 180, 218, 230, 241,
266, 267, 271, 273, 275, 276, 283, 316, 352, 442, 447, 448,
507, 509, 535, 543, 569, 578, 590, 597, 606, 613, 630, 634,
654, 672, 678, 686, 692, 708, 711, 727, 730, 733, 739, 753,
759, 760, 765, 766, 767, 768, 771, 772, 773, 774, 794, 801,
802, 813, 816, 817, 824, 825, 827, 828, 843, 847, 873, 874,
887, 892, 893, 894, 895, 898, 899, 902, 906, 908, 913, 914,
916, 917, 924, 927, 929, 934, 936, 940, 943, 945, 947, 949,
951, 952, 966, 967, 979, 985, 995, 996, 1001, 1002, 1006,
1010, 1011, 1012, 1013, 1014, 1021, 1045, 1046, 1052, 1053,
t
1080, 1091, 1096, 1104, 1121, 1122, 1125, 1132, 1133, 1140,
1144, 1145, 1146, 1161, 1163, 1171, 1180, 1188, 1189, 1206,
1210, 1223, 1227, 1233, 1235, 1253, 1257, 1258, 1260, 1261,
1267, 1269, 1292, 1307, 1310, 1324, 1325, 1327, 1328, 1329,
1333, 1334, 1335, 1337, 1340, 1346, 1375, 1376, 1382, 1396,
1427, 1440, 1447, 1448, 1449, 1453, 1465, 1480, 1482, 1502,
1504, 1521, 1527, 1543, 1555, 1561, 1562, 1568, 1593, 1596,
1611, 1613, 1614, 1615, 1621, 1647, 1648, 1666, 1667, 1675,
1683, 1692, 1693, 1695, 1701, 1702, 1728, 1729, 1732, 1733,
1735, 1741, 1749, 1754, 1756, 1768, 1771, 1781, 1782, 1790
432
-------
Mercury (cont.): 1791, 1800, 1821, 1824, 1831, 1866,
1891, 1924, 1928, 1929, 1936, 1940,
1967, 1981, 1995, 1996, 2000, 2001,
2012, 2015, 2024, 2039, 2070, 2078,
2103, 2106, 2107, 2112, 2113, 2126,
2139, 2141, 2162, 2163, 2168, 2173,
2188, 2206, 2233, 2236, 2244, 2246
Molybdenum: 535, 737, 940, 950, 1176, 1219, 1255, 1465, 1604, 1605,
1628, 1728, 1831, 2019, 2188
Neptunium: 1518
Nickel: 2, 77, 106, 128, 141, 143, 156, 161, 343, 344, 375, 378,
407, 409, 468, 507, 521, 535, 591, 640, 643, 648, 751,754,
898, 940, 950, 994, 1092, 1120, 1121, 1122, 1170, 1171,
1218, 1235, 1346, 1382, 1440, 1449, 1628, 1647, 1709, 1801,
1873, 2051, 2106, 2107, 2141, 2173, 2188f 2227, 2229
Niobium: 383, 535, 539, 605, 940, 1038, 1088, 1437, 1518, 1540, 1612,
1676, 1828, 1917, 1956, 2019, 2227
Palladium: 692, 940
Platinum: 940, 1683
Plutonium: 150, 516, 541, 636, 865, 1044, 1095, 1134, 1293, 1658,
1900, 1918, 1925, 1955, 1968, 2068, 2197, 2227
Polonium: 5, 209, 248, 612, 616, 617, 866, 1154, 1918, 2227
Potassium: 1, 2, 7, 70, 80, 115, 142, 152, 156, 157, 184, 199, 200,
207, 213, 227, 245, 251, 258, 273, 306, 314, 315, 341,
356, 370, 372, 450, 460, 528, 535, 540, 547, 658, 714,
725, 737, 749, 754, 869, 876, 888, 889, 898, 915, 928,
940, 950, 964, 980, 986, 988, 1027, 1038, 1053, 1054,
1083, 1094, 1164, 1197, 1198, 1199, 1210, 1228, 1229,
1235, 1303, 1304, 1357. 1369, 1423, 1437, 1442, 1465,
1560, 1565, 1566, 1569, 1576, 1628, 1633, 1650, 1651,
1652, 1676, 1717, 1727, 1728, 1747, 1766, 1783, 1795,
1796, 1808, 1810, 1811, 1826, 1844, 1848, 1857, 1872,
1902, 1917, 1930, 1946, 1976, 1977, 1983, 2000, 2001,
2004, 2007, 2011, 2019, 2024, 2142, 2146, 2194, 2227,
2243
Praseodymium: 439, 535, 2019
Promethium: 2227
Radium: 248, 273, 326, 350, 391, 401, 588, 928, 2011, 2227
Rhenium: 334, 940, 1604, 1605
Rhodium: 599, 1219, 1828
Rubidium: 156, 334, 535, 754, 940, 1442, 1465, 1628, 2000, 2001,
2024, 2188, 2227
Ruthenium: 28, 53, 150, 281, 310,539, 541, 547, 582, 583, 586, 599.
636, 851, 861, 919, 940, 1038, 1088, 1134, 1156, 1209,
1320, 1369, 1413, 1437, 1518, 1540, 1612, 1676, 1828,
1912, 1917, 1956, 2011, 2019
1879,
1948,
2003,
2080,
2129,
2181,
1889,
1966,
2007,
2086,
2137,
2185,
433
-------
Salinity: 7, 8, 15, 23, 57, 59, 103, 112, 117, 144, 177, 199, 200,
201, 237, 246, 247, 251, 252, 253, 307, 341, 356, 388,
389, 422, 462, 470, 507, 510, 518, 573, 574, 575, 576,
609, 611, 621, 658, 689, 690, 691, 744, 753, 858, 926,
939, 948, 953, 976, 980, 986, 1009, 1103, 1113, 1114,
1126, 1127, 1143, 1169, 1178, 1200, 1225. 1231, 1297,
1300, 1303, 1304, 1306, 1308, 1398, 1401, 1467, 1468,
1477, 1488, 1489, 1~19, 1524, 1546, 1560, 1576, 1649,
1661, 1691, 1700, 1705, 1764, 1766, 1778, 1802, 1844,
1847, 1848, 1850, 1857, 1877, 1915, 1983, 1984, 1985,
2031, 2074, 2093, 2146, 2186, 2209, 2210, 2211, 2212,
2213, 2241, 2242
535, 1465
273, 1465, 1518, 2000, 2001, 2009, 2010, 2011, 2023, 2024
334, 827, 940, 979, 1065, 1149, 1257, 1352, 1465, 1551,
1596, 1611, 1702, 1728, 1762, 1831, 1834, 1838, 1840,
1922, 1940, 1989, 2000, 2001, 2007, 2024, 2056, 2173
Silicon: 309, 535, 1465, 1628, 1717
Silver: 142, 143, 156, 241, 271, 273, 386, 535, 616, 648, 692, 697,
754, 783, 784, 865, 887, 898, 940, 945, 1164, 1171, 1218,
1235, 1311, 1440, 1613, 1625. 1628, 1645, 1647, 1683, 1873,
1987, 2000, 2001, 2023, 2024, 2142, 2188, 2227
Sodium: 1, 2, 7, 15, 80, 99, 108, 113, 115, 123, 128, 142, 152, 156,
157, 162, 163, 164, 165, 184, 199, 200, 213, 225, 239, 245,
251, 258, 264, 273, 307, 341, 356, 452, 528, 535, 621, 658,
714, 725, 749, 754, 798, 869, 876, 888, 889, 898, 915, 920,
940, 950, 980, 981, 986, 987, 988, 1026, 1027, 1053, 1054,
1094, 1103, 1143, 1169. 1197, 1198, 1199, 1210, 1228, 1229,
1230, 1235, 1299, 1300, 1303, 1304, 1306, 1357, 1401, 1423,
1442, 1465, 1488, 1489, 1519, 1560, 1565, 1566, 1569, 1576,
1628, 1633, 1644, 1650, 1651, 1652, 1683, 1700, 1717, 1727,
1728, 1747, 1757, 1765, 1766, 1778, 1795, 1802, 1820, 1826,
1844, 1847. 1848, 1872, 1889, 1902, 1930, 1946, 1976, 1977,
1983, 1984, 1985, 2000, 2001, 2004, 2007, 2011, 2015, 2024,
2092, 2116, 2146, 2194, 2243
Strontium: 4, 16, 53, 67, 68, 69, 75, 79, 80, 142, 150, 156, 169,
170, 184, 188, 222, 242, 261, 262, 264, 310, 349, 359,
360, 368, 371, 379, 380, 381, 403, 435, 439, 443, 444,
445, 449, 450, 455, 458, 459. 474, 514, 524, 525, 535,
541, 547, 589, 603, 605, 616, 633, 636, 648, 674, 677,
749, 754, 851, 862, 898, 928, 940, 1016, 1030, 1034,
1038, 1055, 1056, 1058, 1071, 1139, 1172, 1209, 1216,
1217, 1221, 1234, 1235, 1239, 1302, 1314, 1369. 1378,
1379, 1413, 1414, 1437, 1465, 1470, 1518, 1540, 1612,
1628, 1676, 1711, 1728, 1759, 1796, 1868, 1938, 1954,
1955, 2007, 2011, 2019, 2020, 2024, 2050, 2051, 2138,
2227
Tantalum: 940, 1465, 2024
Samarium:
Scandium:
Selenium:
434
-------
Tellurium: 940, 2019, 2188
Terbium: 2024
Thallium: 156, 273, 369, 535, 754,
Thorium: 334, 401, 940, 977, 1016,
Tin: 106, 142, 294, 403, 409, 535,
2166, 2173
Titanium: 403, 535, 940, 1465, 1520, 1628, 1873, 2188
Tritium: 478
Tungsten: 535, 1465, 1604, 1605, 1831, 2005, 2166
Uranium: 27, 308, 334, 512, 588, 945, 977, 1016, 1017, 1465, 1683,
1955, 2173, 2188, 2227
Ytterbium: 1465
Yttrium: 22, 68, 75, 273, 368, 439, 474, 514, 525, 535, 1030, 1413,
1414, 1540, 1828, 2019, 2227
Vanadium: 106, 403, 535, 940, 1218, 1465, 1556, 1604, 1605, 1628,
2188
Zinc: 3, 18, 19, 20, 40, 48, 53, 62, 76, 77, 78, 79, 81, 93, 94, 95,
97, 98, 106, 108, 109, 123, 128, 142, 152, 154, 156, 157, 179,
184, 198, 203, 205, 207, 209, 217, 222, 229, 233, 234, 238,
241, 242, 250, 273, 282, 284, 287, 288, 292, 314, 315, 327,
328, 329, 330, 334, 343, 344, 345, 360, 362, 378, 383, 394,
398, 406, 407, 408, 409, 411, 412, 430, 431, 432, 436, 437,
438, 454, 463, 464, 471, 479, 480, 481, 482, 487, 488, 489,
490, 491, 492, 493, 494, 495, 496, 504, 507, 521, 535, 539,
540, 564, 583, 597, 604, 605, 640, 643, 644, 648, 655, 656,
660, 661, 663, 664, 665, 666, 667, 668, 669, 675, 678, 682,
685, 697, 708, 713, 745, 749, 751, 752, 754, 758, 759, 785,
802, 804, 827, 837, 843, 851, 859, 862, 865, 887, 898, 899,
940, 950, 951, 952, 973, 977, 979, 994, 998, 1021, 1028, 1035,
1038, 1082, 1083, 1087, 1092, 1098, 1109, 1120, 1121, 1122,
1123, 1129, 1134, 1139, 1141, 1142, 1147, 1156, 1164, 1171,
1178, 1181, 1188, 1191, 1192, 1193, 1195, 1209, 1217, 1218,
1234, 1235, 1251, 1252, 1269, 1279, 1295, 1322, 1346, 1362,
1363, 1364, 1365, 1366, 1373, 1382, 1387, 1404, 1407, 1408,
1413, 1421, 1427, 1431, 1437, 1440, 1448, 1449, 1451, 1465,
1470, 1471, 1518, 1535, 1541, 1554, 1555, 1556, 1564, 1577,
1613, 1625, 1628, 1645, 1647, 1662, 1665, 1683, 1684, 1688,
1689, 1690, 1695, 1709, 1710, 1717, 1728, 1820, 1823, 1826,
1828, 1831, 1838, 1873, 1881, 1907, 1908, 1912, 1919, 1939,
1940, 1954, 1955, 1965, 1971, 1981, 2000, 2001, 2007, 2009,
2010, 2011, 2016, 2019, 2020, 2023, 2024, 2032, 2047, 2050,
2051, 2055, 2060, 2063, 2072, 2079, 2084, 2087, 2088, 2102,
2106, 2107, 2112, 2129, 2137, 2141, 2166, 2173, 2181, 2188,
2201, 2203, 2225, 2227, 2229, 2243, 2244, 2246
Zirconium: 310, 360, 383, 539, 582, 851, 940, 1038, 1088, 1369, 1437,
1518, 1540, 1612, 1628, 1676, 1828, 1917, 1956, 2019,
2227
940, 995, 1683, 2244
1465, 2024, 2188, 2227
775, 940, 1218, 1219, 1465, 1717,
435
-------
FUNGI
Arsenic: 735
Cadmium: 1157, 1449
Calcium: 1449
Chromium: 1449
Cobalt: 1157, 1674
Copper: 735,736, 1157, 1449, 1556, 1674, 1686, 1851,2191
Iron: 921, 1449, 1556, 1674, 1686, 2191
Lead: 1449
Lithium: 1449
Magnesium: 1449, 1514
Manganese: 921, 1157, 1674, 1811, 2191
Mercury: 1157, 1449, 2033, 2034
Molybdenum: 1674, 2191
Nickel: 1157, 1449, 1674
Potassium: 1811
Salinity: 1157, 1513, 1737, 1851
Selenium: 1463
Sodium: 1514
Vanadium: 1556
Zinc: 1079, 1157, 1266, 1449,1556, 1674, 1686,2191
HIGHER PLANTS
535, 570
535, 541, 1038, 1676, 1835, 1917
531, 535, 748, 1118, 1203, 1382, 1697, 1830, 1835, 1837,
2011
Barium: 535
Beryllium: 535, 1038, 1676, 1917
Bismuth: 535, 541
Boron: 570
Cadmium: 535, 681, 802, 873, 950, 995, 1382, 1454, 1539, 1775, 1842,
1886, 2107
Calcium: 535, 570, 737, 880, 950, 1070, 1201, 1369, 1523, 1722,
1759, 1938, 2011, 2138
Cerium: 413, 535, 541, 555, 1038, 1369, 1612, 1917, 2011
Cesium: 19, 306, 310, 399, 400, 413, 535, 541, 555, 568, 587, 818,
1038, 1369, 1424, 1612, 1676, 1917, 2011, 2223
Chromium: 535, 788, 950, 1382, 1603, 1722, 1723, 2011, 2049
Cobalt: 535, 541, 568, 849, 885, 950, 1038, 1057, 1676, 1723, 1835,
1842, 2011, 2049
Copper: 38, 175, 535, 570, 619, 650, 748, 950, 1134, 1382, 1397,
1461, 1539, 1556, 1578, 1709, 1835, 1842, 1878, 2011, 2049,
2096, 2107, 2128
Europium: 1038, 1917
Gallium: 535
Aluminum:
Antimony:
Arsenic:
436
-------
Germanium: 535
Gold: 535
Iron: 535, 541, 570, 802, 885, 921, 950, 1134, 1187, 1279, 1523,
1556, 1603, 1721, 1722, 1723, 1835, 1842, 2011, 2049, 2109
Lanthanum: 535
Lead: 802, 950, 995, 1345, 1382, 1539, 1775, 1842, 1886, 1919, 2107
Lithium: 535
Magnesium: 570, 880, 950, 1201, 1722
Manganese: 541, 555, 570, 802, 849, 921, 950, 1038, 1134, 1279,
1722, 1723, 1835, 1842, 2011, 2049, 2107, 2109
Mercury: 218, 535, 543, 734, 768, 771, 802, 854, 873, 874, 893,
936, 995, 1271, 1382, 1447, 1454, 1527, 1614, 1667, 1822,
2107, 2159, 2220
Molybdenum: 535, 737, 950, 1835, 1842, 2049
Neodymium: 535
Neptunium: 788
Nickel: 535, 950, 1382, 1709, 1723, 1842, 2049, 2107, 2109
Niobium: 535, 555, 1038, 1612, 1676, 1917
Plutonium: 541, 1095, 1134
Potassium: 306, 535, 570, 737, 880, 950, 1038, 1201, 1369, 1676,
1722, 1917,2011
Praseodymium: 535
Promethium: 555
Radium: 391, 401, 2011
Rhenium: 555
Rhodium: 599
Rubidium: 535
Ruthenium: 310, 541, 555, 599, 1038, 1134, 1369, 1612, 1676, 1917,
2011
Salinity: 1187, 1477, 2159
Samarium: 535
Scandium: 2011
Selenium: 1262, 1835, 2056
Silicon: 535
Silver: 535, 1312
Sodium: 535, 570, 950, 1201, 1722, 2011
Strontium: 347, 522, 535, 541, 568, 589, 818, 901, 1038, 1056,
1058, 1070, 1201, 1369. 1612, 1676, 1759, 1938, 2011,
21~8
535, 995
401
Thallium:
Thorium:
Tin: 535
Titanium:
Tungsten:
Uranium:
Vanadium:
Yttrium:
535, 2049. 2232
535
788, 1017
535, 788, 1556, 2049, 2232
535
437
-------
Zinc: 19, 284, 418, 419, 437, 535, 570, 619, 650, 802, 849,
1038, 1123, 1129, 1134, 1273, 1279, 1382, 1454, 1556,
1721, 1775, 1835, 1842, 1886, 1919, 2011, 2049, 2107,
Zirconium: 310, 555, 852, 1038, 1369, 1612, 1676, 1917
950,
1709,
2225
INSECTA
1016
1283, 1284, 1558
1203, 1518, 1550, 2011
797, 1518, 1558
1016
468, 537, 802, 1121, 1212, 1283, 1284, 1360, 1617, 1662,
2147
Calcium: 115, 602, 1283, 1535, 1558, 1617, 1662, 2011, 2147
Cerium: 1518, 1558, 1617, 2011
Cesium: 587, 1016, 1518, 1558, 1617, 2011, 2177
Chromium: 502, 537, 1121, 1283, 1284, 1518, 1535, 1558, 1617, 2011
Cobalt: 468, 537, 1283, 1284, 1518, 1558, 1617, 2011
Copper: 171, 175, 410, 492, 493, 502, 537, 804, 1121, 1283, 1284,
1360, 1397, 1518, 1578, 1625, 1662, 1909, 2011, 2096, 2147
Europium: 1558
Iron: 115, 537, 802, 1283, 1284, 1360, 1518, 1535, 1558, 1617, 1662,
1789, 2011, 2132
Lanthanum: 1518, 1558
Lead: 537, 802, 804, 1360, 1625, 1662, 1809, 1909, 1919
Magnesium: 115, 602, 1283, 1284, 1535, 1662, 1761, 2147
Manganese: 337, 468, 756, 802, 804, 1283, 1284, 1360, 1518, 1558,
1662, 2011, 2147
Mercury: 192, 468, 537, 765, 802, 1046, 1121, 1334, 1527, 1558,
1617, 1928, 1929
Molybdenum: 1283, 1284
Neodymium: 1558
Neptunium: 1518
Nickel: 468, 537, 1121, 1283, 1284, 1360
Niobium: 1518
Potassium: 115, 602, 1558, 2011, 2147
Radium: 391, 588, 2011
Rhodium: 599
Rubidium: 1558
Ruthenium: 599,
Salini ty: 1661,
Scandium: 1518,
Selenium: 1558
Silver: 1360, 1625, 1909
Sodium: 115, 602, 1558, 2011
Strontium: 370,1016,1518,1617,2011
Tantalum: 1558
Actinium:
Aluminum:
Arsenic:
Barium:
Bismuth:
Cadmium:
1518, 1617,2011
1764, 2209
1558, 2011
438
-------
Thorium: 1016, 1558
Uranium: 588, 1016
Vanadium: 1558
Yttrium: 192
Zinc: 217, 284, 286, 410, 493, 537,
1283, 1284, 1360, 1518, 1535,
1909, 1919. 2011, 2147
Zirconium: 1518, 1558, 1617
602, 802, 804, 1121, 1212, 1273,
1558,1617,1625,1662,1788,
MAMMALIA
Antimony: 541, 851, 933, 1038, 1676, 2024
Arsenic: 581, 933, 1382, 1385, 1386, 1462, 1494, 1500, 1550, 1596,
1830, 1834, 1837, 2024
Barium: 202, 797
Beryllium: 1038, 1676
Bismuth: 541
Cadmium: 202, 279, 581, 933, 1382, 1439, 1694, 1775, 1808, 1861,
1935, 2022, 2024
Calcium: 202, 1808, 1861, 2024, 2035
Cerium: 541, 851, 1038, 1956
Cesium: 310, 541, 851, 1038, 1148, 1676, 1956, 2024
Chromium: 597, 788, 1382, 2024
Cobalt: 278, 279, 541, 851, 1038, 1209, 1317, 1676, 2024
Copper: 202, 278, 597, 1356, 1382, 1556, 1694, 2024, 2072
Europium: 851, 1038, 2024
Gold: 202, 1861
Hafnium: 2024
Iron: 541, 615, 1556, 1861, 2024
Lead: 202, 248, 278, 279, 581, 597, 617, 635, 1168, 1382, 1694, 1775,
2022, 2024
Magnesium: 1808, 1861
Manganese: 202, 278, 279, 541, 851, 1038, 1861, 2035
Mercury: 202, 266, 278, 279, 302, 316, 569, 580, 581, 590, 597, 809.
810, 810A, 827, 896, 908, 924, 933, 936, 963, 967, 1011,
1012, 1080, 1096, 1144, 1163, 1180, 1214, 1382, 1396, 1439.
1504, 1527, 1561, 1596, 1611, 1692, 1694, 1736, 1780, 1861,
1929, 2022, 2024, 2035, 2086, 2162, 2185
Molybdenum: 2035
Neptunium: 788
Nickel:' 1382
Niobium: 1038, 1676, 1956
Plutonium: 541, 1044, 1293
Polonium: 248, 617, 1168
Potassium: 1038, 1676, 1808, 1861, 2024, 2035
Radium: 248, 401
Rhodium: 599
Rubidium: 2024
439
-------
310, 541, 599, 851, 1038, 1209, 1676, 1956
2024
827, 933, 1262, 1352, 1596, 1611, 1780, 1834, 1861, 2024,
2056
Silver: .202, 783, 1861, 2024
Sodium: 1861, 2024, 2035
Strontium: 202, 310, 347, 541, 851, 1038, 1056, 1148, 1209, 1676,
2024
Tantalum: 2024
Terbium: 2024
Thorium: 401, 2024
Uranium: 788, 2035
Vanadium: 788, 1556
Zinc: 202, 597, 758, 827, 851, 933, 1038, 1129, 1209, 1382, 1387,
1556, 1694, 1775, 1861, 2024, 2072
Zirconium: 310, 851, 852, 1038, 1676, 1956
Ruthenium:
Scandium:
Selenium:
MISCELLANEOUS
Aluminum: 505
Barium: 392
Bibliography: 366, 750, 1629
Cadmium: 392
Calcium: 392
Cesium: 358
Chromium: 64
Cobalt: 392
Copper: 10, 64, 89, 290, 1373
Iron: 24, 1373
Lead: 52, 89, 104, 392
Magnesium: 392
Manganese: 392
Mercury: 392
Nickel: 64, 392
Potassium: 289
Salini ty: 289
Silver: 392, 563
Strontium: 358
Zinc: 89, 127, 392, 1373
MOLLUSCA
Aluminum:
216, 428, 506, 535, 649, 670, 1106, 1162, 1486, 1503,
1794, 1867, 1992, 2188
466, 535, 541, 638, 951, 1038, 1039, 1224, 1234, 1384,
1627, 1676, 2019, 2023, 2024, 2117, 2188, 2208, 2227
Antimony:
440
-------
Arsenic: 338, 456, 534, 535, 670, 951, 982, 1039, 1238, 1347, 1382,
1386, 1407, 1455, 1462, 1486, 1493, 1500, 1525, 1596, 1604,
1605, 1627, 1631, 1685, 1697, 1813, 1834, 1837, 1839, 1845,
1910, 1962, 2011, 2024, 2118, 2137, 2188
Barium: 535, 557, 769, 1039, 1106, 1563, 1627, 1868, 1978, 2188
Beryllium: 535, 1038, 1101, 1676, 2188
Bibliography: 45, 56
Bismuth: 65, 535, 541, 2188, 2200, 2208
Boron: 1039, 1627, 2036, 2144
Cadmium: 155, 221, 242, 426, 475, 477, 535, 559, 560, 638, 639, 649,
670, 731, 755, 770, 789, 821, 862, 873, 875, 951, 982, 989,
994, 1023, 1039, 1084, 1104, 1115, 1121, 1162, 1305, 1321,
1382, 1415, 1445, 1448, 1486, 1564, 1589. 1591, 1592, 1627,
1646, 1758, 1787, 1845, 1862, 1867, 1901, 1910, 1923, 1974,
1975, 1991, 2024, 2081, 2105, 2106, 2107, 2135, 2137, 2147,
2148, 2149, 2156, 2176, 2188, 2199, 2200, 2236, 2240
Calcium: 32, 33, 61, 65, 66, 115, 158, 184, 204, 530, 535, 629, 674,
700, 749, 769, 806, 832, 1033, 1078, 1106, 1162, 1237,
1341, 1342, 1369, 1384, 1437, 1444, 1464, 1535, 1627, 1637,
1639, 1759, 1779, 1792, 1814, 1868, 1887, 1954, 1963, 2011,
2024, 2025, 2145, 2147, 2164, 2190
Cerium: 28, 190, 224, 383, 425, 439, 457, 466, 535, 539, 541, 582,
583, 586, 600, 862, 955, 1029, 1038, 1156, 1164, 1224, 1369,
1437, 1612, 1955, 1956, 1963, 1990, 2011, 2019, 2208
Cesium: 28, 52, 79, 83, 84, 184, 190, 194, 224, 242, 261, 361, 383,
413, 425, 535, 541, 557, 582, 583, 586, 600, 838, 862, 955,
957, 1029, 1038, 1039, 1078, 1156, 1234, 1277, 1278, 1332,
1369, 1413, 1437, 1442, 1446, 1470, 1612, 1676, 1758, 1956,
1963, 1990, 2011, 2019, 2024, 2050, 2208, 2227
Chromium: 93, 224, 383, 394, 426, 475, 506, 535, 539, 598, 638, 649,
670, 705, 770, 821, 944, 994, 1037, 1039, 1105, 1121,
1162, 1224, 1234, 1309, 1321, 1382, 1384, 1448, 1450,
1486, 1535, 1589, 1591, 1602, 1603, 1627, 1645, 1787,
1934, 1937, 1955, 1972, 2011, 2024, 2081, 2188, 2200,
2237
Cobalt: 79, 184, 194, 224, 242, 261, 312, 383, 426, 535, 541, 561,
583, 623, 649, 784, 838, 974, 975, 994, 1023, 1029, 1038,
1039, 1077, 1078, 1086, 1135, 1162, 1164, 1174, 1175, 1209,
1224, 1234, 1236, 1259, 1286, 1317, 1318, 1341, 1342, 1384,
1437, 1470, 1486, 1563, 1589, 1591, 1627, 1676, 1758, 1828,
1955, 1963, 1990, 2011, 2023, 2024, 2081, 2188, 2200, 2208,
2227
Copper: 44, 72, 108, 133, 175, 187, 197, 220, 221, 240, 244, 338,
377, 394, 396, 405, 421, 426, 475, 477, 504, 509. 535, 552,
553, 558, 559, 583, 598, 610, 620, 638, 642, 649, 670, 695,
699, 700, 728, 731, 742, 770, 804, 821, 857, 875, 935, 954,
982, 989, 994, 1039, 1078, 1115, 1117, 1121, 1136, 1137,
1139. 1162, 1196, 1272, 1301, 1309, 1321, 1326, 1344, 1347,
441
-------
Copper (cant.): 1382, 1390, 1391, 1397,
1486, 1501, 1503, 1525,
1564, 1578, 1589, 1591,
1627, 1646, 1685, 1704,
1715, 1787, 1794, 1845,
1867. 1874, 1875, 1876,
1934, 1937, 1954, 1973,
1993, 2011, 2024, 2027,
2069, 2072, 2081, 2096,
2118, 2137, 2147, 2148,
2190, 2199, 2200, 2217,
Europium: 466, 1038, 1224, 2024, 2227
Gallium: 535, 1039, 1503, 1627
Germanium: 535, 1039, 1627
Gold: 146, 425, 535, 1039, 1604, 1605, 1627
Hafnium: 2024
Iron: 14, 115, 158, 242, 243, 261, 313, 321, 390, 404, 405, 426,
506, 535, 541, 583, 638, 649, 863, 864, 921, 974, 1029, 1078,
1086, 1111, 1117, 1135, 1136, 1162, 1224, 1234, 1272, 1274,
1279, 1344, 1384, 1415, 1419, 1503, 1525, 1535, 1556, 1580,
1589, 1591, 1592, 1601, 1603, 1609, 1616, 1620, 1627, 1677,
1758, 1828, 1862, 1867, 1875, 1876, 1887, 1934, 1954, 1955,
1963, 1973, 1978, 1990, 1991, 1992, 2011, 2024, 2081, 2188,
2190, 2199, 2200, 2227, 2239
Lanthanum: 535, 557, 1224, 1341
Lead: 137, 248, 426, 583, 598, 612, 638, 639, 649, 670, 671, 742,
770, 804, 821, 845, 989, 994, 1039, 1104, 1158, 1159, 1160,
1162, 1309, 1321, 1382, 1407, 1415, 1445, 1455, 1474, 1486,
1501, 1525, 1549, 1589, 1591, 1627, 1646, 1787, 1809, 1845,
1867, 1919, 1973, 1974, 1975, 1991, 1992, 2024, 2081, 2106,
2107, 2110, 2118, 2137, 2156, 2176, 2188, 2200, 2227
Lithium: 32, 61, 535, 629, 769, 957, 994, 1442
Magnesium: 61, 115, 158, 184, 558, 629, 700, 749, 769, 806, 1106,
1162, 1237, 1272, 1444, 1464, 1486, 1535, 1627, 1639,
1792, 1794, 1814, 1887, 1978, 2025, 2036, 2147, 2164,
2190
Manganese: 100, 189, 219, 223, 261, 355, 383, 426, 466, 539, 541,
557, 561, 583, 623, 638, 639, 649, 670, 688, 731, 738,
769~ 785, 804, 811, 821, 921, 1023, 1038, 1039, 1076,
1078, 1086, 1139. 1155, 1156, 1162, 1164, 1234, 1279.
1286, 1341, 1342, 1437, 1564, 1589. 1591, 1592, 1601,
1608, 1609, 1627, 1794, 1828, 1875, 1876, 1934, 1954,
1955, 1963, 1973, 1978, 1991, 1992, 2011, 2019, 2036,
2081, 2106, 2107, 2147, 2188, 2199, 2200, 2208, 2227
Mercury: 266, 267, 302, 316, 352, 421, 509, 535, 553, 590, 598, 670,
671, 695, 699. 712, 731, 742, 767, 768, 770. 772, 867, 873,
874, 877, 882, 883, 894, 896, 908, 925, 934, 935, 949, 951,
989, 996, 1012, 1013, 1104, 1117, 1121, 1125, 1163, 1166,
1415,
1537,
1592,
1709,
1851,
1887,
1974,
2030,
2105,
2149,
2230,
1416,
1549,
1609,
1712,
1858,
1888,
1975,
2036,
2106,
2156,
2237
1419,
1556,
1610,
1713,
1862,
1895,
1991,
2044,
2107,
2158,
1448,
1563,
1620,
1714,
1865,
1923,
1992,
2066,
2108,
2188,
442
-------
Mercury (cont.):
1206, 1226, 1232,
1443, 1448, 1486,
1527, 1533, 1580,
1770, 1771, 1910,
2024, 2067, 2091,
2188, 2220, 2236
638, 1039, 1176, 1604, 1605, 1627,
1321,
1487,
1585,
1934,
2106,
1327,
1501,
1596,
1937,
2107,
1334,
1502,
1648,
1996,
2137,
1382,
1505,
1692,
2013,
2140,
1384,
1506,
1733,
2017,
2163,
Molybdenum: 535,
Neodymium: 535
Nickel: 46, 421, 426, 535, 638,
1078, 1117, 1121, 1162,
1589. 1591, 1627, 1709,
2199, 2200, 2227, 2237
Niobium: 190, 383, 466, 535, 539, 557,
1612, 1676, 1828, 1956, 1963,
Plutonium: 541, 676, 1044, 1095, 1280,
2227
Polonium: 248, 612, 2227
Potassium: 33, 34, 83, 84, 115, 158, 184, 318, 466, 535, 561, 700,
749, 769, 881, 957, 1038, 1076, 1106, 1162, 1164, 1341,
1342, 1369, 1437, 1442, 1676, 1687, 1963, 1990, 2011,
2019, 2024, 2025, 2147, 2190, 2227
Praseodymium: 439, 466, 535, 1627, 2019
Promethium: 466, 688, 2227
Protactinium: 1829
Radium: 65, 248, 466, 1627, 1779, 2011, 2165, 2227
Rhenium: 1604, 1605
Rhodium: 599, 1029, 1828
Rubidium: 535, 957, 1039, 1384, 1442, 2024, 2188, 2227
Ruthenium: 28, 53, 190, 281, 457, 539, 541, 557, 565, 582, 583, 586,
599, 600, 886, 911, 955, 1029, 1038, 1156, 1209. 1320,
1369, 1413, 1437, 1612, 1659, 1676, 1725, 1752, 1828,
1956, 1963, 1990, 2011, 2019. 2208
Salinity: 148, 367, 578, 594, 659, 680, 968, 969, 970, 1152, 1237,
1277. 1278, 1313, 1355, 1403, 1422, 1452, 1486, 1538,
1570, 1660, 1691, 1715, 1764, 1851, 1963, 1978, 1993,
2111, 2145, 2151, 2209
404, 405, 535, 1224
404, 405, 1166, 1224, 1384, 2011, 2023, 2024
1077, 1224, 1384, 1585, 1586, 1596, 1834, 2024
535
221, 535, 638, 639, 649, 670, 671, 695, 742, 783, 784, 821,
982, 1039, 1162, 1164, 1272, 1309, 1312, 1321, 1384, 1486,
1589, 1627, 1645, 1646, 1862, 1910, 1987, 1990, 1991, 1992,
2023, 2024, 2150, 2151, 2188, 2199, 2200, 2227
Sodium: 32, 33, 34, 61, 84, 108, 115, 158, 184, 367, 535, 629, 700,
749, 769, 957, 1106, 1162, 1196, 1341, 1442, 1444, 1687,
2011, 2024, 2025, 2036
2019, 2188
649, 670, 671, 731, 994, 1023, 1039,
1309. 1321, 1341, 1342, 1382, 1415,
1801, 1991, 2081, 2106, 2107, 2188,
1029, 1038, 1166, 1437, 1456,
1990, 2019, 2227
1293, 1587, 1900, 1955, 2068,
Samarium:
Scandium:
Selenium:
Silicon:
Silver:
443
-------
Strontium: 14, 53, 65, 66, 79, 184, 188, 190, 196, 224, 242, 261,
347, 370, 385, 387, 413, 414, 417, 439, 466, 535, 541,
674, 749, 862, 1033, 1037, 1038, 1039, 1078, 1107, 1139,
1162, 1209, 1234, 1239, 1332, 1369, 1413, 1437, 1470,
1595, 1627, 1676, 1758, 1759, 1794, 1814, 1868, 1911,
1954, 1955, 1963, 1978, 2011, 2019, 2024, 2036, 2050,
2145, 2164, 2227
Tantalum: 2024
Terbium: 2024
Tellurium: 2019, 2188
Thallium: 535, 1627, 2245
Thorium: 1224, 2024, 2165, 2188, 2227
Tin: 535, 1039, 1077, 1525, 1563, 1627, 1992, 2118
Titanium: 535, 1039, 1627, 2188
Tungsten: 535, 1604, 1605
Uranium: 1017, 1955, 2188, 2227
Vanadium: 535, 638, 639, 1039, 1107, 1456, 1556, 1604, 1605, 1627,
2188
Yttrium: 387, 439, 466, 535, 1037, 1413, 1595, 1627, 1828, 1963
2019, 2227
Zinc: 53, 62, 79, 93, 108, 135, 136, 145, 146, 147, 148, 158, 172,
174, 184, 194, 217, 219, 220, 223, 224, 242, 284, 313, 354,
383, 394, 395, 404, 405, 421, 424, 425, 426, 451, 457, 475,
477, 504, 506, 524, 533, 535, 539, 553, 557, 559, 560, 561,
562, 583, 598, 623, 637,638, 639, 642, 649, 670, 671, 675,
676, 695, 699, 700, 705, 731, 738, 742, 749, 758, 770, 776,
785, 789, 804, 821, 857, 862, 875, 909, 910, 935, 946, 951,
982, 994, 1037, 1038, 1076, 1086, 1107, 1115, 1117, 1121,
1129, 1135, 1136, 1139, 1156, 1162, 1164, 1166, 1167, 1209,
1234, 1236, 1256, 1272, 1276, 1279, 1286, 1305, 1309, 1321,
1382, 1384, 1388, 1407, 1413, 1415, 1416, 1417, 1419, 1437,
1445, 1448, 1450, 1470, 1471, 1486, 1507, 1535, 1537, 1549,
1556, 1563, 1564, 1589, 1591, 1592, 1609, 1627, 1645, 1646,
1681, 1685, 1704, 1709, 1712, 1713, 1714, 1719, 1746, 1758,
1787, 1828, 1845, 1862, 1867, 1874, 1875, 1876, 1887, 1888,
1892, 1916, 1919, 1923, 1934, 1954, 1955, 1963, 1973, 1974,
1975, 1990, 1991, 1992, 2011, 2019, 2023, 2024, 2050, 2064,
2072, 2073, 2081, 2105, 2106, 2107, 2118, 2137, 2147, 2148,
2149, 2156, 2176, 2188, 2190, 2199, 2200, 2208, 2224, 2227,
2230, 2237, 2239
Zirconium: 190, 194, 383, 466, 539, 557, 582, 1029, 1038, 1166,
1369, 1437, 1612, 1627, 1676, 1828, 1956, 1990, 2019,
2227
NEMATODA
Lead:
2021
444
-------
PHORONIDEA
Aluminum: 535
Antimony: 535
Arsenic: 535
Barium: 535
Beryllium: 535
Bismuth: 535
Cadmium: 535
Calcium: 535, 2145
Cerium: 535
Cesium: 535
Chromium: 535
Cobalt: 535
Copper: 535
Gallium: 535
Germanium: 535
Gold: 535
Iron: 535
Lanthanum: 535
Lithium: 535
Mercury: 535
Molybdenum: 535
Neodymium: 535
Nickel: 535
Niobium: 535
Potassium: 535
Praseodymium: 535
Rubidium: 535
Sal ini ty: 2145
Samarium: 535
Silicon: 535
Silver: 535
Sodium: 535
Strontium: 535, 2145
Thallium: 535
Tin: 535
Titanium: 535
Tungsten: 535
Vanadium: 535
Yttrium: 535
Zinc: 535
PLANKTON
Antimony:
Cal dum:
Cerium:
1959
1859
466, 1959
445
-------
Europium: 1959
Iron: 131, 1859
Manganese: 1859, 1959
Plutonium: 1926, 2068
Praseodymium: 466
Promethium: 1959
Scandium: 1859
Selenium: 2056
Strontium: 1859, 1959
Zinc: 1859
Zirconium: 466, 1959
PLATYHELMINTHES
Aluminum: 1739
Arsenic: 1739
Barium: 1739, 1740
Cadmium: 1739, 1919
Calcium: 1535, 1739, 2145
Chromium: 1535, 1738, 1739
Cobalt: 1739
Copper: 1738, 1739, 1740
Gold: 1739
Iron: 1535, 1739
Lead: 1738, 1739, 1809, 1919, 2021
Magnesium: 1535, 1739
Manganese: 1739, 1811
Mercury: 1738, 1739, 1740
Nickel: 1739
Potassium: 1739. 1811
Salinity: 1351, 2145, 2209
Silver: 1312, 1739, 1740
Sodium: 1738, 1739
Strontium: 1739, 2145
Zinc: 284, 1535, 1738, 1739, 1919
PORIFERA
Aluminum: 535, 1503
Antimony: 535, 1038, 1627, 1676, 1917, 2208
Arsenic: 535, 1238, 1386, 1518, 1627, 2137
Barium: 535, 1518, 1627, 1868
Beryllium: 535, 1038, 1676, 1917
Bismuth: 535, 2208
Boron: 1627
Cadmium: 535, 1627, 1901, 2137
Calcium: 535, 1464, 1627, 1868, 2145
Cerium: 333, 535, 1038, 1518, 1917, 2208
446
-------
Cesium: 535, 1038, 1518, 1676, 1917, 2208
Chromium: 535, 1518, 1627
Cobalt: 333, 535, 1038, 1518, 1627, 1676, 2208
Copper: 535, 1397, 1503, 1518, 1627, 2137
Europium: 1038, 1917
Gallium: 535, 1503, 1627
Germanium: 535, 1627
Gold: 535, 1627
Iron: 535, 1503, 1518, 1627
Lanthanum: 535, 1518
Le ad : 1627, 2 137
Li thium: 535
Magnesium: 1464, 1627
Manganese: 333, 1038, 1518, 1627, 2208
Mercury: 535, 2137
Molybdenum: 535, 1627
Neodymium: 535
Neptunium: 1518
Nickel: 535, 1627
Niobium: 333, 535, 1038, 1518, 1676, 1917
Potassium: 333, 535, 1038, 1676, 1917
Praseodymium: 333, 535, 1627
Radium: 1627
Rubidium: 535
Ruthenium: 584, 1038, 1518, 1676, 1917, 2208
Salinity: 2145
Samarium: 535
Scandium: 1518
Si licon: 535
Silver: 535, 1627
Sodium: 535
Strontium: 535, 1038, 1518, 1627, 1676, 1868, 2145
Thallium: 535, 1627
Tin: 535, 1627
Titanium: 535, 1627
Tungsten: 535
Vanadium: 535, 1627
Yttrium: 535, 1627
Zinc: 535, 1038, 1518, 1627, 1719, 2137, 2208
Zirconium: 333, 1038, 1518, 1627, 1676, 1917
PROTOZOA
Aluminum: 535, 1503, 1793, 2043
Antimony: 535, 1627, 1959
Arsenic: 535. 1203, 1627
Barium: 535, 1627
Beryllium: 535
447
-------
Bismuth: 535
Boron: 1627
Cadmium: 535, 679, 1171, 1448, 1449, 1627, 1846, 1901, 1969
Calcium: 535, 1000, 1361, 1449, 1464, 1599, 1627, 2136, 2145
Cesium: 413, 535
Cerium: 83, 415, 535, 1959
Chromium: 535, 1448, 1449, 1627, 2043
Cobalt: 535, 679, 1171, 1627, 2043
Copper: 535, 662, 956, 1171, 1254, 1397, 1448, 1449. 1503, 1627,
1635, 1793, 1969, 1970, 2043, 2121
Europium: 1959
Gallium: 535, 1503, 1627
Germanium: 535, 1627
Gold: 535, 1627
Iron: 535, 1449, 1503, 1627
Lanthanum: 535
Lead: 679, 823, 1171, 1254, 1449. 1627, 1634, 1635, 1969, 2043
Lithium: 535, 1449, 2136
Magnesium: 1361, 1449, 1464, 1599, 1627, 1793, 2136, 2195
Manganese: 1171, 1627, 1793, 1811, 1959, 2043, 2195
Mercury: 535, 679, 823, 1171, 1448, 1449, 1634, 1635, 1969, 2152
Molybdenum: 535, 698, 1627
Neodymium: 535
Nickel: 535, 1171, 1449. 1627, 1793, 2136
Niobium: 535
Potassium: 83, 535, 1599, 1811, 2136
Praseodymium: 535, 1627
Promethium: 1959
Radium: 1627
Rubidium: 535
Salinity: 2145, 2209
Samarium: 535
Silicon: 535, 1599
Silver: 535, 1171, 1627
Sodium: 535, 1361, 1599, 2136
Strontium: 413, 414, 466, 535, 1000, 1361, 1627, 1793, 1959. 2145,
2195
Thallium: 535, 1627
Tin: 535, 1627, 2043
Titanium: 535, 1627, 1793
Tungsten: 535
Uranium: 1032
Vanadium: 535, 1627
Yttrium: 535, 1627
Zinc: 535, 662, 679, 823, 1171, 1254, 1448, 1449, 1627, 1634, 1846,
1969, 2043
Zirconium: 1627, 1959
448
-------
REPTILIA
Arsenic: 2011
Cadmium: 2026
Calcium: 2011
Cerium: 2011
Cesium: 2011
Chromium: 2011
Cobalt: 2011
Copper: 1356, 2011
Iron: 2011
Lead: 74, 1918
Manganese: 2011
Plutonium: 1918
Polonium: 1918
Potassium: 2011
Radium: 2011
Ruthenium: 2011
Salinity: 743
Scandium: 2011
Sodium: 149, 2011
Strontium: 2011
Zinc: 2011
ROTIFERA
Arsenic: 706, 1830
Cadmium: 1440, 2123
Calcium: 1805
Chromium: 1440, 2123
Coba1 t: 1440
Copper: 1440, 1878, 2121, 2123
Iron: 1572
Lead: 1440, 2123
Mercury: 1440, 2123
Nickel: 1440
Potassium: 1805, 2123
Sa1 ini ty: 1805
Silver: 1440
Zinc: 1440, 2122, 2123
SEDIMENTS
Aluminum:
Antimony:
Arsenic:
Cadmium:
1486
466, 541, 951, 2117
951, 1486, 1962, 1982
478,731,787,873,950,
1991, 2106, 2107, 2236
951, 995, 1445, 1486, 1901, 1969,
449
-------
Calcium: 184, 950, 1369
Cerium: 466, 541, 1369, 1956
Cesium: 79, 184, 399, 541, 762, 818, 1277, 1369, 1956
Chromium: 950, 1486, 1972
Cobalt: 79, 184, 541, 849, 950, 1486
Copper: 48, 339, 477, 731, 950, 1373, 1486, 1709, 1969. 1991, 2066,
2106, 2107, 2215
Europium: 466
Gold: 146
Iron: 48, 541, 707, 950, 1373, 1991
Lead: 787, 950, 995, 1154, 1345, 1445, 1486, 1969, 1991, 2106, 2107
Magnesium: 184, 950, 1486
Manganese: 466, 541, 707, 731, 849, 950, 1991, 2106, 2107, 2215
Mercury: 218, 230, 267, 731, 787, 873, 892, 943, 951, 995, 1011,
1096, 1190, 1253, 1486, 1527, 1543, 1562, 1732, 1733, 1770,
1969, 2070, 2078, 2106, 2107, 2236
Molybdenum: 950
Nickel: 46, 731, 950, 1709, 1991, 2106, 2107
Niobium: 466, 1956
Plutonium: 150, 541, 1293, 1900, 1926, 2068
Polonium: 1154
Potassium: 184, 466, 950, 1369
Praseodymium: 466
Promethium: 466
Radium: 350, 391, 466
Ruthenium: 73, 150, 281, 541, 551, 1369. 1956
Salini ty: 1277, 1486
Selenium: 1262
Silver: 1486, 1991
Sodium: 184, 950
Strontium: 73, 79, 150, 184, 466, 541, 818, 901, 1369
Technetium: 73
Thallium: 995
Tritium: 73
Yttrium: 466
Zinc: 48,79, 101, 147, 184,217,418,419,437,477, 707, 731, 787,
849, 950, 951, 1373, 1445, 1486, 1709, 1969, 1991, 2106, 2107,
2215
Zirconium: 466, 1369, 1956
SESTON
Cadmium: 2204
Copper: 2204
Iron: 2204
Lead: 2204
Zinc: 2204
450
-------
SIPUNCULOIDEA
Salinity:
1764
TUN ICATA
Aluminum: 535
Antimony: 535, 1627
Arsenic: 535, 1627, 1883, 2038
Barium: 535, 1627, 1868
Beryllium: 535
Bismuth: 535
Boron: 1627
Cadmium: 535, 1564, 1627, 1758
Calcium: 535, 1599, 1627, 1868, 2145
Cerium: 535, 1945
Cesium: 83, 535, 1758
Chromium: 526, 535, 1457, 1627, 1945, 2038
Cobalt: 312, 313, 535, 1174, 1627, 1758
Copper: 535, 1564, 1627, 1973
Gallium: 535, 1627
Germanium: 535, 1627
Gold: 535, 1627
Iron: 43, 313, 535, 1204, 1457, 1601, 1627, 1758, 1973, 2038
Lanthanum: 535
Lead: 1627, 1973
Lithium: 535
Magnesium: 1599, 1627
Manganese: 688, 1457, 1564, 1601, 1627, 1973
Mercury: 535
Molybdenum: 535, 1457, 1627, 2038
Neodymium: 535
Nickel: 535, 1627
Niobium: 535, 1456, 1457, 1945, 2038
Plutonium: 1926
Potassium: 83, 535, 1599, 1945
Praseodymium: 535, 1627
Promethium: 688
Radium: 1627
Rubidium: 535
Ruthenium: 584, 1320, 1945
Salini ty: 2]45
Samarium: 535
Silicon: 535, 1599
Silver: 535, 1627
Sodi urn: 535, 1599
Strontium: 535,1627,1758,1868,2145
Tantalum: 1457
451
-------
Thallium:
Tin: 535,
Ti tanium:
Tungsten:
Vanadium:
535, 1627
1627
535, 1457, 1627
535, 1457
535, 1204, 1456, 1457, 1476, 1553, 1627, 1630, 1745,
1797, 1799, 1883, 2038, 2202
Yttrium: 535, 1627
Zinc: 313, 382, 535, 1564, 1600, 1627, 1719, 1758, 1945, 1973
Zirconium: 1457, 1627, 1945
452
-------
INDEX - AUTHORS
Aarkrog, A. 1293
Abbott, N.J. 1294
Abdelmalik, W.E.Y. 568
Abdullah, M.I. 1295, 1296
Abegg, R. 1
Abou-Donia, M.B. 2
Abraham, M. 1297, 1401
Ackefors, H. 569
Adam, F.S. 570
Adams, E.S. 1298
Adelman, loR. 1299, 1300
Adema, D.M. 256
Adema, D.M.M. 1301,1703
Adron, J.W. 1497
Affleck, R.T. 3
Agnedal, P.O. 4, 1302
Agranat, V.Z. 5
Agre, A. L. 6
Ahokas, R.A. 1303, 1304
Ahsanullah, M. 1305, 1428, 2052
Ahuja, S.K. 7, 1306
Akiyama, A. 1307
Alabaster, J.S. 8
Alasia, A.M. 534
Albright, L.J. 571, 572, 1068
Alderdice, D.F. 573, 574, 1308
Aldrich, D.V. 9, 220, 221, 1265
Alessandrell0, D. 1122
Aleti, A. 803
Alexander, G.V. 1309, 1873
Alexander, J.E. 10, 1310
AI-Hamed, M.I. 575
Allee, w.e. 775, 1311, 1312
Allen, J. 2015
Allen, J.A. 2165
Allen, K. 1313
Allen, K.O. 576
Alley, W.P. 577
Almodovar, L.R. 151, 747
Altmann, H. 2009. 2010
Amavis, R. 636
Amend, D.F. 11, 448, 578
Amiard, J.e. 579, 1314, 1315,
1316, 1317, 1318,
1987
Amiard-Triquet, e.
Amiel, A.J. 1319
Amrit, D. 1705
Anas, R.E. 580, 581
Ancellin, J. 28, 583, 584, 585,
586, 600, 955, 1320,
1659, 1815
Ancellin, J.e.M. 582
Anderlini, V. 1321
Anderlini, v.e. 1861
Andersen, A. T. 1322
Anderson, B.G. 12, 13
Anderson, G. 1248
Anderson, G.E. 587
Anderson, J.B. 588
Anderson, J .M. 1292
Anderson, J. W. 1636, 2029
Andrew, R.W. 625
Andrews, H. L. 14
Andrushaitis, G. 589
Andryushchenko, V.V. 1323
Angelovic, J.W. 15, 1559
Anghileri, L.J. 16
Angino, E. E. 17
Annett, e.s. 733, 1324, 1325
Anon. 18,19,20,21,590,591,592,
1326, 1327, 1328, 1329
Antia, N.J. 1330
Antonenko, T.M. 1446
Antonini-Kane, J. 1331
Anwand, K. 22
App 1 eman, D. 1574
Apts, e.w. 1622
Argiero, L. 1332
Arima, S. 1333
Arlhac, D.P. 1381
Armitage, K.B. 23
Armstrong, F.A.J.
579, 1317, 1318
Armstrong, R.L.
Arnholt, T.J.
Arnold, D.C.
Arnold, E.L.
Arnold, J.e.
1161,
1241,
1334
2164
293
593, 594
24
1665
453
1163,
1242,
-------
Arnold, P.W. 810A
Aronson, A.K. 1335
Aronson, A.L. 595
Aronson, J.L. 1335
Arthur, J.W. 25, 596, 625
Ase11, B. 765, 766, 1568
Ashley, L.M. 26
Aten, A.H.W. 27
Atherton, D.R. 401
Atton, F.M. 556, 1233
Aubert, M. Ill, 597, 598, 949
Auerbach, S.l. 599
Auty, E.H. 1845
Avargues, M. 28, 582, 583, 600
Avau1t, J.W., Jr. 576, 1395
Avio, C.M. 29, 1336
Ayers, J.C. 297, 702
Azam, F. 601
Bacci, E. 1125, 2017
Bache, C.A. 947, 1006, 1337
Bachenheimer, A.G. 1338
Bachmann, R.W. 602, 1339
Bachurin, A.A. 1070, 1071, 1100
Backstrom, J. 1340
Bagena1, T.B. 603
Bahns, T.K. 660, 661
Bails, J.D. 760
Bais, P. 1301
Baker; B.E. 1148
Baker, J.T.Po 30
Baker, P.F. 31, 32, 33, 34, 1341,
1342
Bakkum, W.C.M. 27
Bakunov, N.A. 1343
Ba1ani, M.C. 1078
Ball, E.G. 1344
Ball, 1.R. 35, 604
Ballard, J .A. 36
Bandt, H.J. 37
Banerjea, S. 38
Banks, J .W. 1295
Bannister, A.C. 1930
Banus, M. 1345
Banus, M.D. 2176
Baptist, J. 39
Baptist, J.P. 40, 41, 146, 439,
605, 709, 2020
Barber, R.T. 606, 708
Bare11i, M. 597, 598
Bargmann, G.G. 1346
Barinov, G.V. 417
Barker, J.L. 957
Barnard, H.E. 1347
Barnes, H. 607, 1348
Barnes, M. 607
Barszcz, C.A. 2187
Barth, L.G. 608
Barth, L.J. 608
Bartlett, L. 1349
Bartrand, D. 136
Bashamohideen, M.
Bassett, J.W., Jr.
Batte, E.G. 610
Batterman, A.R. 739
Baudouin, M.F. 1350
Baughman, G.A. 2120
Bawden, C.A. 1075
Beadle, L.C. 1351
Bea1, A.R. 1352
Beamish, F.W.H. 611, 658, 1816
Beasley, J. 1084
Beasley, R.M. 46
Beasley, T.M. 386, 612, 613,
614, 615, 616,
617, 782, 1353,
1354, 1466, 1587,
1682
Beauchamp, J.J. 1558
Beaven, G. F . 1355
Beck, A.B. 1356
Bedrosian, P.H.
Beeton, A.M.
Be 11, H. L .
Bellamy, D.
Bellrose, F.C.
Benayoun, G.
609
1698
47
348
537
1357
1358
789, 790, 1359,
1584, 1585, 1586
618
1360
875, 1704
1361
1463
1362,
1364,
1366,
Ben-Bassat, D.
Bender, J.A.
Bender, M.E.
Bender, M.L.
Bengert, G.A.
Bengtsson, B.E.
1363,
1365,
1367
454
-------
Benijts, F.
Benij ts-Claus,
Beninson, O.
Beninson, O.J.
Bennett, E.a.
Bennett, H.J.
Benoit, O.A.
1368
C.
1369
674
1338, 2119
1535
1003, 1004, 1370,
1371, 1372
Benoit, E~J. 529
Benoit, R.J. 48, 1373
Benos, O. 2015
Benson, W.W. 1374, 1375, 1376
Bentley, P.J. 1377
Berg, A. 1378, 1379
Berg, W. 277, 895, 1380
Bergen, W.G. 2243
Berglund, F. 49
Bergman, H. L. 1052
Bergstrom, E. 1778
Berland, B.R. 1381
Berlin, M. 49
Bernard, F.J.
Bernhard, M.
Bernhardt, H.
Bernheim, F.
Bertine, K.K.
Bertrand, G.
1368
50, 51
52, 53, 54, 1382
696
1383
1384
1385, 1386, 1387
1388
Besch, K.W. 619
Besch, W. 461
Betzer, N. 1025, 1389
Betzer, 8.B. 620, 1390, 1391
Beyenbach, K.W. 621
Beyerle, G.B. 622
Bhatt, 8.G. 1019
Bhatt, Y.M. 623, 2064
Bhattathiri, P.M.A. 1076, 1108
Bida, G. 1120
Bidstrup, P.L.
Bieb1, R. 624
Bie1ig, H.J. 2038
Bie1y, J. 1728, 2007
Bieri, R. 1392, 1794
Biesinger, K.E. 625, 626
Biesoit, P. 1393
Biggs, W.R. 1204
Bij an, H. 56
Bi linski, E.
55
627
Bil1en, G.
Bills, T.O.
Binet, L.
Bioko, Z.F.
Birdsong, C.L.
Birke, G. 1396
Bishai, H.M. 59
Bisque, R.E. 893
Bittel, R. 597, 598, 949
Black, G.A.P. 1397
Black, R. 1962
Black, V.S. 1398
Black, W.A.P. 628
Blackburn, R.O. 2128
Blackwelder, P.L. 1399, 2207
Blair. W. 1036
Blake, N.J. 1400
B1anc-Livni, N. 1401
Blankenship, M. L. 1402
B1ankenstein, E. 1014
B1aska, J. 60
Blaustein, M.P.
1394
1857
57
58
1395
31, 32, 33,
61, 629
B1axter, J.H.S. 246, 247
Blaylock, B.G. 873, 874
Bleiler, E.L. 877
Blick, R.A.P. 553
Bligh, E.G. 630, 2173
Blinn, O.W. 2154
Blum, H.F. 1403
Bobenrieth, P.
Bodansky, M.
Boetius, J.
Bogan, M.B.
Bohlen, W.F.
Bohm, E. L.
Bohn, A.
Bolter, E.
Bombowna, M.
Boney, A.D.
Bonham, K.
Bonin, O.J.
Boon, D.O.
Booth, R.S.
Boothe, P.N.
Borght, a.v.
Born, J. W.
711
62, 1404, 2030
63
1566, 1567
731
1405, 1406, 2179
1407, 1408
1275
64
1409, 1410, 1411
2208
1381
631
2177
632
65, 66
1412
455
-------
Bowen, E.S.
Bowen, V.T.
Bowles, M.E.
Boyce, R.
Boyden, C.R.
Boyle, P.J.
Bradley, H.C.
Bradshaw, J. S.
Brady, O.L.
Braek, G.S.
Brafield, A.E.
Braham, H.W.
Braman, R.S.
Branca, G.
Brandt, O.J.
Bransford, M.E.
Brar, 8.8. 209
Breck, W.G. 1753
Brenko, M. H. 1422
Brenner, F.J. 1423
Brereton, A. 637
Breuer, F. 636
Briese, L.A. 1424
Bright, T.J. 2137
Brinckman, F.E. 1036
Bringmann, G. 1425
Brinkman, F. G. 1196
Brisbin, 1. L. 2079
Brock, O.W. 1374, 1375, 1376
Brock, T.O. 1426
Broenkow, W.W. 1860
Brooks, R.R. 638, 639, 640, 867,
1427
1603
641
1428
642, 1429
73
Jr.
1253
Boroughs, H.
Boschetti,
Batt, T. L.
Bougis, P.
Boulton, P.
Bovard, P.
Broquet, O.
Brouse, 0.0.
Brown, B.
Brown, B.E.
Brown, O.J.
Brown, G. W. ,
Brown. H.G.
67,68,69,633,
1413, 1414, 2055
70
M.M.
1433
71
634
582, 583, 584, 1320,
1659
1311
1039. 1758
74
72, 240
1415, 1416, 1417
1418
1419, 1887, 1888
1989
2118
1420
998, 1421
635
1735
636
1285
2120
1346, 1869
Brown, H.R.
Brown, J.H.
Brown, T.E.
Brown, V.M.
Brule, G.
Brungs, W.A.
Brunker, R.L.
Bryan, G.W.
Buckney, R.T.
Buddemeier, R.W.
Bugelski, Y.Y.
Buhler, O.R.
Buikema, A.L.
Buikema, A. L. ,
Burdick, G.E.
577
74
763
75,76,77,78,
643, 644, 1170,
1430~ 1431, 2075,
2138
645
79, 80, 81, 646
693, 1432
1433
82, 83, 84, 85, 86,
87,88,647,648,
649, 650, 651, 652,
653, 812, 1201,
1434, 1435, 1436,
1437, 1438
2166
931
89
1439
2123
Jr. 1440, 2122
90, 972, 1065,
1066, 1067, 1218
724
1441
1477
Burg, A.W.
Burkett, R.O.
Burkholder, P.R.
Burns, C. W. 1499
Burovina, I. V. 1442
Burres, O. 1970
Burrows, W.O. 654
Burton, O.T. 655, 656, 660
Burton, J.O. 951, 952, 1443
Burton, R.F. 1444
Buszman, A. 1799
Butters, K.M. 724
Butterworth, J. 1445
Button, O.K. 657
Buyanov, N.l. 1446
Byrne, A.R. 936, 1790
Byrne, J.M. 658
Cabej szek, l,
Cable, W.O.
Cahn, P.H.
Cain, T.O.
Caines, L.A.
456
91, 92
2150
1482
659
1447
-------
Cairns, J.
Cairns, J.J.
Cairns, J., Jr.
93, 94, 95, 96, 98
97
48, 99, 394,
655, 656, 660,
661, 662, 663,
664, 665, 666,
667, 668, 669,
1191, 1192, 1193,
1251, 1252, 1373,
1440, 1448, 1449,
1450, 1451, 1465,
1665, 2043, 2123
670, 671, 1422,
1452, 1453, 1910,
2151
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Woh1sch1ag,
Wolf, H.W.
Wolfe, D.A.
1540
804, 1275
555, 2223
556
D.E.
366
577, 1156, 1276,
1277, 1278, 1279,
1580, 2224, 2225
926
Wolkoff, F.D.
Wollast, R.
Wong, C.C.
Wong, K.M.
1146
1394
786
1280, 1281, 1925,
1927
Wong, P.T.S. 1463
Wood, J.M. 1282, 2226
Wood, R.A. 558
Woodhead, D.S. 2227
Woodle, C. 2120
Wooldridge, C.R.
Wooldridge, D.P.
Word, C.S. 1941
Word, J.Q. 2014
Wort, D.J. 2228
Wrenn, M.E. 928
Wright, D.A. 2229
Wright, F.S. 2118
Wright, T.D. 1285
Wrobe I, S. 64
Wuite, T.P. 2116
Wurtz, C.B. 2230
1283, 1284
1283, 1284
Yager; C.M.
Yamada, K.
Yamada, M.
Yamaguchi, N.
Yamamoto, J.
Yamamoto, S.
Yamamoto, T.
559, 560
2162
2155
294
1867
269
885, 1601, 1721,
1722, 1723, 1724,
2231
Yamamoto, Y. 2232
Yamanaka, S. 2233
Yamaoka, T. 2231
Yamazi, I. 1601
Yasutake, W. T. 11
Yevich, P.P. 191, 753, 808,
1391, 2187
Yoh , L .
Yokote, M.
Yoshida, T.
Yoshimura, A.
Yoshinari, T.
Young, D.R.
903
996
870
2234
2235
561, 562, 783, 784,
785, 865, 1286,
1309, 1873, 2236,
2237
485
-------
Young, E.G.
Young, L. G .
Young, M. K.
Young, ~1. L.
Young, O.R.
Young, R.G.
Youngs, W.D.
Yousef, Y.A.
Yudkin, J.
2238
1287
303
2289
176
947, 1006, 1288
972, 1219
818
563
Zabarunova, I.S. 387
Zaitsev, Y.P. 417, 1100
Zakhary, R. 244
Zaroogian, G.E. 755, 2240
Zattera, A. 54, 1382
Zavodnov, S.S. 546
Zaystev, V.F. 2184
Zegers, C. 730
Zeitoun, I.H. 2241, 2242, 2243
Zei toun, M. A. 1289
Ze1enko, V. 936
Zender, S.T. 1730
Zesenko, A.Y. 565
Zimmermann, U. 1290
Zitko, P. 1291
Zitko, V. 1292, 1555, 2244,
2245, 2246
Zlobin, U.S. 566
Zlochevskaya, I.V.
Zorn, M. 1468
567
486
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.
TECHNICAL REPORT DATA
(1'1/'11.11' rcod "u.1rlll'lio/l.~ Oil 111(' r(')'('rs(' befor(' CUIIlI"l'liIlX)
1. F1I2I'OHI NO. /1 3. RECIPIENT'S ACCESSIOllrNO.
EPA-600/3-78-005
4. TIT LEA N [) S lJ LJ r 11 L E 5. REPORT DATE
Third Annotated Bibliography on Biological Effects of .T anUiUY 1978
Metals in Aquatic Environments [No. 1293-2246]. 6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S) 8. PERFORMING ORGANIZATION REPORT NO.
Ronald Eisler, Daniel J. O'Neill, Jr., and
Glen W. Thompson
9. PE RFORMING ORG '\NIZATION NAME AND ADDRESS 10. PROGRAM ELEMENT NO.
Environmental Research Laboratory - Narragansett, RI IBA022; ROAP task No. l6AAT/3l
Office of Research and Development 11. CONTRACT /G RANT NO.
U.S. Environmental Protection Agency
Narragansett, Rhode Is 1 and 02882
1:1. SPONSORING AGENCY NAME AND ADDRESS 13. TYPE OF REPORT AND PERIOD COVERED
In-house
Same as above 14. SPONSORING AGENCY CODE
EPA/600/05
15. SUPPLEMENTARY NOTES
16. ABSTRACT
Titles of 954 technical articles are listed on the subject of toxicological,
physiological and metabolic effects of stable and radio-labelled chemical species
of metal cations to marine, estuarine and freshwater flora and fauna. Each
reference was annotated and subsequently indexed by metal, by taxa, and by
author, in cumulative indices which encompass this volume and the initial volumes
in this series (Eis ler, R. 1973. Annotated bibliography on biological effects
of metals in aquatic environments [No. 1-567]. U.S. Envir. Proto Agen. Rept.
R3-73-007: 287 pp; Eisler; R. and M. Wapner. 1975. Second annotated bibliograph
on biological effects of metals in aquatic environments [No. 568-1292]. U.S.
Envir. Proto Agen. Rept. 600/3-75-008: 400 pp).
17. KEY WORDS AND DOCUMENT ANALYSIS
J. DESCRIPTORS b.IDENTIFIERS/OPEN ENDED TERMS C. COSATI Field/Group
Fishes, Cations, Salinity, Metals, Aquati Aquatic invertebrates, 6F
animals, Water pollution, Toxicity, Aquatic vertebrates, 8A
Metabolism, Bibliographies, Radioactive Heavy metals, Trace 8H
isotopes metals, Elemental l3B
composition
18. UISTRII:!UTION STATEMENT 19. SECURITY CLASS (This Report) 21, NO. OF PAGES
Pub Ii c !In r 1 . ,... po! 493
Re lease to 20. SECURITY CLASS (This page) 22. PRICE
Unclassified
EPA Form 2220.1 (9-73)
487
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