&EPA
United States
Environmental Protection
Agency
Environmental Research
Laboratory
Narraoansett Rl 02882
EPA-600 3-79 084
August 1979
Research and Development
Fourth Annotated
Bibliography on
Biological Effects of
Metals in Aquatic
Environments
(No. 2247-3132)
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Resean: h reports oi the Of tic e oi Resedicli ai id Developmei ii, tj S Environmental
Protection Agency, have been grouped mio nine series Fhese nine broad cate-
gories were established to lacihlale iuriher development and application of en-
vironmental technology Elimination of iraditiona grouping was consciously
planned to foster technology Iranstei and a maximum interface in related fields
The nine series aie1
1 Environmental Health Effects Research
2 Environmental Protection Technology
3 Ecological Research
4 Environmental Monitoring
5 Socioeconomic Environmental Studies
6 Scientific and Technical Assessment Reports (STAR)
7 Interagency Energy-Environment Research and Development
8 "Special" Reports
9 Miscellaneous Reports
This report has been assigned to the ECOLOGICAL RESEARCH series This series
describes research on the effects of pollution on humans, plant and animal spe-
cies, and materials. Problems are assessed for their long- and short-term influ-
ences Investigations include formation, transport, and pathway studies to deter-
mine the fate of pollutants and their effects. This work provides the technical basis
for setting standards to minimize undesirable changes in living organisms m the
aguatic, terrestrial, and atmospheric environments
s available io [he public through the National Technical Informa-
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EPA-600j3-79-084
August 1979
FOURTH ANNOTATED BIBLIOGRAPHY ON BIOLOGICAL EFFECTS OF
METALS IN AQUATIC ENVIRONMENTS
(No. 2247-3132)
by
Ronald Eisler, Richard M. Rossoll,
and Gloria A. Gaboury
Office of Health and Ecological Effects
Environmental Research Laboratory
Narragansett, Rhode Island 02882
ENVIRONMENTAL RESEARGI LABOAATORY
OFFI CE OF RESEARGI AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
NARRAGANSETT, RHODE ISLAND 02882
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DISCLAIMER
This report has been reviewed by the Environmental Research
Laboratory-Narragansett, U.S. Environmental Protection Agency,
and approved for publication. Mention of trade names or
commercial products does not constitute endorsement or recom-
mendation 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 account lists 886 titles of selected articles from the
available 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. 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 soun~ data base in updating of existing water
quality criteria for metals in freshwater and marine
environments.
iii
aId K. Phelps
Acting Director
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ABSTRACT
Titles of 886 technical articles are listed on the subject
of toxicological, physiological and metabolic effects of stable
and radiolabelled chemical species of metal cations to marine,
estuarine and freshwater flora and fauna. Almost all of these
articles were published in the two-year period 1977-1978. Each
reference was annotated at length and subsequently indexed by
metal, by taxa, and by author. The first three volumes in this
series, published as U.S. Environmental Protection Agency
Reports R3-73-007, 600/3-75-008, and 600/3-78-005, respectively,
are available from the National Technical Information Service,
Springfield, Virginia 22161.
iv
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Foreword
Abstract
Acknowledgments
III.
I.
Introduction
II.
References
Index
CONTENTS
iii
iv
vi
3
434
v
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ACKNOWLEDGMENTS
We are obligated to Ms. Rose Ann Gamache, Librarian at the
Environmental Research Laboratory/Narragansett, and her
assistant Ms. Karen Gardner, for their efforts in procuring some
of the original articles for consultation through interlibrary
loan and other sources. Personnel from the Computer Sciences
Corporation, especially Dr. John Greaves, Dr. Lawrence Rossner,
Mr. David Sleczkowski, Mr. John Rossell, Mr. Michael Bigbee, Ms.
Dale Ritchie and Mrs. Barbara Gardiner provided computerized
indexing services and a word-programmer retrieval system. We
are also grateful to Mr. Danny Wapner for technical assistance
in early phases of this project, and to Mr. Raymond J. Hennekey
for his editorial assistance.
vi
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SECTION I
INTRODUCTION
~ was true in the three preceding volumes in this
series, the present account lists journal articles and
reports resulting from lab ora tory and fie] d investigations on
toxicological, physiological and metabolic effects of stable and
radioacti ve species of heavy metals and other cations to aquatic
life. Almost all of the references annotated in this fourth
volume were published within the two year period 1977-1978, but
some 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; bioaccumulation; 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, modifying
effects of biotic 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 adudnistratively at
levels which nei ther jeopardize the stabili ty of aquatic
ecosystems nor present a public health hazard via aquatic food
chains.
*Eisler, R. 1973. Annotated bibliography on biological
effects of metals in aquatic environments (No. 1-567). U.S.
Environmental Protection Agency Report R3-73-007:287 pp.
Available from U.S. Department of Corrmerce, National Technical
Information Service, Springfield, Virginia 22161, as Order .No.
PB-228-211 at a current price of $11.00.
Eisler, R. and M. Wapner. 1975. Second annotated bibliography
on biological effects of metals in aquatic environments (No.
568-1292). U.S. Environmental Protection Agency Report
600/3-75-008:400pp. Available from U.S. Department of Commerce,
National Technical Information Service, Springfield, Virginia
22161, as Order No. PB-248-211 at a current price of $13.25.
Eisler, R., D.J. O'Neill, Jr., and G.W. Thompson. 1978. Third
annotated bibJiography on biological effects of metals in
1
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aquatic environments (No. 12a~-2246). U.S. EnvironmentaJ
Protection Agency Report 000/3-18-005:487 pp. Available from
U.S. Department of Commerce, National Technica1 Information
Service, Springfield, Virginia 22161, as Order No. PB-280-953
at a current price of $15.00.
2
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SECTION II
REFERENCES
Each reference is numbered and subsequently indexed by
metal( s), by taxonomic group ( s) and by author( s) in the INDEX
SECTION Section III. Copies of all articles cited in this
volume, as well as the first three volumes in this series, are
on file with the Librarian, U.S. Environmental Protection
Agency, Envi rrnmental Research Lab ora tory, Narrap;ansett, RI
02882, and available for consultation at that location.
3
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2247 .
Abbott, O.J. 1977. The toxicity of anmonium molyhdate
to marine invertebrates. Marine Poll. Bull.
8:204-205.
Toxicity of anmonium molybdate, a constituent of some
industrial wastes, to hermit crab Eupagurus bernhardus, crab
Carcinus maenas, clam Venerupis pullastra, and starfish Asterias
rubens was investigated under conditions of 12-21 C and
23.5-33.2 0/00 S. The LC-50 (48 hr) value for Carcinus was >254
mg Moll in pH 7.0, and 1018 in pH about 5.0. The LC-50 (24 hr)
for Eupagurus ranged between 127 and 254 mg Moll in pH 5. 1-7 = 3;
LC-50 (48 hr) values varied between 191 and 254 mg/l in pH
7.0-7.8. The LC-50 (24 hr) value for Asterias was between
127-254 mg Moll in pH 5.1-8.2 and between 254-509 mg/l in pH
5.1-6.2 for Venerupis. A 50 day chronic experiment of 100 mg
Moll produced no mortality in Eupagurus. It was concluded that
even where hydrolysis produced a reduced pH, which possibly
facilitates toxicity in acute tests, ammonium molybdate was
comparatively nontoxic to marine invertebrates.
2248 .
Abernathy, A.R. and P.M. Cumbie. 1977. Mercury
accumulation by largemouth bass (Micropterus
salmoides) in recently impounded reservoirs.
Environ. Contamin. Toxicol. 17:595-602.
Bull.
Mercury concentrations in axial muscle of bass from
South Carolina in 1973 and 1974 ranged from 0.38 to 0.68 mg/kg
wet wt in Lake Harwell, 0.34 to 3.99 in Lake Keowee, and 1.89 to
4.49 in Lake Jocassee. Levels generally increased as size class
of fish increased from <230 to >380 rom. In 1974, Hg
concentration in axial muscle of 231-340 rom bass from Lake
Jocassee was 1.9 mg/kg wet wt; in 1975, levels averaged 0.69.
In Lake Jocassee, water Hg levels were <0.01 to 0.06 ug/l, and
sediment Hg levels were 0.03 to 0.04 mg/kg dry wt. In
tributaries entering the lake, Hg concentrations were < O. 1 to
0.12 ug/l in water, 0.01 to 0.05 mg/kg dry wt in sediment, and
1.3 to 14.0 mg/kg dry wt in suspended sediment load. Authors
suggest that elevated Hg levels in fish are a transi tory
phenomenon in newly impounded reservoirs, and decline as
reservoirs age. Source of Hg appears to be soil which formed
the oriRinal reservoir sediments.
2249 .
Al-Daham, N.K. and M.N. Bhatti. 1977. Salinity
tolerance of Gambusia affinis (Baird & Girard) and
Heteropneustes fossilis (Bloch). Jour. Fish Biology
11 : 309- 313.
4
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Two species of freshwater teleosts exposed to
concentrations of seawater and sodium chlori de, calchun
chloride, and potassium chloride showed a high tolerance to
seawater and NaCI, and 100 tolerance to KCl. Sodium chloride at
10,000 mg/l had no effect on either species. In 15,000 mg
NaCl/I, 75% of Gambusia died by 144 hrs; all Gambusia died at 72
hrs in 20,000 mg/l. For Heteropneustes, all were dead in 48 hrs
at 15,000 mg/l NaCl, or 8 hrs in 20,000 mg/l. No Gambusia died
in 25% SW; 10% died by 144 hrs in 50% SW; and all died by 24 hrs
in 75% SW. After 144 hrs, 25% of Heteropneutes in 25% SW were
dead; all died by 24 hrs in 50% SW or 8 hrs in 75% SW. In
CaCl2 for 144 hrs, 10% of the Gambusia died in 5,000 mg/l and
83% in 10,000 mg/1; all were dead in 24 hrs at 15,000 mg/l
CaCI2' For Heteropneustes, 70% died after 144 hrs in 5,000
mg/l CaCI2; all were dead by 24 hrs in 10,000 and by 8 hrs in
15,000 mg/l. Total mortality was seen at 48 hrs in 5,000 and
10,000 mg KCI/I and at 8 hrs in 15,000 mg/l for Gambusia, and at
72 hrs, 24 hrs, and 8 hrs with increasing KCI for
Heteropneustes. In all cases, Gambusia were more resistant to
salt concentrations than Heteropneustes.
2250.
Anderson, R.V. 1977. Concentration of cadmium, copper,
lead, and zinc in thirty-five genera of freshwater
macro invertebrates from the Fox River, Illinois and
Wisconsin. Bull. Environ. Contamin. Toxicol.
18: 345- 349.
Nineteen species of aquatic insects contained from
<0.5 to 6.3 mg cadmium/kg dry wt, <1.0 to 74.2 copper, <4.0 to
39.5 lead, and 75.5 to 270.8 zinc. Five species of crustaceans
contained <0.5 to 2.8 mg Cd/kg dry wt, 70.7 to 99.2 Cu, < 4.0 to
25.7 Pb, and 64.7 to 124.9 Zn. Ten species of molluscs
contained from 1.4 to 3.0 mg Cd/kg dry wt, 5.2 to 22.0 Cu, 10.2
to 32.0 Pb, and 3.7 to 353.0 Zn. Two species of hirudinean
annelids had from <0.5 to 3.8 mg Cd/kg dry wt, 7.6 to 16.8 Cu,
<4.0 to 39.8 Pb, and 136.2 to 148.4 Zn. There was a wide range
of values with individual taxa, but the general pattern was Cd <
Cu < Pb < Zn, except in crustaceans where it was Cd < Pb < Cu <
Zn.- High Cu concentrations in crustaceans is believed to be dUe
to Cu pigment in hemocyanin. Zinc was especially high in most
bi valve molluscs, gastropods and several species of insects, and
this may reflect a physiological need for Zn.
2251 .
Anderson, R.V.
1977 .
Concentration of cadmium, copper,
5
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lead, and zinc in six species of freshwater clams.
Bull. Environ. Contamin. Toxicol. 18:492-496.
Concentrations of Cd, Cu, Pb, and Zn were determined
in Lampsilis siliquoidea, L. ventricosa, Strophitis rugosus,
Sphaerium sp., Anodonta marginata, and Lasmigona complanata from
Fox River, Illinois and Wisconsin. Shells of the six clams had
concentrations of 1.2 to 3.7 mg/kg dry wt of Cd, 3.4 to 10.Q of
Cu, 9.2 to 33.0 of Pb, and 3.7 to 11.7 of Zn. Body levels in ~
siHquoidea, L. ventricosa, S. rugosus, and Sphaerium sp. ranged
from 2.5 to 5-:9" mg/kg dry wt for Cd, 7.4 to 22.4 for Cu, 17.6 to
48.2 for Pb, and 130.0 to 319.9 for Zn. In ~ marginata and ~
complanata, concentrations in muscle, gills, and viscera ranged
from 0.4 to 4.8 mg/kg dry wt for Cd, 2.2 to 12.9 for Cu, 1.9 to
24.9 for Pb, and 22.1 to 420.7 for Zn. In only two instances,
Cd for Sphaerium sp. and L. complanata, were shell levels higher
than body levels for a metal. With the exeption of high Zn
values, metal levels in the bodies reflected sediment
concentrations.
2252.
Andrew, R.W., K.E. Biesinger, and G.E. Glass. 1977.
Effects of inorganic complexing on the toxicity of
copper to Daphnia magna. Water Research 11:309-315.
Effects of carbonate-bicarbonate, orthophosphate, and
pyrophosphate on copper toxicity, at concentrations up to 0.127
mg Cull, to Daphnia were studied at constant pH and total
hardness. Mortality rates ~d reciprocal survival times were
directly correlated with Cu + and copper hydroxy ion ~u(OH)nJ
activities as determined by equilibrium calculations. Toxicity
was negatively related to activities of soluble CuC03 and
other comp1exes, and independent of dissolved Cu or total Cu
concentrations.
2253.
Atchison, G.J. 1975. Uptake and distribution of trace
metals in fish. Office of Water Resources Research
Project No. A-038-IND. Technical Report No. 73.
Purdue Univ. Water Res. Res. Cent., West Lafayette,
Indiana: 21 pp.
Bluegill Lepomis macrochirus, largemouth bass
Micropterus salmoides, and golden shiners Notemigonus
6
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crysoleucas, from Palestine Lake, Indiana, the recipient of
wastes from a metal plating shop, were analyzed for cadmium and
chromium in 1975. Muscle from bluegill and bass contained 0.08
to 3.7 mg Cd/kg dry wt, with a high of 16.0 mg/kg, and 0.04 to
8.4 mg Cr/kg dry wt. In gill tissue values were 0.1 to 6.9 for
Cd and 0.5 to 15.0 for Cr; in Jiver 1.0 to ~3.4 for Cd and 0.3
to 45.0 for Cr; and in gastrointestinal tract 0.10 to 51.6 for
Cd and 0.2 to 75.5 for Cr. Whole body concentrations in shiners
were 0.68 to 0.79 mg Cd/kg dry wt and 2.'5 to 3.7 mg Cr/kg dry
wt. Water from Palestine Lake contained 0.03 to 0.05 mg Cd/l
and 0.005 to 0.01 mg Cr/l near the waste water entrance, and
0.001 to 0.002 mg Cd/I and 0.001 to 0.009 Cr/l in other areas.
Sediments near the waste entrance contained 640 to 1300 mg Cd/kg
dry wt and 2080 to 3830 mg Cr/kg dry wt; elsewhere in the lake
these values ranged from 6 to 200 mg Cd/kg and 90 to 1000 mg
Cr/kg.
2254.
Badsha, K.S. and M. Sainsbury. 1977. Uptake of zinc,
lead and cadmium by young whiting in the Severn
Estuary. Marine Poll. Bull. 8: 164-166.
First year whitings, Merlangus merlangus, from
cooling water intakes of Oldbury Nuclear Power Station, Severn
Estuary, England, had maJdmum levels of zinc in November 1975
and maximum lead and cadmium in March 1976. Metal
concentrations from Nov. 1975 to Mar. 1976 ranged from 72.5 to
102.4 mg Zn/kg dry wt, 16.7 to 21.2 mg Pb/kg, and 1.9 to 2.5 mg
Cd/kg. These levels were linearly related to both length and
weight of fish, positively with Pb and Cd, but negatively with
Zn. It was suggested that Zn concentrations reached an upper
threshold limit with no further accumulation; this was quickly
attained as fish moved into polluted areas.
2255.
Bagnyuk, V.M., T.L. Oleynik, N.R. L'vovskaya and L.O.
Eynor. 1976. Extraction of iron from water by
Chlorella vulgaris and Scenedesmus quadricauda.
Hydrobiological Jour. 12:35-41.
Freshwater chlorococcol algae Chlorella and
Scenedesmus accumulated large quanitites of iron from water
containing 1.0 to 370.0 mg Fe/I. Biological Fe utilization
follows tTrX) pathways: uptake of Fe ions by algal cells; and
precipitation as iron hydroxide owing to increases in pH and
7
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oxygen of the medium. In the presence of mixed algal-bacterial
cultures, Fe is oxidized in water, with initial pH 5.5: U~take
of Fe by algae is a direct function of iron concentratIon In
culture medium. Utilization of Fe by algal cells alters the
ratio of hydrolyzed to non-hydrolyzed forms in cells with 80-90%
of the Fe accumulated converted to a non-hemin form. Authors
suggest that ability of algae to promote Fe oxidation, fol~owed
by precipitation as hydroxide, plus ability to accumulate Iron
in large quantities can be used in metallurgical plants for
biological removal of iron from effluents.
2256.
Bakunov, N.A. and S.N. Garanina. 1976. Accumulation of
90Sr and 137Cs by marine and freshwater fish of
the Caspian Basin. Soviet Jour. Ecology 7(4):350-353.
Radionuclide levels were determined in 10 species of
freshwater teleosts: crucian carp Carassius carassius, bream
Abramis brama, perch Perca fluviatilus, pike perch Lucioperca
lucioperca, northern pike Esox lucius, tench Tinca tinca, asp
Aspius aspius, rudd ScardinIUS erythrophthalmus, ide Leuciscus
idus, carp Cyprinus carpio; 5 species of anadromous teleosts
during freshwater migration phase: Caspian roach Rutilus
rutilus, kutum R. frisii, black-spined shad Caspialosa kessleri,
Caspian shad C.-caspia; and two marine species: sprats
Clupeonella engrauliformis, !;. grimmi. In the Volga and Ural
Deltas in 1969, 1971, and 1972, the maximum Sr-90 concentrations
in freshwater fishes, in mCi/kg wet wt x 10-Q were 151 in
carp, 146 in black-spined shad, and 102 in ide. Maximum Cs-137
levels were 55 to 71 x 10-9 mCi/kg wet wt in pike perch and 62
x 10-9 in asp. Black-spined shad, ide, and crucian carp had
Sr-90/Cs-137 values of 12.2, 11.3 and 6.7 respectively; for all
other species this ratio was <4.0. Maximum concentrations of
Sr-90 in marine fishes from the Caspian Sea in 1972 were 36 x
10-9 mCi/kg wet wt in carp and 33 x 10-9 in R. frisii.
Cs-137 was highest in shad at 156 x 10-9 mCi/kg wet wt. R.
frisii and carp had Sr-90/Cs-137 values of 1.7 and 1.4, -
respectively; the rest were <1.0. The relationship between type
of nutrition and radionucHde level is discussed.
2257 .
Banus, M.D. 1977. Copper, iron, and manganese content
of mangrove seedlings from Puerto Rico. In:
Drucker, H. and R.E. Wildung (eds.). Biological
implications of meta] s in the environment. ERDA
Symp. Sere 42:380-389. Avail. as CONF-750929 from
8
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Nat. Tech. Inf. Serv., U.S. Dept. Comm. Springfield,
VA 22161.
Seedlings of red mangroves, Rhizophora mangle from 6
locations in Puerto Rico with varying amounts of chemical
polluticn, were analyzed for iron, manganese, and copper.
Copper concentrations of seedlings from unimpacted areas were
2.3 to 3.5 mg/kg dry wt, with no difference between leafing
(top) and rootlng (bottom). In locations subjected to thermal,
air, and chemical pollution, sewage, and agricultural runoff,
concentrations ranged from 4.1 to 7.2 mg Cu/kg. Iron levels
were 8.6 to 25.0 mg/kg dry wt in tops and 11.3 to 22.7 in
bottoms from all sites. Estuarine mangroves in unpolluted areas
contained 30.0 to 42.6 mg Mn/kg dry wt in tops and 10.2 to 11.0
in bottoms; seedlings from an offshore island had 10.3 mg Mn/kg
in tops and 3.7 in bottoms. From polluted areas, Mn levels
ranged from Z7. 0 to 80.0 mg/kg dry wt in tops and 7.4 to 18.9 in
bottoms. Top to bottom Mn ratios were 2.7 to 4.2 for seedlings
from all areas.
2258.
Barlow, D.J. and W.S.G. Morgan. 1975. Energy dispersive
X-ray analysis (EDAX) as an autopsy technique for
copper-caused fish mortality. Water SA 1(3):109-112.
Energy dispersive analysis of X-rays (EDAX) was used
to indicate copper toxicity in the freshwater fish Sarotherodon
mossambicus after exposure to 5, 10, and 20 mg/l copper
sulphate. Copper absorption, relative to calcium content in
liver, gill and operculum after exposure to 5 mg Cull (control),
respectively was: 0.027 (0.007) in liver; 0.009 (0) in gill;
and 0.0022 (0) in operculum. For the 10 mg Cull group the Cu/Ca
ratios were: 0.019 for liver; 0.021 for gill; and 0.0002 for
operculum. Fish exposed to 20 mg Cull exhibited Cu/Ca ratios of
0.019 for liver; 0.021 for gill; and 0.0003 for operculum. Mean
death time of fi.sh exposed to 5 mg Cull was 384 min; and for
fish in 20 mg Cull 91 min. Copper, as a cause of mortality
could be detected up to 48 hrs after death. It is probable that
the technique is not specific for copper toxicity but could be
used for other metal toxicants in dead fish including
phosphorus, lead, iron and zinc.
2259 .
Barnes, D.J. and C.J. Crossland. 1977. Coral
calcification: sources of error in radioisotope
9
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techniques.
Marine Biology 42:119-129.
Isotopic exchange occurs between coral skeleton Ca-45
and HC-14 03-in seawater. Exchange of C-14 onto skeletons
is more rapId than exchange of Ca-45. Exchange of C-14 from
skeletons to seawater takes place more slowly than exchange of
Ca-45 to seE-water. An increase in temperature increases percent
of radioactivity exchanged onto skeleton. When Acropora
acuminata is incubated in the dark with Ca-45 C12, NaHC-14
03' and C-14 urea for 1 hr, tissues contained more
radioactivity than is associated with skeleton. Tissue
radioactivity reflects permeation of tissues and coelenteron by
radioactive compounds from the incubation seawater. Specimens
pre incubated with 5mM ZnC12 and other metabolic inhibitors
incorporate more Ca-45 hut less C-14 than specimens in filtered
seawater. Addition of alkali, KOH, and two brands of domestic
bleach, to radioactive seawater results in a radioactive
precipitate, part of which becomes associated with any coral
skeletm present, and part of which forms on the wall of the
containing vessel. Strong alkali removes biologically-deposited
radioisotope from coral skeletons. Deposition of C-14 from
HC-14 0iin skeletons of living coral incubated in the dark
is greater than in dead coral. The reverse situation occurs
with Ca-45.
2260.
Basiouny, F.M., L.A. Garrard, and W.T. Haller. 1977.
Absorption of iron and growth of Hydrilla
verticillata (L.f.) Royle. Aquatic Botany 3:349-356.
Tissue levels of iron and chlorophyll in Hydrilla
plants increased as FeEDTA levels in the nutrient solution
increased from 0 to 6.0-8.0 mg/l; however, plant values
decreased in water containing 8.0 to 15.0 mg Fell. Maximum
tissue Fe concentratim was 22,000 mg/kg wet wt after 7 weeks in
6.0 mg Fell solution; Hydrilla absorbed and accumulated more Fe
than was required for optimum growth; growth was greatest in 8.0
mg Fell solutions. Manganese concentrations decreased from 450
to 150 mg/kg wet wt as Fe content in solution increased from 0.0
to 15.0 mg/l. Best growth and highest dry weight of Hydrilla
were obtained at a comparatively high Fe/Mn ratio of 85.
10
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2261.
, / /
Baud in, J.-P. 197q. Premieres donnees sur l'etude
experimentale du cycle du zinc dans l' 8'tang de
l'Olivier. Vie Milieu 2q(1) Ser. B:59-~0.
Zinc-65 transfer from marine lagoon waters to
sediments at 5, 15 and 25 C was measured over a period of ~
days; sediment Zn-65 levels were highest at 25 C and lowest at 5
C. Cladophora sp. of algae concentrated radiozinc from the
medium by factors of 5qO (initial Zn-65 in medium 995 d/m/ml, 12
day study, 5 C), 36q7 (initial Zn-65 530 d/m/ml, 3q day study, 5
C), 1350 (910 d/m/ml, 12 days, 15 C), q6~0 (q75 d/m/ml, 3q d, 15
C), 17~5 (~5 d/m/ml, 12 d, 25 C) and q212 (~5 d/m/ml, 3q d, 25
C). Data are also presented on elimination rates. Radiozinc
transfer through a food chain from labelled Cladophora to a
gastropod Physa acuta, and from Cladophora to an isopod
Sphaeroma hookeri, was also determined. For both predator
species, accumulation was most rapid during the first 10 days of
a 30 day study.
2262.
Bayley, LL. and E.A. Freeman. 1977. Seasonal
variation of selected cations in Acorus calamus L.
Aquatic Botany 3:b5~q.
Seasonal differences in K, Ca, Mg, Mn and Na were
studied for the freshwater emergent macrophyte, Acorus calamus,
collected fram a flood plain in Ontario, Canada. A moderate to
high correlation was found between time of year and magnesium
and manganese concentrations in above ground organs;
concentrations ranged from 2,200 mg Mg/kg dry wt in June to ~OO
in August; and from 1qO mg Mn/kg dry wt in June to 20 in
September. Both Mg and Mn in underground organs were poorly
correlated with season: for Mg, values ranged from 600 mg/kg
dry wt in June to 120 in September; for Mn, it ranged from 160
mg/kg dry wt in June to almost zero in September. Calcium
concentration in above ground organs ranged, in mg/kg dry wt,
from 13,000 in September to 300 in July; subsurface organ values
were ~OO in June, to 300 in October (the latter showed a
moderate correlation between time of year in both above and
underground organs). Potassium values in above ground organs
ranged from Jili,OOO mg/kg dry wt in June to ~OO in October; for
sodium in underground organs these were ~OO mg/kg dry wt in June
to 150 in September.
11
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22b3.
Bebbington, G.N., N.J. Mackay, R. Chvojka, R.J. Williams,
A. Dunn and E.H. Auty. 1977. Heavy metals, selenium
and arsenic in nine species of Australian commercial
fish. Austral. Jour. Marine Freshwater Res.
2tj:277-2tjb.
Mean metal levels in nine species of important
commercial fish from New South Wales waters were: 0.03 to 0.3tj
mg/kg wet wt for mercury, mainly as methyl Hg, 0.04 for cadmium,
0.04 to 0.tj7 for copper, 0.4 to 0.7 for lead, 4.2 to 9.b for
zinc, 0.2 to 2.2 for arsenic, and 0.2 to 0.5 for selenium. All
except one of the 232 fish analyzed had metal concentrations
belCM the National Health and Medical Research Council (NHMRC)
standards of 2.0 mg/kg wet wt for Cd, 30.0 for Cu, 2.0 for Pb,
2.0 for Se, and 1000 for Zn. Specimens of bream Acanthopagrus
australis, snapper Chrysophrys auratus, mulloway Sciaena
antarctica, kingfish Seriola grandis, Australian salmon Arripis
trutta, and yellowfin tuna Thunnus albacares, accounting for 7%
of the total sample, had Hg concentrations in excess of the
NHMRC standard of 0.5 mg/kg wet wt. No sea mullets Mugil
cephalus, flatheads Platycephalus fuscus, or tailors Pomatomous
saltatrix, exceeded this limit. Twenty-one percent of 95 fish
analyzed had As concentrations equal to or greater than the
standard of 1.14 mg/kg. Health risks associated with Hg and As
in these species are discussed.
22b4.
Beckett, J.S. and H.C. Freeman. 1974. Mercury in
swordfish and other pelagic species from the western
Atlantic Ocean. In: U.S. Dept. Conmerce, NOAA Spec.
Sci. Rept. (Fisheries) No. b75:154-159.
Mean mercury content in dorsal muscle of 1 b species
of fishes and elasmobranchs, in mg/kg wet wt were: swordfish X.
gladius 1.15; bluefin tuna Thunnus thynnus O.tjO; white marlin--
Tetrapturus albidus 1.34; escolar Lepidocybium flavobrunneum
O.b2; dolphin Coryphaena hippurus O.tjb; long nose lancetfish
Alepisaurus ferox O.Otj; blue shark Prionace glauca 0.70; sickle
shark Carcharhinus falciformis 1.43; dusky shark C. obscurus
2.0tj; tiger shark Galeocerdo cuvieri 0.tj3; hamnerhead shark
Sphyrna lewini 3.b4; mako shark Isurus oxyrinchus 1.1b;
porbeagle shark Lamna nasus 0.55; mackerel shark 2.0~; white
shark Carcharodon carcharias 1tj.tj5; and basking shark Cetorhinus
maximus O.Otj. Total mercury content in food species taken from
12
-------
stomachs of swordfish in mg/kg wet wt were: butter fish
Centrolophus niger 0.1~; scaled dragonfishes Stomias boa 0.17;
lanternfishes 0.2~; barracudinas 0.20; lancetfishes Alepisaurus
ferox 0.~1; snipe eels Nemichthys scolopaceus 0.2~; cods
Merluccius bilinearis 0.17; jacks 0.13; mackerel Scomber
scombrus 0.17; scorpion fishe~ Sebastes marinus 0.3~; filefishes
0.21 and squids Ilex illecebrosus 0.31. Total mercury content
of selected swordfish tissues in mg/kg wet wt were: red muscle
1.59; abdominal muscle 1.10; liver 3.00; kidney 1.91; heart
1.M; brain 0.90; gill 0.~3; vertebral disc 0.20; and stomach
0.50. Mercury levels were related to fish size with larger fish
having higher levels, but the relationship varied with time and
area of capture. Males tended to have higher levels than
females.
22b5 .
Bedford, J.J. and J.P. Leader. 1977. The composition of
the haemolymph and muscle tissue of the shore crab,
Hemigrapsus edwardsi, exposed to different
salinities. Compo Biochem. Physiol. 57A:3~1-3~5.
Hemigrapsus is a typical euryhaline poikilasmotic
animal. External medium changes produce corresponding though
lesser changes in haemolymph composition over the crab's
survi val range of 25% to 110% seawater. Muscle fiber water rose
by only 25% over this range, while concentration of NaCl in
haemolymph fell by > ~O%. Amounts of intracellular sodium,
chloride, calcium, potassium, and magnesium soowed no
significant changes although ninhydrin-positive substances
(amino acids) amounts fell more than expected by dilution.
Authors suggest that the fall in concentration of haemolymph of
crabs acclimated to dilute media is balanced intracellularly by
a reduction in amount of amino acids.
22bb.
Beers, J.R., G.L. Stewart, and K.D. Hoskins. 1977.
Dynamics of micro-zooplankton populations treated
with copper: controlled ecosystem pollution
experiment. Bull. Marine Science 27 :bb-79.
Taxonomi c compos i ti on, numer ical abundance, and
biomass of microplankton (including protozoa, phoronids,
tunicates, crustaceans, echinoderms, molluscs, anneli ds, and
rotifers) from Saanich Inlet, British Columbia, were monitored
in copper concentrations of 0.005, 0.010, and 0.050 mg/l.
Differences between experimental and control populations were
13
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greatest at 0.050 mg Cull, decreasing with lower
concentrations. The major ciliate groups dropped out of the
contained ecosystem with 0.050 mg Cull and did not reappear.
Oligotrich ciliates developed in 0.005 and 0.010 mg Cull, but
with different species than controls. Among important
micrometazoan taxa, naupliar copepod abundances were lowe:-
relative to controls in 0.050 and 0.010 mg Cull, but not In
0.005 mgll. Observed effects on micro-zooplankton taxa may not
be related to direct action of Cu, but may have resulted from
modifications to other trophic levels of the contained
populations.
22b7.
Bentley-Mowat, J.A. and S.M. Reid. 1977. Survival of
marine phytoplankton in high concentrations of heavy
metals, and uptake of copper. Jour. Exp. Mar. Bioi.
Ecol. 2b:2~9-2b~.
Growth of Phaeodactylum tricornutum, Tetraselmis
spp., Dunaliella primolecta and Cricosphaera elongata
(Hymenomonas elongata) in batch culture was not arrested on
addition of copper, cadmium, or lead concentrations below 10-4
M. Level of Cu in natural waters arOl.md Scotland was 10-7 M
or less. All groups dropped to < 20% yield in 10-4 M to 10-2
M Pb, 10-3 to 10-2 M Cu, or 10-3 to 10-2 M Cd. Ditylum
brightwelli exhibited osmotic disturbance in 10-5 M and 10-4
M Cu, with swelling of cell contents. Phaeodactylum grown in
continuous culture survived single doses of up to 10-.:$ M Cu
with no diminution in growth. Maximum Cu uptake was 0.15 mglkg
of culture held between days 7 and 1e; this decreased in 10-4
M Cu seawater. In 10-3 M Cu, algal concentrations peaked at
2.5 mg Cu/kg after 11 days. Cricosphaera in continuous culture
survi ved up to 10-~ M Cu with no long-term diminution in
growth, but accumulated less Cu than Phaeodactylum. Maximum
uptake in both 10-5 and 10-~ M Cu was about 0.01 mglkg at
day 2 and ~, respectively.
22btS .
Best, E.P.H. 1977. Seasonal changes in mineral and
organic components of Ceratophyllum demersum and
Elodea canadensis. Aquatic Botany 3:337-34e.
Seasonal changes in 1974 and 1975 of some organic and
mineral components of the two dominant macrophytes in a sandpi t
were investigated. Both species occur in the nonnal vegetative
fonn in sUDlller and the dormant form in winter - Calcium content
14
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increased towards winter to 36,000 mg/kg dry wt in
Ceratophyllum, and lili, 000 in Elodea. Minimum concentrations
were 16,000 and 2,300, respectively. Ca in water was lower in
sumner, 40 mg/l, than in winter, 50-54. Magnesium content of
Ceratophyllum ranged from 2500 to 1900 mg/kg dry wt in sunmer
and 4~00 to 4900 in winter. In Elodea, accumulated Mg in
September was 1300-3500, but almost zero in August; ambient
water concentrations fluctuated between 7.7 and 9.0 mg/l.
Manganese contents were high in winter, 17,000 mg/kg dry wt in
Ceratophyllum and 7~00 in Elodea, and decreased to almost zero
in June-July; Mn in water was maximal at 0.24 mg/l in winter,
and minimal at 0.05 in September. Iron was highest in late
sunmer, and lGlest in February 1974 (1300 mg/kg dry wt in
Ceratophyllum and ~oo in Elodea). Fe in lake waters fluctuated
from 0.1 mg/l in January to 0.01-0.03 in August. Carbon,
nitrogen, protein, and starch also fluctuated with season.
2269.
Betz, M. 1977. Investigations on the simultaneous
uptake and release of mercury by Dunaliella
tertiolecta. Marine Biology 41:~9-97.
Uptake and release of mercury by the marine alga
Dunaliella was follGled by adding 0.143 mg/l Hg-203 to the
culture, then, after washing, reculturing in media containing
0.0, 0.04, 0.10, or 0.22 mg HgC12/1 labelled with Hg-197.
After ~ days, only 20% of the original dissolved mercury
remained; volatile Hg increased sharply during this period. In
culture containing nutrients, maximum amounts of gaseous
mercury, increasing with increasing Hg levels of solutions,
occurred at the time of highest chlorophyll a content. In
absence of nutrients, this trend was not as evident.
Chlorophyll a content increased fran 0.70 to 1.02 mg/l as Hg
levels increased in cultures with nutrients; without nutrients
this increase was from 0.5~ to 0.65 mg/l. Excretion of Hg was
independent of dissolved organic carbon. Although roc levels
among cultures did not change, more organic substances were
excreted by nutrient-rich cultures than nutrient-poor cultures.
Cultures with nutrients therefore contained less soluble
mercury. The ratio of gaseous Hg/dissolved Hg was nearly
identical for culture solutions and blanks, showing similar
volatility for the dissolved form in all cases. This led to the
assumption that the main part of dissolved Hg in culture
solutions was in the inorganic state.
15
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2270.
Bishop, J.N. and B.P. Neary. 1977. The distribution of
mercury in the tissues of freshwater fish. In:
Drucker, H. and R.E. Wildung (eds.). Biological
implications of metals in the environment. ERDA
Symp. Ser. 42:452-464. Avail. as OONF-750929 from
Nat. Tech. Inf. Serv., U.S. Dept. Comm., Springfield,
VA 22161.
Mercury concentrations in muscle of fish from
Hg-contaminated areas in Ontario were: 0.46-0.57 mglkg for
carp, 1.04-1.05 for lake trout, 0.76-1.14 for small catfish,
1.43-1.55 for large catfish, 2.1~-2.19 for northern pike, and
2.21-2.27 for pickerel. For some benthopelagic species,
gradients of increasing Hg content towards internal muscle and
the head regions were observed. Lipid content was inversely
related to mercury in muscle. Predaceous walleye and northern
pike did not show these relationships. Proportions of
methylmercury to total mercury did not vary in muscle for any
species examined. Nearly all mercury in fish muscle was in
methyl form, however, methyl to total Hg ratios were as 1& as
53% in nonmuscle organs. Generally, skin, scales, and bone had
low Hg concentrations compared to muscle; liver and kidney
levels were higher. Mercury patterns in organs were examined as
an indicator for Hg uptake by fish. Authors concluded that
"snip" samples from flesh would not provide the same precision
as subsampled fillet homogenates.
2271.
Blaxter, J.H.S. 1977. The effect of copper on the eggs
and larvae of plaice and herring. Jour. Marine Biol.
Assn. U.K. 57:~49~5~.
Estimated time to 50% mortality (ET-50) for
newly-hatched larvae of plaice, Pleuronectes platessa, dropped
from >24 days in 0.00-0.09 mg Cull, to 4-10 days in 0.9 mg/l,
and 1.3 days in 2.0 mg/l. Older larvae, aged 31-42 days, showed
higher mortality in 0.3 mg Cull, with ET-50 of 3.6 to ~.O days,
while controls survived >9 to >21 days. In 0.09 mg Cull, ET-50
for 42 day old larvae was 5.6 days. Newly-hatched larvae of
herring, Clupea harengus, showed an increase in mortality in
>2.0 mg Cull; ET-50 was < 1 day compared with> 12 days in
0:-0-1.0 mg Cull. Herring eggs were more sensi ti ve than larvae,
since successful hatching was a 1& as < 10% in 0.003 mg Cull.
Sublethal effects of copper on feeding of plaice were evident at
about 1.0 mg/l in young feeding larvae, and 0.09 mgll in older
larvae and yolk sac plaice. Growth and differentiation
16
-------
were retarded in feeding plaice larvae at 0.09-0.3 mg Cull.
Acti vity of herring larvae, as shown by a laboratory-scale
vertical migration, was impaired in 0.3 mg Cull.
Blinn, D.W., T. Tompkins, and L. Zaleski. 1977. Mercury
inhibition on primary productivity using large volume
plastic chambers in situ. Jour. Phycology 13:5tS-b1.
Effects of mercury concentrations of <0.02 to 1.25
mg/l 00 primary productioo of phytoplankton in Lake Powell,
Arizona, was studied in 197q and 1975. Photosynthetic activity
was 75-100% of controls in 0.013 to O.OM mg Hg/l, and <35% in
0.ms5 to 1.25 mg/l follCMing 2 or 25 hr exposure. No
significant difference was seen with different time periods.
Sumner phytoplankton assemblages had a toxic Hg threshold of
O.Ob mg/l; productivity decreased from about 1,100 mg C/m2/day
to < qOO. A threshold concentration was absent for the spring
assemblage; productivity decreased linearly from 3bO to 120 mg
C/mf/dayas Hg increased to 0.11 mg/l. Differences between
spring and sumner phytoplankton populations may suggest subtle
differences in Hg sensitivity in combination with temperature
acting on total community metabolism.
2272.
2273 .
Borowitzka, L.J. and B.E. Volcani.
silicon in diatom metabolism.
112: 1 q7 -152.
1977. Role of
Arch. Microbiology
Levels of cyclic nucleotides, cAMP, and cGMP were
monitored in four species of freshwater and marine pennate
diatoms, one in silicon-starved and light-dark synchronized
cultures. In Si-starved cultures of Cylindrotheca fusiformis,
amounts of protein, and to a lesser extent cAMP, increased; cell
number, DNA, and cGMP stayed about level. When 12 mg Sill, as
sodium silicate, was added at hour 25, cAMP, cGMP, and DNA
levels rose rapidly. cAMP and cGMP declined before DNA
synthesis was complete and continued to fall prior to cell
separation. In unstarved synchronies, net synthesis of DNA
continued until cell separation. One hour before cell
separation, cAMP levels fell while those of cG1P rose. Results
support the proposal that cAMP and cGMP may playa part in
diatom cell division, possibly involving silicon.
17
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Bouquegneau, J.M. 1977. ATPase activity in mercury
intoxicated eels. Experientia 33:941-943.
Na+~ATPase activity in gill of eels Anguilla
anguilla in seawater as related to total ATPase ~c~ivity,
declined to one-third of control values upon addltlon of 2.7
mg/l of HgC12' Activity increased to normal with ~.? mM
cysteine in the mercury mixture. Total ATPase actlvlty
decreased 70% in 0.27 mg/l HgC12' and 50% in 0.67 ~o 2.7 mg
Hg/l. In CH3HgCl, enzyme activity dropped to 70% l~ ~1.3 mg/l
and leveled at 50% in from ~2.6-5.2 mg Hg/l. Ouabaln-non
sensitive ATPase activity followed a similar trend.
Ouabain-sensitive Na+~ATPase activity was unaffected in Hg
concentrations from 0.0 to 12.0 mg/l, then decreased as Hg
increased to 19.0 mg/I. Concentrations of Na and Cl were steady
at approximately 150 meqll in concentrations of 0.0 to 12.0 mg
Hg/l, peaked at ZTO (Na) and 230 (Cl) in 1~.O mg Hg/l, and
declined slightly in 19.0 mg Hg/l. Imbalance of eel NaCl levels
was caused by Hg inhibition of ouabain-sensitive Na+~ATPase
activity in gills.
2274.
2275.
Boyden, C. R. 1977. Effect of size upon metal content of
shellfish. Jour. Marine Bioi. Assn. U.K. 57:675-714.
Influence of body size upon whole tissue metal
content of 13 species of estuarine and marine molluscs was
examined for Cd, Cu, Fe, Mn, Ni, Pb, and Zn. Overall,
regression slopes fell into two categories: those around 0.77
and those close to 1. 00. In the former case, Mytilus edulis had
higher zinc concentrations in the smallest individuals; in the
second case, cadmilIDl in M. edulis was independent of size. In
several cases, such as Cd in Patella vulgata, maximum levels
were recorded in the largest specimens. Large Pecten maximus
had very high Cd concentrations. Comparison between species
pOpllations from clean and contaminated environments indicate
that regression slopes could be either constant, such as Zn and
probably Cd in Ostrea edulis and Cd and Zn in M. edulis, or
variable, such as Cd and Zn in f. vulgata with-increase of
slopes in metal elevated environments. Large specimens of
Crassostrea gigas, Ostrea edulis, and M. edulis required >5
months to equilibrate to exceptionally-high environmental Cu
concentrations, the same was true for Zn in f. gigas. Steeper
slopes, and almost twice as much variability, were recorded when
using wet wt data compared with dry wt.
1CS
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2270.
Brkovic-Popovic, I. and M. Popovic. 1977. Effects of
heavy metals on survival and respiration rate of
tubificid worms: part I-effects on survival.
Environ. Poll. 13:05-72.
LC-50 tests for cadmium, copper, mercury, zinc,
chromium, and nickel were conducted with Tubifex tubifex in four
diluents of different hardness and alkalinity. Types of
dilution water ranged in calcium from 0.0 to 94.7 mg/l, in
magnesium from 0.0 to 5.93, and in phosphate from 0.0 to 29.6.
LC-50 (24 hr) values ranged from 0.12 to 75.tS mgll for Zn, O.OtS
to tS6.0 for Cr, 0.12 to 120.0 for Ni, 0.004 to 1.2 for Cd, 0.01
to 1.4 for Cu, and 0.00 to 0.11 for Hg. LC-50 (4tS hr) values
were 0.11 to 60.2 mg/l for Zn, 0.00 to 4.6 for Cr, O.OtS to 61.4
for Ni, 0.003 to 0.72 for Cd, 0.000 to 0.tS9 for Cu, and 0.06 to
0.10 for Hg. Increasing alkalinity and hardness of diluent
reduced toxicity of metal salts tested; correlation coefficients
ranged from 0.94 for Hg to 0.99 for Cu.
2277.
Brkovic-Popovic, I. and M. Popovic. 1977. Effects of
heavy metals on survival and respiration rate of
tubificid worms: part II-effects on respiration
rate. Environ. Poll. 13:93-9tS.
OxygEn consumption of Tubifex tubifex in
concentrations of cadmium, chromium, copper, mercury, nickel,
and zinc for 6 hours was determined using dilution water for BOD
test with phosphate buffer added. Respiration rate increased to
tS50 ml 02/kg wet wt from control value of 750, as Cd
concentration increased from 0.0001 to 0.01 mg/l, then declined
to 650 at the LC-50 (4tS hr) value of 0.06 mg Cd/l and 670 at
LC-50 (24 hr) value of 0.00 mg Cd/l. Increasing Cu caused a
decrease in 02 consumption, to 630 from control of 750 mg
02/kg wet wt, as levels increased from 0.001 to 0.7 mg Cull.
LC-50 (41:S hr) and LC-50 (24 hr) values were 0.3 and 1.0 mg Cull,
respecti vely. Respiration rate peaked at tS50 mg 02/kg wet wt
in 0.01 mg Hg/l, above 750 for controls, then rapidly declined
to 560 as Hg increased to o. tS. LC-50 values for 4tS hr and 24 hr
were approximately 0.1 mg Hg/lo In Zn, maximum respiration rate
was 700 mg 02/kg wet wt at 1.0 mg/l; at 4-5 mg Zn/l, the LC-50
(41:S hr) and (24 hr) values, rates dropped to 660, still above
control respiration of 030. No effect was shown in 0.01 and 0.1
mg Cr/l; however, oxygEn consumption increased to tSOO from
control of 030 mg 02/kg wet wt as levels increased to LC-50
(24 hr) value of 10.0 mg Cr/l; LC-50 (4tS hr) was 20.0 mg Cr/l.
Respiration rate decreased slightly to 770 compared with
19
-------
controls of t500 ml 02/kg wet wt in 1.0 mg Ni/l, but increased
to 1150 at approximately 10 mgll, the LC-50 (llli hr) value; t?e
LC-50 (24 hr) was 30 mg Nill. Authors indicate that <;tlteratl?n
of respiration rate may be useful in toxicity evaluatlon studles.
227t5 .
Brown, B. E. 1977. Uptake of copper and lead by a metal
tolerant isopod Asellus meridianus Rac. Freshwater
Biology 7:235-244.
The Rayle River contains comparatively high
concentrations of copper and trace amounts of lead; the Gannel
Ri ver is a high-lead environment. !.:.. meridians from. si tes on
both rivers accumulate copper from 0.5 mg Cull solutlons and
lead from 0.5 mg Pb/l solutions. Accumulated Cu concentrations
in whole animal after exposure for tS days ranged from 430 to
1170 mg Cu/kg wet wt over control values; for Pb this was 52tSO
to 19,920 mg/kg over controls. Tolerant animals also
accumulated Cu and Pb from metal-enriched food. Copper-tolerant
isopods contained up to 6.tS mg Cu/kg after feeding on a
Cu-enriched diet for 12 days; non-tolerant isopods showed no
evidence of Cu accumulation from food but all died within tS
days. Lead-tolerant animals accumulated up to 2t5 mg Pb/kg
during exposure for 14 days to a lead diet: non-tolerant
animals showed no accumulation of lead from food and all were
dead within 10 days. Electron micrographs of the hepatopancreas
show Cu-storage forms resembling cuprosomes and granular
inclusions bound in spherical vesicles. The discovery of
sulphur-metal complexes in Cu and Pb tolerant Asellus from the
Ri ver Rayle may account, in part, for observed tolerances.
2279.
Brown, B. E. 1977. Effects of mine drainage on the River
Rayle, Cornwall A) Factors affecting concentrations
of copper, zinc and iron in water, sediments and
dominant invertebrate fauna. Rydrobiologia
52:221-233.
In water collected from 13 stations on the River
Rayle, England, at least 70% of the Cu and Fe was associated
with particulate fractions whereas tSO% of Zn was in soluble
form. Total concentrations of Zn in water were generally 0.4 to
1.2 mgll with a peak of 2.6. Water Cu levels ranged from 0.1 to
0.2 mgll, with a maximum of 0.7. In sediments, Cu levels were
generally 1000 to 3000 mg/kg with a maximum of 5000, 3X higher
than Zn which was always <2000 mg/kg. Iron was the most
abundant metal, up to 6.0 mg/l in water and 400,000 mg/kg in
20
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sedllnent. Seasonal differences in total metal content in water
increased during periods of high floo and decreased during low
flew. Cu levels in sedllnent, unlike Fe and Zn, showed higher
values during sumner and minllnal flows. Insect larvae contained
q5 to 1000 mg Cu/kg dry wt, 65 to 5000 mg Zn/kg, and 260 to 9~00
mg Fe/kg. In free living Trichoptera larvae, tissue levels of
Cu and Zn seemed to reflect water metal levels. Species of
crustaceans, molluscs, annelids, and platyhelmintheds were also
found at various sites. Factors affecting animal/metal
relationships are discussed with reference to adaptation to high
environmental concentrations of heavy metals.
22~0.
Brown, D.A. 1977. Increases of Cd and the Cd:Zn ratio
in the high molecular weight protein pool from
apparently nonnal li ver of tumor bearing flounders
(Parophrys vetulus). Marine Biology qq:203-209.
Li ver of tumor bearing flounders was studied for the
role of metallothioneins in binding excess cadmium, copper or
zinc. Composite gel elution profiles for nontumor and tumor
bearing flounders are presented. Total distribution of Cd, Cu
and Zn among protein peaks from liver cytopla3Il of nontumor
flounders in umole/g tissue wet wt were: 0.009~ Cd, 1. e1 Cu,
and 0.1~ Zn. These values in tumor bearing fish were 0.01ge
Cd, 1.~ Cu, and 0.293 Zn. Cadmium and zinc were not increased
significantly in tumor bearing fish relative to nontumor bearing
fish on the metallothionein peak, but were increased 3.3 and
2.q-fold, respectively, on the high molecular weight protein
peak. Overall, there is a 2-fold increase of Cd in tissue
homogenate supernatant of the tumor bearing fish. Increases in
Cd in liver of tumor bearing fish are greater than those of Zn
as indicated by a qO% increase in the Cd:Zn ratio on the high
molecular weight protein peak. Copper shows only small
inconsistent changes in tumor bearing fish relative to nontumor
bearing fish. Author discusses results in terms of competition
of Cd and Zn for Zn-requiring enzymes involved in nucleic acid
metabolism.
22~ 1 .
Brown, E.R., T. Sinclair, L. Keith, P. Beamer, J.J.
Hazdra, V. Nair, and o. Callaghan. 1977. Chemical
pollutants in relation to diseases in fish. In:
Kraybill, H. F., C. J. Dawe, J .C. Harshbarger, and R.G.
21
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Tardiff (eds.). Aquatic pollutants and biologic effects with
emphasis on neoplasia. Annals N.Y. Acad. Sciences 2ge:535-540.
Water analysis was made since 1970 for the
comparatively polluted Fox River, near Chicago, ~d the.
relati vely clean Canadian Lake of the Woods. Maxlmum mneral
concentrations, in mg/l, in Fox River were 55.0-5~.0 fo~
magnesium, 17.5-45.5 for sodium, and 3e.5-45.0 for calClum.
High concentrations for the Canadian Lake were 12.5 for Mg and
14.0-16.0 for Na. Also analyzed were AI, As, Sb, Bi, Mn, Hg,
Ni, Fe, Pb, Cd, Cu, K, Zn, and other minerals and organic
compounds. Frequency of nononcogenic fish diseases was more
than 400% higher in polluted Fox River than Lake of the Woods;
incidence of oncogenic diseases Paralleled but did not match
this finding. Mortality of bluegill sunfish populations exposed
to 5 mg Cd/l was 100%; for 200 mg Mg/l this was 95%; 5 mg Zn/l
killed ~4%; 200 mg Call produced 60% dead; and 5 mg As/l killed
~%.
22~2.
Brown, J.R. and L.Y. Chow. 1977. Heavy metal
concentrations in Ontario fish. Bull. Environ.
Contamin. Toxicol. 17:190-195.
Concentrations of Cd, Cu, Pb, Hg and Zn were
determined in various tissues from 15 species of fish in Baie du
Dore, Lake Huron, and in Toronto Harbour, Lake Ontario.
Concentrations were similar in the various species studied.
Mean concentrations, in mg/kg wet wt, in muscle were 0.00 for
cadmium in fish from Baie du Dore and 0.13 Cd from Toronto
Harbour, 0.45 and 1.9 for copper, 0.19 and 1.e for lead, 4.7 and
30.0 for zinc, and 0.00 and 0.24 for mercury, respecti vely.
Liver had values of 0.10 and 0.13 for Cd, 5.2 and 10.4 for Cu,
0.24 and 1.5 for Pb, and 15.1 and e9.0 for Zn, respectively.
Concentrations in kidney were 0.40 and 0.42 for Cd, 4.7 and 4.3
for Cu, 1.4 and 0.0 for Pb, and 20.1 and 59.4 for Zn,
respecti vely. Heavy metal concentrations in sediments were < 2.5
mg/kg dry wt for Hg and Cd from both areas, 4 from Baie du Dore
and 35 from Toronto Harbour for Cu, 0 and 72 for Pb, and 17 and
ge for Zn, respectively. Concentrations of metals in muscle
from fish in Toronto Harbour were consistently higher than
specimens from Baie du Dor~, reflecting sediment concentrations
of these elements.
22
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22~3.
Bryan, G.W. 1976. Heavy metal contamination in the
sea. In: Johnston, R. (ed.). Marine Pollution.
Academic Press, London:1~5-302.
Contamination of sediments and marine or
marine-related organisms by Ag, Al, As, Be, Ca, Cd, Co, Cr, Cu,
Fe, Hg, La, Li, Mg, Mn, Mo, Na, Ni, Pb, Sb, Se, Sn, Ti, Tl, U,
V, W, Zn, and Zr is reviewed. Topics discussed include sources
of metals, concentrations and fates of metals in seawater and
sediments, concentrations, uptake, toxicity and sublethal
effects in plants and animals, and effects to man.
22~.
Bryan, G . W. and L. G. Humners tone. 1977 . Ind i ca tors of
heavy-metal contamination in the Looe Estuary
(Cornwall) with part i cular regard to si 1 ver and
lead. Jour. Marine BioI. Assn. U.K. 57:75-92.
Looe EsttBry has two branches, one receiving lead and
silver from old mines, and the other receiving silver from
presumed industrial sources. Analyses of Ag, Cd, Co, Cr, Cu,
Fe, Mn, Ni, Pb, and Zn were made in the seaweed Fucus as an
indicator of levels in water; in herbivorous gastropods
Littorina littorea and Patella vulgata, and in filter feeding
bivalves MYtilus edulis and Cerastoderma edule as indicators of
metals in suspended particles; in deposit feeding bivalves
Scrobicularia plana and Macoma balthica and worm Nereis
diversicolor as indicators of sediment levels; and in the
carnivorous gastropod Nucella lapillus. Lead averaged 2~O mg/kg
dry wt in sediments, a maximum of 1~9 in Scrobicularia, and
3~-5~ mg/kg dry wt in Macoma, Fucus, Nereis, and MYtilus. Pb
contamination followed a similar pattern in different species.
Mean Ag level in esttBrine sediments was 1.5 mg/kg dry wt;
maximum averages in animals were ~5 mg Ag/kg dry wt in Macoma
and ~O in Scrobicularia. There was little evidence of
contamination of dissolved silver in the estuary, but
considerable contamination by particles of freshwater origin.
Althou@'l particulate Ag concentrations were of the same
magnitude from both sources, the influence of the non-mining
source was much greater; Ag concentrations ~25X above normal
were found in Scrobicularia upstream. It was concluded that
particles, perhaps silver sulfide, from the mining source were
not as available to organisms as from other sources wherein
silver may be adsorbed onto particles.
23
-------
Average levels of metals in sediments and maximum averages in
organisms, in mg/kg dry wt, were: 0.2 and 12.~ i~ Nucella,
respectively, for Cd; 11.1 and ~.9 in Scrobicularla for Co, 36
and 2.~ in Scrobicularia for Cr; 63 and 300 in Macoma for Cu;
Z7 ,900 and 1640 in Patella for Fe; 426 and 363 in Fucus for Mn;
34 and 44 in Cerastoderma for Ni; and 151 and 974 in
Scrobicularia far Zn.
22~5.
Bryan, G . W ., G. W. Potts, and G. R. Fors ter . 1977 . Hea vy
metals in tre gastropod mollusc Haliotis tuberculata
(L.). Jour. Marine Biol. Assn. U.K. 57:379-390.
Concentrations of Ag, Al, Ca, Cd, Co, Cr, Cu, Fe, Mg,
Mn, Ni, Pb, and Zn were measured in whole soft parts, foot,
viscera and individual tissues of Haliotis. Concentrations in
whole soft parts in mg/kg dry wt were 2.9 Ag; 65 to 67 Al; 11~
to 1190 Ca; 4.~ to 5.6 Cd; 0.23 to 0.44 Co; 0.~2 to O.~ Cr; 2~
to 29 Cu; 306 to 474 Fe; 4210 to 4290 Mg; 2.9 to 3.3 Mn; 13.6 to
15.9 Ni; 2.1 to 2.2 Pb; and 9~ to 103 Zn. In viscera, metal
concentrations always exceeded those in the foot, sometimes by
an order of magnitude. Viscera accounted for about 26% of the
dry weight of the soft parts and contained more than 50% of all
metals except nickel and 90% or more of cadmium, iron and
oobalt. Highest levels of oopper were in blood and left
kidney. High levels of nickel were associated with surface
tissues such as the mantle and epidermis of the foot. The
highest concentrations of other metals were in the digestive
gland or the right kidney which seems to be flIDctionally
different fran the left.
22~6 .
Buchardt, B. and P. Fritz. 197~. Strontium uptake in
shell aragonite from the freshwater gastropod Limnaea
stagnalis. Science 199 :291-292.
Shell aragonite from Limnaea stagnalis grown in
laboratory tanks at different temperatures in water with
variable Sr/Ca ratios were analyzed for strontium. Within the
limi ts defined by natural freshwater environments, the Sr/Ca
ratio in aragonite was linearly related to the Sr/Ca ratio in
water. A distribution ooefficient was lIDaffected by variations
in temperature and growth rate. This finding substantiates the
existence of a strontium-discriminating effect in aragonite
precipitated by mollusks as compared to the case for nonbiogenic
aragonite which contains about five times as much strontium when
precipitated under the same conditions.
24
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22e7 .
Buhler, D.R., R.M. Stokes and R.S. Caldwell. 1977.
Tissue accumulation and enzymatic effects of
hexavalent chromium in rainbow trout (SalIno
gairdner i) . Jour. 1" ish. Res. Bd. Canada 34 : 9-1 tS .
Two-year-old rainbow trout reared far 2 yr in water
containing about 0.00025 mg/l hexavalent chromium (Cr6+)
(Naches trout) or between 0.002 and 0.010 mg/l Cr6+ (Hanford
trout) accumulated appreciable chromium, yielding whole body
residues of about 0.029 and 0.1tSO mg/kg wet tissue,
respecti vely . Naches trout after exposure for 22 days to 2.5 mg
Cr6+ /1, soowed highest concentrations, in mg Cr/kg wet wt in
opercular bone (13.6), spleen (9.4), kidney (9.4), gall bladder
(19.1) and bile (5.2); whole body Cr concentrations at 22 days
was relatively lCM (0. tS7). Upon return of exposed fish to water
containing 0.002-0.010 mgll chromium, the metal was rapidly
depleted from most tissues except kidney, liver, gill, gall
bladder, and bile. Chromium accumulated in tissues of trout
exposed to 2.5 mg/l Cr6+ was not distributed proportionately
among th3 various subcellular fractions but concentrated in cell
cytosol, especially liver and gill. Mitochondrial cytochrome
oxidase, NADH-cytochrame c reductase, and succinate cytochrome c
reductase activities in liver, kidney, gill, and brain tissues
of Naches trout and Hanford trout exposed to 2.5 mg/l Cr6+
were not significantly different except for kidney
NAJ1I-cytochrome c reductase which was lower in Hanford and
chromium treated fish. Microsomal nitroreductase, O-demethylase
and NADPH-cytochrome c reductase and the soluble
glucose-6-phosphate dehydrogenase activities in liver and kidney
from Hanford trout were significantly lCMer than those of Naches
trout. Exposure of Hanford trout to 2.5 mgll Cr6+, however,
did not reduce the activities of these enzymes below control
levels. In vitro studies soowed that trout enzymes were fairly
insensitive to Cr6+ inhibition. These results suggest that
observed differences in enzyme activity between Naches and
Hanford trout may be caused by factors other than chromium
content of the water.
22tStS .
Burrows, W.D. 1977. Aquatic aluminum: chemistry,
toxicology, and environmental prevalence. CRC
Critical Reviews in Environmental Control 7:167-216.
Acute effects of aluminum salts to freshwater and
marine fishes, protozoans, crustaceans, molluscs, bacteria,
algae, and higher plants, plus chronic effects to trout are
25
-------
reviewed. Environmental prevalence of aquatic a~uminum in ~orth
America and selected sites in South America, AfrIca, and ASIa
and in seawater is listed. Also presented is data on chemistry
of Al in water and its determination.
22tS9.
Calabrese, A. 1975 (1976). Effects of heavy metals on
embryonic and adult marine bivalves. Haliotis
5 : 121- 125 .
Results of selected studies on biological effects of
11 metals to bi val ves were surnnarized. Mercury, Ag, Cu, and Zn
were most toxic to embryos of oysters, Crassostrea virginica;
Ni, Pb, and Cd were less toxic and Ai, As, Cr, and Mn least
toxic. Decreasing order of toxicity to clam, Mercenaria
mercenaria, embryos was Hg, Ag, Zn, Ni, and Pb. LC-50 (96 hr)
values for juvenile scallops, Argopecten irradians, showed Ag
and Hg most toxic while Cd and As were less toxic. Oxygen
consumption was increased by sublethal concentrations of Cd and
Ag. Silver also induced oxygen consumption elevations in
larval, juvenile, and adult clams, Spisula solidissima; gills
accumulated up to 4X more Ag than body tissues. In general,
oxygen consumption increased and was salinity-dependent in
Crassostrea, Mercenaria, mussels MYtilus edulis, and soft shell
clams !1@ arenaria exposed to sublethal levels of silver for 96
hrs.
2290.
Calabrese, A., R.S. Collier and J.E. Miller. 1974.
Physiological response of the cunner, Tautogolabrus
adspersus, to cadmium. 1. introduction and
experimental design. In: U.S. Dept. Conmerce NOAA
Tech. Report NMFS SSRF -btS 1 : 1-3.
Too cunner, a marine teleost, was exposed to five
concentrations of cadmium as CdC12, at 250/00 salinity and
21-250C. Cadmium levels tested, in mg/l, (and percent
mortality in 96 hours) were: 0.0 (1.~); 3.0 (3.5); b.O (5.4);
12.0 (1.tS); 24.0 (10.7); and 4~.0 mg/l (26.~%)-
229 1 .
Calabrese, A., J.R. MacInnes, D.A. Nelson, and J.E.
Miller. 1977. Survival and growth of bivalve larvae
under heavy-metal stress. Marine Biology 41 :179-1tS4.
LC-5, -50, and -95 concentrations of mercury, silver,
copper, nickel, and zinc salts to larvae of the oyster,
2b
-------
Crassostrea virginica, and the clam, Mercenaria mercenaria, were
determined. LC-50 (12 day) values for ~ virginica were, in
ug/l, 12 for Hg, 25 for Ag, 33 for Cu, and 12,000 for Ni. LC-5
and -95 values followed a similar pattern. LC-50 (tl-10 day)
values for M. mercenaria, in ug/l, were 15 for Hg, 16 for Cu, 32
for Ag, 195for Zn, and 5,700 for Ni; LC-5 and -95 values showed
the same order of sensitivity. Calculated growth of surviving
larvae fram both species, except clam larvae in nickel-treated
water, was not reduced significantly at the LC-5 values of the
five metals, but was reduced to 6tl to 45% of original growth at
the LC-50 values. No growth was observed for clam larvae at the
LC-50 level of Ni. Embryos from both species were generally
more sensitive than larvae to heavy metal toxicants, with Hg
most toxic and Ni least toxic on the basis of LC-50 values.
2292.
Calabrese, A., F.P. Thurberg, and E. Gould. 1977.
Effects of cadmium, mercury, and silver on marine
animals. U.S. Dept. Camnerce, Marine Fish. Review
39 ( 4 ) : 5-11 .
Effects of various concentrations and exposure times
of cadmium, mercury, and silver on marine molluscs, crustaceans,
and fish are slIDInarized. Data includes oxygen consumption,
osmoregulation, enzyme activity, survival and other toxic
effects, and is based on studies conducted at the Milford
(Conn.) Lab of the Middle Atlantic Coastal Fisheries Center.
2293.
Calamari, D. and R. Marchetti. 1975. Predicted and
observed acute toxicity of copper and ammonia to
rainbow trout (Salmo gairdneri Rich.). Prog. Water
Technol. 7(3/4):569-577-
Trout were placed in cages at various depths for 4tl
hrs in Lake Orta, Italy, from March to September, when copper
and ammonia concentrations varied from 0.006-0.066 mg Cull and
from 5.tl to 7.2 mg N(NH3 and NH4+)/l. Mortality at
different seasons was always higher in depths> 15 m. A maximum
of 67% kill occurred in August at 30 m, when water contained
0.056 mg Cull and 5.6 mg ammonia/l; 61% died in September at 25
m with 0.066 mg Cull and 5.1 mg arrmonia/l, and 60% died in May
at 25 m with 0.05 mg Cull and 4.7 mg ammoniall. Survival
increased fram winter to SlIDIner in the upper layers; mortality
dropped to only 0-10% in August and September when Cu ranged
fram 0.006 to 0.020 mgll and ammonia from 5.1 to 7.2 mg Nil.
Toxicity values for the field matched expected values from
previous laboratory assays.
27
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2294.
Capuzzo, J.M. and J.J. Sasner. 1977. The effect of
chromium on filtration rates and metabolic activity of
Mytilus edulis L. and ~ arenaria L. In: Vemberg,
F.J., A. Calabrese, F.P. Thurberg, and W.B. Vernberg
(eds. ) Physiological responses of marine biota to
pollutants. Academic Press, N.Y.: 225-237.
Chromium, in dissolved and particulate forms, lowered
filtration rates in Mytilus, and to a lesser extent, in ~ .
Exposure of Mytilus to sediments from Pomeroy's Cove, New
Hampshire (150 mg Cr/kg clay) and Fresh Creek (990 mg Cr/kg) for
24 weeks reduced filtration rates in direct proportion to Cr
concentration. No significant difference was observed with
Adam's Point sediment (10 mg Cr/kg). Mytilus and Mya reduced
filtration rates when exposed to 1,200 mg Cr/kg kaolinite clay
for 4-6 weeks. Uptake was probably due to diffusion of dissolved
Cr, since Cr concentration of kaolinite decreased to 500 mg/kg
over this period. In 1000 mg Cr/kg bentonite clay, which did not
reduce in concentration, Mytilus but not ~ exhibited
significantly lowered filtration rates. Exposure to 1.0 mg Cr/l
seawater resulted in reductions in filtering activity in both
species of molluscs. Authors concluded that diffusion from
seawater and particulate uptake were important pathways for Cr
exposure in Mytilus, but only diffusion vas important in ~.
Mytilus gills in 1.0 mg Cr/l or 1000 mg Cr/kg bentonite showed
slow, erratic movements of cilia; oxygen consumption of excised
gill tissue was reduced.
2295.
Chan, K.M. and J.P. Riley. 1966. The determination of
vanadium in sea and natural waters, biological
materials and silicate sediments and rocks. Analytica
Chim. Acta 34:337-345.
Vanadium was concentrated from sea and natural waters
by coprecipitation with iron hydroxide, separated from iron and
other elements by ion exchange using hydrogen peroxide as a
selective eluting agent, and determined photometrically with
d iaminobenzi dine . The ion exchange process was also used to
separate vanadium from other elements in the analysis of silicate
rocks and three species of the marine algae: Fucus vesiculosus,
Laminaria digitata, Ascopyllum nodosum. Concentration of
vanadium (coefficient of variation) in seawater was 0.002 mg/l
(2.8%), in sediment 57.0 mg/kg (1.3%), in Fucus 2.2 mg/kg dry wt
(2.5%), in Laminaria 1.8 mg/kg dry wt (2.5%), and in Ascophyllum
0.9 mg/kg dry wt (2.5%).
28
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2296.
Chau, Y.K. and P.T.S. Wong. 1976. Complexation of metals
in natural waters. In: Andrew, R.W., P.V. Hodson,
and D. E. Konasewich reds.). Toxicity to biota of
metal forms in natural water. Great Lakes Res. Advis.
Ee1., Stand. Corrm. Sci. Basis Water Qual. Criteria,
Intern. Jt. Comm. Res. Advis. Bd.:187-196.
Significant fractions of trace metals in natural
waters are believed to exist in complexed forms together with
miscellaneous organic ligands which regulate availability of
these metals in the system as nutrients or as toxic agents.
Metal concentrations in test water from several Ontario lakes
smwed high labile and total Zn, up to 0.27 mg/l and 0.33 mg/l,
respectively, and maximum total Ni at 1.9 mg/l, total Cu at 0.02
mg/l, total Pb at 0.02 mg/l, and total Cd at 0.005 mg/l. No lake
waters supported algal growth of Ankistrodesmus falcatus higher
than 20% of a laboratory medium, possibly because of low
complexing capacity of these metals. When 0.5 mg Pb/l, as
Pb(ID3)2, was added to each lake, growth of the algae
Sceneaesmus quadricauda was inhibited to 10 to 70 % of controls.
No lake could detoxicate this amount of Pb; however, a direct
relationship between complexing capacity of water and algal
growth was smwn.
2297.
Cheng, L., G. V. Alexander and P. J. Franco. 1976 . Cadmi um
and other heavy metals in seaskaters (Gerridae:
Halobates, Rheumobates). Water, Air Soil Poll.
6:33-38.
Concentrations of cadmium, copper, iron, lead, nickel
and zinc were determined in the oceanic insects Halobates
sobrinus and H. sericeus, and in Rheumotobates aestuarius
collected from mangrove swamps. Mean metal levels, in mg/kg dry
wt, for H. sobrinus were 152 Cd; 50 Cu; 289 Fe; 10 Pb; 18 Ni; 176
Zn. ForlH. sericeus these were 40 Cd; 45 Cu; 178 Fe; 7 Pb; 7 Ni;
176 Zn. Concentrations in R. aestuarius were >5 Cd; 64 Cu; 204
Fe; >2 Pb; 6 Ni; 197 Zn. Authors suggest that Halobates could
become a useful environmental indicator owing to its large body
size, distribution, and ability to accumulate trace metals,
especially Cd.
2298.
Cheng, T.C. 1975. Does copper cause anemia in
Biomphalaria glabrata? Jour. Invert. Pathology
26:421-422.
29
-------
Hemoglobin concentrations in freshwater gastropods, ~.
glabrata, showed no significant differences between snails
exposed to 0.06 or 60.0 mg Cull as CuS04 for 12 hrs, or for 72
hrs, vs controls that had been starved for that period. Pigment
cells-rn connective tissue matrix of the rectal ridge destroyed
by Cu expooure were believed to be hemoglobin-synthesizing
cells. It was concluded that either these cells do not serve
this function, or sufficient cells exist in other parts of the
body to mask loos due to cupric ions.
Chervinski, J. 1977. Note on the adaptability of silver
carp - Hypophthalmichthys molitrix (Val.) - and grass
carp - Ctenopharyngodon idella (Val.) - to various
saline concentrations. Aquaculture 11 :179-182.
Survi val of t1fK> carp species was observed in fresh
water, and in 20% (7.8 0/00), 25% (9.75 0/00), and 30% (11.7
0/00) seawater. Both species survived direct transfer from fresh
wa ter to 20% and to 25% seawater after 48 hrs. In 30%, all
silver carp were dead, but 4/5 of the grass carp survived. After
acclimatization to 20% seawater for 48 hrs, fish were transferred
to 30%; most silver carp and grass carp survived. After
acclimatization to 25% seawater and transfer to 30%, a mean of
0.5 of 5 silver carp and 2.4 of 5 grass carp were still alive.
Upon transfer from fresh water to 25% seawater, no silver carp,
and 3/4 of the grass carp survived after a month.
2299 .
2300.
Clubb, R.W., A.R. Gaufin and J.L. Lords. 1975. Acute
cadmium toxicity studies upon nine species of aquatic
insects. Environ. Research 9: 332-341.
Continuous-flew bioassays were used to calculate LC-50
(96 hr) values for cadmium and freshwater insects. For stone fly ,
pteronarcella badia, this was 18.0 mg Cd/l; and for mayfly,
Ephemerella grandis grandis, it was 28.0 mg Cd/l. pteronarcella
was the most sensitive species tested. Mayflies, stoneflies
true flies, and caddisflies were relatively insensitive to '
cadmium (see table).
Percent survival at maximum cadmium concentration tested:
Species
mg Cd/liter
Days
Percent survival
Diptera (true flies)
Atherix variegata
10.0
21
100
30
-------
Hexatoma ~ 10.0 21 80
Holorusia sp. 42.5 7 50
Ephemeroptera (mayflies)
Ephemerella grandis grandis 42.5 7 0
Plecoptera (stone flies)
Acroneuria pacifica 17.5 21 10
Arcynopteryx signata 17.5 21 10
pteronarcella badia 42.5 7 0
Pteronarcys californica 14.0 14 100
Tricoptera (caddis flies)
Brachycentrus americanus 42.5 7 100
P. badia held in 9.0 mg Cdll solutions accumulated 19.0
mg/kg/day for the first 24 hr and minus 0.005 mg/kg/day during
days 1-4. Post-treatment Cd loss of this group was minus 0.75
mg/kg/day, with loss rate appearing linear. Immature insects
appear to be more sensi ti ve to Cd than larger, mature insects.
Long term studies suggest tffit cadmium inhibits molting
frequency.
2301.
Clubb, R.W., A.R. Gaufin and J.L. Lords. 1975.
Synergi3I1 between dissolved oxygen and cadmium
toxicity in five species of aquatic insects.
Environ. Research 9:285-289.
Continuous-flow bioassays were used to determine the
relatioo between dissolved oxygen and cadmium upon Acroneuria
pacifica, Brachycentrus americanus, Ephemerella grandis grandis,
Holorusia sp. and pteronarcella badia as measured by survival
and body Cd burdens. Survi val decreases with increasing oxygen
concentratioo at given cadmium levels. Uptake of Cd and oxygen
consumption increased at increasing dissolved oxygen
concentrations. For all Cd levels tested, there was sane
survival after 2 weeks in all species during exposure to 1.0-5.0
mg Cdll with dissolved oxygen ranging between 4.6 and 7.6 mg/l.
Exposure of P. badia to 5.0 mg/l Cd at 3.8 mg/l D.O. for 96 hrs
produced bodY-residues of 7 to 114 mg Cd/kg; these values were
significantly higher when D.O. was increased to 6.1 mg/l.
Authors concluded that cadmium absorption may be coupled to
metabolism.
2302.
Conway, H.L, J.I. Parker, E.M. Yaguchi and D.L.
Mellinger. 1977. Biological utilization and
31
-------
regeneration ot' silicon in Lake Michigan.
J:t' ish. Hes. t3d. Canada j~: ~ ::H -~LPL
Jour.
Depth profiles ot' dissolved reactive silicon and
amorphous particulate silicon were made at seven monthly
intervals at stations along a southwest transect from Grand
Haven, Michigan, to the approximate center of the southern basin
ot' Lake Michigan. Biological utilization of reactive silicon
occurred prior to stratification in early June. A shift from a
100% diatom-dominated phytoplankton conmunity in spring to
approximately 1~ diatoms in August was attributed to the low
dissolved Si level ot' <0.002 m mol/l in the surface water during
sunmer. The total amount of biologically active silicon (TBAS)
for the lake was approximately 0.019 m mol/I. Winter values
were approximately 0.002 m mol/l amorphous silicon and 0.017 m
mol/l reactive silicon. During the period June-August, <:50% of
TBAS had been utilized by the diatom community, with only 20%
remaining as reactive silicon. Greater than 50% of THAS was
lost from the water column during spring and early sunmer; the
loss was attributed to settling ot' diatom frustules and sinking
of zooplankton fecal pellets containing frustules. This silicon
was subsequently returned, in a soluble form, to deep water
during the fall. The amount ot' THAS recycled was estimated to
be <:50-100%.
2303.
Conway, H. L. and P. J. Harr ison. 1977. Mar ine d ia toms
grown in chemostats under silicate and ammonium
limi tation. IV. transient response ot' Chaetoceros
debilis, Skeletonema constatum, and Thalassiosira
gravida to a single addition ot' the limiting
nutrient. Marine Biology ~3:33-~3.
Ihe kinetic response of ammonium- or silicate-limited
and arrmonium- or silicate-starved populations of C. debilis, S.
costatum, and ~ gravida was determined by singleaddition 01'-
the limiting nutrient to a steady-state culture and subsequent
monitoring ot' nutrient disappearance. Three distinct modes of
uptake were observed for ammonium- or silicate-limited
populations ot' these three species: surge uptake (Vs);
internally (cellular) controlled uptake (Vi); and externally
(ambient limiting nutrient concentration) controlled uptake
(Ve)' Non-limited populations did not exhibit the three
distinc~ segments of uptake, Vs, Vi, and Ve. Estimates of
the maxlI1lal uptake rate (Vmax) and the Michaelis constant
(Ks) were obtained from nutrient-limited populations during
the Ve segment ot' the uptake curve. Pooled values of Ve for
the three ammonium limited populations yielded Vmax and Ks
estimates ot' 0.16/hr and 0.5 ug-at NH4/1. Kinetic data
32
-------
deri ved from the Ve segment of the uptake curve for
silicate-limited populations yielded Vmax values of 0.18/hr
for ~ debilis, 0.10 for ~ costatum, and 0.03 for ~ gravida.
Ks was 2.2 ug at/l for ~ debilis, 1.3 for ~ costatum, and
0.3 for ~ gravida. In a number of parameters that were
measured, ~ gravida was clearly different from ~ debilis and
S. costatum and its recovery fran nutrieint starvation was the
slcwest. Recovery of all species from silicate limitation or
starvation was slower than fran anmonium lack.
2304.
Crossland, C.J. and D.J. Barnes. 1977. Calcification in
the staghom coral, Acropora acuminata: variations
in apparent skeletal incorporation of radioisotopes
due to different methods of processing. Marine
Biology 43:57-62.
Pieces of branch from A. acuminata were incubated for
one oour with 7.7 mCUrng Ca-45 C12 and 0.6 mCUmg NaHC-14 03
under identical conditions in light or in dark. After specunens
were processed in different ways, tissues were digested in 20 ml
N KOH. In both light and dark incubations, lowest radioactive
incorporations into skeleton were obtained from specimens killed
with liquid N2 and left in running seawater. Ca-45 values
were 230 dpm/rng protein in dark and 1320 in light regimes. The
highest value of Ca-45 incorporation under dark conditions was
1000 dpm/mg protein when specimens were placed directly in KOH;
this was 2730 under light conditions in methanol-
chloroform-water. Skeletal activity of C-14 followed similar
trends. Tissue activity of C-14 02 was low, 160 dpm/mg
protein, when washed in seawater in dark; this was 310 in
light. The highest value, when placed directly in KOH, was 2490
in dark and 2050 in light.
2305.
Cunningham, P.A. 1976. Inhibition of shell growth in
the presence of mercury and subsequent recovery of
juvenile oysters. Proc. Nat. Shellfish. Assn. 66:1-5.
Juvenile oysters, Crassostrea virginica, were exposed
for 12 hrs daily to 0.01 or 0.1 mg Hg/l as mercuric acetate for
47 days. Shell growth, used as an indicator of physiological
stress, decreased significantly by day 15 in both
concentrations. After 47 days, shell growth was reduced by 33%
in 0.01 and by 77% in 0.1 rnglHg/l. Oysters placed in seawater
for a depuration period of 162 days demonstrated shell growth
rates comparable to controls within 20 days for the 0.01 mg/l
group and 34 days for the 0.1 mg/l group.
33
-------
2306.
Cutshall, N.H., J.R. Naidu and W.G. Pearcy. 1977. Zinc
and cadmium in the Pacific hake Merluccius productus
off the western U. S. coast. Marine Biology
44: 195-202.
Mean levels of zinc and cadmium, respectively, in
sane northeast Pacific Ocean organisms in mg metal/kg wet wt
were: euphausiids Euphausia pacifica 13.0, ?23; p~nk shrimp
Pandalus jordani muscle 11.0, 0.060; whole plnk ShrlID~ 58.?,
0.020; flatfish 4.0, 0.017; myctophids 10.0, 0.060; vlperflsh
Chauliodus macouni 7.0, 0.098; sablefish Anoplopoma fimbria 4.0,
0.012; Pacific hake Merluccius productus muscle 4.0, 0.03; whole
Pacific hake 12.0, 0.12; Puget Sound hake muscle 6.0, 0.012; and
Puget Sound hake who le 15.0, 0.086. Zinc and cadmi um levels in
muscle tissue or wh:>le Pacific hake increased with increasing
total wet body weight, especially for smaller fish. These
trends seem to be related to the euphausiid diet of l1ake which
contains high amounts of both metals and also a high Cd:Zn
ratio. No relationship between zinc and cadmium concentration
and collection site was apparent for the isolated hake
population in Puget Sound.
2307.
Cutshall, N.H., J.R. Naidu, and W.G. Pearcy. 1977.
Zinc-65 specific activities in the migratory Pacific
hake Merluccius productus. Marine Biology 40:75-80.
Pacific hake, migrating northward along the
California coastline during sunmer, accumulate radioactive
zinc-65 associated with the southwesterly flowing plume of the
Columbia River. Smaller fish reflect this contamination in both
whole body and in muscle tissue earlier than larger fish. Fish
weighing 0.5 kg wet wt have a Zn-65 concentration, in pCi/g wet
wt whole fish, of about 0.3 at 410 32'N latitude and 0.55 at
430 23'N latitude, while fish weighing 1.25 kg have 0.2 and
0.45 respectively. Zn-65 specific activities increase toward
the north as far as 460N, off the mouth of the Columbia River,
then decline northward along the coast of Washington state. In
tissues and organs, Zn-65 concentrations in pCi/g ash, ranged
fran 145.5 in spleen and 110.5 in ovary to 1.6 in bone; total Zn
in mg/kg ash, ranged from 4290 in liver and 3060 in ovary to 150
in bone; specific activity in nCi Zn-65/g, ranged from 92.5 in
spleen to 10.7 in bone and 9.8 in skin.
2308.
Danell, K., A. Anderson, and V. Marcstrom. 1977. Lead
sh:>t pellets dispersed by hunters--ingested by
ducks. Ambio 6: 235-237 .
34
-------
Incidence of ingested lead shot pellets in 928 ducks
from nine species in Sweden during the hunting season was
determined. Species containing pellets were Anas platyrhynchos,
~ penelope, ~ acuta, Aythya ferina, Aythya fuligula, and
Bucephala clangula. Lead shot pellets were found in ducks from
six of the eight localities sampled. USLBlly one or two pellets
were present, but some ducks contained up to 62 pellets. As the
incidence of ingested pellets in this study is approximately
equal to that found in North America, where the annual duck loss
due to lead poisoning is estimated to be 2 to 3% of the
population, it may be assumed that lead poisoning is a factor in
mortality of Swedish ducks as well.
2309 .
Dawson, M.A., E. Gould, F.P. Thurberg and A. Calabrese.
1977. Physiological response of juvenile striped
bass, Marone saxatilis, to low levels of cadmium and
mercury. Chesapeake Science 18:353-359.
Juvenile bass were exposed to 0.5, 2.5, and 5.0 ug/l
of cadmium as cadmium chloride for 30 to 90 days or to 1.0, 5.0,
and 10.0 ug/l of mercury as mercuric chloride for 30 to 120
days. FollCMing the longest exposure to each metal, the fish
were allowed to recover for 30 days in running seawater.
Gill-tissue respiration, glucose-6-phosphatase, malic enzyme,
aspartate aminotransferase, and magnesium activation of AAT were
measured. Fish exposed for 30 days to 0.5, 2.5 and 5.0 ug Cd/l
consumed significantly less 02 than controls. Exposure to 5
ug Hg/l for 30 days decreased respiration to 1.096 ul 02/hr/mg
compared to 1.742 for controls. At 10 ug Hg/l respiration rates
were 0.97 after 30 days, 0.75 after 60 days and 0.94 after 120
days. There was no significant difference in enzyme activity
during exposure to either metal; however, fish held in Cd-free
seawater for 30 days following exposure to cadmium exhibited a
slight drop in liver AAT and G6PdH.
2310.
deFreitas, A.S.W., M.A.J. Gidney, A.E. McKinnon, and R.J.
Norstrom. 1977. Factors affecting whole-body
retention of methyl mercury in fish. In: Drucker,
H. and R.E. Wildung (eds.). Biologicalimplications
of metals in the environment. ERDA Symp. Ser.
42:441-451. Avail. as OONF-750929 from Nat. Tech.
Inf. Serv., U.S. Dept. Comm. Springfield, VA. 22161.
Efficiency of methylmercury assimilation from the
gastrointestinal tract of fish ranged from 71 to 92% of amount
35
-------
of food ingested. Northern pike Esox lucius, perch Perca
flavescens, brown bullhead Ictalurus-nebulosus, and ling Lota.
Iota were fed minnows injected with Hg-203 methyJroercury, whIle
red ~rse suckers Moxastoma spp., white suckers Catastomus
commersoni, and goldfish Carassius auratus, were given food
containing tracer methylmercury. Variation in assimilation
efficiency was not associated with food type, fish body size, or
species. A positive correlation was observed between dose rate
and retention index of methyJroercury, but whole-body retention,
using goldfish, was not affected by temperature or growth rate.
The equation relating clearance rate and fish body weight did
not appear to be species specific, and seemed to fit measured
levels of methyJroercury in yellow perch.
2311.
Dethlefsen, V. 1977. Uptake, retention, and loss of
cadmium by Crangon crangon. Inter. Coun. Explor.
Sea. Fish. Improv. Camm. C.M. 1977/E:12. 21 pp.
(mimeo) .
After first molt, shrimp were exposed to Cd
concentrations of 0.005-0.100 mg/l as CdC12 for up to 40
days. Uptake curves showed rapid accumulation during the first
3 days, followed by long-term linear accumulation of total body
load. In 0.005 mg Cd/I, Crangon accumulated 1.3 mg Cd/kg dry wt
after 3 days and 3.0 after 30 days. In 0.020 mg Cd/I, levels in
shrimp were 2.0 mg Cd/kg dry wt at 1 day and 7.0 at 30 days. Cd
concentration in exuvia of Crangon exposed until their second
molt was not significantly lower than whole organism. Retention
of Cd for 7-12 days was almost complete. After exposure for 20
days to 0.005 and 0.010 mg Cd/I, little change was seen 30 days
later in body concentration. After 20 days exposure to 0.020 mg
Cd/I, Cd levels dropped from 5.5 to 4.5 mg/kg dry wt by 27
days. Crangon from the Elbe estuary in 1975-1977 contained 0.4
to 1.1 mg Cd/kg dry wt; natural levels of Cd in water averaged
0.0001 mg/I.
2312.
Dethlefsen, V., H. V. Westernhagen, and H. Rosenthal.
1975. Cadmium uptake by marine fish larvae. Helgol.
wiss. Meeresunters. 27: 396-407.
Eggs ?f herring Clupea haren~s, flounder Platichthys
flesus, and garpIke Belone belone, were Incubated in 0.05-5.00
mg Cd/I at 15.7-320/00 salinity and 10 C. Newly hatched larvae
were analyzed for Cd content. Cadmium residues in larvae were
dependent on Cd concentrations employed during incubation. Cd
36
-------
levels in newly hatched flounder and herring larvae, at 7.0 to
23.0 mg Cd/kg dry wt, were 100X higher than in garpike larvae
under the same conditions, at 0.017-0.019 mg/kg. Cadmium
content of herring larvae increased to a maximum of 480 mg/kg
dry wt after 8 days in 0.4 mg Cd/I; in flounder larvae it was 58
mg Cd/kg dry wt after 8 days in 0.5 mg Cd/I. After 34 days in
0.05 mg Cd/I, garpike larvae contained 0.097 mg Cd/ kg dry wt,
significantly higher than controls. No detrimental effects were
shown for garpike larvae grown in up to 2.0 mg Cd/l for about 30
days.
2313.
Dorn, P. 1974. The effects of mercuric chloride upon
respiration in Congeria leucophaeata. Bull. Environ.
Contamin. Toxicol. 12:86-91.
Respiration rates of the marine bivalve mollusc C.
leucophaeata were measured after exposure for 48 h to 0.001~
0.01, 0.1, 1.0 or 10 mg mercury/l as HgC12. Mean respiration
rates in ml 02/g/hr, were respectively: 1.6 (controls); 1.9;
2.4; 2.7; and 2.9 (1.0 mg Hgll). There were no survivors at 10
mg Hg/l; 80% survived 1.0 mg/l; no deaths were recorded at lower
concentrations after 48 h. Departure of respiratory rates from
controls was significant at Hg concentrations above 0.01 mg/l.
Mercury binds to membranes altering ionic distribution and
osmoregulatory activity and this may account for increased
respiratory rates in Congeria.
2314.
Draggon, S. 1977. Interactive effect of chromium
compounds and a fungal parasite on carp eggs. Bull.
Environ. Contamin. Toxicol. 17:653-659.
Effects of hexavalent and trivalent chromium
compounds on a fungal parasite, Saprolegniales, and carp egg
hatchability were reported at levels of 0.1, 0.3, 1.0, 3.0,
10.0, 15.0, 20.0 and 30.0 mg Cr/l for 6 day periods. Sodium
chromate inhibited egg hatching at 0.1 and 0.3 mg Cr/l and
stimulated hatching at all higher levels. Both chromium acetate
and chromium chloride inhibited hatching at 0.1 to 3.0 mg/l,
while higher concentrations were lethal. Sodium chromate
stimulated fungal growth at 0.1 and 0.3 mg/l, but higher Cr
levels inhibited growth. Fungal growth was stimulated by the
three lowest levels of chromium acetate, significantly at 0.1
mg/l; growth decreased at 20.0 and 30.0 mg/l and was
significantly lower at 3.0, 10.0 and 15.0 mg/l. Chromium
chloride stimulated fungal biomass at 0.1 to 3.0 mg/l;
37
-------
concentrations of 10.0 to 30.0 mg/l inhibited growth.
Comparison of data revealed that increased egg mortality and
increased ftIDgal growth were coupled at 100 Cr concentrations.
A mechani3ll for interaction of chemical and biological stress on
carp egg survival in natural systems is presented.
2315.
Drescher, H.E., U. Harms, and E. Huschenbeth. 1977.
Organochlorines and heavy metals in the harbour seal
Phoca vi tulina fran the German North Sea Coast.
Marine Biology 41:99-106.
Tissues of healthy, sick, and dead ~ vitulina from
North German Waddensea were analyzed for heavy metals and
organochlorines. Cadmium concentrations ranged from 0.01 to
0.20 mg/kg wet wt in liver, 0.002 to 0.024 in brain, and 0.06 to
0.38 in kidney. Copper ranged from 2.6 to 17.0 mg/kg wet wt in
li ver and about 2.3 to 4.0 in both brain and kidney. Lead
concentrations were 0.10 to 0.57 mg/kg wet wt for both kidney
and liver, and 0.20 to 0.04 in brain. Amounts of total mercury
were 1.5 to 160.0 mg/kg wet wt in liver, 1.6 to 12.5 in kidney,
and 0.11 to 1.4 in brain. Zinc concentrations ranged from 27.0
to 56.0 mg/kg wet wt in liver, 16.3 to 32.5 in kidney, and 10.8
to 15.0 in brain. Cadmium, Hg, and Pb levels increased with age
of the individuals. DDT concentrations ranged from 2.2 to 27.2
mg/kg wet wt in blubber; kidney, li ver, and brain all had <0.6
mg/kg. PCB content ranged from 27.3 to 564.0 mg/kg wet wt in
blubber, 0.2 to 2.9 in brain, 0.06 to 2.70 in liver, and 0.18 to
1.22 in kidney. Lindane and Dieldrin both ranged from 0.04 to
0.98 mg/kg wet wt in blubber. Brain, liver, and kidney all had
< 0.002 mg/kg. No relationship with age and pesticide levels
was found, since even young seals were contaminated. There was
no clear evidence that concentrations of any compound had
negative effects on health of the seals; however, possible
combined effects cannot be exluded.
2316.
Eisler, R. 1977. Acute toxicities of selected heavy
metals to the softshell clam, ~ arenaria. Bull.
Environ. Contamin. Toxicol. 17:137-145.
Static acute toxicity bioassays with adult softshell
clams and salts of copper, cadmium, zinc, lead, manganese, and
nickel were conducted at 30 0/00 salinity and 22 C.
Concentrations fatal to 50% in 168 hrs, in mg/l (ppm) metal
added at start, were 0.035 for Cu, 0.150 for Cd, 1.55 for Zn,
8.80 for Pb, 300.0 for Mn, and> 50.0 for Ni. Additional tests
38
-------
were conducted with Zn2+ and Cu2+ at 30 0/00 during fall
(17.5 C) and winter (4 C); clams displayed increasing survival
wi th decreasi ng temperature. For Cu, LG-50 <336 hr) values at
17 C and 4 C were 0.086 and >3.00 mg/l,respectively; for Zn
these were 2.65 and >25.0, respectively.
2317.
Eisler, R. 1977. Toxicity evaluation of a complex metal
mixture to the softshell clam ~ arenaria. Marine
Biology 43:265-276.
Adults of the softshell clam were continuously
subjected to a flowing raw seawater solution containing a
mixture of salts of manganese, zinc, lead, nickel, copper, and
cadmium. Final calculated concentrations, in ug/l, of the
toxicant solution were 7200 Mn, 2500 Zn, 70 Pb, 50 Ni, 50 Cu and
1 Cd. These concentrations approximated highest measured levels
within surficial interstitial sediment waters from
mid-Narragansett Bay, Rhode Island. M. arenaria were also
subjected to a 20% solution, i.e., 1440 Mn, 500 Zn, 14 Pb, 10
Ni, 10 Cu, and 0.2 ugll Cd. One study was conducted for 112
days in winter at 0 to 10 C, and another for 16 days in surmner
at 16 to 22 C. In the winter study, all clams exposed to a 100%
solution died between the 4th and 10th week; soft parts of
survivors at 6 wks contained about 19 times more Pb (13.3 mg/kg
wet wt), 15X more Zn (140.5 mg/kg), 12X more Cu (24.6 mg/kg),
10X more Mn (66.0 mg/kg), 3X more Ni (1.2 mg/kg wet wt), and
0.1X more Cd (3.6 mg/kg wet wt) than controls. Relatively minor
changes in whole body elemental content of Ca, Cr, Fe, K, Mg,
Na, Sr, and V were observed. Clams exposed to a 20% solution
during winter survived the 112 day study and contained about 5X
more Cu, 4X more Mn, 3X more Zn and about 2X more Pb than
controls; comparatively minor changes were observed in other
elements examined. In the sumner study, all M. arenaria
subjected to the 100% solution died between 6and 14 days.
Survivors from this group at 7 days contained about 25X more Pb,
13X more Cu, 11 X more Zn, 7X more Mn, and 3X more N i than
controls; other changes in elemental content were not as
pronounced. Mortality in the 20% group during sumner was
slightly higher than controls during the 16 day study; at 14
days survivors fran this group contained about 12X more Mn, 7X
more Pb, 7X more Zn, 4X more Cu, and 3X more Ni than controls.
Survival and bioaccumulation patterns in ~ were not altered
through feeding a supplemental diet of algae. Results of 14 day
static acute toxicity bioassays with the metal mixture at 4 C
demonstrated that softshell clam, quahaug clam Mercenaria
mercenaria and mahogany clam Arctica islandica were up to 3X
39
-------
more resistant than killifish Fundulus heteroclitus and up to 10X
more resistant than rock crab Cancer irroratus. The significance
of these findings are discussed in terms of potential
environmental perturbations, especially local dredging practices.
231~.
Eisler", R. and R.J. Hennekey. 1977. Acute toxicities ot'
Cdc+, Cr+6, ~+, Ni2+, and Zn2+ to estuarine macro-
fauna. Arch. ~viron. Contamin. Toxicol. 6:315-323.
~tatic acute toxicity bioassays were conducted at 20 C
and 20 0/00 salinity with CdC12'2~H20, K2CrOq, HgC12' N~C12.6R20
and ZnC12 using adults of starfish Asterias forbesi, sandworm
Nereis virens, hermit crab Pagurus longicarpus, softshell clam
Mya arenaria, mudsnail Nassarius obsoletus, and munmichog
Fundulus heteroclitus, a fish. Concentrations (mg/l metal) fatal
to 50% of the organisms in 16~ hr ranged from O.OO~ (clam) to O.~
(mummichog) for mercury; 0.7 (clam, worm, crab and starfish) to
qo.o (murrmichog) for cadmium; 0.2 (crab) to 52.0 (munmichog) for
zinc; 0.7 (sandworm) to ~q.o (murmnichog) for hexavalent chromium;
and 13.0 (starfish) to 150.0 (murrmichog) for nickel. Biocidal
action was restricted to a relatively narrow range for all
species-metals combinations tested: i.e. mean LC-75/LC-25 ratios
for individual metals at 16~ hr ranged between 2.~2 (Zn) and 6.02
(Cd); for individual species this ratio extended from 2.76 (fish)
to Q.q6 (clam). It appears that acute toxicity evaluation of
potentially hazardous metals in saline environments requires
utilization of at least several representative species from
divergent taxonomic categories and ecological niches.
2319.
Eisler, R., D.J. O'Neill, Jr. and G.W. Thompson. 197~.
Third annotated bibliography on biological effects of
metals in aquatic environments. (No. 1293-22Q6).
U.S. Environ. Proto Agen. Rept. bOO/3-7~-005: ~~7
pp. Avail. from U.S. Dept. Comn., Nat. Tech. Inform.
Serv., Springfield, VA. 21161.
'l'i ties of 9:>Q technical articles are listed on the
subject ot' 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 the present
~O
-------
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. Environ. Proto Agen.
Rep. R3-73-007: 2~7 pp; ~isler, R. and M. Wapner. 1975.
Second annotated bibliography on biological effects of metals in
aquatic environments (No. 5~-1292). U.S. Environ. Proto Agen.
Rept. 600/3-75-00~: 400 pp.).
2320.
Elder, J.t". 1977. Iron uptake by freshwater algae and
its diel variation. In: Drucker, H. and R.E.
Wildung (eds.). Biological implications of metals in
the environment. ERDA Symp. Sere 42:346-357. Avail.
as CON1"-750929 from Nat. Tech. In!'. Ser'v., U.S. Dept.
Corrm., Springfield, VA. 221b 1.
A mixed algal corrmunity of primarily Aphanizomenon,
Staurastrum, and Fragilaria increased its chlorophyll content
from 65% to 150% of control values over 6 days in 0.01 mg
iron/l. Primary productivity, as measured by C-14 uptake, was
200% of controls after 1 day in 0.01 mg 1"e/l, 1CSO% in 0.01 mg
Fell and 1.0 uM ED'l'A, and 120% in 1.0 uM EDTA alone. Total
dissolved iron in Lake Perris, California, reached a maximum of
almost 0.03 mg/l at a depth of 4-~ m at 1:00 AM, in both
!:,'ebruary and June. Maximum Fe uptake by algae was also at 1 :00
AM in June at the lake surface and at CS m depth. At CS: 00 PM,
uptake was only 5-10%. Author postulates that at daybreak,
dissolved iron is rapidly accumulated by algal cells, resulting
in a decrease of Fe in the lake. Fe uptake drops sharply in the
morning and then more gradually throughout the day. At sunset,
Fe is released by algal cells, increasing P'e levels in the
water; potential for iron uptake increases so that the uptake
cycle repeats itself at daybreak.
2321 .
Elder, J.t". and A.J. Horne. 1977. Biostimulatory
capacity of dissolved iron for cyanophycean blooms in
a nitrogen-rich reservoir. Chemosphere 6:525-530.
Total dissolved iron, in mg/l, in Lake Perris,
California was determined. Between February and September,
1975, Fe ranged between 0.015 and 0.025 mg/l in March and early
April at depths up to 16 m and was
-------
that of controls on days 1 and 4, as measured by C-14 uptake. N
and P addition alone only increased productivity 125%.
Chlorophyll amounts increased to 220% on day 6, after initial
decline to 70%, with Fe, N, and P additions. N and Palone
smwed chlorophyll increases to 150%. Abundance of the
blue-green algae Aphanizomenon flos-aquae increased to 0.4
mm3/1 from 0.08, 5 days after adding Fe, N, and P; N and P
showed no increase. Number of heterocysts also increased in Fe,
N, and P. Algal counts showed that influence of iron was
prlinarily on blue-green algae, and this accounted for
chlorophyll and productivity increase in the entire
phytoplankton community.
2322.
Enk, M.D. and B.J. Mathis. 1977. Distribution of
cadmium and lead in a stream ecosystem.
Hydrobiologia 52:153-158.
Cadmium and lead concentrations were measured in
aquatic insects, teleosts, snails, water and sediments from an
impacted freshwater stream. Concentrations of both metals
increased from water fish sediments invertebrates.
Measured Cd and Pb concentrations in selected species follow.
Lead, in Cadmium, in
mg/ kg wet wt mg/ kg wet wt
Aquatic Insects
M9.yflies
Isonychia sp.
Damselflies
Agrion sp.
Caddis flies
Cheumatopsyche sp.
Hydropsyche sp.
6.83 1. 19
12.59 1.54
11.00 0.81
6.85 0.53
2.55 0.08
2.88 0.15
2.47 0.10
13.64
8.30 0.14
0.5 < 0.02
Fishes
Carpiodes carpio
Etheostoma flabellare
Micropterus dolomieui
Snails
Physa sp.
Sedlinents
Water (mg/l)
2323.
Fargo, L.L. and R.W. Fleming. 1977. Effects of chromate
and cadmi um on most probable number estimates of
nitrifying bacteria in activated sludge. Bull.
42
-------
Environ. Contamin. Toxicol. 18:350-354.
Most probable number (MPN) estimates of two species of
bacteria from activated sludge samples at sewage treatment
facilities were made in media containing several concentrations
of K2Cr04 or CdC12. Nitrosomonas populations from both San
Jose Creek and Whittier Narrows were reduced in 1.0 mg
K2Cr04/kg to 0.01 x 105/ml and in 10.0 mg/kg to 1.0-3.0/ml,
from control values of 1.4-7.9 x 1Q5/ml. Concentrations of
0.01 and 0.1 K2Cr04 had little effect on growth. CdC12 did
not cause significant inhibition of Nitrosomonas at 0.1, 1.0,
10.0, and 100.0 mg/kg. MPN reduced from 1.4-7.9 x 105 to
0.49-1.10 x 105/ml as Cd levels increased. Nitrobacter from
both sites was not inhibited significantly in up to410 mg
K2Cr04/kg, as MPN ranged from 1. 3 x 105 to 2.3 x 10 over
experimental concentrations. In CdC12, bacteria numbern
decreased slittly, from control values of 3.3-7.0 x 10 to
0.46-1.3 x 10 in 100.0 mg Cd/kg.
2324.
Farmer, G.J., J.A. Ritter, and D. Ashfield. 1978.
Seawater adaptation and parr-smolt transformation of
juvenile Atlantic salmon, $almo salar. Jour. Fish.
Res. Ed. Canada 35:93-100.
Presrnolts and smolts, 1 and 2 year old salmon, adapted
to seawater equally well as salinity was increased from 0.1 to
31.0 0/00; marine osmoregulatory mechanisms apparently function
before the completion of parr-smolt transformation. Adaptation
was possible for parrs exceeding 12-13 cm fork length. As
salinity increased to 31 0/00, osmolarity of urine increased from
about 50 to 300 mOsm/l, and serum and intestinal fluid rose from
about 300 to 350 mOsm/l in juvenile salmon 2>- 14 cm; in 31 o/ooS,
serum and intestinal fluid of parr were about 450 mOsm/l. Timing
of transformation for 1 and 2 yr old juveniles was synchronous,
as sho\~ with lipid and moisture content and condition factor
(K). A decrease of K factor and lipids in salmon from New
Brunswick resulted in maximum migratory activity in mid-May, and
at a slightly earlier date in Nova Scotia. Smolt-release dates
are discussed with development of marine osmoregulatory
mechanisms and timing of parr-smolt transformations.
2325.
Flegal, A. R. 1977. Mercury in the seston of the San
Francisco Bay EstU3.ry. Bull. Environ. Contamin.
Toxicol. 17:733-738.
Seston of three sizes (20 urn, 76 um, and 366 urn) from
43
-------
San Francisco Bay estuary were analyzed for total mercury.
Levels of mercury in the 20 um seston sample ranged from 0.22 to
3.7 mglkg dry weight; the range in 76 urn seston was 0.0~-13.3;
and was 0.09-1.1 in the 366 um seston. Mercury levels ln seston
varied temporarily, spatially with size, and with organic.
content, and appear to be higher in phytoplankton andlor organlc
detritus than in zooplankton.
2326.
Flegal, A.R. and J .H. Martin. 1977. Contamination of
biological samples by ingested sediment. Marine Poll.
Bull. 8:90-92.
An inorganic residue, presumed to be ingested
sediment, was found in the gastropods Tegula funebralis and
Acmaea scabra and copepods Acartia tonsa and !. clausi.
Expressed as a percentage of sample weight, residue fraction
correlated positively and significantly with iron, manganese, and
titanium in T. funebralis and iron and manganese in A. scabra
from the CalIfornia and Mexico coast. Correlations between
residue fraction and Ag, Cd, Cu, Ni, Sr, and Zn in these two
species varied from highly significant negative correlations at
some collection sites to highly positive correlations at others.
Because inorganic matter correlated significantly with elemental
composition of marine invertebrates in several cases, authors
suggest that this should be considered during chemical analysis
of marine organisms.
2327.
Foster, P. L. 1977. Copper exclusion as a mechanism of
heavy metal tolerance in a green alga. Nature
269 :322-323.
Chlorella vulgaris from the River Hayle, England,
where copper is found at 0.12 mg/l, showed decreased growth as
copper concentration increased to 1.0 mg/l as CuS04' At 1.0
mgll growth was 100 but not zero. Growth of a non-tolerant
strain of Chlorella from unpolluted waters, i.e. <0.002 mg Cull,
was arrested in as little as 0.05 mg Cull, and was completely
inhibited in 0.30 mg/l. At 0.25 mg Cull, non-tolerant Chlorella
accumulated about 0.11% dry wt as copper while tolerant Chlorella
contained about 0.01%; at 1.0 mg Cull, tolerant strains
accumulated only 0.08% dry wt. The relation between decreasing
growth rate and increasing amount of copper as % dry wt was
identical for both strains of Chlorella, implying that they
respond similarly to the same amount of cellular Cu. It was
concluded that Cu exclusion was the only mechanism of tolerance
in this alga.
44
-------
2328.
Fowler, S. W. 1977. Trace elements in zooplankton
particulate products. Nature 269:51-53.
Whole bodies of euphausiids, Meganyctiphanes
norvegica, from surface waters off Monaco contained high levels
of Sr at 117 mg/kg dry wt, Fe at 64, Zn at 62 and Cu at 48
mg/kg. Amounts of Se, Mn, Pb, Cr, Cd, Ag, Ni, Hg, Ce, Co, Sb,
Cs, So, and Eu, in descending order, were all <4.5 mg/kg dry wt.
Maximum concentrations in moults were generally higher, at 350
mg/kg dry wt for Sr, 232 for Fe, and 146 for Zn; Pb was 22 mg/kg,
Ni was 6.7, and Sb 0.8. Fraction of body burden contained in
moul ts for these elements was as follows: Pb about 150%, Sb 87%,
Ni 78%, Fe 28%, Sr 23%, and Zn 18%. Iron and zinc were high in
euphausiid eggs with 330 mg Fe/kg dry wt and 318 mg Zn/kg. In
faecal pellets, maximum amounts of metals were 24,000 mg Fe/kg
dry wt, 950 for Zn, 243 for Mn, 226 for Cu, and 200 for Ce; all
others were <80 mg/kg dry wt. Faecal pellets contained
significantly higher levels of each element than whole
euphausiids, except for Sr, Hg, and Sc. Metal levels in
microplankton, consisting of copepods, chaetognaths,
phytoplankton, and detritus, were 570 mg Fe/kg dry wt, 520 for
Sr, 483 for Zn, and <20 mg/kg dry wt for remaining metals.
Concentration ratios in pellets from the microplankton diet were
high for non-biologically essential elements such as Ce, Cs, Sc,
Sb, and Eu; high concentration of Fe may be due to ingestion of a
form not easily assimilated. Flux rate by euphausiids due to
faecal pellets was 910 mg/kg euphausiid per day for Fe, 36 for
Zn, and 9.2-1.4 for Ce, Cr, Cu, Mn, Pb, Sb, and Sr; other metals
were <0.8 mg/kg per day. Flux rate due to moults was much lower
for all metals except Sr at 3.2 mg/kg/euphausiid/day.
2329 .
Frederick, R.B. 1976. Effects of lead nitrate ingestion
on open-field behavior of mallard ducklings. Bull.
Environ. Contamin. Toxicol. 16:739-742.
Nine day-old mailard ducklings were fed a diet
consisting of 5.0, 50.0 or 500.0 mg/kg lead as lead nitrate and
duckling movements were measured 3 or 8 days later. Differences
in open-field perfcrmances were insignificant. Mean percentage
weight gains of ducklings after eight days of treatment were: 182
for controls; 158 at 5.0 mg Pb/kg; 190 at 50 mg/kg and 191 at 500
mg/kg.
2330.
Friedrich, A.R. and F.P. Filice. 1976. Uptake and
accumulation of the nickel ion by MYtilus edulis.
45
-------
Bull Environ. Contamin. Toxicol. 16:750-755.
Uptake and accumulation of nickel by mussels during
exposure for 4 weeks was measured in synthetic seawater
containing 0.013,0.025,0.051, or 0.102 mg Ni/l. At 0.018 and
0.03 mg Ni/l, uptake and accumulation was not significantly
different from controls. In groups exposed to 0.056 and 0.107 mg
Ni/l, nickel levels in tissue were approximately 33 and 41 mg
Ni/kg dry wt, respectively. Some mussels died during the four
week experiment but m correlation with increasing Ni
concentration was established. An additional 96 hr study was
conducted in Ni concentrations of 20, 40, and 80 mg/l; mussels
were not fed during this experiment. No animals died during the
96 hr exper iment. Analysis of soft tissue after a 96 hr exposure
to 20, 40 and 80 mg Ni/l showed nickel levels of approximately
420, 450 and 820 mg Ni/kg dry wt, respectively. Nickel uptake
may occur through mucus sheet or via transmembrane absorption.
2331. Fuller, R.H. and R.C. Averett. 1975. Evaluation of
copper accumulation in part of the California
Aqueduct. Water Res. Bull., Amer. Water Res. Assoc.
11:946-952.
Copper sulfate has been used extensively in the
California Aqueduct to control phytoplankton and the alga
Cladophora; since 1969 more than 110,000 kg have been added.
Analysis of water showed m significant increase of copper in the
treated area over untreated water. Twenty-four samples
contained <10 mg Cull, 3 other sites had Cu concentrations of 20,
30, and 50 mg/l. Sediments from treated areas contained 59.7 mg
Cui kg dry wt compared to 29.8 mg/ kg in controls, or about a 100%
increase. Mean copper concentrations in 5 species of freshwater
algae fran treated sites increased 200%, ranging from 19 to 47
mg/kg dry wt; in untreated areas, levels were 8-15 mg/kg. The
clam Corbicula showed a 68% increase of Cu in tissues from
controls of 56.4 mg/kg dry wt to 94.8 mg/kg from areas where
CuS04 was added. Shells of clams contained 13.1 mg Cu/kg dry
wt, a 39% increase over 9.4 mg Cu/kg found in untreated areas.
Copper levels in the snail Helisoma from treated sites were 41.5
mg/kg dry wt, a 77% jncrease over control values of 23.5 mg/kg.
Authors state that none of the concentrations found were
considered harmful to biota.
2332.
Galtsoff, P.S. and V.L. Loosanoff. 1939. Natural history
and method of controlling the starfish (Asterias
46
-------
forbesi, Desor).
(31 ) : 75 - 132 .
Bull. U.S. Bur. Fish. XLIX
Copper sulfate and other chemicals were tested for
starfish population control. Groups of five starfish in 240/00
S took 0.1 to 3 min to die in 1,000 mg Cu304/1, 0.25 to 5 min
in 500 mg/l, 1.0 to 35 min in 100 mg/l, 1.3 to 75 min in 50 mg/l,
3 to 110 min in 20 mg/l and 5 to 150 min. in 10 mg/l. No effect
was smwn in 1.0 or 5.0 mg Cu 304/1 for 24 hrs. Tolerance to
Cu increased as starfish size increased. Three starfish were
used with one oyster per tank in a second test for practical
purposes of starfish control in nature. After 7 days in 0.07 mg
CuS04/1, all were alive. Tw::> starfish and the oyster died by
day 7 in 0.15 mg/l, all starfish died by day 5 and the oyster on
day 6 in 0.31 mg/l; all starfish by day 2 and the oyster on day 3
in 0.62 mg/l, and all starfish by day 1 and the oyster on day 2
in 1. 25 mg CuS04/l. With 150 mg zinc sulfate in 2 cu ft tanks,
starfish turned aborally were unable to right themselves after 1
day; one of the five died on day 5. Various chromium salts,
ranging in concentration from 0.08 to 10.0 mg/l, had little
effect on starfish. Calcium oxide, at 300 Ibs/acre of bottom in
experimental tanks killed all starfish within 5 to 10 days. On
25 acres of starfish-infested oyster beds, treated with 480 Ibs
calcium oxide/acre, up to 80% of starfish were effected by skin
lesions 1 week after application.
2333.
Gentner, S.-R. 1977. Uptake and transport of iron and
phosphate by Vallisneria spiralis L. Aquatic Botany
3:267-272.
Using Fe-59 and P-32 as tracers, uptake and transport
of ircn and phosphate fran the medium by roots and tissues of the
vascular freshwater aquatic plant ~ spiralis were studied.
Fe-59 levels in shoots varied from 0.9 to 48.5 x 103 cpm/gm wet
wt when water Fe ranged from 0.03 to 0.63 x 103 cpm/ml.
Maximum concentration factor of plant to water was 96 for roots.
Roots accumulated more iron than shoots. Fe levels in roots
varied from 3.3 to 49.1 x 103 cpm/gm wet wt, with concentration
factors up to 152. Phosphate was taken up equally by roots and
smots. Transport within the plants occurred principally in the
tissue to root direction.
2334.
George, S.G. and R.L. Coombs. 1977. The effects of
chelating agents on the uptake and accumulation of
cadmium by Mytilus edulis. Marine Biology 39:261-268.
47
-------
Uptake, storage, and excretion of cadmium by mussels
was studied at sub-lethal concentrations using Cd-115m as a
marker. Maximum accumulation of Cd in soft tissues was 0.018
mg/kg dry wt at 1500 ug/l CdC12 in seawater after 5 days. The
concentration factor (mg/kg in tissue divided by mWl in medium)
was highest, 1.7 x 10-2, at 700 ug/l Cd in water. Accumulation
of Cd by mussels exposed to 200 ug CdC12/l over 20 days showed
a high concentration factor of 3.75 x 10-3 in kidney, while
visceral mass, gills, mantle, and muscle were much lower; ratios
were approximately 44:11 :10:4:2. Exposure for 21 days to 100 ug
Cdll as complexes with EDTA, alginic acid, humic acid, or pectin
soowed all with a rate of accumulation into each tissue twice
that of CdC12 in seawater. During cadmium accumulation in 200
ug CdC12/l for 20 days, there was a marked decrease of iron in
mantle, a slight decrease of copper in viscera, and slight
increases of iron, copper, and zinc in muscle, and of copper in
gills. After exposure to 100 ug CdC12/l for 2 days, mussels
lost linearly up to one third of the absorbed cadmium over the
next 11 days; excretion rate was 18 times slooer than uptake rate.
2335.
Gergely, A., K. So'os, L. Erd~lyi and V. Cieleszky. 1977.
Determination of mercury in fish from rivers and lakes
in Hungary by atomic absorbtion technique. Toxicology
7:349-355.
Mercury levels in muscle from 9 species of fish
collected fran all important rivers and lakes in Hungary averaged
0.36 mg Hg/kg wet wt. Average levels of different samples ranged
from 0.10 mg Hg/kg for bass Aspius rapax, to 0.57 for pike-perch
Lucioperca sandra. Fish from the Danube River contained an
average of 0.59 mg Hg/kg wet wt; fish fran all other sites
contained < 0.50 mg Hg/kg wet wt.
2336.
Gibson, V.R. and G.D. Grice. 1977. Response of
macro-zooplankton pOpllations to copper: controlled
ecosystem pollution experiment. Bull. Marine Science
27 : 85-91 .
Fluctuations in planktonic abundance and species
composition of coelenterates, ctenophores, annelids, crustaceans,
48
-------
molluscs, chaetognaths, phoronids, echinoderms, tunicates, and
fish in Controlled ExperimEntal Ecosystems (CEE) were studied in
copper concentrations of 0.005, 0.01, and 0.05 mg/l. Abundance
of zooplankton was reduced by 82 to 99% in all CEE's, including
controls. A portion of the population decline was attributed to
grazing by carnivorous ctenophores and medusae, making it
difficult to quantitatively assess Cu effects. Abundance of
ctenophores and medusae remained at 150-400/m3 in controls,
while falling below 100/m3 after 22 days in 0.005 mg Cull,
indicating that these organisms are adversely affected by Cu
concentrations tested. At 0.05 mg Cull, Pseudocalanus sp. and
Acartia longiremis were reduced to 50% of their original numbers
3-3.5X faster than in controls. Results in 0.005 and 0.01 mg
Cull were more variable and less significant. It is not known
whether these effects were the direct result of Cu on the
organisms, or an indirect result of alterations at lower trophic
levels.
2337 .
Giesy, J.P., Jr., G.J. Leversee and D.R. Williams.
Effects of naturally occurring aquatic organic
fractions on cadmium toxicity to Simocephalus
serrulatus (Daphnidae) and Gambusia affinis
(Poeciliidae). Water Research 11:1013-1020.
1977 .
Cadmium toxicity to daphnids and teleosts in soft well
water containing various sized organic fractions isolated from
pond water was determined, and compared to Cd binding capacity of
each water type. Cadmium was bound by Skinface Pond water and by
organic fractions isolated from Skinface Pond water, reducing
amount of free Cd2+ as determined by Cd selective ion
electrode. Cadmium was toxic to both S. serrulatus and G.
affinis. The LC-50 (48 hr) in well water for S. serrulatUs was
7.0 ug/l. Cadmium binding capacities of soft highly organic
waters studied here were sufficienty great to affect acute Cd
toxicity to S. serrulatus but not G. affinis. The three larger
organic fractions isolated from Skinface Pond water reduced Cd
toxicity to S. serrulatus, while the smallest fraction slightly
increased toxicity though it exhibited greatest binding
capacity. Cadmium LC-50 values for ~ serrulatus and ~ affinis
could not be predicted from Cd binding capacities. While Cd
binding capacity has little effect on acute toxicity of Cd to ~
affinis, it may have greater effect on chronic Cd toxicity and
Cd uptake by fish.
49
-------
2338. Giesy, J.P., Jr. and J.G. Wiener. 1977. Frequency
distributions of trace metal concentrations in five
freshwater fishes. Trans. Amer. Fish. Soc.
106:393-403.
Whole body concentrations of Cd, Cr, Cu, Fe, and Zn
were determaned for samples of chain pickerel Esox niger,
bluegill Lepomis macrochirus, blueback herring Alosa aestivalis,
brook silverside Labidesthes sicculus, and golden shiner
Notemigonus crysoleucas collected near Aiken, North Carolina.
Mean concentrations of Cd ranged from 0.08 to 0.29 mg/kg dry wt
for the five species, Cr from 0.09 to 0.28 mg/kg, Cu from 1.84 to
5.56 mg/kg, Fe from 130.9 to 149.3 with a low of 39.9 mg/kg in
pickerel, and Zn from 101.8 to 232.9 mg/kg dry wt. Species
differences in mean concentrations of each metal were compared to
normal, lognormal, Weiball, and exponential distributions.
Authors concluded that in most cases either the normal
distribution, as exhibited by the known required elements Cu, Fe,
and Zn, or lognormal, as shown by Cd and Cr, may be
satisfactorily employed as statistical models of frequency
distributions of trace metal levels in fish.
Gillespie, R., T. Reisine, and E.J. Massaro. 1977.
Cadmium uptake by the crayfish, Orconectes P~~Pi~~UUS
propinquus (Girard). Environ. Research 13:3 -3 .
Freshwater crayfish were exposed at 11 C to 10, 100,
and 1000 ug/l Cd containing 0.09 uCi/l Cd-109 for 1, 4, 10, 22,
46, 94, and 190 hrs. At 10 ug/l, whole body Cd residues up to 94
hrs were essentially the same. By 190 hrs, crayfish in the 10
ug/l group had accumulated 18.4 mg/kg Cd wet wt, which was
significantly higher than concentrations accumulated during
shorter exposures. At 100 ug/l, Cd uptake at 1 hr was
significantly looer than groups exposed for 22-190 hrs; uptake at
4.5 hrs was less than the 94 and 190 hr groups; and uptake in the
10 hour exposure group was less than the 190 hr group. At 1000
ug/l uptake increased with time and was significantly greater at
every time interval monitored; by 190 hrs, these crustaceans had
accumulated a mean Cd concentration of 534 mg/kg. For all time
intervals at 1000 ug/l, Cd uptake was significantly higher than
the 100 and 10 ug/l concentrations; uptakes at 100 and 10 ug/l
were not significantly different.
2339.
2340.
Goering, J.J., D. Boisseau, and A. Hattori. 1977.
Effects of copper on silicic acid uptake by a marine
50
-------
phytoplankton population: controlled ecosystem
pollution experiment. Bull. Marine Science 27:58-65.
Effect of added copper concentrations of 0.0025,
0.005, 0.010, or 0.025 mg/l, for 1 to 6 days on silicic acid
uptake by natural populations of phytoplankton was studied. In
general, Cu inhibited uptake. At 25 mg Cull, uptake ranged from
49-98% of control values, with a mean of 60%. Rates of Si-30
(OH)4 uptake were 0.0039-0.0055 mg atoms Si/1/24 hr for
controls, and decreased to 0.0009-0.0015 as Cu concentrations
increased to 0.025 mg/l. Estimated rates of dissolution of
silica from phytoplankton cell walls in the presence or absence
of Cu were lCM, implying that exposure of siliceous phytoplankton
to Cu (up to 0.025 mg/l) does not significantly alter dissolution
rates.
2341 .
Gould, E. and J.J. Karolus. 1974. Physiological response
of the cunner, Tautogolabrus adspersus, to cadmium.
V. observations on the biochemistry. In: U.S. Dept.
COIIID., NOAA Tech. Rep. NMFS SSRF-681: 21=25.
Aspartate aminotransferase activity in liver from
cunner, a marine teleost, exposed to 3 and to 24 mg/l Cd for 96
hr was 71 % and 59%, respectively, of control values. Fish
exposed for 96 hr to 24 mg Cd/l required 20 roM magnesium to
activate nicotinamide-adenine dinucleotide; for controls 2 roM was
required. Authors suggest that a possible metal-complexing group
of proteins in serum of cadmium-exposed cunners warrants further
electrophoretic study.
2342.
Gould, E. and J.R. MacInnes. 1977. Short-term effects of
two silver salts on tissue respiration and enzyme
activity in the cunner (Tautogolabrus ads4~sus).
Bull. Environ. Contamin. Toxicol. 18:401- .
Oxygen consumption in the marine teleost ~ adspersus
decreased from control rate of 810 ml 02/h/kg dry wt gill
tissue to 637 and 599 when exposed to 0.5 mg silver/l as AgN03
and AgC2H302, respectively, for 96 hrs in 24 0/00 S at 22
C. Enzyme activity of aspartate aminotransferase in liver of
cunner decreased to 226 umoles NADH oXidized/min/mg protein in
0.5 mg AgN03/l for 96 hrs, and increased to 273 in 0.5 mg
AgC2H302/l. Neither value was significantly different from
controls at 252. Glucose-6-phosphate dehydrogenase activity in
liver decreased to 125 umoles NADP reduced/min/mg protein in 0.5
51
-------
mg AgC3H20'1/l for 96 hrs, and dropped significantly to 104
in 0.5 mg AgN03/l, from control activity of 14? .~uvate
kinase-activity in cunner skeletal muscle was lnhlblted by 0.004
mg/l cadmium chloride by 12.5% in controls, 19.1% in fish exposed
to 0.5 mg AgN03/l for 96 hrs, and 18.6% in fish exposed to 0.5
mg AgC2H302/1.
2343.
Greig, R.A., A. Adams, and D.R. Wenzloff. 1977. Trace
metal content of plankton and zooplankton collected
from the New York Bight and Long Island Sound. Bull.
Environ. Contamin. Toxicol. 18:3-8.
Nineteen collecting stations in the New York Bight
contained major percentages of comb jellyfish, rock crabs,
shrimp, or red hake in zooplankton collections. Trace metal
concentrations in zooplankton from these stations ranged from
<0.5 to 1.4 mg/kg dry wt for Ag, 1.2 to 2.6 for Cd, <3.3 to 35.2
for Cr, <1.6 to 54.4 for Cu, 1.7 to 4.6 for Ni, 10.1 to 81.0 for
Pb, and 9.9 to 625.0 for Zn. Concentrations, in mg/kg dry wt, of
trace metals in plankton from 11 stations in Long Island Sound
ranged from 0.5 to 0.7 for Ag, 1.5 to 1.8 for Cd, <1.1 to 4.7 for
Cr, <2.0 to 39.3 for Cu, 0.9 to 4.5 for Ni, 11.1 to 22.6 for Pb,
and 7.1 to 136.0 for Zn. Only one sample was speciated, and this
consisted mainly of copepods.
2344.
Greig, R.A., A.E. Adams and B.A. Nelson. 1974.
Physiological response of the cunner, Tautogolabrus
adspersus, to cadmium. II. uptake of cadmium by
organs and tissues. In: U.S. Dept. Comm., NOAA Tech.
Rep. NMFS SSRF-681:5-9.
Uptake and clearance data were obtained on a marine
fish exposed to various concentrations of cadmium as CdC12 . 2!
H20 in artificial seawater. In the uptake study, cunners were
exposed to 0, 3, 6, 12, 24 and 48 mg/l cadmium for 96 hrs. Liver
cadmium levels, in mg/kg dry wt, at the above concentrations were
5, 54, 119, 198, 390 and 761, respectively. Cadmium values in
gill tissue were 5, 16, 17, 31, 66, and 171, respectively. Mean
cadmium residues were 8.2 times higher in liver than gill.
Cadmium, in mg/kg wet wt, from organs and tissues of cunners
after exposure for 96 hrs to 24 mg Cd/l (and one month
post-treatment in natural seawater) were: 0.17 (0.12) in flesh;
8.1 (3.5) in gill; 6.6 (1.8) in red blood cells; 5.9 (1.5) in
serum; and 4.8 (3.5) in carcass. Cadmium in liver immediately
after exposure ranged from 30 to 117 mg/kg wet
52
-------
wt; those held one month in fla-ring seawater after exposure, had
5 to 11 mg/kg (3 fish) or 62 to 155 mg/kg (4 fish).
2345.
Greig, R.A. and D.R. Wenzloff. 1977. Trace metals in
finfish fran the New York Bight and Long Island
Sound. Marine Poll. Bull. 8: 198-200.
Metal concentrations in livers of the teleosts
Urophycis chuss, Q=.. tenuis, Pseudopleuronectes americanus,
Limanda ferruginea, and the elasmobranch Mustelus canis, caught
in the New York Bight and Long Island Sound from April 1971 to
December 1973 were as follows: 0.06 to 0.80 mg/kg wet wt for Ag;
0.09 to 0.40 for Cd; < 0.1 to 0.5 for Cr; 0.6 to 13.8 for Cu; < 0.03
to 0.17 for Hg; 0.03 to 2.5 for Mn; < 0.2 to 1. 7 for Ni; < 0.2 to
1.2 for Pb; and 15.0 to 45.0 for Zn with a low of 3.2 in
Mustelus. Concentrations of metals in muscle were generally
lcwer, but folla-red the same trend between fish and between
si tes. Trace metal contents were similar for the various species
examined, except Zn in dogfish; single species also had similar
values at different catch locations. These levels agree with
previous data on North Atlantic fish.
2346.
Granov, V. V. 1976. Studies on the sorption of iron group
elements from seawater by the radiotracer method.
Jour. Radioanal. Chern. 30:181-195.
Methods of radioactive labelling seawater and
conditions for reaching the equivalent of physico-chemical states
of radiotracers and corresponding stable nuclides in seawater are
discussed. Bioassimilation, the uptake and release by plankton,
is considered as the way of fast stabilization of
physico-chemical forms of radiotracers in the medium, as shown
with Co-60, Pu-239, Ru-106, and Tc-99. Sorption of iron, cobalt,
nickel, and manganese by the typical ocean bottom sediments of
deep-water red clay, diatomic ooze, and carbonate deposit is also
analyzed .
2347.
Gupta, A.S. 1977. Calcium storage and distribution in
the digestive gland of Bensonia monticola
(Gastropoda:Pulmonata): a histological study. BioI.
Bull. 153:369-376.
Calcium in the pulmonate is found in two principal
locations, calcium cells in the acini where Ca is bound to acid
53
-------
mucopolysaccharides as spherites, and in calcium distributing
cells surrounding blood vessles, where it is unbound, granular,
and labile. It appears that the latter cells extrude Ca directly
into blood vessels. Author suggests that the two cell types are
responsible respectively for fulfilling slow, long-term needs and
rapid, immediate demands, as a system of blood Ca regulation.
2348.
Guth, D.J., H.D. Blankespoor and J. Cairns, Jr. 1977.
Potentiation of zinc stress caused by parasitic
infection of snails. Hydrobiologia 55:225-229.
The influence of two species of digenetic trematode
parasites, Schistosomatium douthitti and Trichobilharzia sp., on
tolerance of the gastropod Lymnaea stagnalis to 24 and 75 mg/l of
zinc (acutely lethal concentrations) was investigated. LC-50
values for Lymnaea, in mg/l, were 64 (6 hr); 10 (14 hr); 6.7 (24
hr) and 5.6 mg/l at 48 hrs. Significant reduction in tolerance
to zinc occurred for snails with patent infections at both zinc
concentrations tested. Snails parasitized with Trichobilharzia
Spa showed the greater effect.
2349.
Guthrie, R.K., F.L. Singleton and D.S. Cherry. 1977.
Aquatic bacterial populations and heavy metals-II.
influence of chemical content of aquatic environments
on bacterial uptake of chemical elements. Water
Research 11:643-646.
Bacillus sp., Sarcina sp., Achromobacter sp.,
Flavobacterium sp., Brevibacterium sp., Chromobacterium sp.,
Pseudomonas sp., Azotobacter sp., and Streptomyces Spa from a
coal ash basin, a brackish lake and a freshwater lake were
isolated and analyzed for elemental composition under the
influence of mercury or copper addition. Elemental uptake in
mg/kg wet wt of bacterial cells in brackish water of salinity 9.0
0/00 at 25 C with copper or mercury addition was significantly
higher for all elements as indicated in the following table.
Bacterial cells - uptake mg/kg wet wt
Water, Control Cu added Hg added
mg/l (2 mg/l) (0.04 mg/l)
Co
Cr
0.04
0.4
0.04
o. 1
0.2
0.7
0.08
0.3
54
-------
Cu 1.2 >1.4 4.0 3.4
Fe 16.0 >48.0 162.0 100.0
Hg 0.008 > o. 08 0.02 0.2
Mn 0.09 0.3 2.2 1.0
Zn 0.5 >0.8 9.5 18.0
Light metals
Al-Si 13.0 > '8.6
Mg 6.2 > 6.3
Ti 1. 1 > 8.3
Active metals
Ca 21.8 16.1
K 9.7 > 13.8
Na 19.0 13.6
43.0
13.3
29.0
27.7
40.8
11.0
18.8
21.0
40.0
18.5
23.0
22.0
Mercury addition was associated with a greater
increase in metal uptake by bacteria than copper addition to
brackish water and ash basin water; however the reverse was true
of freshwater. Effects were less pronounced in ash basin water
and freshwater. Results indicate that elemental uptake by
bacteria is influenced by particular combinations of metals in an
aquatic source.
2350.
Gutknecht, J. 1961.
by Ulva lactuca.
Mechanism of radioactive zinc uptake
Lilnnol. Oceanogr. 6:426-431.
Effects of metabolism, pH, carrier ions, and
temperature upon uptake and accumulation of zinc-65 by the marine
algae Ulva lactuca from seawater in light and dark were
investigated. Uptake of Zn-65 decreased with decreasing light
intensity. The compensation point was at 80 ft-c, with uptake
slightly greater than in the dark. At 2 C, Zn-65 accumulation in
live Ulva was < 1000 counts/min/cm3 over 24 hrs, while at 22 C,
tiE value was almost 4000. Dead Ulva at 22 C accumulated Zn-65
more rapidly during the first 6 hrs than live Ulva. When
photosynthesis was inhibited by 10-3M phenylurethane, zinc up-
take was also inhibited. Uptake by living specimens decreased as
pH decreased from 9 to 7 at 22.5 C. Maximum accumulation was
after 15 hrs in pH 9 in presence of li ght. When Ul va were
killed, uptake increased drastically, regardless of available
light or pH. Author suggests that the physical process of
adsorption or cation exchange is primarily responsible for Zn-65
uptake. The relationship between photosynthesis and Zn
absorption is primarily a secondary effect related to
surface/volume ratio and pH.
55
-------
2351.
Hale, J.G. 1977. Toxicity of metal mining wastes.
Environ. Contamin. Toxicol. 17:66-73.
Bull.
Upstream from the confluence of a mine effluent in
South Dakota, Whitewood Creek contained the following
concentrations of heavy metals in mg/l: < 0.01-0.01 for As,
< 0.002-0.005 for Cd, < 0.01-0.03 for Cr, < 0.03 for Cu, < 0.05 for
Pb, 0.0006-0.002 for Hg, < 0.01-0.02 for Ni, < 0.01 for Ag, and
<0.004-0.05 for Zn. Toxicity of these metals, using pricipally
nitrate forms, to 2-month-old rainbow trout in Whitewood Creek
water was tested in continuous flow bioassays using a mobile
unit. LC-50 (96 hr) values, in mg/l, were 10.8 for As, 0.007
for Cd, 24.1 for Cr, 0.25 for Cu, 8.0 for Pb, 0.03 for Hg, 35.5
for Ni, 0.029 for Ag, and 0.55 for Zn. Author suggests that
metal concentrations in Whitewood Creek water may act additively
in combination with test concentrations to produce artificially
low LC values.
2352.
Hall, A.S., F.M. Teeny and E.J. Gauglitz, Jr. 1976.
Mercury in fish and shellfish of the northeast
Pacific. II. sablefish, AnOP104oma fimbria. U.S.
Dept. Comm., NOAA Fish. Bull. 7 :791-799.
Mean mercury levels, in mg/kg wet wt, of decapitated,
eviscerated sable fish from various geographic locations were
0.04 from the Bering Sea, 0.28 southeast Alaska, 0.37 Washington
State, 0.40 Oregon, 0.26 northern California, 0.47 central
California, and 0.60 in southern California. Mercury levels in
this species showed a gradual increase in magnitude from north to
south; the average length of sablefish decreased from north to
south. Approximately 30% of the 692 specimens exceeded the U.S.
Food and Drug Administration action level of 0.50 mg Hg/kg wet
wt. A positive correlation between fish size and mercury content
was observed.
2353.
Hall, A.S., F.M. Teeny, L.G. Lewis, W.H. Hardman and E.J.
Gauglitz, Jr. 1976. Mercury in fish and shellfish of
the northeast Pacific. 1. Pacific halibut,
Hippoglossus stenolepis. U.S. Dept. Cornro., NOAA Fish.
Bull. 74:783-789.
Muscle from 1,227 hali but were analyzed for mercury.
The mean mercury concentration in mg/kg wet wt from five
geographic locations was: 0.15 Bering Sea; 0.20 Gulf of Alaska;
0.26 southeast Alaska; 0.32 British Columbia; and 0.45 from
56
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Washington-Qregon. Mercury was uniformly distributed from nape
to tail in edible muscle. Within each geographic area Hg
concentration increased with fish size. Mercury concentration
also increased in fish of the same size from the northern to the
southern part of the species range.
2354.
Hamdy, M.K., O.R. Noyes, and S.R. Wheeler. 1977. Effect
of mercury en bacteria: protection and
transmethylation. In: Drucker, H. and R. E. Wildung
(eds.). Biological-rffiplications of metals in the
environment. ERDA Symp. Ser. 42: 20-35. Avail. as
CONF-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Comm., Springfield, VA. 22161
Seven genera of bacteria, from three different
sedllnents, were screened for mercury resistance. Bactericidal
levels of HgC12 over 48 hrs were 500 mg Hg/l for Bacillus, 400
for Escherichia, 150 for Staphylococcus, 60 for Streptococcus,
1.1 for Bacteriodes, and 1.0 for Clostridium. Minimum lethal
concentrations were 1200 mg Hg/l for resistant strains of
Enterobacter aerogenes after adaptation by serial dilution, but
only 50 mg/l for sensitive strains. The resistant culture
produced methylmercury from HgC12 under both aerated and
unaerated conditions; production was cyclic and decreased with
DL-homocysteine but increased with methylcobalamin. Authors
suggest methylmercury production is a mechanism by which
inorganic Hg is detoxified and secreted into the environment.
One Bacteriodes culture exposed to 10 mg Hg/l showed that 2.5 or
5.0 mg dry wt of sedllnent protected bacterial cells against Hg
toxicity. This effect was probably due to presence of organic
matter since ashed sediment afforded no protection. Sedllnent
may, therefore, protect aquatic bacterial communities from
deleterious effects of mercury.
Hand, S.C. and W.B. Stickle. 1977. Effects of tidal
fluctuations of salinity on pericardial fluid
composition of the American osyter Crassostrea
virginica. Marine Biology 42:259-272.
Oysters were subjected to simulated tidal fluctuations
of salinity of 20-10-20 0100, 15-10-15 0100, and 10-5-10 0100
during 24.8 hr patterns. Pericardial fluid Mg2+ was hyperionic
by as much as 3 11M as ambient water salinity decreased during
the cycle, and then became slightly hypoionic as salinity
increased. Under a 2-week diurnal fluctuation pattern
2355.
57
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between 20 and 10 0/00 S, pericardial fluid Mg2+ became more
intermediate between high and low salinity values after day 5.
Osmolarity, Na+, Cl-, and Ca2+ followed similar patterns in
all experiments, while K+ levels did not follow ambient
seawater as closely. The ionic composition of dilution water had
li ttle effect on the osmotic or ionic response of the osyter' s
pericardial fluid. Ninhydrin-positive substances in oysters and
percent body water varied inversely with salinity. Solute
movement accounted for most of the change in pericardial fluid
osmolarity. During 20-10-20 0/00 cycles, oyster valves stayed
open 56% of the time. However, when salinity changed abruptly
from 20 to 10 0/00, valves closed within 5 min and stayed closed
for 19 hrs.
2356.
Harding, J.P.C. and B.A. Whitton. 1977. Environmental
factors reducing the toxicity of zinc to Stigeoclonium
tenue. British Phycol. Jour. 12:17-21.
Influence of pH, Mg, Ca, and P on toxicity of zinc to
the freshwater algae ~. tenue was shown to differ between a Zn
tolerant population and one that was sensitive. Tolerance Index
Concentration (T.LC.) of zinc of the sensitive population
increased from 0.6 to 0.7 mg Zn/l as pH rose from 7.1 to 7.6 in
1.0 mg Call, and increased from 0.9 to 1.0 mg/l as pH rose in
10.0 mg Call. Tolerance by this population also increased to
slightly above 1.0 mg Zn/l as Mg rose to 299 mg/l and P04-P
rose to 30 mg/l, and increased to 2.0 mg Zn/l as Ca rose to 200
mg/l. More pronounced differences were seen with the Zn tolerant
population. T.LC. increased from 3.4 to 11.0 mg Zn/l as pH rose
from 6.6 to 7.6 in 1.0 mg Call, and increased from 7.8 to 14.1
ffiWl as pH rose in 10.0 mg Call. When Mg and Ca levels
approached 200 mg/l, tolerance by algae increased from < 1.0 to
20.0 mg Zn/l; and increased from about 5.0 to 20.0 mg Zn/l as
P04-P rose to 30 mg/l.
2357.
Harrison, P.J., H.L. Conway, R.W. Holmes, and C.O. Davis.
1977. Marine diatoms grown in chemostats under
silicate or ammonium limitation. III. cellular
chemical composition and morphology of Chaetoceros
debilis, Skeletonema costatum, and Thalassiosira
gravida. Marine Biology 43:19-31.
.e.:.. costatum, ~ debilis, and ~ gravida were grown
under no limitation and ammonium or silicate limitation or
starvation. Changes in cell morphology were correlated with
58
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observed changes in chemical composition. Cultures grown under
silicate starvation or limitation showed a decrease in
particulate silica, from 0.8 x 10-7 ug-at/l/cell in non-limited
cells for S. costatum, to 0.7 x 10-7 (starvation) and 0.4 x
10-7 (limitation). For C. debilis, Si dropped from 3.0 x
10-7 to 2.3 x 10-7 (starvation) and 1.1 x 10-7 (limitation)
and from 20.0 x 10-7 to 10.8 x 10-7 and 12.8 x 10-7 for T.
gravida. Particulate carbon, nitrogen, phosphorus, and
chlorophyll a increased in diatoms. The most sensitive indicator
of silicate limitation or starvation was the ratio C:Si, being 3
to 5X higher than values for non-limited cells. The ratios
Si:chlorophyll a, and Si:P were lower and N:Si higher than
non-limi ted cells by a factor of 2 to 3. Anmonia-starved and
NH4-limited cells contained 0.7 and 0.8 x 10-7 ug-at Sill per
cell, respectively, for S. costatum, 3.0 and 2.7 x 10-9 for C.
debilis, and 16.3 and 13:1i" for ~ gravida. NH4-starved cells
also contained more chlorophyll a, C, N, and P per cell volumes
than NH4-limited cells. N:Si was the most sensitive ratio for
anmonium limitation or starvation, being 2 to 3X lower than
non-limited cells. Limited cells had less of the limiting
nutrient per unit cell volume than starved cells and more of the
non-limiting nutrients, i.e silica and phosphorus for
NH4-limited cells. This suggests that nutrient-limited cells
rather than nutrient-starved cells should be used along with
non-limited cells to measure the full range of potential change
in cellular chemical composition for species under nutrient
limitation.
2358.
Harrison, W.G. and J.M. Davies. 1977. Nitrogen cycling
in a marine planktonic food chain: ni trogen fluxes
through the principal components and the effects of
adding copper. Marine Biology 43:299-306.
Nitrogen cycling in a natural planktonic food chain
(seston, copepods, ctenophores) was followed before and after
perturbation by 10 ug/l of copper. Changes attributed to "copper
effects" were: more pronounced initial decrease in seston-N
after copper addition, followed by elevated settling rates and
more pronounced subsequent recovery of seston-N; significantly
more rapid decrease in zooplankton stocks, essentially
disappearing by the third week after copper addition; inhibition
of nitrate-specific assimilation rate during the first week after
copper addition; inhibition of zooplankton grazing. Since
zooplankton stocks and fluxes were most drastically affected by
copper, its overall effect on N-cyclying through the planktonic
food chain would depend largely upon the importance of
59
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zooplankton in regulating the production of the remaining seston.
2359.
Harrison, W.G., R.W. Eppley, and E.H. Renger. 1977.
Phytoplankton nitrogen metabolism, nitrogen budgets,
and observations on copper toxicity: controlled
ecosystem pollution experiment. Bull. Marine Science
27 : 44-57 .
In 0.005 mg/l copper, assimilation rate of N03 in
phytoplankton in the top 9 meters was reduced to 0.003-0.033
umoles N/l/hr, from control values of 0.01-0.09. In 0.01 mg Cull
the rate was 0.006-0.017 t.nnole N/l/hr, and in 0.05 the rate was
0.001-0.003. Assimilation rates of NH4 declined from control
values of 0.007-0.055 t.nnoles N/l/hr to 0.02-0.03, 0.008-0.013,
and 0.004-0.010 in the three respective Cu concentrations. After
2-3 days, nitrate assimilation decreased to 0.5 x 103/hr in
0.05 mg Cull and to 0.6 in 0.005 mg Cull from control values of
6.2-13.0. Ammonit.nn assimilation rate decreased only to 5.2 x
103/hr from controls of 8.3 in 0.005 mg Cull for 3 days.
Photosynthetic C assimilation and synthesis of nitrate reductase
were inhibited and cell disruption and loss of accumulated NH4
were seen in Noctiluca sp. in Cu treated seawater. Evidence
suggests that addition of copper to enclosures resulted in acute
inhibition of phytoplankton growth and a replacement of the
initial phytoplankton by a copper-tolerant assemblage. Bioassay
experiments indicated that even after shifts to copper-tolerant
forms, copper in enclosures remained in a chemical form still
toxic to phytoplankton and that degree of copper-tolerance of
phytoplankton was related to ambient copper concentrations.
2360.
Hewett, C.J. and D.F. Jefferies. 1976. The acct.nnulation
of radioactive caesit.nn from water by the brown trout
(Salmo trutta) and its comparison with plaice and
rays. Jour. Fish Biology 9:479-489.
Patterns of acct.nnulation of Cs-137 from water by
tissue and organs of trout are described. The ratio of Cs-137 in
fish/g to Cs-137 in water/g after exposure for 420 days in Cs-137
solutions were 1.9 in blood cells; 0.31 in blood sert.nn; 5.7 in
liver; 8.9 in gut; 5.7 in kidney; 5.2 in gill; 2.8 in skin; 8.0
in muscle; and 4.2 in bone. In all tissues and organs examined,
other than muscle, the rate processes of trout were intermediate
between plaice, a flounder-like fish, and ray, an elasmobranch.
It is concluded that most of the cesit.nn acct.nnulated by trout from
water enters other than by gut, probably through gills; but as
60
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with plaice and ray, the main source of cesium, possibly 90%,
comes from food. Despite differences in levels of accumulation,
the ratios of tissue to blood steady state concentrations are
very similar in all three species. The steady state cesium
concentration of blood appears to be directly related to red
blood cell count of the fish.
2361.
Hodson, P. V. 1976. 0 -amino levulinic acid dehydratase
acti vity of fish blood as an indicator of a harmful
exposure to lead. Jour. Fish. Res. Bel. Canada
33: 268-271 .
Acti vity of red cell 0 -amino levulinic acid
dehydratase (ALA-D) of rainbow trout was depressed after exposure
to lead; the effect increased with both lead concentration and
exposure time. At 143 ug Pb/l ALA-D activity declined 50% after
1 week and 74% after 16 weeks. At 23 ug Pb/l, ALA-D activity
dropped sharply after 2 weeks but returned to normal after 4
weeks. The lowest lead concentration tested, 13 ug/l, caused
significant inhibition after 4 weeks, with 40% reduction after 16
weeks. Assays of ALA-D activity may provide a short-term
indication of long-term harmful effects of lead.
2362.
Hodson, P.V., B.R. Blunt, D.J. Spry and K. Austen. 1977.
Evaluation of erythrocyte 0 -amino levulinic acid
dehydratase activity as a short-term indicator in fish
of a harmful expooure to lead. Jour. Fish. Res. Bel
Canada 34:501-508.
The acti vi ty of erythrocyte 0 -amino levulinic acid
dehydratase (ALA-D) of fish is easily measured under a variety of
experimental conditions. Exposure of rainbow trout Salmo
gairdneri, brook trout Salvelinus fontinalis, goldfish Carassius
auratus, and pumpkinseeds Lepomis gibbosus to Pb consistently
inhibited ALA-D within 2 wks at concentrations as low as 10, 90,
470, and 90 ug/l, respectively. In rainbow and brook trout these
concentrations were closely related to the published minimum
effecti ve concentrations causing sublethal harm. Blood lead
concentrations ranged from 30-600 ug/l in controls and up to 5400
ug/l in treated fish. There were significant negative
correlations between 1) ALA-D activity and log of blood Pb
concentration and 2) ALA-D activity and log of Pb in water. A
positive correlation between blood Pb and water Pb is shown.
Near lethal exposures to cadmium, copper, zinc, and mercury did
not significantly inhibit ALA-D acti vi ty. Recovery
61
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of ALA.-D activity of rainboo trout after transfer from 120 ug/l
lead to clean water occurred in 8 weeks. This enzyme provides
fast, consistent, specific, and sensitive estllnates of lead
concentrations causing sublethal harm to fish and may help to
relate sources of lead to degree of exposure of fish populations
in the field.
2363.
Hoppenheit, M. and K.-R. Sperling. 1977. On the dynamics
of exploited populations of Tisbe holothuriae
(Copepoda, Harpacticoidae) IV. the toxicity of
cadmium: response to lethal exposure. Helgol. wiss.
Meeresunters. 29:328-336.
Adult copepods and nauplii were exposed to 0.148,
0.222, 0.333, 0.500, 0.750 or 1.125 mg Cd/I, with weekly
exploitation rates of 10, 30, 50, 70, or 90%, under conditions of
surplus food, 22 C, and 30 0/00 S. All populations exposed to
0.500 mg/l or higher, and 20% exposed to 0.333 mg/l, died within
3 to 9 weeks. Cope pods in lower concentrations survived the
experllnental exposure period of 30 weeks. Authors found no
relation betwen survival and exploitation rates. Significant
numbers of dead copepods were detected in sampling regllnes of 5
times per week but not in weekly samples due to rapid
decomposition and cannibalism.
2364.
Hoss, D.E., L.C. Coston, J.P. Baptist and D.W. Engel.
1975. Effects of temperature, copper and chlorine on
fish during simulated entrainment in power plant
condenser cooling systems. In: Environmental effects
of cooling systems at nuclear-power plants.
IAEA-SM-187/19 Inter. Atom. Ener. Agen. Vienna,
Austria: 519-527.
Conditions of entrainment were simulated in the
laboratory to investigate effects of thermal shock, combined
effects of thermal shock and copper, and combined effects of
thennal shock and chlorine on survival of larval fish. Survi val
of larval pinfish, Lagodon rhomboides, held for 24 h in water
containing 1.0 mg/l copper prior to thermal shock was
significantly reduced at shock temperatures of 12 and 15 C above
acclimation temperatures. Salinity did not significantly affect
survi val.
62
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2365.
Howard, H.H. and S.W. Chisholm. 1975.
of manganese in a eutrophic lake.
Natural. 93:188-197.
Seasonal variation
AIDer. Midland
Manganese at one m strata was monitored for 15 months
in a small, dimictic eutrophic lake near Saratoga Springs, N.Y.
Concentrations were lowest in surface strata, 0.01-0.11 mg/l, and
highest in anaerobic bottom waters, 0.04-2.49 mg/l. Levels in
bottom waters consistently increased after stratification until a
maximum was reached just before overturn. Overturn markedly
raised Mn concentrations at the surface for a period of 6-12
weeks. Manganese particles smaller than 0.45 u accounted for
almost all of the Mn found in anaerobic water but only 0-13% in
aerobic water. Total Mn varied from 170 kg minimum, after spring
overturn, to 2550 kg at the end of sunmer stratification.
Possible effects of Mn cycling on algae are discussed.
2366.
Howard-Williams, C. and W.J. Junk. 1977. The chemical
composition of Central Amazonian aquatic macrophytes
with special reference to their role in the
ecosystem. Arch. Hydrobiologie 79:446-464.
Mineral content of 27 species of aquatic macrophytes
collected from lakes in the Central Amazon region was
determined. Sodium levels in free floating species averaged from
400 to 16,600 mg/kg dry mass, in plants rooted in floating mats
200 to 2,700, and in sediment-rooted plants 100 to 16,600 mg/kg.
Average concentrations, in mg/kg dry mass, for potassium were
17,800 to 56,900 (free-floating), 16,600 to 36,900 (mats), and
850 to 33,300 (rooted); for magnesium it was 1,600 to 7,900
(floating), 900 to 4,600 (mats) and 700 to 4,400 (rooted); for
calcium these values were 5,200 to 42,800 (floating), 2,300 to
14,200 (mats) and 1,500 to 14,800 (rooted); and for silicon 1,300
to 28,400, 2,600 to 28,700 and 1,800 to 37,200, respectively. P
and K were high compared to values in soils and waters in the
area, while Ca was low. Measurements were also taken for
nitrogen, phosphorus, ash, dry matter, polyphenols, potential
energy, and cell wall material. Aquatic plants of the area may
act as nutrient reservoirs in water bodies and playa major role
in biogeochemical cycling in Amazonian aquatic ecosystems.
2367.
Hughes, G.M. and R.J. Adeney. 1977. The effects of zinc
on the cardiac and ventilatory rhythms of rainbow
trout (Salmo gairdneri, Richardson) and their
63
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responses to environmental hypoxia.
11:1069-1077.
Water Research
Recordings were made of trout cardiac and ventilatory
rhythms during exposure to 40 and 10 mg/l zinc. Exposure to 40
mg Zn/l for at least 12 hours produces increases in ventilatory
and coughing frequency rates and a decrease in heart rate; the
percentage coupling between the two rhythms usually increased.
At 10 mg Zn/l effects are not as apparent. Exposure for 4 hours
to 10 mg Zn/l modifies the response of trout to hypoxia by
decreasing both the degree of bradycardia and increase in
ventilation usually associated with lowering of ambient oxygen
tension. Authors concluded that zinc interferes with mechanisms
invol ved in uptake of oxygen at the gills and consequently can
alter ability of trout to respond to the additional stress of
oxygen deprivation.
2368.
Hung, T.-C. and T.-T. Lin. 1976. Study on mercury in the
waters, sediments and benthonic organisms along Cahi-I
coastal area. Acta Oceanogr. Taiwanica 6:30-38.
Mercury and possible complexing inorganic ligands were
analyzed from the Chai-I coastal area in Taiwan including the
Potzu and Peikang Rivers during December 1974 to October 1975.
Nitric acid, at pH 1.0, was added to preserve mercury in the
samples, since concentrations of 0.001 and 0.002 mg Hg/l reduced
to almost zero over 30 days without acidification. Hg content in
coastal waters averaged 0.08 to 0.43 ug/l; river water averaged
0.12 to 0.72 ug Hg/l. Of the major ligands, 58.0 to 82.4% of
HgC1ZI2 was found in coastal ocean water and 81.3 to 97.5% of
HgC100 in Potsu River. Mud and sand sediments contained an
average of 0.015 to 0.070 mg Hg/kg. Mercury levels in oysters
ranged from 0.01 to 0.05 mg/kg wet wt, with accumulation factors
of 70 to 360 over coastal waters. Clams contained 0.01 to 0.03
mg Hg/kg, with accumulation factors of 24 to 225.
2369.
Innes, D.J. and L.E. Haley. 1977. Genetic aspects of
larval growth under reduced salinity in Mytilus
edulis. Biol. Bull. 153:312-321.
Growth of mussel larvae at 30 or 18 0/00 salinity for
18 days was not significantly different. Slower growth was
observed in 11 and 16 0/00 salinity after 3 and 11 days,
respecti vely. Larvae from these two groups showed no abnormal
development or swiITIDing behavior when compared to the 30 0/00
64
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group. When families of known genetic parentage were reared at
different salinities, genetic analysis indicated substantial
variation in larval length 16 days after fertilization, and
genetic interaction with salinity. This is interpreted as the
presence of genes influencing larval growth (which are dependent
on salinity for expression), and this may be related to a past
selective influence of a fluctuating environment.
2370.
Ishak, M.M., S.R. Khalil, and W.E.Y. Abdelmalik. 1977.
Distribution and tissue retention of cesium-134 and
cobalt-60 in the Nile catfish Clarias lazera (Cuv. &
Val.) Hydrobiologia 54:41-48.
Nile catfish concentrated Cs-134 and Co-60 from the
aquatic environment. Rate of Cs-134 uptake increased with
increasing exposure time to a maximum concentration factor of
0.37 in 15 days; for Co-60 the maximum CF of 0.36 occurred after
one day. Internal distribution of Cs-134 in fish organs due to
uptake from the aquatic environment, in decreasing order, was
muscle, bone, gills, stomach, kidneys, intestine, and liver.
Concentrations for Co-60, in decreasing order were bone, muscle,
gills, intestine, kidney, stomach, and li ver. Internal
distribution due to ingestion of these radionuclides followed a
similar pattern.
2371 .
Jackim, E., G. Morrison, and R. Steele. 1977. Effects of
environmental factors on radiocadmium uptake by four
species of marine bivalves. Marine Biology 40:303-308.
Temperature, salinity, bottom-sediment type, and zinc
concentration all influence Cd uptake by !1@ arenaria, Mytilus
edulis, M.llinia lateralis and Nucula proxima. Radiocadmium-109
uptake during short-term exposures differed widely among
species. However, for all species increasing temperature or
decreasing salinity was associated with increasing uptake. The
presence of bottom sediment depresses Cd accumulation in some
benthic animals. Zinc, at 0.5 mg/l, substantially decreased Cd
uptake by M. edulis and M. lateralis. During exposure for 14
days to 5 ug Cd/l, M. arenaria contained 2.2 mg Cd/kg dry wt at
10 C, and 4.2 at 2OC; M. edulis contained 9.3 and 9.4,
respectively; M. lateraITs contained 3.6 and 8.9. After exposure
to 20 ug Cd/l for 14 days, M. arenaria contained 16.8 mg Cd/kg
dry wt at 10 C and 29.0 at 20 C; for M. edulis it was 50.6 and
60.4, respectively; for M. lateralis it was 10.3 and 20.5; and
for !!:.. proxima it was 2.0- and 4. 6 mg Cd/kg dry wt, respectively.
65
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M. arenaria subjected to 5 ug Cd/l plus tracer for 7 days
contained 6111 cpn when no sediment was present in aquaria, 4730
with sand, and 2881 with mud; all treatments were significantly
different. M. lateral is, under the same respective conditions,
showed an average of 2294, 2264, and 1496 cpm, with no
significant difference between treatments. When exposed to 2 ug
Cd/l plus tracer for 21 days at 10 C, M. edulis contained 83 ug
Cd/kg dry tissue in 20 0/00 salinity, but only 32 in 30 0/00 S.
M. lateralis had 52.0 ug Cd/kg dry wt (10 C) and 24 (20 C),
respecti vely, and!h. proxima had 21.0 and 0.6. Under the same
exposure at 20 C, M. edulis contained 108 ug Cd/kg dry wt in 20
0/00 salinity and Eb in 30 0/00 S; for M. lateralis it was 36 ug
Cd/kg wet wt (10 C) and 8 (20 C) respectively; for ~ proxima
this was 5.4 and 2.6. Authors concluded that important species
and temperature, salinity, zinc and sediment type should be
considered in studies an cadmium accumulations by benthic marine
organisms.
2372.
Jennings, C.D. 1977. 55Fe in Pacific Ocean plankton.
Marine Biology 44:223-226.
Mixed plankton samples, mostly copepods and
chaetognaths, collected from a large part of the eastern South
Pacific in the vicinity of atmospheric nuclear tests were
analyzed for Fe-55. Specific activity of Fe-55 in plankton
increased from below detectable limits at 200N to a maximum of
130 nCilg Fe at 200S and then decreased to 5 at 500S. Along
an east-west track near 150S, a peak of 90 occurred at
135OW. It is suggested that this maximum is the result of
fallout from French nuclear tests at Mururoa Atoll (220S;
1390W). The increase in Fe-55 at high latitudes observed in
previous studies in the North Atlantic Ocean and North Pacific
Ocean did not occur in the South Pacific Ocean which supports the
suggestion that belts of high tropospheric fallout accounted for
the increase in northern oceans.
2373.
Khobot'yev, V.G., V.I. Kapkov, Y.G. Rukhadze, N.V.
Turunina, and N.A. Shidlovskaya. 1976. Algal uptake
of copper from compounds and its effect on salt
metabolism in algae. Hydrobiological Jour. 12:29-34.
Copper accumulation in the the freshwater algae
Scenedesmus quadricauda and Anabaena variabilis was directly
related to algicidial action of the Cu compound tested. Toxicity
of Cu was due to the cells' ability to accumulate Cu to a greater
66
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degree from compounds such as [CuCS -Pyc)2]C12, with a
coordination bond between metal and ligand, than from CuC12
with an ionic bond, or from [Cu(oo-PYC)2J having a coordinate-
co valant bond. Max imllll uptake by Anabaena was 25, 000 mg Cui kg
dry wt in o. 99 mg Cu/l on day 30; for Scenedesmus this was 18,000
mg/kg in 4.95 mg Cull on day 10. Copper complex concentrations
of 0.50 to 4.95 mg/l disturbed salt metabolism in algal cells due
to Cu accumulation or Kloss; Na and Ca levels remain relatively
constant. In 4.95 mg/l of Cu complex, cellular K content
decreased by 80% within 30-60 minutes.
2374.
Khristoforova, N.K., N.A. Sin'kov, G.N. Saenko, and M.D.
Koryakova. 1976. Content of the trace elements Fe,
Mn, Ni, Cr, Cu and Zn in the proteins of marine
algae. Soviet Jour. Marine Biology 2(2):124-128.
Concentrations of Fe, Mn, Ni, Cr, Cu, and Zn were
determined by emission spectroscopy in protein extracts of three
species of red algae Rhodomela laris, Polysiphonia japonica,
Ptilota filicina, and the brown algae Agarum cribrosum. Protein
resi dues contained more than O. 1 % Mn, up to 0.085% Fe and up to
0.025 % Zn. Copper levels in proteins fran aqueous and saline
extracts did not exceed 0.0005-0.0006%. Large quanitites of Mn
and Zn were found in the aqueous and saline protein extracts.
Alkali -soluble proteins contained chiefly Fe, Ni, Cr, and Cu.
Metal content of all algal species in mg/kg dry wt were 248 to
954 for Fe, 139 to 825 for Mn, 10 to 12 for Zn, 11 to 25 for Ni,
7 to 13 for Cr, and 1.3 to 5.7 for Cu.
2375.
Kidder, G.M. 1977. Pollutant levels in bivalves, a data
bibliography. U.S. Environ. Protect. Agenc. Contract
No. R-80421501, Avail. from Scripps Inst. Ocean., La
Jolla, Calif.
Published information on concentrations of four major
pollutant groups in bivalve molluscs, is presented to provide
baseline data for present and future studies. The four major
catagories of pollutants investigated were metals, pesticides and
halogenated hydrocarbons, radionuclides , and petroleum
hydrocarbons. Metals listed included Ag, Al, As, Au, Ba, Bi, Ca,
Cd, Ce, Co, Cr, Cs, Cu, Eu, Fe, Ga, Ge, Hg, K, La, Li, Mg, Mn,
Mo, Na, Nb, Ni, Pb, Po, Pu, Ra, Rb, Ru, Sb, Sc, Se, Si, 3m, Sn,
Sr, Tc, Th, Ti, V, Zn, and Zr.
67
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2376.
Kim, J.H., E. Birks, and J.F. Heisinger. 1977.
Protecti ve action of selenium against mercury in
northern creek chubs. Bull. Environ. Contamin.
Toxicol. 17: 132-136.
Pretreatment of the freshwater teleost, Semotilus
atromaculatus, with 3.0 mg/l selenium as selenium dioxide for 48
hrs at 24 C produced higher survival than non-treated groups
after exposure to mercuric chloride concentrations for 48 hrs at
concentrations up to 0.19 mg Hg/l. Se pretreatment at 3.0 mg/l
had no obvious effects upon the fish, but higher concentrations,
of 12.0 mg Sell, were associated with heavy mucous accumulation
on gills of survivors and high mortality. At Hg concentrations
of 0.01, 0.04, and 0.07 mg/l Se, pretreatment appeared to favor
Hg accumulation. At 0.07 mg/l, Hg in pretreated fish was 24.5
mg/kg dry wt and in tmtreated only 18.6. However, all pretreated
fish survived while 30% of too untreated group died. At Hg
concentrations of 0.10, 0.13 and 0.16 mg/l, body Hg dropped
before rising again in Se pretreated fish and was below the level
in tmtreated specimens. In 0.16 mg Hg/l, both groups had
approximately 28.0 mg Hg/kg dry wt.
2377.
Kim, K.C., R.C. Chu and G.P. Barron. 1974.
tissue and lice of northern fur seals.
Contamin. Toxicol. 11:281-284.
Mercury in
Bull. Environ.
Tissues of nursing cows, newborn and suckling pups of
Callorhinus ursinus, and their obligate, permanent sucking
ectoparasite lice Antarctophthirus callorhini and
Proechinophthirus fluctus were analyzed for mercury. Mean Hg
levels in nursing cows, in mg/kg wet wt, were: 4.e7 in air dried
hair; 0.099 in whole blood; and 0.014 in whole milk. In newborn
pups, Hg levels were 3.68 hair, 0.019 blood, and 0.22 in A.
callorhini. In 2 month old pups, mercury levels were 5.4-hair,
0.069 blood, 0.63 in A. callorhini and 0.51 in P. fluctus.
Presence of mercury in milk could account for the higher mercury
content in the 2 month-old pups. Mercury in hair and blood of
newborn pups indicates that mercury is able to cross placental
membranes. A positive correlation existed between level of
mercury in blood and that in hair and in lice. Authors suggest
that hair and lice samples show promise for monitoring Hg levels
in northern fur seals.
2378.
Klein, A.E. 1977. A study of heavy metals in Lake
Abbaya, Ethiopia, and the incidence of non-parasitic
68
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elephantiasis. Water Research 11:323-325.
Surface water from Lak~ Abbaya and nearby hot springs
contained, in mg/l: 0.05-1.00 Asj+; 0.2-16.0 B; 0.002-0.85 Hg;
0.04 Au; 0.002-0.04 Pb; and 0.001-0.47 Cr. No detectable amounts
of Zn, Cu, Cd, Ba, or Ag were found. Author suggests that the
high incidence of non-parasitic elephantiasis in humans from the
lake region may be due to mercury and arsenic contamination.
2379. Kobayashi, N. and K. Fujinaga. 1976. Synergi3ll of
inhibiting actions of heavy metals upon the
fertilization and development of sea urchin eggs.
Science Engin. Rev. Doshisha Univ. 17:54-69. (In
Japanese) .
Effects of cadmium, copper, nickel, and zinc on sea
urchin egg development was determined. After 24 hrs, development
was retarded for Hemicentrotus pulcherrimus in 0.08-0.32 mg Cull,
0.20-0.82 mg Znll, 0.37-1.47 mg Ni/l, and 0.35-1.41 mg Cd/I.
After 15 hrs, retardation occurred for Anthocidaris c~assisPina
eggs in 0.16-0.64 mg Cull, 0.41-1.64 mg Zn/l, 0.37-1.7 mg Ni/l,
and 0.70-2.81 mg Cd/I. Metals induced decreased rates of
fertilization, cell division, gastrulation, and occurrence of
polyspermy, permanent blastula and exogastrula. Eggs developed
normally in 0.04 mg Cull, 0.10 Zn, 0.18 Ni, and 0.18 Cd for
Hemicentrotus; and in 0.08 mg Cull, 0.20 Zn, 0.18 Ni, and 0.35 Cd
for Anthocidaris, the more tolerant species. When used at their
respective concentrations, strong synergistic actions appeared
for mixtures of Cu and Zn and secondarily for Cu-Cd and Zn-Cd.
Mixtures of Cu-Ni, Zn-Ni, and Cd-Ni acted additively on eggs from
both species of echinoderms.
2380.
Koe 11 er, P. and J. R. Parsons. 1977 . The growth of young
salmonids (Onchorhynchus keta): controlled ecosystem
pollution experiment. Bull. Marine Science 27:114-118.
Presence of 0.0025 mg/l inorganic copper, lOX ambient
level, for 47 days caused no observable effect on growth or
survival of juvenile salmon held at about 30 0/00 salinity.
Controlled ecosystems, with no metal added, supported fish growth
when large crustacean zooplankton were available, but not when
only small zooplankton were present. This suggests that factors
(pollutants or natural events) which alter the spectrum of prey
items available to young fish may be more important than direct
effect of physical or chemical factors on juveniles.
69
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2381. Koli, A.K., W.R. Williams, E.B. McClary,
J.M. Burrell. 1977. Mercury levels
fish of the state of South Carolina.
Contamin. Toxicol. 17: 82-89.
E.L. Wright, and
in freshwater
Bull. Environ.
Samples of fish from rivers, lakes, and ponds in South
Carolina collected during the surrmers of 1974 and 1975 were
analyzed for mercury. Mercury, in mg/kg wet wt, in muscle was
0.02-0.07 for redbreast, 0.05-0.11 for white bass, 0.04-0.05 for
shad, 0.04-0.12 for bluegill, 0.06-0.09 for catfish, 0.64 for
pike, 0.63 for mudfish, 0.49 for warmouth, and 0.53 for
largemouth bass. Concentrations increased with increased body
weight and at higher levels on the food chain, suggesting
bioamplification of Hg up the food chain. Pike from Lake Murray
had Hg levels of 0.95 mg/kg wet wt in liver, 0.72 in kidney, 0.64
in muscle, and < 0.33 in other organs; ratio of muscle:liver Hg
was 0.67. Hg levels in mudfish from Edisto River were 0.83 mg/kg
wet wt in liver, 0.69 in kidney, 0.63 in muscle, and.:::.O.3 in
other organs; muscle:liver Hg ratio was 0.76. Authors state that
carnivorous and bottom-feeding fishes are the most reliable Hg
pollution indicators.
2382.
Koyama, J. and Y. Itazawa. 1977. Effects of oral
administration of cadmium on fish - I. analytical
results of the blood and bones. Bull. Japan. Soc.
Sci. Fish. 43:523-526. (In Japanese).
Carp, Cyprinus carpio, were fed diets containing 0.0,
28, 140, 570, 1700, or 5700 mg Cd/kg dry wt for 30 or 60 days.
As cadmium content increased, alkaline phosphatase activity of
serum decreased and Ca concentration decreased in serum from 100
to 40 mg/l, in vertebrae from 2750 to 2250, in vertebrae ash from
5250 to 4750, and in cranial ash from 3750 to 3500 mg/kg.
Inorganic phosphorus concentration of serum increased from 70 to
100 mg/l with increasing Cd in the diet. Violent swimming and
tetany were observed in fish fed Cd. This may have been due to
hyperexci tability of the nervous system and muscles, which is
attributable to low Ca and high inorganic P levels in plasma.
2383. Koyama, J. and Y. Itazawa. 1977. Effects of oral
administration of cadmium on fish - II. results of
morphological examination. Bull. Japan. Soc. Sci.
Fish. 43:527-533. (In Japanese).
As cadmium content increased to 1700 mg/kg in dry food
70
-------
given to carp, weight gain in fish was reduced up to 15%, and
weight of hepatopancreas, in relation to whole body weight,
generally decreased. Lateral curvature of vertebral column was
observed in 13 of 93 fish fed a diet containing ~ 140 mg Cd/kg;
these exhibited violent swimfidng and tetany. In Cd-exposed fish,
abnormal black granules accumulated around blood vessels in the
liver, proximal renal tubules exhibited degeneration; and cells
seemed to have lost protoplasm. A possible mechanism for lateral
curvature of the vertebral column is: degeneration of renal
tubules attributable to orally administered Cd produced low Ca
and high inorganic P levels of plasma and low Ca of vertebrae.
This induced hyperexcitability of the nervous system and muscles,
resulting in violent swimfidng and tetany, lateral bending of
centra, and, finally, lateral curvature of vertebral column.
2384. Kulikov, N.V. and L.N. Ozhegov. 1976. Accumulation of
90Sr_90y by developing eggs and larvae of
whitefish Coregonus lavaretus L. Soviet Jour. Ecology
7 : 175-177 -
Whitefish eggs and larvae were held in a solution of
Sr-90 C12, at 0.01 mCi/l. No strontium-90 was accumulated in
eggs over 120 days; for yttrium-90 the coefficient of
accumulation (CA) on a wet wt basis was 25 at day 40, 55 at day
80, and 80 at day 120. Larval accumulation of Sr-90 increased
almost linearly from CA of 0.3 at start to 1.5 on day 32. y-90
level was always slightly higher, with a CA of 3.5 on day 32.
Excretion of radionuclides decreased with time in both eggs and
larvae: Sr-90 in eggs dropped to 0.0 in 1 day; y-90 dropped to
25% on day 4, 10% on day 8 , and 0.0 on day 16. In larvae, Sr-90
content declined to 60% on day 2, 50% on day 8, and 40% on day
16; y-90 decreased to 60% on day 2, and continued at that level
through day 16.
2385.
Latz, M. I. and R.B. Forward, Jr. 1977. The effect of
salinity upon phototaxis and geotaxis in a larval
crustacean. Biol. Bull. 153:163-179.
Larvae of the crab Rbi thropanopeus harrisii
acclimatized to 20 0/00 S showed a greater positive phototaxis to
higher intensities of light and a reduced negative phototaxis to
100 light intensities when suddenly exposed to 40 0/00 S.
Exposure to 5 0/00 S generally reversed phototaxis at light
71
-------
intensities above 0.01/Wm2. A salinity decrease of 1 to 2 0/00
reversed the phototaxic sign for both stage I and IV zoeae,
regardless of acclimation salinity. Total recovery to positive
phototaxis occurred in about five minutes. At all test
salinities, between 5 and 40 0/00, stage IV larvae maintained a
lower position in the water column than stage I larvae,
regardless of light conditions. Stage I zoeae moved downward in
salinities below acclimation and upward in higher salinities,
responding to phototaxis rather than geotaxis. Stage IV zoeae
also migrated downward upon salinity reduction, responding to
geotaxis. Ascent in higher salinities occurred only under
overhead lights, indicating movement resulting from phototaxis.
Authors concluded that these behavioral responses act as a
negative feedback system to keep larvae within a region of
acclimation salinity in a vertical water column.
2386.
Lloyd, E.T., W.T. Schrenk, and J.O. Stoffer. 1977.
Mercury accumulation in trout of southern Missouri.
Environ. Research 13:62-73.
Concentrations of mercury in rainbow and brown trout
ranged from 0.08 to 0.49 mg/kg wet wt in flesh; concentrations in
li ver were slightly higher. There was no relation between
mercury content and fish size. Previous analyses of trout
collected in the mid- to late 1940s from the same areas indicated
mercury accumulation of approximately 3.0 mg/kg. Over the past
25 years there appears to be a decrease in mercury found in trout
of southern Missouri.
2387.
Lorz, H.W. and B.P. McPherson. 1977. Effects of copper
and zinc on smoltification of coho salmon. U. S.
Environ. Protect. Agen. Rept. EPA-600/3-77-032,
Corvallis, Oregon: 68 pp.
LC-50 (96 hr) values for Cu as CuC12 for yearling
coho salmon, Oncorhynchus kisutch, ranged from 0.060 to 0.074
mg/l, depending on degree of smoltification. For Zn, the LC-50
(96 hr) value for yearling coho in April was 4.60 rng/l, at 10 to
120C. Exposure to 22.00 mg Zn/l for 144 hrs in freshwater had
little effect on Na+, K+-activated ATPase activity in gill
microsomes or on survival of yearling coho when transferred to
seawater. However, immersion in 0.005-0.030 mg Cull in
freshwater for a maximum of 172 days had deleterious effects on
downstream migration in natural streams, lowered gill ATPase
activity, and reduced subsequent survival in seawater. Exposures
72
-------
>10 days to Cu had more severe effects than 6 days on migration
and survival, but not on gill ATPase. Coho yearlings transferred
to non-toxicant freshwater, following exposure to toxicants,
showed higher survival upon transferral to seawater than fish
transferred immediately. Fish ceased feeding in 0.02 and 0.03 mg
Cull, and did not resume feeding for several weeks to 4 months;
mean lengths and condition factors of these groups were lower
than controls. Exposure of year lings to 0.02 and o. 03 mg Cull in
freshwater affected normal maintenance of osmotic pressure and Cl
concentrations in blood plasma; plasma osmolarity and Cl levels
increased significantly compared to controls when transferred to
seawater. These responses are attributed in part to suppression
of Na+, K+-activated ATPase activity in gills.
23B8.
Lowman, F.G., J.H. Martin, R.Y. Ting, S.S. Barnes, D.J.P.
Swift, G.A. Seiglie, R.G. Pirie, R. Davis, R.J.
Santiago, R.M. Escalera, A.G. Gordon, G. Telek, H.L.
Besselievre, and J.B. McCanless. 1970.
Bioenvironmental and radiological-safety feasibility
studies, Atlantic-Pacific interoceanic canal.
Estuarine and Marine Ecology, Vol. I-IV. Prepared for
Battelle Memorial Institute, 505 King Ave., Columbus,
OH, Contract AT (26-1)-171.
Hundreds of species of algae, fish and invertebrates
collected from Panamanian and Columbian waters during 1967 were
analyzed by atomic absorption for Zn, Fe, Mn, Ca, and Sr.
Results were presented for each sample on wet, dry and ash weight
bases. Maximum values recorded, in mg element per kg ash wt for
each taxonomic group sampled during the dry season of 1967 are
surrmarized below (max. scandium value for plankton was 7.7 mglkg
ash wt).
Zinc Iron Manganese Calcium Strontium
plankton 2150 67,000 475 274,700 100,000
pelycopod flesh 340 500 12 17
pelycopod shell 2050 142 50 506 1750
gastroPOd flesh 6500 13,000 370 92 510
gastropod shell 330 6BO 140 500 2194
gastropod viscera 13,000 6100 23 53 84
gastropod operculum 6000 50, 000 17 , 000 85 200
shrimp flesh 1600 920 24 100 510
shrimp carapace 1200 8300 100 720 6000
shrimp whole 790 640 90 480 1500
lobster flesh 600 34 11 18 59
73
-------
lobster carapace ~~ 100
lobster head 140 130
fish, plankton feeders
flesh 770 130
viscera 260 75
skin 590 97
bone 400 1~0
whole 400 300
fishmeal bOO 1040
fish, pelagic
white flesh 1200 2700
dark flesh ~OO 3100
viscera 21,000 3000
skin 9500 5100
bone eeo 5000
fish, bottomfish
flesh 640 200
viscera 1700 39, 000
skin 1000 11 , 000
bone 420 1200
whole 1000 10,000
21
26
36
73
43
125
2~
12
22
72
45
16
470
69
170
170
230 4000
200 6~00
42
24
220 trace
500 trace
76 130
157
52 200
14 100
7000 130
460 150
430 420
ge
170 300
400 1900
500 630
320 300
Lowman, F.G., D.K. Phelps, R.Y. Ting, and R.M. Escalera.
1966. Progress Sunmary Report No.4, Marine Biology
Program June 1965-June 1966. Puerto Rico Nuclear
Center Rept. PRNC ~5: 57 pp. and Appendices A-F.
23~9.
The amounts of the trace elements iron, manganese,
cobalt, copper, nickel, chromium, zinc, cadmium, strontium,
lithium, lead, rubidium, scandium, samarium, and the major
elements potassium, calcium, and magnesium have been determined
in marine organisms (including algae, plankton, mollusks,
coelenterates, crustaceans, fishes, elasmobranchs, sponges,
echinoderms), seawater, seston and marine sedilnents as well as
selected rocks, minerals, and soils of the Culebrinas, Anasco and
Guanaj i bo Ri ver valleys. The amounts of trace elements in
org:misms have been related to ash, wet and dry weights, and to
organic carbon and nitrogen. Concentration factors of algae,
bacteria, crustaceans, and polychaete annelids for Ta-1~2, Na-24,
Zn-65, and Ag-110 are in progress. Stable element analyses have
been incorporated into a study of the partitioning of Fe, So, Zn,
and 3m within a benthic infaunal conmunity. Trace element
relationships in various food webs are in progress.
2390.
Luana, S. N. 1976. The uptake and interorgan distribution
of mercury in a carnivorous crab. Bull. Environ.
74
-------
Contamin. Toxicol. 16:719-723.
Portunid crabs, Thalamita crenata, were fed Hg-203 (70
ug/kg fresh wt stable Hg) labelled polychaetes, Neanthes
succinea, for 13 days. Feeding rates among the crabs ranged from
0.17 to 1.02 ug Hg-203 ingested/kg crab/day due to variations in
body weight. Slopes of the regressions comparing feeding rate
with Hg-203 uptake soow Hg accumulation into body muscle by 7.5
times. Mercury concentrations in tissues of crabs in ug/kg wet
wt ranged from 20 to 5e in chela muscle, 27 to 61 in body muscle,
21 to 44 in viscera, and 33 to 119 in gills. In contrast to
laboratory studies, total Hg levels in body muscle of crabs
collected from field locations were always higher than visceral
levels.
2391.
Luoma, S.N. 1977. Physiological characteristics of
mercury uptake by two estuarine species. Marine
Biology 41:269-273.
Rapid uptake and sloo loss of mercury will result from
short expooures of some organisms due to transfonnation of Hg to
a slooly exchanging form within the organisms. Differences
between expooure times and depuration times depend on rate of
transformation during uptake. Concentrations of Hg-203 labeled
HgC12 that exceeded stable Hg levels in seawater, by at least
ten times were used i.e. 0.03 to 0.05 ug/l. The largest
proportion of Hg accumulated by the worm, Neanthes succinea,
e4-92%, was in the slowly-exchanging, ethanol-insoluble
physiological compartment of the body, from seawater containing
from U.5 to ? 1 ug Hg-~U3/1. After ~~ hrs in 1.0 ug/l, the
concentration in the ethanol-insoluble compartment was 0.2e ug
Hg/kg, while the ethanol-soluble section was approximately 0.05.
The shrimp, Palaemon debilis, also took up most (65%) of its Hg
into the slowly-exchanging compartment. Influx of Hg in the
worm, in 1.0 to 1.2 ug Hg/l solute, into the whole animal and
slowly-exchanging compartment at 111.0 and 92.0 ug/kg/hr,
respecti vely, was much higher than efflux from both rapidly and
slowly-exchanging compartments at 3.6 and 0.4 ug/kg/hr. The
influx into whole body of shrimp at 15.7 ug/kg/hr was also higher
than efflux from its rapidly and slowly-exchanging compartments
at 9.3 and 0.5 ug/kg/hr, respectively. Author concluded that
interspecies differences in susceptibility to mercury may be
determined by differences in biological transformation rates and
physiological penneability.
75
-------
2392.
Luoma, S.N. 1977. The dynamics of biologically available
mercury in a small estuary. Estuarine Coastal Marine
Sci. 5:643-652.
Concentrations of total mercury in the shrimp Palaemon
debilis and the polychaete Nereis succinea from Ala Wai Canal in
Hawaii were 15-302 ug/kg, and 8-130 ug/kg wet wt, respectively.
In the laboratory, mercuric chloride accumulation by worms fed
terrigenous sediment was 1~05 ug/kg dry wt after 11 days; for
shrimp accumulation was 194 ug/kg dry wt after 14 days.
Accumulation of Hg from solution exceeded concentrations in the
water by 100-350 times. Salinities as low as 6 0/00 had no
effect on Hg uptake by shrimp; however, Hg accumulation in worms
decreased at salinities below 16 0100. A simulation of mercury
levels in shrimp from the estuary, based upon a mathematical
model of Hg-203-HgC12 exchange in this species, showed that
mercury concentrations in P. debilis were never at steady state
during the field sampling period. Shrimp appeared to rapidly
concentrate solute mercury which periodically entered the estuary
in storm runoff. Between rainstorms little of the mercury
remaining in the estuary (primarily in sediment-bound form)
appeared to be available to either the deposit-feeding shrimp or
the worm. Because net loss of mercury from both species was slow
relative to the rate of uptake, long periods of time were
necessary to lose the mercury accumulated during rainstorms.
2393.
Luoma, S.N. 1977. Detection of trace contaminant effects
in aquatic ecosystems. Jour. 1"ish. Res. Ed. Canada
34:436-439.
Tolerance to toxicants by various aquatic groups
including algae, fish, insects, and annelids is reviewed, noting
examples with Cd, Cu, Ni, Pb, and Zn. If one population of a
species is more resistant to a toxicant than other populations,
it is considered evidence that concentrations of the toxicant in
the environment of resistant populations is sufficient to elicit
biological effects. Presence of a toxicant-resistant population
of one species in an ecosystem further suggests that other
species may have been affected by the resistance-eliciting
substance.
2394.
MacInnes, J.R., F.P. Thurberg, R.A. Greig, and E. Gould.
1977. Long-term cadmium stress in the cunner,
Tautogolabrus adspersus. U.S. Dept. Camm. Fish. Bull.
75: 199-203.
76
-------
Mean gill-tissue respiratory rates exhibited by
control fish and those exposed to 0.05 and 0.10 mg/l Cd were 972,
736, and 665 ml 02/hr/kg dry wt, respectively, after 30 days;
and 1036, 702, and 587, respectively, after 60 days. At 0.05
mg/l Cd, mortality was 6.9% after 30 days and 11.7% after 60
days. For 0.10 mg/l Cd, these values were 12.1% and 32.3%.
Changes were also observed in two liver enzymes: aspartate
aminotransferase activity was lowered and glucose-6-phosphate
dehydrogenase activity was increased in the presence of 0.05 and
0.10 mg Cdll. Gill, muscle, and liver tissues from each exposure
group were analyzed for Cd uptake; nearly all experimental
samples and controls were below analytical detection limits.
2395.
Mackenzie, F.T., M. Stoffyn, and R. Wollast. 1978.
Aluminum in seawater: control by biological
activity. Science 199:680-682.
The distribution and concentration of dissolved
aluminum in a vertical hydrographj c profile of the Mediterranean
Sea near Corsica are controlled by biological activity. The
concentrations of dissolved silica and aluminum covary in the
profile and exhibit minima coincident with the seasonal
thermocline, a nitrate minimum, and an oxygen maximum. These
observations support the hypothesis that the silicon and aluminum
cycles in the oceans are linked through the activity of diatoms.
2396.
MacLeod, M.G. 1977. Effects of salinity on food intake,
absorption, and conversion in the rainbow trout, Salmo
gairdneri. Marine Biology 43:93-102.
In trout acclimatized to experimental salinities,
weekly food intake was a maximum of 26% dry wt at 15.0 and 28.0
0/00 S; 23 and 24% at 0.0 and 7.5 0/00 S respectively; and a low
of 17% at 32.5 0/00 S. Daily food intake in freshwater varied
from 0 to 42 g over 40 days. When salinity was abruptly
increased, growth rates decreased in relation to food intake
decrease. Weekly growth rate decreased from> 7% to -3% as
salinity increased from 0.0 to 7.5 to 15.0 to 28.0 0/00. Over
the same salinities, weekly food intake decreased from 35 to 15%
dry wt. Recovery of food intake and growth rates to pre-change
levels occurred within 14 days. Absorption efficiency was
negati vely related to salinity. Total dry matter decreased in
efficiency from 0.e9 to o.eo as salinity increased from
freshwater to 32.5 0/00 S. Total energy decreased from 0.92 to
0.e3 and total nitrogen decreased from 0.96 to 0.90 over the same
increase. Conversion efficiency declined with salinity
77
-------
increase. Dry matter in trout 50 to 95 g in weight decreased in
efficiency from about 0.25 to about 0.16 as salinity increased
from 0.0 to 32.5 0/00 S. Energy decreased from 0.27 to 0.17, as
total nitrogen declined from 0.35 to 0.21. In trout weighing ~O
to 155 g, conversion efficiencies of all three parameters
increased slightly until salinity reached 2~.0 to 32.5 0/00 S,
when efficiency dropped sharply.
2397.
MacLeod, M.G. 1977. Effects of salinity on fasted
rainba.-l trout, Salmo gairdneri. Marine Biology
43: 103-10~.
Trout which had been maintained for 120 days in
freshwater and salinities of 7.5, 15.0 and 32.5 0/00 at 10 C were
starved for up to 48 days under these same environmental
conditions. Live ~ight loss between days 7 and q~ of starvation
could be described by a straight line, as could the decrease in
condition factor. Trout maintained in 32.5 0/00 S showed a
significantly greater weight loss than those in lesser
salinities. Muscle water content fell from 78.0 to 7Q.0% between
days 19 and 32 in 32.5 0/00 S; water content increased slightly
from 77.5 to 78.5% in other salinities. Liver water content and
volume of gall bladder contents changed slightly.
2398.
Marchyulenene, D.P. and G.G. POlikarpov. 197b. Role of
water and food in the entry of certain radionuclides
into the organism of the pond snail. Soviet Jour.
Ecology 7:170-172.
Accumulation ot" strontium-90, cesium-137, cerium-144,
and ruthenium-lOb from the medium by snails, Limnaea stagnalis,
and plants, Elodea canadensis, was observed. Snails nourished by
labelled Elodea for an unrestricted time accumulated 1.4X more
radionuclides in body and shell than molluscs fed only 3-4 hrs
each day; with Sr-90, shell accumulated 3.4X more with
unrestricted feeding. Maximum coefficient of accumulation (CA)
on a dry wt basis was 10,500 for Ce-1Q4 in body over labelled
water. CA values for radionuclides in snails maintained in
labelled water were significantly higher than in nonlabelled
water regardless ot" diet. Molluscs accumulated more Sr-90 in
body by 27X and in shell by 50X, and more Ce-144 in body by 2X
and in shell by 20X from labelled water than from labelled
Elodea. When radionuclide concentration in snails from labelled
water with labelled Elodea was computed as 100%, molluscs
accumulated Sr-90 and Ce-144 from labelled food in shells only at
7~
-------
2 and 5%, respectively, and in body at 4 and 26%. Higher levels
of accumulation of Ce-144 and Ru-106 in mollusc body with
labelled Elodea were apparently connected with high CA of these
radionuclides in the food material, 1040 and 216, respectively.
2399 .
Martin, M., M.D. Stephenson, and J.H. Martin. 1977.
Copper toxicity experiments in relation to abalone
deaths observed in a power plant's cooling waters.
Calif. Fish Game 63:95-100.
Toxicity or copper as CuS04 to adult and larval red
abalone, Haliotis rufescens, and adult black abalone, Haliotis
cracherodii, was determined by static bioassay in seawater at 14
C. The LC-50 (96 hr) values were 50 ug Cui 1 for adult black
abalone, and 65 ug/l for adult red abalone. The LC-50 (48 hr)
value for red abalone larvae was 114 ug Cull. Copper accumulated
in gills of red and black abalone from ambient seawater
concentrations of 5b ug Cull. Histopathological abnormalities in
gill tissues was observed at seawater concentrations of 32 ug
Cull and higher.
2400.
Matsl.IDaga, K. 197b. Estimation of variation of mercury
concentration in the oceans during the last several
decades. Jour. Oceanograph. Sac. Japan 32: 48-50.
Mercury in the northern North Pacific Ocean and Bering
Sea from the surface to a depth of 1600 m ranged from 0.003 to
0.004 mg/l in sumner 19b5. As body length of rock fish, Sebastes
iracunda, recently caught from this area, rose from 25 to 45 rom,
Hg body concentrations rose linearly from 0.10 to 0.55 mg/kg dry
wt. This same relationship was observed in fish caught in 1962,
1953 and 1951. It was concluded that there was little variation
of mercury concentration in these oceans during the last several
decades.
2401.
Mayes, R.A., A.W. McIntosh, and V.L. Anderson. 1977.
Uptake of cadmium and lead by a rooted aquatic
macrophyte (Elodea canadensis). Ecology 5~:1176-11~0.
Elodea were grown in two lakes with different sediment
concentrations of Pb and Cd. Wildlife Area Lake sediments
contained 0.5 to 3.~ mg Cd/kg dry wt and 16.6 to 23.7 mg Pb/kg
dry wt. Little Center Lake sediments contained 88.4 to 125.3 mg
Cd/kg and 392.5 to 4~7.~ mg Pb/kg. Little Center Lake
79
-------
receives waste water from a nearby electroplating plant.
Specimens in each lake were anchored in either control or
contaminated (Cd and Pb) sediments. Water samples from Wildlife
Area were below detection limits of 0.0002 mg Cd/l and 0.005 mg
Pb/l. Little Center waters averaged 0.002 to 0.006 mg/l Cd in
sumner, and 0.009 to 0.027 mg Pb/l. Plants grown in the same
water but in sediment fran different sources had significantly
different concentrations of Pb and Cd. Elodea, with initial Cd
at 0.3 mg/kg dry wt, grown in WA Lake decreased from 2.0 to 0.3
mg/kg when anchored in WA sediment, and from 7.5 to 4.0 in LC
sediment over 9 weeks. In LC Lake, Cd levels in Elodea peaked at
12.2-26./j mg/kg in WA sediment at b weeks before decreasing,
while peaking at 23.b-32.3 in LC sediment. Initial Pb
concentration in Elodea was 2.9 mg/kg. This level decreased from
10.4 to 5.2 mg Pb/kg in WA Lake with WA sediment, and fran b4.1
to 1~.4 in LC sediment. In LC Lake, Pb levels peaked at
32.7-~5.9 mg/kg in WA sediment at 6 weeks before decreasing,
while peaking at 114.2-160.9 in LC sediment.
2402. McCarty, L.S., J.A.C. Henry, and A.H. Houston. 197~.
Toxicity of cadmium to goldfish, Carassius auratus, in
hard and soft water. Jour. .fish. Res. Ed. Canada
35 : 35-42.
Goldfish were exposed to up to 60 mg Cd/l in
relatively soft, (~20 mg/l as CaC03)' and hard (~140 mg
CaC03/l) waters. In soft water, the LC-50 (48 hr) value was
2.76 mg Cd/l; the LC-50 (9b hr) was 2.13; and the LC-50 (240 hr)
1. 78 mg/l. During trials in hard water, there were transient
increases in particulate Cd and sharp decreases in total Cd.
Total alkalinity, pH, and conductivity exhibited Cd-dependent
variations. LC-50 (4~ hr) was 46.9 mg Cd/l and LC-50 (9b hr) was
26./j mg/l. The LC-50 (240 hr) value of 40.2 mg Cd/l was
considered less precise due to water quality variations.
2403.
McKim, J.M. 1977. Evaluation of tests with early life
stages of fish for predicting long-term toxicity.
Jour. Fish. Res. Ed. Canada 34:1148-1154.
Partial and complete life-cycle toxicity tests with
fish, involving all developmental stages, have been used
extensively in the establishment of water-quality criteria for
aquatic life. During extended chronic exposures of fish to
selected toxicants, certain developmental stages have frequently
shown a greater sensitivity than others. In 56 referenced
~O
-------
life-cycle toxicity tests completed during the last decade with
34 organic and inorganic chemicals (including Cd, Cu, Cr, Pb, Ni,
Zn, methylmercury) and four species of' freshwater teleosts, the
embryo-larval and early juvenile life stages were the most, or
among the most, sensitive. Tests with these stages can be used
to estimate the maximum acceptable toxicant concentration (MATC)
within a factor of two in most cases. Therefore, toxicity tests
with early life stages of fish should be useful in establishing
water-quality criteria and in screening large numbers of
chemi cals . MATC values for Cd ranged from 1. 7 to tSO. 0 ug/l; for
Cu these were 9.5-40.0 ug/l; for Cr 200.0 to 3950.0 ug/l; for Pb
31.3-119.0 ug/l; Ni 3tSo.0-730.0 ug/l; Zn 2b.0-13be.0 ug/l;
mixtures of Zn, Cd, and Cu 3.9-42.3 ug/l; and for CH3Hg+
0.07-0.93 ug/L
2404.
McLean, R.O. and A.K. Jones. 1975. Studies of tolerance
to heavy metals in the flora of the rivers Ystwyth and
Clarach, Wales. Freshwater Biol. 5:431-444.
The river Ystwyth is contaminated by heavy metals,
especially belCM the areas of' old lead mines. Hormidium rivulare
was the most tolerant filamentous green algae present. Scapania
undulata was a tolerant bryophyte on the Ystwyth and Clarach
ri vers and was found alone in polluted sites, but was less
frequent in cleaner areas. Metal extracts from Scapania mirrored
variations in environmental metal concentrations and it was
suggested that Scapina would be useful as an indicator of water
quality. In general, lower levels of Fe, Pb, and Mn were found
in Scapania comPared with the less tolerant bryophyte, Fontinalis
squamosa. When Fontinalis was transplanted to polluted si tes , an
increase in Pb, Cu, Zn and Mn content was measured within b wks,
wi th death to decay after 1 e wks. Scapania survived when it was
transplanted from its natural polluted habitat to a less polluted
area, with no marked change in metal composition. Elemental
concentrations of Fe, Zn, Cu, Cd, Pb, and Mn in transplanted and
non-transplanted samples of Fontinalis and Scapania are
presented. Radiozinc studies under controlled conditions
demonstrated that both species of bryophytes had similar zinc
uptake patterns, with uptake slightly higher in Fontinalis.
2405.
McNurney, J.M., R.W. Larimore, and M.J. Wetzel. 1977.
Distribution of lead in the sediments and fauna of a
3llall midwestem stream. In: Drucker, H. and R. E.
Wildung (eds.). Biologicar-implications of metals in
tS1
-------
the environment. ERDA Symp. Ser. 42:167-177. Avail.
as CONf-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Comm., Springfield, VA 22161.
Lead distribution in sediments and fauna in Saline
Ditch, Illinois, over a two-year period was highly variable.
Differences in sediment Pb levels between stations were
associated with amount of urban runoff, whereas differences
between samples at a station were attributed to sediment
composition. Mean Pb concentration in totally urban drainage
areas was nearly 400 mg/ kg dry wt; samples from rural areas
averaged 13.6 mg/kg. Maximum sediment Pb levels were associated
with reduced particle size and increased organic content. Lead
levels in sediments, ranging from 10 to 400 mg/kg dry wt, were
generally 6 orders of magnitude higher than water
concentrations. Lead burdens in many aquatic organisms were
affected by substrate contact, as well as stream location. Pb
accumulations in benthic organisms, including mayflies Hexagenia
limbata, tubificid and nontubificid oligochaete worms, crayfish
Orconectes virilis, and pelecypod ranged from 5.3 to 16.0 mg/kg
dry wt. Fishes Etheostoma nigrum, CatostonR.lS commersoni,
Pimephales notatus, Semotilus atromaculatus, Ericymba buccata,
and Notropis umbratilus contained 1.4 to ~. 1 mg Pb/kg dry wt.
Oligochaetes, which burrow in and ingest sediment, had highest Pb
levels.
2406.
Mearns, A.J., P.S. Oshida, M.J. Sherwood, D.R. Young, and
D.J. Reish. 1976. Chromium effects on coastal
organisms. Jour. Water Poll. Contra Feder.
48 : 1929-1939.
Juvenile and adult polychaetes, Neanthes
arenaceodentata, exposed to mean concentrations of 1.15 to 1.59
mg/l hexavalent chromium for 7 days, showed LC-50 (~ day) values
of 2.22 to 3.63 mg/l. Juveniles exposed to trivalent chromium
had LC-50 (4 day) values of 12.5 mg/l. Fifty percent mor~ality
in adult polychaetes was observed on day 184 in 0.1 mg Cr +/1
and on day 59 in 0.2 mg Cr6+/1. Chronic effects of Cr6+
showed a reduction of growth and reproductive efficiency in two
generations of worms at the lowest concentration tested of 0.0125
mg/l. No significant differences in test parameters were evident
between controls and worms exposed to trivalent chromium. A
surrmary of environmental levels of chromium and effects of Cr6+
and Cr3+ to marine organisms is presented.
52
-------
2407.
Mearns, A.J. and M.J. Sherwood. 1977. Distribution of'
neoplasms and other diseases in marine fishes relative
to the discharge of' waste water. In: Kraybill, H.F.,
C.J. Dawe, J.C. Harshbarger, and RJ3. Tardiff (eds.).
Aquatic pollutants and biologic effects with emphasis
on neoplasia. Annals N.Y. Acad. Sci. 298:210-224.
Concentrations of trace metals, in mg/kg dry wt, in
digestive glands of mussel Mytilus californianus from southern
California coastal waters were 14-69 for copper and 2.7-61.0 for
chromium, as reported earlier. Copper in liver of Dover sole,
Microstomus pacificus, from the same areas had been reported as
1.1-32.6 mg/kg wet wt. In an 8-year study (1969 to 1976), fin
erosion in~. pacificus was the only disease that appeared to be
directly associated with municipal waste discharges into southern
coastal California. It occurred primarily at Palos Verdes shelf,
apparently resulting from exposure to contaminated sediments.
Tumor diseases discussed in this report did not appear to be
related to municipal waste water discharge sites or discrete
sources of pollutants.
2408.
Mears, H. C. and R. Eisler. 1977. Trace metals in li ver
from bluefish tautog and tile!'ish in relation to body
length. Chesapeake Science 18:315-318.
Livers from bluefish Pomatomus saltatrix, tilet'ish
Lopholatilus chamaeleonticeps, and tautog Tautoga onitis
collected during the summer of 1971 off the New Jersey coast were
analyzed for Cd, Cr, Cu, Fe, Mn, Ni, and Zn by atomic absorption
spectrophotometry. For all samples the following extreme values,
in mg element/kg liver ash, were recorded: tautog Cd all < 7, Cr
20-450, Cu 280-3700, Fe 2500-31,000, Mn 20-300, Ni 30-470, Zn
700-2300; bluefish Cd 10-150, Cr 30-390, Cu 150-1600, Fe
3900-60,000, Mn 100-240, Ni 20-330, Zn 1100-7600; tilefish Cd
20-270, Cr 10-40, Cu 80-590, Fe 13,000-38,000, Mn 60-150, Ni
10-40, and Zn 1100-2800. Liver ash from male and female tautog
contained decreasing concentrations of Ni with increasing body
length. Smaller males also contained greater levels of Cr and Cu
in liver than larger male tautogs. Larger tilefish contained
proportionately more Cd, Cu, and Fe in liver than smaller
tilefish. Decreasing levels of Mn and Zn with body length were
apparent only for female tilefish. Livers from larger male
bluefish were associated with higher concentrations of Fe than
those from smaller males, while those from larger females
contained lower concentrations of Cr than did livers of smaller
females. Authors concluded that body length should be a factor
in interpretation of trace metal residues in marine teleosts.
83
-------
2409.
Meisch, H.-U., H. Benzschawel and H.-J. Bielig. 1977.
The role of vanadium in green plants II. vanadium in
green algae - two sites of action. Arch. Microbiol.
144: 67 -70.
Cells of Chlorella pyrenoidosa, derived from vanadium-
free agar slants, were sensitive to microamounts of V as
NH4V03. Between 0.01 and 1.0 ug V/l, algae responded with a
continuous increase in dry weight. Addition of 0.1 and 1.0 ug
V/l increased dry weight 43% and 67%, respectively, after 7
days. At higher V concentrations, increased biomass was
accompanied by an increase in chlorophyll content. The maximum
effect on both parameters occurred at 500 ug V/l with a 100%
increase in weight in 7 days. However, both weight and
chlorophyll content decreased at 25 mg V/l and higher, with death
evident at 100 mg V/l. Vanadium residues above 150-200 mg/kg dry
wt in Chlorella were toxic. Two different pH optima for V action
were observed. The first at pH 7 was associated with an increase
of 100% in dry weight over 7 days. The second at pH 7.5-8
accounted for a 90% increase in chlorophyll content over 7 days,
and suggests the existence of two V-dependent metabolic events in
green algae.
2410.
Menasveta, P. and R. Siriyong. 1977. Mercury content of
several predacious fish in the Andarnan Sea. Marine
Poll. Bull. 8:200-204.
Total mercury concentrations in fish muscle collected
from the Andarnan Sea 0 ff Tha iland in Apr il 1975 ranged from 0.026
to 0.234 mg Hg/kg wet wt in yellowfin tuna Neothunnus albacora,
from 0.027 to 0.233 in bigeye tuna Parathunnus sibi, and from
0.057 to 0.478 in the sharks Isurus guntheii, BUIamia
ftallamzami, Sphyrna tades, and Alopius sp. A positive linear
correlation existed between Hg concentration and weight for all
species. Rates of total Hg accumulation between yellowfin and
bigeye tuna were not significantly different. Comparison between
Hg levels in Andarnan yellowfin and higher values in Central
Pacific yellowfin is discussed.
2411.
Merlini, M. and G. Pozzi. 1977. Lead and freshwater
fishes: part 2 - ionic lead accumulation. Environ.
Poll. 13:119-126.
When 0.5 mg Pb/l was added to Lake Maggiore water in
North Italy as lead nitrate, only 8% remained in ionic state.
Immature goldfish, Carassius auratus, in lake water with Pb-203
84
-------
and 0.5 mg Pb/l, accumulated lead rapidly to a concentration
factor (CF) of 390 by day 10 and leveled off to 425 by day 25.
In Pb-203 and 0.5 mg Pb/l after 10 day pretreatment with 0.5 mg
Pb/l, goldfish took up lead slightly faster, with CF of 409 on
day 10 and 492 on day 27. CF values were 772 and e96 on days 10
and 27, respectively, when goldfish were exposed only to Pb-203
in lake water. After 27 day exposure to the three conditions of
lead, total body burden of Pb-203 in fish held 7 days in
non-labelled water had declined from 43.5 to 30.2% with Pb-203
and stable Pb, 46.1 to 22.6% with pretreabment, and 36.4 to 14.8%
with only Pb-203. Authors conclude that fish accumulate lead in
ionic form, and that Pb-203 was rapidly taken up and lost in two
exponential phases.
2412.
Middaugh, D.P., W.R. Davis and R.L. Yoakum. 1975. The
response of larval fish, Leiostomus xanthurus, to
environmental stress follCMing sublethal cadmi um
exposure. Contrib. Marine Sci. 19:13-19.
An incipient LC-50 concentration of approximately
0.2-0.3 mg Cd/l was calculated following exposure for 200 hours.
The LC-50 (30 hr) was 6 mg Cd/ 1, for 172 hrs the LC-50 was o. 3
mg/l. No larvae died after 200 hr exposure to 0.1 mg/l. Whole
body turdens of survivors in mg Cd/kg ash, after 96 hr exposure
to 0.09, 0.5, and o.e mg Cd/l were 20, 42 and 137, respectively.
Larval spot exposed to the four highest concentrations of
cadmium, 0.e-8.0 mg/l, died rapidly with no indication of
irritability prior to death. Larvae subjected to concentrations
of 0.3 and 0.6 mg/l exhibited a phase of disoriented swimming at
the surface of treatment aquaria for 5-7 hrs before dying.
Subsequent short-term sublethal tests were conducted to determine
the relationship of cadmium exposure and accumulated whole body
residues on response of larvae to thermal stress and to low
dissolved oxygen. Results indicated a significant decrease in
the critical thermal maximum for larvae exposed to 0.5 and O. e
mg/l cadmium for 96 hrs at 20 C. Significant decreases in
survival of larvae subjected to a dissolved oxygen level of 1.6
mg/l after exposure to 0.5 and O. tS mg/l cadmium were also
observed.
2413.
Middaugh, D.P., and J.M. Dean. 1977. Comparative
sensitivity of eggs, larvae and adults of the
estuarine teleosts, Fundulus heteroclitus and Menidia
menidia to cadmium. Bull. Environ. Contamin. Toxicol.
17:645-652.
tS5
-------
Mortality or non-emergence of larvae from eggs of
Fundulus in 0.32 mg cadmiumll was 20% in 20 0/00 salinity and 23%
in 30 0/00 salinity. Cd at 1.0 mg/l killed 27 (20 0/00) and 47%
(30 0/00); 3.2 mg Cd/l killed 30 and 50%; 10.0 mg Cd/l killed ~O
and 5~%, and in 32.0 mg Cd/I 5~ and 54% were dead, respectively.
Death in controls was 17% and 33%. For Menidia, mortality in
0.32 mg Cd/I was 50% in 20 0/00 S and 38% in 30 0/00 S; 1.0 mg/l
killed 36 and 36%, 3.2 mg/l killed 5~ and ~O%, 10.0 mg/l killed
52 and 3e%, and 32.0 mg/l killed 66 and 50%, respectively. In
controls, mortality was 36% (20 0/00 S) and 33% (30 0/00 S). In
20 0/00, LC-50 (~8 hr) values, in mg Cd/I, for Fundulus larvae
were 16.2 at age 1 day, 9.0 at 7 days, and 32.0 at 1~ days. In
30 0/00, values for larvae were 23.0, 12.0, and 7.~ at the
respecti ve ages. Menidia larvae, in 20 0/00, had LC-50 4~ hr
values, in mg Cd/I, of 3.~ at age 1 day, 3.2 at 7 days, and 2.2
at 1~ days. In 30 0/00, values for larvae were 5.6, 3.~, and 1.6
at the respective ages. The LC-50 ~8 hr values, in mg Cd/I, for
adult Fundulus were 60.0 in 20 0/00, and ~3.0 in 30 0/00. For
adult Menidia, values were 13.0 mg Cd/I in 200/00 and 12.0 in
30 0/00.
From results, authors emphasize use of different developmental
stages of test species when establishing water quality criteria.
241~.
Miller, W.E., J.C. Greene, and T. Shiroyama. 1975.
Applications of algal assays to define the effects of
wastewater effluents upon algal growth in multiple use
river systems. In: Biostimulation and nutrient
assessment (PRID16e-1) workshop proceedings. Water
Research Lab, Utah State Univ., Logan, Utah: 77-92.
Zinc concentrations in the Spokane River system in
Washington and Idaho ranged from < 0.02 mg/l to 7.5 mg/I. Biomass
of the algae Selenastrum capricornutum was 0.02-0.03 mg dry wt/l
after 1~ days imnersion in O.O~ or 0.10 mg Zn/I. Addition of 1.0
mg EDTA/l to zinc water supported growth comparable to controls,
indicating metal toxicity was suppressed. Growth in metal-free
was higher water at 10 mg dry wt/I. Algal growth was also
correlated positively with N and P content of natural waters.
2~15. Mills, A.L. and R.R. Colwell. 1977. Microbiological
effects of metal ions in Chesapeake Bay water and
sediment. Bull. Environ. Contamin. Toxicol. 1e:99-103.
Effect of chromium, cadmium, cobalt, lead, and mercury
e6
-------
salts on C-14 02 uptake by marine algae and microorganisms from
Chesapeake Bay was determined. The alga Dunaliella was not
affected by 25 or 100 mg/l of Cr, Cd, or Co. Uptake in 25 mg
Pb/l was reduced to 75% of control values; in 100 mg Pb/l this
was reduced to 50%. Hg at 2.5 and 10 mg/l decreased uptake to 25
and 22~, respectively. Chlorella showed no effect to 25 or 100
mg/l of Cr, Co, or Pb, or 100 mg/l of Cd. Uptake was reduced to
87% in 25 mg Cdll, to 3L1% in 2.5 mg Hg/l, and to 0% in 10 mg
Hg/lo Microogranisms in Bay water were not affected by levels
tested of Cr or Pb. However, uptake was reduced to 67 and 48% in
25 and 100 mg Cd/l, respectively, to 93 and 60% in 25 and 10 mg
Coil, and to 8 and 4% in 2.5 and 10 mg Hg/l. Inhibition of C-14
glucose oxidation to microorganisms in water and sediment samples
from two sites in the Bay was Ll7-100% and 73-100% in 10 and 100
mg Coil, respectively, 0-35% and 0-94% in 10 and 100 mg Cr/l,
19-73% and 30-81% in 10 and 100 mg Pb/l, and 0-~4% and 51-94% in
10 and 100 mg Cd/l. In 10 mg Hg/l, C-14 glucose oxidation was
reduced up to 97% for water, 0% for sediment; for 100 mg Hg/l a
similar pattern was recorded. Heterotrophic microorganisms from
Colgate Creek, a recipient of high anthropogenic metal input,
were more metal-resistant than those from relatively clean
Chesapeake Beach.
2416. Mills, B.J., P. Suter, and P.S. Lake. 1976. The amount
and distribution of calcium in the exoskeleton of
intermoult crayfish of the genera Engaeus and
Geocharax. Austral. Jour. Marine Freshwater Res.
27 :517 -523.
Total exoskeleton calcium concentration is low in
crayfish Engaus fossor, ~ leptorhynchus, Engaeus sp., and
Geocharax falcata in comParison with most other crustaceans,
especially decapods. Concentrations ranged from 45,600 to 74,700
mg Ca/kg wet wt with mean percentage concentrations of
5.21-6.15~. Results suggest that total exoskeleton Ca decreases
with increasing size in Engaeus sp. and~. fossor, while ~
falcata maintains a constant Ca level with increasing size.
Reduction in relative calcification may be an adaptation to low
Ca concentrations in water inhabited by crayfish. Distribution
of Ca in exoskeletons of the four species were 133,000-245,000 mg
Ca/kg wet wt in cheliped, 'dB, 000-200, 000 in antenna,
82,000-195,000 in carapace, 63,000-119,000 (also a high of
~~0,000) in legs, ~2,000-150,000 in abdomen, 108,000-164,000 in
telson, and 71,000-141,000 in uropod. Ca distribution was
dissimilar between crayfish species; significance of these
differences is discussed in relation to habitat requirements of
each species.
87
-------
2417.
MitcheJl~ I).D. and M.C. Geddes. 1977. Distribution of
the brine shrilnps Parartemia zietziana Sayce and
Artemia salina (L.) along a salinity and oxygen
gradient in a south Australian saltfield. Freshwater
BioI. 7: 461-467 .
The seasonal distribution of P. zietziana and A.
salina was studied in a south Australian saltfield. P. zIetziana
occurred alone at salinities from 112 to 214 0/00 andA. salina
occurred alone at salinities above 2~5 0/00; the two species
overlapped in the range 214 to 285 0/00. Respiration experiments
irrlicated that A. salina had a lower 'critical' oxygen
concentration than P. zietziana, apparently due to the presence
of hemoglobin in A.salina. This may result in an adaptive
advantage at high-Salinity and low dissolved oxygen.
2418.
Mukherjee, S. and S. Bhattacharya. 1977. Variations in
the hepatopancreatic a -amylase activity in fishes
exposed to some industrial pollutants. Water Research
11:71-74.
Effects of phenol, sulphide, copper and anmonia on
~ylase activity was determined in the freshwater teleosts
Ophicephalus punctatus and Clarias batrachus. Three dosage
levels of Cu were tested: a low dose in whi ch ~0-1 00% of the test
fishes survived (28.0-51.5 mg/l); an LC-50 (48 hr) level
(41.5-70.0 mg/l); and a high dose where survival was only 20%
(54.0-90.0 mg/l). At low Cu concentrations enzymatic inhibition
reached 40% in Q. punctatus and 21% in ~ batrachus. Enzyme
inhibition was greater in the crude effluent of the four
pollutants for 4e hr than in the irrlividual pollutants. This may
be due to the high anmonia or to a synergistic action of the
toxicants present in the effluent. A 90 day chronic exposure to
the undiluted effluent caused no mortality but produced 74%
enzyme inhibition in ~ punctatus.
24 19 .
Munda, LM. 1977. Combined effects of temperature and
salinity on growth rates of germlings of three Fucus
species from Iceland, Helgoland, and the North
Adriatic Sea. Helgol. wiss. Meeresunters 29:302-310.
Growth rate of germlings of Fucus distichus edentatus
from Iceland, F. vesiculosus from Helgoland, North Sea, and F.
virsoides from-the North Adriatic Sea was investigated for b--
months in temperatures from 3 to 15 C and salini tes from 2.7 to
ee
-------
31.1 0/00. Maximum growth rate for F. distichus was at 9 C;
growth rate generally increased with-temperature for the other
tID species. Growth increased with increasing salinity for all 3
species of algae. Reduction of growth upon dilution was most
pronounced in F. vesiculosus, though in view of its overall
distribution, a higher salinity tolerance was expected.
Susceptible strains may have developed at Helgoland, where
salinity rarely drops beloo 30 0/00.
2420.
Munda, LM. and B.P. Kremer. 1977. Chemical composition
and physiological properties of fucoids under
corrlitions of reduced salinity. Marine Biology
42:9-15.
Thallus segments of two seaweeds, Fucus serratus and
F. vesiculosus, were grom in seawater media at salinities
between 32.7 and 2.3 0/00 for a least 2 weeks. Compared to
controls, both species exhibited a reduction in dry ~ight, ash
weight, chloride, and mannitol content with decreasing salinity.
Total N, in terms of protein contents, increased. Respiratory
02-consumption was markedly increased at looer salinities,
whereas rate of photosynthetic 02-evolution showed some
depression. Salinity had relatively little effect on
distribution of photosynthetically assimilated C-14 among the
phosphate esters, amino acids, organic acids, and mannitol.
Release of C-14 assimilates into the medium never exceeded 2% of
total C-14 uptake, but was stimulated in media of reduced salt
content. Results are discussed with emphasis on long-term
adaptation and osmoregulation.
2421.
Nakamura, R., Y. Suzuki, and T. Ueda. 1977. Distribution
of radionuclides among green alga, marine sediments
and seawater. Jour. Radiation Res. 1~:322-330.
Distributions of Co-bO, Zr-95-Nb-95, Ru-10b-Rh-106,
and Cs-137, each added at 0.02 mCi, were examined for 14 days in
green alga Ulva pertusa, seawater, and marine sediments from the
coast of Japan. Major portions of Co-60, Zr-95-Nb-95, and
Ru-1Ob-Rh-106 were in sediments, at ~, 54, and b3%,
respectively; ~2% of Cs-137 was found in seawater. Ulva
contained 41% of the available Zr-95-Nb-95, 26% of Ru-10b-Rh-106,
4% of Co-60, and O.tS" of Cs-137. Activity ratios of marine
sediments (radioactivity in sediments vs. seawater) were 4000 for
Co-60, 30 for Cs-137, 900 for Ru-106-Rh-10b, and 1~00 for
Zr-95-Nb-95.
~9
-------
2422.
Namminga, H. and J. Wilhm. 1977. Heavy metals in water,
sediments, and chironomids. Jour. Water Poll. Contr.
Feder. 49: 1725-1731.
Concentrations in water of Cu, Cr, and Zn at 5
stations along Skeleton Creek, Oklahoma, ranged from 0.003-0.014
mg copper/l in winter to 0.0003-0.004 in summer; from below
detection to 0.003 mg chromiumll in winter and from below
detection to 0.001 in summer; and from 0.007-0.028 mg zinc/l in
winter to below detection-0.004 in summer. Concentrations were
dramatically higher at stations near industrial and domestic
outfalls. Metal concentrations in sediments along Skeleton Creek
were 0.4-1.9 mg/kg in winter and 1.3-6.4 mg/kg in summer for CUi
1.3-6.3 and 2.4-14.7, respectively, for Cr; 1.0-6.2 and 1.0-10.1
for Pb; and 2.2-9.2 and 2.3-26.6 for Zn. Maximum concentrations
were found below waste outfalls. Concentration factors of Cu,
Pb, and Zn but not Cr in larval chironomid insects exceeded
factors for sediments.
2423.
Nelson, D.A., A. Calabrese and J.R. MacInnes. 1977.
Mercury stress on juvenile bay scallops, Argopecten
irradians, under various salinity-temperature
regimes. Marine Biology 43 :293-297.
Scallop survival was significantly affected by
mercuric chloride and by salinity, as well as by interaction
between temperature-Hg concentration, and temperature-salinity.
Mercury, then salinity, were the two most important variables
affecting survival. Maximal survival at 52 ug Hg/l was estimated
to occur between 15.0 and 2~.5 C, and salinities between 17.4 and
24.4 0/00. Biocidal properties of mercury at ~89 u/l was higher
at 25 C and 15 0/00 than at 15 C; this enhancing effect
diminished at higher mercury concentrations. The lowest LC-50
(96 hr) value recorded of 57.6 ug Hg/l occurred at the highest
temperature, 25 C, and lowest salinity, 15 0/00, tested. The
highest LC-50 (96 hr) value of 13~.0 ug/l was observed at 25 C
and 22.6 0/00.
2424.
Nestler, J. 1977. Interstitial salinity as a cause of
ecophenic variation in Spartina alterniflora.
Estuarine Coastal Marine Sci. 5:707-714.
Height of Spartina alterniflora plants on salt marshes
in Georgia was related to total dissolved salt concentration of
the underlying substrate. Horizontal stability of interstitial
90
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water allows formation of interstitial salinity clines on the
salt marsh. Pore water salinities are lowest near sources of
est uari ne or freshwater (20 0/00) and hi ghest in areas removed
elevationally from low saline water sources (up to 40 0/00).
Growth of S. alterniflora is inversely related to interstitial
salinity along these clines; growth is robust in lower salinities
and weak in higher saline areas. Causal relationship between
interstitial salinity and plant growth forms is presented.
2425.
Nevman, M.W. and S.A. MacLean. 1974. Physiological
response of the cunner, Tautogolabrus adspersus, to
cadmium. VI. histopathology. In: U.S. Dept.
Commerce NOAA Tech. Rept. NMFS SSRF-681:27-33.
Histopathological effects of acute exposure of a
marine fish to water containing cadmium chloride were evident in
kidney, intestine, hemopoietic tissue, epidermis and gill. Few
significant changes were noted in cunners exposed to less than 48
mg Cd/l for 96 hrs. The results implicate renal failure as the
probable cause of death after acute exposure to Cd. At 24 mg
Cd/l, there was same swelling of intestinal epithelium; at 48
mg/l, columnar cells were swollen, nuclei hypertrophied and
nucleoli prominent. At 48 mg Cd/l, kidneys from 3 of 6 fish
exhibited diffuse tubular necrosis, and one of these exhibited
focal tubular necrosis. Blood spaces in kidneys of fish exposed
to 24 and 48 mg Cd/l contained large numbers of cells thought to
be imnature thrombocytes. Gills of cadmium-exposed fish showed
epithelial hypertrophy, hyperplasia of interlamellar epithelium,
and desquamation. At 48 mg/l, the epidermis showed swelling of
epithelial cells and a paucity of mucus secretion. Percent
leucocytes in normal cunner blood (and after 96 hr exposure to 48
mg Cd/l) were: 69.3 (35.9) in mature thrombocytes; 15.6 (50.2) in
neutrophils; 11.2 (4.5) in small lymphocytes; 2.2 (1.5) in medium
lymphocytes; 0.7 (1.4) in eosinophils; and 1.1 (6.1) in blasts.
2426.
Nielsen, S.A. 1975. Cadmium in New Zealand dredge
oysters: geographic distribution. Inter. Jour.
Environ. Anal. Chemistry 4:1-7.
Mean cadmium levels of 1.4 to 7.9 mg/kg wet wt or 8.7
to 49.6 mg/kg dry wt were found in dredge oysters, Ostrea
lutaria, from 24 stations around Foveaux Strait, New Zealand.
The Cd content was proportional to body weight up to a body
average of about 8-10 g; in larger oysters the Cd content was
independent of body wt. These data, in consideration with
91
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prevailing winds, indicate that the source of Cd must be west of
Foveaux Strait, possibly in Fiordland. High Cd levels in these
oysters are naturally occurring since there is no industrial
pollution in the area. Compared with Cd concentrations in other
oyster species, ~ lutaria may have a predilection for
accumulating Cd.
2427.
Nimmo, D.R., D.V. Lightner, and L.H. Bahner. 1977.
Effects of cadmium on the shrimps, Penaeus duorarum,
Palaemonetes pugio and Palaemonetes vulgaris. In:
Vernberg, F.J., A. Calabrese, F.P. Thurberg, and W.B.
Vernberg Ceds.). Physiological responses of marine
biota to pollutants. Academic Press, N.Y.:131-1e3.
~ vulgaris were acutely and chronically more
sensitive to Cd as cadmium chloride than P. duorarum. No
significant differences were shown with Ca-as acetate, sulfate,
or nitrate. Bioaccumulation of Cd from water occurred at
concentrations as law as 0.002 mg/l in P. duorarum and 0.008 in
~ vulgaris. Cd in tissues of ~ duorarum did not plateau at
concentrations <0.003 mg/l, but did plateau in ~ pugio at >0.005
mg/l within 7 days. Cd in P. duorarum varied with water
concentrations up to 1.0 mg/l with highest uptake in
hepatopancreas, followed by gills, exoskeleton, muscle, and serum
in that order. Levels of Cd increased in muscle after Cd-exposed
shrimp were transferred 'to Cd-free water. Natural Cd levels in
shrimp were reduced by h:>lding feral animals in flowing water.
P. duorarum, exposed to Cd near the LC-50 C 96 hr) concentration
of 3.5 mg/l, consistently developed blackened foci or blackened
lamellae in branchia. Occasionally, blackened cuticular lesions
on appendages and general body surfaces were also observed.
Cadmium collected by hemocytes and accumulated in gills may be
sloughed during post-treatment. Shrimp that survived Cd
expooures and were placed in Cd-free water sloughed blackened
portions of branchia, with normal appearance within 14 days.
When ~ vulgaris were exposed to 0.075 mg Cd/l for 10 days, gill
lamellae were blackened, necrotic and distended due to congestion
wi th larger numbers of hemocytes. When Artemia containing Cd
were used as food, transfer of Cd to ~ vulgaris was much less
efficient than transfer directly from water. To produce
equivalent whole body residues in shrimp, about 15,000 times more
Cd must be introduced in food than could be obtained from
seawater.
2428.
Noel-Lambot, F. and J.M. Bouquegneau. 1977. Comparative
study of toxicity, uptake and distribution of cadmium
92
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and mercury in the sea water adapted eel Anguilla
anguilla. Bull. Environ. Contamin. Toxicol.
18:418-424.
Mortali ty of seawater adapted eels reached 100% in 5
hrs during imnersion in 10 mg Hg/l, in 20 days in 1 mg Hg/1, in
just over 10 hrs in 200 mg Cd/l, and in 6 days in 50 mg Cd/l.
After 15 days, mortality was 25% in 0.1 mg Hg/l and 50% in 30 mg
Cd/l. Distribution of cadmium in eels exposed to 0.13 mg Cd/l
for 60 days was 16 mg/kg wet wt in kidneys, 6 in digestive tract,
4 in liver, and <2 in other organs; total body concentration was
0.6 mg Cd/kg wet wt. M..1scle contained 27% of total body Cd,
digestive tract 25%, and kidneys 20%. Eels exposed to 0.1 mg
Hg/l for 32 days had 116 mg Hg/kg dry wt in kidneys, 110 in
spleen, 67 in gill filaments, 48 in liver, and 19 to 13 in other
organs. Total body concentration was 15 mg Hg/kg wet wt; muscle
contained 66% of total body Hg, and skin 13%.
2429 .
O'Conner, J.S. 1975. Contaminant effects on biota of the
New York Bight. In: Proc. Gulf Caribbean Fish.
Instit. 28th Annual Session, Bal Harbour, Fla.:
50-63.
Annual quantities of contaminants reaching the New
York Bight include 3,940 to 32,000 metric tons from atmospheric
fallout of Cd, Cr, Cu, Fe, Pb, and Zn, plus a variety of sources
of municipal am industrial sludge, wastewater, and runoff.
Examples of impact on marine resources include a high prevalence
of diseases in fish and crustaceans; major alterations in
distribution and abundance of bottom living organisms away from
local bays; widespread distribution in exceptionally high numbers
of coliform and fecal coliform bacteria, indicative of pathogenic
bacteria, leading to closure of clam fishery operation; presence
of transfer-resistant (R+) bacteria which are relatively
insensitive to a broad spectrum of heavy metals and antibiotics;
and noxious concentrations of suspended particulate material,
flotsam and surface slicks.
2430.
Oduleye, S. O. 1976. The effects of hypophysectomy,
prolactin therapy and environmental calcium on
freshwater survival and salinity tolerance in the
brom trout Salmo trutta L. Jour. Fish. Biology
9:463-470.
Hypophysectomy resulted in a loss of ability of the
93
-------
euryhaline brown trout to survive in freshwater. The mean
survival time was 4-5 days. Maintenance in a medium containing 5
roM calcium increased the mean survival time to ~ days while 10 roM
decrease:i it. Injection of 0.2 LU./gm prolactin enabled
hypophysectomize:i fish to survive the 2-week duration of the
experiment. High environmental calcium, or pre-adaptation to a
medium of high calcium, increased salinity tolerance of the brown
trout probably by promoting a quick return of plasna electrolyte
concentration to normal after transfer to seawater.
2431.
Okazaki, R.K. 1976. Copper toxicity in the Pacific
oyster, Crassostrea gigas. Bull. Environ. Contamin.
Toxicol. 16:65~-654.
Oysters were exposed to copper levels of 0.10, 0.25,
0.50, 0.75, or 1.00 mg/l for three separate 96-hr intervals at
12-15 C and 33 0/00 S. One 336-hr exposure to Cu concen-
trations of 0.010, 0.025, 0.050, 0.075, or 0.100 mg/l was
performed to test sublethal effects. The 96 hr LC-50 was 0.56
mg/l; all deaths occurred after 72 hrs. However, at 1.00 mg Cull
oyster mortality averaged 67%. Thus, the LC-50 may represent the
up~er limit of response to lower but lethal concentrations of
Cu +. Copper at 1.00 mg/l may become biologically IIDavailable
due to precipitation, but oysters may also be able to sense this
chemical form and cease feeding by closing their valves. The
author's preliminary experiments show 100% survival of oysters
exposed to 5.b and 7.5 mg Cull for 96 hrs. In the 336 hr test,
oysters survived all concentrations without reaching 50%
mortality. Survival ranged from 60-~0% and death first appeared
after 144 hrs.
2432.
Olsson, M. 1976. Mercury level as a function of size and
age in northern pike, one and five years after the
mercury ban in Sweden. Ambio 5:73-76.
Mercury levels in muscle of Esox lucius collected from
a lake previously polluted by a papermill in central Sweden
decreased after mercury discharge fran the mill ceased. Several
fish in 196~ contained ~5.0 mg Hg/kg wet wt. In 1972, all fish
contained <4.0 mg Hg/kg. Of five tested parameters of size,
length was best with positive correlation coefficients with Hg
levels of 0.67-0.77. Male pike, whi ch grow more slowly, had
significantly higher Hg levels in muscle than females. Males of
different ages but the same length showed similar Hg
accumulation. Correlation between Hg levels and condition factor
94
-------
was weakly negative; during starvation, mercury levels
seemed to increase. Author suggests that size of fish
metabolic Hg turnover role should be of prime interest
prediction of fish mercury levels.
in pike
or
in
2433.
Pace, F., R. Ferrara, and G. Del Carratore. 1977.
Effects of sublethal doses of copper sulfate and lead
nitrate on growth and pigment composition of
Dunaliella salina Teed. Bull. Environ. Contamin.
Toxicol. 17:679-6tl5.
Concentrations of 0.5, 1.25, or 2.5 mg Cull added as
copper sulfate inhibited growth of the green flagellate
Dunaliella salina over 31 days; number of cells was always lower
than controls. No growth was recorded at 5.0 mg Cull. Sublethal
Cu concentrations retarded onset of 10garithITdc growth phases.
In 2.5 mg Cull, this growth phase occurred after 1tl days,
compared to 3 days for controls. Lead nitrate, at 0.3 mg Pb/l,
slightly inhibited culture growth, while 0.9, Q.5, and 15.0 mg
Pbll ~ignificantlY reduced algal growth after day 16. Addition
of Pb + as lead chloride produced similar results. Normal
Dunaliella cells undergo pigment content reduction during rapid
10garithITdc growth. In Cu-treated cells, growth was sl~er and
pigment content reached higher values, up to 14.9 x 10-
mg/cell in 2.5 mg Cull at 12 days, before decreasing. However,
total pigment content of culture generally decreased with
increasing concentrations of both metals. Carotenoid content of
cells in 4.5 and 15.0 mg Pbll increased compared to controls. An
increase in carotenoid pigments is normally associated with a
general decrease of nutrients in the medium.
2434.
Palmer, J.B. and G.M. Rand. 1977. Trace metal
concentrations in two shellfish species of commercial
importance. Bull. Environ. Contamin. Toxicol.
1tl:512-520.
In fall 1974, spring 1975, and summer 1975, the
scallop Placopecten magellanicus and quahaug Arctica islandica
were collected from the Continental Shelf south of Long Island
and analyzed for metal content. Concentrations, in mg/kg wet wt,
for ~ magellanicus ranged from O.~ to tl.7 for cadmium, 0.2 to
2.4 for chromium, 0.3 to 3.0 for copper, 0.4 to 2.2 for lead,
<0.1 to 0.3 for mercury, <0.5 to 3.3 for nickel, and 9.3 to 24.0,
with a high of 109.0, for zinc. In A. islandica, values ranged
from <0.06 to 0.9 for Cd, 0.3 to 2.5for Cr, 0.1 to 3.tl for Cu,
95
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<1.0 to 2.6 for Pb, 0.1 to 1.2 for Hg, 1.1 to 7.0 for Ni, and 2.4
to 25.tl for Zn. Mean Cd level was 7.5X higher in P. magellanicus
than in A. islandica; for all other metals P. mageIIanicus
containeCi"equal or lower average amounts. -
2435.
Parker, J.I., H.L. Conway and E.M. Yaguchi. 1977.
Dissolution of diatom frustules and recycling of
amorphous silicon in Lake Michigan. Jour. Fish. Res.
Ed. Canada 34:545-551.
Levels of diatom frustules and amorphous silicon per
kilogram of dry sediment were measured at 5 m intervals in the
upper water column (0-40 m), in sediment traps at 37 and 60 m
belOd the surface, and in a sediment core. The average
concentration of frustules/kg ot' dry sediment in the water5column
was 3.14 x 105. Mean levels at 37 and 60 m were 1.16 x 10
and 5.03 x 104 frustules/kg dry sediment, respectively.
Subsamples from the sediment core averaged 6.31 x 103
frustules/kg dry surficial sediment. The average proportion of
amorphous silicon/kg dry sediment was 0.009% in the water column,
0.008% in the 37 m traps, 0.006% in the 60 m traps and < 0.002% in
subsamples from the sediment core. The major fraction of
amorphous silicon produced annually as diatom frustules was
decomposed before incorporation in the permanent sediment. A
comparison of the annual silicon requirement for diatom
production and silicon inputs showed that the watershed
contributed <5.0% of the dissolved reactive silicon required for
annual diatom production. These observations suggest that
recycling of biogenic silicon provides the major source of
soluble reactive silicon required for diatom blooms in Lake
Michigan.
2436.
Parker, J.I., H.L. Conway and E.M. Yaguchi. 1977.
Seasonal periodicity of diatoms, and silicon
limitation in offshore Lake Michigan, 1975. Jour.
Fish. Res. Ed. Canada 34:552-558.
Seasonal distributions of soluble reactive silicon and
diatom biomass shOd a strong relationship. Diatom biomass maxima
occurred in spring and fall and produced a bimodal bloom
sequence. As the spring bloom progressed, the diatom
accumulation rate declined and soluble reactive silicon was
reduced from 0.013 to 0.007 mmole/l. In summer, after the bloom,
silicon was at a minimum of 0.001 mmole/l and diatom biomass was
also at seasonal minima. Diatom biomass increased
96
-------
agpin in October when silicon supplies were replenished and the
concentration exceeded 0.007 mmoles/l. A critical silicon
concentration of approxllnately 0.006 mmoles/l may control the
development and timing of offshore diatom populations in Lake
Michigan.
2437.
Parvaneh, V. 1977. A survey of the mercury content of
the Persian Gulf shrllnp. Bull. Environ. Contamin.
Toxicol. 1~:77~-782.
Mercury levels in 100 samples of Persian Gulf shrimp
ranged from 0.08 to O.~~ mg/kg wet wt with a mean of 0.24 mg/kg.
Eight percent of these samples taken from different fishery
stations and retail shops showed mercury content above 0.5
mg/kg. In most samples the value was below 0.3 mg/kg.
2438.
Pascoe, D. and D. L. Mattey. 1977. Studies on the
toxicity of cadmium to the three-spined stickleback
Gasterosteus aculeatus L. Jour. Fish Biology
11 : 207 -215.
Cadmium was lethal to sticklebacks at all
concentrations tested between 100.0 and 0.001 mg Cd/l, with an
LC-50 (96 hr) at 23 mg Cd/l. Median pericx:l of survival in
minutes was ~,OOO at 0.001 mg/l; 23,500 at 0.01 mg/l; 11,000 at
0.1 mg/l; 19,200 at 1 mg/l; 2,~0 at 10 mg/l and 413 mins at 100
mg/l. The pattern of mortality shown by a tllne-concentration
curve suggests that toxicity is not due to a single mechanism but
changes with concentration. Unusua.l swinming behavior was
associated with high Cd levels. Fish accumulated Cd with whole
body levels increasing from 0.90 mg/kg wet wt at 0.001 mg Cd/l
exposure concentration to 51.0 mg/kg at 100 mg Cd/l. The
concentration factor decreased with increasing exposure
concentration from 0.51 at 100 mg/l to 511 at 0.001 mg/l. The
plerocercoid parasite Schistocephalus solidus in the host's
perivisceral cavity contained at least 50% less cadmium than the
tissue of its host.
2439.
Patrick, F.M. and M.W. Loutit. 1977. The uptake of heavy
metals by epiphytic bacteria on Alisma plantago
-aquatica. Water Research 11:699-703.
Epiphytes of the bacteria Sphaerotilus on too surface
of the freshwater plant Alisma plantago-aquatica collected from a
polluted river were a major factor contributing to the total
97
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metal concentrations of the plant. Estllnations of metal
concentrations in mg/kg dry wt in young leaves of Alisma with
epiphytes (and without) were: 2.6 t 1.9) for Cr, 155 (70) Cu,
1306 (151~) Mn, 11~5 (~6~) Fe, 14 (1~) Pb, and 119 (9B) for Zn.
Removal of epiphytes from leaf surface of young and old plants
resulted in significant reductions in levels of Cr (reduced by
15-50%), Cu (30-35%), and Fe, Pb, and Zn t 10-50%). Increases in
total metal concentration of leaves were paralleled by similar
increases in percentage of Cu and Zn retained in epiphytes of
young lea.ves. Both the numbers of epiphytes and total
concentrations of Cr, Pb and Zn of plants increased in polluted
water. These observations indicate that absorption of metals by
Alisma roots provides a basal level of metals in plant tissues,
and that these levels are subject to plant metabolic
requirements, sedllnent metal concentrations, and supplementation
by absorption of metals from water by epiphytic bacteria. Amount
of metal absorbed by root system and by epiphytes appeared to
increase by the same degree in polluted water. Levels of metals
in the sedllnents in mg/kg dry wt were: 10-M Cr, 1~0-2~6 Cu,
~5-130 Mn, 6~9-1593 Fe, 53-79 Pb, and 100-3~5 for Zn.
2~~0.
Patterson, C. and D. Settle. 1977. Comparative
distributions of alkalies, alkaline earths, and lead
among major tissues of the tuna ThUMUS alalunga.
Marine Biology 39:289-295.
Concentrations of potassium, rubidium, cesium,
calcium, strontium, barium, and lead in various tissues of ttma
caught off San Diego, California were determined. Potassium, Rb,
and Cs were all distributed uniformly throughout the organs,
muscles, and skeleton, with 900 to 6,800 mg/kg of K wet wt being
the most prevalent of the three. The skeleton contained 95% of
the Ca and Sr, and 70% of the Ba and Pb, wh He tSO% of the K, Rb,
and Cs are in muscle, as percent of total body metal in the
organ. Smaller amounts of Cs, Ba, and Pb are associated with the
nutrient metals K and Ca in marine animals compared to
terrestrial animals. This difference is a result of the purity
of K and Ca in seawater and the smaller amotmts of trace metals
associated with them ccmpared to the llnpurity of K and Ca in
terrestrial rocks. Food-chain enhancement and depletion of
metals can be evaluated by ccmparing ratios of trace metals to
abundant nutrient metals in seawater and ttma. Cesium, for
example, is enriched relative to K, in going fran seawater to
tuna, by a factor of 13; Sr and Ba are both depleted by factors
of 5 relative to Ca; and Pb is enriched relative to Ca by a
factor of 1~.
9~
-------
2~~ 1.
Pearse, J.B. 1977. Report to the working group on
pollution baseline and monitoring studies in the Oslo
Conmission and ICNAF areas on heavy metals in selected
finfish and shellfish from the northwest Atlantic.
International Council for the Exploration of the Sea.
Fisheries Improvement Corrnnittee. C.M. 1977/E:34. 97
pp.
Concentrations of Ag, As, Cd, Cr, Cu, Mo, Ni, and Pb
in fish, elasmobranchs, crustaceans, and molluscs from the
northwest Atlantic were tabulated. Other than mercury, no
samples contained mean levels of metals which exceeded values
considered harmful for human consumption. Same demersal species,
such as dogfish and marlin, contained individual Hg levels that
exceeded 0.5 mg/kg wet wt "action levels". Possible
relationships between size of fish, geographic area of catch,
species, or feeding behavior and metal concentrations have not
been confirmed.
2~~2.
Pentreath, R.J. 1976. The accumulation of mercury by the
thomback ray, Raja clavata L. Jour. Exp. Mar - BioI.
Ecol. 25:131-1~O:--
Maximum mercury concentration occurring naturally in
30 g rays from Suffolk, England was 0.22 mg/kg wet wt in blood
cells, making up 2.0% of total body Hg. Gut and gill filaments
of this elasmobranch contained 0.16 and 0.13 mg/kg, respectively,
making up 10.4 and 4.5% total body Hg. Muscle, with 0.05 mg/kg,
had the highest proportion of body Hg with 59.5%. Blood pla3I1a
had only 0.001 mg/kg, O.O~% total body Hg. Concentration factor
of Hg-r03 in rays over that in Hg-203 Cl2 labelled seawater (5
x 10-1 mCi/l) rose to 40 in 4 days, and to 500 in 64 days.
Loss of Hg-203 after 7~ days was < 20%. Concentration factor in
rays, using CH3Hg-203 Cl seawater, increased linearly from 0 to
1100 in (:$5 days. ~fimum mean concentration of Hg-203/blood
plasma from 5 x 10- mCi/l Hg-203 C12 labelled seawater was
B1 in gill filaments. Other high values were rectal gland 70,
spleen 58, and kidney 5~. Minimum levels were blood cells 9,
muscle 7 and cartilage 3. These concentrations after 91 days
lass were gill filament 96, rectal gland 86, spleen 73, kidney
71, blood cells 12, muscle 10, and cartilage 6. Accumulation
for 91 days of Hg-203 from CH3Hg-203 Cl seawater produced
Hg-203/blood pla3I1a values of ~2 for rectal gland, gill filaments
34, liver 32, heart 28, and 6 for cartilage. Concentrations
after 7~ days loss were gill filaments 37, 1i ver 30, muscle 29,
rectal gland 29, blood cells 7, and gonad 5. Retention of
99
-------
Hg-203 5 to e days after rays were fed labelled Nereis worms was
only 8.b-20.3% from Hg-203 C12 and 94.0-99.5% from CH~Hg-203
Cl. After 35 days, retention was only 15-6% from Hg-203 C12
and 90% from CH3Hg-203 Cl. Distribution, as Hg-203
concentration/plasma, in organs was 340 for stomach, 37 kidney,
27 liver, 1 muscle and 0.9 cartilage from Nereis fed Hg-203
C12' From CH3Hg-203 Cl, values ranged from ~5. b for heart ~
b8.7 muscle, 54.5 liver, 43.0 blood cells, to 5.9 for cartilage.
2443.
Pentreath, R.J. 1977. The accumulation of arsenic by the
plaice and thornback ray: some preliminary
observations. International Council for the
Exploration of the Sea. Fisheries Improvement
Commi t tee. C . M. 1977 /E: 17. 11 pp .
Accumulation of As-74, as sodium arsenate, from
seawater and from labelled food by plaice, Pleuronectes platessa,
and r'ays, Raja clavata, was compared. Uptake from seawater, with
0.001-0.003 mg As/l and 0.001 mCi/l as tracer, was slow and
resulted in uniform labelling of all internal organs after 42
days. Concentration factor of As in plaice eggs was only O.b
after 14 days, while larvae had CF of 2 after ~ days. Retention
of As-74 from labelled polychaete worms, Nereis sp., as food was
t55% for the ray 10 days later, but was 10% for the plaice. Both
species contained the largest fraction of As-74 in muscle, 75% in
rays on day 45 and 95% in plai ce on day 35, although rays also
had high concentrations in kidney.
2444.
Pesch, G., B. Reynolds and P. Rogerson. 1977. Trace
metals in scallops from wi thin and around two ocean
disposal sites. Marine Poll. Bull. 8:224-228.
Concentrations of iron, copper, chromium, aluminum,
silver, manganese, lead, cobalt, nickel, vanadium, cadmium, zinc
and titanium were determined in sea scallops Placopecten
magellanicus collected from the vicinity of two ocean disposal
sites off the U.S. mid-Atlantic coast. Mean metal
concentrations, in mg/kg dry wt, in soft tissues were: Ag 1.8;
Al 338.0; Cd 20.9; Co 0.5; Cr 3.0; Cu 7.3; Fe ~03.0; Mn 29.t5; Ni
4.4; Pb 3.64; Ti 9.e; V 28.5; and Zn 105.0. Patterns of metals
distribution show that Ag, Cu, Ni, Cd, and V may be used as tags
for individual wastes disposed at the two sites; that disposed
material are transported by currents south and southwest from
disposed sites; and that biological availability and
100
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potential toxicity of some metals pose a threat to marine biota.
2445.
Phillips, D.J.H. 1977. Effects of salinity on the net
uptake of zinc by the common mussel Mytilus edulis.
Marine Biology 41:79-88.
Net uptake of chloride salts of zinc, cadmium and
copper by mussels at 35 0/00 salinity and under a fluctuating
salinity range between 35 and 15 0/00 was determined. Mussels
subjected to a mixture, in mg/l, of 0.5 Zn, 0.05 Cd, and 0.1 Cu
for 5 days smwed mean concentrations in mg/kg dry wt soft parts
as follows:
Salinity Regime Zinc Cadmium Copper
Control, 35 0/00 (start) 258 9.7 7.5
Control, 35 0/00 (Day 5) 233 10.0 6.9
5 Days, 35 0/00 431 20.0 33.8
5 Days, 35128 0/00 426
5 Days, 35~22 0/00 542 28.8 78.0
5 Days, 35~15 0/00 409
Two groups of mussels, one from Western Port Bay, Australia, with
salinity range 35 to 36 0/00 and another from Port Phillip Bay with
salinity range 8.5 to 33.5 0/00, were exposed to sublethal
concentrations of zinc chloride of 1.0, 0.8, 0.4 mg/l for 13 days at
35 0/00 salinity. Maximum concentrations for zinc, in mg/kg dry wt.
were as follows:
Location Nominal ZN Zn, in mg/kg dry wt
Concentration (mg/l) Exp I Exp II
Port Philli p Bay 0.4 1167 629
0.8 1215 776
1.0 1241 945
Western Port Bay 0.4 474 591
o.~ 537 703
1.0 629 742
Because salinity affects zinc uptake by mussels under conditions of
stress, this factor should be considered when mussels are used as
indicators of environmental zinc levels.
2446.
Phillips, D.J.H. 1977. The common mussel Mytilus edulis
as an indicator of trace metals in Scandinavian
waters. 1. zinc and cadmium. Marine Biology
43: 283-291.
101
-------
Concentrations of zinc in mg/kg dry wt whole soft
parts of mussels from 54 locations in Scandinavia ranged from
14-460; for cadmium this range was 0.4-12.9. Local variations in
concentrations of the tWJ metals found in samples taken close to
industrial sources of zinc and cadmium confirmed the ability of
mussels to act as accurate indicators of pollution by these
metals over the entire range of salinities in which this species
can exist. In addition, offshore samples remote from industrial
discharges revealed higher concentrations of Zn and Cd in mussels
from low-salinity areas than mussels from high-salinity areas.
Major decreases in metal concentrations in mussels were apparent
in regions of the Sound and Great Belt, which are areas of rapid
salinity change due to mixing of Baltic water with water from the
Kattegat. Comparison of these results with those reported for
zinc and cadmium in water throughout the study area suggested the
existence of a higher biological availability of these metals in
regions of 100 salinity.
2447.
Phillips, D.J.H. 1977. The use of biological indicator
organisms to monitor trace metal pollution in marine
and estLE.rine environments--a review. Environmental
Pollution 13:2~1-317.
Use of biological indicator organisms to define areas
of trace metal pollution appears more attractive than water or
sediment analysis, as these organisms not only concentrate metals
from water, allowing inexpensive and relatively simple analysis,
but they may also represent a moving time-averaged value for
relative biological availability of metals at each site studied.
The present state of knowledge on use of indicator organisms to
study trace metal pollution is reviewed, with emphasis on
macroalgae, bi val ve molluscs, and teleosts, but also includes
barnacles and decapod crustaceans, limpets, and polychaetes.
Data is presented for Ag, As, Cd, Co, Cr, Cu, Fe, Hg, Mn, Ni, Pb,
and Zn. It is suggested that macroalgae and bi val ves are the
most efficient and reliable indicators at present. It is further
suggested that effects of sampling and environmental variables
have been largely overlooked, and that further field and
laboratory stu:iies are necessary before results of surveys using
biological indicator organisms can be relied upon.
2448.
Pickering, Q., W. Brungs and M. Gast. 1977. Effect of
exposure time and copper concentration on reproduction
of the fathead minnow (Pimephales promelas). Water
Research 11:1079-10~3.
102
-------
The chronic effect of prespawning exposure to various
concentrations of copper on minnow reproduction was determined.
Copper was introduced 6, 3 and 0 months prior to spawning at
concentrations ranging from 4.2 (control) to 98 ug/l. Survival
was not affected by copper at any of the chronic exposure
levels. Prespaming copper exposure time had no significant
effect on reproduction. Number of eggs produced per female
decreasoo at copper levels of 37 ug/l and higher. Final length
of females exposed to 60 and 98 mg Cull for 6 months was
significantly lower than controls; final weight was significantly
lower after 6 month exposure to 98 ug/l. The LC-50 (96 hr)
values were 490 ug Cull for o-week-old fry and 400 ug/l for 6
month old subadult fish. Maximum acceptable toxicant
concentration (MATC) was estimated to be 32.0 ug/l and the EC-50
for egg production (eggs per female) as compared to controls was
41.7 ug/l.
2449.
Price, H.H., II, C.T. Hess, and C.W. Smith. 1970.
Observations of Crassostrea virginica cultured in the
heated effluent and discharged radionuclides of a
nuclear power reactor. Proc. Nat. Shellfish. Assn.
b6:54-b8.
American oysters were grown on rafts for 26 months at
4 sites in effluent waters near the Maine Yankee Nuclear Power
Reactor in Montsweag Bay from 1973 to 1975. At l5he closest site,
accumulation of Co-58 and Mn-54 both reached 10- mCi/kg live
wt. Uptake of radionuclides and growth of oysters were
accelerated at warmer water sites. Calculations from the pulse
driven relaxator model described amplitude and time variation of
Co-58 and Mn-54 concentrations in the field study better than an
existing concentration factor model.
2450.
Prabhu, N. V. and M.K. Hamdy. 1977. Behavior of mercury
in biosystem. 1. uptake and concentration in
food-chain. Bull. Environ. Contamin. Toxicol.
18: 409-417 .
Mercury was followed through 3 trophic systems:
bacteria Bacillus licheniformis; larvae of mosquito Aedes
aegypti; and guppy Lebistes reticulatus, using Hg-203 as mercuric
nitrate or phenyJmercuric acetate. In 0.11 mg Hg-203/kg medium
in inorganic (nitrate) form, maximum uptake by bacteria at 23 C
was 54% of total Hg in media after 72 hr incubation. At 37 and
45 C, maximum uptake was achieved at 24 hr at 78 and 66%,
respecti vely. In 0.11 mg/kg organic Hg-203, uptake was highest
103
-------
in ~5 C, at 66% after 72 hrs. Concentration factor of Hg in
bacteria over media increased with time of incubation for both
inorganic and organic forms of Hg-203, with maximum values
reached within 24 to 72 hr. The highest CF was 78 with
inorganic Hg at 37 C after 72 hr. Higher CF values were
obtained for inorganic as compared to organic Hg at all
incubation temperatures, and values at 23 C were always lower
than those at 37 or 45 C. Hg uptake in mosquito larvae, aged 3,
5, and 7 days, rose steadily in all cases to a maximum of 14-17%
at day 96, in 0.022 mg Hg-203/l as inorganic Hg. In organic Hg,
uptake was highest at 72 hr, being 20% for 7 day old larvae, 15%
for 5 day old, and 13% for 3 day old; all values declined at
later incubation times. CF of Hg in larvae over water was a
maximum at 72 hr in organic Hg for all 3 age groups, ranging
from 381 to 579, and was a maximum at 96 hr in inorganic Hg,
ranging from 95 to 130. Values increased as age of larvae
increased. Uptake of Hg by guppies in 0.015 mg Hg-203/l peaked
at 24% on oour ~ for organic and on hour 72 for inorganic Hg.
CF in guppies over water was higher for organic Hg. Maximum
value for the organic form was 275 at 48 hr which then
decreased, while for inorganic form was 175 at 72 hr before
decreasing.
2451 .
Ramamoorthy, S., S. Springthorpe, and D. J. Kushner.
1977. Competition for mercury between river sediment
and bacteria. Bull. Environ. Contamin. Toxicol.
17: 505-511.
Uptake of mercury by bacteria, Pseudomonas
fluorescens, and by clay sediment was studied in bags suspended
in Ottawa River water with 1.45 mg Hg/l added as Hg(N01)2.
By 25 hrs, bacteria contained 1000 mg Hg/kg dry wt, ana at 72
hrs, almost 1300. Hg concentration in sediment did not reach
100 mg/kg dry wt by 72 hrs. The thick suspension of bacteria
had a much greater binding capacity than sediment, which
normally provides a very efficient sink. When clay sediment was
pre loaded with 400 mg Hg/kg, and washed to remove unadsorbed
material, bacteria accumulated O.~5 mg Hg/kg dry wt by ~ hrs,
and increased to 1. 5 at 96 hrs. Bacteria removed Hg from
sediment even with too dialysis membrane barriers between them.
2452.
Raw 1 ence, D.J. and J.S. Whitton. 1977. Elements in
aquatic macrophytes, water, plankton, and sediments
surveyed in three North Island lakes. New Zealand
Jour. Marine Freshwater Res. 11 :73-93.
10~
-------
Aquatic macrophytes Elodea canadensis, Lagarosiphon
major, Potamogeton crispus, ~ ochreatus, ~ cheesemanii, and
Myriophyllum elatinoides were collected from lakes in New
Zealand and analyzed for 26 elements. Data was provided on
variability within a single strand, and change in element
content during seasons and stages of growth. Surface water,
plankton, and sediment samples were also collected and analyzed
for the same elements. Average composition, in mg/kg dry wt, of
plankton, mainly phytoplankton, was high for Si (160,000), Ca
(13,000), Na (10,000), Al (5,400), K (5,300), Mg (5,200), Fe
(2,600), Mn (420), and Ba (260). Zn, Cu, Co, Mo, Ni, V, Sr, Cr,
and Pb levels were all < 100 mg/kg. Content of N, P, S, Cl, Ti,
B, Ga, and Zr was also determined. Average levels of Mg (5,tSOO
mg/kg), Mn (5,tSOO), Na (5,tSOO), Fe (710), B (33), V (9.2), and
Cr (5.0) and P and Cl were highest in macrophytes from Lake
Rotoaira, which apparently has a higher nutrient level than the
other lakes. M3.xima also reflect differences in catchment
geology between the three lakes.
2453.
Reeve, M.R., J.C. Gamble, and M.A. Walter. 1977.
Experimental observations of the effects of copper on
co pep ods and other zooplankton: controlled ecosystem
pollution experiment. Bull. Marine Science 27 :92-104.
Ingestion, filtration, and fecal pellet production
rates of the copepods Pseudocalanus sp. and Calanus sp.
generally decreased as ambient seawater increased in copper
concentration at levels of 0.000, 0.005, and 0.010 mg/l. Origin
of food (contaminated or not) affected these rates. Feeding
rates of Euphausia pacifica and the ctenophore Pleurobranchia
bachei at both 0.005 and 0.010 mg Cull levels were between 45
and 70% of control values. Egg production varied widely between
animals in different concentrations, while fecal pellet
production remained similar at all Cu levels, based on sediment
trap data. Population control by predation and grazing is also
discussed.
2454.
Reeve, M.R., M.A. Walter, K. Darcy, and T. Ikeda. 1977.
Evaluation of potential indicators of sub-lethal
toxic stress on marine zooplankton (feeding,
fecundity, respiration, and excretion): controlled
ecosystem pollution experiment. Bull. Marine Science
27:105-113.
&1all copepods representing Acartia, Pseudocalananus,
105
-------
Paracalanus, Temora and Oithona genera from three different
locations were exposed to 0.00, 0.01, 0.02, 0.05, or 0.10 mg/l
copper for up to 7 days. These generally showed a decrease in
fecal pellet and egg production with increasing copper
concentrations. A similar trend was evident for copepods
exposed to 0.00, 0.002, or 0.01 mg/l mercury for up to 10 days.
LC-50 (48 hr) concentrations were 0.032 mg/l for Hg, 0.105 mg/l
for Cu, and 0.017 mg/l for a Hg-Cu mixture. Authors state that
although effects could be demonstrated in the 0.001-0.01 mg/l
range, many biological and chemical factors combined to make it
pointless to specify toxicity levels more precisely,
particularly where the aim is to extrapolate data to other
situa.tions for regulatory purposes. Species composition,
season, temperature, and chemical complexing capacity of the
water would all introduce variability. It is suggested that at
this concentration range, chemical species present may be less
important than total amounts. Respiration and excretion rates
of zooplankton were not sensitive indicators of metal stress
under test conditions.
2455.
Reish, D. J. 1977. Effects of chromium on the life
history of Capitella capitata (Annelida:
Polychaeta). In: Vernberg, F.J., A. Calabrese, F.P.
Thurberg, and W. B. Vemberg (eds.). Physiologi cal
Responses of Marine Biota to Pollutants. Academic
Press, N.Y.: 199-207.
Effects of hexavalent chromium at levels of 0.025,
0.05, 0.1, 0.2, and 0.4 mg/l on life cycles of the worm
Capitella capitata were determined over a five month period. In
controls and two lowest concentrations, ~2-95% of the worms
survived, 58 and 57% survival in 0.1 and 0.2, respectively, and
21% in 0.4 mg Cr/l. In concentrations of 0.1 mg Cr/l and lower,
31 to 40 females reproduced, at the two highest concentrations
only 3 to 4 females deposited ova. Average numbers of offspring
from females in <0.1 mg Cr/l was 243-279; this decreased
significantly at Cr levels of 0.1 mg/l and higher, to 144-174
larvae. Percent occurrence of abnormal larvae increased from
0.0 to 1. 7 as Cr concentration increased to 0.4 mg/I. Abnormal
metatrochophore larvae had bifurcated posterior ends and
aberrant sw~ng behavior.
10b
-------
2456.
Reish, D.J. and R.S. Carr. 197~. The effect of heavy
metals on the survival, reproduction, development, and
life cycles for two species of polychaetous annelids.
Marine Poll. Bull. 9:24-28.
Effects of exposure to heavy metals on survival and
reproduction of two polychaetes Ctenodrilus serratus and
Ophryotrocha diadema were measured at concentrations of 0.1-10.0
mg/l for Cd, 0.05-50.0 for Cr, 0.01-1.0 for Cu, 0.1-20.0 for Pb,
0.001-0.5 for Hg, and 0.05-20.0 for Zn. Reduction in number of
the original 40 specimens of Ctenodrilus after 96 hrs occurred at
5.0 mg Cd/I, down to 13, and 10.0 mg Cd/I, with none left; at 5.0
mg Cr/l, down to 13; at 0.25 mg Cull, 30 left, 0.5 Cu with 1
left, and 1.0 Cu with none remaining; at 0.05 mg Hg/l, down to
15, and 0.1 and 0.5 Hg with none; and at 10.0 mg Zn/l, down to
34, and 20.0 with none left. Thirty-six remained at 20.0 mg
Pb/l. Population size of Ctenodrilus increased slightly after 21
days in laver concentrations of Cd, Cu, and Hg. Reproduction was
significantly suppressed in >2.5 mg Cd/I, all levels of Cr, ~0.1
mg Cull, >1.0 mg Pb/l, >0.05-mg Hg/l, and >0.5 mg Zn/l. All-
worms were dead after 21 days in the highest concentrations of
each metal. Reduction in the 40 original specimens of
Ophryotrocha after 96 hrs was as follows: in 5.0 mg/l Cd to 11
and 10.0 Cd to 0; in 0.25 mg Cull to 5, and 0.5 and 1.0 Cd to 0;
in 5.0 mg Pb/l to 34, 10.0 Pb to 22 and 20.0 to 17; in 0.05 mg
Hg/l to 35,0.1 Hg to 16 and 0.5 Hg to 0; and in 1.75 mg Zn/l to
8 and 2.5 Zn to O. Thirty-nine specimens still remained in 5.0
mg Cr/l. Population size of Ophryotrocha increased slightly over
21 days in lower concentrations of Cd, Cu, Pb, Hg, and Zn.
Reproduction was significantly suppressed in 21.0 mg/l for Cd and
Cr, ~0.25 mg Cull, 25.0 mg Pb/l, 20.1 mg Hg/l, and 20.5 mg Znll.
Except for populations exposed to Pb, all worms were dead after
21 days in the highest metal concentrations. Suppression of
reproduction for both worms generally occurred at levels 100X
less than LC-50 (96 hr) values.
2457 .
Robertson, J.D. 1953. Further studies on ionic
regulation in marine invertebrates. Jour. Exper.
Bioi. 30:277-296.
Blood or coelanic fluid was ana lysed for Ca, Mg, Na
and K in echinoderms, sipunculids, molluscs, and crustaceans to
determine extent of ionic regulation. Little regulation is shown
Qy the echinoderm Holothuria; however, the bivalves Ostrea and
Mytilus regulate K, up to 135% of seawater concentrations. The
nudibranch Archidoris accumulates K at 128%, Ca at 132%, and Mg
107
-------
at 107%, while the sipunculid Plascolosoma has lower Mg, (69%)
but higher Na (104%). The cephalopod Sepia regulates all
examined ions except Mg. Values, as % concentration in dialysed
plasma, were Na 92-94%, Ca 84-97%, K 193-223%, and Mg 97-100%.
Vi treous humour of the cephalopod eye in Sepia, Loligo, and
Eledone, may have only 10-20% Mg but ;>115% Na of concentrations
in plasna dialysate. Decapod and stomatopod crustaceans studied
regulated all ions, ranges being Mg 32-99%, Ca 84-137%, Na
97 -111%, and K 120-156%. Portunus, Eupagurus, and the stomatopod
Squilla show more regulation than Dromia and spider crabs Maia
and Hyas. In Pachygrapsus, plasna ions are maintained below
equilibrium values, especially Mg at 24%; total ions are 1,163
mg/kg water compared with 1,353 in seawater. An inverse
relationship existed between degree of activity and Mg blood
content in 16 species of crustaceans; more active species have
lower Mg concentrations. Levels of Cl, 804 and NH4 were also
considered in icn regulation studies of these invertebrates.
2458 .
Robinson, A.V., T.R. Garland, G.S. Schneiderman, R.E.
Wildung, and H. Drucker. 1977. Microbial
transformation of a soluble organoplutonium complex.
In: Drucker, H. and R.E. Wildung (eds.). Biological
implications of metals in the environment. ERDA Symp.
Ser. 42: 52-62. Avail. as CONF-750929 from Nat. Tech.
Inf. Serv., U.S. Dept. Comm., Springfield, VA 22161
Plutonium-resistant fungi, from a Ritzville silt loam,
were grown in liquid culture containing Pu2(DTPA)3 for about
10 days. This organisn was capable of transporting Pu into the
cell and modifying the original organoplutonium complex, as shown
by chrcmatographic and electrophoretic behavior. The several
Pu-containing intra- and exocellular components, which differed
from Pu2(DTPA)'i' exhibited a negative charge and globular
protein equivalent molecular wts < about 3000.
2459.
Robohm, R.A. and M.F. Nitkowski. 1974. Physiological
response of the cunner, Tautogolabrus adspersus, to
cadmium. IV. effects on the irmnune system. In: U.S.
Dept. Comn. NOAA Tech. Rept. NMFS SSRF-681: 15-20.
Two elE'lTlents of the irmnune system in cunners were
examined after 96-hr exposure to cadmium: 1) clearance of
intracardially injected bacteria from the bloodstream and 2)
ability to produce antibody against intraperitoneally injected
sheep red blood cells (SRBC). Exposure to 12 mg/l cadmium
108
-------
increased the rates of bacterial uptake in phagocytes of liver
and spleen but significantly decreased rates of bacterial killing
within these cells. Exposure of fish at 3 to 24 mg/l cadmium
failed to influence antibody production against SRBC. All fish
injected with 48 mg/l of cadmium died within two weeks post-
treatment. Authors suggest that Cd in cunners may increase
susceptibility to infection.
2460.
Roegge, M.A., W.P. Rutledge, and W.C. Guest. 1977.
Chemical control of Zoothamnium sp. on larval
Macrobrachium acanthurus. Aquaculture 12: 137 -140.
Tm chemicals were tested for ability to control
outbreak of Zoothamnium ciliates on larval crustaceans, M.
acanthurus. After 2~ hrs in 0.5 mg/l copper sulfate, 5 to 10% of
Zoothamnium were removed, while larvae had poor movement and
color. In 5.0 mg/l potassium permanganate, < 5% of Zoothamnium
were removed, and again larvae showed poor movement and color.
Only formalin, at 50 mg/l, gave complete control of Zoothamnium
with no ill effects on larvae.
2461.
Romeril, M.G. 1977. Heavy metal accumulation in the
vicinity of a desalination plant. Marine Poll. Bull.
8:8~-~n .
At the Channel Isles of Jersey, England, a
desalination plant operates during summer months to alleviate a
water shortage problem associated with a seasonal tourist
influx. Brine effluents produced by the plant contained elevated
levels of Cu and Zn. Copper content of limpets, Patella vulgata,
before the plant began operation in May was 20 mg Cu/kg dry wt,
but was 282 mg/kg prior to closing in August. For the same
period the copper level in algae, Fucus serratus, increased from
5.9 mg/kg to 204 mg/kg; Fucus spiralis increased from ~. 1 mg/kg
to 231 mg/kg. Zinc in Patella increased from 175 mg/kg to 255.
Observed copper concentrations remained elevated during the
winter, possibly due to the Cu coating retained on boulders and
pebbles in the area.
2462.
Ronald, K., S. V. Tessaro, J.F. Uthe, H.C. Freeman, and R.
Frank. 1977. Methylmercury poisoning in the harp
seal (pagO~hilUS groenlandicus). Science Total
Environ. :1-11.
109
-------
Hematological and blood chemistry values were examined
in harp seals exposed to daily oral dosages of methylmercuric
chloride (MM:). Tw:> seals, exposed to 0.25 mg MMC/kg body wt/day
for 60 and 90 days, respectively, did not show abnormal blood
values. Tw:> other seals exposed to 25.0 mg MMC/kg body wt/day
died on day 20 and 26 of exposure with 26.~ and 30.3 mg Hg/l in
blood, respectively. Blood parameters indicated toxic hepatitis,
uremia and renal failure. Total mercury and methylmercury values
in tissues of harp seals fed mercury suggested that this species
tolerates high levels of mercury in brain and that observed renal
and hepatic dysfunctions were related to high accumulations of
mercury in these tissues. Total mercury levels (mg/kg wet wt) in
tissues of seals exposed to 0.25 mg/kg/day of MMC for 90 days
were: 82.5 in liver; 50.6 in kidney; 42.7 in muscle; 21.~ in
brain; 17.1 in small intestine; 20.0 in spleen; 15.9 in heart;
1~.2 in lung; 25.0 in adrenal; 13.1 in blood; 1.6 in hair; 22.3
in claws and 0.2 in blubber. Tests of renal function were useful
in cases of severe methylmercury poisoning.
2Llb3.
Rosenberg, R. 1977. Effects of dredging operations on
estuarine benthic macrofauna. Marine Poll. Bull.
8: 102-10Ll.
Dredging operations in a Swedish estuary reduced the
number and diversity of benthic species. Larval recruitment in
the vicinity of the dredged area was strongly affected.
Concentrations of mercury and cadmium increased at one site from
March to October 197Ll in scallop Pectinaria koreni and polychaete
worm Nephtys hombergi fran 13 to 16 and 9 to ~9 mg Cd/kg wet wt,
respectively, and from 0.04 to about 0.15 mg Hg/kg wet wt in both
species. Of polychaetes and molluscs examined, concentrations
generally increased 2-3X, being higher in deposit feeders than
suspension feeders. Maximum increases of 30X were recorded in
Philine sp. and ~ hombergi. From 1971 to 1974, maximum zinc
increases were in deposit feeding molluscs Chenopus pespelicani,
2890 mg Zn/kg, and Abra alba, 1110 mg/kg. Copper increased at
one station to 150 mg/kg in N. hombergi and to 260 mg/kg in ~
alba, but no increase was found at other stations. Values of
lead were> 100 mg/kg in 3 species in 1974. Nickel concentrations
increased 70X at several stations; 9 species, particularly
carnivores and deposit feeders, contained >100 mg/kg. One and a
half years later, after dredging was stopped, concentrations of
metals in benthic fauna studied had decreased. Reductions of Hg
in filter feeders Mytilus edulis and Ostrea edulis were 16-52%,
while in ~ hombergi, a carnivore and deposit feeder, it was
no
-------
>55%.
Zn in oysters decreased 37-69% and in ~ hombergi 95-98%.
2464.
Ryndina, D.D. and L.1. Rozhanskaya. 1976. The role of
polysaccharides of the brown algae Cystoseira barbata
in the extraction of Mn from seawater. Soviet Jour.
Mar. Biology 1(3):221-224.
Accumulation of manganese from seawater by living,
dead and decomposing thallomes of C. barbata under normal
conditions and under an oxygen deficiency, as well as by
individual polysaccharides (alginic acids and algulose) isolated
from these algae, was determined. Carbohydrate composition of
dead algae had no significant influence on absorption of Mn-54.
A lcwering of oxygen tension from the control value of 6 mg/l to
2.3-3.0 mg/l lower~ absorption capacitY40f ~ barbata for Mn-54
by 7.4 fold for Mn + and 9.~ fold for Mn +. Concentration
function of alginic acids and algulose of detritus origin
increased by 3.9 and 12.7 fold, respectively. This is associated
with a change in pH of the medium. Polysaccharides from freshly
collected samples of algae absorbed substantial amounts of
Mn-54. Barium fucoidan, possibly formed in Cystoseira
intracellular fluid concentrated Mn-54, but a lowering of oxygen
tension reduced accumulation rate.
2465.
Saliba, L.J. and M.G. Vella. 1977. Effects of mercury on
the behavior and oxygen consumption of Monodonta
articulata. Marine Biology 43:277-282.
The trochid snail M. articulata was exposed to
me~curic sulphate at concentrations of 0.2, 0.5, o.~ and 1 mg/l
Hg<:-+. At 24 ws, retraction into the shell was observed in O.~
and 1 mg/l HgL+. Retracted snails died if held in the
solutions, but generally recovered within 24 to 48 hrs if
transferred to uncontaminated seawater. Irnmersion-emersion
behavior and interface activity were studied over 24 hr by means
of an aktograph. Snails in normal seawater spent more time below
than above the water surface, and exhibited frequent periods of
activity. Exposure to mercu2ic sulphate at concentrations of
0.25, 0.5, 0.8 and 1 mg/l Hg + progressively reduced both t~e
length and frequency of activity periods. From 0.5 mg/l Hg +
upwards, emersicn periods increased, and irrmersion periods
decreased. Oxygen consumption of snails was measured in seawater
and in ~ercuric sulphate at concentrations of 0.2, 0.5, 0.8 and 1
mg/l Hg +. Values in ul/g/hr were 257 (controls), 91 (0.2), 78
111
-------
(0.5), 66 (O.~) and 59 (1.0 mg Hg/l). It is postulated that
mercury affects M. articulata by interfering with respiration,
initially reducing interface activity, then forcing the snail out
of the water for longer and longer periods. Retraction occurs
when activity is no longer possible. It is concluded that
respiratory and behavioral alterations of this nature would
afford a good indicator of the presence of sublethal
concentrations of pollutants.
2466.
Sandhu, S.S. 1977. Study on the post-mortem
identification of pollutants in the fish killed by
water pollution: detection of arsenic. Bull.
Environ. Contamin. Toxicol. 17:373-378.
Herbicidal (arsenical) aerial spraying of a cotton
field in South Carolina produced contamination of an adjoining
reservoir, with resultant fish kill. Three dead catfish,
Ictalurus punctuaus, each about 400 gms, collected 30 hours after
spraying, contained 5. 1 mg arsenic/kg in muscle. Water
concentration in the pond was 2.5 mg As/I. Collections 7 weeks
later showed 12.4 mg As/kg in catfish and 1.9 mg As/l in water,
suggesting that As bioaccumulation 00ntinued in surviving fish
though water levels decreased. The fall in As water content may
have been due to flushing by heavy rains between sampling times,
as well as by absorption by bottom sediments.
2467.
Sarsfield, L.J. and K.H. Mancy. 1977. The properties
of cadmium complexes and their effect on toxicity to a
biological system. In: Drucker, H. and R.E. Wildung
(eds.). Biological~plications of metals in the
environment. ERDA Syrnp. Ser. 42:335-345. Avail. as
CONF-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Corrm., Springfield, VA 221b1.
Relative toxic strength of cadmium ions is a function
of their complex forms within cells. Intracellular Cd
concentrations which inhibited photosynthetic oxygen production
50%, (ID50)i' in algal cells of Chlorella pyrenoides, exposed
to cadmium-ligand s~~utions not exceeding 0.112 mg Cd/I, f~r 8
days, were 146 x 10 mg/cell f9s uncomplexed Cd, 220 x 10 5
mg/~~l for phthalate, 253 x 10 mg/cell for citrate, and 373
x 10 mg/cell for ethylenediamine diacetic acid in one
str~in. A second algal strain had (ID50)t values of 124 x
101 mg/cell for uncomplexed Cd, 217 x 10 5 ~g/cell for
ethylenediamine diacetic acid, and 270 x 101 mg/cell for
112
-------
quinolate. Stability constants (Ks) of complexes were directly
correlated to these toxicity results.
2468.
Sartory, D.P. and B.J. Lloyd. 1976. The toxic effects of
selected heavy metals on unadapted populations of
Vorticella convallaria var similis. Water Research
10: 1123-1127 .
The presence of large amounts of heavy metals in
sewages may cause severe disruption of the biological processes
involved in sewage treatment, and thus a decline in quality of
the effluent produced. Unadapted populations of a sessile
peritrich protozoan abundant in healthy rivers, activated sludge,
percolating filters and slow sand filters were subjected to a
range of 0.0001-100.0 mg/l of Pb, Hg or Zn. Vorticella were
killed by concentrations of 0.0005 mg/l and higher of lead or
mercury. Colonies were also killed by concentrations~0.075 mg/l
of Zn. LC-50 (12 hr) values were 0.0036 mg Pb/l, 0.005 mg Hg/l,
and 0.29 mg Zn/l.
2469 .
Say, P.J., B.M. Diaz, and B.A. Whitton. 1977. Influence
of zinc on lotic plants. 1. Tolerance of Hormidium
species to zinc. Freshwater Biology 7:357-376.
Field studies from sites in Europe polluted by past or
present mining activities, supplemented by laboratory studies,
were conducted on zinc tolerance of the algae H. rivulare, H.
flaccidum, and H. flui tans. Maximum mean metal levels in mg/l
from these sites were 22.8 for Zn, 0.37 for Cu, 0.97 for Pb, 0.88
for Cd, 585.2 for Mg, and 211.5 for Ca. H. rivulare and H.
flaccidum were found at the site with the-highest zinc level.
Tolerance index concentrations of Zn for H. rivulare ranged from
1.2 to 17.0 mg/l, for H. flaccidum 1.0 to-13.5 and for H.
fluitans 1.6 to 2.7; populations from sites with higher-Zn levels
showed increased resistance to zinc. Cadmium and lead appear to
increase the toxicity of zinc to these filamentous green algae;
magnesium, calcium, and various hardness factors decrease zinc
toxicity. An increase in P04-P and decrease in pH may also
reduce Zn toxicity, at least in g. rivulare.
2470.
Say, P.J. and B.A. Whitton. 1977. Influence of zinc on
lotic plants. II. Environmental effects on toxicity
of zinc to Hormidium rivulare. Freshwater Biology
7: 377 -3tS4.
113
-------
Tolerance index concentrations (T.I.C.) for a
zinc-sensitive algal population of H. rivulare ranged from 0.54
to 1.65 mg/l for Zn, and 0.04 for Cd; T.I.C. for a zinc-tolerant
population were 5.2 to 16.tS for Zn and 0.3~ for Cd. Cadmium
alone was 34X more toxic than zinc to a Zn + Cd sensitive
population, and 15.5X more toxic to a Zn + Cd tolerant one.
Toxic effects of zinc and cadmium were synergistic at levels
: 0.01 mg Cd/i. Toxicity of zinc was decreased by rises in
magnesium, calcium, and phosphate levels, and increased by rises
in pH. Sodium, chloride, and sulphate had no detectable
influence on zinc toxicity. When applied at 50 mg/l or higher,
Ca was always more effective than Mg at reducing Zn toxicity,
raising the T.I.C. to about ~O mg Zn/l. The reverse was
sometimes true at lower concentrations. Calcium had a
proportionately greater effect in decreasing Cd toxicity, which
was highly toxic, than Zn toxicity. Both Mg and PO~-P were
more effective with Zn-tolerant than Zn-sensitive populations.
2471.
Schmidt-Nielsen, B., J. Sheline, D.S. Miller, and M.
Deldonno. 1977. Effect of methyJrnercury upon
osmoregulation, cellular volume, and ion regulation in
winter flounder, Pseudopleuronectes americanus. In:
Vernberg, F.J., A. Calabrese, F.P. Thurberg, and W.B.
Vemberg (eds.). Physiological responses of marine
biota to pollutants. Academic Press, N.Y.:105-117.
Winter flounder in seawater were given methyJrnercury
injections daily or every other day corresponding to 1 mg Hg/kg
wet wt for each fish. Accumulation of Hg, in mg/kg wet wt per
dosage, were 0.11 for muscle, 0.92 for intestine, and 2.0 for
liver. With a total dose of 13 mg Hg/kg, Hg levels rose steadily
to 2.0 in muscle, 10.0 in intestine, and 22.0 in liver. Only one
fish survived the 13 mg Hg/kg total dosage. Between 2 and 13 mg
Hg/kg total dose, Hg ranged from 3 to 9 mg/kg wet wt in red
cells, 7 to 1~ in kidney, and 13 to 25 in gill. Control had< 1
mg Hg/kg in muscle, intestine, liver, and kidney, and < 3 in red
cells and gill. As Hg concentration increased to 24 mg/kg wet
wt, no significant change in intracellular concentrations of K,
Cl, Ca, or Mg occurred in all tissues tested; water content of
cells was not affected; and plasma osmolarity decreased
slightly. Na+, K+-ATPase activity was higher in bladder and
kidney of Hg-treated fish than controls, but no differences were
evident in gill or intestine.
2472.
Scott, J. S.
1977.
Back-calculated fish lengths and Hg
114
-------
and Zn levels from recent and 100-yr-old cleithrum
bones from Atlantic cod (Gadus morhua). Jour. Fish.
Res. Ed. Canada 34:141-150.
Dimensions of cleithrum bones from fresh Atlantic cod
were measured and plotted against observed fish lengths to
back-calculate cod lengths from cleithra collected in 1864. Mean
mercury concentration in 100 year old bones was 55.6 ug/kg dry wt
and 69.0 ug/kg in recent cod. Neither showed an increase in Hg
with fish length as well. Overall zinc levels appear to have
increased since 1865, with Zn showing increases with fish length
as well. Average concentration of Zn in recent cod was 53.5
ug/kg and 45.1 ug/kg in 100-yr-old cod.
2413.
Seeliger, U. and P. Edwards. 1911. Correlation
coefficients and concentration factors of copper and
lead in seawater and benthic algae. Marine Poll.
Bull. 8: 16-19.
As total copper in seawater from Raritan Bay, near
metropo li tan New Y or k , rose from O. 002 to O. 022 mg/l, Cu in
seaweeds increased linearly from approximately 2 to 160 mg/kg dry
wt in Blidingia minima, from 11 to 11 mg/kg in Entermorpha linza,
14 to 38 mg/kg in Ulva sp., and 8 to 48 in Fucus vesiculosus.
Most of the copper was in suspended rather than dissolved form.
As total lead in the same water rose from 0.002 to 0.010 mg/l, Pb
in seaweeds also increased linearly, from about 12 to 172 mg/kg
dry wt in Blidingia, from 18 to 68 mg/kg in Enteromorpha, 20 to
16 mg/kg in Ulva, and 8 to 38 mg/kg in Fucus. &1spended lead
made up almoStSO% of total Pb found in algae and water. Metal
levels generally decreased as distance from the inlets of Raritan
Bay increased. Concentration factors of Cu in algae (mg/kg dry
wt) over seawater (mg/l) were 1100-18,300 for Blidingia,
5600-1100 for Enteromorpha, 4100-8600 for Ulva, and 3600-1400 for
Fucus. CF's of lead were 27, 000-~2, 000, -
20,000-45,000,11,000-49,000, and 13,000-24,000 for the respective
algal species. CF's of Cu and Pb for Blidingia are among the
highest reported to date.
2414.
Sheline, J. and B. Schmidt-Nielsen. 1911. Methyl-
mercury-selenium: interaction in the killifish,
Fundulus heteroclitus. In: Vernberg, F.J., A.
Calabrese, F.P. Thurberg~and W.B. Vemberg (eds.).
Physiological responses of marine biota to
pollutants. Academic Press, N.Y.:119-130.
115
-------
Interaction of selenium and mercury in killifish was
studied in groups injected with the following: 1.0 mg Hg/kg body
wt Hg-203 methylmercury, with or without previous injection of
0.4 mg Se/kg body wt 30 mins. before Hg addition; 1.0 Hg/kg of
C-14 methylmercury, with or without 0.4 mg Se/kg pretreatment.
Se pretreatment had no effect on Hg retention from Hg-203 or C-14
labelled doses in whole body of fish. After 5 hrs, Hg levels in
all groups were 0.99 to 1.09 mg/kg; after 25 hrs, levels were
0.(\6 to 1.03. Hg distribution 3 hrs after methylmercury
injection showed lower kidney/gill ratios with Se pretreatment,
significantly lower red cell/gill ratios, higher liver/gill
ratios, and significantly higher muscle/gill ratios. At 5, 25,
and 73 hrs after injections, kidney/gill Hg-203 ratios of Se
pretreated fish were half that for fish with no See Kidney
concentrations were 1.3 and 1.6 mg Hg/kg with only Hg, and 0.7
with Hg and Se after 73 hrs. Liver/gill Hg-203 ratios were
slightly lower with Se pretreatment, but not significantly. Hg
in liver at 73 hrs was 1.6 to 2.0 mg/kg with only Hg, and 1.1
with Hg and See Distribution of C-14 and Hg-203 in various
tissues was identical under all conditions; indicating that Se
caused little or no increased breakage of C-Hg bonds in
methylmercury. Authors concluded that all findings in Fundulus
were similar to those reported for ri1aIm1alian tissues, viz,
pretreatment with selenite causes no changes in overall body
retention of Hg, a marked redistribution of Hg among organs, and
no measureable increase in C-Hg bond cleavage in methylmercury.
2475.
Sheppard, C.R.C. 1977. Relationships between heavy
metals and major cations along pollution gradients.
Marine Poll. Bull. 8:163-164.
Along some pollution gradients in the Mediterranean,
animal tissue concentrations of several physiologically important
cations vary greatly, up to 4X, corresponding to levels of toxic
metals, which may be the underlying cause of stress. In the
presence of Pb, Cu, Ni, or Zn, calcium levels increased
significantly in urchins Paracentrotus and Arbacia and in the
limpet Patella. Magnesium levels also increased slightly, while
potassium decreased in these invertebrates; sodium decreased in
urchins but increased in Patella. Mean values of Ca ranged from
3900-6200 mg/kg wet wt in animals from least polluted waters and
9400-22,300 from the most polluted waters; Mg was 620-2100 and
2600-4900 mg/kg wet wt, respectively; K range was 4300-10,100 and
1200-1700, respectively. Na was 9200-12,100 in least polluted
gradients and 4300-4700 in most polluted in urchins, while 2(\00
in least polluted and 15,100 in most polluted in Patella.
116
-------
Seawater values from central Mediterranean were 480 mg Cd/l, 1490
Mg, 410 K, and 12, 100 Na.
2476.
Sheppard, J.C., and W.H. Funk. 1975. Trees as
environmental sensors monitoring long-term heavy metal
contamination of Spokane River, Idaho. Environmental
Sci. Tech. 9:b3B-643.
Ponderosa pine trees growing on the bank of the
Spokane River, Idaho, were used to monitor the River's past
concentrations of Hg, Cr, Ag, Rb, Zn, Co, and Fe. Sections of
cores and tree rings were analyzed by neutron activation to
determine the trees' metal content as a function of tree ring
age. Results indicate that these are in rough agreement with
sediment core data for Coeur d'Alene Lake and the volume of ore
mined in the Coeur d 'Alene mining district provided that
allcwances are made for metal holdup in Coeur d' Alene Lake. Mean
concentration ranges of various elements in mg/kg dry wood were
0.005-0.022 Hg, 0.09-0.90 for Cr, < 0.02-0.18 for Ag, 0.06-0.92
for Rb, 37.7 to 109.3 for Zn, 0.019 to 0.Ob5 for Co, 7.0 to 52.2
for Fe, 31.3 to 143.0 for Na, 631.0 to 3034.0 for K, 0.97 to 1.63
for Mn, 0.0015 to 0.00B2 for La, 0.0024 to 0.0110 for Sb, and
0.0010 to 0.0035 for Au.
2477.
Sherwood, M.J. and A.J. Mearns. 1977. Enviromental
significance of fin erosion in southern California
demersal fishes. In: Kraybill, H.F., C.J. Dawe, J.C.
Harshbarber, and R-:G. Tardiff (eds.). Aquatic
pollutants and biologic effects with emphasis on
neoplasia. Annals N.Y. Acad. Sciences 298:177-189.
Dover sole, Microstomus pacificus, was the most
heavily affected teleost with eroded fins along the southern
California coast. Incidence of fin erosion was highest on Palos
Verdes shelf, site of a major municipal waste water discharge.
Levels of trace metals, in mg/kg dry wt, in muscle of M.
pacificus fran this area were 0.5-3.2 for copper, 15-2ofor
zinc, < 3.0 for cadmium, < 0.2 for chromium, and < 1.0 for lead.
There were no significant differences in elemental composition
between apparently healthy fish and those with moderate to severe
fin erosion. Sole exposed to shelf sediments in the laboratory
had higher concentrations of Cd in muscle and liver, Cu in liver,
Pb in muscle and liver, and Zn in muscle than fish kept with
silica sand. Specimens in silica sand were higher in Cr in
muscle and liver, and Zn in muscle. Both groups had equal levels
117
-------
of Cu in muscle. Authors state that these levels were probably
not associated with fin erosion. Diseased sole when compared to
unaffected specimens had higher concentrations of total DDT, a
tendency towards higher levels of total polychlorinated biphenyls
in muscle, and a greater liver to body weight ratio. Laboratory
exposure to chlorinated hydrocarbons resulted in development of
fin erosi on.
2478.
Shore, R., G. Carney, and T. Stygall. 1975. Cadmium
levels and carbohydrate metabolism in limpets. Marine
Poll. Bull. 6:187-189.
Glucose levels and carbohydrate metabolism were
investigated in Patella vulgata from several sites with varying
degrees of cadmium contamination in the Bristol Channel, England,
from September 1974 to May 1975. Generally, as Cd levels in
digestive glands increased fram 27 to 537 mg/kg dry wt,
glycolytic rate decreased from 0.45 to 0.25 umol lactate/mg
protein/hr, and amount of haemolymph glucose increased fram 5. 1
to 8.6 mg%. Maximum glycolytic rate of 0.48 umole lactate/mg
protein/hr and minimum haemolymph glucose levels of Ll.3 mg% were
found in limpets containing 116 mg Cd/kg dry wt. Results
tentatively suggest a correlation between cadmium concentrations
and reduced ability to utilize glucose.
2479.
Shumway, S. E. 1977. Effect of salinity fluc~uation on
the osmotic pressure and Na+, Ca2+ and Mg + ion
concentrations in the hemolymph of bivalve molluscs.
Marine Biology 41:153-177.
Chlamys opercularis, Modiolus modiolus, Mytilus
edulis, Crassostrea gigas, Scrobicularia plana, and Mya arenaria,
all osmoconformers, were exposed to gradual and abrupt salinity
fluctuations. In both regimes fluctuating between ~OO% (32 0/00
S) and 50% seawater, hemolymph concentrations of Mg +
fluctuated between 55 roM and 35 to 25 roM, respectively, in C.
opercularis. Hanolymph Na+, Ca2+, and osmotic concentrations
also followed external ion concentrations. Ionic and osmotic
concentrations of hemolymph and mantle fluid followed the
external concentrations in M. modiolus, M. edulis, C. gigas, and
~. plana only while shell valves remained open. w~ged-open M.
edulis, supplied with a constant supply of 10 roM Ca +, showed-
greater changes in hemolymph concentrations due to fluctuating
salinity than specimens without Ca+ supply. C. opercularis and
M. modiolus survived in 50% seawater minimum gradual fluctuations
118
-------
for 10 days; wedged-open M. modiolus survived only 3 days.
Burrowing had no effect on hemolymph concentrations in M.
arenaria or ~. plana in fluctuating salinity.
2480.
Shumway, S.E. and J. Davenport. 1977.
the physiology of Arenicola marina
exposed to fluctuating salinities.
Assn. U.K. 57:907-924.
Some aspects of
(Polychaeta)
Jour. Mar ine BioI.
When confronted with abrupt dilution to 30% SW of the
water above their burrows, Arenicola became inactive and
compressed themselves at the bottom of the burrow; they "sampled"
overlying water about once every hour. Normal activity was
resumed when salinity returned to the initial value of 32 0/00.
In sinusoidal salinity regimes fluctuating between 100% and 30%
SW, activity stopped at 55% SW external concentration. Animals
held in glass tubes rather than sand burrows ceased activity at
about 70% SW, suggesting that Arenicola derives a proportion of
its water for irrigation from interstitial rather than surface
water. The combina.tion of behavioral response and exploitation
of interstitial water was extremely effective in maintaining
coelomic fluid and tissue osmotic and ionic concentrations at a
constant level. In contrast, non-burrowed worms exhibited
fluctuating levels of Na, K, Ca, Mg, 304' and ninhydrin-
positive substances with salinity changes, as expected from a
highly permeable osmoconformer.
2481.
Sidwell, V.D., D.H. Buzzell, P.R. Foncannon, and A.L.
Smith. 1977. Composition of the edible portion of
raw (fresh or frozen) crustaceans, finfish, and
mollusks. II. macroelements: sodium, potassium,
chI or ine, calcium, phosphorus, and rnagnesi um. U. S.
Dept. Commerce, Marine Fisheries Review 39:1-11.
Na, K, Ca, P, Cl, and Mg body levels reported in the
li terature for about 160 species of fresh or frozen marine and
freshwater crustaceans, echinoderms, elasmobranchs, fish,
molluscs, and rnanmals are summarized. Sodium concentration
ranges were 450-2760 mg/kg in crustaceans, 700-1790 in
elasmobranchs, 240-3970 in fishes, 110-6180 in molluscs, and
98-242 in mammals. Potassium levels were 550-5000 mg/kg in
crustaceans, 1140-5490 in elasmobranchs, 250-7120 in fishes,
35-570 in molluscs, and 3600-3700 in mammals. The range of
calcium was 160-5500 mg/kg in crustaceans, 40-1640 in
elasmobranchs, 50-7500 in fishes, 100-2170 in molluscs, and 15 in
119
-------
mammals. Magnesium concentrations ranged 120-1300 mg/kg in
crustaceans, 100-440 in elasmobranchs, 100-2020 in fishes, and
120-2300 in molluscs.
2482.
Sigmon, C.F., H.J. Kania, and R.J. Beyers. 1977.
Reductions in biomass and diversity resulting from,
exposure to mercury in artificial streams. Jour.
Fish. Res. Ed. Canada 34:493-500.
Mercury levels of 0.0001 and 0.0010 mg Hg/l, as
HgC12' caused significant reductions in freshwater algal
numbers, standing stock, and diversity over 12 months in
artificial streams in South Carolina. Periphyton Hg
concentrations ranged from 10 to 50 mg/kg dry wt in 0.0001 mg
Hg/l and from 150 to >3000 mg/kg dry wt in 0.001 mg Hg/l;
controls contained < 20 mg/kg dry wt over this period.
Concentration factor from water to periphyton was about 106 for
both treatments. Reductions in diversity resulted from a
decrease in evenness of distribution of numbers among species
and a slight decline in number of species. Decline in algal
standing crop could indirectly affect other food chain members
that are Hg resistant. No direct or indirect impact on
her bi vorous or carnivorous mi dges was seen, however, si nce the
impact on primary producers was not sufficient to be transferred
to consumer trophic levels.
2483.
Singleton, F.L. and R.K. Guthrie. 1977. Aquatic
bacterial populations and heavy metals--I. composition
of aquatic bacteria in the presence of copper and
mercury salts. Water Research 11 :b39-642.
Effects of addition of copper as CuS04 and mercury
as HgC12 was studied in bacteria pOpllations including
Pseudomonas sp., Flavobacterium sp., Brevibacterium sp.,
Enterobacter sp., Achromobacter sp., Escherichia sp., Sarcina
sp ., Caulobacter sp., Proteus sp., Micrococcus sp., Streptomyces
sp., and Bacillus sp. from fresh and brackish waters. Treatment
of bacterial populations with 2.0 mg/l copper or 0.04 mg/l
mercury for 14 days caused an increase in total colony forming
units (TCFU), a reduction in diversity, and a varied percentage
of chromagens in the pOpllation. Similar results were observed
when Cu and Hg were added simultaneously to a single system. The
largest reduction in chromagenic percentage in Hg treated
brackish water colonies occurred at days 9-10, coinciding with
greatest increase in TCFU. Examination of the present genera
120
-------
confirmed that Flavobacterium sp. and Brevibacterium sp. were
absent at the end of the 14 day test. Other organisms lost or
reduced in metal treated systems included Sarcina sp.,
Enterobacter sp., Achromobacter sp., and Escherichia sp. Results
indicate that heavy metal addition reduced bacterial community
stability by reduction in diversity coincident with increased
TCFU of surviving organisms.
2484.
Skipnes, 0., T. Roald, and A. Haug. 1975. Uptake of zinc
and strontium by brown algae. Physiol. Plant
34:314-320.
Accumulation of Sr-85 by tips of Ascophyllum nodosum
was reversible, and similar in living and killed plants. In 12
mg Sr/l seawater (32.7 0/00), equilibrium of Sr exchange was
reache::i in 1 day, at 200 mg/kg wet wt algae. Accumulation seemed
to be an ion-exchange process involving negatively charged
intracellular polysaccharides, mainly arginate. Only a small
fraction of Zn uptake in living algae seemed to be due to a
similar ion exchange with intracellular polysaccharides. Zinc
uptake was a slrn, irreversible accumulation of 5.5 mg/kg wet wt
algae in 4 days in 0.1 mg Zn/l as ZnC12' and of 27.0 mg/kg wet
wt algae by 7 days in 0.3 mg/l. Rate of Zn uptake was 0.8 mg/kg
wet wt algae/day in 0.1 mg Zn/l and rose to 1.3 and 1.4 in 0.3
and 1.0 mg/l. In dead algae, uptake was reversible and rapid, 95
mg/kg wet wt algae by 7.5 days in 0.1 mg Zn/l seawater. Authors
suggest that algae contain Zn-binding substances, but these were
not directly accessible to Zn ions in seawater prior to death.
Transfer of Zn from reversible intercellular sites to
irreversible cellular sites continued undisturbed during low tide
periods. Intercellular charged polysaccharides thus function as
ion ooffers, allrning ion uptake into the cell at a constant
rate, independent of tidal movements.
2485.
&nith, R.I. 1976. Exchanges of sodium and chloride at
lrn salinities by Nereis diversicolor (Annelida,
Polychaeta). Bioi. Bull. 151:587-600.
The Na-uptake mechanisms in this marine polychaete
reach half the maximal uptake rate at an external Na
concentration of 1tS4-230 mg/l (2% SW) and becomes "saturated" or
reaches a plateau of uptake at 920-1380 mg Na/l (10% SW) up to
8050 mg/l (75% SW); above this, Na-exchange is proportional to
external concentration. The Cl-uptake curve shows a relative
depressioo at very low salinities before reaching "saturation" at
121
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Cl concentrations of 1770-2124 (10% SW). Cl-uptake becomes
proportional to external concentrations of 50% SW or greater,
suggesting passive diffusion in the ionic and osmotic conforming
range. Body wall permeability to both Na and Cl is reduced at
very 100 salinities. Author suggests that the inside negative
body wall potential is related to the depression of the Cl-uptake
curve in salinities below 10% SW. Activation of Na-uptake at low
salinities was not conclusively demonstrated because of the body
wall permeability reduction.
2486.
Saner, E. 1977. Heavy metals in the Baltic.
International Council for the Exploration of the Sea.
Fisheries Improvement Committee. C.M. 1977/E:9. 37
pp.
Baltic Sea sources, transport processes, uptake in
organisms, and recommended monitoring procedures of As, Cd, Cr,
Cu, Hg, Mo, Ni, Pb, and Zn are presented. Mercury concentrations
in biota near discharge areas exceeded administrative limits and
accumulated up the food chain to sea birds and sea mammals.
Copper concentrations were generally higher in the open sea and
are detected only near discharge areas along the coast. Elevated
zinc levels were found only close to discharges, with moderately
toxic effects. Lead, in spite of high input, and cadmium, in the
Bal tic have li ttle effect on biota or man. The role of
molybdenum should be investigated as a limiting factor for
primary production and nitrogen fixation in blue-green algae.
Recommended monitoring organisms and tissues for Hg is flmmder
muscle; for Cd and As it is flounder liver; for Pb, Zn, and Ni it
is whole mussel; for Cu whole mussel and flounder liver; and for
Cr sed iment and polychaetes.
2487.
Sonntag, N.C. and W. Greve. 1977. Investigation of the
impact of mercury on enclosed water columns using a
zooplankton simulation model. Jour. Fish. Res. Bd.
Canada 34:2295-2307.
A computer simulation model of a phytoplankton-
zooplankton-salman system was used to investigate possible causes
of different population dynamics of the copepod, Pseudocalanus
minutus, in 0.001 and 0.005 mg/l mercury over 70 days. Diatoms
and flagellates, copepods, and fingerling chum salmon,
Oncorhynchus keta, were represented in the model. In general,
simulated and observed growth of all organisms in 0.001 mg Hg/l
was equal to or better than controls; in 0.005 mg Hg/l little
122
-------
growth was seen. The model supported the hypothesis that
observed reductions in Pseudocalanus populations after day 25
could have been a direct consequence of different flagellate
populations in the system rather than lethal effects of Hg on
molting and reproduction success of copepods.
2488.
Stevens, D. G. 1977. Survi val and immune response of coho
salmon exposed to copper. U.S. Environ. Protect.
Agen. Rept. EPA-600/3-77-031: 36 pp.
Juvenile coho salmon, Oncorhynchus kisutch, were
vaccinated with bacteria Vibrio anguillarum, by oral
administration during copper exposure and intraperitoneal
injection prior to exposure in order to investigate effects of Cu
upon survival and inmune response to vibriosis. Measured Cu
concentrations of 0.018 to 0.034 mg/l caused 35 to 100% mortality
among coho fry over 30 days. Survivors from 20.014 mg Cull
exposed to V. anguillarum in seawater had at least 60% mortality
after 24 days. The reduced number of dead fish positive for V.
anguillarum suggests that sublethal Cu stress and difficulty with
seawater adaptation caused several deaths. Mortality of 17 to
69% among coho fingerlings exposed to at least 0.025 mg Cull
occurred over 31 days. Most survivors were unable to adapt to
seawater and died wi thin 3 days of V. anguillarum challenge.
Eighteen percent mortality occurred-auring seawater adaption in
survivors from 0.018 mgll, whereas only 2% died during 31 days of
Cu exposure. Antibody level against ~ anguillarum, measured by
agglutinin titer, was significantly reduced in fish exposed to
0.018 mg Cull compared to controls.
2489.
Stewart, J.G. 1977. Effects of lead on the growth of four
species of red algae. Phycologica 16:31-36.
Three species of marine red algae, Platythamnion
pectinatum, P. decumbens, and Pleonosporium squarrulosum were
grown in medIa containing up to 10 mg Pb/l. No effects of added
lead on morphology or development of reproductive structures were
observed, although algae grew more slowly in media containing
lead. Growth of cells of Tiffaniella snyderae over 15 days was
reduced in 0.5-10.0 mg Pb/l during days 4-8; divison rate of
apical cell was not different than controls. Growth of filaments
and cell division rate of this species over 28 days were both
reduced in 0.5-10.0 mg Pb/l, but not 0.1 mg/l.
123
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2490.
Stickel, L.F., W.H. Stickel, M.A.R. McLane, and M. Bruns.
1977. Prolonged retention of methyl mercury by
mallard drakes. Bull. Environ. Contamin. Toxicol.
18:393-400.
Retention of mercury residues by mallard ducks, Anas
platyrhynchos, during 16 wks was reported following dietary----
expasure to 8 mg Hg/kg as methylmercury dicyandiamide for 2 wks.
WhJle body concentratirn rose to 9.1 mg Hg/kg wet wt from < 0.5,
after dietary dosages, then dropped to 6.~ at 1 wk, 4.4 at 12
wks, and 2.2 at 16 wks. In carcass, Hg increased to li.5 mg/kg
wet wt, from < 0.05, during feeding, then decreased to 2.6 at 4
wks, rose again to 3.4 at 8 wks, and decreased to 0.9 at 16 wks.
Concentrations in liver rose to 16.5 mg Hg/kg wet wt, from 0.06
before expasure, then declined to 11.4 at 1 week, 7.0 at 12
weeks, and 4.2 at 16 weeks. Kidney Hg increased to 17.6 mg/kg
wet wt from 0.CJ7, upon dietary dosages, then decreased to 13.8 at
1 week, 9.5 at 12 wks, and 4.6 at 16 wks. Although Hg loss was
slOd between 1 and 8 wks, with one half of initial concentrations
still retained by 12 weeks, lass resumed concurrently with new
feather growth and continued through the close of the 16 week
study.
2491 .
Stokes, P. and T.C. Hutchinson. 1976. Copper toxicity to
phytoplankton, as affected by organic ligands, other
cations and inherent tolerance of algae to copper.
In: Andrew, R.W., P.V. Hodson, and D.E. Konasewich
rects.). Toxicity to biota of metal forms in natural
water. Great Lakes Res. Advis. Ed., Standing Conm.
Sci. Basis Water Quality Criteria Inter. Jt. Comm.
Res. Advis. Bd.: 159-155.
Maximum metal concentrations in selected Ontario lakes
near mining and smelting activities were 0.07 mg/l for Cu, 2.00
for Ni, 0.12 for Zn, 0.16 for Co, 0.33 for Mn, 0.28 for Fe, and
60.50 for Ca. High algal growth of Chlorella vulgaris correlated
with law Cu and Ni levels and high Cu-complexing capacity of lake
waters. Scenedesmus acuminatus was more sensitive than Chlorella
which is a facultative heterotroph; its ability to use organic
carbrn from organic matter may have caused amelioration of metal
toxicity. Growth of Scenedesmus in waters spiked with 0.2 mg
Cull showed that tolerance of Cu was related to the waters'
complexing capacity. Complexing capacity of lakes was a function
of season, and amounts of organic carbon and ligands including
EDTA and acetate. Copper at 0.3 and 1.0 mg/l ac ted
synergistically with 0.0, 1.0 and 3.0 mg Ni/l on growth
124
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inhibition of Scenedesmus.
2492.
Sturesson, U. 1976. Lead enrichment in shells of Mytilus
edulis. Ambio 5:253-256.
Enrichment of lead in various fractions of mussel
shells was studied during imnersion for 35 to 150 days in
seawater concentrations of 0.00, 0.02, 0.10, and 0.50 mg Pb/l.
Maximum enrichment at 0.02 mg/l was 180 mg/kg in newly formed
calcium carbonate. At O. 1 mg/l this was 550 in periostracum from
older shell, and at 0.5 mg/l it was 4200 in older periostracum.
Intermediate levels were found in new periostracum and the
organic conchiolin matrix. Minimum Pb values were from older
calcium carbonate, and pure carbonate from calcitic and
calcitic/aragonitic regions. Lead accumulation in older
periostracum increased from 550 mg/kg in O. 1 mg/l to 4200 mg/kg
in 0.5 mg/l, while newly formed periostracum increased from 300
to 1500 mg/kg. Levels in newly formed carbonate fractions
increased from 300 to 1100 mg Pb/kg at the same seawater
concentration intervals, while older carbonate increased from 50
to 100 mg/kg. Two suggested paths for lead enrichment are
passive accumulation by adsorption on surfaces in direct contact
with the seawater, and active accumulation through the mantle
governed by metabolic processes.
2493.
Sullivan, C.W. 1976. Diatom mineralization of silicic
acid. I. Si(OH)4 transport characteristics in
Navicula pelliculosa. Jour. Phycology 12:390-396.
Uptake of silicic acid by the freshwater diatom, N.
pelliculosa, using Ge-68(OH)4 as a tracer, was initially --
dependent en cell number, pH, temperature, and light, and was
promoted by certain cations in the medium. Compared with
controls, initial uptake rate was 68-97% in 32.2 mg Na/l, 49-73%
in 54.7 mg K/l, and < 20% in 9.7 mg Li/l or 25.2 mg NH4/1.
Uncouplers and inhibitors of oxidative phosphorylation and of
photophosphorylation reduced uptake by 40-95% of controls.
Uptake was also especially sensitiv9 to 10- M sulfhydryl
blocking agents; valinomycin at 10- M inhibited uptake by 82%.
The Si(HD)4 transport system displayed Michaelis-Menten-type
saturation kinetics. Acid-soluble silicic acid pool size
suggested that intracellular levels of Si could reach 562 mg/l
and as much as 480.5 mg/l free silicic acid, maintaining a
250-fold concentration gradient over the medium. Initial uptake
rate of SiCOH)4 in logarithmic phase cells was constant, but
125
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uptake rates increased linearly for 6 hrs in stationary phase
cells. Efflux from preloaded cells was dependent on temperature
and external SiCOH)4 concentration. In 96,000 mg/l "cold"
Si(OH)4, about 30% of silicic acid in pre loaded cells was
exchanged in 20 min. Results suggest that the first step in
silica mineralization by diatoms is active transmembrane
transport of Si(OH)4 by an energy dependent, saturable,
membrane-carrier mechanism which requires Na+ and r<+ and is
sensitive to sulfhydryl blocking agents. Silicic acid transport
activity also appears to be regulated during different growth
stages of the diatom.
2494.
Sullivan, J.T. and T.C. Cheng. 1976. Comparative
mortality studies on Biomphalaria glabrata (Mollusca:
Pulmonata) exposed to copper internally and
externally. Jour. Invert. Pathology 28:255-257.
Higher mortality resulted in freshwater snails, ~
glabrata, when incubated in copper concentrations than injection
with Cu to attain the same concentrations in hemolymph. All
snails died within 24 hrs when incubated in 500 mg Cull, while
only 20% died when injected with this concentration. After
injection of 1,000 mg Cull, ~O% of the snails died over 24 hrs;
all died with an injection of 2500 mg/l. Injection of Cu into
the hemocoel of ~ glabrata resulted in formation of a
non-cellular hemolymph precipitate, most likely denatured
protein, at the injection site, which was most noticeable with
higher concentrations. It was concluded that external levels of
Cu are more toxic to snails than internally injected
concentrations, supporting the hypothesis that biocidal action of
Cu is due to an attack on the snail's surface epithelia.
2495.
Sutterlin, A.M., L. R. MacFarlane, and P. Harmon. 1977.
Growth and salinity tolerance in hybrids within Salmo
Spa and Salvelinus Spa Aquaculture 12:41-52.
Attempts were made to complete all possible
interspecific hybrid crosses between Atlantic salmon Salmo salar,
rainbow trout ~ gairdneri, brook trout Salvelinus fontinalis,
lake trout ~ namaycush, and Arctic char ~ alpinus. Survival
was appreciable only in the matings (female listed first) of lake
x brook, salmon x char, brook x char, and char x brook.
Different species and hybrids may be divided into four groups
exhibiting increasing tolerance to 39.4 0/00 sainity, at 12 C: C
xC=LxL=BxB=BxC< SxB=SxS
-------
Salvelinus spp. and their intrageneric hybrids have less
tolerance to increasing salinity than SalIno spp. The least
tolerant group had 98% mortality in just over 10 hours, while the
mes t tolerant (S xC) had 80% mortali t y by 100 hours.
2496.
Suzuki, T., T. Miyama and C. Toyama. 1973. The chemical
form and bodily distribution of mercury in marine
fish. Bull. Environ. Contamin. Toxicol. 10:347-355.
Many types of fish, including mackerels Auxis
tapeinosoma, Trachurus japonicus, and Caranx sexfasciatus,
grouper Epinephelus septemfasciatus, rockfish Sebastes inermis,
greenling Hexagrammos otakii, hairtail Trichiurus lepturus, blue
runner Caranx equula, yellowtail Seriola quinqueradiata,
nemipterid Nemipterus virgatus, catalufa Priacanthus
macrocanthus, crimson sea bream Evyunis japonica, and lethrinid
Lethrinus choerorhyncus, were collected from the South China Sea,
off northwestern Australia and in the Japan Sea. All were
analysed for mercury content. Mean values of total mercury in
orgpn and gpstric content of all fish in mg/kg wet wt was: 0.20
in muscle; 0.~6 in liver; 0.66 in brain; 0.72 in kidney; and
0.072 in gpstric content. Mean inorganic mercury levels were
0.006 muscle, 0.27 liver, 0.015 brain, 0.25 kidney, and 0.030 in
gastric content. In muscle, the highest percent of inorganic
mercury of the total Hg content was 17.6 in catalufa. In the
brain of one hairtail, the level of total Hg was 7.36 mg/kg, all
organic. In the case of inorganic mercury, 3 significant
correlations were found: kidney to muscle; kidney to liver; and
liver to brain. For organic mercury the significant correlations
were: muscle to brain; liver to kidney; and brain to kidney.
Total mercury in the gastric content correlated significantly
with total Hg in liver or muscle. For inorganic Hg, gastric
content correlated significantly with liver, kidney and muscle.
2497.
Sylvester, A.J. and G.C. Ware. 1977. Laboratory studies
on the effect of metals on oxygen uptake by sewage
sludge in brackish water. Marine Poll. Bull. ~:45-48.
Cadmium, lead, and zinc industrial wastes dumped into
the Bristol Channel apparently stimulates the growth of certain
bacteria in water and may hasten the self-purification process.
In the laboratory 100 ml of artificial seawater and a known
concentration of a heavy metal was added to 100 ml of sewage
sludge. Dissolved oxygen consumption was recorded as a measure
127
-------
of bacterial action. Cadmium, as CdC12' at 10 mg Cd/l
increased rate of 02 uptake of sludge during a period of 12
hours, 100 mg Cd/l reduced 02 uptake rate; 1 mg Cd/l had no
observable effect. A total of 200 mg/l of lead as Pb(N03)2
stimulated 02 uptake after 6 hrs; 20 mg Pb/l had no observable
effect; 500 mg Pb/l reduced 02 uptake rate. At 500 mg Zn/l as
ZnC12' 02 uptake rate after 4e hrs was stimulated; 50 mg Zn/l
had no effect and 1000 mg Zn/l reduced 02 uptake although it
parallelled control values. This increased rate of 02 uptake
due to moderate concentrations of metals may be an example of the
Arndt-Schultz effect, which describes the general tendency for
poisonous substances in low concentrations to stimulate rather
than depress biological processes.
2498.
Tafanelli, R. and R.C. Summerfelt. 1975. Cadmium-induced
histopathological changes in goldfish. In: Ribelin,
W.E. and G. Migaki (eds.). Pathology offishes.
Univ. Wisconsin Press, Madison, WI:613-645.
Toxicity, body distribution, and histological damage
effects of cadmium on goldfish, Carassius auratus, is presented.
LD-50 in intraperitoneal injections of CdC12 was 30 mg/kg (24
hr), 23 (48 hr), and 20 (96 hr). Liver, because of its larger
mass, contained the largest quantity of Cd, but kidney had the
highest concentration. Concentrations were >400 mg Cd/kg dry wt
in kidney, up to 300 in liver, < 100 in ovary and < 6.5 in muscle.
Authors suggest that Cd may have serious effects on
osmoregulation, hematopioesis, and gametogenesis, resulting in
reduced fecundity and destruction of vital organs. Cadmium
residues in flesh of fish suggests biological magnification
through the food chain, with possible transfer to man.
2499.
Takeuchi, T., F.M. D'Itri, P.V. Fischer, C.S. Annett, and
M. Okabe. 1977. The outbreak of Minamata Disease
(methyl mercury poisoning) in cats on Northwestern
Ontaria reserves. Environ. Res. 13:215-228.
Pathological, histochemical, and analytical studies
confirmed the presence of Minamata Disease in at least one of two
cats from near Indian Reserves in Northwest Ontario, Canada,
after long-term ingestion of fish from the English River.
Maximum concentrations of mercury reported from other sources in
freshwater fish from the Ontario waters were 19.6 mg/kg wet wt of
muscle in Stizostechion vitreum, 24.8 for Lota lota, and 27.e for
Esox lucius, and these approximated levels--rrlfish from
128
-------
mercury-contaminated Minamata Bay, Japan. Tissue levels of total
mercury in the two cats were 16.4 and 6.9 mg/kg wet wt in brain,
4.9 and 4.3 in pancreas, 13.4 and 10.8 in kidney, 67.1 and 14.2
in liver, 17.6 in blood (one cat only), and 392 and 121 in fur.
The cat with higher values, comparable with symptanatic cats in
Japan, developed acute neurological symptoms including ataxic
gait, uncontrolled howling, and seizures.
2500.
Tarao, R., T. Tabata, and M. Yasuhara. 1976. The
accumulation of mercury in the fishes reared in the
sea water contaminated by suspended solids containing
mercury. Bull. Japan. Soc. Sci. Fish. 42:1411-1422.
Three species of marine teleosts, bream Chrysophrys
major, majina Girella punctata, and rockfish Sebasticus
marmoratus were reared in seawater containing mercury-
contaminated mud from Minamata Bay, Japan. One group was reared
in seawater-mud suspensions containing 600 mg Hg/kg dry wt; a
second group in 100 mg Hg/kg dry wt; and a control of 0.1 mg/kg.
Hg in muds was present mainly as insoluble compounds. Total and
methylmercury in fish flesh increased slightly over 90 days
although equilibrium values were low; the maximum value recorded
for total Hg was 0.28 mg/kg wet wt in majina, and for methyl Hg
it was 0.14 in rockfish. Fishes reared in aerated seawater
irradiated with ultraviolet light had slightly higher equilibrium
values: 0.32 mg/kg for total Hg, and 0.17 for methyl Hg. As
total Hg from mud suspensions varied from 600 to 0.1 mg/kg dry
wt, no change in rate or extent of Hg accumulation was seen.
Authors concluded that there was little possibility of mercury
accumulation into fish from mud suspensions containing insoluble
Hg exceeding established maximum permissible levels.
2501.
Terhaar, C.J., W.S. EWell, S.P. Dziuba, W.W. White, and
P.J. Murphy. 1977. A laboratory model for evaluating
the behavior of heavy metals in an aquatic
environment. Water Research 11: 101-110.
A dynamic biological system capable of simultaneously
distinguishing between bioaccumulation and bianagnification
through successive trophic levels in an aquatic ecosystem is
described, using algal cultures of predominately Scenedesmus sp.,
Daphnia magna, freshwater mussels Ligumia sp. and Margaritifera
sp., and fathead minnows Pimephales promelas. Effects of
thioslufate-complexed mercury, at 0.002 and 0.005 mg/l, and
silver, at 0.5 and 5.0 mg/l, were studied over 10 weeks. Maximum
129
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concentration factors in organisms exposed to 0.5 mg Ag/l were
240 for algae after 5 wks, 36 for Daphnia after 5 wks, 8.2 for
mussels after 7 wks, and 2~ for fish after 10 wks. CF in 5.0 mg
Ag/l were l~er for each organism. Biomagnification indices for
fish increased to 90 in 0.005 mg Hg/l, but stayed at 0 in 5.0 mg
Ag/l. Metal concentrations in control animals never exceeded 0.1
mg Hg/kg wet wt or 11.0 mg Ag/l over 10 wks. Authors concluded
that both Hg and Ag were bioaccumulated in fish, with Hg greater
than Ag; Hg but not Ag was biomagnified. Freshwater mussels were
relatively poor indicators of metal contamination.
2502.
Thomas, W.H., O. Holm-Hanse, D.L.R. Seibert, F. Azam, R.
Hodson, and M. Takahashi. 1977. Effects of copper on
phytoplankton standing crop and productivity:
controlled ecosystem pollution experiment. Bull.
Marine Science 27:34-43.
Copper concentrations of 0.01 and 0.023-0.05 mg/l
added at day 2 initially inhibited phytoplankton photosynthesis
and growth. Total particulate organic carbon, biomass-carbon and
phytoplankton-carbon levels dropped from >1 mg C/l to 0.035-0.30
at day 5 in both QOncentrations. Productivity decreased from 7.0
to 0.9-0.1 mg C/mj/hr. Crops and photosynthesis recovered, so
that at the end of the 27 day experiment, values were similar to
controls. Excretion of C-14 organic carbon reached 85% during
the first half of the experiment in Cu treated groups before
returning to control values. There were no significant
differences in C:N or C:P ratios between control and test
enclosures, indicating that Cu did not change gross chemical
composition of the phytoplankton. In enclosures which received
0.005 and 0.01 mg Cull on day 8, the algal standing crop, but no
photosynthesis rate, increased over control levels.
Phytoplankton-C, ATP, and productivity were higher in
experimental groups after 20-25 days. Authors suggest that
observed lack of inhibition due to Cu may be associated with
large numbers of residual Cu-resistant microflagellates and that
biomass increase could be due to inhibition of zooplankton
grazing.
2503.
TOOmas, W.H. and D.L.R. Seibert. 1977. Effects of copper
on the dominance and the diversity of algae:
controlled ecosystem pollution experiment. Bull.
Marine Science 27:23-33.
Addition of 0.01 or 0.05 mg/l copper to experimental
enclosures caused diatoms, Chaetoceros sp., in the top 10 meters
130
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to decline from 55-~5% total carbon to a~ost zero after 21
days. These populations were replaced mainly by
microflagellates. Nitzschia delicatissima became the dominant
diatom in 0.01 mg Cull and Navicula distans in 0.05 mg/l.
Taxonomic diversity declined in both control and experimental
enclosures, but was much lower in Cu treated groups. Biomass
diversities also decreased, but with no significant difference
between groups. In a second experiment, algal populations
acclimatized for 10 days received 0.005 or 0.01 mg Cull.
Although Chaetoceros sp. was dominant before Cu was added, N.
delicatissima slowly replaced Chaetoceros as the dominant species
by day 17 and comprised 75-90% of the crop at 28 days.
2504.
Thurberg, F.P., A. Calabrese, E. Gould, R.A. Greig, M.A.
Dawson, and R.K. Tucker. 1977. Response of the
lobster, Homarus americanus, to sublethal levels of
cadmium and mercury. In: Vernberg, F.J., A.
Calabrese, F.P. Thurberg, and W.B. Vernberg (eds.).
Physiological responses of marine biota to
pollutants. Academic Press, N.Y.: 185-197.
Oxygen consumption in lobsters increased from 710 m1
02/hr/kg for controls to 775 after 30 days in 0.003 mg Cd/l and
to 820 after 30 days in 0.006 mg Cd/l. No changes in serum
osmolality were noted in lobsters exposed to test concentrations
of Cd or Hg; osmolality was maintained at 40 mOgn above
seawater. No significant difference in activity of heart
aspartate aminotransferase was evident between control and
exposed lobsters. Cd concentration in digestive gland varied
only slightly after exposure to 0.0, 0.003, and 0.006 mg Cd/l:
20.3 to 23.5 mg Cd/kg wet wt after 30 days, and 12.9 to 13.9
after 60 days. Cadmium in muscle increased with increasing
concentrations: 1.5 to 3.4 mg/kg wet wt after 30 days, and 1.6
to 2.6 after 60 days. Muscle concentrations were< 0.12 mg Cd/kg
wet wt for all 3 concentrations at 30 and at 60 days. At Hg
exposures of 0.0, 0.003, and 0.006 mg/l for 30 days, Hg levels
ranged from 0.12 to 15.2 mg Hg/kg wet wt in digestive glands,
0.14 to 85.3 in gills, and 0.23 to 1.0 in tail muscle; higher
concentrations reflected increasing Hg exposure levels. After 60
days, gills contained 0.05 to 119.5 mg Hg/kg wet wt, increasing
with increasing exposure level.
131
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2505.
Thurberg, F.P. and M.A. Dawson. 1974. Physiological
response of the cunner, Tautogolabrus adspersus, to
cadmium. III. changes in osmoregulation and oxygen
consumption. In: U.S. Dept. Cornm. NOAA Tech. Rpt.
NMFS SSRF-681 :11-13. Avail. from D 83, Tech. Inf.
Div., Environ. Sci. Inform. Center, NOAA, Wash., D.C.
20235.
Cunners exposed to 3-24 mg/l cadmium for 96 hrs showed
no change in serum osnolality from the normal value of
approximately 340 mOsm determined in control fish. Serum
osmolality in fish exposed to 48 mg Cd/l rose to a mean of 390
mOsm. Cadmium reduced gill tissue oxygen consumption rates at
all concentrations tested. A normal rate of 0.75 ul/hr/mg was
reduced to 0.51 ul/hr/mg after exposure to Cd at concentrations
of 3, 6, 12, and 24 mg/l. Oxygen consumption was 0.58 ul/hr/mg
after exposure to 48 mg Cd/l.
2506.
Thurberg, F.P., and R.S. Collier.
response of cunners to silver.
8: 40-41.
1977. Respiratory
Marine Poll. Bull.
Oxygen-consumption rates of the marine teleost,
Tautogolabrus adspersus, were measured after exposure for 96
hours to AgN03 in seawater. Significant respiratory depression
was observed at 0.12 mg Ag/l; concentrations above 0.50 mg Ag/l
were lethal. No significant changes in blood serum osmolarity
were observed during exposure.
2507.
Timourian, H. and G. Watchmaker. 1977. Assay of sperm
motility to study the effects of metal ions. In:
Drucker, H. and R.E. Wildung (eds.). Biological
implications of metals in the environment. ERDA Symp.
Sera 42:523-535. Avail. as CONF-750929 from Nat.
Tech. Inf. Serv., U.S. Dept. Comm., Springfield, VA
2216 1 .
Motility of sperm from sea urchin, Strongylocentrotus
purpuratus, was determined during exposure to Zn, Ni, and Cu
salts. Optical anisotropy of sperm permitted determination of
orientation by a spectrophotometer with flCM cells. Zinc
concentrations of 0.006 to 0.654 mg/l, added as sperm were first
released, increased sperm motility; motility decreased at these
concentrations when zinc was added 50 min after sperm release.
At 6.54 mg Znll, motility decreased regardless of time of
132
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addition. Nickel increased sperm motility at 0.006 to 0.587 mg/l
as sperm were first released, and decreased motility at 5.87 to
587 mg/l. After 4.5 hrs exposure to Ni, inhibitory effects were
overcome and motilty returned to normal. When added 50 min after
released, 0.587 to 0.006 mg Ni/l caused only a slight change
while 5.87 mg Ni/l caused a decrease. Copper concentrations of
0.006 and 0.0006 mg/l increased sperm motility and 0.064 to 6.35
mg/l caused a decrease, regardless of time of addition.
2508.
Topping, G. and H.L. Windom. 1977. Biological transport
of copper at Loch Ewe and Saanich Inlet: controlled
ecosystem pollution experiment. Bull. Marine Science
27:135-141.
Chemical studies in experimental enclosures showed
that a large percentage of added copper was lost from the water.
Concentration of copper in the enclosure with 0.05 mg Cull as
CuS04 dropped to 0.03 mg Cull during the first day, and
gradually decreased to 40% of the nominal level after 25 days.
Ambient concentration of Saanich Inlet water was 0.001 mg Cull.
Similar trends were exhibited with initial doses of 0.010 and
0.005 mg/l added to Loch Ewe waters. Settlement material,
consisting mainly of decaying phytoplankton, showed an increase
in Cu after a short decline. In the enclosure with 0.050 mg/l,
Cu concentration increased fran 250 mg/kg dry wt to 800 in 20
days. In 0.01 mg/l, settled material increased from 300 to 470
mg Culkg dry wt. The quantity associated with settlement
material was a small percentage of that lost from the water
column. Copper lost by settlement appeared to be directly
proportional to primary production level at both 0.005 and 0.01
mg/l levels. Loss was significantly correlated with carbon
concentrations and to concentration of soluble Cu added. Cu:C
ratios were higher in samples that consisted mainly of fecal
pellets than those with mostly phytoplankton. Cu:Zn ratios in
detritus increased to 1.2 in 0.05 mg Cull and 0.6 in 0.005 mg/l;
for controls, this value was 0.2.
2509.
Ueda, Tn R. Nakamura, and Y. Suzuki. 1976. Canparison
of 5IDed accumulation from sediments and sea water
by polychaete worms. Bull. Japan. Soc. Sci. Fish.
42 :299-306.
Deposit feeding worms, Nereis japonica, directly in
contact with Cd-115m contaminated sediments accumulated 6x more
133
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cadmium than control worms after 8 days. Concentration factor in
worms from seawater with 0.05 mCi Cd/l was 22 after 8 days, 200X
the accumulation from sediments. Excretion patterns of Cd-115m
in worms showed a biological half-life of 4 days in the short
component; the long component had a much longer half-life. Upon
addition of 0.01 mCi Cd/l to a simulated ecosystem, 75% of the
activity was in seawater, 15% in sediments, and 10% in algae,
Ulva pertusa. A rapid Cd decrease in seawater with an increase
in sediments was seen during the first three days, while algal
level remained constant. On day 13, Cd-115m distributions were
60, 32, and 8% in seawater, sediments, and algae, respectively.
Activity ratios of Cd-115m were 9 for sediments and 21 for algae,
similar to 27 for worms.
2510.
Ueda, T., R. Nakamura, and Y. Suzuki. 1977.
of influences of sediments and sea water
accumulation of radionuclides by worms.
Radiation Res. 18:84-92.
Comparison
on
Jour.
Concentration factors of radionuclides from seawater,
after 10-11 days exposure, in unfed polychaetes, Nereis japonica,
were 6 for Co-60, 4 for Zr-95-Nb-95, 6 for Ru-106-Rh-106, and 6
for Cs-137. Similar concentration factors were found in worms
fed contaminated algae. Excretion patterns show biological half
li ves in fed worms of 6 days for Cs-137, and 37, 32, and 35 days
for Co-60, Zr-95-Nb-95, and Ru-106-Rh-106, respectively. Half
lives were slightly longer in all cases for unfed worms.
Transfer ratios of radionuclides from sediments to worms were 5%
for Co-60, 0.9 for Zr-95-Nb-95, 0.6 for Ru-106-Rh-106, and 17.9
for Cs-137, in cpm/g in reference to initial sediment activity.
Biological factors of sediments, calculated by comparing
concentration factors with transfer ratios, were 120 for Co-60,
440 for Zr-95-Nb-95, 1000 for Ru-106-Rh-106, and 30 for Cs-137.
2511.
Vaccaro, R.F., F. Azam, and R.E. Hodson. 1977. Response
of natural marine bacterial populations to copper:
controlled ecosystem pollution experiment. Bull.
Marine Science 27:17-22.
Addition of CuS04' at 0.01 and 0.05 mg Cull to two
enclosed marine ecosystems produced a 100 to 1000 fold increase
in relative numbers and activity of bacterial heterotrophs. Two
days after addition, glycine assimilation at 5 m depth increased
by an order of magnitude over controls. Between days 8 and 16
there was a decline in heterotrophic activity, corresponding to a
134
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slight decline in controls. For the remainder of the 26 day
period, assimilation was faster in the two copper treated
enclosures. TI1is acceleration appeared to follow release of
available organic carbon from one or more copper-sensitive
components of the original ecosystem. Ultimately, bacterial
survivors, which demonstrated an increased tolerance to copper
with time, provided a source of plant nutrients suitable for
establishment of succeeding phytoplankton regimes.
2512.
VanLoon, J.C. and R.J. Beamish. 1977. Heavy-metal
contamination by atmospheric fallout of several Flin
Flon area lakes and the relation to fish populations.
Jour. Fish. Res. Bd. Canada 34: 899-906.
Concentrations of Zn, Cu, Ni, Pb, Fe, Cd, Ca, Mg,
S042, Hg and As were measured in lakes near the Flin Flon
smelters. In a study of 31 lakes, 7 had Zn levels above 100
ug/l, 6 had levels between 50 and 100 ug/l, and the remainder had
concentrations <50 ug/l. Hamell Lake contained an average of 300
ug Zn/l and 15 ug Cd/l. The lake supported populations of
walleye, yellow perch, northern pike, lake whitefish, and white
sucker; none of the fish, except perhaps yellow perch, were
stunted. An examination of ovaries did not show abnormal
development. Cliff Lake had an average of 85 ug Zn/l and 10 ug
Cull. The lake contained an abundance of all the fish in Hamell
Lake plus lake herring, burbot, trout perch and spot tail
shiners. There was no indication of abnormal growth or abnormal
reproduction in any of these populations.
2513.
Vattuone, G.M., K.S. Griggs, D.R. McIntyre, J.L.
Littlepage and F.L. Harrison. 1976. Cadmium
concentrations in rock scallops in comparison with
some other species. U.S. Energy Research and Dev.
Admin. UCRL 52022: 1-11. Avail. from Nat. Tech.
Inform. Ser., U.S. Dept. of Cornm., 5285 Port Royal
Rd., Springfield, VA 22151.
Cadmium concentrations were determined in rock
scallops Hinnites multirugosus and mussels Mytilus californianus
collected in 1973 from the Channel Islands, Southern California
Bight. Mean Cd concentrations in mg/kg wet wt were 1.8 in mussel
soft tissue; 31.2 in rock scallop soft tissue; 0.3 in scallop
adductor muscle; and 46.3 in scallop visceral mass. Scallop Zn
and Cd mean levels in mg/kg wet wt were 37.2 and 10. 1, in kidney
respectively, and 68.8 and 211.0, in digestive gland plus
135
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stomach, respectively. Cadmium levels in algae Macrocystis sp,
Laminaria sp. Egregia laevigata and Bossea sp., abalone Haliotes
corrugata, lobster Panulirus interruptus, and sea urchin
Strongylocentrotus franciscanus are also reported. Maximum Cd
values were 2.7 mg/kg wet wt for algae, 82.2 for abalone
digestive gland, 0.3 for abalone muscle, 29.3 for lobster
repatopancreas, 0.2 for lobster muscle and 0.6 for urchin gonad.
Tracer experiments with Cd-109 confirmed that rock scallop
tissues concentrated Cd to a greater degree than the
corresponding tissues of the mussel. Maximum CF values recorded
for Cd were 11,800 for scallop kidney, and 4500 for mussel
kidney; lcwest CF values were in body fluid of scallop (15) and
mussel (4).
2514.
Vernberg, W.B., P.J. DeCoursey, M. Kelly, and D.M. Johns.
1977. Effects of sublethal concentrations of cadmium
on adult Palaemonetes pugio under static and
flow-through conditions. Bull. Environ. Contamin.
Toxicol. 17:16-24.
Mortality and cadmium uptake in grass shrimp increased
with increasing salinity during immersion in seawater containing
0.05 mg Cd/l. Maximum mortality was in 30 0/00 S with 25% dead
in 21 days. Cd concentration in shrimp held in 30 0/00 increased
to 8 mg/kg dry wt at 3 days, 13 at 7 days, 29 at 14 days, and 36
mg/kg at 21 days. At 25 C for 7 days, Cd levels in P. pugio
decreased as salinity increased to 30 0/00 in both static and
flow-through systems. Shrimp in flow-through tests had higher Cd
concentrations at lcwer salinities than shrimp tested under
static conditions. At 15 C, Cd levels in flow-through again
decreased with increasing salinity; however, levels increased
with increasing salinity in static systems. In both flow-through
and static systems, oxygen uptake rates at 25 C or 15
C-acclimatized shrimp in 5, 15 or 30 0/00 with 0.05 mg Cd/l were
generally reduced in higher salinities, but not in a predictable
manner. Because of differences between the two water systems
tested, authors suggest that data from flow-through systems be
used since it is more applicable to field situations. Molting
frequency of shrimp in 0.05 mg Cd/l under static conditions was
significantly increased in 10 and 20 0/00 but not in 5 and 30
0/00. Authors state that ~ pugio is too resistant and tolerant
a species to be of value for short-term bioassay studies on Cd.
2515.
Walker, G.
1977.
"Copper" granules in the barnacle
136
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Marine Biology 39:343-349.
Balanus balanoides.
Barnacles from Dulas Bay, U.K., which receives high
heavy metal runoff, contained two different types of granules
within prosomal parenchyma cells. X-ray microprobe analysis
shows one to be a "zinc" granule comprised of concentric layers
and high concentrations of phosphorus and zinc. The "copper"
granule is homogenous with high sulphur and copper content.
While "zinc" granules are composed of inorganic phosphate, the Cu
in "copper''' granules is probably complexed with organic matter.
Both granules were relatively insoluble. Although "zinc" and
"copper" granules were present together in the prosoma, atomic
absorption analyses of whole bodies (prosoma plus thorax) show
that zinc content (50.3 mg/kg dry wt) is much higher than copper
(3.8 mg/kg dry wt); other elements detected were magnesium at
4.9, calcium at 2.3, and iron at 0.9 mg/kg dry wt.
2516.
Weigel, H.P. 1977. On the distribution of particulate
metals, chlorophyll, and seston in the Baltic Sea.
Marine Biology 44:217-222.
Water samples from the Baltic Sea were analyzed for
Cu, Fe, Zn, Cd, Pb, chlorophyll and seston during the end of the
phytoplankton spring bloom. Mean metal concentrations in
surface waters of the Baltic Sea in ug/l were: 0.13 Pb, 0.07 Cu,
0.006 Cd, 5.79 Fe and 0.99 Zn. Correlations between metal
concentrations and chlorophyll, seston, phytoplankton carbon and
cell-count were calculated for both photic layer and deeper
waters. Significant correlations were found only in the photic
layer. Posi ti ve correlations ~re found between copper and
chlorophyll; phytoplankton carbon and cell counts; cadmium and
chlorophyll; Cd and phytoplankton carbon; iron and chlorophyll;
iron and seston; and ircn and phytoplankton carbon.
2517.
Weis, J. S. 1977 . Limb regenera ti on in fi ddler crabs:
species differences and effects of methylmercury.
BioI. Bull. 152:263-274.
Under identical conditions, isolated specimens of the
crab, Uca pugnax, found in temperate waters regenerate limbs and
molt faster than ~ pugilator. The tropical species ~ rapax and
~ speciosa also regenerate faster than ~ pugilator from the
same location. ~ thayeri regenerate more slowly when kept in
groups of their own species. Q. Thayeri will not complete
regeneration nor molt, ~ pugilator is slightly retarded in
regeneration, and ~ rapax is delayed in molting. Newly
137
-------
regenerated limbs of all 4 species are lighter in color than old
limbs, and only in ~ pugilator do they not darken in a few weeks
after ecdysis. When treated with 0.5 rng methylmercury/l in 9
0/00 salinity, regeneration growth was halted in ~ thayeri. For
~ pugilator, growth was decreased to about 0.33 of controls by
21 days. Growth was inhibited least in ~ rapax with 50% of
crabs reaching ecdysis in 32 days. In 0.3 rng methylmercury/l,
25% of ~ rapax reached ecdysis by 21 days at 9 0/00 S, while
37.5% had molted at 36 0/00 S. Methylmercury concentrations of
0.001, 0.01 and 0.1 rng/l had no effect on growth of ~ rapax, and
0.1 mg/l had none on ~ thayeri or Q. pugilator. Melanin was
absent in regenerated limbs of all three species of Uca exposed
to 0.5 mg/l methylmercury, in all ~ rapax exposed to 0.3 rng/l,
in 25% of ~ thayeri in 0.1 mgl at 9 0/00 Sand 50 to 80% at 36
0/00 S, and in 25% of ~ pugilator in 0.1 mg/l at both
salinities. Pigment lack was attributed to inhibition of melanin
synthesis.
2518.
Weis, P. and J.S. Weis. 1977. Methylmercury
teratogenesis in the killifish, Fundulus
heteroclitus. Teratology 16:317-326.
Abnormalities resulted from exposure for 3 days of
developing eggs of seawater-adapted Fundulus heteroclitus during
imnersi on in seawater soluti ons containing 0.03 or 0.04 rng/l of
methylmercuric chloride. Percentage of axis formation was
reduced and embryos developed cyclopia or intermediate conditions
leading to cyclopia, reflecting interference with induction of
the forebrain. The heart failed to differentiate properly into
chambers and was a thin, feebly beating tube incapable of
circulating blood. Other tissues continued developing normally;
embryos showed spontaneous movement comparable to controls.
Embryos with severe cardiovascular or optic defects did not
hatch. Upon hatching, some fish which had previously appeared
normal exhibited skeletal malformations such as vertebral bends
or inability to uncurl from the chorionic position. Exposure for
shorter periods of time (6, 12, or 24 hrs), or to lower
concentrations (0.01 or 0.02 mg Hg/l) reduced incidence of
abnorrnali ti es.
2519.
Weis, J.S., and P. Weis. 1977. Effects of heavy metals
on development of the killifish, Fundulus
heteroclitus. Jour. Fish Biology 11:49-54.
When f..:.. heterocli tus embryos were exposed to inorganic
138
-------
mercury at concentrations of 0.03 or 0.1 mg/l at the early
blastula stage, the percentage of successful axis formation was
reduced and a significant proportion of embryos developed
cyclopia or intermediate conditions leading to cyclopia. At the
late blastula stage, embryos were more resistant to mercury.
Embryos which developed in concentrations of 1 and 10 mg/l of Pb
were nonnal in appearanre until hatching, at which time they
exhibited spinal curvature defects. No significant effects of
cadmium on killifish developnent at concentrations up to 10 mg
Cd! 1 were noted.
2520.
Wentsel, R., A. McIntosh, W.P. McCafferty, G. Atchison and
V. Anderson. 1977. Avoidance response of midge
larvae (Chironomus tentans) to sediments containing
heavy metals. Hydrobiologia 55:171-175.
Avoidance reactions of chironomid insect larvae to
contaminated sediments taken from a lake impacted with heavy
metals W8re studied. Heavy metal levels in the test sediment
ranged from background levels of 0.6 mg/kg dry wt of cadmium, 77
mg/kg of zinc and 17 mg/kg of chromium to a maximum of 1029 mg/kg
of cadmium, 17 ,262 mg/kg of zinc and 2106 mg/kg of chromium. A
linear relationship was established between cadmium and zinc
levels in the sediment, and avoidance by chironomids. An
approximate threshold avoidance of metals in the sediment was
determined to be between 213-422 mg/kg cadmium, 4385-8330 mg/kg
zinc and 799-1513 mg/kg chromium.
2521.
Wharfe, J.R. and W.L.F. Van Den Brook. 1977. Heavy
metals in macroinvertebrates and fish from the Lower
Medway Estuary, Kent. Mari ne Poll. Bull. 8: 31- 34.
Macroinvertebrates and fish collected between April
1973 and January 1976 from 10 industrialized locations were
analyzed for mercury, zinc, copper, lead and cadmi urn. Mean metal
concentrations in mg/kg wet wt in the periwinkle, Littorina
littorea, were Hg 0.09-0.24; Zn 15.5-24.3; Cu 23.8-36.1; Pb
0.28-3.03; and Cd 0.43-0.90. For the shore crab, Carcinus
maenas, these were Hg 0.14-0.29; Zn 25.1-38.8; Cu 15.4-31.4; Pb
0.38-3.32; Cd 0.96-2.07. In mussel, Mytilus edulis, these values
were Hg 0.14-0.30; Zn 29.0-41.8; Cu 1.9-2.3; Pb 0.75-2.17; Cd
0.71-1.21; in ragwonn, Nereis diversicolor, these were Zn
22.0-37.5; Cu 1.6-5.1; Pb 0.1-4.8; Cd 0.2-0.5. For shrimp,
~ vulgaris, the mean concentrations were Hg 0.17; Zn 26.4;
Cu 18.5; Pb 1.22; and Cd 0.59. For eel, Anguilla anguilla,
139
-------
muscle concentrations in mg/kg wet wt were Hg 0.36-0.54; Zn
23.8-27.2; Cu 0.5-0.6; Pb 0.48-1.05; Cd 0.12-0.17. For eel liver
the values were Hg 0.35-1.73; Zn 51.9-71.9; Cu 14.9-25.1; Pb
0.84-2.68; Cd 0.24-0.37- Levels in muscle tissue of whiting,
Merlanguis merlangus, were Hg 0.37-0.45; Zn 9.1-9.2; Cu 0.6-0.7;
Pb 0.29-0.36; Cd 0.13-0.21. In whiting liver the values were Hg
0.33; Zn 28.3; Cu 2.4; Pb 0.89; Cd 0.15. Gut wall levels in
whiting were Hg 0.23: Zn 23.1; Cu 1.4; Pb 0.45; Cd 0.15.
Flounder, Platichthys flesus, muscle tissue concentrations were
Hg 0.10-0.64; Zn 12.3-18.2; Cu 0.3-1.3; Pb 0.28-0.39; Cd
0.06-0.07. In flounder liver these were Hg 0.08-0.24; Zn
53.8-68.9; Cu 12.9-18.3; Pb 0.94-1.38; Cd 0.18. Flounder gut
wall concentrations were Hg 0.17; Zn 36.2; Cu 2.7; Pb 0.72; Cd
0.19. Ovary metal concentrations in flounder were Hg 0.12; Zn
146.8; Cu 2.4; Pb 0.12; Cd 0.08. Plaice, Pleuronectes platessa,
muscle tissue metal concentrations were Hg 0.15-0.27; Zn
10.0-11.9; Cu 0.8-1.1; Pb 0.70-1.15; Cd 0.08-0.14. Plaice liver
tissue levels were Zn 38.9; Cu 3.3; Pb 1.34; Cd 0.18. Gut wall
values in plaice were Hg 0.07; Zn 27.5; Cu 2.4; Pb 1.33; Cd
0.22. Sandy go by , Pomatoshistus minutus, whole body metal
concentrations were Hg 0.16; Zn 28.7; Cu 1.17; Pb 1.0; Cd 0.24.
Sprat, Sprattus sprattus, whole body concentrations were Hg 0.16;
Zn 38.5; Cu 1.1; Pb 1.03; Cd 0.29.
2522.
Wolverton, B.C. and R.C. McDonald. 1975. Water hyacinths
and alligator weeds for removal of silver, cobalt, and
strontium from polluted waters. NASA Tech. Mem.
T~X-72727:1-12. Avail. from NASA, Nat. Space Tech.
Lab., Bay St. Louis, Miss. 39520.
Effects of removal of Ag, Co, and Sr from static water
systems by water hyacinths Eichhornia crassipes, and alligator
weeds Alternanthera philoxerides, were investigated. These
plants rapidly removed heavy metals from water by root absorption
and concentra ti on. Wa ter hyaci nths removed o. 44 mg of silver,
0.57 mg of cobalt, and 0.54 mg of strontium in an ionized form
per gram of dry plant material in 24 hrs. Therefore, one hectare
of water hyacinths is potentially capable of removing 263 g of
silver, 340 g of cobalt, and 326 g of strontium per day.
Alligator weeds removed a maximum of 0.44 mg of silver, 0.13 mg
of cobalt, and o. 16 mg of strontium per gram of dry plant
material per day.
2523.
Wolverine, B. and R.C. McDonald. 1976. Don't waste
waterweeds. New Scientist 72:318-320.
140
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Water hyacinth, Eichhornia crasspipes, which clogs
waterways, was investigated as a means of treating effluents,
producing biogas and fertilizer, and feeding livestock.
Canposition, in % dry wt, of water hyacinth grown in sewage
containing about 35 mg Nil and 10 mg P/l from South Mississippi
was 2.0-3.5 for K, 1.5-2.5 for Na, 0.6-1.3 for Ca, 0.2-0.3 for
Mg, 0.03-0.05 for Fe, 0.005-0.05 for Zn, and 0.005-0.008 for Mn.
A 0.2 hectare canal covered with water hyacinths reduced silver
in laborat
-------
body, with decreasing salinity. Hepatopancreas levels ranged
from 22.5 to 33.7 mg Cd/kg wet wt and muscle levels stayed < 6.0
mVkg. Uptake in 1.1 mg Cd/l soowed similar trends. Over 68
days in 2.3 mg Cd/I, Cd was steadily accumulated by the carapace,
to 78.7 and 45.0 mg/kg wet wt in 50 and 100% SW, respectively.
Gill Cd concentration reached a maximum in 50% SW after about 14
days, which was eventually overtaken by Cd concentrations in
animals in 100% SW at 40-45 days. No salinity effect on Cd
uptake in gills was seen after 48 days; animals in both
salini ties leveled at 33.7 mg Cd/kg wet wt. Hepatopancreas Cd
also plateaued at this concentration, muscle soowed almost no Cd
uptake, and maximum hemolymph concentrations were 0.7 to 0.9 mg
Cd/I. Salinity had no apparent effect over this period on these
three tissues. Whole body Cd was 258.5 mg/kg wet wt in 50% SW
and 89.9 mg/kg in 100% after 68 days. Crabs loaded with Cd for a
37-day period lost 50% of whole body Cd concentration within 11
days in clean water, from 19.1 to 10.1 mg/kg wet wt. Losses from
carapace and gills accounted for much of this reduction. Calcium
levels in gills of crabs exposed to Cd were 0.31 mg/kg wet wt in
100% SW and 0.24 in 50%; in muscle Ca was 0.24 and 0.13 mg/kg,
respectively, and in hepatopancreas it was 6.0 and 3.9.
Magnesium concentrations in the respective salinites were 0.55
and 0.35 mg/kg wet wt in gills, 0.37 and 0.25 in muscle, and 1.71
and 1.01 in hepatopancreas. No relationship was established
between Cd and either Ca or Mg.
2526.
Wright, D.A. 1977. The uptake of cadmium into the
haemolymph of the soore crab Carcinus maenas: the
relationship with copper and other divalent cations.
Jour. Exper. Biology 67:147-161.
Haemolymph Cd levels of C. maenas exposed to 2.3 mg
Cd/l were initially dependent upon salinity. After 14 days, Cd
in haemolymph was o. 63 mgll in 50% seawater crabs and 0.38 mg/l
in 100% SW specimens. This trend, however, was not sustained
over 68 days. In both field and experimental conditions, nearly
all ha.emolymph Cd in crabs became bound to haemolymph protein
within several days. Although haemolymph copper and protein
concentrations are highly correlated, Cd formed a significant
positive relationship with each only after 21-28 days uptake.
Exposure to 2.3 mg Cd/l had no obvious effects on haemolymph
protein concentrations and copper up to 0.07 mg Cull, which were
clearly dependent on feeding status. Crab mortality was often
proceded by a rise in haemolymph Cd, usually before any signs of
tisSLE breakdown were noticed. In 100% SW with 2.3 mg Cd/I,
haemolymph Ca dropped from 0.56 to 0.50 and serum Ca from 0.44 to
142
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0.38 mg/l during Cd uptake over 68 days. Haemolymph Mg and serum
Mg dropped from 0.55 to 0.48 and 0.55 to 0.54 mg/l, respectively,
over this period. Ca and Mg levels in 50% SW crabs showed no
distinguishable trend during Cd accumulation. It was concluded
that Cd loos via urine was probably unimportant. Urine Cd
concentrations of 0.03 to 0.22 mg/l often exceeded serum Cd
levels with a maximum of 0.07 mg/l, indicating that cadmium may
sometimes be eliminated in bound form.
2527 .
Wright, D.A. 1977. The effect of calcium on cadmium
uptake by the shore crab Carcinus maenas. Jour.
Exper. Biology 67:163-173.
Ac cumul a ti on of cadmi um by ~ maenas was, to some
extent, dependent upon calcium concentration of the external
medium. This effect was apparently independent of overall
salinity. Whole body Cd had a highly significant inverse
relationship with external Ca concentration. This was reflected
by Cd levels in haemolymph, but was less obvious in
hepatopancreas, gill, and carapace. Both haemolymph and gill
cadmium were inversely related to tissue calcium concentrations.
Postmolt crabs exposed to 2.3 mg Cd/l for 6 days in 100% SW
accumulated up to 5.0 mg Cd/l and up to 960 mg Call in
haemolymph, which was more than intermolt animals. Postmolt
crabs in Cd-free seawater contained 350 to 585 mg Call in
haemolymph, generally lower than intermol ts. Rise in Ca levels
in the presence of cadmium may indicate some degree of
competition for deposition sites between Cd and Ca.
2528.
Yamamoto, T., Y. Otsuka, and K. Uemura. 1976. Gallium
content in seaweeds. Jour. Oceanogr. Sac. Japan
32: 182-186.
Gallium content of 30 species of seaweeds from near
Torno Island, Wakayama Prefecture ranged from 0.02 to 0.64 rng/kg
dry wt with an average of 0.14 mg/kg. Aluminum, ranging from 57
to 3290 mg/kg dry wt, averaged 533 mg/kg; iron, ranging from
47-3310 mg/kg dry wt, averaged 501 mg/kg in seaweeds. Gallium
content had a close relationship to4Al and Fe. The average
weighE ratio of Ga/Al was 3.8 x 10- and ratio of Ga/Fe was 4.0
x 10-. Fe/ Al ratio was 0.96. Ga/ Al weight ratio was4similar
to that reported. fer shallow water de~osi ts (2. 1 x 10- ), but
was lcwer than in seawater (1.5 x 10- ).
143
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2529.
Young, D.R., and T.-K. Jan. 1977. Fire fallout of metals
off California. Marine Poll. Bull. 8:109-112.
Major farest or brush fires near highly-industrialized
areas may create significant inputs of trace contaminants to
coastal ecosystems by remobilizing metals previously deposited on
land and foliage through aerial fallout. Trace metal quantities,
in ug, obtained over a 7-day interval in 3 post-fire fallout
samples from 0.075 m2 dishes were Ag 0.005, Cd 0.098, Cr 0.40,
Cu 4.0, Fe 300.0, Mn 5.8, Ni 0.78, Pb 12.0, and Zn 18.0.
HCMever, with the excepti on of iron, manganese and lead,
estimated inputs of metals to the coastal marine ecosystem via
this route during both fire and non-fire periods were one to two
orders of magnitude lower than the sutmarine discharge of
municipal wastewater.
2530.
Zafiropoulos, D. and A.P. Grimanis. 1977. Trace elements
in Acartia clausi from Elefsis fuy of the Upper
Saronikos Gulf, Greece. Marine Poll. Bull. 8:79-81.
The planktonic copepod ~ clausi is abundant in
polluted areas of the Mediterranean; therefore it may play an
important role in cycling and redistribution of trace elements in
this ecosystem and may also prove to be a useful trace element
indicator organisn. Mean concentrations, in mg/kg dry wt, of 12
trace elements found ln A. clausi from Elefsis Bay as determined
by neutron activation were: As 2.9, Cd 0.61, Co 0.28, Cr 3.2, Cu
55.3, Fe 738.0, Hg 0.29, Mn 9.3, Sb 0.31, Sc 0.04, Se 1.8, and Zn
1270.0. Most concentrations were higher in January/74 than in
February/74 probably owing to termination of active vertical
convection. Higher levels of Co, similar levels of Fe and
slightly decreased levels of Cr were recorded in A. clausi from
the fuy of RogLEbrune. Slightly decreased concentrations of Sb
and Zn as well as higher concentrations of As and Cd were fmmd
in other copepods.
2531 .
Zauke, G.-P. 1977. Mercury in benthic invertebrates of
the Elbe estuary. Helgol. wiss. Meeresunters.
29:358-374.
In general, mercury residues from benthic
invertebrates of the Elbe estuary were highest at llinnic sites
and lc:west at marine locations. Maximum Hg concentrations were
found in the crustacean Asellus aquaticus and gastropod Radix
balthica collected upstream from Hamburg, at 0.35 and 0.34 mg/kg
144
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wet wt, respectively. Concentrations in garmnarid crustacean
species decreased from 0.20 mg Hg/kg wet wt in the limnic region
to 0.02-0.05 in brackish and marine waters. Geographical
distribution of Hg in crustaceans was similar to that in the clay
fraction of sediments, which may reflect actwl Hg levels in this
ecooystem. Mercury levels in organisms from the brackish region
were: 0.08-0.16 mg/kg wet wt for the mollusc Littorina littorea;
0.04-0.09 for shrimp Crangon~; 0.05-0.10 for crustacean
Corophium volutator; and 0.04-0.0ff-for the annelid Nereis
ctiverSlCOlor. Other crustaceans, bivalves, polychaetes, and fish
were also analyzed for Hg. These concentrations were compared to
levels found in organisms from other areas. Factors which
influence heavy metal accumulations in aquatic organisms are
discussed, including food chain, weight of organism, and
elimination via molting in crustaceans.
2532.
Zavodnik, N. 1977. Note on the effects of lead on oxygen
production of several littoral seaweeds of the
Adriatic Sea. Botanica Marina XX:167-170.
The influence of lead, ranging from 0.1 to 1.0 mg/l,
on oxygen production of seaweeds was studied over 6 days in 37
0/00 S at 15 C. In Fucus virsoides, oxygen production was
slightly reduced from 0.41 to 0.31 ml 02/g/hr; and in Ulva
rigida, from 1.53 to 1.21 in light as Pb levels increased. Rates
generally decreased from day 1 to 6. Production rates in dark
gave lower, but similar, results. Padina pavonia and Laurencia
obtusa did not adapt to Pb exposure and smwed signs of decay
wIthin 3 days. Author concludes that Pb ioo concentrations in
the O. 1-1.0 mg/l range are belCM levels detectably toxic to the
investigated algae in short term tests.
2533.
Zitko, V. and W.G. Carson. 1977. Seasonal and
developmental variation in the lethality of zinc to
juvenile Atlantic salmon (~lmo salar). Jour. Fish.
Res. Ed. Canada 34: 139-141.
The incipient lethal level (ILL) of zinc to juvenile
Atlantic salmon in freshwater at a water hardness of 14 mg/l
varies from 150 to 1000 ug/l as a function of season and
developmental stage of the fish. The ILL increases from 500 to
1000 ug/l during the 1st yr and decreases to 150 ug/l in the
following spring. The more sensi ti ve stage in the salmon's 1 ife
history, evidenced by decrease of ILL, coincides with and is
probably related to initial stages of the parr-smolt trans-
145
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formation.
2534.
Zitko, v. 1976. Structure-activity relations and the
toxicity of trace elements to aquatic biota. In:
Andrew, R.W., P.V. Hodson, and D.E. Konasewich
(eds.). Toxicity to biota of metal forms in natural
wa ter . Grea t Lakes Res. Adv. Bd., Stand. Comm. Sc i.
Basis Water Qual. Criteria Inter. Jt. Comm. Res.
Advis. Bd. :9-32.
Toxicity of inorganic Cu, Pb, Cd, Zn, Be, Ni, Ca, Sr,
Mg, Mn, Co, Ba, Hg, Cd, As, Sb, Bi, V, Nb, Ta and other compounds
to aquatic life is influenced by intrinsic toxicity of the
element and availability to aquatic life as determined by
occurrence, complexation and other chemical reactions, and
adsorption. Glycine binding constants of metal cations may be
correlated to their toxicity, as shown with copepod, fish, and
mussel examples. Bicarbonate binding and competition for active
sites are suggested as mechanisms for the decrease of toxicity of
cations with increasing hardness of water. Analogous mechanisms
may control the effects of organic compounds on toxicity of
cations to aquatic biota.
2535.
Anderson, P.D. and L.J. Weber. 1976. The multiple
toxicity of certain heavy metals: additive actions
and interactions. In: Andrew, R.W., P.V. Hodson, and
D.E. Konasewich (ed~). Toxicity to biota of metal
forms in natural water. Great Lakes Res. Advis. Bd.,
Stand. Comm. Sci. Basis Water Qual. Criteria Inter.
Jt. Comm. Res. Adv. Bd.:263-282.
When aquatic organisms are exposed to several discrete
toxicants in receiving waters containing anthropogenic wastes,
there is the possibilty of interplay of toxic agents, either
kinetic (uptake, accumulation, elimination) or dYnaffiic (mode of
action). Mixtures of copper and nickel, alone and with other
chemical pollutants, exhibited strict additivity, or acted
similarly, on survival of mature male guppies Poecilia reticulata
over 96 hours. Mixtures of zinc and copper acted synergistically
on guppies; lethal potency increased 2.5X over predictions on
basis of strict additivity.
2536.
Andrew, R.W. 1976. Toxicity relationships to copper
forms in natural waters. In: Andrew, R.W., P.V.
146
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Hodson, and D.E. Konasewich (eds.). Toxicity to biota
of metal forms in natural water. Great Lakes Res.
Adv. Bd., Stand. Conm. Sci. Basis Water Qual. Criteria
Inter. Jt. Comm. Res. Adv. Bd.:127-143.
LC-50 (96 hr) values for fathead minnows increased to
25 mg Cu2+/l as total phosphate rose to 7.0 mg P/l. ~aphnia
magna survival time increased to 544 min in 4.0 mg Cu T/l as
added NaHC03 rose to 10 roM. Toxicit2 was directly related to
the ionic activity of cupri~ ion, Cu +, at a given pH. Author
suggests that increasing Cu + toxicity at high pH resulted from
interactions with sulfhydral-containing proteins or enzymes.
Biological reactivity, and thus toxicity to minnows, was limited
by bicarbonate alkalinity, pyrophosphate, or orthophosphate; Ca
and Mg had no effect. Copper complexes such as soluble CuC03
or Cu NTA's were much less toxic to aquatic organisms than cupric
ions. Precipitates of copper were rather biologically active or
toxic.
2537.
Bass, E.L. 1977. Influences of temperature and salinity
on oxygen consumption of tissues in the American
oyster (Crassostrea virginica). Compo Biochem.
Physiol. 58B:125-130.
Oxygen consumption in oysters acclimated to 10 0/00 S
rose to 1400 ul/hr per g in gill tissues over 21 days, higher
than in 20 or 30 0/00 S at 500-800 ul/hr per g. Oxygen
consumption of mantle tissues was also higher when acclimated to
10 0100 S, reaching 1000 ul/hr per g after 10 days. In 20 and 30
0/00 S, rate was fairly constant at 400 over 21 days. No
significant differnces were observed in muscle tissues of oysters
exposed to different salinities; consumption rate remained at
about 50 to 80 ul/hr per g.
2538.
Beasley, T.M., M. Heyraud2 J.J.W. Hif50' R.D. Cherry, and
S. W. Fc:wler. 1978. 10po and 2 Pb in
zooplankton fecal pellets. Marine Biology 44:325-328.
Mean concentrations of Po-210 and Pb-210 in fecal
pellets from zooplanktonic euphausiids, Meganyctiphanes
norvegica, collected between Monaco and Nice, France, were 49
dpm/gm dry wt for Po and 23 dpm/gm dry wt for Pb. The
Po-210:Pb-210 activity ratio of 2.2 is close to that found in
suspended particulate matter in surface seawater. Estimates of
Po-210 and Pb-210 removal times from mixed layers by fecal
147
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pellets alone are the same order of magnitude as removal times by
all routes. Authors suggest that zooplanktonic fecal pellets
playa significant role in removal of these nuclides from ocean
surface layers.
2539.
Bissonnette, P. 1977. Extent of mercury and lead uptake
from lake sediments by chironomids. In: Drucker, H.
and R. E. Wildung (eds.). Biological implications of
metals in the environment. ERDA Symp. Ser-
42:609-622. Avail. as CONF-750929 from Nat. Tech.
Inf. Serv., U.S. Dept. Comm., Springfield, VA 22161.
Average metal concentrations in sediments from four
lakes in western Washington were 0.48 mg Hg/kg dry wt and 24.7 mg
Pb/kg dry wt (A), 0.42 Hg and 17.6 Pb (B), 0.24 Hg and 13.6 Pb
(C), and 0.5 Hg and 11.7 Pb (D). Metal levels were higher in the
middle of the lakes than at peripheries, due to particle size.
Metal content in chironomid insects from the respective lakes
were 0.06 mg Hg/kg dry wt and 4.2 mg Pb/kg dry wt (A), 0.12 Hg
and 1. 7 Pb (B), o. 03 Hg ( C ), and o. 30 Hg and 2.3 Pb (D).
Concentration ratios of organism to sediment for all lakes ranged
from 0.55 to 37.5 for mercury and from 0.24 to 6.3 for lead.
Chiromid insect larvae, which constitute the bulk of the benthic
biomass and food source for fish, are potential links between
high sediment mercury and lead concentrations and predators.
Brown, L.M. and J.A. Hellebust. 1978. Ionic dependence
of deplasmolysis in the euryhaline diatom Cyclotella
cryptica. Canadian Jour. Botany 56:408-412.
Cells of ~. cryptica became plasmolyzed when subjected
to a sudden increase in extracellular osmotic pressure from 0.3
to 1.0 osmol/l. Protoplasts regained their original volume if
certain ions were present in the plasmolyzing solution. KCl was
the most important ion, being the only electrolyte a11CMing
deplasmolysis when supplied alone at 2000-8000 mg ~/l. Cells
did not deplasmolyze without KCl. Ca2+ at 440 mg/l, Mg2+ at
1340 mg/l, and Na+ at 11,500 mg/l were necessary for high rates
of deplasmolysis. Neither light nor ouabain had any effect on
deplasmolysis rate; 2,4-dinitrophenol acted as a reversible
inhibitor. Deplasmolysis appeared to be based on
energy-dependent uptake of KC1, which is affected by Na+ and
divalent cations.
2540.
148
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2541.
Brown, V.M. 1976. Aspects of heavy metals toxicity in
fresh waters. In: Andrew, R.W., P.V. Hodson, and
D.E. Konasewich-reds.). Toxicity to biota of metal
forms in natural water. Great Lakes Res. Adv. Bd.,
Stand. Conm. Sci. Basis Water Qu:d. Criteria Inter.
Jt. Camm. Res. Adv. Bd.:59-75.
Heavy metal contamination of waters, toxicity of heavy
metals to aquatic biota, and chemical states of metals in natural
waters is discussed. Man-induced rates of mobilization of metals
in fresh waters is 100X greater than geological rates for Sn, 30X
for Sb, 11-13X for Pb, Fe, Cu, and Zn, and 1-4X for Mo, Mn, Hg,
Ag, and Ni. Arsenic, Ba, Cd, Cr, Se, and V are also of
environmental concern. Water conditions and complexing of metals
effect biocidal properties of these elements. Median survival
period for fish in 0.05 mg Cull was < 300 min at pH 7.5 and 1000
min at pH 6.5. LC-50 (48 hr) varied from 0.004 mg Cull at pH 7.5
to 0.04 mg/l at pH 6.5. In hard water where Cd is present
exclusi vely as the ionic form, exposure to 0.001-0.002 mg Cd/l
for months affected reproduction of rainbow trout;
histopathological changes occurred at 0.008 mg Cd/I. Author
suggests that "acceptable" metal levels determined do not
consider possible indirect effects to biota or effects of mixture
of chemi cals .
2542.
Brungs, W.A., J.H. McCormick, T.W.
C. E. Stephan, and G. N. Stokes.
pollution on freshwater fish.
Control Feder. 49:1425-1493.
Neiheisel, R.L. Spehar,
1977. Effects of
Jour. Water Poll.
A literature reviEM of'pollution effects to freshwater
fishes, amphibians, echinoderms, molluscs, crustaceans, and
protozoa is presented for Am, As, Cd, Ca, Cs, Cr, Co, Cu, Fe, La,
Pb, Mg, Mn, Hg, Mo, Ni, Pu, K, Ra, Sc, Se, Ag, Na, Sr, U, Y, and
Zn. Water quality data, salinity, pesticides, and domestic,
industrial and radioactive pollutants are also discussed.
2543.
Castilla, J.C. and E. Nealler. 1978. Marine
environmental impact due to mining activities of El
Salvador copper mine, Chile. Marine Poll. Bull.
9: 67 -70.
Untreated mining wastes discharged from the El
Sal vador copper mine directly onto the Chilean shore at Caleta
Palito have hindered harbor activities, caused geomorphological
coastal modifications, and affected marine coastal ecosystems and
149
-------
recreational activities. Tailing discharges are accumulating at
25,000 tons of fine sediment daily, plus unknown quantities of
copper, arsenic, and cyanide. From Jan. 1975 to July 1976, this
site received over 13 million tons of sediments. Massive fish
and shellfish mortalities were reported in Feb. 1975, a few days
after initiation of discharging. In July 1975 and July 1976,
massi ve mortality was detected in i nterti dal and s ubti dal areas.
Species affected were starfish Stichaster striatus, limpets
Collisella spp., Fisurella spp., sea urchin Tetrapigus niger,
crabs Hemigrapsus crenulatus, Homolaspis plana, barnacle
Concholepas concholepas, and fishes Sicyases sanguineus, Aphos
porosus, as well as several species of algae. A variety of
invertebrates and fishes not found at Caleta Palito were present
at Pan de Azucar about 25 krn away.
2544.
Caviglia, A. and F. Cugurra. 1978. Further studies on
the mercury contents in some species of marine fish
and molluscs. Bull. Environ. Contamin. Toxicol.
19:528-537.
Mercury levels were determined in 53 species of marine
fish and molluscs from the Ligurian Sea, Italy, in 1974 and
1975. Samples of 11 species, Aristeomorpha foliacea, Arnoglossus
sp., Eledone sp., Etmospterus spinax, Gaidropsarus sp., Maena
maena, Noephrops norvegicus, Pagrus pagrus, Penaeus keraturus,
Serranus cabrilla, and Trachurus sp., contained maximum levels of
0.73 to 2.50 mg Hg/kg wet wt, or levels that were in excess of
the legal admissable tolerance limit in Italy of 0.7 mg/kg wet
wt. In 7 other species, Conger conger, Octopus vulgaris, Scomber
scombrus, Scyllarus sp., Serranus scriba, $olea vulgaris, and
Sphyrema sphyrema, maximum total mercury content of 0.51 to 0.7
mg Hg/kg was determined. This is in excess of the 0.5 mg/kg wet
wt limit imposed in the USA, Canada, and other countries. Mean
mercury concentrations in the remaining species of fish and
molluscs ranged from 0.02 to 0.46 mg Hg/kg wet wt. Possible
sources of mercury pollution in Liguria are noted.
2545.
Chynoweth, D.P., J.A. Black, and K.H. Maney. 1976.
Effects of organic pollutants 00 copper toxicity to
fish. In: Andrew, R.W., P.V. Hodson, and D.E.
Konasewich (eds.). Toxicity to biota of metal forms
in natural water. Great Lakes Res. Adv. Bd., Stand.
Conm. Sci. Basis Water Qual. Criteria Inter. Jt. Cormn.
Res. Adv. Bd.:145-157.
150
-------
Mortality of guppies Lebistes reticulatus after 96 hr
expcsure to copper was 76-88% in 0.170-0.175 mg Cull, 85-100% in
0.192-0.216 mg Cull, and 83-100% in 0.232-0.235 mg Cull.
Relative toxicity of copper to guppies decreased in 36 x 10-6M
NTA, EDTA, and glycine and in 5.0 mgll total organic matter of
humic acid; LC-50 (96 hr) values ranged from 0.183 to 0.224 mg
Cull canpared to controls of O. 112-0. 138 mgll. Egg albumin and
sewage effluent at 5.0 mg organic matter/l increased toxicity
with LC-50 (96 hr) values of 0.102 and 0.099 mg Cull,
respecti vely, while 36 x 10-6M cysteine had no effect. An
inverse relationship was observed between degree or copper
binding and Cu toxicity. Organic binding and toxicity was not
correlated to Cu uptake by fish.
2546.
Conway, H.L. 1978. Sorption of arsenic and cadmium and
their effects 00 growth, micronutrient utilization,
and photosynt}~tic pigment composition of Asterionella
formosa. Jour. Fish. Res. Ed. Canada 35:286-294.
Sorption of arsenic by freshwater diatom poPula~~ons
eXQosed for up to 22 days, rose linearly to 0.035 mg As/10
um3 as As concentration increased to 0.13 mg/l, then
plateaued. Cadmium sorption was a function of ambient levels and
time; ~ximum bioaccurnulation rate was 17,000, with 0.34 mg
Cd/101 urn3 during irmnersion in 19.6 mg Cd/l for 2 days.
Cellular As and Cd were desorbed in sane cases, and there
appeared to be an active regulatory mechanism keeping As at a
non-toxic level. No detrimental effects on growth, or nitrate,
phosphate, and silicate utilization were observed in all
experimental As levels up to 0.16 mg/l. Ambient concentrations
of 0.002 mg Cd/l, however, reduced population growth rate by an
order of magnitude; populations exposed to >0.01 mg Cd/l ceased
growth and micronutrient utilization in 20-30 hrs. By follooing
radio-labelled metals, cellular As was found to associate with
the organic layer surrounding the frustule, while Cd associated
with cell contents.
2547.
Cross, F.A., J.N. Willis, L.H. Hardy, N.Y. Jones, and J.M.
Lewis. 1975. Role of juvenile fish in cycling of Mn,
Fe, Cu, and Zn in a coastal-plain estuary. In:
Cronin, L. E. (ed.). Estuarine Research, vol-:-1.
Chemistry, biology, and the estuarine system.
Academic Press, Inc., N.Y.: 45-63.
Daily flux of manganese, iron, copper and zinc was
151
-------
estimated for fish during summer months in the Newport River
estuary, North Carolina, from the equation I = A + E. Ingestion
rate of metal (I) was determined by rate of food consumption
multiplied by metal concentration in stomach contents.
Assimilation rate (A) was the sum of increase rate of metal body
burda1 and rate of metal loss in biological turnover. Egestion
rate of unassimilated metal (E) was estimated by subtracting (A)
from (I). Mean concentration levels found in juvenile fish
stomach contents were: 110 mg Zn/kg dry wt, 22,000 mg Fe/kg, 270
mg Mn/kg, and 25 mg Culkg for menhaden Brevoortia tyrannus; 620
mg Zn/kg dry wt, 26,000 Fe, 520 Mn, and 92 Cu for spot
Leiosotomus xanthurus; and 75 mg Zn/kg dry wt, 5200 Fe, 55 Mn,
and 13 Cu for pinfish Lagodon rhomboides. Flux of Zn in fish
showed an assimilatioo efficiency of 36% in menhaden which
accumulated 1.67 ug/day in tissues, 2!0 efficiency in spot which
accumulated 0.6 ug/day, and 19% efficiency in pinfish which
accumulated 0.58 ug/day. Assimilation efficiency of Fe was 1% in
menhaden, 0.3% in spot, and 0.6% in pinfish; respective tissue
accumulation was 10.0, 3.6, and 1.5 ug/day. Mn assimilation
efficiency was 3.0% in menhaden, 0.7% in spot, and 7.0% in
pinfish, with tissue accumulations of 0.28, 0.19, and 0.17
ug/day, respectively. Cu assimilatioo efficiency was 9.0% in
menhaden, 1.0% in spot, and 2.9% in pinfish; accumulation was
0.09, 0.05, and 0.04 ug/day, respectively. Flux of metals in the
estrnry through whole juvenile populations of each species was
also calculated.
2548.
Davey, E.W. 1976. Potential roles of metal-ligands in
the marine environment. In: Andrew, R.W., P. V.
Hodson, and D.E. Konasewich (eds.). Toxicity to biota
of metal forms in natural water. Great Lakes Res.
Adv. Bd., Stand. Canm. Sci. Basis Water Qrnl. Criteria
Inter. Jt. Comm. Res. Adv. Bd.:197-209.
Population growth of the marine diatom Thalassiosira
pseudonana from 2500 to 40,000 cells/ml over 45 days in controls
was reduced to 7500 cells/ml over 45 days as copper concentration
rose to 0.01 mg/l. In 0.02 to 0.05 mg Cull, population size
increased to only 3500 to 4500 cells/ml. T. pseudonana
populations exposed to 0.01 mg Cull ~one decreased to 5-15% of
control numbers. Addition of 1 x 10- M EDTA slightly increased
diatom tolerance. In 5 x 10-7M EDTA or 5.5 x 10:::'JM
histidine, diatom population size stayed within 90% of controls
in 0.02 mg Cull; size declined to 15% in 0.05 mg Cull. T.
pseudonana tolerated copper exposure better in relati vely
unpolluted seawater than water from a polluted industrial area.
152
-------
Author ooncluded that it is not necessarily total metal amounts
present, but the form of metal, that determines its biological
action.
2549.
Davies, P.H. 1976. The need to establish heavy metal
standards on the basis of dissolved metals. In:
Andrew, R. W., P. V. Hodson, and D. E. Konasewich
(eds.). Toxicity to biota of metal forms in natural
water. Great Lakes Res. Adv. BeL, Stand. Canm. Sci.
Basis Water Qual. Criteria Inter. Jt. Conm. Res. Adv.
Bd. :93-126.
In water with hardness of 385 mg/l as CaC03 at 14 C,
all rainbow trout died when exposed to 5.29 and 6.54 mg Pb/l for
4 days. In 0.79 mg Fb/l 30% died, but no mortality was observed
in 0.48 mgll. In hard water with 290 mg CaC03/l at
7 C, all trout were killed in 2.85 to 7.56 mg Pb/l over 4 days,
30% died in 1.30 mg Fb/l, and none died in 0.25 mg/l. In soft
water with 32 mg CaC03/l at 10 C, 85% of the trout died in 1.60
mg Pb/l over 4 days, 5% died in 0.43 and 0.78 mg Pb/l, and all
survi ved in 0.13 and 0.22 mg/l. LC-50 (96 hr) values for trout
in hard water were 471 mgll total Pb or 1.47 mgll dissolved Pb;
in soft water, this was 1.17 mg/l total (or dissolved) Pb.
Concentrations of 0.12-0.36 mg total Pb/l or 0.02-0.03 mg
dissolved Pb/l in hard water, and 0.007-0.015 mg Fb/l in soft
water were not fatal. The LC-50 (96 hr) cadmiun concentration
was 1.75 ug/l in soft water. No effect was seen in 0.7-1.5 ug
Cd/l in soft water or 13.5-21.0 ug Cd/l in hard water. After one
year exposure to silver, 38% mortality of trout was observed
after "swim-up" in 0.50 ug Agll, 24.5% in 0.32 ug/l, 19% in 0.18
ug/l, and 3% in 0.13 ug/l. Use of dialysis tubing and filtration
to distinguish dissolved and complexed metal forms, and effects
of pH on metal speciation are discussed.
2550.
Eaton, J.G., J.M. McKim, and G.W. Holcombe. 1978. Metal
toxicity to embryos and larvae of seven freshwater
fish species-I. cadmium. Bull. Environ. Contamin.
Toxiool. 19:95-103.
Minimum cadmium concentrations at which fish standing
crop was significantly lower than controls were determined. For
each species, exposure to Cd was up to 10 days as embryos and 27
to 33 days as larvae-juveniles. Deleterious cadmium
ooncentrations were 11.2 to 12.9 ug Cd/l for white sucker
Catostomus commersoni, northern pike Esox lucius, smallmouth bass
153
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Micropterus dolomieui, lake trout Salvelinus namaycush, and late
eyed embryo of brown trout Salmo trutta. A concentration of 3.4
ug Cd/I was deleterious to Lake Superior coho salmon Oncorhynchus
kisutch. Mortality in lake trout exposed for 64 days as larvae
was not different than that for shorter exposure; however, lethal
concentration dropped to 3.7 ug/l in late brown trout embryos
exposed for 61 days. Populations of coho salmon decreased in
12.5 ug Cd/l when exposed for 20 days as embryos and 27 or 62
days as larvae. For brook trout Salvelinus fontinalis exposed
for 24 days as embryos and 31, 65, or 126 days as larvae these
values were 0.5 to 11.7 ug Cd/l. In brown trout exposed for 50
days as embryos and 33 or 60 days as larvae this value was 11. 7
ug Cd/l. Larvae or juveniles were more sensi ti ve than embryos in
all cases.
2551 .
Fletcher, P.E. and G.L. Fletcher. 1978. The binding of
zinc to tre plasna of winter t1.ounder
(Pseudopleuronectes americanus): affinity and
specificity. Canadian Jour. Zoology 56:114-120.
Tre binding affinity of winter flounder plasma
proteins for zinc was ~etermined by equilibrium dialysis.
Percentage of bound Zn + dropped sharply from 100 to 35% as
total zinc present rose to 200 ug/l. A Rosenthal type plot
indicated m0+re tgan one binding site for zinc. The association
constant, 10 -10 , was similar to that of mannnalian serum
albumin. It required twice the nonnal total plagna zinc
concentration to saturate the higher affinity binding system.
Al~ plagna Zn was removed by dialyzing with 0.01 M histidine.
Cu + competed significantly with Zn binding to p~asma;
competition was diminished with Tris buffer. Cd +, Ca2+,
Co2+, Cr2+, Fe2+, Hg2+, Mg2+, Mn2+, and Ni2+ had no
effect on binding of Zn2+ to the plasma. EDTA had a greater
effect on Zn binding than predicted from its theoretical binding
capaci ty for zinc. Percentage of Zn-65 bound to plasma was only
33.6% with 0.0048 uMol EDTA, compared to 99.7% without EDTA.
2552.
Fletcher, G.L. and M.J. King. 1978. Seasonal dynamics of
Cu2+, Zn2+, Ca2+, and M~+ in gonads and Ii ver
of winter t1.ounder (PseudoPleuron~ctes americanus):
evidence for surrmer storage of Zn + for winter gonad
development in females. Canadian Jour. Zoology
56:284-290.
Male and female gonads of winter flounder initiated
development in August and spawned in June. Maximum testes weight
154
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was observed in October, corresponding to the end of experimental
feeding period. Maximum ovary weight was not observed \IDtil
February, indicating that ovarian growth occurred after feeding
ceased. Zinc, Cu, Ca and Mg exhibited seasonal variations in
gonads and livers. Total im accumulation of zinc reached 6.0
mglkg body wt in ovaries in Feb. and 2.0 mg/kg in testes in Nov.;
copper reached 0.15 mg/kg body wt in ovaries in March and 0.03
mglkg in testes in Nov.; and calcium reached 11. 0 mg/kg body wt
in ovaries in Mar. and 5.0 mg/kg in testes in Nov. Testes
accumulated more Mg th3.n ovaries: 0.024 mg/kg body wt in male
gonads in Dec. and 0.021 mg/kg in females in April. Ovaries
continued to incorporate all four elements after flounder ceased
eating;2levels i~ liver decreased from winter months to April.
Same Zn + and Cu + requirements could have been met by
utilizing liver stores, although most Zn was probably obtained
from other storage ~eas. The sour~e of the ovaries postfeeding
requirements for Ca +, Cu2+, and Mg + could have been metal
absorption from seawater by fiounder.
2553.
Fox, F.R. and K.R. Rao. 1978. Characteristics of a
Ca2+-activated ATPase from the hepatopancreas of the
blue crab, Callinectes sapidus. Camp. Biochem.
Physiol. 59B:327-331.
Calcium-activated ATPase from crab hepatopancreas
required 800 mg Call for maximal activity of 0.35 umoles Pirog
protein/min. Magnesium, at up to 240 mg/l, was less effective in
activating ATPase; barium was also a relatively poor activator.
T~ maximal activity evoked by strontium alone was greater than
Ca +. Potassium was not required for activation. Enzyme
acti vity due to 95 mg Mgll alone was significantly lower than
that produced by 800 mg Ca2+/l alone, ~ut mixtures of 1370 mg
Ba2+/l and 800 mg Ca2+/l, or 875 mg Sr +/1 and 800 mg
Ca2+/l were associated with elevated values. Combinations of
Ca with K, Na, or Mg produced no significant difference in
act~ vi ty. 1he Km of the Ca-acti vated enzyme for ATP was 4. 1 x
10- M. Maximal activity was noted at 45-50 C and pH 7.5.
2554.
Friedman, M.A., L.R. Eaton, and W.H. Carter. 1978.
Protective effects of freeze dried swordfish on
methylmercury chloride toxicity in rats. Bull.
Environ. Contamin. Toxicol. 19:436-443.
155
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Average body weight in rats fed a 15% casein or 15%
freeze dried swordfish diet for 10 days was 350-375 gms; with 20
mg/kg methyl HgCl added to each diet, body weight was 200-225
gms. In another st udy, all 10 rats di ed between 2 and 5 weeks
when fed 40 mg Hg/kg with either diet. Five rats died between 7
and 10 wks when fed 15% casein and 20 mg Hg/kg; only 2 died with
15% swordfish and 20 mg Hg/kg. Neurotoxic behavior appeared in
all rats fed 40 mg Hg/kg after 6 wks; effects were observed
first in animals eating casein rather than swordfish. Ten
percent showed toxic effects by 10 wks with 20 mg Hg/kg and
casein, but not with swordfish. Freeze dried swordfish
protected rats from methyJmercury. Swordfish contained 0.30 to
1.67 mg Hg/kg and 0.79 to 4.84 mg Se/kg; Hg content paralleled
fish size but did not correlate to solid content. Selenium was
assumed to be the protective agent against Hg, although protein
and caloric content also differed between the two diets.
2555.
Gre, ichus Y.A., A. Greichus, B.D. Ammann, and J.
Hopcraft. 1978. Insecticides, polychlorinated
biphenyls, and metals in African lake ecosystems.
III. Lake Nakuru, Kenya. Bull. Environ. Contamin.
Toxicol. 19:454-461.
Average metal concentrations in water column (mg/l)
and bottom sediments (mg/kg dry wt) of Lake Nakuru, Africa, were
0.006 and 35.0 for arsenic, 0.021 and 0.27 for cadmJum, 0.002
and 6.2 for copper, 0.024 and 550.0 for manganese, 0.005 and
34.0 for lead, 0.049 and 140.0 for zinc, and < 0.001 and 0.26 for
mercury. Among organisms collected from the lake, arsenic
concentrations of 7.5 mg/kg dry wt were determined for
chironomid insects, 0.14 in other aquatic insects, and 1. 80 in
fish; cadmium at 0.19 mg/kg dry wt, 0.45, and 0.26,
respectively; copper at 4.6 mg/kg dry wt, 11.0, and 10.0,
respectively; manganese at 78.0 mg/kg dry wt, 12.0, and 19.0,
respectively; lead at 1.3 mg/kg dry wt, 0.82, and 0.84,
respectively; zinc at 61.0 mg/kg dry wt, 70.0 and 110.0,
respectively; and mercury at 0.26 mg/kg dry wt, 0.16, and 0.22
in respective groups. Cadmium levels were higher than reported
for other African lakes. Insecticide and polychlorinated
biphenyl concentrations are also listed.
2556.
Greichus, Y.A., A. Greichus, H.A. Draayer, and B.
Marshall. 1978. Insecticides, polychlorinated
biphenyls and metals in African lake ecosystems.
II. Lake McIlwaine, Rhodesia. Bull. Environ.
156
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Contanlin. Toxicol. 19:444-453.
Average metal concentrations in Lake McIlvaine Itlere:
As 0.003 mg/l and 37.0 mg/kg dry wt in bottom sediment, Cd 0.001
mg/l and 0.39 mg/kg sediment, Cu 0.010 mg/l and 38.0 mg/kg
sediment, Mn 0.032 mg/l and 350.0 mg/kg, Pb 0.010 mg/l and 41.0
mg/kg, Zn 0.012 mg/l and 100.0 !;!1g/kg, and Hg < 0.001 mg/l and
0.28 mg/kg sediment. Organisms from the lake contained arsenic
at 2.9 mg/kg dry wt in plankton, 6.0 in oligochaetes, 1.3 in
benthic insects, and 1. 4 in fish; cadmi urn at 1. 5 mg/kg dry wt,
0.05, 0.08, and 0.12, respectively; manganese at 220 mg/kg dry
wt, 28.0, 8.8, and 27.0, respectively; lead at 78.0 mg/kg dry
wt, 1.3, 0.91, and 0.84, respectivelYi zinc at 190 mg/kg dry wt,
130, 78, and 48 in respective organisms; mercury at 0.26 mg/kg
dry wt in plankton, 0.08 in oligochaetes, and 0.23 in fish; and
copper at 7.2 mg/kg dry wt in oligochaetes, 10.0 in benthic
insects, and 5.4 in fish. Average concentrations in cormorants
from Lake McIlwaine were 1. 4 mg/kg dry wt in carcass, 0.94 in
brai.n, and 1.2 in feathers for As; 0.04, 0.10, and 0.38,
respectively, for Cd; 3.1, 9.0, and 8.7 for CUi 4.9, 1.6, and
21.0 for Mn; 2.7, 1.3, and 2.4 for Pb; 77, 33, and 180 for Zn,
and 2.8, 1.3 and 0.65 in respective tissues for Hg. Levels of
polychlorinated biphenyls and insecticides in Lake McIlwaine and
its organisrns are also listed.
2557.
Greig, R.A., D.R. Wenzloff, C.L. MacKenzie, Jr., A.S.
Merrill, and V.S. Zdanowicz. 1978. Trace metals in
sea scallops, Placopecten magellanicus, from eastern
United States. Bull. Environ. Contamin. Toxicol.
19:326-334.
Metal concentrations in sea scallops collected from
42 stations in the North Atlantic between Cape Hatteras and
George's Bank were: <0.08 to 0.24 mg Ag/kg wet wt in muscle,
0.13 to 0.69 Ag in gonads, and 0.22 to 1.9 Ag in visceral
mass; <0.06 to 0.12 mg Cd/kg wet wt in muscle, 0.47 to 3.2 in
gonads, and 3.7 to 27.0 in visceral mass; < 0.26 to 0.64 mg
Cr/kg wet wt in muscle, < 0.29 to 1.7 in gonads, and 0.37 to 4.0
in visceral mass; 0.27 to 1.1 mg Cu/kg wet wt in muscle, 1.1 to
10.6 in gonads, and 1.3 to 5.6 in visceral massj<0.08 to 0.18 mg
Hg/kg wet wt in all tissues; <0.26 to 0.68 mg Nilkg wet wt in
muscle, 0.23 to 2.5 in gonads, and 0.31 to 1.6 in visceral
mass; < 0.4 to 1. 7 mg Pb/kg wet wt in muscle, < 0.44 to 1. 5 in
gonads, and 0.45 to 1.6 in visceral mass; and 2.0 to 8.1 mg
ZnI kg wet wt in muscle, 4. 7 to 75.4 in gonads, and 7. 4 to 22. 5
in visceral mass. Most metals, except Zn, were bela,.] detection
157
-------
limits in muscle. Silver, Cd, Cu, and Zn were generally
detectable in gonads; females had higher concentrations of Cu
and Zn than males. Only Hg and Pb were belcw detection in
muscle and most concentrations were similar to gonadal levels.
2558.
Hamanaka, T., H. Kato, and T. Tsujita. 1977. Cadmium
and zinc in ribbon seal, Histriophoca fasciata, in
the Okhotsk Sea. Res. Inst. N. Pac. Fish., Hokkaido
Univ., Spec. Vol.:547-561.
Ribbon seals Histriophoca fasciata, harbor seals
Phoca vitulina largha, and ringed seals Pusa hispida, collected
off Sakhalin Island, Japan, in 1975, contained 0.31 to 1.10 mg
Cd/kg dry wt and 34.0 to 171.0 mg Zn/kg dry wt in muscle; 1.37
to 11.0 and 111 to 264, respectively, in liver; 1.57 to 6.69 and
43 to 124, respectively, in spleen; 0.91 to 6.33 and 81 to 106,
respectively, in pancreas; 0.35 to 3.59 and 47 to 176,
respectively, in stanach wall; and 0.14 to 0.19 and 1.8,
respectively, in fat. Male and female ribbon seals showed no
significant differences in metal content of muscle. Maximum
cadmium and zinc levels occurred in ribbon seal liver; high
pancreas Cd content suggests this organ is important for metal
storage along with kidney and liver. Cadmium in harbor seals
was lower than ribbon seals, partially due to their diet of fish
rather than squid (which have high liver Cd). Pacific cod,
Gadus macrocephalus, contained 0.14 mg Cd/kg dry wt in muscle
and 0.17 in liver; and 6.5 mg Zn/kg in muscle, 79 in gonad, and
18 in liver. Squid, Ommastrephes bartrami, contained 0.72 mg
Cd/kg dry wt in muscle, 0.35 in gonads, and 80.6-85.5 in muscle;
and 54 mg Zn/kg in muscle, 73 in gonads, and 115-124 in liver.
2559 .
Hamdy, M.K. and N. V. Prabhu. 1978. Behavior of mercury
in bio-systems. II. depuration of 203Hg2+ in
various trophic levels. Bull. Environ. Contamin.
Toxicol. 19:365-373.
Effects of temperature and form of Hg-203 ion on
depuration of mercury by bacteria Bacillus licheniformis,
mosquito Aedes aegypti larvae, and guppies Lebistes reticulatus
were investigated. Rate of biological elimination (k) of
organic C6~Hg-203OCCH3 by bacteria at 4 C was -0.24/day
and of inorganic Hg-203(N03)2 was -0.44/day. At 23 C, 37 C,
and 45 C, elimination rate increased to between -0.09 and
-0.23/day for organic Hg and -0.23 and -0.26/day for inorganic
Hg. Biological half-life of Hg-203 ion in bacteria generally
158
-------
Hg-203 ion in bacteria generally decreased with rising
temperature from 11.8 to 4.5 days for organic and from 22.3 to
17.8 days for inorganic Hg. Elimination rate of organic Hg-203
in mosquito larvae at 27 C was -0.221 day; k was rapi d at
--O.08/day for inorganic Hg-203. Half-lives were 11.2 days
organic and 4. 1 days inorganic Hg. In guppies at 23 C, k was
-0. 14/day for organic and -0. 13/day for inorganic Hg; respective
half-lives were 7.2 days and 6.5 days. fucteria cells washed
with water retained 35% organic and 25% inorganic Hg-203 after 5
rinses. After 5 washes with 0.05 Na phosphate buffer, retention
was 50% organic and 55% inorganic Hg-203.
2560.
Hartung, R. 1976. Pharmacokinetic approaches to the
evaluation of methylmercury in fish. In: Andrew,
R. W., P. V. Hodson, and D. E. Konasewich ---reds.) .
Toxicity to biota of metal forms in natural water.
Great Lakes Res. Adv. Ed., Stand. Canm. Sci. fusis
Water Qual. Criteria Inter. Jt. COIJIn. Res. Adv.
Bd. :233-248.
Mathematical models were appplied to describe uptake,
distribution, storage, and elimination kinetics of mercury in
several species of freshwater fishes using previous laboratory
and field studies. Uptake differences between species were not
significant. Temperature effects, possibly due to metabolic
rate, were pronounced and systematic. Author suggests that
bioaccumulation experiments may be more precise and their
duration shortened under certain conditions, and that
comparisons between experimental and monitoring data may be
improved.
2561.
Hendricks, A.C. 1978. Response of Selenastrum
capricornutum to zinc sulfideso Jour. Water Poll.
Control Feder. 50:163-168.
Oxygen production by algae, S. capricornutum, was
decreased by 50% after 4 hr expos ure to -1 . 0 mg Zn/l and to 2. 5
mg/l of sulfide. In 1.5 and 2.5 mg Znll, oxygen production was
only 10% compared to controls, while production was 75 to 115%
in 0.75 mg Znll. When Zn and S were added at a 2: 1 ratio,
oxygen production was near control rates even with 5.0 mg Zn/l
and 2.5 mg Silo Lowest production rates were obtained at the
extreme ratios of 1:2 or 5:1 Zn to S. Results show zinc and
sulfide act antagonistically to reduce their toxic effects.
159
-------
2562.
Herricks, E. E. 1977. Effects of pollution on freshwater
invertebrates. Jour. Water Poll. Control Feder.
49: 1493-1506.
Studies of effects of metals and various chemicals
lli1d oils to freshwater bacteria, protozoans, sponges,
coelenterates, rotifers, platyhelminthids, annelids, molluscs,
crustaceans, insects, fishes, and birds are reviewed. Toxicity,
bioaccumulatian, and community effects are discussed for silver,
cadmium, cobalt, chromium, copper, iron, mercury, potassium,
sodium, nickel, lead, ruthenium, and zinc.
2563.
Hildebrand, S.G., A.W. Andren, and J.W. Huckabee. 1976.
Distribution and bioaccumulation of mercury in biotic
and abiotic compartments of a contaITdnated
river-reservoir system. In: Andrew, R.W., P.V.
Hodson, and D.E. Konasewich (eds.). Toxicity to
biota of metal forms in natural water. Great Lakes
Res. Adv. Bd., Stand. Conm. Sci. Basis Water Qual.
Criteria Inter. Jt. Comm. Res. Adv. Bd.:211-232.
Dissolved mercury appeared to be leaching from waste
ponds at an abandoned chlor-alkali plant on the Holston River in
Tennessee during 1973 and 1974. Water above the plant contained
0.036-0.048 ug/l total mercury and 0.013-0.016 ug/l dissolved
mercury. M3.ximum values of Hg were found at the waste ponds
with 0.203 ug/l total and 0.174 ug/l dissolved. Mercury levels
120 km downstream were similar to those above the plant. In
sediments, 20.7 mg total Hg/kg was found at the pond, compared
to 0.24-0.32 upstream. Sediment Hg levels generally remained
< 1.0 mg/kg for 250 km belCM the plant. Methylmercury was not
detected in sediment. Total mercury in axial muscle of fishes
Ambloplites rupestris, Hypentelium nigricans and Notropis spp.
was 0.28-0.70 mg/kg wet wt above the plant, 1.42-1.70 mg/kg at
the pond, and 0.43-1.26 mg/kg 135 km downstream; >78% was as
methylmercury at all locations. A composite of benthic
invertebrate taxa, primarily insects and crustaceans, contained
an average of 0.05 mg Hg/kg wet wt in whole animals upstream
from the plant, 1.55 mg/kg at the pond, 0.79 mg/kg 20 km
downstream and 0.20 mg/kg 135 km bela-l the plant. Methylmercury
accounted for 44.7-56.5% of the total Hg body burden. Dietary
uptake by fish feeding 00 benthic invertebrates is considered an
important route far methylmercury.
2564.
Hoppenheit, M.
1977 -
On the dynamics of exploited
160
-------
populations of Tisbe holothuriae (Copepoda,
Harpacticoid3.). V. the toxicity of cadmium:
response to sub-lethal e»''P0sure. Helgol. wiss.
Meeresunters. 29:503-523.
Populations ~f copepods, T. holothuriae, were exposed
to 0.148 or 0.222 mg Cd +/1, combined with weekly exploitation
rates of 10, 30, 50, 70, or 90% over 70 weeks. Cadmium addition
prolooged and reinforced downward trends of the normal U-shaped
density patterns. Age structures shifted more toward nauplii as
population densities fell below a certain value; more pronounced
reductions did not increase the naupl~i fraction. Within 23
weeks (20 generations), effects of Cd + on copepod densities
were counteracted by metal acclimation. No relationship was
seen between exploitation rate and population density. Possible
limi tations of the significance of results and revisions on the
adaptabili ty of parametric methods on dispersioo of data are
discussed.
2565.
Ishii, T., H. Suzuki, and T. Koyanagi. 1978.
Determinaticn of trace elements in marine organisms -
I factors for variation of concentration of trace
element. Bull. Japan. Soc. Sci. Fish. 44:155-162.
(In Japanese).
Mar ine fishes from the Japanese coast showed only
snail variations in metal concentrations; however, invertebrates
and algae smwed marked species specificity. The teleosts
Paralichthy~ olivaceous, Argyrosomus argentatus, Hexagrammos
otakii, Sebastes thompsoni, ~. nivosus, Lateolabrax japonicus,
Seriola quinqueradiata, and Evynnis japonica contained metal
concentrations, in mg/kg dry wt muscle, of 0.31 to 0.79 for Mn,
6.1 to 23.0 Fe, 0.007 to 0.022 Co, 0.31 to 0.55 Ni, 0.51 to 1.61
Cu, 16.0 to 39.0 211,2.4 to 4.0 Rb, and 0.06 to 0.16 Cs. Copper
and Zn showed regional variation. Among invertebrates, soft
parts of the mussel Mytilus corscum contained maximum
concentrations of Mn at 7.7 mg/kg dry wt, Fe at 150.0, and 211 at
160.0; clam Gomphina melanaegis contained maximum Co at 0.70
mg/kg dry wt, Ni at 3.2, and Rb at 5.2; squid Sepia esculenta
contained maximum Cu at 35.0 mg/kg dry wt; and prawn Penaeus
japonica contained maximum Cs at 0.046 mg/kg dry wt. The
stamatoPod Squilla oratoria, clam Meretrix lamarckii, and snail
Notohaliotis discus were also analyzed. Maximum metal
concentrations, in mg/kg dry wt, in marine algae were 6.9 for
Ni, 14.0 for Cu, and 170.0 for Zn in Chodrus ocellatus; 41.0 for
Mn and 0.07 for Cs in Sargassum thunbergi; 590.0 for Fe in
161
-------
Sargassurn thunbergi; 590.0 for Fe in Ulva pertusa; 52.0 for Rb
in Hizikia fusiforme; and 0.43 for Co in Sargassurn
kjellmanianurn. Also analyzed were Enteromorpha sp., Ahnfel tia
paradoxa, Undaria pinnatifida, Eisenia bicyclis, Sargassurn
sagamianurn, ~ ringgoldianurn, and ~ horneri. For most metals,
concentrations in algae increased with distance fran the growing
tip; this was especially pronounced for Fe. Iron levels tended
to decrease with increasing growth of algae but other metals
varied little. Seasonal variations showed maximum Fe, Co, and
Zn concentrations in March in Sargassurn. Iv1aximum concentration
factors for marine organisms were 9000 for Mn, 10,000 for Fe,
and 40 for Rb in Sargassurn; 4000 for Co, 100 for Ni, 4000 for
Cu, and 4000 for Zn in shellfish; and 70 for Cs in fish muscle.
2566.
Kari, T. and P. Kauranen. 1978. Mercury and sel eni um
contents of seals from fresh and brackish water in
Finland. Bull. Environ. Contamin. Toxicol.
19:273-280.
Mercury and selenium concentrations in seal Phoca
hispida muscle caught in 1974 and 1975 from Bothnian Bay in the
Baltic Sea were 0.47-1.16 mg Hg/kg wet wt and 0.44-0.92 mg Se/kg
wet wt; 14-300 for Hg and 6.1-110.0 for Se in liver, and 2.8-5.2
for Hg and 2.5-3.3 for Se in kidney. In P. h. saimensis from
Lake Saimaa, Finland, metal concentrationS were 1.3-6.1 mg Hg/kg
wet wt and 0.24-2.8 mg Se/kg wet wt in muscle, 72-210 for Hg and
29-170 for Se in liver, 1.9-13 for Hg and 0.34-3.0 for Se in
kidney, and 0.14-0.46 for Hg and 0.06-0.11 for Se in blubber.
Correlation coefficients between Hg and Se tissue contents were
high in liver of all seals, but levels in kidney, flesh, and
muscle were not strongly correlated. Baltic herring, pike,
vendace, and whitefish, all potential food sources for seals in
Bothnian Bay, contained 0.09-0.23 mg Hg/kg wet wt and 0.24-0.50
mg Se/kg wet wt in muscle; burbot from a Hg-polluted area
contai ned 1. 0 mg Hg/ kg and O. 21 mg Se/ kg . Metal contents in
roach, perch, and vendace from Saimaa were O. 12-0.26 mg Hg/kg
and 0.29-0.43 mg Se/kg in muscle and 0.07-0.22 for Hg and
0.37-0.50 for Se in whole fish.
2567.
Kayser, H. 1977. Effect of zinc sulphate on the growth
of mono- and multispecies cultures of sane marine
plankton algae. Helgol. wiss. Meeresunters.
30: 682-696.
Effects of up to 5 mg/l zinc sulphate on multipli-
162
-------
cation rate, in vivo chlorophyll fluorescence, maximurn cell
densities, and species equilibrium were investigated in cultures
of dinoflagellates Scrippsiella f~eroense, ~r'orocentr1~ micans,
and GYmnodinium splendens, and of diaton~ Schroederella
schroederi ffild Thalassiosira rotula. In monocultures,
inhibi tirn oCl~urred in O. 01 to O. 10 mg Znll over 38 days.
Diatoms were more sensiti'ffi than dinoflagellates. Sensitivity
to zinc increased with the number of species combined. In a 5
species culture, sublethal changes appeared at 0.005 to 0.010 mg
Znll. Schroederella and 1~alassiosira populations were reduced
to 2J~% and 71%, respectively. Interspecific compe~,i tion ffild Zn
toxicity both decreased algal growth. At low cell numbers
resulting from competitior1j zinc effects were seen only in
higher concentrations of 5.0 to 10.0 mg/I. Morphological
aber'rations were observed in Scrippsiella at 1.0 mg 2n/l ffild in
diatoms at 0.01 mg/I. Re:3ul ts shav that mul tispecies
experiments are a more sensi ti ve test for zinc t.oxicity than
monocultures. Author suggests that hea'ljl metal toxicity may
become effective at lower limit concentrations ion natural
planktonic commUllities.
2568.
Kunze, J., H. Buhringer, and U. Harms. 1978.
Accumulation of cobalt during embcyonic development
of rainbow trout (Salmo gairdned Rich.) Aquaculture
13:61-66.
During incubation at 8 C in rearing water containing
0.5 ug Coil and calcium content of 100 mgll? trout eggs
contained between 0.0003 and 0.0013 ug Co/egg thrOU~1 hatching.
In 5.0 ug Coil and 100 mg Ca2+/l, eggs accumulated up to
0.0033 ug Co/egg by the eyed stage; larvae contained only 0.0005
ug after mtching. Uptake of co~lt-57 by eggs exposed to 1000
ug Coil varied inversely with Ca + water levels. By the eyed
stage, eggs had accumulated up to 20,000 counts/min/egg in 50 rng
Call, up to 13,000 in 100 mg Call, and up to 10,000 in 200 mg
Call; Cobalt levels dropped to 5000-10,000 just before
hatching. Bivalent Co ions were reversibly bound to egg
surfaces by the binding force of chorion-mucopolysaccharide. No
increase in Co was found in larvae hatched from these eggs.
2569.
Lakshmi, G. J., A. VEnkataramiah, and H.D. Howse.
Effect of salinity and temperature changes on
spontaneous muscle necrosis in Penaeus aztecus
--
Aquaculture 13:35-43.
1 978.
Ives.
163
-------
Spontaneous muscle necrosis or appearance of
irregular white foci in abdominal segments was studied in brown
shrimp, P. aztecus, in relation to salinity and temperature
changes. - Shr imp were accl ima ted at 17 0/00 S, or 50% SW, and
exposed to salinities considered sub-optimal (0.34-3.4 0/00 S),
optimal (8.5-17.0 0/00 S), or supra-optimal (42.5-59.5 0/00 S).
In optimal salinity, 1.0-2.7% shrimp developed necrosis in 21 to
31 C, but all survived. In low salinity, 6.7% developed
necrosis at 21 C within minutes, 8.0% at 31 C, and all died at
both temperatures; 4.0% were afflicted at 26 C with 78%
mortality. In high salinity, 10.5% shrimp showed necrotic
symptoms at 21 C with 80% mortality, and 13.6% affected at 31 C
with 87% mortality; 1.0% were afflicted at 26 C with 67% dead.
Incidence of necrosis and subsequent mortality was directly
related to magnitude of salinity and temperature change.
Histopathological studies of necrotic muscles showed no
p3.thogens.
2570.
Leland, H.V., S.N. Luoma, and D.J. Wilkes. 1977. Heavy
metals and related trace elements. Jour. Water Poll.
Control Feder. 49:1340-1369.
Surveys from literature of trace metal concentrations
in freshwater and marine plankton, algae, and higher plants,
annelids, bacteria, bryophytes, coelenterates, crustaceans,
echinoderms, insects, molluscs, nematodes, protozoans, fishes,
birds, and mamnals are listed. Toxicity, bioaccumulation, and
bianagnification in these organisms is discussed. Also reported
are metal concentrations in seawater and sediments fran around
the world. Metals mentioned include Ag, Al, As, B, Be, Bi, Ca,
Cd, Co, Cr, Cs, Cu, Eu, Fe, Ge, Hg, K, Li, Mg, Mn, Mo, Na, Ni,
Pb, Pu, Rb, Sb, Sc, Se, Si, Sn, Th, Ti, Tl, V, and Zn.
2571 .
Luana, S.N. and E.A. Jenne. 1977. The availability of
sediment-bound cobalt, silver, and zinc to a
deposi t-feeding clam. In: Drucker, H. and R. E.
Wildung (eds.). Biological implications of metals in
the environment. ERDA Symp. Sere 42:213-230. Avail.
as CONF-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Comm., Springfield, VA 22161.
Availability of sediment-bound Co, Zn, and Ag to
clams, Macoma balthica, was dependent 00 physical and chemical
natures of the metal-sediment association. Uptake of zinc
coprecipitated with amorphic iron oxide sediment exhibited a
164
-------
concentration factor (CF) for dry clam tissue to dry sedilnent of
0.003-0.009 after 14 days, and with manganese oxide sediment, a
CF of 0.006-0.007. Cobalt had a CF of 0.002-0.005 and
0.001-0.002 for the respective sediment sinks, which are common
in nature. Silver was accumulated by Macoma from iron oxide
precipitate by a factor of 0.04-0.15. All metals were taken up
from detrital organics; CF for Ag was 0.03, 0.08-0.12 for Zn,
0.02-0.05 for Co. Quantitatively minor sinks in aquatic
sedilnents may be ilnportant sources of metals. Uptake rates for
Zn with a CF of 0.13-0.19, and Co with a CF of 0.07-0.10, from
biogenic carbonates (crushed clam shells) were significantly
higher than other si nks. Sil vel" uptake was maximum from
biogenic carbonates, at 0.3-0.8, and synthetic calcites, at
3.7-6.1. Sinks with maximum metal bioaccumulation also had
greatest rates of sedilnent-to-water desorption. When such sinks
are abundant in nature, bioavailability of sediment-bound metals
may be enhanced through uptake of injested particles by deposit
feeders and through sedimentary desorption, resulting in higher
concentrations of solute metals.
2572.
Madgwick, J., A. Haug, and B. Larsen. 1978. Ionic
requirements of alginate-modifying enzymes in the
marine alga Pelvetia canaliculata (L). Dcne. et
Thur. Botanica Marina XXI: 1-3.
A stable, semi-pure, freeze-dried powder containing
alginate 5-epilnerase and alginate lyase activity was prepared
f~m a brown alga. Maxi~al epimerase acti vi t y was at 136 mg
Ca +/1 and at 5490 ~g Mn +/1. Alginate lyase a~tivity was
activated by 136 Ca +/1 but was inhibited by Mn +. Ion
combinations of 136 mg Call and 549 mg Mnll were optilnal for
epimerisation, but inhibited lyase activity by 90% of Ca2+
alone. Increasing concentrations of substrate polymannuronate
removed Mn inhibition of lyase. Zinc at 654 mg/l and nickel at
587 mg/l strongly inhibited both enzymes; 589 mg/l cobalt
suppressed lyase but did not affect epimerase. Magnesium,
sodium, cesium, potassium, rubidium, and lithium did not
signfificantly alter activities.
2573.
Martin, J.H., K.M. Bruland, and W.W. Broenkow. 1976.
Cadmium transport in the California Current. In:
Windom, H.L. and R.A. Duce (eds.). Marine pollutant
transfer. D.C. Heath and Co., Lexington, MA:
159-184.
Cadmi um levels in seawater from 95 si tes off the
California coast ranged from 0.016 to 0.156 ugll at the
165
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interface, and generally increased from 0.0039-0.027 ug Cd/l to
0.0051-0.124 ug/l with increasing depth to 90 m. Cadmium levels
were directly proportional to phosphate and nitrate
concentrations in waters except in the Southern California Bight
area. Metal concentrations reached a maximum at 20 m at one
station analyzed; Cd rose to 0.150 ug/l, Cu to 0.240 ug/l, Pb to
0.525 ug/l, Mn to 0.600 ug/l, Ni to 0.825 ug/l, and Zn to 4.500
ug/l. Plankton collected from Southern California waters
contained 0.03 to 0.51 mg Ag/kg, 13.0 to 3710.0 Al, < 3.0 to
737.0 Ba, 7800 to 33,700 Ca, 2.2 to 24.7 Cd, 2.9 to 17.7 Cu, 36
to 3870 Fe, 3600 to 13,800 K, 6100 to 26,400 Mg, 3.5 to 35.9 Mn,
50,900 to 250,000 Na, 2.1 to 18.5 Ni, 0.8 to 13.6 Pb, 3000 to
242,000 Si, 1000 to 16,800 Sr, and 3.2 to 86.9 Zn.
2574.
McKim, J.M., J.G. Eaton, and G.W. Holcombe. 1978. Metal
toxicity to embryos and larvae of eight species of
freshwater fish - II: copper. Bull. Environ.
Contamin. Toxicol. 19:608-616.
Standing crops of freshwater fishes exposed to
various concentrations of copper as embryos, larvae, and early
juveniles, were compared to controls. Rainbow trout Salmo
gairdneri numbers reduced to 10% after exposure to 30 ug Cull of
embryos for 11 days, or 35 days for larvae-juvenile; white
sucker Catostomus commersoni reduced to 30% after 13 day embryo
and 27 day larvae-juvenile exposure to 30 ug/l. Brook trout
Salvelinus fontinalis populations after 16 day embryo exposure
and 60 day larvae-juvenile exposure, and lake trout~. namaycush
after 27 day embryo and 66 day larvae-juvenile exposure to 50 ug
Cull dropped to 60% of controls; lake trout further reduced to
40% in 120 ug/l. A concentration of 100 ug Cull was fatal to
rainbow trout, brook trout, sucker, and pike; 450 ug Cull killed
all lake trout. Standing crop of trout exposed to 50 ug Cull
for 127 days was reduced to 40% of control values; these values
were 80% and 100% of control values at 97 and 71 days,
respectively. All brook trout died in 110 ug Cull after 127
days and in 500 ug/l after 97 and 71 day exposures.
Concentrations of 104 ug Cull and higher reduced standing crop
of lake herring Coregonus artedi, and smallmouth bass
Micropterus dolomieui after 30 days. Larvae and early juvenile
stages of all species were more sensi ti ve to copper than embryos.
2575.
Mearns, A.J. and D.R. Young. 1977. Chromium in the
southern California marine environment. In: Giam,
166
-------
C. S. (ed.). Pollutant effects on marine organisms.
D.C. Heath and Co., Lexington, MA: 125-142.
Marine life in coastal waters of southern California
is naturally exposed 60 approximately 0.2 ug/l of dissolved
chromium: 0.15 ug Cr +/1 and 0.05 ug Cr3+/1.
Uncontaminated sediments contain up to 40,000 ug Cu/kg dry wt.
Chromium from municipal wastewater, mainly bound to
particulates, contaminates sediments by 20X and seawater by 2 to
5X near outfalls. Most chromium is in the Cr3+ form. In
1972, the State of California established a limit of 5.0 ug/l
total Cr for discharges into coastal water up to 50% of the time
and 10.0 ug/l not to exceed 10% of the time. Adductor muscles
of scallops showed a 10X enhancement of Cr in response to
wastewater discharge. Total chromium concentrations in the
polychaete annelid Neanthes arenaceodentata after 150 days
increased to 3g,000 ug/kg dry wt when PEaced in media containing
up to 30 ug Cr +/1. LC-50 values of Cr + to Neanthes were
2200-4300 ugll at 96 hr, 1440-1890 ugll ag 7 days, and 200 ug/l
at 59 days. Spawning ceased in 100 ug Cr +/1 and reduction in
brood size was observed at 12.5 to 50.0 ugl1. After 44 days,
flounders Citharichthys stigmaeus contained 100,000 ug Cr/kg dry
wt in intestine, 10,000 in liver, and 3000 in muscle when
exposed to up to 3000-5000 ug/l. Fish accumulated Cr during
long term expCX3ure at levels as lCM as 16 ug Cr/l. Most tissues
in fish, except gonads, remained at ambient Cr levels dgspite
eXQos ure to contaminated sediments. In contrast to Cr+ ,
Cr5+ was not toxic to marine life, possibly due to its
relative insolubility at normal pH of seawater.
2576.
Meier-Brook, C. 1978. Calcium uptake by Marisa
cornuarietis (Gastropoda; Ampullarii dae ), a predator
of schistosome-bearing snails. Archiv fur
Hydrobiologie 82:449-464.
Marisa is a predatory gastropod which vigorously
feeds on intermediate host snails of schistomes and other
trematodes and shows a high net uptake of calcium from the
water, up to 400 ug/individual/hr or more. Uptake is about 20X
higher than Biomphalaria glabrata, an important snail host of
intestinal schistosomiasis. Results suggest that Marisa is
unable to establish its life cycle in tropical soft water
containing suboptimal levels of Ca, where its application as a
biological control agent would be desirable. Net Ca uptake of
Marisa aged 12 to 25 weeks vari ed between 0.20 and 0.45 mg
Ca2+ lindi vidual/hr in 100 mg Call water. Net Ca uptake was
167
-------
significantly reduced in < 50 or 75 mg Call. Acclimation to 25
mg Call for 5~ wreks led to an increase of net uptake of 0.30
mg/ind/hr when transferred to 70 mg Call. Growth of Marisa
increased when reared in 100 rather than 25 mg Call; shells in
100 mgll gained 41% more weight over 33 weeks.
2577. Meisch, H.-U. and J. Bauer. 1978. The role of vanadium
in green plants. IV. influence on the formation of
&-aminolevulinic acid in Chlorella. Arch.
Microbiology 117:49-52.
Vanadium, at 20.0 ug Vil as NH4V03' enhanced
synthesis of 6-aminolevulinic acid (6-ALA) in green alga
Chlorella pyrenoidosa, as evidenced by increased release of this
amino acid into the medium in the presence of levulinic acid
(LA). Exogenous levels of a-ALA after 5 days in media of pH 6.0
were 2.7 mg/l without V and 10.4 mg/l with 20.0 ug Vil in
presence of 34 mM LA; % a -ALA/algal dry wt was 0.3 without V and
0.9 with V. Levels of a-ALA were significantly lower at pH 7.0
and 7.5. Intracell ular ly accumulated 1 evels of 0 -ALA increased
only slightly with added vanadium. Vanadium uptake without LA
dropped from 13.4 mg Vlkg dry wt to 4.5 over 6 days; with 34 mM
LA, uptake ranged from 9. 1 to 10. 7 mg V / kg dry wt over this
period. Authors suggest that vanadium acts as a catalyst in
converting 4,5-dioxovaleric acid to 6-ALA by transamination.
2578. Meisch, H.-U. and H. Benzschawel. 1978. The role of
vanadium in green plants. III. influence on cell
division of Chlorella. Arch. Microbiology 116:91-95.
Vanadium, although essential for growth and
chlorophyll formation in green algae, exhibited deleterious
effects on cell division of Chlorella pyrenoidosa over the same
concentration range as pooi ti ve effects. It ms been shown that
1.0 ug Vil increased algal dry wt, 500 ug/l promoted chlorophyll
synthesis, but above 25,000 ug/l vanadate is toxic to algal
metabolism. Cell volume of Chlorella grown in 20.0 ug VI1, as
NH4V03' was evenly distributed over the 200 to 1600 um3
range. Wi thout V, moo t cells were smaller, 200-650 um3 after
3 days and 100-400 um3 after 7 days. Mean cell volume
increased to 1500 um3 ~s V added to medium rose to 500 ug/l,
th~n dropped to 920 um in 100,000 mg V/1; mean volume was 320
um in the absence of vanadium. Uptake by Chlorella rose to
100% of applied dose after 24 hrs under continuous light, and up
to 60% by 28 hrs in the dark. Under synchronous conditions of
168
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algal cultivation (16:8 hr), V completely arrested cell division
after 3 periods; this stop lasted for the next 3 cycles. Later
asynchronous divisions led to larger autospores and giant nuclei
with multiple chromosome sets. Under these conditons, C.
pyrenoidosa is not synchronizable in presence of vanadium.
2579.
Montgomery, J.R., M. Price, J. Thurston, G.L. de Castro,
L.L. Cruz, and D.D. Zimmerman. 1978. Biological
availability of pollutants to marine organisms. U.S.
Environ. Protect. Agen. Rept. EPA-600/3-78-035,
Narragansett, R.I.:134 pp.
Uptake rates of Cd, Cr, Cu, Ni, Pb, and Zn leached
from sewage sludge by seawater by a turtle grass, Thalassia
testudinum, ecosystem were studied. Cadmium, Pb, and Zn uptake
in the "fouling organisms" closely paralleled net loss of metals
from sewage sludge. Thalassia leaves contained up to 3 mg Cd/kg
dry wt above control values during 120 days exposure to sludge,
up to 35 mg Cu/kg, up to 60 mg Cr/kg, up to 80 mg Pb/kg, up to
45 mg Ni/kg, and up to 25 mg Zn/kg. The urchin Lytechinus
variegatus, a herbivore which consumes Thalassia leaves, showed
net uptakes of all metals except Cd over 120 days: 15 mg Cu/kg
dry wt, 45 mg Cr/kg, 30 mg Pb/kg, 30 mg Ni/kg, and 70 mg Zn/kg.
The sea cucumber Holothuria mexicana accumulated metals up to 30
mg Cu/kg dry wt, 40 mg Cr/kg, 65 mg Pb/kg, 40 mg Nilkg, and 50
mg Zn/kg, but did not accumulate Cd. Maximum uptake in mangrove
Rhizophora mangle roots was 5 mg Cu/kg dry wt, 25 mg Cr/kg, 5 mg
Pb/kg, 10 mg Ni/kg, and 20 mg Zn/kg. Uptake in mangrove roots
was directly related to sediment metal concentration. No
significant metal uptake was found in the clam Codokia
orbicularis, oyster Crassostrea rhizophora, or snail Nerita
tessplata, possibly due to lack of sufficient sample mass.
Authors concluded that dumping of sewage sludge in coastal
tropical waters may lead to uptake and concentration of toxic
metals by members of a turtle grass cormnuni ty .
2580.
Moore, M.N. 1977. Lysosomal responses to environmental
chemicals in some marine invertebrates. In: Giam,
C.S. (ed.). Pollutant effects on marine organisms.
D.C. Heath and Co., Lexington, MA: 143-154.
Cytoplasmic lysosomes in the hydroid Campanularia
flexuosa and mussel Mytilus edulis accumulate various metal
ions. Maximum activity of the enzyme lysosomal hexosaminidase
in Campanularia, as shown by staining intensity, increases to
169
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180-200% over controls at 50 ug Cull, 100 ug Cd/l, or 0.5 ug
Hg/lo Further increase in metal levels sharply decreased
acti vity. Cytochemical thresholds of the lysosomal enzyme were
at 1.2-1.9 ug Cull, 40-75 ug Cd/l, and 0.17 ug Hg/l. Addition
of hy~ocortisone decreased enzyme activity, with or without 20
ug Cu + in media.
2581.
Neff, J.M. and J.W. Anderson. 1977. The effects of
copper (II) on mol ting and growth of juvenile lesser
blue crabs Callinectes similis Williams. In: Giam,
C.S. (ed.). Pollutant effects on marine organisms.
D.C. Heath and Co., Lexington, MA: 155-165.
Median LT-50 values in crabs, ~ similis, exposed to
0.50 mg Cull were 3.7 days for megalops and 7.7 days for first
crab stage. LT-50 in 0.25 mg Cull was 30 days for first crab
stage. LT-O and LT-100 in 0.50 mg Cull was 1 and 31 days,
respectively, for megalops and 3 and 49 days for first crab
stage. In 0.25 mg Cull, the LT-O was 20 days and LT-100 was 68
days for first crabs. Death usually occurred during or
immediately after a molt. No mortalites were observed for
megalops or juveniles exposed to 0.05 mg Cull for 130 days.
Chronic exposure to 0.05 mg Cull resulted in decreased intermolt
periods, especially during later juvenile stages; however,
growth rate was faster than controls. Average wet weight of
crabs was reduced in 0.05 mg Cull. Resul ts are discussed in
relation to suspected modes of toxic action of copper in marine
animals.
2582.
Nimmo, D.R., R.A. Rigby, L.H. fu.hner, and J.M. Sheppard.
1978. Tm acute and chronic effects of cadmium on
the estuarine mysid, Mysidopsis bahia. Bull.
Environ. Contamin. Toxicol. 19:80-85.
Mysid shrimp, M. bahia, showed no significant
decrease in survival when exposed to 4.8 or 6.4 ug Cd/I for 23
days under flew-through conditions. Only 10% survived in 10.6
ug Cd/I for 23 days; none survived after 13 days in 28.0 ug/I.
LC-50 values were 15.5 ug Cd/l for 96 hrs and 11. 3 ug/l during a
17-day life history expc:sure. Mysids were more sensi ti ve to
cadmium than other crustaceans: selected species had LC-50 (96
hr) values extending fran 120.0 to 720.0 ug Cd/I. Authors
suggest that life-cycle bioassays can aid in establishing water
quality criteria for marine and estuarine organisms.
170
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2583.
Oikari, A. 1978. Aspects of osmotic and ionic
regulation in two Baltic teleosts: effects of
salinity on blood and urine composition. Marine
Biology 44:345-355.
Hydromineral regulation was studied in two species of
brackish water teleosts, Myoxocephalus scorpius and !1.
quadricornis, in water ranging from freshwater to 33 0/00 s. M.
scorpius tolerated freshwater and !1. quadricornis tolerated
seawater of 33 0100 for only 24 hr; survival time of M. scorpius
in 33 0100 Sand !1. quadricornis in freshwater was up-to several
weeks. !1. scorpius exhibited balanced plasma ionic
concentrations at salinities as low as 2.5 0100 during immersion
for 2 weeks; some regulation was evident for Na+, Cl-,
Mg2+, and Ca2+. Death of M. scor~us in freshwater was
associated with increased plasma and decreased Na+,
Cl-, and Mg2+ in plasma and to a lesser extent in urine,
partial remolysis, and increased red bloexi cell volume after 24
hrs. Death of !1. quadricornis in 33 0100 S was associated with
increases in plasma Na+, Cl-, and Mg2+ and total
o3D.olarity. Renal excreti rn of ions approached that of marine
teleosts, showing reduced Na+ and ~ and elevated Cl-,
Mg2+, and Ca2+ after 24 hrs. Red blood cell volume
generally followed changes in plasma osmolarity or Na+ and
Cl- concentrations, the most abundant ions in fish plas~a and
urine in most cases. Both species increased tubular Mg +
secretion in 33 0100 S when compared to 6 0100 S; M.
quadricornis reabsorbed Na+ almost completely from-urine.
2584.
Osterberg, C. and S. Keckes. 1977. The state of
pollution of the Mediterranean Sea. Ambio 6:321-326.
The Medi terranean is expected to be one of the first
seas to suffer harm from man's impact because of its
configuration and proximity to a number of more developed
nations. Mercury levels as high as 2.5-3.5 mg/kg wet wt have
been found in tuna in the Mediterranean, levels 3X higher than
in Atlantic tuna. Cadmium in offshore waters are generally
<0.003 mgll. Water concentrations of copper increase markedly,
up to 0.022 mgll, in areas of land runoff. Mussels reflected
this increase, containing 0.095 mg Cu/kg dry wt off Marseille,
France. High levels of zinc, 0.20 mgll, found in coastal areas
drop to 0.005-0.015 mgll in the open sea; Zn is rapidly removed
by biota, dispersion, and diffusion. Little data are available
on lead. Sewage and oil pollutirn appear to be the principal
problems alrng the northwest Mediterranean basin.
171
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2585.
Pagenkopf, G.K. 1976. Zinc speciation and toxicity to
fishes. In: Andrew, R.W., P.V. Hodson, and D.E.
Konasewic~(eds.). Toxicity to biota of metal forms
in natural water. Great Lakes Research Adv. Bel.,
Stand. Camm. Sci. Basis Water Quality Criteria Inter.
Jt. Comm. Res. Adv. Bel.:77-91.
Zinc speciation was calculated using data from
literature dealing with Zn toxicity to fishes, mainly fathead
minnows, bluegills, and rainbow trout. Calcium and magnesium in
test waters reduced effects of Zn; concentrations for LC-50 (96
hr) rose as water hardness increased from 50 to 200 mg/l as
CaC03. Increasing pH from 6 to 8 decreased LC-50 zinc
concentrations 20-50X. Amounts of solid Znco3 in water
increased with this pH change; however, relatlve toxicity of
solid and soluble Zn forms has not yet been established.
2586.
Patrick, R. 1978. Effects of trace metals in the
aquatic ecosystem. American Scientist 66:185-191.
Various concentrations of Cr, Se, and V may cause
shifts in species composition of freshwater algal communities.
Diatoms generally remained at control levels when exposed to 3.5
to 2000 ug V/1; however, growth declined slightly during one
trial in Sept-Oct. in 8.9 and 19.2 ug V/l. Occurrence of
diatoms was rare in 39 ug V/l in Sept.-Oct. and 4000 ug/l in
Nov. -Mar. Blue-green algae were rare to frequent in lower
concentrations of vanadium, and more common in 4000 ug/l than
control medium. Green algae were rare in up to 39 ug V/l in
Sept.-Oct., but common in 2000 and 4000 ug/l in Feb.-Mar. Algal
bi anass accumula ti on rose to 25, 800 mgl kg in 4000 mg V 11 ,
although concentration factors (CF) were maximum at 17,000 in
lower concentrations. When exposed to6chromium, diatoms were
dominant in controls and 96-99.5 ug Cr +/1; green and
especially blue-green algae became abundant in 376 and 405 ug
Cr/l. The green alga, Stigeoclonium lubricum, was the most
conmon in hi~ Cr and V levels. Algal populations contained up
to 3360 mg Cr +/kg in 376 ug/l; CF was over 29,000 in lower
concentrations. Diatoms were cOllmon in all concentrations of
selenium tested (1.0 to 40.5 ug/l) although diversity decreased
at higher concentrations. Green and blue-green algae were
common only during Apr.-May in 1.1 to 10.4 ug Sell. As
selenate, Se was toxic to diatoms at all concentrations tested.
Maximum Se levels in bianass was 8800 mg/kg in 40 ug/l; maximum
172
-------
mg/kg in 40 ug/l; maximum CF was only 680 in the lcwest
concentration.
2587.
Patterson, C., D. Settle, B. Schaule, and M. Burnett.
1976. Transport of pollutant lead to the oceans and
within ocean ecosystems. In: Windom, H.L. and R.A.
Duoe (eds.). Marine pollutant transfer. D.C. Heath
and Co., Lexington, MA: 23-38.
Approximate total lead inputs into oceans from all
sources in tons/yr, were 300,000 from industrial inputs and
114,000 fran neolithic inputs. Lead concentrations reported in
coastal waters near urban regions ranged from 0.025 ug Pb/l to
0.150 ugll in polluted areas. Surface waters off Los Angeles,
California, in 1973-1975, had 0.11-0.33 ug Pb/l; 1.30 ug/l was
detected at 30 m depth. Lead in surface waters at La Jolla and
areas south of Los Angeles was 0.016-0.036 ug/I. As the
proportion of sewage lead in seawater increases, fraction of
freely available Pb decreases. Authors recommend that actual
enrichment or depletion of lead in marine organisms be expressed
relati ve to bulk of calcium. In a seawater - kelp Macrocystis
pyrifera - gastropod Norrisia norrisii food chain, Sr/Ca ratio
increased by 8, OO/Ca by 20, and Pb/Ca by 2000 going from
seawater to kelp. Metal concentrations were depleted using kelp
for gastropod food: Sr/Ca decreased by 70, OO/Ca by 600, and
Pb/Ca by 150 for total gastropod. Ratios decreased by only
2.0-10.0 in reference of kelp to gastropod muscle. Metals
present at the lowest and highest trophic levels in another food
chain were: calcium, 400 mg/l in seawater and 8800 mg/kg wet wt
in albacore tuna; strontium, 8.1 and 36.0 respectively; barium
0.03 and 0.1; and lead, 0.00002 and 0.008. Calcium ratios in
albacore are lower than in a terrestrial food chain, possibly
due to passive adsorption effects in the marine ecosystem.
2588.
Pentreath, R.J. 1977. Radionuclides in marine fish.
Oceanogr. Mar. BioI. Ann. Rev. 15:365-460.
Environmental levels and accumulation-retention
studies of radionuclides of Ag, Am, As, Au, 00, Bi, Ca, Cd, Ce,
Cm, Co, Cr, Cs, Cu, Eu, Fe, Hg, K, La, Mn, Mo, Nb, Np, Pa, Pb,
Po, Pr, Pu, Ra, Rb, Rh, Ru, Sb, Sc, Sr, Tc, Te, Th, Tl, U, W, Y,
Zn, and Zr were reviewed for marine fishes. Concentration
factors of stable Ag, Au, Ce, Co, Cr, Cs, Fe, Mn, Sb, Sr, and Zn
in fish fran different areas are listed. Author discusses the
environmental application of metal levels determined. A
173
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bibliography of about 360 references is appended.
2589.
Phillips, D.J.H. 1978. The common mussel MYtilus edulis
as an indicator of trace metals in Scandinavian
waters. II. lead, iron, and manganese. Marine
Biology 46:147-156.
Metal concentrations in mussel soft parts from 54
locations in Scandinavian waters ranged from 3.0 to 264.0 mg/kg
dry wt for lead, from 14.0 to 1367.0 mg/kg dry wt for iron, and
from 4.9 to 91. 7 mg/kg dry wt for manganese. Maximum Pb and Fe
levels were found in mussels collected near an ironworks. In
agreement with previously published data, indicator ability of
mussels for Pb and Fe was supported over the entire salinity
range; Mn indicatim appeared questionable at least in lON
salinity ranges. Higher concentrations of Pb and Fe were found
in mussels from lON salinity waters east of Sweden than mussels
from higher salinity waters to the west. Mn tissue
concentrations followed this trend only weakly, possibly owing
to partial regulation of body loads in M. edulis. Low salinity
waters seem to be associated with greater biological
availability of Pb and Fe; this may be related to lON primary
productivity whEn compared to typically marine waters.
2590.
Pirt, S.J. and M. Walach. 1978. Biomass yields of
Chlorella from iron (Yx/Fe) in iron-limited batch
cultures. Arch. Microbiol. 116:293-296.
Biomass in iron-limited photosynthetic algal batch
cultures of Chlorella increased as the logarithm of the iron
concentration. Growth yield from iron (Yx/Fe) was inversely
related to specific growth rate. Maximum biomass yield, in mg
dry wt/mg Fe consumed, was 7500 with specific growth rate
0.108/hr; minimum yield was 790 with growth rate 0.145/hr.
Maximum specific growth rate in the exponential phase of
Fe-limited cultures over 30 days was higher as initial Fe
concentration was increased to 0.469 mg/l. Fe-limited growth
made cells adhere to glass surfaces.
2591.
Prater, B.L. and M.A. Anderson. 1977. A 96-hour
bioassay of Otter Creek, Ohio. Jour. Water Poll.
ContrA Feder. 49:2099-2106.
Bioassays of 96 hour duration were conducted using
174
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the crustacean Daphnia magna, the insect Hexagenia Iimbata and
the isopod Asellus communis exposed to sediments from various
locations along Otter Creek in Ohio. Less than 10% of each
species died when exposed to sediments upstream from any
industrial site. Sediments contained 23,000 mg Fe/kg dry wt,
17,000 mg Al/kg, 475 mg Mg/kg, 110 mg Zn/kg, 100 mg B/kg, 79 mg
Pb/kg, and ~O mg/kg in decr>easing order of Ni, Cr, Co, Cu, Cd,
and As. Pretest water used in all trials contained 51 mg Call,
13.6 mg Mg/l, 6.7 mg Nail, 0.1 mg Snll and < 0.1 mg/l for AI, As,
Ba, Be, B, Cd, Cr, Co, Cu, Fe, Pb, Mn, Hg, Mo, Ni, Ag, Ti, V,
and Zn. Concentrations of other chemicals present are also
listed. Most metal levels in solution increased during the
experiment. Mortality among Daphnia was >95% whEn exposed to
sediments from 4 other sites downstream from industrial and
municipal outfalls. Sediments downstream from one industrial
outfall killed 15-30% of Hexagenia and 35-45% of Asellus. After
the second outfall, all Hexagenia and Asellus died in 96 hrs in
sediments containing 28,000 mg Fe/kg dry wt, 14,000 mg Al/kg,
665 mg Mn/kg, 185 mg Cr/kg, 135 mg Zn/kg, 130 mg B/kg, and < 70
mg/kg for other metals tested. Sediments downstream from the
third outfall killed 60-80% of Hexa enia and 100% of Asellus;
after the fourth outfall, 90-100 of Hexagenia and 100% of
Asellus died after sediment expasure. Authors concluded that
sediments in the lcwer two thirds of Otter Creek are not
conduci ve to life support of aquatic biota.
2592.
Ranta, W.B., F.D. Tomassini, and E. Nieboer. 1978.
Elevation of copper and nickel levels in primaries
from black and mallard ducks collected in the Sudbury
district, Ontario. Canadian Jour. Zoology 56:581-586.
Primary flight feathers of black ducks, Anas
rubripes, and mallard ducks, !. platyrhynchos, collected from
northern Ontario and northern Saskatchewan, Canada, during fall
1975, were analyzed for copper, nickel, and zinc. Ducks
collected 20 to 30 kID from the Copper Cliff 3llel ter, a h:noWD
source of particulate fallout, contained 99 to 132 mg Znlkg dry
wt. Concentrations were 103 to 129 mg Zn/kg from ducks 50-60 kID
117 to 130 mg/kg at 85 kID, and 108 to 150 mg/kg at 95-140 kID
away from the smelter. Zinc was 101 to 144 mg/kg dry wt in
ducks from from Saskatchewan as a control. Mean copper in birds
ranged from 11 to 23 mg/kg dry wt with a high of 53 at 20-30 km
from the smeltery, 9.0 to 19.0 mg/kg at 50-60 kID, 11.0 to 24.0
mg/kg at 85 kID, 5.0 to 17.0 mg/kg at 95-140 kID, and 0.0 to 14.0
from Saskat chewan. Mean ni ckel concentra ti ons ranged from 2, 0
to 12.5 mg/kg dry wt, with a high of 36.7 at 20-30 kID, 0.2 to
3.8 mg/kg at 50-60 kID, 0.2 to 1.5 mg/kg at 85 kID, 0.0 to
175
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4.3 mg/kg at 95-140 km, and 0.0 to 0.4 mg/kg from Saskatchewan.
Zinc concentrations did not vary with population sampled; mean
copper, and especially nickel, levels were highest near the
smel ter in Sudsoory. No trends in metal levels were apparent
with species, sex, age, or wing type analyzed.
2593.
Ray, S. 1978. Bioaccumulation of lead in Atlantic salmon
(Salmo salar). Bull. Environ. Contamin. Toxicol.
19:631-636.
Juveniles of 1470-1940 g wet wt, and parr of 8.0-18.4
g wet wt, fran the Miramichi River, New Brunswick, Canada, in
June 1974, were analyzed for lead. Muscle contained 0.02-0.17
mg Pb/kg dry wt in juveniles and 0.7-2.2 mg Pb/kg in parr; gill
contained 1.9-7.5 and 6.6-20.6, respectively; liver, 1.5-11.2
and 16.4-139.6, respectively; kidney, 11.4-51.2 and 21.2-173.5,
respectively; and spine, 0.4-1.2 and 4.1-13.1, in respective
specimens. Lead concentrations in tissues fran parr were 2.5 to
15X higher than juveniles.
2594.
Rehwoldt, R.E., W. Mastrianni, E. Kelley, and J. Stall.
1978. Historical and current heavy metal residues in
Hudson River fish. Bull. Environ. Contamin. Toxicol.
19: 335- 339.
Average metal concentrations, in ug/kg dry wt, in
Hudson River fish from four information sources between 1924 and
1976 were: 91-120 for caOOJ.urn, 160-210 for mercury, and 300-610
for lead in alewife Alosa pseudoharengus; 96-110 for Cd, 310-460
for Hg, and 710-820 for Pb in sturgeon Acipensor oxyrhynchus;
12-72 for Cd, 140-240 for Hg, and 410-1100 for Pb in killifish
Fundulus diaphanus; 41-72 for Cd, 520-610 for Hg, and 990-1060
for Pb in smallmouth bass Micropterus dolomieui; 71-160 for Cd,
160-220 for Hg, and 590-770 for Pb in shiner Notropis hudsonius;
43-99 for Cd, 320-510 for Hg, and 210-920 for Pb in striped bass
Morone saxatilis; 260 for Cd, 420 for Hg, and 250 for Pb in
sunfish Lepomis gibbosus; and 62-100 for Cd, 300-510 for Hg, and
800-1060 for Pb in perch Morone americana. Residues appeared to
be independent of time or industrial development.
2595.
Reish, D.J., T.J. Kauwling, A.J. Mearns, P.S. Oshida, and
S. S. Rossi. 1977. Marine and estuarine pollution.
Jour. Water Poll. Contr. Fed. 49:1316-1340.
176
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A literature review on pollution effects to marine
organism by Ag, Al, As, Ca, Cd, Co, Cr, Cu, Fe, Hg, K, Pb, Mg,
Mn, Na, Ni, Se, Si, Sr, Ti, Tl, Zn, petroleum, and several
detergents and oil dispersants is presented. Data include
natural residues and sublethal and lethal effects to algae,
annelids, bacteria, crustaceans, echinoderms, fish, mammals,
molluscs, and sipunculids.
2596.
Rickard, W.H. and H.A. Sweany. 1977. Radionuclides in
Canada goose eggs. In: Drucker, H. and R.E. Wildung
(eds.). Biological implications of metals in the
environment. ERDA Symp. Ser. 42:623-627. Avail. as
CONF-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Corom., Springfield, VA 22161.
Radionuclide levels, in pCi/kg ash wt, in Canada
goose eggs from deserted nests along the Columbia River,
Washington, in 1974 ranged from: 20,000 to 22,000 in inner egg
contents and 3600 to 4200 in eggshells for K-40; 560 in eggs and
1300 to 1700 in shells for Sr-90; 170 to 6300 in eggs and 23 to
32 in shells for Cs-137; 230 to 430 in eggs and 180 in shells
for Zn-65; 45 to 60 in eggs and 58 to 72 in shells for Ru-106;
70 in eggs and 27 to 81 in shells for Zr-Nb-95; and 28 to 39 in
eggs and 5.0 to 8.0 in shells for Co-60. Inner egg contents
also contained 41 to 104 pCilkg Mn-54, 19 to 24 for Na-22, and
3.0 for Pu; eggshells contained 324 for Be-7 and 95 for Ce-144.
Although Sc-46, Sb-125, 00-140, and Eu-155 were routinely
measured in air at Richland, WA, they wer'e not detected in egg
contents.
Saifullah, S.M. 1978. Inhibitory effects of copper on
marine dinoflagellates. Marine Biology 44:299-308.
Exposure of Scrippsiella faeroense to 0.020 mg Cull
for 25 days decreased population size; 0.005 and 0.010 mg Cull
reduced growth rates while 0.001 mg/l showed no effect. All
levels of Cu decreased population size in semicontinuous
cultures of Scrippsiella after 8 days. Populations of
Gynmodinium splendens were decreased only in 0.020 mg Cull for
19 days; lesser concentrations showed no effect on growth.
Prorocentrum micans populations decreased during exposure to
0.020 mg Cull for 21 days, exhibited reduced growth in 0.010
mg/l, and showed no response to 0.001 and 0.005 mg/l. Uptake of
labelled carbon was reduced in Scrippsiella populations ilDmersed
in 0.010 or 0.020 mg Cull for 16 days; after an initial decline
in 0.005 mg/l, uptake rate returned to normal by day 16. It was
2597 .
177
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suggested that copper inhibits cell growth by arresting cell
division, or by disrupting internal cell metabolism.
2598.
Santerre, M.T. and R.C. May. 1977. Some effects of
temperature and salinity on laboratory-reared eggs
and larvae of Polydactylus sexfilis
(Pisces:Polynemidae). Aquaculture 10:341-351.
Temperature and salinity effects on eggs and larvae
of the marine teleost P. sexfilis were examined. Maximum larval
length was observed between 23.8 and 28.6 C at 34 0/00 S.
Normal development increased at 26 to 34 0/00 S at intermediate
temperatures. Larvae reared in 34 0/00 S through yolksac had
> 50% survival between 21.9 and 28.0 C. Upper and lower salinity
tolerances of 42-hr larvae were reduced at the two extreme
temperatures, and were broadest at 26.2 C. Larvae 72 hrs old
were more tolerant to high temperature than newly fertilized
eggs. Authors recorrmended conditions of 24-28 C and 26-34 0/00
S for rearing f. sexfilis eggs.
2599 .
Sastry, K.V. and P.K. Gupta. 1978. Alterations in the
activity of some digestive enzymes of Channa
punctatus, exposed to lead nitrate. Bull. Environ.
Contamin. Toxicol. 19:549-555.
After exposure for 15 days to 3. 80 mg/l of lead
nitrate, the freshwater fish, Q. punctatus, exhibited decreases
in alkaline phosphatase activity of intestine and pyloric caeca,
but not liver and stomach; acid phosphatase was decreased in
intestine and pyloric caeca, but not liver and stomach; trypsin
increased in intestine and pyloric caeca; and pepsin increased
in stomach. Fish exposed for 30 days to 3.80 mg Pb/l showed a
decrease of alkaline phosphatase activity in pyloric caeca, an
increase of acid phosphatase in all tissues, a greater increase
of trypsin in both tissues analyzed, and an increase of pepsin
in stomach. Among carbohydrase enzymes, amylase activity
increased significantly in all tissues of fish exposed to 3.80
mg Pb/l for 15 days, maltase increased in all but liver, and
lactase increased in liver, but lactase decreased in intestine
and pyloric caeca. After 30 days exposure, amylase increased in
liver, but decreased in stomach, intestine, and caeca; maltase
decreased in caeca, and lactase increased only in stomach.
Pattern of alteration in enzyme activities due to lead exposure
is different in liver and digestive system.
178
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2600.
Shen, A.C.Y. and J.F. Leatherland. 1978. Effect of
ambient salinity on ionic and osmotic regulation of
eggs, larvae, and alevins of rainbow trout (Salma
gairdneri). Canadian Jour. Zoology 56:571-577.
Osmotic and ionic concentrations of eggs, larvae, and
alevins of rainbow trout Here measured in distilled water and
dilute seawater of 11 and 13 0/00 S. Osmotic concentration, in
mean depression of freezing point, was 0.05 in perivitelline
fluid in distilled water, 0.43 in 11 0/00 S, and 0.49 in 13 0/00
S; only in distilled water was fluid osmotic pressure higher
than ambient medium. Tissue water content decreased slightly in
eggs from 65.5% to 63.6 and 63.9% in dilute seawater; water
content in larvae dropped from 62.1% to 58.4 and 56.8% and. in
alevins from 66.9% to 60.6 and 57.8%. Na+:~ ratio rose in
eggs from 0.27 to 0.42 and 0.50 with an increase in salinity,
remained steady in larvae at 0.26 to 0.28, and dropped in
alevins from 0.55 to 0.29 and 0.25. Tissue Na+ concentration
increased significantly in eggs from 336 mg/kg wet wt in
distilled water to 543 in 11 0/00 S and 614 in 13 0/00 S; larvae
increased Na+ only slightly, and in alevins decreased
significantly from 570 to 419 and 391 mg/kg in dilute seawater.
Tissue K concentrations increased slightly in eggs only in 11
0100 S; larvae increased significantly from 2370 to 2428 and
2506 mg K/kg in seawaters, and alevins showed a slight
increase. Over the 25 day period prior to hatching, egg Na
levels rose from 299 to 529 mg/kg wet wt in distilled water,
from 345 to 690 in 11 0/00 S, and from 391 to 805 mg Na/kg in 13
0100 S. Authors suggest that early stages of trout possess
limited osmotic or ionic regulation; larvae regulate tissue
Na+ by increasing Na+ in perivitelline space and alevins
tolerate an increase of tissue K+ and decrease in tissue water
content.
2601.
Somero, G.N. and T.J. Chow. 1977. Lead effects on the
estuarine teleost fish Gillichthys mirabilis:
salinity and temperature effects on tissue-specific
accumulation rates and lead effects on respiration
rates. In: Giam, C.S. (ed.). Pollutant effects on
marine organisms. D.C. Heath and Co., Lexington,
MA: 36. (Abstract).
Lead accumulation in G. mirabilis occurred in
tissue-specific patterns; spleen~gills, intestine, and fins
accumulated maximum levels and muscle and liver the least.
Lead-exposed fish that were returned to normal seawater lost lead
179
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in gills, intestine, and fins. Rapid Pb turnover in mucus-rich
tissues may result from lead complexing to mucus, followed by
sloughing of the mucus layers. Lead accumulation rates were
directly proportional to temperature and inversely proportional
to salinity. Oxygen consumption and excitability increased in
fish exposed to Pb; gill tissue respiration did not change.
Authors suggest that lead influences central nervous system
functions in fish, especially neurotransmitter metabolism, as is
the case with higher vertebrates.
2602.
Sullivan, J.K. 1977. Effects of salinity and
temperature on the acute toxicity of cadmium to the
estuarine crab Paragrapsus gaimardii (Milne
Edwards). Austral. Jour. Mar. Freshwater Res.
28: 739-743.
LC-50 (96 hr) values for cadmium chloride on crabs,
f. gaimardii, in static tests at 5 C rose from 22.4 to 101.9
mg/l as salinity increased from 8.6 to 34.6 0/00. In 19 C,
LC-50 (96 hr) values rose from 15.7 to 34.3 mg Cd/l as salinity
increased. Mortality in crabs was greater at higher temperature
and at lower salinity.
2603.
Suzuki, Y., M. Nakahara, and R. Nakamura. 1978.
Accumulation of cesium-137 by useful mollusca.
Japan. Soc. Sci. Fish. 44:325-329.
Bull.
Octopus, Octopus vulgaris, exposed to labeled cesium
for 14 days, had Cs-137 activity ratios (cpm/g tissue ~ cpm/g SW)
of 12.8 for liver, 10.9 for ovotestis, 8.0-8.3 for kidney,
funnel, and branchial heart; 6. 1 and 7.5 for heart, arms and
tentacles, buccal bulb, ctenidia, and gastric caecum; 4.7-5.7
for stomach, sucker, oesophagus, and sali vary gland; and 3.5 for
mantle. Of the total body Cs-137, arms and tentacles contained
75%, mantle 11%, and other tissues <5.0%. Squid, Doryteuthis
bleekeri, showed activity ratios after 6 days of 8.0 to 11.0 in
arm, ctenidia, liver, and mantle, in decreasing order.
Elimination of Cs-137 by Octopus tissues showed decreases from
about 10,000 to 1000 cpm/g in arms over 75 days and to 500 in
liver, ctenidia, and mantle. Biological half-life of cesium was
90 days. Elimination by the clam Gomphina melanaegis over 70
days showed decreases of 10,000-13,000 to 1000-1200 cmp Cs-137/g
in muscle and viscera; biological half-life was 31 days.
Concentration factors were similar among the classes of
molluscs, which were close to values for crustaceans and slightly
180
-------
lower than Cs concentration factors for marine fish.
2604.
Trefry, J.H. and B.J. Presley. 1976. Heavy metal
transport from the Mississippi River to the Gulf of
Mexico. In: Windom, H.L. and R.A. Duce (eds.).
Marine pollutant transfer. D.C. Heath and Co.,
Lexington, MA:39-76.
Concentrations of Al, As, Cd, Co, Cr, Cu, Fe, Hg, Mn,
Ni, Pb, and Zn in water and sediments of the lower Mississippi
River and Gulf of Mexico are listed. Metal distributions in
Sargassum and mixed phytoplankton fran about 20 sites in the
Mississippi Delta and Northwest Gulf were determined and ranged
from 33 to 13,450 mg Al/kg dry wt, 2.9 to 82.0 for As, <0.05 to
46.0 for Cd, <0.5 to 6.6 for Co, 1.2 to 25.2 for Cu, 61 to 7550
for Fe, 2.5 to 39.2 for Pb, 4.5 to 181.0 for Mn, 0.9 to 15.6 for
Ni, and 13.0 to 129.0 for Zn. Metal levels in zooplankton
samples consisting of salps, coelenterates, ctenophores,
chaetognaths, amphipods, copepods, decapods, euphausiids,
ostracods, and fish larvae, ranged from 44.0 to 6000.0 mg Al/kg
dry wt, 1.9 to 29.5 for As, 0.4 to 4.4 for Cd, <0.5 to 2.1 for
Co, 3.5 to 74.0 for Cu, 62 to 4760 for Fe, < 0.5 to 62.5 for Pb,
4.7 to 114.0 for Mn, <0.5 to 8.2 for Ni, and 41.0 to 200.0 for
Zn. Authors concluded that there is little evidence of
excessive metal levels in the lower Mississippi River. Although
some phytoplankton samples contained elevated Pb and Cd content,
overall concentrations are similar to unaffected areas.
Sedimentary records showed increases in Pb and Cd, but not Co,
Cr, Cu, Mn, Ni, or Zn from the Mississippi River.
2605.
Ueda, T., R. Nakamura, and Y. Suzuki. 1978. Compar ison
of influences of sediments and sea water on
accumulation of radionuclides by marine organisms.
Jour. Radiation Res. 19:93-99.
Accumulations of ruthenium-rhodium and cesium by the
clam Gomphina melanaegis, after exposure for 13 days to 0.2 mCi
of radionuclides, is reported. A concentration factor (CF) of
tissue over seawater of 4.0 in muscle, 1.5 in visceral organ,
and 2.0 in edible parts was observed for Cs-137. For
Ru-106-Rh-106, the CF was 8.0 in muscle and 6.0 in visceral
organs and edible parts. For the alga Cyrtymenia sp., a CF
after 11 days was about 3.0 for Cs-137 and 200 for
Ru-106-Rh-106. Accumulation of radionuclides from sediments
containing 0.2-1.0 mCi after 14 days was expressed as a transfer
181
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ratio (TR); this was 0.045 for Cs-137 and 0.0007 for
Ru-106-Rh-106 in Gomphina, and 0.069 for Cs-137 and 0.054 for
Ru-106-Rh-106 in Cyrtymenia. Biological factors of sediments
(CF fran seawater/TR from sediment) were 160 for Cs and 2900 for
Ru-Rh in Gomphina and 70 for Cs and 5400 for Ru-Rh in
Cyrtymenia; comparable values of seawater and sediment
contamination were reported for the annelid Nereis japonica.
2606.
Ui, J. and S. Ki tamuri. 1971. Mercury in the Adriatic.
Marine Poll. Bull. 2:56-58.
Total mercury in fish from six polluted sites in
France and Italy ranged from 0.17 to 7.39 mg/kg dry wt; methyl
mercury content ranged from 0.07 to 6.37 mg/kg dry wt. Factory
effluent at Ravenna, site of maximum mean Hg levels in fish of
3.4 mg/kg total and 2.8 methyJmercury, was 0.48 mg/l total Hg
and 0.001 mg/l methylmercury. Fish from Nice, as a control,
contained an average of 0.95 mg/kg dry wt total Hg and 0.34
methyl Hg. Mercury content in feathers of birds fed fish from
one contaminated area was 17.4 mg/kg total Hg in gulls and 1.39
in chickens; methylmercury was 16.94 and 0.45 mg/kg,
respecti vely. Hair from fishermen and their families in
villages near polluted water ranged from 1.52 to 11.61 mg/kg
total Hg and 0.34 to 5. 53 mg/ kg methyl Hg. Max imum levels were
found near the Ravenna factory. People from Nice contained
1.58-7.39 mg/kg total and 0.75-7.16 methyl Hg in their hair.
2607.
Windom, H. 1975. Heavy metal fluxes through salt-marsh
estuaries. In: Cronin, L.E. (ed.). Estuarine
research, vol:" 1. Chemistry, biology, and the
estuarine system. Academic Press, Inc., N.Y.:
137 - 152.
Flux of heavy metals through estuaries is controlled
by adsorption-desorption reactions, flocculation, precipitation,
and sedimentation, which occur at river-estuary and salt
marsh-sediment boundaries. Sane biological processes, such as
uptake by vegetation, recycle metals from estuarine sediments.
Mean metal concentrations in leaves and stalks of Spartina
alterniflora along the southeastern Atlantic coast is 750 mg
Fe/kg dry wt, 50 mg Mn/kg, 3.7 mg Cu/kg, 0.5 mg Cd/kg, and 0.2
mg Hg/kg. Average annual uptake by Spartina accounts for 3.0 to
17% of total imput of each metal into estuaries. Fates of
dissolved and particulate fractions of Fe, Mn, Cu, Cd, and Hg in
estuaries is discussed.
182
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2608.
Windom, H.L., W.S. Gardner, W.M. Dunstan, and G.A.
Paffenhofer. 1976. Cadmium and mercury transfer in
a coastal marine ecosystem. In: Windom, H.L. and
R.A. Duce (eds.). Marine pollutant transfer. D.C.
Heath and Co. Lexington, MA:135-157.
Transfer of cadmium and mercury from river discharge
and atmosphere through the Georgia Embayment along the SE
Atlantic coast is summarized. Average content of Georgia waters
is 0.10 ug Cdll and 0.06 ug Hg/l, with mean resident times of 2
yrs for Cd and 18 yrs for Hg. Sediments contained 1. 6 mg Cd/kg
dry wt and 0.07 mg Hg/kg dry wt. Among estuarine biota
salt-marsh grass Spartina alterniflora contained 0.5 mg Cd/kg
dry wt and 0.20 mg Hg/kg dr'Y wt; crab Uca sp. 0.2 for Cd and 0.3
for Hg; and snail Littorina sp. 0.8 for Cd and 2.6 for Hg. As
added Cd reached 10.0 ug/l, Cd concentration in the diatom
Skeletonema costatum increased to 4.0 mg/kg dry wt. The copepod
Pseudodiaptomus coronatus, included in the next higher trophic
level, followed similar Cd uptake patterns. Mixed phytoplankton
of Carteria sp., Dunaliella tertiolecta, and Nitzchia closterium
accumulated up to 2.0 mg Hg/kg dry wt as water levels rose to
o. 35 ug Hg/l. Cadmi um concentra ti ons in A tlanti c crooker,
Micropogon undulatus, a secondary consumer, increased to 0.23
mg/kg dry wt in stomach in 0.06 ug Cd/l, and to 0.27 ug/kg in
gills in 0.6 ug Cd/l; liver and muscle levels were not elevated
over controls. Cadmium and mercury transfer through an
estLBrine food chain was followed: 0.10 ug Cd/l and 0.06 ug
Hg/l in seawater; 0.20 mg Cd/kg dry wt and 0.45 mg Hg/kg dry wt
in phytoplankton; 0.15 and 0.15, respectively, for copepod
primary consumers; 0.40 and 0.06 for shrimp, and 0.04-0.07 and
0.10-0.50, respectively, for fish secondary consumers; and
0.05-0.22 and 0.17-1.07, respectively, for fish tertiary
consumers. Transfer efficiences for Georgia Embayment food
chains were 0.20 Cd for primary consumer, 0.08-0.80 for
secondary consumers, and 0.03-0.15 for tertiary consumer. For
mercury, efficiencies were 0.08, 0.1-0.9, and 0.8-3.0 for
respective trophic levels.
2609.
Wu, L. and J. Antonovics. 1978. Zinc and copper
tolerance of Agrostis stolonifera L. in tissue
cui ture . Amer. Jour. Botany 65: 268-271 .
When grown en basic medium without additional copper
and zinc, callus tissue from gFdsses Agrostis stolonifera
tolerant to neither metal had a greater dry wt than calluses
from tolerant plants. The Cu and Zn tolerant clones came from a
183
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copper refinery near Liverpool, England, where the soil was
heavily contaminated with Zn (700 mg/kg) and Cu (4000 mg/kg).
Grown on media containing 1.0 mg Cull or 12.0 mg Zn/l, tolerant
individuals produced calluses 5X the weight of nontolerant
ones. Metal uptake in culture resembled uptake by whole plants;
tolerant tissues accumulated higher metal concentrations.
Tolerant calluses contained up to 233 mg Cu/kg dry wt in 1.0 mg
Cull and 2.0 mg Znll and up to 470 mg Znlkg dry wt in 12.0 mg
Zn/l and 0.01 mg Cull. Maximum metal concentrations in
nontolerant calluses were 71 mg Zn/kg and 118 mg Cu/kg in
respective media. Plants regenerated from calluses had the same
Cu and Zn tolerance as parent clones regardless of time of
growth in culture and origin of shoot or root. Results support
previous evidence that metal tolerance is genetically determined
and acts at the cellular level.
2610.
Boyden, C.R., B.E. Brown, K.P. Lamb, R.F. Drucker, and
S.J. Tuft. 1978. Trace elements in the Upper Fly
River, Papau New Guinea. Freshwater Biology
8:189-205.
Concentrations of Ca, Mg, Cd, Co, Cu, Fe, Mn, Ni, Pb,
and Zn were determined in waters, sediments, and biota at
various sites in the Upper Fly River, New Guinea, between June
and September, 1974. Concentrations of ions and soluble metals
along the rivers ranged from 5500 to 42,300 ug/l for Ca, 700 to
1450 for Mg, 1 to 14 for Cu, 41 to 468 for Fe, < 2 to 39 for Mn,
-------
and 58-175 for Zn; and in liver and muscle of fishes
Melanotaenia vanheurni, Nematocentris rubrostriatus, Neosilurus
gjellerupi, Nedystoma dayi, Therapon sp., Parambassis gulliveri,
Ambassis sp., Lates calcarifer, Zenarchopterus novaeguineae,
Mogurnda mogurnda, and Lutjanus sp., 0.6-9.4 for Cd, 1-62 for
Cu, 10-5121 for Fe, 3-13 for Mn, 3-93 for Ni, 5-44 for Pb, and
36-612 for Zn. Metal levels in biota generally reflected
background concentrations at each site. Concentrations of Cd,
Cu, and Zn were la-ler in starved insects than unstarved
individuals, but no consistent changes were observed for Fe or
Mn.
2611.
Cunningham, P.A. and D.S. Grosch. 1978. A comparative
study of the effects of mercuric chloride and methyl
mercury chloride on reproductive performance in the
brine shrimp, Artemia salina. Environ. Pollution
15: 83-99.
Exposure to 0.01 rng/l mercuric chloride produced a
reduction in reproductive lifespan of Artemia from 54 days in
controls to 27 days; male lifespan decreased from 56 days in
controls to 34 days in 0.01 mg HgC12/1 and female lifespan
decreased from 53 to 20 days. Irrmersi on in O. 001 and 0.005 mg
HgC12/1 had no significant effects on lifespan. Mean brood
production dropped from 9.3 in controls to 6.2 in 0.001 mg
HgC12/1 and to 3.5 in 0.01 mg/l. When exposed to 0.005 and
0.01 mg/l methylmercuric chloride, Artemia had reduced
reproducti ve lifespans of 11.4 and 2.3 days, respectively,
compared to controls of 44 days. Also, male lifespan dropped
from 44.8 days to 2.0-28.6 days in 0.01-0.002 mg CH~HgCl/l,
and female lifespan decreased from 44.0 to 7.9 and 2.7 days in
0.005 and 0.01 rng/l. Mean brood productions dropped
significantly from 6.8 to 0.3-4.8 in 0.01-0.001 rng CH3HgCl/l.
Survi val of nauplii produced by treated parents was not reduced
at any mercuric chloride exposure tested, up to 0.01 mg Hg/l.
Naupliar survival vas reduced in several broods in 0.001 and
0.002 rng Hg/l as methylmercuric chloride. Pairs of adults
exposed to >0.002 rng CH3HgCl/l did not produce nauplii. Cysts
produced by pairs exposed to all concentrations of HgC12 or
0.001 and 0.01 rng CH3HgCl/l ~isplayed 50% less viability and
hatchability than controls. Methylmercuric chloride was more
toxic to adult Artemia than mercuric chloride, affecting both
production and offspring survival. Reciprocal cross experiments
wi th methylmercury exposure suggest that females are more
physiologically stressed than males in 0.001 and 0.002 mg
CH3HgCl/1.
185
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Finley, M.T. and R.C. Stendell. 1978. Survival and
reproductive success of black ducks fed methyl
mercury. Environ. Pollution 16:51-64.
A diet containing 3.0 mg Hg/kg was fed to black
ducks, Anas rubripes, for periods of 28 weeks during two
consecuti ve breeding seasons. Hens fed mercury had reduced
hatchability of eggs, 44 to 52% compared to 57 to 72% for
controls. Clutch size, egg production, and number of eggs
incubated were also reduced compared to controls over both
years. Breeder pairs fed mercury diets produced only 16
ducklings during t~ years, none of which survived more than one
week; controls produced 73 ducklings. Mercury residues in eggs,
embryos, and ducklings associated with contaminated diets
averaged about 30% lower during the second breeding season than
first year levels. Third eggs laid by treated hens contained a
mean of 6. 1 and 3.9 mg Hg/kg wet wt during the first and second
years. Brains of dead ducklings contained mean values of 3.2 to
7.0 mg Hg/kg wet wt and showed lesions characteristic of mercury
poisoning. Duckling muscle contained 5.4 to 6.2 mg Hg/kg, liver
contained 10.2 to 14.5, and feather 40.8 to 65.6 mg Hg/kg wet
wt. Mercury contents in tissues of adults fed mercury were 2.8
to 3.8 mg Hg/kg wet wt in brain, 4.0 to 4.5 in muscle, 11.2 to
16.0 in kidney, 21.3 to 23.1 in liver, and 56.1 to 65.7 in
feathers. Mercury levels did not differ in males and females.
2612.
2613.
Glandon, R.P. and C.D. McNabb. 1978. The uptake of
boron by Lema minor. Aquatic Botany 4:53-64.
Ambient boron was a determining factor in rate of
boron accumulation in tissue of the freshwater plant, L. minor.
After 6 days in 0.01 mg B/l, plants contained 0.01 mg B/kg dry
wt; levels were 0.06 mg/kg in 0.11 mg B/l and 0.09 mg/kg in 1.01
mg B/1. 1. minor growing in a pond in Belding, Michigan,
contained 988 to 3249 mg B/kg dry wt over the 1973 growing
seasoo. Ceratophyllum demersum from the same pond and collected
at the same time accumulated 69 to 195 mg B/kg, or 10-45X less
boron than L. minor.
2614.
Ka?1!lierczak, A., M. Adamska, and R. Gondko. 1978. The
content of copper, iron, and proteins in the serum of
decapoda occurring in Poland. Compo Biochem.
Physiol. 60A:11-12.
Copper and iron in hemolymph from 3 species of Polish
186
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freshwater crayfish were determined. Astacus astacus contained
44.0 mgll total Cu, 2.3 mgll free Cu, 41.4 mg/l bound Cu, and
1.4 mg bound Cu/g protein; ~. leptodactylus contained 30.9 mg
Cull, 2.5, 30.0, and 1.3 for respective Cu types; Orconectes
limosus contained 55.9 mg Cull, 3.5, 53.5, and 1.4 for
respective Cu types. Observed differences in total Cu
concentrations were due to differences in protein concentrations
between species. Irm content of A. astacus serum were 1.38
mg/l total and 1.33 free Fe; in~. IePtodact~ there were 1.89
and 1.55, respectively; and in O. limosus 3.1 and 2.37,
respectively. No bound iron was detected, indicating a lack of
ferro-proteins in serum.
2615.
Martin, J.-L.M., A. Van Wormhoudt, and H.J. Ceccaldi.
1977. Zinc-hemocyanin binding in the hemolymph of
Carcinus maenas (Crustacea, Decapoda). Compo
Biochem. Physiol. 58A:193-195.
Hemolymph of the crab C. maenas contained 44.7 mg
Culkg wet tissue and 32.2 mg Zn/~. Ninety-three percent of the
copper, or 41.6 mg/kg, was associated with hemocyanin; fibrin
contained 2.1 mg Cu/kg and blood cells, lipids, and carotenoids
contained 0.4 mg Cu/kg. All copper-binding proteins were
hemocyanin. Sixty-eight percent of the zinc, or 22.0 mg/kg, was
associated with hemocyanin; fibrin contained 2.3 mg Zn/kg and
blood cells, lipids, and carotenoids contained 3.1 mg Zn/kg. Zn
linked with hemocyanin was found on high molecular protein
fractions only. Specific zinc-binding proteins were not found
in serum of C. maenas.
2616.
Melhuus, A., K.L. Seip, H.M. Seip, and S. Myklestad.
1978. A preliminary study of the use of benthic
algae as biological indicators of heavy metal
pollution in Sorfjorden, Norway. Environ. Pollution
15:101-107.
Mean concentrations of Zn, Cu, Pb, and Cd in seawater
at 4 sampling sites in Sorfjorden, Norway, decreased from 313 to
113 ug Zn/l at sites closer to the mouth of the fjord, and
generally decreased from 6.3 to 3.7 ug Cull, from 8.9 to 4.3 ug
Pb/l, and from 2.2 to 0.81 ug Cd/l closer to the mouth. Range
of levels in seawater were 8.0 to 900.0 ug Zn/l, 1.0 to 23.0 ug
Cull, 1.0 to 92.0 ug Pb/l, and 0.5 to 9.0 ug Cd/l, with no trend
according to sampling site. Mean zinc concentrations in algae
Fucus vesiculosus, f. serratus, Ascophyllum nodosum, Chorda
187
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filum, and Enteromorpha sp. ranged from 950 to 7350 mg/kg dry
wt. Concentration factors (CF) for F. vesiculosus and A.
nodosum were 7100 to 24,000 over seawater at all sites.- Mean
levels of copper were 10.0 to 114.5 mg/kg dry wt with CF in 2
species ranging from 4800 to 20,000. Lead concentrations ranged
from 10.4 to 163.4, with a high of 301.5 mg/kg dry wt; CF were
1200 to 26,000 in 2 species. Mean cadmium levels were 3.0 to
29.0 mg/kg dry wt; CF were 4200 to 13,000. CFts for Zn and Cd
exhibited no trends with sampling location; however, Cu and Pb
CF values decreased towards the mouth of the fjord.
2617.
Murr~3 ~~. and R. Fukai. 1978. Measurement of
~+ 4 Pu in the northwestern Mediterranean.
Estuar. Coast. Mar. Sci. 6:145-151.
Measurements of Pu-239+240 were determined in
seawater, sediments, and mussels from the NW Meditteranean Sea
during 1973 and 1974. Levels ranged from 0.0005 to 0.0085 pCi/l
for seawater from the surface to 2000 m depth, 0.3 to 4.2 pCi/kg
dry wt for sediments along the shoreline and Rhone River, and
0.42 to 0.74 pCi/kg wet wt for whole body of mussels, Mytilus
galloprovincialis, 0.19 pCi/l for pallial fluid, 0.18 pCi/kg for
soft parts, and 0.61 for shells of mussels from the coastal
area. Relatively higher plutonium concentrations were found in
deep water, possibly correlated to vertical water movements
characteristic of this portion of the Meditteranean.
2618.
Murzina, T.A., loP. Lu~Oanov, and A.M. Chaplina. 1976.
Accumulation of Sr by freshwater plants in the
Ukrainian steppe zone. Hydrobiological Jour.
12:66-70.
Fifteen species of freshwater plants from five
reservoirs and ponds in the Ukrainian steppe zone concentrated
strontium-90 over water by concentration factors (CF) ranging
from 4.0 to 189.0 during spring, sumner, and autumn of 1971 and
1972. CF of Sr-90 was related to species and ecological
features of the plant. Accumulation values" in decreasing
order, were submerged and rooted plants, submerged and rooted
with leaves floating on the water surface, submerged and not
rooted, and semisubmerged plants. Strontium-90 levels increased
during the spring and sumner, generally reaching maxima in
July-August, then declined in autumn. CF in plants were
dependent on salt composition of water and, in particular, Ca
levels which ranged from 43 to 225 mg/l. Authors concluded that
188
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submerged plants Potamogeton perfoliatus, Myriophyllum spicatum,
and especially Chara sp. may serve as biological indicators of
strontium contamination.
2619.
Panigrahi, A.K. and B.N. Misra. 1978. Toxicological
effects of mercury on a freshwater fish, Anabas
scandens, Cuv. & Val. and their ecological
implications. Environ. Pollution 16:31-39.
Climbing perch, Anabas scandens, exposed to
concentrations of 5.0 to 15.0 mg Hg/l as mercuric nitrate died
within 24 hours. In 3 mg Hg/l, perch appeared lethargic and did
not feed for 5 days, then regained pre-test activity by day 8;
however, blindness and exophthalmia were noted in 24 of 35 fish
between days 20 and 36. Respiration rate was reduced from 0.19
to 0.02 mg 02/gm/hr after 21 days in 3.0 mg Hg/l, but fish
recovered partially when transferred to fresh Hg-free water.
After 45 days, treated fish accumulated 2.8 mg Hg/kg wet wt in
muscle and 3.0 in liver; control fish contained <0.002 mg Hg/kg
in both tissues. Haemoglobin percentage, red blood cell count,
body wt, and protein content of Hg-exposed fish were reduced
considerably when compared to controls. Physiological and
biochemical disorders were related to mercury concentrations in
tissue. Algae accumulated 0.76 mg Hg/kg wet wt and Hydrilla
plants 0.83 mg/kg wet wt during exposure for 45 days in 0.3 mg
Hg/l.
2620.
Ryndina, D.D. 1976. Accumulation and fixation of
radionuclides by algal polysaccharides.
Hydrobiological Jour. 12:33-37.
Sorption and desorption of nuclides of calcium,
cesium, cobalt, iron, manganese, strontium, yttrium, and zinc by
polysaccharides, alginic acid, cellulose-algtilose, and barium
complex of fucoidan, was measured in marine brown algae
Cystoseira, Padina, Laminaria, and Phyllophora collected from
several Ukrainian bays. Algulose accumulated Ce-144 by a factor
of 2740, Co-57 to 990, Y-91 to 9960, and Zn-65 to 9960 from the
environment. Algulose from fresh C. barbata concentrated
Ce-144, Co-57, Fe-55, Mn-54, and Zn-65 to a greater extent than
samples from decomposing organisms, apparently owing to
polysaccharide structural changes during detritus formation.
Alginic acids from Cystoseira concentrated Ce-144 by 3360X,
Fe-55 to 350, Sr-90 to 440, and Y-91 to 300. Accumulation
coefficients of the barium complex of fucoidan in Cystoseira
reached 31,410 for Ce-144, 9710 for Co-57, 6340 for Mn-54, 2320
189
-------
for Y-91, and 12,220 for Zn-65. High sorption properties make
Ce-144, Co-57, and Y-91 extraction from the environment very
efficient. Stability of fixation was high for Y-91 with all
three polysaccharides; desorption at equilibrium was only 0.6 to
12.0%, with a high of 37.2%. Desorption of Zn-65 from algulose
was 24 to 47%, Mn-54 from barium fucoidan was 44 to 45%, and
Fe-56 from algulose was 12 to 57%, with a high of 90%. Other
radionuclides generally did not form stable bonds with
polysaccharides.
2621 .
Sarkka, J., M.-L. Hattula, J. Janatuinen, and J.
Paasi virta. 1978. Mercury and chlorinated
hydrocarbons in plankton of Lake Paijanne, Finland.
Environ. Pollution 16:41-49.
Total mercury content in plankton composed mainly of
copepods and other small crustaceans, rotifers, and algae during
1972-1974 ranged between 23 and 718 ug Hg/kg dry wt, with a mean
of 178 ug/kg. Differences in mercury content due to time of
year or size fraction of plankton sample were not significant.
Mercury levels were generally of the same order as marine
plankton, but lCMer than polluted regions elsewhere.
Concentrations of polychlorinated biphenyls and DDE and DDT were
also determined.
2622.
Sharpe, M.A., A.S.W. deFreitas, and A.E. McKinnon.
1977. The effect of body size on methylmercury
clearance by goldfish (Carassius auratus). Environ.
Biol. Fishes 2:177-183.
WhJle body retention of methylmercury ingested by
goldfish, ranging in body weight from 1.0 to 50 g, was measured
by adding tracer amounts of labelled CH3HgCl to a single
ration of food. Mean amount of methylmercury ingested ranged
from 0.9 to 12.9 mg/fish, with amount deposited in body tissue
extending from 0.7 to 11.0 mg CH3Hg/fish. Body methylmercury
was cleared faster in snaller fish per unit weight, with a
biological half-life of 53 days for 5 gm fish compared to 160
days for 43 gm fish. Whole body clearance was a first order
process in which mercury acted as a single rmogeneous
compartment described by: Rpcl = kclPW-°.5 , where R 1
is elimination rate from body (ug/day); kcl = eliminarion
constant for 1 gm fish, is 0.029/day; P is methylmercury body
content (ug); and W weight of fish (gm). Results suggest
metabolic rate could be a factor in controlling clearance rate;
190
-------
TECHNICAL RHORT OAT A
(/'/, (He r[,h//JllIn" I/Um "II rll,' I,' ,n,' 1>''101<' CUIJI/'/CI/IIK)
1_~ii~~'~(;U-79~ 13-;---1_... -----. ---~-l3_~_E_C~1 EN_~~S_AC_C~~S~ O_~ :~-'------
.. TITLI.ANDSUI3IITl.[ \5,REPORTDATE
Activated Carbon Process for Treatment of Wastewaters July 1979 issuing date
,uA:;~;~,:~i:g_~eXa~alen t ChromiU=-___nnu -u u uu~__I:~~:::::::::::::::::::: :::~AT NO
C. P. Huang and Alan R. Bowers 1
;nE::;:~ ~-~~-Oo~G~:~~:~::NAM.E- AN DADD.R.E-s-s---~-- -.. ~R01GB~:~ ~ LEMENT NO.
Newark, Delaware 19711 \11, CONTRACT)GRANT NO.
I
R-804656
-------~+ -----~~- ~
13. TYPE OF REPORT AND PERIOD COVERED
Final
114. SPONSORING AGENCY CODE
I
I EPA/600/12
12. SPONSORING AGENCY NAME AND ADORESS
Industrial Environmental Research Lab.
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati Ohio 45268
15. SUPPLEMENTARY NOTES
- Cinn, OH
16. ABSTRACT
The removal of hexavalent chromium. Cr(VI), from dilute aqueous solution by an
vated carbon process has been investigated. Two removal mechanisms were observed:
valent chromium species were removed by adsorption onto the interior carbon surface
or through reduction to the trivalent state at the external carbon surface.
The effects of Cr(VI) concentrations, pH, carbon dosage and extent of mixing in the
reaction vessel were studied in the batch mode and in continuous flow packed column ex-
periments in the laboratory. The adsorptive capacity of the carbon and the rates of
Cr(VI) adsorption and reduction have been determined.
Thermal regeneration of the exhausted carbon was examined. along with caustic or
acid stripping solutions and a combined caustic-thermal process.
A case study was presented and the experimental data and rate expressions obtained
from the data were used to evaluate the design variables (i.e., pH, carbon dose. Cr(VI)
concentration and mixing in the reaction vessel). Several Cr(VI) treatment schemes were
proposed. together with an economic analysis of each scheme.
acti-
hexa-
and/
DlSCHlf'rOAS
KEY WOROS AND DOCLIMENT ANALYSIS
l'.IUENTIFIERS/OPEN ENDED TEAMS
c. COSATI Fio)ld/Group
17.
Adsorption
Reduction
Activated
Carbon
Batch mode adsorption
Packed Carbon Column
Regeneration
Hexavalent Chromium
13B
i~ CIsr-RIBUTION STATEMEN r
-- - --
--------~9 SECURITY CLASS (TJlisReport) 121. NO, OF PAGES
Unclassified 81
'20 s'E'cu'RIT-yTu\ss7filis pasej---!22. PAiCE------
Unclassified I
Release to Public
t.f'A Form 2220.1 (9.73)
71
~ U,S, GOVERNMENT PRINTING OFFICE. 1979 -657 -060 /5 3 56
-------
uptake. An effective negative feedback appeared to operate
continually on the Na transport mechanism, which generated
carrier-mediated exchange and resembled those of freshwater
mosquito and chironomid larvae.
2627.
Sullivan, J.F., B.R. Murphy, G.J. Atchison, and A.W.
McIntosh. 1978. Time dependent cadmium uptake by
fathead minnows (Pimephales promelas) during field
and lab ora tory exposure. Hydrobiologia 57: 65-68.
Minnows exposed to 2.5 ug Cd/l in an industrially
polluted lake accumulated 3.19 mg Cd/kg whole body dry wt in 12
hrs; pretest level was 0.29 mg Cd/kg. Minnows, averaging 0.002
mg Cd/kg whole body, exposed to 48 ug Cd/l as CdC12 in a
continuous flow laboratory system contained 0.5 mg Cd/kg dry wt
after 10 hrs, and did not reach comparable field levels until 8
days, at 3. 57 mg Cd/ kg. Whole body Cd in lab ora tory exposures
peaked at 8.26 to 10.70 mg/kg within 17-20 days. Authors
suggest that the more rapid uptake of cadmium by fish in the
field may be due to additional physiological stress of other
pollutants or interactions between pollutants, increased water
turbidity and temperature which increases fish ventilation and
metabolism, and decreased hardness which increases the
percentage of total metal in ionic form and therefore available
for biological accumulation.
2628.
Weis, P. and J. S. Weis. 1978. Methylmercury inhibition
of fin regeneration in fishes and its interaction
with salinity and cadmium. Estrnr. Coast. Marine
Sci. 6: 327 - 334.
Regeneration of amputated caudal fins in mullets,
MugU cephalus, was retarded by exposure to methylmercuric
chloride in diluted seawater of 9 0/00 S. By 13 days,
regenerated fin length was 3.0 rmn in controls, 2.7 nm in fish
from 0.001 mg CH3HgC1/l, and 2.4 in 0.01 mg CH3HgCl/l. The
response was correlated with whole body uptake of mercury;
mullets contained < O. 1 mg Hg/kg in control water, 0.3 mg/kg in
0.001 mg CH3Hg/l, and 5.0 mg/kg in 0.01 mg/l. Fin
regeneration after 14 days in killifish, Fundulus, reached
3.3-3.4 nm in 36 0/00 S and only 2.4-2.7 in 9 0/00 S. Addition
of 0.01 and 0.05 mg CH~Hg/l reduced regeneration rates to 2.9
and 2.4 mm, respectively, in full strength SW; no significant
decrease was observed in diluted SW with methylmercury, in which
growth rate was already depressed. Mean fin regeneration in
193
-------
Fundulus in 36 0/00 S was 2.6-3.2 rom in 0.025 mg CH3HgCl/l and
2.9-3.4 in 0.025 mg CdC12/1 at day 14, compared to 3.2-3.6 in
controls. Mixtures of 0.005 or 0.025 mg Cd/l with 0.005 or
0.025 mg Hg/l counteracted growth inhibition of methylmercury,
so that fish exhibited fin growth rates similar to controls over
14 days exposure.
2629.
Wentsel, R., A. McIntosh, and G. Atchison. 1977.
Sublethal effects of heavy metal contaminated
sediment on midge larvae (Chironomus tentans).
Hydrobiologia 56:153-156.
Insect larvae were maintained for 17 days in lake
sediments of learn or silt-learn containing various levels of Cd,
Cr, and Zn. Survival was 82% in control sediment containing 0.6
mg Cd/kg dry wt, 17.0 mg Cr/kg, and 77.0 mg Zn/kg; 70% survived
in sediments of 420 mg Cd/kg dry wt, 1510 mg Cr/kg, and 8330 mg
Znlkg; 53% survived in 210 mg Cd/kg, 800 mg Cr/kg, and 4390 mg
Zn/kg; 50% survived in 960 mg Cd/kg, 2130 mg Cr/kg, and 16,400
mg Znlkg; and 47% survived in 1030 mg Cd/kg, 1640 mg Cr/kg, and
17,300 mg Zn/kg. Mean length and weight of larvae from control
sediment were 1.83 cm and 2.86 mg; 3Ilallest larvae were found in
sediments with 960 mg Cd/kg dry wt, 2130 mg Cr/kg, and 16,400 mg
Znlkg, with mean length of 0.82 cm and weight of 0.20 gm. A
linear relationship was found for the square root of length vs.
sed iment metal levels. -
2630.
Wentsel, R., A. McIntosh, and W.P. McCafferty. 1978.
Emergence of the midge Chironomus ten tans when
exposed to heavy metal contaminated sediment.
Hydrobiologia 57:195-196.
In test chambers with uncontaminated sediment
containing 0.6 mg Cd/kg dry wt, 17.0 mg Cr/kg, and 77.0 mg
Zn/kg, a mean of 14.2 adult chironomids, C. tentans, emerged
from larval stages over 14 days following-the first emergence.
When exposed to sediments containing 1030 mg Cd/kg dry wt, 1640
mg Cr/kg, and 17,300 mg Zn/kg, an average of ooly 4.3 adults
emerged. Number of emergences per day peaked at 8 to 16 over
the trial period in controls, maximum emergences were 4 to 7 per
day in contaminated sediments, with a delay of 2 days before
adult emergence. Authors concluded that test sediments caused a
decline and delay in emergence of chironomids by stressing or
killing the insects.
194
-------
2631 .
Whitaker, J., J. Barica, H. Kling, and M. Buckley. 1978.
Efficacy of copper sulphate in the suppression of
Aphanizomenon flos-aquae blooms in prarie lakes.
Environ. Pollution 15:185-194.
Five shallow eutrophic prarie lakes in the
Erickson-Elphinstone area of Manitoba, Canada, were treated with
copper sulphate to control A. flos-aquae algal blooms and prevent
summer fish kills. ConcentratIOnS of 25 to 360 ug Cull were
added to lakes and 100 to 3000 ug Cull to experimental tubes in
early July when algal filaments were about 10 mm in length.
Chlorophyll a concentrations were 48 to 55 ugll and bloom
compositions-were 90 to 98% A. flos-aquae before treatment.
Algal control was achieved at all test concentl'ations. In
general, chlorophyll a declined to 2.0 to 4.0 ug/l after 4 days
and A. flos-aquae completely disappeared. Algal biomass remained
low for2to 3 wks before gradually increasing. Chlorophytes,
diatoms, and chryophytes usually dominated the algal community
for the remainder of the ice-free season. In two other lakes,
however, cyanophytes Microcystis spp. were predominant.
Concentrations between 25 and ~o ug Cull, below recommended
levels by provincial agricultural departments, were effective in
Microcvstis-dominated lakes. Copper concentrations in water
returned to background levels in 8 to 10 days. Single
applications <40 ug Cull are below toxic concentrations for
rainbCM trout; therefore, Cu fish kills will not occur, and Cu
will not concentrate in fish stock.
2632.
Whittle, K.J., R. Hardy, A.V. Holden, R. Johnston, and
R.J. Pentreath. 1977. Occurrence and fate of organic
and inorganic contaminants in marine animals. In:
Kraybill, H.F., C.J. Dawe, J.C. Harshbarger, ana-R.G.
Tardiff (eds.). Aquatic pollutants and biologic
effects with emphasis on neoplasia. Annals New York
Acad. Sci. 298:47-79.
Concentrations of contaminants in marine systems
including hydrocarbons, organochlorine and organophosphorus
pesticides, other organic compounds, heavy metals, and
radionuclides are reviewed. Estimates of mean seawater
concentrations of important heavy metals are 2.3 to 2.6 ug/l
arsenic, 0.05 to 0.1 cadmium, 0.5 to 0.6 chromium, 3.0 copper,
0.03 lead, 2.0 manganese, 0.05 to 2.0 for mercury, 2.0 to 7.0
nickel, 0.09 to 0.45 selenium, O. 1 to 0.3 silver, and 5.0 to 10.0
zinc. Mean values from the literature for Hg, Pb, Cd, Cr, and As
195
-------
in some conmercially important marine animals are: fishes
(flounder, cod, haddock, hake, pollock, tuna) 0.07 to 0.51 mg
Hg/kg wet wt, 0.28 to 1.64 for Pb, 0.03 to 0.26 for Cd, 0.08 to
0.11 for Cr, and 2.14 to 2.56 for As; molluscs (clams, oysters)
0.08 to 0.10 mg Hg/kg wet wt, 1.60 to 24.9 for Pb, 0.22 to 1.88
for Cd, 0.12 to 0.33 for Cr, and 3.13 to 9.12 for As; and
crustaceans (blue crab, brown shrimp) 0.16 to 0.70 mg Hg/kg wet
wt, 0.46 to 0.54 for Pb, 0.09 to 3.62 for Cd, 0.07 to 0.14 for
Cr, and 8.71 to 12.16 for As. Dose rates of radionuclides,
including Cs-137, Pu-239, and Sr-90, to phytoplankton,
zooplankton, molluscs, crustaceans, and fish from various
environmental sources are also listed.
2633.
Wittig, K.P. and S.C. Brown. 1977.
newt, Notophthalmus viridescens.
Physiol. 58A:49-52.
Sodium balance in the
Compo Biochem.
Sodium fluxes of N. viridescens were higher than those
of any amphibian previously examined. Total sodium loss from
unfed newts was 1136 mg/kg/day, about 102% of total body Na/day.
Integumental loss accounted for 68% of the total, and urinary
loss the remainder. Integumental Na uptake exhibited saturation
kinetics. M3.ximum rate of transport was 5380 mg/kg/day;
indicating only a weak affinity for Na. The high capacity of the
transport system allowed losses to be replaced at external sodium
concentrations approaching 2.3 mg/l.
2634. Yamamoto, Y., T. Ishii, M. Sato, and S. Ikeda. 1977.
Effect of dietary ascorbic acid on the accumulation of
copper in carp. Bull. Japan. Soc. Sci. Fish.
43:989-993.
Dietary L-ascorbic acid (AsA) decreased the rate of
copper accumulation in carp, Cyprinus carpio, exposed to 0.05 mg
Cull as CuS04 for 9 weeks. Control fish contained 1.0 to 2.5
mg Cu/kg wet wt in gills and 5.0 to 15.0 mg Cu/kg in
hepatopancreas after 9 weeks regardless of AsA in diet. Carp
exposed to Cu and fed AsA contained 3.5 mg Cu/kg wet wt in gill
by 9 weeks and 25.0 mg/kg in hepatopancreas; exposed carp with no
AsA contained 4.5 mg Cu/kg dry wt in gill and accumulated up to
55.0 mg/kg in hepatopancreas. Copper contents in other tissues
were also maximum in carp exposed to Cu without AsA: kidney
contained 4.0 mg/kg wet wt, intestine 8.1, vertebra 2.7, and
serum contained 2.7 mg Cull after 9 weeks. Accumulation of
copper reduced hepatopancreas AsA levels to 125 and 60 mg/kg wet
196
-------
wt in exposed fish with and without dietary AsA, respectively.
Controls contained about 250 mg AsA/kg. Hepatic L-gulonolactone
oxidase activity was also reduced in carp maintained in 5.0 mg
Cull. Body weight in control fish increased from 85 to 125 gm
over 9 weeks, while Cu-exposed carps weighed 80-85 gm after this
period; presence of dietary AsA made no difference to either
group. Authors concluded that AsA prevented copper accumulation
and that accumulated Cu decreased AsA level in hepatopancreas by
inhibiting biosythesis of AsA in carp.
2635.
Anon. 1978. Selected pollution profiles: North
Atlantic, North Sea, Baltic Sea, and Mediterranean
Sea. Ambio 7:75-78.
Data from the International Council for the
Exploration of the Seas (ICES) monitoring programs between 1972
and 1976 for mercury, DOT and polychlorinated biphenyls in the
Baltic and North Seas and North Atlantic were summarized and
compared with data from the Mediterranean. Mercury levels ranged
from <0.02 to 0.09 mg/kg wet wt for mussels and 0.04 to 0.18
mg/kg for shrimp in the North Sea, with no significant difference
between years. Deep sea prawns from the North Atlantic all had
lcw levels of < 0.03 mg Hg/kg; no appra isal was made from the
Baltic Sea because only small numbers of bivalves were analyzed
during this period. Codfish muscle contained mean mercury levels
of 0.02 to 0.48 mg/kg over the 6 years in the North Sea;
concentrations ranged from 0.02 to 0.88 mg Hg/kg in the Baltic
Sea with the highest value from Oresund. In the North Atlantic,
mercury concentrations ranged from 0.01 to 0.09 mg/kg wet wt in
cod liver and 0.02 to 0.32 in muscle; lowest muscle levels were
from Greenland and highest from the Irish Sea. In general, fish
from the Mediterranean had higher concentrations, from 0.15 to
0.40 mg Hg/kg, than mussels, but the same as squid and octopus.
Hg levels 2-3X higher than fish from the Atlantic and above
official "safe" standards used by most Mediterranean countries
were found in tuna and swordfish, reaching 2.5 to 3.5 mg/kg wet
wt in tuna.
2636.
Austin, B., D.A. Allen, A.L. Mills, and R.R. Colwell.
1977. Numerical taxonomy of heavy metal-tolerant
bacteria isolated from an estuary. Canadian Jour.
Microbiol. 23:1433-1447.
A total of 230 strains of metal-tolerant bacteria from
Chesapeake Bay and Colgate Creek, where environmental levels were
197
-------
52 mg Coil, 18 mg Pb/l, 39 mg Hg/l, and 8.0 mg Mo/l in water and
0.0 mg Co/kg, 26-38 mg Pb/kg, 8.0-13.0 mg Hg/kg, and 4.0-24.0 mg
Mo/kg in sediments, were isolated on a medium containing 100 mg
Coil, 100 mg Pb/l, 10 mg Hg/l, and 100 mg Mo/l. Biochemical,
cultural, morphological, and physiological characters were
analyzed; simple matching and Jaccard coefficients were
calculated from the taxonomic data. Bacillus, Erivinia,
Mycobacterium, Pseudomonas, and coryneforms were identified from
the strains. It was concluded that metal tolerance in estuarine
water and sediment bacteria occurs among a restricted range of
taxa distributed throughout the estuarine environment.
2637.
Bradley, B.P. 1975. The anomalous influence of salinity
on temperature tolerances of sumner and winter
populations of the copepod Eurytemora affinis. Biol.
Bull. 148:26-34.
Times to succumb (TS) and time to recover (TR) from
temperature shock, by raising or lowering temperature one degree
every fi ve minutes, were measured in copepods acclimated for 24
hrs at 4 salinities. Temperature tolerance limits were
determined as the temperature at which half the test animals
became inactive. Copepods collected in March, when environmental
salinity was 6 0/00 S, had TS values from 3 minutes in 3 0/00 S
up to 5 minutes in 15 0/00 S; TR values ranged from 19 min in 3
0/00 S to 3 min in 15 0/00 S. TS values for copepods collected
in August, when salinity was < 1 0/00 S, were from 4 min in 3 0/00
S up to 13 min in 15 0/00 S; TR values ranged from 13 min in 3
0/00 S to <2 min in 15 0/00 S. TS and TR values were
significantly different between populations and between
salinities of 3, 9, 12, and 15 0/00 S. Without prior acclimation
to test salinities, TS values for copepods collected in March
were 2.9 min in 0.0-1.0 0/00 Sand 3.4 min in 12 0/00 S; TR
values were 20 min and 12 min, respectively. TS values for
copepods collected in August were 3 min in 0.0-1.0 0/00 S and 5
min in 12 0/00 S; the TR values were 13 and 10 minutes.
2638.
Cardwell, R.D., D.G. Foreman, T.R. Payne, and D.J.
Wilbur. 1976. Acute toxicity of selenium dioxide to
freshwater fishes. Arch. Environ. Contamin. Toxicol.
4:129-144.
Decreasing order of species sensitivity to selenium
dioxide was determined as: fathead minnow Pimephales promelas,
flagfish Jordanella floridae, brook trout Salvelinus fontinalis,
198
-------
channel catfish Ictalurus punctatus, goldfish Carassius auratus,
and bluegill Lepomis macrochirus. LC-50 values for juvenile
minnows were 31.2 mg Sell (15.5 hr), 7.3 mg/l (96 hr), and 2.9
mg/l (168 and 220 hr); for adult trout these values ranged from
87.3 mg Sell (6 hr) to 14.3 mg/l (96 hr); for juvenile catfish
LC-50 values extended from 46.7 mg Sell (23 hr) to 19.1 mg/l (94
hr); for juvenile goldfish these were 110.0 mg Sell (12 hr), 36.6
mg/l (96 hr), and 8.8 mg/l (336 hr); for juvenile bluegill LC-50
values ranged from 126.6 mg Sell (8 hr) to 17.6 mg/l (336 hr);
and for juvenile flagfish LC-50 values ranged from 37.6 mg Sell
(44 hr) to 11.2 mg/l (83 hr). Minnow and flagfish juveniles
exposed to Se for 24 hr showed a limited delayed mortality but no
effect on growth over a 28 day period.
2639.
Casterline, J.L., Jr., and G. Yip. 1975. The
distribution and binding of cadmium in oyster,
soybean, and rat li ver and ki dney . Arch. Envi ron .
Contamin. Toxicol. 3:319-329.
Tissue of oysters grown for 6 days in water with 0.1
mg CdC12/1 contained 2.66 mg Cd/kg in the combined cell
fraction of nuclei, mitochondria, and microsomes, with 24.4 mg
Cd/kg in total homogenate and 21.4 mg/l in total supernatant.
Cadmium was principally bound to proteins of 9,200 to 13,800
molecular wt. Significant amounts were also associated with
fractions 3,000 and 50,000. Distribution of cadmium after
exposure to Cd and/or Cd-109 was also determined in soybeans and
rat liver and kidneys.
2640.
Dieter, M.P., M.C. Perry, and B.M. Mulhern. 1976. Lead
and PCB's in canvasback ducks: relationship between
enzyme levels and residues in blood. Arch. Environ.
Contamin. Toxicol. 5:1-13.
Blood samples from ducks Aythya valisineria collected
from Chesapeake Bay in winter of 1974 were analyzed for lead and
organochloride contamination. Delta-aminolevulinic acid
dehydrogenase (ALAD) activity in blood provided an estimate of Pb
contamination in waterfowl. Ducks containing normal blood levels
of lead, that is 59-64 ug Pb/l, had ALAD activities of 98-110
units, with no difference between sexes. Sixteen of 95 ducks
showed >50% enzyme inhibition with a mean activity of 28 units
with blood lead concentrations of 263 ug/l, 4X normal. Ducks
containing 525 to 630 ug Pb/l in blood had enzyme activities of
{25 units. Lead was a more prevalent environmental contaminant
199
-------
than organochloride compounds in ducks; 17% of the blood samples
had <50% ALAD activity due to Pb contamination, but only 11%
exhibited abnormal activities of two other enzymes known to
respond to organochloride poisoning.
2641 .
Dillon, T .M. 1977. Mercury and the estuarine marsh clam,
Rangia cuneata Gray. 1. toxicity. Arch. Environ.
Contamin. Toxicol. 6:249-255.
LC-50 (96 hr) values for clams exposed to mercuric
chloride were 0.122 mg Hg/l when clams were acclimated in 2 0/00
S, and 0.058 mg/kg in 15 0/00 S. The LC-50 (72 hr) values were
0.242 mg Hg/l in 2 0/00 S, and 0.057 in 15 0/00 S. Clams
acclimated to 0.008 mg Hg/l for 2 weeks, followed by 9 days in
mercury-free seawater, survived longer during exposure to 0.87 mg
Hg/l than non-acclimated clams. At 170 hrs, 75% of
non-acclimated clams were dead; at 220 hrs, only 55% of
acclimated clams had succumbed. At 168 hours dead non-acclimated
specimens contained 12 mg Hg/kg wet wt, and dead acclimated clams
32 mg Hg/kg.
2642.
Eganhouse, R.P. and D.R. Young. 1978. Total and organic
mercury in benthic organisms near a major submarine
wastewater outfall system. Bull. Environ. Contamin.
Toxicol. 19:758-766.
Mercury levels were measured in marine benthic animals
to determine whether sediment concentrations of 0.14 to 5.50 mg
Hg/kg dry wt and wastewater particulate concentrations of 4.0 to
5.0 mg Hg/kg dry wt, off Palos Verdes Peninsula, California, were
reflected in local biota. Median mercury levels in ug/kg wet wt,
in Dover sole Microstomus pacificus from Palos Verdes were 52 in
muscle, 99 in liver, 41 in kidney, and 24 in gill; Hg content in
Dover sole from Catalina Island, a control site, was generally
hjgher at 157 in muscle, 141 in liver, 30 in kidney, and 19 in
gills. Crabs Mursia gaudichaudii from Palos Verdes contained 18
ug Hg/kg wet wt in muscle and 33 ug/kg in digestive gland;
specimens from Catalina Island contained 158 and 81,
respecti vely. Muscle of prawns Sycionia ingentis contained 38 ug
Hg/kg wet wt from Palos Verdes and 49 from Catalina; gonads of
urchins Allocentrotus fragilis contained 20 ug Hg/kg wet wt from
Palos Verdes and 34 from Catalina; and whole body of sea slugs
Pleurobranchaea california contained 16 ug Hg/kg wet wt from
Palos Verdes and 11 from Catalina. Instead of showing enhanced
uptake and accumulation, outfall organisms generally had similar
200
-------
and sometimes depressed tissue concentrations of mercury. Mean
organic mercury concentrations, in ug/kg wet wt, in animals
collected off Palos Verdes Peninsula were for sole, 41 in muscle,
9 in liver, and 10 in gills; for crabs, 17 in muscle and 5 in
digestive glands; for prawns, 29 in muscle; for urchins, 3.0 in
gonads; for sea slugs, 7.0 in whole body; and for snails
Callinaticina oldroydi, 16 in viscera. Average percent organic
mercury ranged from 9.6% in liver from sole to 87.1% in crab
muscle.
2643.
Frank, R., M.V.H. Holdrinet, and W.A. Rapley. 1975.
Residue of organochlorine compounds and mercury in
birds' eggs from the Niagara Peninsula, Ontario.
Arch. Environ. Contamin. Toxicol. 3:205-218.
Eggs from 20 species of birds from both terrestrial
and aquatic food chains, were collected from the Niagara
Peninsula, Ontario, Canada, in 1971, and analyzed for total
mercury, organochlorine insecticides, and polychlorinated
biphenyls. Among marsh and aquatic feeders, the
herbivorous-insectivorous red-winged blackbird Agelaius
phoeniceus, Canada goose Branta canadensis, and mallard Anas
platyrhynchos contained mean mercury levels of 0.68, 0.12, and
0.15 mg/kg, respectively, in whole eggs. Mean mercury
concentrations in eggs from the aquatic carnivores herring gull
Larus argentatus, black-crowned night heron Nycticorax
nycticorax, and common tern Sterna hirundo, were 0.74, 0.64, and
0.83 mg Hg/kg. Eggs of carnivorous species at the top of the
aquatic food chain had the highest mean mercury residues. Eggs
of terrestrial carnivores contained 0.06 to 0.09 mg Hg/kg, eggs
of omnivores contained 0.12 mg Hg/kg, and herbivores-insectivores
contained 0.06 to 0.07, with a high of 0.18 in starling eggs.
2644.
Giddings, J.M. and G.K. Eddlemon. 1977. The effects of
microcosm size and substrate type on aquatic microcosm
behavior and arsenic transport. Arch. Environ.
Contamin. Toxicol. 6:491-505.
The fate of 0.05 mg As/I, labelled with H3As-7404'
was studied in 12 freshwater microcosms of two sizes and
substrates. Most of the arsenic moved into mud of lake sediment
microcosms within 2 weeks, but remained in water in sand
microcosms. Water in large (70 1) aquaria with lake sediment
contained 0.007-0.012 mg As/I and in small (7 1) aquaria
contained 0.001-0.004 mg/l after 5 weeks; water in tanks with
201
-------
sand contained 0.046-0.050 and 0.029-0.037 mg As/l,
respectively. Lake sediments contained 0.40-0.68 mg As/kg dry wt
in large tanks and 0.28-0.51 in small tanks; sand contained only
0.13-0.18 mg As/kg in large tanks and 0.08-0.12 in smaller
microcosms. Arsenic concentrations, in mg/kg dry wt, in algae
communities with sediment were 10.5 to 19.1 in 70 1 tanks and 6.0
to 12.9 in smaller tanks and with sand were 33.8 to 65.7 in large
and 9.3 to 14.3 in small tanks; levels in snails were 1.8 to 3.3,
1.2 to 1.5, 0.44 to 0.58, and 0.37 to 0.79, respectively, and in
zooplankton were 6.8 in 70 1 tanks with sediment and 8.3 to 10.4
in 70 1 tanks with sand. Maximum bioaccumulation ratios over
water were in sediment microcosms; ranging from 970 to 9190 for
algae, 164 to 1030 for snails, and 630 for zooplankton.
2645.
Greichus, Y.A., A. Greichus, B.D. Amman, D.J. Call, D.C.D.
Hamman, and R.M. Pott. 1977. Insecticides,
polychlorinated biphenyls and metals in African lake
ecosystems. I. Hartbeespoort Dam, Transvaal and
Voelvlei Dam, Cape Providence, Republic of South
Africa. Arch. Environ. Contamin. Toxicol. 6:371-383.
Average metal concentrations in Hartbeespoort Dam and
Voelvlei Dam in water, respectively, were 0.001 and 0.003 mg
As/l, <0.001 and 0.002 for Cd, 0.003 and 0.013 for Cu, 0.045 and
0.038 for Mn, 0.004 and 0.012 for Pb, 0.036 and 0.025 for Zn,
and <0.001 for Hg; levels in sediments were 75 and 16 mg As/kg
dry wt, 0.87 and 0.19 for Cd, 41 and 15 for Cu, 680 and 340 for
Mn, 63.0 and 9.0 for Pb, 260 and 49 for Zn, and 0.6 and 0.06 for
Hg. In fish composite samples these values were 2.3 and 2.3 mg
As/kg dry wt, 0.05 and 0.06 for Cd, 2.9 and 3.8 for Cu, 12.0 and
9.2 for Mn, 1.0 and <0.1 for Pb, 120 and 55 for Zn, and 0.52 and
0.39 for Hg. In Hartbeespoort, algae contained 1.5 mg As/kg dry
wt, 0.06 Cd, 2.7 Cu, 96 Mn, <0.1 Pb, 39 Zn, and 1.6 Hg; water
hyacinth contained 4.1, 0.23, 12, 840, 2.6, 42, and 0.71,
respecti vely. Worms from Voelvlei contained 5.2 mg As/kg dry
wt, <0.01 for Cd, 21 for Cu, 15 for Mn, 5.1 for Pb, and 41 for
Zn; insects contained 5.2, 0.09, 22, 28, 5.6, and 78,
respecti vely. Metal levels in carcasses of fish-eating birds
were, for cormorants from Hartbeespoort and darters from
Voelvlei, respectively, 1.7 and 1.3 mg As/kg dry wt, 0.59 and
0.05 for Cd, 4.8 and 6.3 for Cu, 8.8 and 5.0 for Mn, 2.4 and 0.28
for Pb, 130 and 62 for Zn, and 1.6 and 1.1 for Hg. In general,
metal concentrations were higher in feathers and lower in brain
tissue than in carcasses. Darter eggs without shells contained
2.3 mg As/kg dry wt, <0.01 for Cd, 5.8 for Cu, 1.3 for Mn, < 0.1
for Pb, 41 for Zn, and 0.84 for Hg. Hartbeespoort Dam had higher
202
-------
levels than Voelvlei for all metals in sediments and birds except
Cu in carcasses. Mercury levels in bird carcasses ranged from 2
to 5X greater than fish, and lead ranged from 2 to 10X higher.
2646.
Greig, R.A., D.R. Wenzloff, A. Adams, B. Nelson, and C.
Shelpuk. 1977. Trace metals in organisms from ocean
disposal sites of the middle eastern United States.
Arch. Environ. Contamin. Toxicol. 6:395-409.
Concentrations of Ag, As, Cd, Cr, Cu, Hg, Mn, Pb, and
Zn were determined for marine fish and shellfish collected near 3
ocean dumping sites, 3 inshore areas, and a control site. Silver
in flesh of rock crabs Cancer irroratus averaged 0.79 mg/kg wet
wt in the New York Bight disposal site compared with 0.24-0.38 mg
Ag/kg for 4 other areas. Cadmium, manganese, and zinc
concentrations were highest in crab flesh from Long Island Sound,
not a known disposal site, compared to 3 other areas; mean levels
were 1.0 mg Cd/kg wet wt vs 0.1, 29 mg Mn/kg vs 0.8-1.0, and 64
mg Zn/kg vs 32-36. Mn content in crab gills was 22 mg/kg from
the Sound-compared to 6.0 mg/kg in crabs from Chincoteague Inlet,
Virginia. Crab flesh from all sites contained about 1.9 mg As/kg
wet wt, <0.3-0.6 mg Cr/kg, and 0.15-0.19 mg Hg/kg. Digestive
glands of channel whelks Busycon canaliculatum from Long Island
Sound disposal site contained maximum amounts of silver, cadmium,
and zinc at 20 mg Ag/kg wet wt, 24 mg Cd/kg, and 2650 mg Zn/kg,
and a high level of copper at 1100 mg/kg wet wt. Metal
concentrations in surf clams Spisula solidissima and windowpane
flounder Scophthalmus aquosus, and arsenic, chromium, and mercury
in all organisms did not vary significantly among geographic
areas. Clam and whelk muscle contained <0.2 mg Ag/kg wet wt,
1.3-9.0 mg As/kg, <0.1-0.21 mg Cd/kg, <0.8 mg Cr/kg, 0.9-21.0 mg
Cu/kg, <0.05-0.14 mg Hg/kg, 0.5-3.5 mg Mn/kg, <0.5-0.9 mg Pb/kg,
and 18.4-29.5 mg Zn/kg. Flounder flesh contained <0.1 mg Ag/kg
wet wt, 1.4-2.8 mg As/kg, < 0.1 mg Cd/kg, <0.2-0.6 mg Cr/kg,
0.7-1.4 mg Cu/kg, 0.12-0.27 mg Hg/kg, 0.18-0.40 mg Mn/kg,
<0.5-1.0 mg Pb/kg, and 4.6-6.3 mg Zn/kg. Ranges in metal content
of sediments from the 3 dumping sites, in mg/kg dry wt, were <1.0
for Ag, <1.0 for Cd, <2.0 to 58.0 for Cr, <4.0 to 86.0 for Cu,
<0.1 to 0.2 for Hg, 13.0 to 280.0 for Mn, 3.6 to 97.0 for Pb, and
5.6 to 154.0 for Zn.
2647.
Horowitz, A. and B.J. Presley. 1977. Trace metal
concentrations and partitioning in zooplankton,
neuston, and benthos from the south Texas Outer
Continental Shelf. Arch. Environ. Contamin.
203
-------
Toxicol. 5:241-255.
Marine biota collected along the Texas Outer
Continental Shelf were analyzed for Cd, Cr, Cu, Fe, Mn, Ni, Pb,
and Zn. Average metal concentrations, in mg/kg dry wt in
zooplankton were 13.4 for Cu, 103 for Zn, 3.0 for Cd, 8.0 for Pb,
5.6 for Cr, 4.6 for Ni, 725 for Fe, and 29.7 for Mn; sargassum
contained average levels of 4.1, 36.0, 1.8, 4.7, 1.6, 5.2, 218,
and 31.4, respectively; plankton contained 8.1, 90.8, 1.9, 12.1,
5.0, 4.4, 624, and 21.7, respectively; squid contained 65.7, 144,
1.0, 2.0, 4.7, 2.5, 19.3, and 1.8, respectively in flesh
including skin; brown and rock shrimp contained 24.2-31.1,
47.7-56.3,0.16-0.25, 1.1-1.6,2.1-2.8, 1.4-1.6, 14.2-40.2, and
1.5-8.0, respectively. Muscle from flatfish, long-spined porgy,
rough scad, sea robin, sand sea trout, black-ear bass, Atlantic
croaker, and wenchman contained average metal levels of 1.1-3.4
for Cu, 15.5-59.3 for Zn, 0.08-0.26 for Cd, 0.8-6.5 for Pb,
2.0-8.1 for Cr, 0.6-4.9 for Ni, 7.7-177.0 for Fe, and 0.4-18.4
for Mn, all on a dry wt basis. Lead concentrations in organisms
increased from north to south and cadmium increased from
nearshore to offshore, reflecting sediment patterns.
Exoskeletons of shrimp and skin of squid and fishes generally had
higher metal levels than flesh, possibly the result of adsorption
from seawater or internal detoxification by the organism.
Enriched Cd, Cu, Fe, Pb, and Zn levels found in squid "pens" may
be attributed to internal detoxification or storage of necessary
metabolites, but not to adsorption since the pen is imbedded in
tissue and not exposed to seawater.
2648 .
Johnson, G.D., A.W. McIntosh, and G.J. Atchison. 1978.
The use of periphyton as a monitor of trace metals in
two contaminated Indiana lakes. Bull. Environ.
Contamin. Toxicol. 19:733-740.
Concentrations of cadmium and zinc were determined in
two Indiana lakes Which received effluents from nearby
electroplating facilities. In Palestine Lake, metal levels in
water at 6 sites ranged from 0.0018 to 0.0098 mg Cd/I, and in
algae from 80 to 430 mg Cd/kg dry wt, with two low concentrations
of 5.6 and 8.8 mg/kg. Zinc levels in Palestine Lake ranged from
0.03 to 0.27 mg/l in water and from 330 to 13,000 mg/kg dry wt in
algae. Water samples from Little Center Lake extended from
0.0007 to 0.0027 mg Cd/l and algal samples from 27 to 54 mg Cd/kg
dry wt; concentrations of Zn were 0.032 to 0.087 mg/l and 900 to
9700 mg/kg dry wt, respectively. Algal metal concentrations did
204
-------
not always correlate to water concentrations at each site, but
maximum levels of both Cd and Zn in algae and water were found at
sites nearest to industrial outfalls in both lakes.
2649 .
Liu, M.S. and J.A. Hellebust. 1976. Effects of salinity
changes on growth and metabolism of the marine centric
diatom Cyclotella cryptica. Canadian Jour. Botany
54 : 930-937 .
Growth rates of euryhaline diatoms were about 2 cell
divisions/day after 0-2 days acclimation in salinities of 10 to
50% SW (100% equals 34 0/00 S). Growth was reduced in salinities
of 80% to 150% SW, but division was still >1 division per day,
with a longer lag phase prior to logarithmic growth. Transfer of
diatoms from 33% SW to higher salinities of 50 to 150% SW
resulted in temporary plasmolysis and decreased photosynthetic
and protein synthesis. Rapid accumulation of free amino acids,
including proline, either from photoassimilated carbon or from
heterotrophic assimilation of glucose in the dark also occurred.
On transfer to low salinities, diatoms rapidly decreased amino
acid concentrations. Contents of chlorophylls a and c varied
little, from 5 and 3 million ug/cell, respectively, after 6 days
in middle salinities of 33 to 100% SW, but levels dropped to
2-3.5 million and 2-2.5 million, respectively, at both high and
low salinity extremes.
2650.
Liu, M.S. and J.A. Hellebust. 1976. Effects of salinity
and osrrolarity of the medium on amino acid metabolism
in Cyclotella cryptica. Canadian Jour. Botany
54: 9 3tS-9LR:>.
Diatoms subjected to a sudden increase in salinity,
from 33% to 80% SW (100% SW = 34 0/00 S), exhibited a reduction
in total uptake of amino acids and subsequent assimilation into
proteins within 2 hrs. Under water-stress conditions, proline
was synthesized from glutamate, arginine, and ornithine.
Increases in medium osmolarity, whether by KC1, mannitol, or
sucrose, but not glycerol, increased synthesis of proline and
levels of intracellular K and total amino acids. Proline levels
were reduced when diatoms were retransferred to low osmolarity
media. Loss of C-14 from proline was accompanied by
incorporation into proteins and by conversion of proline into
other cell components. Addition of salts and organic matter to
low salinity media, or KCl or glycerol alone, caused plasmolysis
205
-------
followed by rapid deplasmolysis. Proline levels were relatively
low in high-salinity adapted diatoms and proline turned over
rapidly. Authors suggest that proline accumulation is a response
to abrupt changes of intracellular ionic strength during
adaptation to increased salinity.
2651.
Merlini, M. 1978. Hepatic storage alteration of vitamin
B12 by cadmium in a freshwater fish. Bull. Environ.
Contamin. Toxicol. 19:767-771.
Sunfish, Lepomis gibbosus, were pretreated for 2 weeks
with 0.04 mg CdS04/1 In lake water. Subsequently, these and
controls were fed a single ration containing vitamin B12
labelled with Co-58. Five days later, amounts of labelled
vitamin B12 were 3900 cpm/g in controls and 3700 cpm/g in
experimentals. Relative concentration (R) of labelled vitamin in
tissue divided by amount in whole fish was significantly higher
in liver of control fish at 74 than treated specimens at 45; R
was significantly lower in controls for digestive tract at 3. 1
compared to 5.7, gall bladder at 7.2 to 15.1, and head 0.3 to
0.5. No difference in R was found between groups for kidney and
body residue. Controls were able to stock vitamin B12 in
liver. Cadmium appeared to accelerate vitamin elimination, as
shown by higher levels in digestive tract of Cd-exposed fish, by
stimulating biliary excretion into the digestive tract with
excretion via gills.
2652.
Morishita, H. and H. Takada. 1976. Sparing effect of
lithium ion on the specific requirement for sodium ion
for growth of Vibrio parahaemolyticus. Canadian Jour.
Microbiol. 22:1263-12~.
Maximal growth of the bacteria V. parahaemolyticus was
obtained at 29,250 mg NaCl/l in a synthetic medium. When the
medium was kept isotonic with 29,250 mg NaCl/l by sucrose, good
growth was obtained with 5850 mg NaCl/l. By reducing osmotic
pressure and decreasing NaCl to 5850 mg/l, the same growth was
obtained with 11,700 mg NaCl/l and 3400 mg LiCl/l; this was not
the case for sucrose addition. Authors concluded that ionic
strength and osmotic pressure, besides Na, were important
environmental factors affecting growth. Minimal essential sodium
requirement for Vibrio growth was 69 mg Na+/l, since this was
not replaced by any other cation. Osmotic support was required
when NaCl was decreased to 2925 mg/l. Of LiCl, KC1, RbCl, and
NH4Cl added to 175.5 mg NaCl/l, Li+ was the most accelerative
206
-------
for growth in synthetic media.
2653.
Oguri, M. and Y. Ooshima. 1977. Early changes in the
plasma osmolarity and ionic concentrations of rainbow
trout and goldfish following direct transfer from
fresh-water to sea water. Bull. Japan. Soc. Sci.
Fish 43:1253-1257.
When transferred from freshwater to full seawater with
an osmolarity of about 1000 mOsm/1, plasma osmolarity of
euryhali ne ra i nbrn trout, Salmo gai rder i , increased from 31 0 to
345 mOsm/l within 15 min, then declined gradually over the next
45 min to 330 mOsm/l. During 60 min in seawater, plasma Na
increased slightly from 3565 to 3910 mg/1 and plasma Cl increased
from 42,600 to 47,900 mg/l. No trout mortality was observed.
Goldfish, Carassius auratus, which are stenohaline freshwater
fishes, all died within an average of 33 min when transferred
directly to full seawater. During this period, plasma osmolarity
rose sharply from 275 to 350 mOsm/l, plasma Na level rose from
3220 to 4140 mg/l, and plasma Cl from 37,300 to 55,000 mg/l.
2654.
Reimer, A.A. and R.D. Reimer. 1975. Total mercury in
some fish and shellfish along the Mexican coast.
Bull. Environ. Contamin. Toxicol. 14:105-111.
Fish and shellfish obtained from local markets,
packing houses, or fishermen along the Gulf and Pacific coasts of
Mexico were analyzed for mercury. Highest mean levels were found
in the teleosts Mugil curema, Sphyraena guachancho, and Polynemus
virginica from Veracruz and Centropomus sp. from Coatzacoalcos
markets, ranging from 0.04 to 0.27 mg Hg/kg wet wt. Gray mullet,
MugU cephalus, from Tampico, Guaymas, Tololobampo, and Mazatlan
fish markets contained mean mercury levels of 0.03 to 0.07 mg/kg
wet wt in muscle and 0.01 to 0.09 in liver. Mojarra, Anisotremus
interruptus and white mojarra, Diapterus sp., contained 0.12 and
0.06 mg Hg/kg wet wt, respectively, in muscle and 0.26 and 0.07
in liver. The shrimps Penaeus aztecus, P. setiferus, P.
californiensis, and P. stylirostris contained 0.05 to 0.12 mg
Hg/kg wet wt in muscle. Mean mercury concentrations in bivalve
molluscs Crassostrea virginica, Codakia orbicularis, and Anadara
tuberculosa ranged from 0.02 to o. 09 mg/kg wet wt. Maximum
levels found in individual specimens were 0.61 mg Hg/kg in whole
fish, 0.64 in fish muscle, and 0.47 in fish liver, 0.67 in shrimp
muscle, and 0.22 in bivalves.
207
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2655.
Simola, L.K. 1977. The effect of lead, cadmium,
arsenate, and fluoride ions on growth and fine
structure of Sphagnum nemoreum in aseptic culture.
Canadian Jour. Botany 55:426-435.
The highest concentration tested having little effect
on growth of bog moss, Sphagnum nemoreum, during a period of 100
days was 20,700 mg/l lead, 1120 mg/l cadmium, and 75 mg/l
arsenate. Inocules died rapidly in 75,000 mg As/l as
Na2HAs04 or 11,200 mg Cd/l as CdS04j 207,000 mg Pb/l as
Pb(NOj)2 was growth-retarding. Chloroplasts accumulated
starcn and hyaline cell differentiation was inhibited in 7500 mg
As/l. Cytoplasm accumulated lipids in 20,700 mg Pb/l.
2656.
Sims, R.R., Jr. and B.J. Presley. 1976. Heavy metal
concentrations in organisms from an actively dredged
Texas bay. Bull. Environ. Contamin. Toxicol.
16:520-527.
In general, crustaceans, molluscs, and fish from San
Antonia Bay, Texas, a site of active dredging, had lower
concentrations of heavy metals than organisms from areas where
dredging and pollution are thought to be minimal. Soft portions
of oysters, Crassostrea virginica, contained an average of 1.3 mg
As/kg dry wt, 3.2 Cd, 161.0 Cu, <0.8 Pb, 0.05 Hg, and 322.0 Zn.
Clams, Rangia cuneata. contained 0.5 mg Cd/kg dry wt, 25.0 Cu.
1.1 Pb, and 51.0 Zn. Average concentrations in brown shrimp were
0.6 mg As/kg wet wt, <0.4 for Cd, 34.0 for Cu, <0.2 for Pb, <0.02
for Hg, and 14.0 for Zn, and in blue crabs were 0.6 for As, 0.1
for Cd, 54.0 for Cu, <0.2 for Pb, and 14.0 for Zn. Metal levels,
in mg/kg dry wt, in whole body and flesh of the fishes, Atlantic
croaker, silverside, spot, white sea trout, spotted sea trout,
bay anchovy, menhaden, gizzard shad, and southern flounder,
ranged from <0.1 to 1.8 Cd, 1.3 to 4.3 Cu, <0.2 to 2.3 Pb, and
6.3 to 117.0 Zn. M3.ximum metal concentrations, in rng/kg dry wt,
reported for organisms from unpolluted and undredged areas along
the U.S. coast were: in bivalves, <1.6 As, 40.0 Cd, 126 Cu, 7.7
Pb, 0.45 Hg, and 1533 Znj in shrimp and crabs, 11.0 As, 0.4 Cd,
34.0 Cu, 0.2 Pb, 0.24 Hg, and 75.0 Znj and in fishes, 6.1 Cd,
10.0 Cu, 8.6 Pb, and 397 Zn.
2657.
Sorensen, E.M.B. 1976. Thermal effects on the
accumulation of arsenic in green sunfish, Lepomis
208
-------
cyanellus.
Arch.
Environ. Contamin. Toxicol. 4:8-17.
Arsenic uptake increased in liver, gut, and muscle of
sunfish with increasing temperature (10 to 30 C), concentration
of As (0.0 to 60 mg/l as sodium arsenate), and time of exposure
(up to 5 wks). Maximum accumulation in liver was 1460 mg As/kg
wet wt in 60 mg As/l at 30 C for 2 wks, and at 1090 mg As/kg in
30 mg/l at 20 C for 4 wks. Maximum gut uptake was 240 mg As/kg
wet wt in 60 mg As/l at 20 or 30 C for 2 wks, and at 250 mg/kg in
30 mg/l at 20 C for 4 wks. Maximum muscle uptake was 80 mg As/kg
wet wt in 30 mg As/l at 30 C for 2 wks, and at 60 mg As/kg in 60
mg/l at 20 C for 4 wks. Mean temperature quotient (Q10) values
for As uptake in liver was 4.5. Other Q10 values for the genus
Lepomis range from 1.6 to 3.0. Higher Q10 values suggest that
elevated temperatures and high metal concentrations act
synergistically in metal uptake. Biological half-life of As in
Ii ver and gut of fish exposed to 30 and 60 mg As/kg at 10 C was
about 1 wk. LT-50 times in 60 mg As/l were 678 hrs at 10 C, 210
hrs at 20 C, and 124 hrs at 30 C; LT-50 times in 30 mg As/I were
527 hrs at 20 C and 209 hrs at 30 C.
2658 .
Talbot, V. and R.J. Magee. 1978. Naturally-occurring
heavy metal binding proteins in invertebrates. Arch.
Environ. Contamin. Toxicol. 7:73-81.
Low molecular weight cadmium, copper, and zinc binding
proteins have been isolated from mussels, Mytilus edulis,
collected from the cadmium polluted areas of Corio Bay,
Australia. Of 3 protein fractions, fraction II contained the
major proportion of Cd at 0.46 mg/kg, Cu at 0.20 mg/kg, and Zn at
0.20 mg/kg. Fraction III contained 0.44 mg Cd/kg, 0.20 mg Cu/kg,
and 0.20 mg Zn/kg, and fraction I contained 0.14 mg Cd/kg, 0.10
mg Cu/kg, and 0.03 mg Zn/kg. Authors suggest that the synthesis
of this protein, which probably belongs to the metallothionein
family of metal binding proteins, was induced in cyctoplasmic
solutions in cells as a regulatory mechanism to avoid
intoxication by excess uptake of metals.
2659 .
Ueda, T., and M. Takeda. 1977. On mercury and selenium
contained in tuna fish tissues - IV. methyl mercury
level in muscles and liver of yellowfin tuna. Bull.
Japan. Soc. Sci. Fish. 43:1115-1121.
Concentrations of methylmercury in 39 specimens of
yellowfin tuna, Thunnus albacares, averaging 35.0 kg in weight,
209
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from the Middle Pacific, West Pacific, and Fast Indian Oceans,
ranged from 0.04 to 0.46 mg CH3Hg/kg wet wt in dark muscle with
a mean of 0.21, from 0.02 to 0.41 mg CH3Hg/kg in dorsal.mus~le
with a mean of 0.19, and from 0.01 to 0.40 mg CH3Hg/kg ln Ilver
with a mean of 0.11. Concentrations of methyJmercury in other
tissues were 0.16-0.27 mg/kg in abdominal muscle, 0.06-0.10 in
spleen, and 0.06-0.07 in kidney. Methylmercury levels were
directly correlated to total mercury in both dorsal and dark
muscles and 1i ver. Total mercury content was sign i fi cantly
greater than methylmercury in dorsal muscle, averaging about 0.04
mg/kg higher. No difference was noted between the two mercury
forms in dark muscle or liver. Order of mercury levels in
tissues was est:imated as: total Hg of dorsal muscle'" total Hg
of dark muscle", methyl Hg of dark muscle> methyl Hg of dorsal
muscle> methyl Hg of liver'" total Hg of li ver.
2660.
Anderson, D.M. and F.M.M. Morel. 1978.
sensitivity of Gonyaulax tamarensis.
Oceanogr. 23:283-295.
Copper
Limnol.
Short term responses of the dinoflagellate G.
tamarensis to copper included rapid loss of motility and reduced
photosynthetic carbon fixation. Toxicity was a unique function
of cupric ion activity, as demonstrated by chelators tris
hydroxymethylaminamethane (Tris) and ethylenedinitrilotetraacetic
acid (EDTA). Copper additions to EDTA medium equilibrated with
the chelator relatively slowly, resulting in misleading short
term data. This kinetic effect was not seen with Tris or when
copper was added in chelated form with EDTA. Variations in
manganese or zinc concentrations over two orders of magnitude did
not alter results. Cells of Q. tamaren~~ were 100% nonmotile at
a calculated cUP,~c4ion activity of 10-. M, with 50% of cells
nonmotile at 10- . M. Nonmotile cells did not divide or grow
larger. Growth was totally inhibited at cupric ion acti vi ties
that only partially inhibited growth of four other species.
Since toxicity occurred at the calculated copper activity of
natural waters, assuming only inorganic copper complexation,
authors concluded that organic chelation may be necessary before
G. tamarensis can successfully compete with other algal species
Tn coo.stal waters.
2661 .
Anderson, R.V. and J.E. Brower. 1978. Patterns of trace
metal accumulation in crayfish populations. Bull.
Environ. Contamin. Toxicol. 20:120-127.
210
-------
Metal concentrations in whole crayfish, Orconectes
viri1is, from 3 sites in Illinois were: 2.22 mg Cd/kg dry wt
from an E1grin river, 1.04 from an E1grin pool, and 1.09 from an
Algonquin river; 64.3 mg Cu/kg dry wt, 61.2, and 71.3,
respectively; 27.4 mg Pb/kg dry wt, 8.4, and 11.3, respectively;
and 78.3, 87.1, and 101.3, mg Zn/kg dry wt. Previous data showed
that metal levels were generally higher in E1grin water,
sediment, and biota than similar data from the Algonquin. No
significant differences in metal concentrations were evident
between sexes of crayfish and no consistent trends existed among
size classes of these freshwater crustaceans. Maximum metal
levels were found in gills for Cd at 1.5 mg/kg dry wt and for Cu
at 120.7, in gills and viscera for Zn at 82.0 and 82.4 mg/kg,
respff)tive1y, and in exoskeleton for Pb at 23.4 mg/kg. Muscle
had the lowest concentrations of all metals tested except Zn.
2662.
Barbaro, A., A. Francescon, B. Polo, and M. Bilio.
Balanus amphitrite (Cirripedia:Thoracica) - a
potential indicator of fluoride, copper, lead,
chromium, and mercury in North Adriatic lagoons.
Marine Biology 46:247-257.
1978.
The capacity of barnacles to accumulate pollutants
above ambient levels was examined in two North Adriatic lagoons.
Levels in soft tissues ranged from 41 to 109 mg/kg dry wt for
copper, 7 to 12 for lead, 2 to 4 for chromium, and from 1.0 to
1.4 for mercury. Concentration factors were about 1000 for Cu.
and possibly higher than 1000 for Pb, Cr, and Hg. B. amphitrite
that had set on experimental panels had levels similar to those
found in specimens collected from long-term natural populations
as early as 42 days after irmnersion of panels. Compared with
literature data, accumulation levels found in B. amphitrite for
copper and lead were considerable, but exceeded by others
published for B. balanoides; chromium and mercury were 10X lower
than values reported for other suspension-feeders or indicator
organisms. It was concluded that B. amphitrite possesses most of
the properties considered essential for a biological indicator.
Eventual determination of response time of barnacles to changes
in environmental level could profitably be carried out utilizing
experimental panels.
2663.
Bohm, L. 1978. Application of the 45Ca tr'acer method
for determination of calcification rates in calcareous
algae: effect of calcium exchange and differential
saturation of algal calcium pools. Marine Biology
211
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47 : 9- 14.
Calcium exchange and differential saturation of algal
calcium pools complicate application of the Ca-45 tracer method
for determination of net deposition rates of Ca in calcareous
algae. Calcium incorporation occurs in two stages: a fast
stage, saturating exchangeable Ca pools, and a slow stage, giving
rise to net deposition. Reliability of the method depends on
determination of the second rate constant. Calcium exchange and
recycling of tracer lower the second rate constant, hence the
method gives rise to minimum values. Application of the method
was demonstrated for the following algae: Halimeda incrassata,
H. opuntia, Penicillus pyriformis, Udotea flabellum, Cymopolia
barbata, Padina sanctae crucis and Amphiroa fragilissima.
Calculated rate constants ranged from 67 to 220 cpm/mg/hr.
Results show close agreement of data with independent chemical
estimates.
2664.
Borgmann, U., O. Kramar, and C. Loveridge. 1978. Rates
of mortality, growth, and biomass production of
LYmnaea palustris during chronic exposure to lead.
Jour. Fish. Res. Bd. Canada 35:1109-1115.
Chronic exposure of freshwater snails, L. palustris,
to lead nitrate as low as 19 ug Pb/l significantly-increased
mortality, but did not affect growth during immersion from newly
hatched eggs until reproductive maturity. Lead-induced mortality
was proportional to Pb concentration raised to the power of 2.5.
Mortality as a rate function was superior to LC-50 or LT-50
values. A 50% drop in biomass production rate was observed at 36
ug Pb/l; and zero production at 48 ug/l. Lead uptake in whole
snails was proportional to lead concentration, with a
concentration factor of 8500 per dry weight.
2665.
Brown, D.A., and T.R. Parsons. 1978. Relationship
between cytoplasmic distribution of mercury and toxic
effects to zooplankton and chum salmon (Oncorhynchus
keta) exposed to mercury in a controlled ecosystem.
Jour. Fish. Res. Bd. Canada 35:880-884.
After exposure for 72 days to mercuric chloride, total
cytoplasmic Hg in salmon liver increased from 0.12 mg Hg/kg wet
wt in controls to 0.17 mg/kg in 1.0 ug Hg/l and 0.95 mg/kg in 5.0
ug Hg/lo Copper decreased from 114 to 89 mg/kg wet wt and zinc
decreased from 10.5 to 7.2 mg/kg in cytoplasm of liver as Hg
212
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increased in fish exposed to 5.0 ug Hg/kg. Total cytoplasmic Hg
in tissue of zooplankton increased from 0.08 mg Hg/kg wet wt in
controls to 3.9 mg/kg after 72 day exposure to 5.0 ug Hg/l;
coincidental loss of Cu and Zn also occurred. Pathological
effects coincided with saturation of metallothionein and
"spillover" of Hg into the high molecular ~ight protein
(enzyme-containing) pool. Tertiary and quaternary structural
changes in metalloen~es resulted from replacement of Cu and Zn
by Hg. Decreases in tissue Cu and Zn with increasing Hg
concentration are discussed as an intracellular displacement of
metals and as duodenal and cellular exclusion processes.
2666.
Cardwell, R.D., C.E. Woelke, M.L Carr, and E. Sanborn.
1978. Variation in toxicity tests of bivalve mollusc
larvae as a function of termination technique. Bull.
Environ. Contamin. Toxicol. 20:128-134.
Toxicities of cadmium, methoxYchlor, and dodecyl
sodium sulfate to larvae of oysters Crassostrea gigas and clams
Tresus capax were compared between direct sampling of larvae and
filtering larvae before sampling. For oysters, EC-50 for
abnormal shell development was 1.3 mg Cd/l with filtering and 0.9
mg/l without filtering; LC-50 values were 0.9 mg Cd/l filtered
and 2.5 unfiltered. For clams, EC-50 values were 0.05 mg Cd/l
for both filtered and unfiltered samples; LC-50 values were 0.1
mg Cd/I filtered and 0.7 mg/l unfiltered. Authors concluded that
filtering resulted in loss of smaller larvae from test
populations and that a greater proportion of those lost were
abnormal.
2667.
Cawthorne, D.F. 1978. Tolerance of some cirripede
nauplii to fluctuating salinities. Marine Biology
46:321-325.
Effects of fluctuating salinity on mortality of newly
released nauplii of three species of barnacles, Elminius
modestus, Balanus balanoides, and B. hameri, were measured.
Larvae were exposed to three different types of salinity
regimes. In all cases, a regime which fluctuated between 100%
seawater (33.5 0/00 S) and a reduced concentration of about 15%
SW in a 12 hr cycle was found to be least damaging. Abruptness
of salinity shock and degree of exposure to reduced salinity each
influenced mortality, but it was concluded that abruptness of
change was the more important. Mortality of barnacles dropped
belcw 10% when minimum seawater dilution encountered for 24 hrs
213
-------
was 15 to 25% for E. modesta, 25 to 30% for B. balanoides, and 25
to 40% for B. hameri.
2668.
Chisholm, S.W., F. Azam, and R.W. Eppley. 1978. Silicic
acid incorporation in marine diatoms on light:dark
cycles: use as an assay for phased cell division.
Limnol. Oceanogr. 23:518-529.
Silicon incorporation in diatom populations grown on
light:dark cycles was monitored using [Ge-6EQGe(OH)u as a
tracer for Si(OH)4. Frustule formation closely followed the
time-course of cell division in all 6 species examined
(Thalassiosira pseudonana, T. fluviatilis, Chaetoceros gracilis,
Ditylum brightwelli, Lithodesmium undulatum, Skeletonema
cestatum). Timing of these processes relative to light:dark
cycle was different for each species. M:lximum silicic acid
uptake over 24 hrs ranged from 0.96 to 2.11 mg SHOH) 4/diatom
sample; incorporation reached 2.11 mg Si(OH)4/sample for one
species. Seawater samples from the Gulf of California and
Southern California Bight also showed periodicity in Si(OH)4
incorporation when incubated under ambient light and surface
temperature. Authors concluded that degree of periodicity is
inversely correlated with diatom species diversity in samples,
consistent with the hypothesis that pulses in Si(OH)4
incorporation reflect phased cell division in individual species
of diatoms.
2669.
Chou, C.L., J.F. Uthe, and E.G. Zook. 1978.
Polarographic studies on the nature of cadmium in
scallop, oyster, and lobster. Jour. Fish. Res. Bd.
Canada 35:409-413.
Free and bound forms of cadmium ~re determined in raw
shellfish by differential pulse polarography and atomic
absorption spectrophotometry. Total cadmium in muscle of various
species of scallops averaged 5.3 mg/kg wet wt; in oyster species
tissue Cd was 0.8 mg/kg, and in lobsters Homarus americanus 0.03
mg/kg. Both scallop and lobster muscle contained no free
cadmium. Oyster had about 50% of its total cadmium present in
free form, a phenomena as yet unexplained. Detection limit for
free Cd was 0.05 mg/kg raw tissue.
2670.
Fowler, S.W., M. Heyraud, and J. La Rosa. 1978. Factors
affecting methyl and inorganic mercury dynamics in
214
-------
mussels and shrimp.
Marine Biology 46:267-276.
Accumulation and loss of inorganic and methylmercury
in mussels, Mytilus galloprovincialis, and benthic shrimp,
Lysmata seticaudata, were studied with radiotracers.
Methylmercury was accumulated by both species from both water and
food (labelled phytoplankton) to a greater degree than inorganic
mercury. In the temperature range 8 to 18 C, accumulatton was
slightly greater at higher temperatures. After 5 days in 18 C,
mussels had concentration factors of 500 for CH3HgCl and 375
for HgC12. Small mussels averaging 1.7 gm wet Wt concentrated
more mercury than larger mussels weighing 5.0 gIn; the reason
remains unclear. Viscera contained the largest fraction of total
body Hg, at 46% in shr imp and 16% in mussels. Methylmercury was
eliminated by both animals more slowly than inorganic mercury;
loss was slightly faster at higher temperatures of 23 C. Mussels
maintained in their natural environment had enhanced Hg
elimination attributed to availability of food and subsequent
growth. Authors concluded that observed differences underscore
the need for caution in predicting in situ flux of metals such as
mercury in certain species based solely on data derived from
laboratory experiments.
2671.
George, S.G., B.J.S. Pirie, A.R. Cheyne, T.L. Coombs, and
P.T. Grant. 1978. Detoxication of metals by marine
bi valves: an ultrastructural study of the
compartmentation of copper and zinc in the oyster
Ostrea edulis. Marine Biology 45:147-156.
Mechanisms of detoxication of copper and zinc by
oysters was investigated using Cu-impacted and non-perturbed
populations. Oysters from polluted areas contained 21 mg Cull
and 160 mg Zn/l in whole hemolymph and 220 mg Cu/kg wet wt and
1260 mg Zn/kg in soft tissue. Gills and mantle contained highest
metal concentrations of 2400 and 2200 mg Cu/kg wet wt,
respectively, and 15,000 and 13,000 mg Zn/kg, respectively.
Specimens from unpolluted areas contained 2 mg Cull and 60 mg
Znll in heroolymph and 23 mg Cu/kg wet wt and 590 mg Zn/kg in
whole tissue. Gills contained 250 mg Cu/kg and 10,000 mg Zn/kg
and mantle 2200 mg Cu/kg and 6200 mg Zn/kg. Copper and zinc were
compartmentalized in separate, specific, granular amoebocytes and
ilnrnobilized in membrane-limited vesicles as different chemical
compounds. Copper was associated with sulphur and zinc with
phosphorus. Chemical analyses of serum and tissues of normal and
contaminated oysters indicated that Cu and Zn are accumulated
independently; that Cu and Zn in serum, while higher than in
215
-------
surrounding seawater, are maintained at a 10X lower level than
tissues; and that toxicity is reduced by active uptake from serum
into granular amoebocytes, where it is further reduced by
compartmentation in membrane-limited vesicles. Individual cell
types may contain as much as 13,000 mg Cu/kg and 25,000 mg Zn/kg.
2672.
Glover, H.E. 1978. Iron in Maine coastal waters;
seasonal variation and its apparent correlation with a
dinoflagellate bloom. Limnol. Oceanogr. 23: 534-537 .
Soluble iron concentrations in the top 20 m of wateY'
off Boothbay Harbor, Maine, were 4.0-5.0 ug Fell in October and
November 1975 during the fall dinoflagellate bloom. These
concentrations were 3X greater than levels encountered in August
and September. Particulate iron levels increased to 3.5 ug Fell
prior to the bloom (mainly Gymnodinium sp.). Nutrient enrichment
and other experiments indicated that low iron concentrations
limited phytoplankton populations. In August, 1976, increased
iron concentrations from land runoff, near Monhegan Island,
preceded a dinoflagellate bloom.
2673.
Gnass i-Bare 11 i, M.. M. Romeo, F. Laumond, and D. Pesando.
1978. Experimental studies on the relationship
between natural copper complexes and their toxicity to
phytoplankton. Marine Biology 47: 15-19.
Toxicity of copper to phytoplankton depends on the
metal's physicochemj cal form. Organic substances liberated into
the culture medium by Cricosphaera elongata are able to detoxify
and complex copper. Molecular weight ranges of these organic
substances were determined by ultrafiltration. Over 50% of 0.025
mg Cull added to medium was found in the 500-1000 MW and
1000-10,000 MW fractions. Growth of Cricosphaera was inhibited
by a minimum of 0.025 mg Cull in seawater and 0.05 mg Cull in
culture medium.
2674.
Goldberg, E.D., V.T. Bowen, J.W. Farrington, G. Harvey,
J.H. Martin, P.L. Parker, R.W. Risebrough, W.
Robertson, E. Schneider and E. Gamble. 1978. The
mussel watch. Environ. Conserv. 5:101-125.
Environmental research has suggested that some
bivalves, namely Mytilus edulis, M. californianus, Crassostrea
virginica, and Ostrea equestris may be valuable as sentinel
216
-------
organisms for indicating levels of pollutants in coastal marine
waters. These organisms concentrate numerous pollutants to a
marked degree over seawater levels. Several species thus
bioaccumulate some, or even most, members of the four identified
categories of marine pollutants: heavymetals, transuranic
elements, petroleum hydrocarbons, and halogenated hydrocarbons.
A given species, however, may have unique enrichment factors for
any or all of these groups of substances. Baseline levels of
pollutants in molluscan tissues from U.S. coastal waters have
been determined for the year 1976. Zones of high pollutant
concentrations have been identified. No significant seasonal
variations of Ag, Cd, Cu, Ni, Pb and Zn concentrations were
observed in the monthly samples taken at Narragansett Bay, RI, or
at Bodega Head or Point La Jolla, California. No zones of high
general levels of metal pollution were discerned, although
locally high levels of individual metals were frequently
observed. Oysters were much more effective bioaccumulators of
silver, zinc, copper, and nickel than mussels, while the latter
appear to be better concentrators of lead. East- and Gulf-Coast
samples generally exhibited levels of transuranic nuclides or
Cs-137 that can be attributed to weapons-testing fallout; one
anomalous sample originated near a coastal nuclear-power reactor
at Plymouth, Massachusetts. West Coast samples exhibited
generally higher concentrations of plutonium, and much higher
ratios of Am-241 to Pu-239,240 than found in the other two
species, but the source of these transuranics is obscure. These
data are strongly suggestive of the hypothesis that mussels and
oysters draw radionuclides analyzed from suspended particles
rather than from solution in water. The byssal threads of
mussels show much greater enrichment of Pu-239,240, and often of
Am-241, than soft parts of these organisms. Mussel shells record
Am-241:Pu-239,240 ratios usually within a factor of two of ratios
found in viscera. Monthly collections at Bodega Head and at
Narragansett Bay show systematic but different changes in
Pu-239,240 and Am-241 levels in mussels over the periods
sampled. It was concluded that varying degrees of pollution in
U.S. coastal waters have been indicated by elevated levels of one
or more pollutants in bi valves, collected at more than one
hundred localities around the United States.
217
-------
2675.
Hodson, P.V., B.R. Blunt, and D.J. Spry. 1978.
pH-induced changes in blood lead of lead-exposed
rainbow trout (Salmo gairdneri). Jour. Fish. Res.
Bd. Canada 35:437-445.
Blood of juvenile rainbow trout exposed to up to 1.0
mg Pb/l in water showed increasing lead concentrations as pH of
test water decreased from 10.0 to 6.0. A decrease in pH by 1.0
unit from any reference pH resulted in an increase of blood lead
by a factor of 2. 1 within 24 hrs. In water with pH range from
6.0 to 9.0, blood Pb levels rose from 0.06-0.11 to 1.0-6.0 mg/l
as ambient lead increased from 0.003 to 1.0 mg/l. Since
sublethal lead toxicity is related to uptake, results suggest
that toxicity increases as pH decreases. Reactions of lead with
inorganic constituents of test water were complete within 3 hrs
and blood lead was at equilibrium with water lead within 48
hrs. Therefore, at time of blood sampling in the pH experiment,
both lead complexation processes in the exposure system, plus
lead uptake and release from blood, were at equilibrium.
2676.
Jackson, G.A. and J.J. Morgan. 1978. Trace
metal-chelator interactions and phytoplankton growth
in seawater media: theoretical analysis and
comparison with reported observations. Limnol.
Oceanogr. 23:268-282.
Effects of trace metal chelators in seawater with Ag,
AI, Ba, Ca, Cd, Co, Cr, Cu, Fe, Hg, K, Mg, Mn, Na, Ni, Pb, Sr,
and Zn were examined theoretically in terms of equilibrium
chemical speciation in seawater, including chemical interactions
between all metals; naturally occurring ligands such as Si03;
added organic chelating agents of various binding strengths and
total concentrations; and transfer of trace metals to
phytoplankton cell surface. An equilibrium model involving 18
metals and 8 ligands was applied to find the metal species in
natural seawater, chelator-amended seawater, and synthetic
seawater media. Three mechanisms for enhanced supply of iron
via chelation were examined: transport through membrane; ligand
exchange at cell surface; and increased supply of iron to cell
surface by dissociation of a chelate. None accounted for
observed effects of chelator variations on growth rate of
phytoplankton. Detoxification of toxic metals via chelatio~
showed a strong correlation between growth rate and free Cu +
computed at equilibrium in solution.
218
-------
2677.
Marquis, R.E., K. Mayzel, and E.L. Carstensen. 1976.
Cation exchange in cell walls of gram-positive
bacteria. Canadian Jour. Microbiol. 22:975-982.
Relative affinities of cations for anionic sites in
isolated bacterial cell walls of 6 species were assessed by
displacement of ope cation by anQther. Affini~y strength
determined was Laj+» Cd2+ > Sr2+ > Ca2+ > ~+ >
[+ > Na+ > Li+; hydrogen had a higher affinity than all
other ions. High affinity was correlated with low mobility of
bound ions in an electric field. Cation exchange capacities of
cell walls were estimated by completely displacing magnesium
from cell walls with Na+ or~. Total magnesium displaced
varied from 1.77 mg Mg/g dry wt for Staphylococcus aureus to
about 12.64 mg Mg/g for Bacillus megaterium. Amount of
displaceable Mg was inversely related to physical compactness of
baterial cell walls. Mg or Ca ions can each neutralize, or pair
with, two anionic groups in walls in ion-deficient media;
previous work indicated these ions pair with only one group at
high ionic strength. Authors suggest that there is flexibility
in the arrangement of charged groups in the walls. It was
concluded that for cells growing in laboratory media, which
generally contain excesses of monovalent over divalent cations,
there is a mix of small cationic counterions in walls and
monovalent cations may predominate even though the wall has a
greater affinity for divalent ions.
2678.
McFarlane, G.A., and W.G. Franz in. 1978. Elevated heavy
metals: a stress on a population of white suckers,
Catostomus commersoni, in Hamell Lake, Saskatchewan.
Jour. Fish. Res. Bd. Canada 35:963-970.
Mean annual metal concentrations, in ug/l, in two
lakes receiving heavy metal fallout from a base metal smelter
complex near Flin Flon, Manitoba, were for Mn, 30 in Hamell Lake
and 114 in Thompson Lake; for Fe, 59 and 110, respectively; for
Cu, 13 and 15; for Cd, 0.6 and 0.1; and for Zn, 245 and 20.
Whi te suckers from Hamell Lake showed signs typical of a
population under stress, which included increased length and
weight, increased fecundity, and earlier maturation, reduced
spawning success, reduced larval and egg survival, smaller egg
size, and reduced longevity compared with Thompson Lake white
suckers. Authors attributed these differences to elevated Cd,
Cu, and Zn in Hamell Lake waters, particularly in early spring,
a critical period in the reproductive cycle of these fish.
219
-------
2679.
Miller, J.C. and R. Landesman. 1978. Reduction of heavy
metal toxicity to Xenopus embryos by magnesium ions.
Bull. Environ. Contamin. Toxicol. 20:93-95.
Embryos of the amphibian Xenopus laevis were exposed
for 6 days to concentrations of 0.001 to 10.0 mg/l of Cd, Mn, or
Pb, or 0.001 to 1.0 mg/l of Hg in solution with 0.0 to 200 mg
Mg/l. Deformities observed, with increasing metal ions,
included: decreased swimming; reduced eye and body pigment;
decreased growth; edema; lack of pigmentation; paralysis; and
almost no intestinal coiling. Minimum metal levels which
reduced growth and intestinal coiling in 20 mg Mg/l were 1.0 mg
Cd/I, 0.5 mg Pb/l, 0.05 mg Hg/l, and greater than the maximum of
10 mg Mn/l tested. Survival of embryos at these concentrations
were 59% for Cd, 96% for Hg, and 100% for Pb. Decreasing the
ambient magnesium levels from 2.0 to 0.2 mg/l increased
mortality and severity of deformities at all concentrations of
Cd, Hg, Mn, and Pb used and in controls.
2680.
Mirkes, D.Z., W.B. Vernberg, and P.J. DeCoursey. 1978.
Effects of cadmium and mercury on the behavioral
responses and development of ~ur~anopeus depressus
larvae. Marine Biology 47:1 3-1 7.
Development time from megalops to juveniles for
larval estuarine mud crabs was extended in 10 ug Cd/I.
Cadmium-exposed specimens reached 100% megalops on day 26 and
100% juveniles on day 44, compared to day 22 for megalops and
day 34 for juveniles in controls. Survival of stage I zoeae
dropped to 80% in 24 hrs in cadmium and 95% in controls.
Increased mortality also occurred for megalops and early crab
stages exposed to Cd. Swimming rates were elevated for late
zoeal stages exposed to 10 ug Cd/l, while 1.8 ug Hg/l depressed
swimming rates of early stages.
2681.
Nelson, D.M. and J.J. Goering. 1978. Assimilation of
silicic acid by phytoplankton in the Baja California
and northwest Africa upwelling systems. LimnoL
Oceanogr. 23:508-517.
Rates of silicic acid uptake by natural phytoplankton
populations were measured from coastal upwelling regions off
Baja California and northwest Africa, using Si-30. Silicic acid
uptake in both systems extended below the 1.0% light penetration
220
-------
depth and occasionally to 0.01% light depth, about twice the
depth of carbon and nitrogen assimilation, and continued at
substantial rates throughout the 24 hr day. Uptake rates of
diatoms from stations with lowest near-surface silicic acid
concentrations were not shown to be substrate limited. Surface
particulate silicon concentrations ranged from 0.45 to 7.2 ug
Sill. Upwelling velocities, nutrient concentrations, and
nutrient uptake rates suggest that silicon limitation in the
Baja California system was prevented by high rates of silicic
acid regeneration resulting from dissolution of diatom silica.
2682.
Olson, K.R., K.S. Squibb, and R.J. Cousins. 1978.
Tissue uptake, ~ubcellular distribution, and
metabolism of 1 CH3HgCl and CH3 203HgCl by
rainbow trout, Salfuo gairdneri. Jour. Fish. Bd.
Canada 35:381-390.
Distribution of methylmercury (MeHg) by rainbow trout
was studied during, a 6 week post-exposure period following a
single 24 hr exposure to C-14 H~HgCl and CH3Hg-203 Cl.
Gills contained 100 ug Hg/kg wet wt, approxllnately 10 times more
MeHg than any other tissue after 24 hr exposure; concentrations
were lowest for brain and skeletal muscle, at 1.2 and 0.8 ug/kg,
respecti vely .In 2 wks following exposure, gill MeHg
concentrations decreased to 14.6, comparable with most other
tissues; methylmercury in most other tissues increased and then
decreased during the subsequent 4 wk period. Methylmercury
levels in brain, skeletal muscle, and gonad were highest at 6
wks, at 7.0,7.5, and 18.1 mg/kg wet wt, respectively. Six
we~ks following MeHg exposure, percent of mercury as inorganic
HgL+ increased in gill, kidney, and liver and to a lesser
extent in all other tissues except skeletal muscle. Total MeHg
was greatest in cytosol fractions and usually comprised 50 to
80% of total tissue mercury. In liver cytosol, a methylmercury
binding metallothionein-like s~ecies accounted for up to 40% of
total methylmercury bound. Hgc+, probably derived from
demethylation of methylmercury, was associated with a
metallothionein-like protein in gill tissue, but no more than 6%
of the total mercury in the soluble fraction was bound. Mercury
binding to metallothionein-like proteins in kidney and splenic
fractions was minimal in spite of relatively large amounts of
mercury in cytosol from these tissues. Authors suggest that
metallothionein acts as a binding scavenger for methylmercury
and inorganic mercury in fish.
221
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2683.
Overnell, J. 1976. Inhibition of marine algal
photosynthesis by heavy metals. Marine Biology
38:335-342.
Maximum rates of light-induced oxygen production by
marine algae Attheya decora, Brachiomonas submarina, Dunaliella
tertiolecta, Isochrysis galbana, Monochrysis lutheri,
Phaeodactylum tricornutum and Skeletonema costatum were compared
when exposed to copper, cadmium, mercury, zinc, and an
herbicide. I-50 values (concentrations producing 50% inhibition
of photosynthesis) after 15 min incubation ranged from 0.2 to
20.0 mg Hg/l, 1.3 to 4.4 mg Cull, and 1.3 to 65.4 mg Zn/l; Cd
was considered to be non-toxic to algae. S. costatum and A.
decora were especially sensitive to Cu and-Hg ions, while D.
tertiolecta was insensitive to Hg. It was concluded that A.
decora is a useful indicator of estuarine water quality.
2684.
Pearcy, W.G., E.E. Krygier, and N.H. Cutshall. 1977.
Biological transport of zinc-65 into the deep sea.
Limnol. Oceanogr. 22:846-855.
Specific activities of zinc-65 (Zn-65:Zn) in pelagic
and benthic fishes and crustaceans collected off Oregon were
correlated with depth of capture to estimate vertical biological
transport rates. About 2 yrs are required for transport of
Zn-65 from near-surface to abyssobenthic animals at 1000 m
depths. Vertical transport appears to be slower in upper
waters, suggesting recycling of zinc within biological
communities, and more rapid below 500 m. Long vertical
transport times for zinc contrasts with shorter times estimated
for transport of Zn and other elements by fecal pellets.
Authors suggest that this raises questions about the importance
of fecal pellets as a rapid transport mechanism for biologically
required materials into the deep sea.
2685.
Ramprashad, F. and K. Ronald. 1977. A surface
preparation study on the effect of methyl mercury on
the sensory hair cell population in the cochlea of
the harp seal (Pagophilus groenlandicus Erxleben,
1777). Canadian Jour. Zool. 55:223-230.
Effect of ingestion of methylmercuric chloride for 3
months on sensory cell populations in the organ of Corti of four
harp seals was determined. Sensory hair cell damage along the
length of the cochlea in seals on an oral daily dose of 25 mg
222
-------
CH3Hg/kg exceeded damage to seals fed 0.25 mg CH Hg/kg
dally. Two other seals on 25 mg/kg diets died after 3 to 4
weeks from mercury intoxication. Low level damage occurred to
hair cells throughout the length of the cochlea in surviving
seals; greatest damage was in the middle cochlear coil. Seals
on the high Hg diet had 20-24% sensory cell damage at the upper
middle coil, whereas only 4-5% damage was found in seals on the
low Hg diet. Damage was confined to the three outer rows of
hair cells, especially the outermost row. Authors concluded
that lack of specificity and low level damage to sensory hair
cells was characteristic of mercury and in contrast to other
known ototoxic agents.
2686 .
Schreck, C.B. and H.W. Lorz. 1978. Stress response of
coho salmon (Oncorhynchus kisutch) elicited by
cadmium and copper and potential use of cortisol as
an indicator of stress. Jour. Fish. Res. Bd. Canada
35:1124-1129.
Serum cortisol levels were elevated within 2 hrs in
juvenile coho salmon exposed to 60 to 210 ug Cull, as CuC12'
in freshwater. Treatment with up to 12 ug CdC12/1 did not
elevate cortisol, even in moribund fish. Stressing salmon with
sublethal levels of Cu or handling plus close confinement
resulted in a return to prestress levels in cortisol titers.
Stress produced similar cortisol elevations in controls, but Cu
reduced survival after handling and confinement. Salmon exposed
to 15 to 90 ug Cull had depressed serum chloride levels when
transferred to seawater; all fish exposed to 60 and 90 ug Cull
died between 40 and 96 hrs after transferral. Cadmium did not
influence serum chloride levels or saltwater tolerance. Authors
suggest that cortisol levels and other characteristics of stress
should not be universally applied as indicators in salmon.
2687.
Smith, T.G. and F.A.J. Armstrong. 1975. Mercury in
seals, terrestrial carnivores, and principal food
items of the Inuit, from Holman, N.W.T. Jour. Fish.
Res. Bd. Canada 32:795-801.
Ringed seals Phoca hispida had mean total mercury
levels of 27.5 mg/kg wet wt in liver and 0.72 mg/kg in muscle;
methylmercury levels were 0.96 mg/kg in liver and 0.83 in
muscle. Selenium concentrations were 15.5 mg/kg in liver and
1.1 in muscle. Bearded seals Erignathus barbatus contained 143
223
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and 0.53 mg/kg total Hg in liver and muscle, respectively, and
0.3 mg/kg methyl Hg in liver. Both species showed significant
positive correlations of Hg with age and weight. Total mercury
in muscle of the trout-like Atlantic char Salvelinus alpinus was
0.05 mg/kg. Arctic fox and sledge dogs, which feed on ringed
seals, had total mercury contents of 0.77 mg/kg in liver and
0.32 in muscle of fox and 11.5 and 0.79 mg/kg, respectively, for
dogs. Blood Hg levels in local people, whose diet includes
principally fish and some seals, have been reported as above
average, though not constituting a health risk.
2688.
Sullivan, J.F., G.J. Atchison, D.J. Kolar, and A.W.
McIntosh. 1978. Changes in the predator-prey
behavior of fathead minnows (Pimephales promelas) and
largemouth bass (Micropterus salmoides) caused by
cadmium. Jour. Fish. Res. Bd. Canada 35:446-451.
Prey vulnerability of fathead minnows to largemouth
bass increased significantly at a minimum concentration of 0.375
mg CdC12/1 in acute 24-hr exposure and 0.025 mg CdC12/1 in
subacute 21-day exposure. The latter concentration 1S well
below maximum toxicant concentrations reported of 0.037-0.057 mg
Cd/l for minnows. Cadmium exposure caused altered behavior
patterns, such as abnormal schooling in prey.
2689.
Swallow, K.C., J.C. Westall, D.M. McKnight, N.M.L. Morel,
and F.M.M. Morel. 1978. Potentiometric
determination of copper complexation by phytoplankton
exudates. Limnol. Oceanogr. 23:538-542.
Potentiometric copper titrations were done on culture
media in which eight algal species, Thalassiosira pseudonana,
Ankistrodesmus falcatus, Chlamydomonas sp., Pediastrum sp.,
Staurastrum gracile, Gloeocystis gigas, Tribonema sp., and
Cyclotella cryptica were grown to cell concentrations of 100,000
to 1,000,000 cells/ml. Only Q. gigas produced extracellular
organic compounds that measurably reduced cupric ion activity in
63.5 ug/l total copper by complexation.
2690.
Wobeser, G. 1975. Acute toxicity of methyl mercury
chloride and mercuric chloride for rainbow trout
(Salmo gairdneri) fry and fingerlings. Jour. Fish.
Res. Bd. Canada 32:2005-2013.
224
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LC-50 values for methylmercuric chloride at 24, 48,
and 96 hrs were 0.084, 0.045, and 0.024 mg Hg/l, respectively,
for fry; and 0.125,0.066, and 0.042 mg Hg/l, respectively, for
fingerlings. LC-50 (24 hr) value for mercuric chloride and
fingerlings was 0.90 mg/l. Fingerlings exposed to
methylmercuric chloride concentrated mercury in their tissues
much more rapidly than those exposed to mercuric chloride.
Concentration factors (CF) for tissue over water MeHgCl
increased from 36 to 220 as exposure time increased to 96 hrs;
maximum mean tissue concentration was 7.9 mg Hg/kg in 0.04 mg
MeHgCl/l. CF of HgC12 was only 1.6 to 3.0 at 24 hrs. Acute
toxic action of both compounds was exerted on gills. Mercuric
chloride caused severe epithelial necrosis over 108 hrs;
methylmercuric chloride exposure resulted in epithelial cell
swelling and hyperplasia, a marked increase in number of
epithelial cells in mitosis, and terminal epithelial
desquamation.
2691 .
Wobeser, G. 1975. Prolonged oral administration of
methyl mercury chloride to rainbow trout (Salmo
gairdneri) fingerlings. Jour. Fish. Res. Bd. Canada
32 :2015-2023.
Rainbow trout fingerlings were fed rations containing
4.0 to 24.0 mg Hg/kg as methylmercuric chloride over 105 days.
Fish receiving 16 and 24 mg/kg had significantly higher blood
packed cell volumes than controls. Hyperplasia of gill
epithelium was the only morphologic alteration detected. Fish
accumulated up to 30 mg Hg/kg in muscle over 14 wks, but no
mortality could be attributed to mercury. Authors suggest that
trout can tolerate a large body burden of mercury with time.
2692.
Wold, W.S.M. and I. Suzuki. 1976. The citric acid
fermentation by Aspergillus niger: regulation by
zinc of growth and acidogenesis. Canadian Jour.
Microbiol. 22:1083-1092.
Citric acid fermentation by fungi is divided into two
phases, a growth phase during which cells proliferate but do not
accumulate citrate, followed by an accumulation phase during
which citrate is produced and reproduction proceeds slowly or
not at all. Growth phase was maintained with 64 to 130 ug Zn/l
in a low sucrose (0.4 to 0.8%) minimal salts medium; however,
growth became limited by zinc deficiency of < 65 ug Zn/l and
cells passed into accumulating phase over 48 hrs. Addition of
225
-------
101 ug Zn/l to accumulating cultures reversed phases to growth.
Iron, manganese, copper, and calcium, at concentrations up to
942 ug Fell, 274 ug Mn/l, 24 ug Cull, and 200 ug Call, had no
influence on growth or citrate accumulation over 70 hrs; only
zinc appeared to regulate growth-accumulation alternating phases.
2693.
Wold, W.S.M. and I. Suzuki. 1976. Regulation by zinc
and adenosine 3',5'-cyclic monophosphate of growth
and citric acid accumulation in Aspergillus niger.
Canadian Jour. Microbiol. 22:1093-1101.
The growth phase-citrate accumulation phase
alternative of citric acid fermentation in fungi is controlled
by external zinc content. Zinc at 130 ug/l maintained growth of
Aspergillus, while levels <6 ug Zn/l signaled transition to the
accumulating phase within 50 hrs. Cyclic AMP affected growth
and acidogenesis rates of cultures in low but not high zinc
concentrations; authors concluded that zinc, not AMP, induced
phase transition.
2694.
Wong, P.T.S., Y.K. Chau, and P.L. Luxon. 1978.
of a mixture of metals on freshwater algae.
Fish. Res. Bd. Canada 35:479-481.
Toxicity
Jour.
Recommended levels of metals for Great Lakes Water
Quality Objectives, in ug/l, include 50 for As, 0.2 for Cd, 50
for Cr, 5.0 for Cu, 300 for Pb in Lake Superior, 20 for Pb in
Lake Huron, and 25 for Pb in the remaining lakes, 0.2 for Hg, 25
for Ni, 10 for Se, and 30 for Zn. In a mixed-metal solution,
however, primary productivity of the diatom, Scenedesmus
quadricauda, was reduced to 60-80% of control values in 10% of
recommended metal concentrations; productivity decreased to
30-60% in 50% of metal concentrations and to 20-30% in all
recommended concentrations. Diatoms were more sensitive to
metals than reported values for blue-green and green algae.
2695.
Wrench, J.J. 1978. Biochemical correlates of dissolved
mercury uptake by the oyster Ostrea edulis. Marine
Biology 47:79-86.
Equilibrium concentration factors for dissolved
mercury in oyster digestive glands were previously found to be
3-4X higher than in gills. In this study, an analysis of
soluble protein showed values of 49,300 mg protein Ikg wet wt
226
-------
for digestive glands and 700 mg/kg for gills. Starvation
significantly reduced soluble protein level of digestive glands
to 31.1 mg/kg and to below detection limits in gills.
Differences in concentration factors between gills and digestive
glands may be based on a quantitative difference in
macromolecular binding sites. However, since Hg2+ uptake over
48 hrs in 0.05 mg Hg/l was 9.2 mg/kg wet wt in gills and only
1.7 mg/kg in digestive glands, it appeared that soluble protein
content influenced final concentrations but not rates at which
equilibrium is reached. Dissolved mercury uptake in isolated
gills was inhibited by 5 mM 2-4 dinitrophenol, by the absence of
a readily metabolizable substrate such as dextrose in uptake
medium, and by 1170 mg ~/l. Strophanthin G (ouabain), an
inhibitor of ~ transport, at 0.01 mM, caused a significant
increase in mercury uptake.
2696.
Adams, C.E., Jr., W.W. Eckenfelder, Jr., and B.L.
Goodman. 1975. The effects and removal of heavy
metals in biological treatment. In: Krenkel, P.A.
(ed.). Heavy metals in the aquatic environment.
Pergamon Press, New York:277-292.
Authors conclude that quality of effluent from
activated sludge and anaerobic treatment processes deteriorates
at comparatively low concentrations of copper, zinc, chromium,
and lead with no increasing deterioration at higher
concentrations. These metals tend to form organometallic
complexes at low concentrations with certain essential
extracellular constituents, thereby inhibiting normal microbial
activities. These complexes absorb onto biological floes and
are partially removed from solution along with precipitated
metallic ions. A significant portion of the metals are removed
through the treatment process depending on metal, metal
concentration, pH, and abundance of microorganisms.
2697.
Agadi, V.V., N.B. Bhosle, and A.G. Untawale. 1978.
Metal concentration in some seaweeds of Goa (India).
Botanica Marina XXI:247-250.
Seventeen species of marine algae from five sites in
Goa, India, showed considerable variations in concentrations of
Co, Cu, Fe, Pb, Mn, Ni, and Zn. Cobalt ranged from 1.3 to 15.2
mg/kg dry wt, copper from 3.2 to 80.4, iron from 130 to 1800,
lead from 3.0 to 197.5, manganese from 25 to 3420, nickel from
0.5 to 39.1, and zinc from 2.8 to 203.9. The role of different
227
-------
seaweeds as indicators of metal pollution is discussed in
relation to degree of metal accumulation.
2698.
Ahsanullah, M. and G.H. Arnott. 1978. Acute toxicity of
copper, cadmium, and zinc to larvae of the crab
Paragrapsus quadridentatus (H. Milne Edwards), and
implications for water quality criteria. Austral.
Jour. Marine Freshwater Res. 29:1-8.
LC-50 (96 h) values for crab larvae were 0.17,0.49
and 1.23 mg/l for copper, cadmium, and zinc salts,
respectively. Larvae were 9X more sensitive to Zn and at least
29X more sensitive to Cd than adults. Larval LC-50 (96 hr)
values multiplied by an application factor of 0.01 (as
recommended in Australian water quality criteria) results in
derived "safe" concentrations, which in the case of copper and
zinc are below the stated "minimal risk concentrations" of 10
and 20 ug/l, respectively- In view of the known greater
sensitivity of larvae of many taxa to heavy metal toxicity, the
validity of using the same application factor for both adult and
larval stage is questioned.
2699.
Atchison, G.J., B.R. Murphy, W.E. Bishop, A.W. McIntosh,
and R.A. Mayes. 1977. Trace metal contamination of
bluegill (Lepomis macrochirus) from two Indiana
lakes. Trans. Amer. Fish. Soc. 106:637-640.
Bluegill sunfish from two industrially contaminated
Indiana lakes were analyzed for cadmium, zinc, and lead.
Bluegill from several uncontaminated sites were used to
establish background metal concentrations. The highest mean
concentrations of Cd and Zn in mg/kg dry wt whole fish were
found in Palestine Lake bluegill (3.4 Cd, 220.0 Zn) and the
highest mean concentration of Pb was found in Little Center Lake
bluegill (6.1). These mean concentrations were significantly
higher than background.
2700.
Badsha, K.S. and M. Sainsbury. 1978. Aspects of the
biology and heavy metal accumulation of Aliata
mustela. Jour. Fish Biology 12:213-220.
Feeding habits, growth rate, fecundity and other
aspects of the general biology of this marine teleost from the
Severn Estuary and the Bristol Channel are reviewed for the
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-------
period 1974/76. Also, the changes in accumulation of 2n, Pb,
and Cd during this time were measured. Concentrations of zinc
in eviscerated fish, in mg/kg dry wt, for all collections ranged
from 45.0 to 98.1; for lead these values were 8.1-24.5; and for
cadmi~ 1.4-4.2. An attempt was made to relate metal residues
in fish to dietary patterns.
2701.
Berger, V.Y., V.V. Khlebovich, N.M. Kovaleva, and Y.V.
Natochin. 1978. The changes of ionic composition of
cell volume during adaptation of molluscs (Littorina)
to lowered salinity. Compo Biochem. Physiol.
60A:447-452.
Changes of water content, volume of inulin space, and
Na, K and Mg content in foot muscle and hepatopancreas of
gastropod molluscs Littorina littorea, L. saxatilis and L.
obtusata acclllnated to lowered salinity-of 14-16 0/00 were
investigated. Molluscs were unable to completely regulate cell
volume, hydration level of which increases sharply at the first
period of hypotony with partial reestablishment during prolonged
acclllnation to dilute seawater by 6 to 10 days. During
adaptation of L. littorea to lowered salinity, the role of ions,
especially K, Tn cell osmoregulation increases. Potassium is
retained in cells of these molluscs; ionic quantity does not
decrease even in the first steps of hypotony, when loss of
sodium and magnesium occurs.
2702.
Billard, R. 1978. Changes in structure and fertilizing
ability of marine and freshwater fish spermatozoa
diluted in media of various salinities. Aquaculture
14:187-198.
Spermatozoa of marine teleosts (sea bass,
Dicentrarchus labrax; sea bream, Sparus auratus) or freshwater
teleosts (trout Salmo gairdneri; pike, Esox lucius; guppy,
Poecilia reticulata) were diluted in media of different
salinities. Motility, morphological changes and fertilizing
ability were used to judge effects of such treatments. The
medium best adapted to dilution of marine fish sperm was about
20 0/00 S. Sperm motility was increased and prolonged, and
fertilization rate significantly llnproved for sea bass at 0.037
0/00 S. For trout and pike, an extender with about 7 0/00
salinity increased motility time and fertility. After dilution
in freshwater, structure of trout spermatozoa was considerably
altered, such as rupture of plasma membrane and mitochondrial
229
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swelling. When spermatozoa were diluted in the extender, there
were no significant structural changes in trout, but alteration
occurred in mid-piece of guppy spermatozoon. It was concluded
that freshwater or seawater are not the best media for
artificial insemination of freshwater or marine fish produced in
aquaculture.
2703.
Brinckman, F.E., K.L. Jewett, W.R. Blair, W.P. Iverson
and C. Huey. 1975. Mercury distribution in the
Chesapeake Bay. In: Krenkel, P.A. (ed). Heavy
metals in the aquatic environment. Pergamon Press,
New York:251-252.
Concentrations of total mercury in sediments,
unfiltered seawater, and plankton at 10 stations in Chesapeake
Bay are reported. For sediments, concentrations in mg/kg dry wt
ranged from 0.04 to 1.12; for water 0.02 to 0.68 ug/l; and in
zoo- and phytoplankton from 0.06 to 1.65 mg/kg dry wt.
Plankton/water mercury ratios ranged from 570 to 7650.
2704.
Bryan, G.W. and L.G. Hummerstone. 1978. Heavy metals in
the burrowing bivalve Scrobicularia plana from
contaminated and uncontaminated estuaries. Jour.
Mar. BioI. Assn. U.K. 58:401-419.
Concentrations of Ag, Cd, Co, Cr, Cu, Fe, Mn, Ni, Pb,
and Zn were analyzed in clam soft tissues from sites in the
Gannel and Camel Estuaries in South-West England. In the Gannel
Estuary, which receives wastes from old lead mines, clams
contained about an order of magnitude higher concentrations of
lead, cobalt, cadmium and zinc than in the Camel Estuary, and
higher concentrations of other metals also. Maximum
concentrations recorded, in mg/kg dry wt soft parts, from
Scrobicularia collected from the Gannel were 1.2 for Ag, 14.9
for Cd, 66.0 for Co, 2.2 for Cr, 86.0 for Cu, 1240.0 for Fe,
87.0 for Mn, 11.9 for Ni, 828.0 for Pb, and 2940.0 for Zn. In
both populations, less than 50% of the total silver, copper and
iron was found in digestive gland. For the other metals over
50% occurred in this organ and, in large Gannel animals, more
than 90% of the lead, cobalt, cadmium and zinc, implying that
they are chiefly absorbed from ingested sediment. In
contaminated Gannel animals, all metal concentrations, with the
exception of Mn and Fe, increased with increasing size. The
main contrast in the Camel animals concerned the concentrations
of cadmium and zinc, which were independent of size. This
230
-------
suggests a possible relationship between the slope of the
concentration/size regression and level of contamination,
although differences in growth rate may also be involved. When
animals were exchanged between the two estuaries, their metal
concentrations approached those of the natives very slowly.
Even after a year, concentrations of lead, cobalt, cadmium and
zinc in the digestive gland were still markedly different from
those of native animals. The use of Scrobicularia as an
indicator of metal contamination is discussed. It is concluded
that Scrobicularia should normally be regarded as a long-term
integrator of the chronic type of contamination usually
associated with estuarine sediments.
2705.
Bryan, G.W. and H. Uysal. 1978. Heavy metals in the
burrowing bivalve Scrobicularia plana from the Tamar
estuary in relation to environmental levels. Jour.
Mar. BioI. Assn. U.K. 58:89-108.
Concentrations of Ag, Cd, Co, Cr, Cu, Fe, Mn, Ni, Pb,
and Zn were measured in whole soft parts and digestive gland of
Scrobicularia plana over its range of distribution in the Tamar
estuary. Four metals (Cu, Fe, Mn, Zn) were analyzed in the
individual tissues, including shell. As far as possible,
concentrations in animals were related to those in the
environment. Seasonal variation, distance from shore, and size
of animal have also been considered. Partitioning of metals
between the digestive gland and remaining soft tissues suggests
that uptake of Cd, Co, Cr, Ni, Pb, and Zn occurs mainly through
ingestion of sediments. Generally, more than 75% of these
metals were found in digestive gland. This organ contributed
less to the total amount of Cu and Ag (30-40%), Mn (51-80%) and
Fe (3-20%). Lower values of Mn and Fe were found upstream where
the availability of 'soluble' metals to clams was higher.
Concentrations of Cd, Co, Cr, Ni, Pb and Zn in whole soft parts
increased markedly with size, whereas Fe remained relatively
constant and levels of Ag, Cu and Mn decreased. In shell, most
of the Mn was incorporated in the matrix, presumably via mantle,
whereas appreciable amounts of Cu, Fe and Zn were probably
incorporated directly from solution by adsorption.
Scrobicularia appears to have potential as an indicator of the
availability of metals in estuaries and results for Cu, Fe, Mn,
and Zn suggest that there were no important changes in the Tamar
estuary between 1969 and 1974.
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2706.
Bull, K.R., R.K. Murton, D. Osborn, P. Ward, and L.
Cheng. 1977. High levels of cadmium in Atlantic
seabirds and sea-skaters. Nature 269:507-509.
Cadmium concentrations in mg/kg dry wt were
determined in liver and kidney from six species of marine
seabirds: fulmar, Fulmaris glacialis; shearwater, Puffinus
puffinus; puffin, Fratercula arctica; Leach's petrel,
Oceanodroma leucorhoa; storm petrel, Hydrobatus pelagicus; and
raz orb ill, Alca torda. Cadmium in liver ranged from 1.4
(razorbill)~57.0 (Leach's petrel); for kidney these values
extended from 14.6 (razorbill) to 240.0 (fulmar). Sea-skaters
of the genus Halobates are widely-distributed pelagic marine
insects which live at the sea surface and feed on zooplankton
trapped at the air-sea interface. Samples of H. micans from
tropical areas of the Atlantic Ocean contained-a mean cadmium
concentration of 22.7 mg/kg dry wt (range 0.0-309.0). Although
most species of seabirds do not eat large quantities of
Halobates, at least 2 Pacific species have been proven to eat
them; however, authors expect these insects to be among the
sources from which storm petrels could obtain Cd. It was
concluded that the high Cd concentrations found in seabirds
originated from natural rather than anthropogenic sources.
2707.
Cardasis, C.A., H. Schuel, and L. Herman. 1978.
Ultrastructural localization of calcium in
unfertilized sea urchin eggs. Jour. Cell Sci.
77:101-115.
The pyroantimonate technique was employed to identify
binding sites for calcium in unfertilized Arbacia punctulata and
Strongylocentrotus purpuratus eggs. Since antimony is
non-specific and binds with a variety of cations, the
identification of calcium was established by specific chelation
with ethyleneglycol tetra-acetic acid (EGTA) and X-ray
microprobe analysis. Antimony deposits were observed on the
egg's membranes, the plasma, cortical (secretory) granule,
pigment granule, smooth-surfaced vesicle, and yolk platelet.
Deposits were also observed in the mitochondria, rod-containing
vesicles, and the vitelline layer. Two types of yolk platelets
were observed: a more numerous electron-opaque platelet which
had precipitate along its limiting membrane as well as within
the stored-matrix substance, and a less-frequently seen platelet
with lower electron opacity which contained precipitate only
along its limiting membrane. Deposits were reduced at all sites
fOllCMing exposure of eggs to EGTA either prior to or after
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osmium-antimonate fixations. Initial fixation in glutaraldehyde
followed by postfixation in osmium-antimonate solutions provided
better preservation of structure by less precipitation than
direct fixation in osmium-antimonate. The organelle sites of
calcium binding identified within unfertilized sea urchin eggs
may participate in stimulus-secretion coupling and activation of
embryogenesis at fertilization.
2708.
Cheng, T.C. and J.T. Sullivan. 1977. Alterations in the
osmoregulation of the pulmonate gastropod
Biomphalaria glabrata due to copper. Jour.
Invertebrate Pathology 29:101-104.
Freshwater snails were exposed to 0.06 mg/l of
copper, as CUS04. Wet weights of exposed snails increased
with time, while those of controls decreased. Dry weights of
both experimentals and controls decreased equally. Finally, the
ratio of wet wt to dry wt of experimentals was significantly
higher than controls after 24 and 48 hr of exposure. Osmolality
of hemolymph of exposed snails was significantly lower than
control hemolymph after 12, 24, or 36 hr of exposure. Authors
concluded that exposure of!!. glabrata to copper resulted in
osmotic influx of water into tissues and caused death.
2709 .
Couch, J.A. 1977. Ultrastructural study of lesions in
gills of a marine shrimp exposed to cadmium. Jour.
Invertebrate Pathology 29:267-288.
Pathologic black gills of 20 pink shrimp, Penaeus
duorarum, exposed to 763 ug/l of cadmium chloride for 15 days
were compared with gills of controls. Twelve Cd-exposed shrimp
developed black gills. Local as well as extensive areas of cell
death and necrosis were found in distal gill filaments of gills
from these shrimp. It is proposed that necrosis of specialized
epithelial cells and septum cells in black gill filaments and
contiguous nanblack gill tissue could cause osmoregulatory,
detoxifying, and respiratory dysfunction in crustacea,
particularly among individuals undergoing environmental stress.
2710.
Davenport, J. 1977. A study of the effects of copper
applied continuously and discontinuously to specimens
of MYtilus edulis (L.) exposed to steady and
fluctuating salinity levels. Jour. Mar. BioI. Assn.
U.K. 57:63-74.
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Survival and behavior of mussels exposed to
discontinuous and continuous copper regimes was investigated in
both fluctuating salinity conditions and in constant full
strength seawater. Continuous 0.5 and 0.25 mg/l added copper
caused damage to mussels within 1-2 days. The LT-50 for 0.5
mg/l Cu was about 2 days; for 0.25 mg/l Cu it was 4-5 days. In
full strength seawater, a 6 hr on-6 hr off 0.5 mg/l Cu regime
caused no damage in 5 days, because Mytilus can detect copper in
its environment and close its shell valves to avoid exposure to
copper. In fluctuating salinity regimes the timing of copper
delivery was extremely important. Animals survived copper
delivery occurring at low or falling salinities because of
interacting closure responses to copper and low salinities. It
is suggested that these results cast doubt upon the usefulness
of Mytilus, and other animals which possess similar closure
mechanisms, for use as a biological pollutant monitor.
2711.
Delcourt, A. and J.C. Mestre. 1978. The effects of
phenylmercuric acetate on the growth of Chlamydomonas
variabilis Dang. Bull. Environ. Contamin. Toxicol.
20: 145-14B.
Exposure to phenylmercuric acetate caused a delay in
growth of phytoplankton C. variabilis. Lag time before
exponential growth increased to 5 days as mercury levels
increased to 5.0 ug Hg/l in initial algal populations of 21,000
cells/ml. Algae at lower densities had longer lag times at each
phenylmercuric acetate concentration.
2712.
Dillon, T.M. and J.M. Neff. 1978. Mercury and
estuarine marsh clam, Rangia cuneata Gray.
uptake, tissue distribution and depuration.
Environ. Res. 1:67-77.
the
II.
Marine
During St two-week period, Rangia accumulated (by a
factor of 1132) H~+ from solutions containing 30 to 50 ug
Hg2+/1; most of the mercury located in gill and mantle
tissue. Initial depuration (5 hr) in clean seawater was rapid
in all tissues. Between 10 and 192 hours, concentrations of
mercury in gill, foot and adductor muscles remained stable while
mantle, haemolymph and viscera levels continued to fluctuate in
a manner suggesting internal redistribution of mercury. After
eight days of depuration, viscera contained the most mercury and
appeared to be the only tissue to increase its proportionate
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share of total tissue mercury. After 15 weeks of depuration,
residual mercury in whole clams was about 20% of initial
concentrations. Acute decreases in salinity (15 0/00 S to 2
0/00 S) enhanced the ability of Rangia to depurate mercury.
2713.
Doi, R. and J. Ui. 1975. The distribution of mercury in
fish and its form of occurrence. In: Krenkel, P.A.
(ed). Heavy metals in the aquaticenvironment.
Pergamon Press, New York:197-221.
Authors emphasize the present aspects of mercury
related environmental pollution in Japan, and Japanese
Government countermeasures. "The Japanese Government
disregarded for a long time the occurrence of Minamata disease
in both Kumamoto and Niigata prefectures and therefore had no
basic policy in relation to mercury pollution of the human
environment. It has been only in the last few years that the
Government has begun to carry out periodical environmental
surveys."
"In this regard, the Kumamoto University Minamata
Disease Research Group published its findings in relation to the
third occurrence of Minamata disease on May 21, 1973, and with
it came the possibility that Minamata disease had spread to many
other parts of the country. As a result of this pressure, the
Government was compelled to begin seriously working out a plan
of action in relation to the possibility of pervasive mercury
pollution. On June 24 of that year it published guidelines on
permissible limits for mercury concentrations in fish along with
a tentative schedule of allowable intake of methylmercury
tainted fish. Along with this action, on June 25 a decision was
made to perform immediate surveys in the water basins in Japan,
i.e., in Minamata Bay, Yatsushiro Sea, Tokuyama, Arihama,
Mizushima, Himi, Uozu, and the port of Sakata. The results of
this survey should be published soon. The government further
decided to carry out extensive surveys for mercury, PCB,
cadmium, lead, and BHC by the end of this year at 8000 locations
throughout Japan."
"In spite of this governmental counteraction there is
no reason to expect that the present conditions of environmental
pollution in Japanese waters will improve in the near future.
Further, there is no reason to believe that the high level of
mercury contamination in the Japanese people will be changed in
any way simply by the expediency of setting limits on the
mercury consumption through guidelines on fish consumption.
These guidelines are as follows. 1. Permissible levels for
fish are less than 0.4 ppm for methylmercury. Fish containing
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mercury above these levels cannot be sold. The exception to
this rule is in the sale of tuna, marlin, swordfish, and
freshwater fish with little marketability. Recently six other
species of fish were added to the exception for the reason that
the consumption of these species is quite small though these
fishes contain mercury higher than the permissible levels. 2.
The allowable level of methylmercury intake for an adult of 50
kg of weight is 170 ug/week."
"These limitations and permissible levels have little
meaningful significance because most of the fish commonly
consumed by the Japanese people are of small to medium size and
thus contain mercury levels far lower than indicated in the
Government guidelines. Also tuna, marlin, and swordfish are not
subject to the application of these governmental standards. The
allowable levels of methylmercury intake were determined on the
basis of a combination of information derived out of anllnal
experiments with monkeys, allowable intake levels derived from
research done by the Kumamoto University Minamata Disease
Research Group, and levels of permissible intake published by
the World Health Organization. Typical cases of methylmercury
poisining will not occur if all of the people can keep strictly
to the allowable intake levels, and through this the higher
mercury levels in fishermen, sushi workers, and fish retailers
would be lowered. But for the general public these guidelines
are meaningless, for they will not! have any lowering effect on
the mercury contamination level in the general population
because the daily intake of fish per man is about 100-150 g of
small size fish with relatively low mercury levels, which
results in the absorption of about 50-70 ug/week of
methylmercury."
'~oreover, there have been many instances that make
it very difficult for us to believe the statements of the
authorities in the central government related to environmental
pollution. It is undeniable that the extreme secrecy and
endless bureaucracy of the Government have made it difficult to
get meaningful information as to basic conditions relevant to
environmental pollution in Japan. There were many instances of
problems related to restriction on the availability of
information in the compilation of this report."
2714.
Eganhouse, R.P. and D.R. Young. 1978. In situ uptake of
mercury by the intertidal mussel, MytTIUS--
californianus. Marine Poll. Bull. 9:214-217.
Uptake of mercury in tissues was studied by exposing
mussels to waters near a submarine wastewater discharge.
236
-------
Digestive gland concentrations increased rapidly, from 24.7 ug
Hg/kg wet wt to 39.7-62.6 ug/kg after 24 wks. Mercury levels in
adductor muscles rose slightly from 22.7 ug/kg wet wt to
31.9-46.4 ug/kg and in gonads from 5.1 ug Hg/kg wet wt to a
maximum of 7.4 ug/kg. No correlation with depth was observed.
Mussels taken from two uncontaminated stations in California
contained 21.1-26.7 ug Hg/kg wet wt in digestive glands,
19.3-28.3 in adductor muscles, and 4.5-6.4 in gonads; specimens
from the vicinity of an outfall site contained 62.8 ug Hg/kg wet
wt in digestive glands, 61.8 in muscles, and 14.2 in gonads.
2715.
Ellgaard, E.G., J.E. Tusa, and A.A. Malizia, Jr. 1978.
Locomotor activity of the bluegill Lepomis
macrochirus: hyperactivity induced by sublethal
concentrations of cadmium, chromium and zinc. Jour.
Fish Biology 12:19-23.
During a two-week period, locomotor activities of
fish in 0.1 and 0.25 mg/l of cadmium were, respectively, 1.5 and
7.8 times that of controls. Fish surviving 0.5 mg/l cadmium, a
concentration fatal to 30% in 2 weeks, were less active than
controls. Fish in 0.05, 2.4 and 24.0 mg/l chromium were,
respectively, 1.2, 3.6, and 6.5 times as active more than
controls. Metals apparently effect hyperactive locomotor
responses by bluegills in a concentration-dependent relationship.
2716.
Eyres, J.P. and M. Pugh-Thomas. 1978. Heavy metal
pollution of the River lrwell (Lancashire, UK)
demonstrated by analysis of substrate materials and
macro invertebrate tissue. Environ. Pollution
16:129-136.
Macroinvertebrate benthos of the River lrwell are
impover ished to an extent that cannot be explained solely in
terms of organic pollution. Relatively high dissolved oxygen
levels are maintained as a result of turbulence.
Substrate-bound levels of lead, copper, and zinc are higher than
an unpolluted river over almost the entire length of the lrwell,
and at some sites the contamination is particularly severe.
Concentrations in water are very low, but high pH, about 7,
leads to rapid precipitation of discharged metals to substrate
materials. Metal concentrations in sediment were 24 to 500 mg
Cu/kg dry wt, 36 to 13,900 mg Pb/kg, and 110 to 1100 mg Zn/kg;
levels in freshwater louse, Asellus aquaticus, were 160 to 300
mg Cu/kg dry wt, 150 to 600 mg Pb/kg, and 150 to 200 mg Zn/kg.
237
-------
In leeches, Erpobdella octoculata, these values were 15 to 55
Cu, 30 to 110 Pb, and 980 to 1600 Zn/kg dry wt. Accumulation
ratios in Asellus over substrate reached 2.6 for Cu, 1.1 for Pb,
and 0.3 for Zn; in Erpobdella these were 0.5 for Cu, 0.2 for Pb,
and 2.2 for Zn. Higher accumulation ratios were obtained in
lower ambient metal concentrations.
2717.
Fletcher, G.L. 1977. Circannual cycles of blood plasma
freezing point and Na+ and Cl- concentrations in
Newfoundland winter flounder (Pseudopleuronectes
americanus): correlation with water temperature and
photoperiod. Canadian Jour. Zoo1. 55 :789-795.
A 4-year field program was conducted on flounder to
correlate changes in plasma Na+, Cl-, and freezing point
depression with sea-floor water and sediment temperatures, day
length, salinity, depth of capture and observations on
burrowing in sedbnents. Plasma Na+, Cl-, and freezing point
depression showed annual cycles with maxima in winter
(temperature-1.1 to 1.4 C) and minbna in summer (10-14 C). The
change in freezing point depression from summer to winter was
about 0.65 C; 20% of this was attributable to Na+ and Cl-
and the remaining 80% to the presence of an 'antifreeze'. Data
suggest that plasma 'antifreeze' appeared in November (4-6 C)
and disappeared during May (-1.0 to 3.0 C). During winter,
flounder were found only in deeper areas of sampling sites and
usually buried up to 12-15 cm in sedbnents which were warmer
(0.1 to 0.4 C) than seawater. Plasma Na+, Cl-, and freezing
point depression of flounder held in the laboratory for 7 days
were always significantly lower than the field-sampled fish.
Differences between these two groups were greatest during
summer, suggesting that effects of 'stress' during capture
differ seasonally.
2718.
Fletcher, G.L. and M.J. King. 1978. Copper, zinc,
calcium, magnesium and phosphate in the gonads and
livers of sockeye salmon (Oncorhynchus nerka) during
spawning migration. Compo Biochem. Physio1.
60A:127-130.
On entering freshwater during spawning migration, Ca
content in testes increased slightly to 40 mg/kg wet wt, Cu
decreased slightly to 0.2, Mg decreased slightly to 150, and Zn
decreased to 5.0 mg/kg. Metal concentrations in ovaries were
lower in Ca at 550 mg/kg wet wt, lower in Cu at 20, equal in Mg
238
-------
at 550, and lower in Zn at 25 mg/kg in freshwater. Liver metal
concentrations, in mg/kg wet wt, after migration were 60 in
females and 30 in males for Ca; 100 and 250, respectively, for
Cu; 275 and 175 for Mg; and 40 and 50 for Zn. Total ovarian Ca,
Mg, and Zn increased during migration while total testicular Zn
declined. Authors hypothesize that ovarian Zn and most Ca and
Mg was obtained from body stores other than liver, since salmon
do not eat during migration.
2719.
Garside, E.T., D.G. Heinze, and S.E. Barbour. 1977.
Thermal preference in relation to salinity in the
threespine stickleback, Gasterosteus aculeatus L.,
with an interpretation of its significance. Canadian
Jour. Zool. 55:590-594.
Thermal preferences were determined in thermal
gradients of freshwater and seawater of 32 0/00 for acclimation
of 5, 15, and 25 C in seawater. Preferred temperatures
increased through acclimations of 5-25 C, with those for
freshwater tests being about 2 C lower at each acclimation.
Final preferenda were 16 and 18 C for freshwater tests and
seawater tests, respectively. Final preferendum in such
haloplastic species is defined as the highest obtainable
preferendum that equals acclimation temperature. A later series
of disjunct preference determinations in approximately isosmotic
water (10.5 0/00) for fish acclimated to 7? 15, and 20 C yielded
mean values of 17.7, 18.2 and 18.7 C, respectively. A final
preferendum has not been designated since samples were of
separate origins. A parallel exists between these responses and
the response of this and other haloplastic species in
determination of upper lethal temperatures. The llnmediate cause
appears to be differentials in metabolic loading occasioned by
osmoregulative stresses.
2720.
Giddings, J. and G.K. Eddlemon. 1978. Photo-
synthesis/respiration ratios in aquatic microcosms
under arsenic stress. Water, Air, Soil Pollution
9 :207 -212.
The ratio of net photosynthesis (P) to total
ecosystem respiration (R) usually declines when an aquatic
ecosystem is subjected to various types of stress. PIR ratios
were measured in 12 80-1 microcosms containing water, sediment,
and entire biotic communities (dominated by Elodea sp. but also
including protozoans, rotifers, copepods, cladocerans,
239
-------
oligochaetes, nematodes, snails and insects) from a shallow
pond. P and R were estimated from changes in dissolved 02
concentrations during the day and night, respectively. After 10
weeks, the microcosms were stressed by the addition of sodium
arsenate at concentrations of 0, 0.066, 11.5, and 143.0 rng/l (as
As). P/R ranged from 1.0 to 1.4 in all microcosms before
arsenate was added. Under stress, both P and R declined in the
11.5 and 143.0 mg/l microcosms, with negative net photosynthesis
(i.e., decreases in dissolved 02 during the day) observed on
several occasions. P IR in these microcosms fell to zero or
below, returning to 1.0 after three weeks. P/R remained above
1.0 in the 0.066 mg/l and control microcosms. Authors suggest
that the P/R response could be used for screening suspected
mzardous substances in microcosms, as well as for monitoring
natural ecosystems.
2721 .
Goreau, T.J. 1977. Coral skeletal chemistry:
physiological and environmental regulation of stable
isotopes and trace metals in Montastrea annular is.
Proc. Royal Soc. London B. 196:291-315.
A detailed study has been made of C-13, 0-18,
calcium, magnesium, aluminum, strontium, and iron contents in
coral skeleton deposited dur'ing a two-year period. Strong
seasonal variations in C-13 and Mg contents have been found, and
appear to be linked to changes in growth rate. Oxygen-18
content does not show equilibrium physicochemical temperature
effects, and its lack of correlation with C-13 indicates complex
metabolic isotope fractionation. Strontium content shows little
variation. This difference from Mg is predicted on grounds of
biochemical ion transport. Iron is detrital in origin.
Measured concentrations of metals, in mg/kg dry wt, ranged from
1148 to 2253 for Mg, < 125 for Al, 347,000-385,000 for Ca,
6300-7160 for Sr, and 363-506 for Fe. Seasonal records of trace
constituents in coral skeleton are shown to differ from those
predicted by previous investigators, indicating that metabolic
effects cannot be ignored in paleoenvironmental interpretation
of carbonate skeletal chemistry. Stable isotopes are
demonstrated to be useful tools in understanding overall carbon
metabolism of photosynthetic calcifying organisms. A model of
carbon isotope fractionation is developed, and used to place
bounds on the sources of carbon used in photosynthesis and
calcification. It is estimated that approximately 40% of the
carbon supply is from seawater bicarbonate and 60% from recycled
respiratory 002'
240
-------
2722.
Hall, A.S., F.M. Teeny, and E.J. Gauglitz, Jr. 1977.
Mercury in fish and shellfish of the northeast
Pacific. III. spiny dogfish, Squalus acanthias.
U.S. Dept. Commerce, Fish. Bull. 75:642-645.
Mean (range) mercury concentration in dogfish shark
from the state of Washington were 0.92 mg/kg wet wt in fillets
(0.09-2.58), and 0.93 mg/kg wet wt in belly flaps (0.14-2.24),
with a positive correlation between mercury content of fillets
and fish weight. Mercury levels of most samples exceeded the
Food and Drug Administration's action level of 0.5 mg/kg wet wt.
2723.
Hansen, N., T.R. Folsom, and W.E. Weitz, Jr. 1978.
Determination of alkali metals in blood from North
Pacific albacore. Compo Biochem. Physiol.
60A:491-495.
Concentrations of alkali metals in blood of albacore
tuna were, in ug/kg wet wt, 6.2 for cesium, 2.6 for sodium, 2.2
for potassium, 443.2 for rubidium, and 21.5 for lithium. In
liver, mean concentration for cesium was 26.7; for sodium, 1.2;
and for potassil~, 3.2. In muscle, mean concentrations were 37.1
for Cs, 0.4 for Na, and 4.1 for K. Total alkali content was
almost constant, while individual alkali metals varied with
respect to each other and with specimen wet weight.
2724.
Hartman, A.M. 1978. Mercury feeding schedules: effects
on accumulation, retention and behavior in trout.
Trans. Amer. Fish Soc. 107:369-375.
Rainbow trout, Salmo gairdneri, were exposed to 0.5
and 2.0 mg/kg doses of ethyl-mercury (p-toluene sulfonanilide)
"Ceresan" each day for a full year and 2.5 and 10.0 mg/kg doses
delivered every 5th day of feeding during the year. A further
study extended dose levels from 5.0 to 25.0 mg/kg Ceresan given
daily. Exposure to lower doses of mercury for either feeding
schedule led to concentrations of mercury in muscle that were
similar to the average daily index of dose for as long as 6
months of feeding. Assessment of concentration in muscle at 9
months of feeding showed a breakdown of the effect in all groups
except the one receiving 0.5 mg/kg of Ceresan daily. Both dose
level and schedules influenced the concentrations of mercury in
muscle. Concentrations in excess of 0.5 mg Hg/kg wet wt muscle
were observed among trout exposed for 270 days or longer to 0.5
mg Hg/kg diet, or 90 days and longer to trout fed diets
241
-------
containing 2.0 mg/kg or higher. Daily treatment with higher
doses of 5.0 through 25.0 mg/kg led to dose-related
concentrations of mercury in muscle. Orders of mercury
concentration in a variety of other tissues differed
significantly and were generally related to dose. Fish
receiving 10.0 mg/kg of mercury every 5 days or 5.0 mg/kg or
greater doses every day in their feed were unable, with few
exceptions, to learn to avoid shock when preceded by a
signal-light. However, beyond performance on the learning task,
there was no evidence of impairment of general behavior, nor was
there any indication of physical debilitation resulting from any
treatment. There appeared to be a rapid loss of Hg from
selected tissues, although estimates of total body burden of Hg
remained high after 6 months on a mercury-free diet.
2725.
Harvey, E.J., Sr. and L.A. Knight, Jr. 1978.
Concentration of three toxic metals in oysters
(Crassostrea virginica) of Biloxi and Pascagoula,
Mississippi estuaries. Water, Air, Soil Pollution
9:255-261.
Concentrations of cadmium- lead, and mercury were
determined in oysters from 3 Mississippi estuaries in 1973 and
1974 oysters contained mean mercury levels from 0.02 to 0.41
mg/kg wet wt; these apparently reflected the low natural
background levels. Lead content ranged from 0.07 to 1.65 mg/kg
wet wt in Mississippi oysters comparable to levels in Atlantic
coast specimens. Mean cadmium concentration ranged from 0.04 to
0.94 mg/kg, approximately 6.7X lower than Atlantic oysters.
There was no statistically significant relation between oyster
size and content of Cd, Pb, or Hg.
2726.
Hoss, D.E., D.S. ~eters, W.F.6Hettler and L.C. Clements.
1978. ExcretIon rate of 5Zn: is it a useful tool
for estimating metabolism of fish in the field?
Jour. Exp. Mar. Biol. Ecol. 31 :241-252.
Experiments were conducted with pinfish, Lagodon
rhomboides, and black sea bass, Centropristis striata, to
determine the practicality of using loss rate of Zn-65 to
estimate metabolic rate of fish under natural conditions. No
significant correlations were found between this and oxygen
consumption, feeding rate, fish size, or temperature.
Restricting fish movement had no consistent effect on zinc loss,
nor did elevated level~ of. inorganic zinc in the diet. Because
242
-------
of the lack of positive results, it was concluded that rate of
loss of Zn-65 is not a practical method for estimating field
metabolism of fish.
2727.
Humphrey, H.E.B. 1975. Mercury concentrations in humans
and consumption of fish containing methylmercury.
In: Krenkel, P.A. (ed.). Heavy metals in the
aquatic environment. Pergamon Press, New York:33.
Certain species of fish from Lake St. Clair contain
over 0.5 mg/kg Hg wet wt. Accordingly, the relationship between
whole blood total mercury concentrations and human consumption
of fish was studied in this and another area of Michigan.
Randomly sampled adult residents of Algonac who eat less than
2.7 kg of fish annually from the St. Clair River illld Lake St.
Clair (noneaters) were contrasted with residents eating 11.8 kg
or more of such fish annually (eaters). These were compared
with similarly defined noneaters and eaters in South Haven where
LaKe Michigan fish contained <0.5 mg/kg of mercury. Blood
mercury levels of 65 Algonac noneaters averaged 5.7 ug/l and
ranged from 1.1 to 20.6 ug/l. Comparative values for 42 South
Haven noneaters were 5.2 and 1.6-11.5 ugll, respectivel".
Mercury levels for persons who ate fish were higher in both
communities. Blood mercury levels for 42 Algonac fish eaters
averaged 36.4 ug/l and ranged from 3.0 to 95.6 ug/l.
Comparative levels for 54 eaters from South Haven were lower,
averaging 11.8 ug/l and ranging from 3.7 to 44.6 ug/l. These
data show a direct relationship between quantity of fish
consumed and concentration of mercury measured in human blood.
Preliminary tests for methylmercury in the same human blood
samples indicate relationships similar to those observed for
total mercury. Eating of sport fish from the St. Clair waters
apparently lead to some absorption of methylmercury, but at
lower than known toxic levels.
2728.
Iverson, W.P., C. Huey, F.E. Brinckman, K.L. Jewett, and
W. Blair. 1975. Biological and nonbiological
transformations of mercury in aquatic systems. In:
Krenkel, P.A. (ed.). Heavy metals in the aquatiC-
environment. Pergamon Press, New York:193-195.
Mercury-tolerant bacterial isolates, especially
Pseudomonas, from Chesapeake Bay waters and sediments were
examined for their ability to volatilize mercury from trace
concentrations of inorganic and organomercury compounds. All of
243
-------
the nine isolates examined produced metallic mercury primarily.
One strain of Pseudomonas demonstrated a ~lerance to ~ variety
of metals in agar media: 1000 mg/kg of Al +~ 10-50 As +; 50
Co2+; 10 cr3+; 50 H~+; <10 000 Mg2+; 100 Pb~+; 10
Sn2+; 1000 Sn+4; and 10 Te+6.
2729.
Jernelov, A. and B. Asell. 1975. The feasibility of
restoring mercury-contaminated waters. In: Krenkel,
P.A. (ed.). Heavy metals in the aquatic
environment. Pergamon Press, New York:299-309.
The feasibility of dredging, covering, and other
methods to contain or remove mercury-contaminated sediments and
effects on biomagnification potential in native freshwater fish
populations is discussed.
2730.
Katz, M. 1975. The effects of heavy metal- on fish and
aquatic organisms. In: Krenkel, P.A. (ed.). Heavy
metals in the aquatiC-environment. Pergamon Press,
New York:25-30.
Author briefly reviews literature on effects of
various metals including Cu, Zn, Hg, As, Pb, Se, Fe, Ni, Co, Cr,
Cd, Na, Ca, Mg, K, Sr, Ba, Mn, Sn, Al, and pt on freshwater fish
behavior, reproduction, disease, blood chemistry, survival.
histopathology and growth. Survival, reproduction, and growth
of freshwater insects, crustaceans and gastropods is also
reviewed. A bibliography of 29 references is appended.
2731.
Krygier, E.E. and W.G. Pearcy. 1977. The source of
cobalt-60 and migrations of albacore off the west
coast of North America. U.S. Dept. Commerce, Fish.
Bull. 75:867-870.
Concentrations of Co-60 in liver of albacore tuna
Thunnus alalunga caught along the west coast of North America
between 1963 and 1969 were determined. Variations in Co-60
content between geographic locations were evident and discussed
in terms of fallout from atmospheric tests of nuclear weapons,
effluents from nuclear reactors, ocean circulation patterns,
biological turnover rates, and migratory routes. Authors
concluded that Co-60, unlike Zn-65 and Mn-54 levels, were
derived primarily from fallout.
244
-------
2732.
Kumaraguru, A.K. and K. Ramamoorthi. 1978. Toxicity of
copper to three estuarine bivalves. Marine Environ.
Res. 1 :43-48.
Static LC-50 (96 hr) values for copper to Anadara
granosa, Meretrix casta, and Crassostrea madrasensis was
determined at 25 0/00 S, pH 8.0 and 27 C. Values were 60 ug
Cull for!. granosa, 72 for ~. casta, and 88 for f.
madrasensis. Revival rates of bivalves which survived exposure
to the LC-50 concentrations for the 96-hr period and were then
released in the natural environment were 67% for !. granosa and
f. madrasensis, and 83% for ~. casta.
2733.
Lorens, R.B. and M.L. Bender. 1977. Physiological
exclusion of magnesium from Mytilus edulis calcite.
Nature 269:793-794.
The mussel, which normally secretes low magnesium
calcite, incorporates anomalously high amounts of Mg into its
calcite shell layer when grown in solutions of higher than
normal magnesium content. In normal conditions, Mytilus
physiologically excludes Mg from its shell-f0rming fluid. At
higher Mg concentrations, ion regulatory systems break down
causing a substantial increase in content of Mg coprecipitated
into mussel shell calcite.
2734.
Lux, F.E., J.R. Uzmann, and H.F. Lind. 1978. Strandings
of short fin squid, Illex illecebrosus, in New England
in fall 1976. Marine Fisheries Rev. 40:21-26.
Massive strandings of squid were observed at Cape Cod
Bay, Massachusetts, during 1976. "With the exception of cadmium
and copper, which were somewhat higher in the stranded squid,
the results were similar to those for the 1972-73 samples caught
farther offshore. It is not known if any significance can be
attached to the higher levels of cadmium and copper, since the
1976 samples (stranded squid) were based on the entire animals,
compared with mantles only for the 1972-73 samples". There was
no apparent increase in mercury.
2735.
MacLeod, M.G. 1978. Effects of salinity and starvation
on the alimentary canal anatomy of the rainbow trout
Salmo gairdeneri Richardson. Jour. Fish Biology
12:71-79.
245
-------
Effects of salinity, starvation and their
interactions on the alimentary canal of immature trout was
studied. Intestinal and rectal cross-sectional areas a.nd height
of intestinal villi increased with salinity. The thickness of
none of the tissue layers measured in the intestine and rectum,
including columnar epithelium and tunica propria, was influenced
by salinity. There was a significant negative correlation
between salinity and mucous cell distribution density in both
intestine and rectum. In trout acclimated to salinities of 15
0/00 and higher, there was a high incidence of deep depresssions
in columnar epithelum. The oesophagus and stomach were not
visibly affected by salinity There was a marked decrease in
intestinal and rectal cross-sectional area and height of
intestinal villi with starvation, except in 32.5 0/00 seawater.
Mean intestine epithelial cell height decreased with starvation
at 32.5 0/00. A 48-day period of starvation had little effect
on the posterior oesophagus and cardiac stomach.
Z736.
Mangi, J., K. Schmidt, J. Pankow, L. Gaines and P.
Turner. 1978. Effects of chromium on some aquatic
plants. Environ. Pollution 16:285-291.
Algal growth was inhibited after 14 days exposure to
10 mg CrO~-/l in freshwater. Unicellular Pamella mucosa
and Palmellococcus protothecoides declined in cell number;
filamentous Oedogonium sp. and Hydrodictyon reticulatum lost
weight; and duckweeds Lemna minor and Spirodela polyrrhiza grew
fewer new fronds than controls. Plants exposed to 10 mg Cr/l
generally accumulated 100 to 5000 mg Cr/kg over 14 days;
Palmellococcus accumulated over 1,000,000 mg/kg. Maximum
enrichment values in algae of 200 to 500 over medium were
reached in lower Cr levels of 0.001 mg/l. Chromium was taken up
by dead algae. Heat-killed Oedogonium removed 70-90% of Cr in
solution over 6 days.
2737.
Marchetti, R. 1978. Acute toxicity of alkyl leads to
some marine organisms. Marine Poll. Bull. 9:206-207.
Following the wreck of the Yugoslavian cargo ship
"Cavtat" in the Adriatic Sea in 1974 with resultant spillage of
alkyl lead compounds, an investigation was conducted to
establish the acute toxicities of alkyl lead compounds to
representative marine organisms. Concentrations of tetramethyl
lead and tetraethyl lead, in ug/l, that reduced oxygen
consumption by 50% over 48 hrs in marine bacteria were 1900 and
246
-------
200, respectively. Photosynthesis decreased 50% in algae,
Dunaliella tertiolecta, in 1650 and 150 ug/l, respectively.
LC-50 (48 hr) values for brine shrimp larvae, Artemia salina,
were 250 (tetramethyl) and 85 ug/l (tetraethyl). For fish
larvae, Morone labrox, LC-50 (48 hr) values were 100 and 65
ug/l, respectively. No effect was seen during 48 hrs at
tetramethyl lead and tetraethyl lead levels of 900 and 80 ug/l,
respectively, for bacteria, 450 and 100 for algae, 180 and 25
for brine shrimp, and 45 and 10 ug/l for fish.
Z738.
McCarty, L.S. and A.H. Houston. 1977. Na+:~- and
HC03- stimulated ATPase activities in the gills
and kidneys of thermally acclimated rainbow trout,
Salmo gairdneri. Canadian Jour. Zool. 55:704-712.
Gill and kidney Mg2+-dependent, Na+:~- and
Hoo3: stimulated ATPase activities were estimated at 25 C
and at acclimation temperature in trout acclimated to 2, 10 and
18 C, as were plasma levels of Na, K, and chloride. Sodium and
chloride exhibited no si~nificant variation between 2 and 18 C.
When assayed at 25 C, ~+ -dependent and HC,'J3- stimulated
ATPase activities did not vary consistently or significantly in
relation to acclimation temperature. Under comparable assay
conditions both gill and kidney Na+:~-stimulated activities
declined at higher acclimation temperatures. Significant
increases in all activities were encountered when preparations
were incubated at the appropriate acclimation temperature.
Results suggest that the branchial Na+:~-ATPase system
serves primarily as a high-temperature amplifier of Na uptake,
and may contribute little to the maintenance of Na balance in
the cold-adapted animal. No evidence of a critical involvement
of HOOf stimulated ATPase in ionic regulations was
obtained.
Z739.
Miettinen, J.K. 1975. The accumulation and excretion of
heavy metals in organisms. In: Krenkel, P.A.
(ed.). Heavy metals in the aquatic environment.
Pergamon Press, New York: 155-162.
Mechanisms and rates of absorption and excretion of
heavy metals in fish, molluscs, crustaceans and especially man
are briefly reviewed. Examples are listed for Cd, Hg, Pb, Zn,
Se with emphasis on biological half-time of mercury compounds in
aquatic organisms.
247
-------
2740.
Moller, H. 1978. The effects of salinity and
temperature on the development and survival of fish
parasites. Jour. Fish Biology 12:311-323.
In brackish water the variety of marine and
freshwater parasite species is considerably reduced. The
distribution of most marine endoparasites in brackish water is
restricted by salinity tolerance of hosts, with most parasite
species more tolerant than hosts. The influence of salinity and
temperature on nine parasite species has been examined; first
stage larvae of Contracaecum aduncum (a nematode) develop in
0-32 0/00 salinity; Cryptocotyle lingua (trematode) proved to be
infective at salinities as low as 4 0/00. The greatest
resistance was found in Anisakis (nematode) larvae from herring,
Clupea harengus, which survived for more than half a year.
Parasites in fish intestines appear to be unaffected by changing
water salinities, as osmolarity in intestines stays nearly
constant. Marine ectoparasites (Acanthochondria depressa and
Lepeophtheirus pectoralis, copepods) survive about three times
longer than freshwater species (Piscicola geometra, a leech;
Argulus foliaceus, an arguloid crustacean) when salinity is 16
0/00. High temperature increases effects of adverse salinities
on parasites. There is evidence that none of these
ectoparasitic species can develop within 7-20 0/00 salinity.
2741.
Munda, I.M. 1978. Trace metal concentrations in some
Icelandic seaweeds. Botanica Marina XXI:261-263.
Trace metal concentrations in 11 species of marine
algae, 4 of Rhodophyceae and 7 of Phaeophyceae ranged from 0.3
to 11.9 mg/kg dry wt for Co; 1.8 to 8.8, with a high of 80, for
Cu; 13 to 130, with maxima of 680, for Mn; and 2.5 to 75.0 mg/kg
for Zn. Metal levels varied between species; two Porphyra
species contained highest values of Cu and Zn. In general,
concentrations of Co, Mn, and Zn varied inversely with salinity.
2742.
Munda, I.M. and C. Garrasi. 1978. Salinity-induced
changes of nitrogenous constituents in Fucus
vesiculosus (Phaeophyceae). Aquatic Botany 4:347-351.
When marine algae, f. vesiculosus, were transferred
from water of 32 0/00 S to lower salinity of 5 to 15 0/00,
chemical composition of the thallus was altered. The total
amount of nitrogenous compounds was distinctly enhanced with
248
-------
tllne and salinity reduction, including changes in amino acid
pattern. After 33 days in 5 0/00 S water, percent dry wt, ash
content, and mannitol content decreased and protein nitrogen
increased.
2743.
Murray, C.N., M. Hoppenheit, and H. Rade. 1978.
Accumulation of americium-243 in selected brackish
and marine invertebrates. Helgolander wiss.
Meeresunters 31:34-54.
Accumulation of americium in the polychaete worm
Nereis diversicolor, the brackish-water amphipod Gammarus
duebeni and the harpacticoid copepod Tisbe holothuriae was
studied under laboratory conditions over a 10-day period. Large
differences in concentration factors occurred for the same
organisms, depending upon aging of the contaminated medium.
Much higher and more variable values were found when uptake was
from freshly contaminated solutions than from those aged up to a
week. The interaction of specllnens with physico-chemical
reactions of americium which appear to take place within the
first few days after its introduction into water are considered
to be responsible for these differences. Uptake from
contaminated water that had been allowed to age in the absence
of organisms appears to be unaffected by subsequent conditioning
by specllnens. Americium concentration factors show a strong
tendency to increase with decreasing size of the species,
varying from over 1000 for T. holothuriae to about 3 for N.
diversicolor. The possibility that the mechanisms regulaIing
the uptake of actinides in different species may depend upon pH
is briefly discussed.
2744.
Myklestad, S., I. Eide, and S. Melsom. 1978. Exchange
of heavy metals in Ascophyllum nodosum (L.) Le Jod.
in situ by means of transplanting experiments.
Environ. Pollution 16:277-284.
Newly-grown tips of brown algae, A. nodosum,
transferred from a metal-llnpacted locality to an uncontaminated
site had cadmium, lead, mercury, and zinc contents similar to
local uncontaminated plants after 5 months. Tips contained < 1.0
to 2.0 mg Cd/kg dry wt, <3.0 mg Pb/kg, 0.04 to 0.10 mg Hg/kg,
and 100 to 140 mg Zn/kg. In older parts of algae, Hg and Zn
decreased slightly in the uncontaminated area to 1.0 to 1.4 and
1430 to 2710 mg/kg dry wt, respectively; Cd and Pb remained
steady in older sections at 4.0 to 7.0 and 9.0 to 39.0 mg/kg,
respec ti vely .
249
-------
2745.
Nagahama, Y., W.C. Clarke, and W.S. Hoar. 1977.
Influence of salinity on ultrastructure of the
secretory cells of the adenohypophyseal pars distalis
in yearling coho salmon (Oncorh~nchus kisutch).
Canadian Jour. Zool. 55:183-19.
Six different types of secretory cells were
identified in adenohypophyseal pars distalis of salmon
acclimated to fresh- or saltwater. Prolactin cells are markedly
more active in freshwater than seawater acclimated fish.
Prolactin cells exhibit definite functional activity 3 days
after transfer from salt- to freshwater, indicating an
osmoregulatory role of prolactin in freshwater. Plasma Na
showed a significant decline 6 hr after transfer from seawater
to freshwater and after one week, remained lower than in fully
acclimated freshwater fish. Corticotropic cells did not appear
cytologically different in freshwater and seawater fish. GH
cells, the most prominent cells in the proximal pars distal is,
appear more numerous and more granulated in seawater fish,
suggesting an osmoregulatory involvement in young coho salmon.
Putative thyrotropic and putative gonadotropic cells (GTH) can
be distinguished by differences in granulation. Only one type
of GTH cell is evident with ultrastructural features that differ
from those of sexually mature salmon. Stellate, non-granulated
cells occur in all regions of the adenohypophysis but more
frequently in the prolactin follicles; they are much more
prominent in seawater than freshwater fish.
2746.
Nakahara, H., T. Iskikawa, Y. Sarai, I. Kondo, and S.
Mitsuhashi. 1977. Frequency of heavy-metal
resistance in bacteria from inpatients in Japan.
Nature 266:165-167.
Frequency of resistance in 564 strains of E. coli,
331 strains of K. pneumoniae, 787 strains of f. aeruglnosa-and
515 strains of ~. aurens to Hg, Cd, As and Pb was determined.
Frequency of a heavy metal resistance was the same as, or higher
than, that of an antibiotic resistance, and many isolates were
heavy-metal resistant but drug sensi ti ve. A total of 317 R
plasmids with an Hg resistance from Hg-resistant E. coli and K.
pneumoniae (91.1% frequency) were isolated. In addition 297 R
plasmids mediated arsenic resistance.
2747 .
Nakazawa, S. 1977. Development of Fucus eggs, as
affected by iodine, lithium and nitroprusside.
Japan. Soc. Phycol. 25, Suppl.:215-220.
Bull.
250
-------
Eggs from the hermaphroditic marine alga Fucus
evanescens were cultured with KI, NaI, CaI2' KCl, KBr, L1Cl,
2,4-dinitrophenol, and sodium nitroprusside. Iodine induced
giant or multiple rhizoids, but lithium (about 500 mg Li+/l)
counteractively diminished rhizoidal development. Nitroprusside
completely inhibited rhizoid formation without affecting
cleavage.
2748 .
Nichols, K.M. and R. Rikmenspoel. 1978. Control of
flagellar motion in ChlamYdOm~S and Eu~lena by
mechanical microinjection of T and Ca T and by
electric current injection. Jour. Cell Sci.
29:233-247.
Upon impalement with a microelectrode in a
Ca2+-free medium containing 5 roM ATP, a Chlamydomonas cell
lost its flagellar activity within 45 sec, and the injection of
either positive or negative direct current did not stimulate the
flagella to beat after that time. When 3 roM ~+ was added to
external medium, the bnpaled cell exhibited a flagellar
fr~quency of 22 Hz. With 5 roM ATP and 3 roM Mi2+ in a
Ca +-free medium, negative direct electric current inhibited
flagellar frequency and positive direct electric current
enhanced flagellar activitv. The fl~~~ll~ ~~~~vered to
approx bna tely their characteristic frequency (20 Hz) upon the
cessation of current. Euglena and Chlamydomonas cells were
mechanically microinjected with ea2T or MgZT ions contained
in 1.0 M KC12filled microelectrodes, In both cells, injection
of 0.02 M ea + resulted i2 a decrease in flagellar frequency
dependent on amount of Ca + injected. Th14frequency decreased
to zero ~4upon the injection of 16 x 10- 1 in Euglena and
3.5 ~ 10- 1 in ~~domonas. The microinjection of 10 x
10-1 1 of 0.2 M ;nto Euglena cells resulted in an
approxbnately 2-fold increase in flagellar frequency.
Ch domonas flagella, which stop beating upon bnpalement in a
-!r~e medium, began to beat when the cell was injected
with MgL+ ions. The flagella exhibit1~ an average fr~quency
of 16 Hz when injected with 1.5 x 10- 1 of 0.2 t;1 MgL+.
The data indicate that an increase in internal ~+ stimulates
flagellar frequency and that microinjection of Ca2+ inhibits
flagellar motility.
2749.
Paskins-Hurlburt, A.J., s.C. Skoryna, Y. Tanaka, W.
Moore, Jr., and J.F. Stara. 1978. Fucoidan: its
binding of lead and other metals. Botanica Marina
XXI: 13-22.
251
-------
A sulphated polysaccharide derived from marine algae
Ascophyllum nodosum was studied for its ability to bind Ba, Ca,
Cd, Co, Cr, Cu, Fe, Ag, Mg, Mn, Ni, Pb, Sr and Zn with specific
reference to lead and calcium. Studies were carried out in
vitro and in vivo using rats. Using the efficiency of
ion-exchange reactions with divalent cations, the order of
preferential binding was established for fucoidan. This
polyelectrolyte had the greatest affinity for lead with
relatively little binding of calcium. Studies in vivo
demonstrated a 70% reduction in Pb absorbed by rats when using
fucoidan. It was concluded that this naturally occurring
non-toxic polyelectrolyte is a suitable binding agent for lead
and that the insignificant binding of calcium is an llnportant
criteria for biological and clinical application. The high
biological activity of this compound depends on position and
availability of functional groups for the ion-exchange process,
and viscosity of the solution.
ZT50.
Patel, G.B. and L.A. Roth. 1977. Effect of sodium
chloride on growth and methane production of
methanogens. Canadian Jour. M;crobiol. 23:893-897.
Methanobacterium hungatii were not affected by up to
5680 mg NaCl/l; however, growth was inhibited at higher
concentrations. Concentrations >890 mg NaCl/l were inhibitory
to~. thermoautotrophicum and an unidentified methanogen.
OptllnUffi growth and methane production occurred at 890 mg/l for
the unidentified species.
ZT51.
Paul, M. and R.N. Johnston. 1978. Uptake of Ca2+ is
one of the earliest responses to fertilization of sea
urchin eggs. Jour. Exper. Zoology 203:143-149.
Strongylocentrotus purpuratus eggs accumulate Ca-45
for 10 min following insemination. Although 90% of this uptake
occurs after the beginning of the cortical reaction and may
represent external binding of Ca to the egg surface coats, there
is a brief phase of uptake (0-30 sec) which precedes the
cortical reaction and this may represent a Ca flux into eggs.
2752.
Pribil, S. and P. Marvan. 1976. Accumulation of uranium
by the chlorococcal alga Scenedesmus quadricauda.
Arch. Hydrobiol. suppl. 49:214-225.
252
-------
Effect of pH, temperature, uranium concentration, and
biomass on algal accumulation of U was examined. Accumulation
occurred in two phases; about 60% of 18 mg U/l in solution was
removed by algae in the first minute, then uptake equilibrium
was reached within 7 hrs. After 6 hours at 20-30 C, maximum
accumulation in 9.5 mg U/l, was 29,000 mg U/kg dry wt at pH 5.9
to 6.8; in 18 mg U/l, this was 67,000 mg U/kg. In dilute algal
solutions of 30 mg biomass/I, accumulation was much greater, up
to 94,400 mg U/kg, than in denser cultures. Uranium
concentrations in algae reached 79,000 to 100,000 mg U/kg when
water residual levels were 3.5-10.0 and 10.0-35.0 mg U/l.
Authors concluded that interpretation of U accumulation is
complicated by the variety of uranyl ion forms that occur, by
physiological processes of algae, and by the variability of
accumulation coefficients due to environmental conditions.
2753.
Rice, D.W., Jr. and F.L. Harrison. 1978. Copper
sensitivity of Pacific herring, Clupea harengus
pallasi, during its early life history. U.S. Dept.
Comm., Fish. Bull. 76:347-356.
Embryos and larvae of herring were exposed to copper
using a flow-through bioassay system. Embryos were exposed
continuously from 12 hrs after fertilizat"on until hatching, and
larvae from time of hatching until yolk sac absorption. Embryos
were also exposed to 36-hr duration pulses of copper. Pulsed
exposures started at 62, 98, or 136 hrs after fertilization.
The following measurements were taken as indices of the toxic
effects of copper: cumulative mortality, percent hatching, and
larval length upon hatching. The onset of rrortality of herring
embryos continously exposed to copper began 90 hrs after
fertilization, with deaths occurring over a short interval
thereafter. Significant embryo mortalities occurred at a copper
concentration as low as 35 ug/l. Larvae continuously exposed to
copper showed significant mortality at 300 ug/l copper, with no
delay in onset of rrortality. Embryos exposed to 36-hr pulses of
copper during different developmental stages showed reduced
sensitivity when exposed after the response period. Larvae that
hatched from eggs exposed to a 36-hr pulse of copper before the
response period grew significantly less than those hatched from
eggs exposed during later developmental stages.
2754.
Rolfe, G.L. and J.C. Jennet. 1975. Environmental lead
distribution in relation to automobile and mine and
smelter sources. In: Krenkel, P.A. (ed.). Heavy
253
-------
metals in the aquatic environment.
New York:231-240.
Pergamon Press,
Differences in concentrations of Pb from freshwater
fish, macrophytes, sediments, and benthos collected in 1972-1973
from rural areas and sediments and benthos from urban areas were
attributable primarily to lead emissions from automobiles.
Stream sediments from urban areas contained about 6X more Pb in
the upper 10 cm than sediments from rural areas; for the 10-20
cm fraction this difference was about 7X. Mean concentrations
of Pb in aquatic biota from rural compartments, in mg/kg, ranged
from 1.8-2.4 for fish, 16.2-24.1 for macrophytes, and 5.4-18.9
for benthos. Urban benthos contained 139.6-518.8 mg/kg.
2755.
Rosenberg, R. and J.D. Costlow, Jr. 1976. Synergistic
effects of cadmium and salinity combined with
constant and cycling temperatures on the larval
development of two estuarine crab species. Marine
Biology 38:291-303.
Various developmental stages of blue crabs,
Callinectes sapidus, were tested in 12 combinations of cadmium
(0, 50, and 150 ug/l) and salinity (10, 20, 30, and 40 0/00) at
25 C. A reduction in survival and a significant delay in
development from megalopa to third crab occurred in each
salinity in 50 ug Cd/lover about 25 days. Cadmium-induced
developmental delay, when compared within each salinity regime,
was most pronounced in salinities normally preferred by
Callinectes. However, comparison within each Cd concentration
showed similar development rates regardless of salinity.
Developmental stages from hatch onwards of mud crabs,
Rhithropanopeus harrisii, were examined in 63 combinations of
cadmium (0, 50, and 150 ug/l), salinity (10, 20, and 30 0/00),
constant temperature (20 to 35 C), and cycling temperature (20
to 25, 25 to 30, and 30 to 35 C). Cycling temperatures appeared
to have a stimulating effect on survival of larvae compared to
constant temperatures, both in presence and absence of cadmium.
Zoeal larvae were more susceptible to Cd than mepalops.
Development was generally prolonged in high Cd and low
temperature; salinity effects were variable.
2756.
Sanders, J.G. 1978. Enrichment of estuarine
phytoplankton by the addition of dissolved
manganese. Marine Environ. Res. 1:59-66.
254
-------
The response of natural phytoplankton over a period
of 4 hours to additions of excess Mn up to 1.6 mg/l in an
estuary receiving sewage effluent varied with tidal amplitude.
During periods of low tidal amplitude, when dissolved organic
carbon (DOC) concentrations were high, carbon uptake by
phytoplankton was stimulated. When tidal amplitudes were
relatively high, carbon uptake was not affected by Mn addition.
The link between high DOC concentrations and stimulation
suggests that Mn addition either relieves a deficiency in
available Mn caused by organic complexation, or complexes
organics from sewage effluent which are otherwise harmful to
phytoplankton productivity. Sewage effluent entering estuaries
can be both beneficial and detrimental to the phytoplankton
population. Productivity is increased by the addition of
inorganic nutrients but may be depressed by organics in the
effluent.
2757.
Shapiro, M.A. and D.W. Connell. 1975. Investigations of
heavy metals and other persistent chemicals,
Westernport Bay, Australia. In: Krenkel, P.A.
(ed.). Heavy metals in the aquatic environment.
Pergamon Press, New York:247-250.
Investigations conducted on Cu, Pb, Zn, and Cd, in
algae, fish, crustaceans, and molluscs from Westernport Bay are
briefly summarized.
2758.
Siebers, D. and H.-P. Bulnheim. 1977. Salinity
dependence, uptake kinetics, and specificity of
amino-acid absorption across the body surface of the
oligochaete annelid Enchytraeus albidus. Helgolander
wiss. Meeresunters. 29:473-492.
Enchytraeus can absorb dissolved C-14-labeled amino
acids (glycine, L-alanine, L-valine, a-aminoisobutyric acid) and
an amino acid mixture from ambient water across the body surface
against considerable concentration gradients. Absorption of
neutral amino acids is an active process. Results on inhibition
of glycine uptake by a variety of low-molecular-weight
substances indicate that glycine absorption is highly specific
for neutral amino acids and somewhat less for basic amino acids,
and is unspecific for non-a-amino acids, acidic amino acids,
carbohydrates, and organic acids. Rates of trans integumentary
net influx of glycine are nearly identical to C-14-glycine
influx, suggesting that only small amounts of amino acids are
255
-------
released, compared with uptake capacity. Glycine uptake is
positively correlated to external salinity. In freshwater,
glycine absorption is nearly zero; between 10 and 20 0/00,
uptake increases markedly, reaching maximum values at 30 0/00;
these remain almost constant at 40 0/00. Transport constants
and maximum uptake rates increase with rising salinities. Since
absorption of glycine and L-valine is susceptible to sodium
depletion, similar mechanisms presumably underlie
salinity-dependent uptake of amino acids and sodium-dependent
solute transport. Oxygen consumption is not significantly
modified by different external salinities. Estimates of
nutritional profit gained from absorption of amino acids vary
between 4 and 15% of metabolic rate for glycine absorption and
between 10 and 39% for uptake of an amino-acid mixture,
according to external concentrations and salinities.
2759.
Sivalingam, P.M. 1978. Biodeposited trace metals and
mineral content studies of some tropical marine
algae. Botanica Marina XXI: 327-330.
Concentrations of trace metals in waters and sediment
of Batu Ferringhi, Penang Island, in 1976 and 1977, indicated
that almost all levels fall within the category of water-type I
(unpolluted). Biodeposited trace metals in one species of
Cyanophyta, 9 of Rhodophyta, 4 of Phaeophyta, and 6 of
Chlorophyta showed high values compared to the same water-type
category in the Oresund, Sweden, area with the exception of Zn.
Metal levels observed, in mg/kg dry wt, ranged from 74 to
242,000 for Ca, 4.0 to 16.0 for Cd, trace to 59 for Cr, trace to
50 for Cu, 350 to 15,500 for Fe, 2000 to 110,100 for K, 3100 to
41,000 for Mg, 24 to 320 for Mn, 2000 to 168,000 for Na, 1.7 to
56.0 for Pb, and 14 to 210 for Zn. No significant correlation
of biodeposited trace metals among algal groups was observed.
Some algal species, though living in unpolluted water-type I,
had biodeposited Zn, Cu, and Pb at concentrations above 100, 20,
and 10 mg/kg, respectively, which are values only observable in
algal species from polluted areas. Concurrent studies on
biodeposited concentrations of elements such as Ca, K, Na, Mg,
Mn, and P also showed similar trends. It was proposed that
certain algal species within the tropical zone could be used as
pollution indicators.
2760.
Sturesson, U. 1978.
Mytilus edulis.
Cadmium enrichment in shells of
Ambio 7:122-125.
256
-------
Accumulation of cadmium was measured in periostracum,
nacre, and calcitic and calcitic/aragonitic calcium carbonate
sections of shells of mussels exposed to various CdC12
levels. Maximum cadmium levels were found in periostracum and
nacre; concentrations rose to 75 mg Cd/kg and 17 mg Cd/kg,
respectively, as ambient levels increased to 200 ug/l for up to
50 days. Mussels accumulate more lead, as shown by previous
uptake studies, than cadmium in shells under similar conditions.
2761.
Suckcharoen, S., P. Nuorteva, and E. Hasanen. 1978.
Alarming signs of mercury pollution in a freshwater
area of Thailand. Ambio 7:113-118.
Mercury concentrations in the teleosts Ophiocephalus
striatus, Mystus nemurus, Notopterus chitala, Charias
macrocephalus, and Pangasius pangasius in 1973 were among the
lowest in the world, ranging from 0.002 to 0.30 mg Hg/kg wet wt
with a mean of 0.07 in flesh. Aquatic birds, cormorants,
herons, and egrets, contained 0.15 to 0.56 mg/kg wet wt, with a
mean of 0.27 in pectoral muscle. Mercury in human hair from
unpolluted areas was 0.77 to 14.0 mg/kg, averaging 2.3 mg/kg. A
local increase was, however, observed in the flesh of the fish
O. striatus in the vicinity of a recently established Japanese
caustic soda factory, where mercury measured 0.32 to 3.6 mg/kg
wet wt flesh. Hg accumulation was observed in human hair of
males but not females living in the polluted area.
2762.
Tilton, R.C. and B. Rosenberg. 1978. Reversal of the
silver inhibition of microorganisms by agar. Applied
Environ. M"crobiol. 35:1116-1120.
Three agar media were tested for their ability to
neutralize bacteriostatic effects of silver on Escherichia
coli. Silver, at 50 ug/l, killed all E. coli within 10 min.
However, when thioglycolate-thiosulfate reagent was added with
agars, initial colony size was larger and only 50% of the cells
died in 10 min. Algal growth was equivalent to controls in up
to 400 mg Ag/l with tryptone glucose agar. Growth media
differed in their neutralizing capacity; non-;nhibitory media
tryptone glucose agar and Trypticase soy agar showed more
neutralizing capacity than eosin methylene blue agar. The
neutralizing effect was a function of the soluble component of
the media and not of agar itself.
257
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2763.
Torma, A.E. 1978. Oxidation of gallium sulfides by
Thiobacillus ferrooxidans. Canadian Jour.
Microbiol. 24:888-891.
Bacterial oxidation of a naturally occurring
gallium-bearing chalcopyrite concentrate and a pure synthetic
gallium sulfide was investigated at pH 1.8 and 35 C, using a
culture of Thiobacillus ferrooxidans. This oxidation process
may proceed by direct or by indirect bacterial action. Maximum
dissolved gallium and copper concentrations were about 2,200 and
40,200 mg/l, respectively. Order of specific rate of oxygen
uptake by T. ferrooxidans was approximately CuFe~ > Ga-bearing
CuFe~ > Fe"S2 > 'GuS> CU2S > Ga2S3. -
2764.
Wood, J.M. 1975. Metabolic cycles for toxic elements in
the environment. A study of kinetics and mechanism.
In: Krenkel, P.A. (ed.). Heavy metals in the
aquatic environment. Pergamon Press, New
York: 105-112.
Author categorizes selected elements into three
groups according to their toxicity: noncritical elements, i.e.
Na, K, Mg, Ca, Fe, Li, Rb, Sr, Ba, Al, Si; very toxic and
relatively accessible elements such as Be, Co, Ni, Cu, Zn, Sn,
As, Se, Te, Pd, Ag, Cd, Pt, Au, Hg, Tl, Pb, Sb, Bi; and toxic
but very insoluble or very rare elements Ti, Hf, Zr. W, Nb, Ta,
Re, Ga, La, Os, Rh, Ir, Ru. The role of bacteria in the mercury
and arsenic cycles is emphasized and illustrated.
2765.
Azam, F., R.F. Vaccaro, P.A. Gillespie, E.L. Moussalli,
and R. E. Hodson. 1977. Controlled ecosystem
pollution experiment: effect of mercury on enclosed
water columns. II. marine bacterioplankton. Marine
Science Commun. 3:313-329.
Effects of 1.0 and 5.0 ug/l added mercury on natural
marine bacterioplankton were examined in Controlled Experimental
Ecosystems, plastic cylinders containing 1300 m3 of seawater
and its complement of natural biota from Saanich Inlet, British
Columbia. Heterotrophic activity, measured as D-glucose
assimilation and respiration, was initially inhibited by 1.0 ug
Hg/l to less than 1% of the control, followed by a rapid
recovery within 5 days to control levels. Bacterial biomass,
estimated from adenosine-5'-triphosphate in bacterial size
fraction, decreased to 8-40% of controls, but also recovered
258
-------
within 5-7 days. Succeeding bacterial populations showed
enhanced mercury tolerance and were also copper tolerant,
although no copper additions were made to enclosures. It is
suggested that, whereas decrease in bacterial standing stocks
and heterotrophic activity is only transient, dominance of
mercury- (and copper-) tolerant bacteria in mercury-polluted
ecosystems may have implications for the biologically-mediated
rate of mercury.
2766.
Baldwin, G.F. and L.B. Kirschner. 1976. Sodium and
chloride regulation in Uca adapted to 175% sea
water. Physiological Zoology 49: 158-171.
Sodium and chloride regulation in fiddler crabs
adapted to 175% seawater showed that turnover rate for both ions
averaged 38%/hr. With urine produced at a rate of 0.5% body
weight/day, renal losses contributed 0.1% of the total flux for
Na+ and 0.3% for Cl-. Intestinal route provided
approximately 5% of the total influx of both ions assuming
complete absorption of all ingested salts. Deletion of Na+ or
Cl- from the medium reduced efflux of the corresponding ion,
an effect associated with exchange diffusion. However, other
results indicate such effects could also be due to permeability
changes in the absence of Na+ or Cl-. Whether or not
exchange diffusion occurs, flux ratio analysis indicated that
both Na+ and Cl- were actively pumped from crabs in 175%
seawater.
2767.
Baldwin, G.F. and L.B. Kirschner. 1976. Sodium chloride
regulation in Uca adapted to 10% sea water.
Physiological Zoology 49: 172-180.
Aspects of Na+ and Cl- regulation in fiddler
crabs adapted to 10% seawater were examined. Total body
turnover rate averaged 8%/hr for Na+ and 19% /hr for Cl-.
Urine was produced at the rate of 5% body weight/day. Based on
the assumption that blood and urine were isotonic, the renal
route represented 3-4% of total efflux of both ions. The
intestinal route provided a negligible influx of a salt.
Deletion of Na+ from the medium caused little change in efflux
of this ion. Depletion of Cl- medium caused approximately 50%
reduction in Cl- efflux; however, Na + efflux was also
reduced in Cl-free medium. Flux ratio analysis indicated that
both Na+ and Cl- were actively absorbed by fiddler crabs in
dilute seawater.
259
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2768.
Beers, J.R., M.R. Reeve, and G.D. Grice. 1977.
Controlled ecosystem pollution experiment: effect of
mercury on enclosed water columns. IV. zooplankton
population dynamics and production. Marine Science
Commun. 3:355-394.
Taxonomic composition and abundance of total
zooplankton populations contained in three 1300 m3 enclosures
(Controlled Experimental Ecosystems or CEEs) in Saanich Inlet,
British Columbia, Canada, were studied over a 72 day period from
May to July, 1976; inorganic mercury vms introduced at nominal
concentrations of 5.0 and 1.0 ug/l into CEE 5 and CEE 1,
respectively. Immediately following mercury addition,
zooplankton populations declined in CEE 5, but the control a.nd
CEE 1 remained relatively similar in total numbers and
proportional taxonomic composition. In the two latter CEEs,
large increases of herbivores occurred as a consequence of
nutrient additions and lack of predator pressure. CEE 5
populations showed slight increases, but different dominant
forms. The original decrease and failure of copepods
Pseudocalanus and Acartia to subsequently increase their
populations rapidly were attributed to direct effects of
mercury, although food quality may have affected some of the
observed population fluctuations. When mercury level had
subsided in CEE 5, some protozoan taxa with short generation
times equalled or exceeded the abundance attained in the other
CEEs. As a consequence of the few predators present and the
correspondingly low mortality of copepod developmental stages,
it was possible to compute the production of Pseudocalanus and
Acartia, the two copepods comprising the bulk of the
mesoplankton. For CEE 1 and the control at least 29% and 18%,
respectively, of the primary production apparently was converted
to the next higher trophic level.
2769.
Bengtsson, B.-E. 1977. Accumulation of cadmium in some
aquatic animals from the Baltic Sea. Ambio, Spec.
Rept. 5:69-73.
Salinity is an important modifying factor in
accumulation of cadmium in freshwater minnows, Phoxinus
phoxinus, and marine gobies, Pomatoschistus minutus. In 50 ug
Cd/I, minnows accumulated 3.0 mg Cd/kg dry wt by 10 days and 12
mg Cd/kg by 24 days in freshwater; this was 6-10X higher than
accumulation in 50 ug Cd/l in 7.2 0/00 S. Minnows contained 8.0
mg Cd/kg after 10 days and 17 mg/kg after 24 days when exposed
260
-------
to 300 ug Cd/l ~n freshwater. Mean cadmium content in minnows
exposed to 50 ug Cd/l for 10 days ranged from 2.0 mg Cd/kg dry
wt in freshwater to 1.5 mg Cd/kg in 25 0/00 S. Shrimp, Leander
adsperus, took up 2X more cadmium at 15 C compared to 6 C.
After 35 days in 100 ug Cd/l, shrimp whole body levels were 75
mg Cd/kg dry wt in 15 C water and about 37 mg Cd/kg in 6 C.
When mortality occurred in cadmium exposed groups of bleaks,
Alburnus alburnus, accumulation patterns based on surviving fish
was confusing compared to experiments where no mortality
occurred. Moribund fish contained elevated whole body cadmium
concentrat:ons of 125 to 225 mg Cd/kg dry wt in 25 mg Cd/l for
up to one week. Consequently, with mortality, the highest water
concentrations of cadmium produce a strong selection among
individuals. Author concludes that it might be misleading to
base an opinion of pollution load on a fish population, unless
the magnitude of a dir>ect (pollutant itself) or indirect (Le.
selective predation) mortality caused by the pollutant is known.
2770.
Bohn, A. and B.W. Fallis. 1978. Metal concentrations
(As, Cd, Cu, Pb and Zn) in shorthorn sculpins,
oxoce halus scorpius (Linnaeus), and Arctic char,
Ivellnus alpinus (Linnaeus), from the vicinity of
Strathcona Sound, Northwest Territories. Water
Research 12:659-663.
Mean metal levels determined in sculpin from near
Strathcona Sound prior to industrial activity were: for As, 40
mg/kg dry wt in muscle and 81 mg/kg in liver; Cd, 1.4 in muscle
and 4.1 in liver; Cu, 4.1 in muscle and 7.6 in liver; Pb, 0.3 in
liver; and Zn, 43 in muscle and 100 in liver. In landlocked
char, concentrations were: for As, 0.5 mg/kg dry wt in muscle
and 0.7 mg/kg in liver; Cd, 2.0 in liver; Cu, 2.4 in muscle and
87 in liver; Pb, 0.4 in liver; and Zn, 23 in muscle and 130 in
liver. Concentration of arsenic in both muscle and liver from
sculpins displayed a positive correlation to body weight over
the entire size range, and substantially exceeded the maximum
recommended level for arsenic of 5.0 mg/kg wet wt in marine
animal products established by the Canadian Food and Drug
Directorate. Concentrations of Cd, Cu, Pb, and Zn were either
not correlated to body weight or the data were non-linear. No
correlation between metal concentrations and body weight was
found in Arctic char.
Z171.
Bruland, K.W., G.A. Knauer and J.H. Martin. 1978.
Cadmium in northeast Pacific waters. Limnol.
Oceanogr. 23:618-625.
261
-------
Northeast Pacific water was collected by five
different methods and the Cd in it was preconcentrated by both
chelex-ion exchange and chelation-organic extraction
techniques. All sampling and preconcentration methods yielded
essentially the same data. Cadmium was significantly correlated
with phosphate and nitrate at all depths and it appears that the
resulting equations, ng Cd/l = -3.6 + 34.9 (umol P04/1) and ng
Cd/l = 5.1 + 2.45 (umol NO~/l), can be used to predlct oceanic
Cd values. Cadmium concentrations are lowest in
nutrient-depleted surface waters (4.5 ng/l) and greatest (125 ng
Cd/l) at the depths of the P04 and NO~ maxima. Hence, Cd
has one of the highest deep enrichments:surface depletion ratios
( ~30) yet observed. Cadmium and phosphorus are also correlated
in microplankton, and it is apparent that these organisms and
their organic remains are a dominant factor in the
biogeochemical cycling of this element.
2772.
Bursey, C.R. 1978. Temperature and salinity tolerance
of the mole crab, Emerita talpoida (Say) (crustacea,
anamura). Camp. Biochem. Physiol. 61A:81-83.
Adult crabs were subjected to 25 temperature-salinity
combinations within the range of 5-35 C and 15-65 0/00 S. E.
talpoida tolerated 15-65 0/00 salinity at 20 C and below
throughout 15 hr trials. Optimum salinity for survival at
stressful temperatures was 40 0/00; survival -time was 6 hrs at
30 C and 2 hrs at 35 C. Crabs transferred directly from one
salinity to another experienced changes in osmoconcentration
toward that of the new salinity over 3 hrs. Temperature
modified the rate of change toward the experimental salinity.
2773.
Button, K.S. and H.P. Hostetter. 1977. Copper sorption
and release by Cyclotella meneghiniana
(Bacillariophyceae) and Chlamydomonas reinhardtii
(Chlorophyceae). Jour. Phycology 13:198-202.
.. Initial C~2+ sor~~ion ~y ~. meneghiniana (Cu2+
sensltlve) and~. relnhardtll (CU + resistant) was rapid in
the first 5 min of Cu2+ incubation with little sorption after
2~. On a cell to cell basis, Cyclotella sorbed about 5X more
Cu + from the medium than Chlamydomonas. In media with EDTA,
CY~loteGla and Chlamydomonas cells sorbed 1.33 and 0.28 ug
CU2T/IO cells, respectively, after 6 hr in 0.3 ID~
Cu +/1. Proportionally similar quantities of Cu~ were
262
-------
sorbed when cells were Cu2+ incubated in media containing
citrate or filtered lake wa~er. Cleaned gell walls of
Cyclotella sorbed little Cu + (0.11 ug/10 cells) as
compared to living2cells (1.11) in 3 hr. Therefore, in living
Cyclotella most Cu + taken up is absorbed by protoplasm or
perhaps by the organic layer surrounding the silica ~ll. 6
Cleaned cell walls of Chlamydomonas sorbed 0.22 ug Cu +/10
cells and living ChlamYdomona~ cells sorbed 0.16. This
indicates that most of the Cu + sorbed by Chlamydomonas cells
remained bound to the cell wall and proba~ly did not readily
en~er into protoplasm. When placed in Cu + free medium after
Cu + incubation, Cyclotella and Chl~domonas cells released
46 and 59%, respectively, of the Cu sorbed.
2774.
Cox, J.A., L. Kohler, and G. Benzonana. 1976. Ionic
composition and distribution of myogen proteins in
the tail muscle of fresh water crayfish. Compo
Biochem. Physiol. 53B:101-105.
Ionic concentrations in myogen of tail muscle of
crayfish Astacus (pontastacus) ~ptodact~lus leptodactylus were,
in mg/kg wet wt 510 Na, 44 Ca, 230 Mg, 1 40 K, 2.3 Cu, and 15
Zn; Na and Ca were predominantly extracellular and the others
intracellular. Haemolymph concentrations were, in mg/l, 3100
Na, 430 Ca, 43 Mg, 100 K, 23 Cu, and 0.6 Zn. One of several
major myogen proteins binds most of the calcium present in
myogen and appears to be different from Ca-binding proteins
described previously in muscle.
Danil'chenko, O.P. 1977. The sensitivity of fish
embryos to the effect of toxicants. Jour.
Ichthyology 17:455-463.
Effects of triethyl stannic chloride (TESC),
tripropyl stannic chloride (TPSC), dimethyl stannous chloride
(DMSC), and other toxicants on various developmental stages of
perch Perca fluviatilis, ruffe Acerina cernua, loach Misgurnus
fossilis, and sturgeons Acipenser guldenstadt, !. stellatus, and
A. nudiventris were investigated. For all species, organotin
compounds were most toxic and larval stages appeared to be the
most sensitive. Maximum concentrations of individual toxicants
tolerated by larvae of loach were 0.1 mg/l for TESC, 0.01 for
TPSC, and 100.0 for DMSC; for sturgeon larvae these were 0.01
mg/l for TESC and O. 000001 mg/l for TPSC.
2775.
263
-------
2776.
1978.
Davies, P.H., J.P. Goettl, Jr. and J.R. Sinley.
Toxicity of silver to rainbow trout (Salmo
gairdneri). Water Research 12:113-117.
Mean LC-50 (96 hr) values of silver and rainbow trout
were 6.5 ug/l and 13.0 ug/l in soft water of approximately 26 mg
CaOO3/1 hardness and in hard water of 350 mg/l hardness,
respectively. The long-term "no observed effect" concentration
for silver nitrate was bracketed by 0.09 and 0.17 ug Ag/l after
18 months exposure in soft water. No mortalities attributable
to silver occurred at 0.09 ug Ag/l, whereas 17% mortality
occurred at 0.17 ug/l. The "no effect" concentration does not
reflect possible effects of silver on spawning behavior or
reproduction, since female rainbow trout will not generally
reach sexual maturity before 3 yrs. At concentrations of 2: o. 17
ug/l, silver caused premature hatching of eggs and reduced
growth rate in fry. In one experiment, the eggs were completely
hatched within 10 days of exposure; control eggs completed
hatching after 42 days. Prematurely-hatched fry were not well
developed and frequently died; growth rate of surviving fry wa-
greatly reduced.
2777.
Dooris, P.M. and D.F. Martin. 1978. Effects of chelated
iron on the growth of two species of Vallisneria
Water Resources Bull. 14:1088-1093.
Iron, added as (Fe-EDTA)-, was found stimulatory to
~. spiralis at a concentration of 0.05 mg/l. (Fe-EDTA)- had
no effect upon growth of ~. neotropicalis as measured by changes
in dissolved oxygen and dry weight. Results are compared with
those derived from similar studies with Hydrilla verticillata
and Egeria densa. The growth response of Vallisneria to various
iron concentrations compared with that of Hydrilla reveals that
the higher iron concentrations which stimulated Hydrilla (0.10,
0.15 mg/l) were inhibitory to~. spiralis. Under some
conditions Vallisneria exhibit higher survival where compared to
other aquatic plants such as Hydrilla as a function of iron
content of waters.
2778.
Freeman, R.F.H. and T.J. Shuttleworth. 1977.
Distribution of intracellular solutes in Arenicola
marina (polychaeta) equilibrated to diluted sea
water. Jour. Marine BioI. Assn. U.K. 57:889-905.
264
-------
Measurements were made of sodium, potassium and
chloride in tissues of ~. marina equilibrated to 100%, 50%, 35%,
30%, and 25% seawater. Summed amounts of these ions in cells
remained approximately constant in dilutions down to 30%
seawater, and decreases in concentration were due to increased
hydration of cells. Worms in 25% SW accumulated intracellular
ions nearly 15% above worms in full-strength seawater; their
intracellular concentration was greater than predicted from the
change in water content. The percentage contribution which
these ions make to the total intracellular concentration
increased from 40% in 100% SW to 61% in 25% SW. Authors
concluded that restriction on entry of water into cells in
dilute media is by loss of solutes which were not measured in
this investigation, and that failure of cell volume regulation
in 25-30% seawater is associated with a maximal loss of 52% of
these unmeasured solutes.
2779.
Gould, E. 1977. Alteration of enzymes in winter
flounder, Pseudopleuronectes americanus exposed to
sublethal amounts of cadmium chloride. In:
Vernberg, F.J., A. Calabrese, F.P. Thurberg, and W.B.
Vernberg (eds.). Physiological responses of marine
biota to pollutants. Academic Press, New
York:209-224.
Adult flounder were exposed for 60 days at 3-6 C to
0, 5, or 10 ug Cd +/1. At 60 days fish were removed, and
samples of kidney and hemopoeitic tissue analyzed for enz~e
activity. Significant decreases were observed at 10 ug Cd +/1
in activities of leucine aminopeptidase, carbonic anhydrase and
glucose-6-phosphate dehydrogenase. Author concludes that
sublethal amounts of cadmium affect enzymes whose catalytic
activity is largely dependent upon allosteric mechanisms.
2780.
Grice, G.D. and D.W. Menzel. 1978. Controlled ecosystem
pollution experiment: effect of mercury on enclosed
water columns. VIII. summary of results. Marine
Sci. Cammun. 4:23-31.
Natural marine communities of bacteria,
phytoplankton, zooplankton, and chum salmo~ were exposed to 1.0
and 5.0 ug/l mercury for 72 days in 1300 m plastic
enclosures. Results of productivity, growth, abundance, and
taxonomic distribution of plankton, and growth and Hg tissue
accumulation of salmon are summarized.
265
-------
2781 .
Hain, J.H.W. 1975. The behaviour of migratory eels,
Anguilla rostrata, in response to current, salinity
and lunar period. Helgol. wiss. Meeresunters.
27:211-233.
Behavior of migratory silver eels and immature yellow
eels, Anguilla rostrata, was studied in a choice-chamber
apparatus. Silver eels reversed their response to a positive
rheotaxis when saltwater was introduced into the tank.
Rheotaxis and the salinity response are proposed as an effective
orientation mechanism in the seaward migration of the silver
eel. Responses are anticipatory in nature and are thought to be
only part of a sequential arrangement of orientation behaviors.
Yellow and silver eels in heterogenous samples showed similar
rheotactic responses in freshwater but were segregated by
response in saltwater. The non-orientation of the yellow eels
in the freshwater-saltwater choice suggests that it is the
response to salinity which contains yellow eel in its feeding
habitat and later guides the silver eel away from it.
Perception of saltwater by silver eels is olfactory.
2782.
Hanson, R.C., D. Duff, J. Brehe, and W.R. Fleming.
1976. The effect of various salinities,
hypophysectomy, and hormone treatments on the
survival and sodium and potassium content of juvenile
bowfin, Amia calva. Physiological Zoology
49 :376-3~
Young-of-the-year bowfin were tested for salinity
tolerance and effects of hypophysectomy on survival. These fish
lived well in 24% seawater but promptly failed when transferred
into 30% seawater. They retained Na+ well, but lost
whole-body ~ rapidly, in both distilled water and dilute
seawater. It is suggested that ~ loss may largely reflect
the effect of starvation on young rapidly growing animals.
Hypophysectomy caused an increase in Na+ permeability which
was reversed by ovine prolactin. This hormone, however, caused
a marked drop in serum protein levels. While ovine prolactin
did prolong survival somewhat, it would not do so indefinitely.
This hormone was highly toxic when injected into intact
animals. Bovine prolactin and Amia pituitary injection were the
most effective treatments for prolonging survival of
hypophysectomized bowfins.
2783.
Harding, J.P.C. and B.A. Whitton.
1978.
Zinc, cadmium
266
-------
and lead in water, sediments and submerged plants of
the Derwent Reservoir, Northern England. Water
Research 12:307-316.
A partial budget is presented of Zn, Cd, and Pb
entering the Derwent Reservoir. Mean levels in water upstream
of inflow are: Zn, 0.216 mg/l; Cd, 0.023; and Pb, 0.065.
Levels after passage through the 4. 1 km reservoir declined by
70.3% for Zn; Cd, 98.3%; and Pb, 89.2%. Most of these metals
are deposited in sediments, with mean values of: Zn, 1035
mg/kg, Cd, 13; and Pb, 827. Lead, a higher percentage of which
occurs as particulate material, is deposited more rapidly than
zinc; this effect is especially obvious when streaming of colder
water along the bottom of the reservoir takes place at the time
of floods. Sediment levels of Ca and Ag were correlated with
Pb; Zn, Ni, Cu, and Co were correlated with Fe; Cd showed only
weak correlations with Pb, Fe, and Cu, a strong relation with
Ni, but none with Zn. Macroscopic plants are only occasional in
this reservoir, due perhaps in part to heavy metal loadings. Of
the two most common submerged species, Nitella flexilis probably
accumulates almost all of its metal content directly from
water. However, data suggest that sediments are a source of
some heavy metals accumulated by Glyceria fluitans. Metal
content in Nitella decreased from >1750 to 250-500 mg/kg dry wt
for Zn, from >21 to 6.9-9.0 for Cd, and from >875 to 0-125 for
Pb as distance from inflow increased. Lead decreased in
Glyceria from >175 to 0-125 mg/kg dry wt in the same pattern.
2784.
Harrison, W.G., E.H. Renger, and R.W. Eppley. 1978.
Controlled ecosystem pollution experiment: effect of
mercury on enclosed water columns. VII. inhibition
of nitrogen assimilation and ammonia regeneration by
plankton in seawater samples. Marine Science
Commun. 4:13-22.
Additions of mercury at concentrations from 1.0 to
100 ug/l to natural samples of coastal seawater caused
inhibition of nitrate and ammonia assimilation by phytoplankton,
and ammonia regeneration by bacteria and/or microzooplankton
down to 25 to 50% of control rates in 24-48 hr experiments.
Phosphate uptake was similarly reduced. Synthesis of nitrate
reductase was stimulated by low concentrations of mercury and
inhibited by higher concentrations of 5.0 ug Hg/l.
2785.
Heinis, J.J., L.R. Beuchat, and F.C. Boswell.
1978.
267
-------
Antimetabolite sensitivity and magnesium uptake by
thermally stressed Vibrio parahaemolyticus. Applied
Environ. Microbiol. 35:1035-1040.
Metabolic inhibitors were added to a culture medium
inoculated with thermally stressed bacteria Vibrio
parahaemolyticus to obtain information pertaining to
biosynthetic processes required for recovery from heat damage.
Ribonucleic acid and protein syntheses, in addition to membrane
repair, were requir~d during recovery of injured cells. Neither
nucleic acid nor MgL+ leakage was noted while celAs were
subjected to heat stress. Studies showed that ~+ was taken
up by cells of ~. parahaemolyticus during the first 30 min after
thermaA treatment, indicating a possible increased requirement
for ~+ for membrane or ribosome stability and repair.
2786.
Hewett, C.J. and D.F. Jefferies. 1978. The accumulation
of radioactive caesium from food by the plaice
(Pleuronectes platessa) and the brown trout (Salmo
trutta). Jour. Fish Biology 13:143-153.
Patterns of accumulation of Cs-137 from food by
tissues and organs of a marine flounder and a freshwater trout
were compared. Mean ratios of Cs-137 accumulation in plaice
from food over accumulation from water ranged from 0.65, 0.65,
and 0.46 in gut, liver, and gill, respectively, over 40 days, to
0.34 in skin. The mean ratio of all tissues excluding liver and
gut was 0.41. Accumulation ratios in trout ranged from 0.81,
0.75, and 0.75 in gut, liver and kidney, to 0.57 and 0.55 in
gill and skin; overall mean excluding gut was 0.66. Biological
half-life of Cs-137 in whole plaice was 57.9 days, ranging from
139.0 days in muscle to 9.6 days in kidney. Cs-137 half-lives
in trout were 68.8 days in whole fish, a maximum of 126.4 days
in muscle, and a minimum of 21.4 days in gills. Rate constants
were similar to those obtained from the accumulation from water
studies. Plaice gut and liver had an 11% increase and trout gut
a 6% increase in their share of Cs-137 intake arising from
accumulation from food, compared with accumulation from water.
These increases were balanced by decreases in the muscle share
of the intake. The overall absorption of Cs-137 from food was
42% for plaice and 67% for trout.
2787.
Howarth, R.S. and J.B. Sprague. 1978. Copper lethality
to rainbow trout in waters of various hardness and
pH. Water Research 12:455-462.
268
-------
LC-50 (96 hr) values of total dissolved copper to
trout varied from 20 ug/l in soft acid water to 520 ug/l in hard
alkaline water, in hardness ranging from 30 to 360 mg/l as
CaC03 and pH from 5 to 9. The 3-dimensional response surface
was complex; an increase in hardness usually made copper less
toxic. A good prediction of copper LC-50 at usual combinations
of hardness and pH was given by the equation:
LC-50 = antil~g (1.933 + ~.0592 PT + 0.4912 HT +
0.4035 PTHr + 0.4813 PT + 0.1403 H 2) where HT =
hardness and PT = pH.
The transformed variables are:
H - Log10 hardness - 2.01671
T - 0.62308
PT = pH - 7.0
2.0
Trout of 10 g wt were 2.5X more resistant than 0.7 g
trout regardless of hardness and pH combination, and eff[ffit was
predictable by an equation LC-50 = Constant x Weight 0.3 .
Ionic c~~per (Cu2+) and two ionized hydroxides (CuOW and
CU20H2 ) seemed to be the toxic species of copper, since
they yielded the smoothest response surface with the best fit to
measured LC-50's. The sum of these ions produced LC-50's
ranging from 0.09 ug Cull in soft alkaline water to 230 ug/l in
hard acid water. The ions were different in relative toxicity.
or became more toxic at high pH, or both
2788.
Jacobs, R. and 0. Lind. 1977. The combined relationship
of temperature and molybdenum concentration to
nitrogen fixation by Anabaena cyclindrica. Microbial
Ecology 3:205-217.
The joint effects of growth temperature, incubation
temperature, and molybdenum concentration on nitrogen fixation
rate of Anabaena cylindrica were determined. The
nitrogen-fixation response to increased molybdenum concentration
var i ed among three growth temperatures (15, 23, and 30 C). The
pattern of rate change was similar within a growth temperature
but increased overall in magnitude with the three incubation
temperatures (also 15,23, and 30 C). The maximum rate of
nitrogen fixation occurred at 30 C regardless of previous growth
temperature. The minimum molybdenum concentration necessary to
yield substantial acetylene reduction varied with growth
temperature: at 15 C, 15 ug Moll was effective; at 23 C, less
than 5 ug/l was effective; and at 30 C, 50 ug/l was effective.
269
-------
At all three growth temperatures, increases in molybdenum
concentration above the minimum effective concentration produced
increases in acetylene reduction. However, at higher molybdenum
concentrations inhibition of nitrogen fixation occurred.
2789.
Jennings, C.D. 1978. Selective uptake of 55Fe from
seawater by zooplankton. Marine Science Commun.
4 : 49 -58 .
Iron-SS levels in water from the South Pacific 00.~~n
during August and September, 1972, ranged from
-------
0.5 to 0.2 and 0.03 to 0.01 mg/kg, respectively, over the same
period. There was a decreased abundance of the favored prey
items (copepods and decapod and barnacle larvae) in the CEE with
the higher mercury concentration. Indirect effects of mercury
pollution, such as a decrease in population of organisms at
lower trophic levels, may be as important in reduction of fish
production as direct toxic effects upon fish.
2792.
Koike, I., A. Hattori, and J.J. Goering. 1978.
Controlled ecosystem pollution experiment:
mercury on enclosed water columns. VI.
denitrification by marine bacteria. Marine
Commun. 4:1-12.
effect of
Science
Effects of 5.0 ug/l mercury on denitr~fication by
natural populations of marine bacteria in 1300 m Controlled
Experimental Ecosystems (CEE) were investigated over a period of
62 days using N-15 labeled nitrate. Denitrifying activities,
i.e. N2 production, 27 days after mercury addition, were
similar in bottom water and in newly formed sediments in a CEE
containing 5.0 ug Hg/l and controls. After 62 days,
denitrifying activity in Hg CEE sediments exhibited a 6X higher
half saturation constant (Km) for nitrate than control CEE
sediments. Apparently a selection for denitrifying bacteria
with a high Km occurs when natural populations of marine
denitrifiers are exposed to 5.0 ug Hg/l for 62 days.
2793.
Kumar, H.D. and L.C. Rai. 1978. Zirconium-induced
precipitation of phosphate as a means of controlling
eutrophication. Aquatic Botany 4:359-366.
A potentially promising method of controlling
eutrophication by means of zirconium oxychloride, a chemical
precipitant for phosphate, is described. Zirconium oxychloride
precipitates phosphate and limits algal growth at fairly low
concentrations (100 mg/l) within a pH range of 2-11. At 100
mg/l, ZrOC12 does not seem to be harmful either to algae
Chlorella vulgaris after 15 days, or teleosts Heteropneustes
fossilis and Clarius sp. after 2 months.
2794.
Linko, R.R. and K. Terho. 1977. Occurrence of methyl
mercury in pike and Baltic herring from the Turku
archipelago. Environ. Pollution 14:227-235.
271
-------
Content of methylmercury in pike, Esox lucius, and
Baltic herring, Clupea harengus, from seven areas of the Turku
archipelago along the SW coast of Finland was studied. Pike
muscle contained an average of 0.27 mg Hg/kg wet wt. However,
concentrations of methylmercury varied considerably, from 0.06
to 1.3 mg/kg, between individuals from the same fish population
depending on weight (and age) of fish. Methylmercury in
standardized weight (1 kg) pikes ranged between 0.19 and 0.25
mg/kg in all areas of the archipelago except near the city of
Turku, where slight contamination up to 0.39 mg/kg was noticed.
The level of tissue methylmercury decreased in the following
order: muscle >liver.:-kidney »gonads. Liver contained from
0.03 to 2.1 mg Hg/kg wet wt from various sites, kidney 0.03 to
2.7 mg/kg, and gonads from 0.005 to 0.56 mg/kg. Baltic herring
muscle contained an average of 0.09 mg Hg/kg wet wt; one-third
that in pike muscle.
2795.
McBride, B.C. and T.L. Edwards. 1977. Role of the
methanogenic bacteria in the alkylation of arsenic
and mercury. In: Drucker, H. and R.E. Wildung
(eds.). Biological implications of metals in the
environment. ERDA Symp. Ser. 42:1-19. Avail. as
CONF-750929 from Nat. Tech. Inf. Serv., U.S. Dept.
Comm., Springfield, VA. 22161.
Methanogenic bacteria reduce and alkylate arsenate
and a number of arsenic derivatives to demethylarsine. An
unidentified carbon-arsenic compound with similar properties is
produced in natural anaerobic ecosystems. It appears unlikely
that the methane bacteria alkylate mercury. The reaction
proceeds in anaerobic ecosystems, but is probably not associated
with methane biosynthesis.
2796.
Mullen, T.L. and R.H. Alvarado. 1976. Osmotic and ionic
regulation in amphibians. Physiological Zoology
49 : 11-23.
Osmomineral regulation in four species of anurans
from diverse habitats was studied under aquatic conditions.
Ascaphus truei is aquatic, Rana pipiens is semiaquatic, Hyla
regilla and Bufo boreas are terrestrial. The rate of osmQsis is
faster in terrestrial forms than aquatic forms. In ul/cITf/hr,
mean values were!. truei = 4.0, ~. pipiens = 4.8, ~. regilla =
5.6, and~. boreas = 16.0. Higher values reflect higher skin
permeability to water and a higher osmolality of body fluids.
272
-------
Plasma Na+ is closely regulated at about 2300 mg/l, which is
over 100 times more concentrated than the pond water these
species encounter in nature. Unidirectional fluxes of sodium
were measured with Na-22 or Na-24. At a given bath
concentration of Na+, exchange rates were higher in the
terrestrial species. Influx of Na+ displays saturation
kinetics with increasing bath Na+ concentration. Over 90% of
the influx is thermodynamically acUve. Compared with
terrestrial species, aquatic species are characterized by high
affinity-low capacity transport systems. Sodium efflux consists
of renal and diffusive components. No exchange diffusion of
Na+ was found. Renal efflux of Na+ was lower in aquatic
species than terrestrial species. The integumentary loss of
Na+ is a function of the transepithelial electrical potential
difference which is a function of bath Na+ concentration.
Body fluids become more electropositive to the bath by about 35
mV per decade increase in bath Na+ concentration. The
constant field equation accurately predicts the increase in
integumentary Na+ efflux with increasing bath Na+
concentration. The most aquatic species, Ascaphus, had the
lowest integumentary efflux; Bufo, a terrestrial form, the
highest. All species maintained chloride balance in dilute
baths in the face of an unfavorable electrochemical gradient.
Chloride influx, measured with Cl-36, is predominantly carrier
mediated, consisting of exchange diffusion and active transport
in all species but B. boreas, in which exchange diffusion was
absent. Efflux of Cl- was lowest in Ascaphus and highest in
Bufo. Renal loss was lower in aquatic species than terrestrial
species. The efflux was further partitioned into diffusive and
exchange diffusive components. Permeability of the skin to
Cl-, based on diffusive efflux, was lower for aquatic Ascaphus
than for terrestrial Bufo. While anurans appear to possess
common basic mechanisms for osmomineral regulation in
freshwater, significant adaptive modifications have evolved
which may affect species distribution.
2797 .
Nakahara, M. and F.A. Cross. 1978. Transfer of
cobalt-60 from phytoplankton to the clam (Mercenaria
mercenaria). Bull. Japan. Soc. Sci. Fish.
44 : 419 -425 .
Transfer of cobalt-60 from phytoplankton to clams was
investigated to obtain additional information about the movement
of cobalt-60 in the marine ecosystem. The percent retention of
cobalt-60 in clams after feeding on radioactive phytoplankton
varied with size of clam and with phytoplankton cell density and
273
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specie8 of phytoplankton. At high cell densities (2 x 108 and
5 x 10 cells/I), retention of cobalt-60 by clams was reduced
with increasing cell density and size of clam. More than 43% of
the radioactivity introduced into the pallial cavity of clams
with the di~tom, Nitzschia closterium, at cell densities less
than 5 x 10 cells/l was retained in clams two days after
feeding.
2798.
Noro, T. 1978. Effect of Mn on the growth of a marine
green alga, Dunaliella tertiolecta. Japan. Jour.
Phycol. 26:69-72. (In Japanese, English Summary).
Effects of manganese on growth, protein,
carbohydrate, and chlorophyll content of Dunaliella during the
stationary phase of growth were studied. Growth was optimal
between 0.1 and 0.5 mg Mn/l. Toxic effects on growth became
apparent above 10 mg/l; 16 mg Mn/l resulted in rapid death of
cells. Cells grown in 0.1 mg Mn/l decreased in growth rate and
cell length; carbohydrate and protein also decreased, while
chlorophyll remained unaffected at this concentration.
Chlorosis arose as a result of chlorophyll reduction when grown
in medium lacking both iron, a hydrogenase activator, and
manganese. This phenomenon was manifested exclusively under the
depletion of these two elements. It is suggested that D.
tertiolecta is a hydrogenase-containing alga and its chlorophyll
is stable under conditions of Mn depletion.
2799.
Paffenhofer, G.A. and S.C. Knowles. 1978. Laboratory
experiments on feeding, growth, and fecundity of and
effects of cadmium on Pseudodiaptomus. Bull. Marine
Science 28:574-580.
The influence of cadmium on feeding, growth, food
conversion, and reproduction of the estuarine copepod P.
coronatus was studied at a Cd-concentration of 5 ug/l.- Grazing,
ingestion, growth rates, and gross growth efficiencies were not
affected. The only detectable effect was a reduction of the
daily reproductive rate to 50% of that of copepods not exposed
to Cd.
2800.
Parchevskii, V.P., Z.P. Bur18kova, K.M. Khailov, and L.A.
Lanskaya. 1977. Influence of population density of
marirte unicellular algae on radionuclide
accumulation. Soviet Jour. Ecology 8:273-275.
274
-------
Increase in population density of the algal species
Peridinium trachoideum or G~Odinium kovalevskii decreased the
coefficient of accumulation CA) for yttrium-91 and zinc-65. CA
for Y-91 declined from 50,000,000 to about 10,000 as algal density
rose from 0.1 to 10 mg dry wt/l; Zn-65 CA dropped from 1,000,000
to 10,000 over the same algal population range. CA of both
radionuclides for any cell density was higher for Peridinium,
which is 7X greater in surface area than Gymnodinium.
2801 .
Patrick, F.M. and M.W. Loutit. 1978. Passage of metals
to freshwater fish from their food. Water Research
12 :395-398.
Tubificid worms concentrated various heavy metals in
mg/kg dry wt, to 32.2 (Cr), 230 (Cu), 870 (Fe), 13.7 (Mn), 160
(Pb) and 660 (Zn) after ingesting metal-enriched heterotrophic
bacteria for 14 days. When tropical fish, Hyphessobrycon serpae,
were fed these worms, fish exhibited increased tissue metal levels
within 4 days. Metal content after 14 days was 5.9 to 9.1 mg
Cr/kg dry wt, 146 to 199 for Cu, 144 to 181 for Fe, 18.5 to 20.0
for Mn, 36.3 for Pb, and 36.3 for Zn. Only Pb was increased in
contaminated fish after 2 days. Increased levels of most metals
in fish reflect metal concentrations of food if fish are exposed
to food longer than 2-4 days. Older fish had lower Cu, Fe, and Zn
concentrations, higher Cr, and similar Mn and Pb levels compared
to young fish when fed contaminated worms.
2802.
Pozzi, G. and M. Merlini. 1977. Th55accumulation,
distribution, and loss of zinc ( Zn) in the
gastropod ViviEarus ater (Cristofori and Jan).
Malacologia 1 :227 -230.
The prosobranch gastropod, V. ater, is a preferred food
by the freshwater fish Lepomis gibbosus. This snail populates the
li ttoral zone of Lake Maggiore, a large subalpine lake of NW
Italy. Reactor effluent discharges into fresh waters prompted the
study of one of the radioelements, Zn-65, in this snail which is a
possible source of radioactivity for the fish. Laboratory studies
indicate that radiozinc is accumulated primarily in visceral mass
and hepatopancreas of both sexes, that females transmit radiozinc
to developing embryos, and that within 14 days snails concentrate
sufficient radiozinc in soft tissues ( >2,000,000 dpm/snail) to
substantially add to the radioactivity of their fish predator.
275
-------
2803.
Ravera, o. 1977. Effects of heavy metals (cadmium,
copper, chromium, and lead) on a freshwater snail:
Biomphalaria rlabrata Say (Gastropoda,
Prosobranchia. Malacologia 16:231-236.
Effects of cadmium, copper and chromium on mortality
and fecundity of adult Biomphalaria glabrata and embryo
viability were investigated. Embryos were also tested for
l~d. Conc~ntrations used ranged from 0.0 t064.0 mg/l for
Cd + and Cu + and from 0.0 to 1.4 mg/l for Cr +. Cadmium
and copper were far more toxic than chromium. Fertility was
abolished by 0.1 mg/l of cadmium and copper, and fecundity
severly affected by chromium. Survival of hatchlings treated
with chromium was of the same order of magnitude as controls,
and sexual maturity did not show any delay. Forty-o~e percent
of the embryos kept at concentrations of 0.1 mg/l Pb +
completed their development in 51 days, that is, with a delay of
37 days. Hatchlings at 0.1 mg Pb/l died after 15 days.
2804.
Sabosk i, E. M. 1977. Effects of mercury and tin on
frustular ultrastructure of the marine diatom,
Nitzschia liebethrutti. Water, Air, Soil Poll.
8:461-466.
Marine diatoms were maintained for 14 days in 1.5
ug/l of either inorganic Hg or Sn ions. Frustule abnormalities
were significantly greater in diatoms grown with Hg and Sn than
controls. Abnormalities conmon to both Hg and Sn were reduction
in length and width, fused carinal dots and reduction in number
of carinal dots/frustule. Curved raphes and carinal dots
aligned parallel to the raphe appeared only in frustules from Sn
trea tment.
2805.
Shultz, C.D. and D. Crear. 1976. The distribution of
total and organic mercury in seven tissues of the
Pacific blue marlin, Makaira nigricans. Pacific
Science 30:101-107.
Tissue samples from Pacific blue marlin were
collected at Kona, Hawaii, in August, 1973. Analyses of total
and organic (methyl-) mercury indicated that the marlin may be
biotransforming methylmercury to inorganic mercury; about 90% of
mercury body burden was in the inorganic form. The difference
between total and organic mercury concentrations was equal to
inorganic mercury by weight. Average mercury concentrations, in
276
-------
mg/kg wet wt, in marlins were 4.3 total mercury and 0.4 organic
mercury in muscle, 13.4 and 0.2, respectively, in liver, 7.3 and
0.2 in spleen, 0.3 and 0.1 in gill, 0.7 and 0.2 in gonad, 1.1
and 0.1 in stomach, and 0.3 and 0.1 mg/l in blood. Inorganic
mercury levels were 2.3 mg/kg wet wt in muscle, 11.0 in liver,
and 8.5 in spleen.
2806.
Stewart, J. 1977. Relative sensitivity to lead of a
naked green flagellate, Dunaliella tertiolecta.
Water, Air, Soil Poll. 8:243-247.
Cells of Dunaliella spp., unicellular marine green
algae, differ from most other plant cells in lacking a cell
wall. Responses of D. tertiolecta grown in a synthetic seawater
medium with Pb added-were similar to those of other algae
previously tested, disproving the idea that cell wall might
"protect" cells. D. tertiolecta growth was reduced in minimum
concentrations of 0.2 to 0.5 mg Pb/l after 8 days when in
salinities 20, 24, and 30 0100. Population size was lower in 35
0/00 at each level of Pb to 2.0 mg/l, at which concentration
growth regardless of salinity was greatly reduced compared to
controls.
2807 .
Stoneburner, D.L. 1978. Heavy metals in tissues of
stranded short-finned pilot whales. Science Total
Environment 9:293-297.
Tissues from 4 short-finned pilot whales,
Globicephala macrorhyncha, stranded at Cumberland Island
National Seashore were analyzed for total cadmium, mercury and
selenium. Cadmium reached a maximum mean wet wt concentration
of 31.4 mg/kg in kidney. Maximum mean concentrations of
mercury, 230.9 mg/kg, and selenium, 44.2 mg/kg, were found in
liver. The lowest mean concentration of each metal was in
blubber, at 0.2 to 2.4 mg Hg/kg, 0.8 to 1.4 mg Se/kg, and 0.3 to
0.8 mg Cd/kg. Postmortem examination showed that the whales had
no food in their stomachs. The whales may have been utilizing
metabolic reserves, contaminated with residual concentrations of
heavy metals, prior to beaching. This utilization of reserves
probably resulted in the high concentrations of Cd, Hg, and Se
in liver and kidney. Since metal concentrations were 3-4X
greater in stranded whales, then in apparently healthy whales of
the same species, author suggests that heavy metal toxicosis may
have been a factor contributing to this stranding.
277
-------
2808.
Thomas, W.H., D.L.R. Seibert, and M. Takahashi. 1977.
Controlled ecosystem pollution experiment: effect of
mercury on enclosed water columns. III.
phytoplankton population dynamics and production.
Marine Science Commun. 3:331-354.
Effects of inorganic mercury on natural assemblages
of marine phytoplankton were studied in large plastic cylinders
(CEEs) which were moored in Saanich Inlet, British Columbia,
Canada, and contained associated zooplankton assemblages.
Following addition of 1.0 and 5.0 ug Hg/l to two CEEs, there was
an initial inhibition of productivity and phytoplankton crops as
compared to controls. Bottle bioassays suggested that these
levels of mercury would be inhibitory in CEEs, but that
adaptation and recovery of the crops would occur. After about
21 days of mercury treatment, microflagellate crops increased in
1.0 ug Hg/l; phytoplankton that increased in 5.0 ug Hg/l were
dinoflagellates and centric diatoms. These were much less
abundant in controls in which a silicoflagellate bloom developed
between days 42 and 72. Percent similarity and diversity
indices were different in control and treated CEEs late in the
experiment. Since zooplankton crops were inhibited strongly in
5.0 ug Hg/l, differences in phytoplankton taxa and crops between
this CEE and the control could be attributed to differential
grazing pressure.
2809.
Turner, J.C., S.R.B. Solly, J.C.M. Mol-Krijnen, and V.
Shanks. 1978. Organochlorine, fluorine, and
heavy-metal levels in some birds from New Zealand
estuaries. New Zealand Jour. Science 21:99-102.
Five species of birds: black-backed gulls Larus
dominicanus, red-billed gulls Larus novaehollandiae scopulinus,
South Island pied oystercatcher Haematopus ostralegus finschi,
pied stilt Himantopus himantopus leucocephalus, and pukeko
Porphyrio porphyrio melanotus, collected from 7 estuarine areas
of New Zealand in 1973 and 1974 were analyzed for organochloride
residues, flourine, As, Cd, Cu, Hg, Pb, Se, and Zn. Mean metal
concentrations, in mg/kg wet wt or bone-ash, ranged from 0.01 to
0.99 for As in feather, 0.01 to 2.55 for As in liver, 0.08 to
1.48 for Cd in liver, 0.05 to 7.98 for Cd in kidney, 2.78 to
11.97 for Cu in liver, 0.10 to 7.99 for Hg in feathers, 0.01 to
1.15 for Hg in liver, 0.12 to 180.9 for Pb in bone, 1.18 to 4.10
for Se in kidney, and 21.1 to 87.6 for Zn in liver. Species
differences for some of the heavy metals were probably related
to type of diet. In general, the survey indicated little
278
-------
pollution of the environment, even near the most highly
industrialized areas of the country.
2810.
Vannucchi, C., S. Sivieri, and M. Ceccanti. 1978.
Residues of chlorinated naphthalenes, other
hydrocarbons and toxic metals (Hg, Pb, Cd) in tissues
of Mediterranean seagulls. Chemosphere 7:483-490.
A total of 5 seagulls, Larus ridibundus, from two
si tes 00 the Mediterranean coast of Italy were captured during
winter 1975-1976. Mercury, lead and cadmium levels in various
tissues on a mg/kg wet wt basis, ranged as follows: Ii ver Hg
1.32-2.39; liver Pb 2.00-18.30; liver Cd 0.22-2.60; muscle Hg
0.95-1.81; muscle Pb 2.39-11.01; muscle Cd 0.25-1.90; kidney Hg
0.62-1.40; kidney Pb 1.52-40.00; kidney Cd 0.36-2.10; brain Hg
0.65; brain Pb 30.00; brain Cd 1.40. Authors infer that these
metals are present in amounts approaching toxicological interest.
2811 .
Winner, R.W., T. Keeling, R. Yeger, and M.P. Farrell.
1977. Effect of food type on the acute and chronic
toxicity of copper to Daphnia magna. Freshwater
Biology 7:343-349.
Based on survival, brood size, and instantaneous rate
of populatioo growth, Daphnia fed algae were less sensi ti ve to a
chronic copper stress than Daphnia fed a trout-granule diet.
Longevity of copepods and brood size were significantly lower
than controls in 20 ug Cull for trout food populations. Daphnia
fed algae decreased in loogevity in 60 ug Cull; brood size was
similar to or greater than controls in up to 100 ug Cull.
Maximum allowable toxic concentrations (MATC) for chronic
exposure were 40 ug Cull and 10 ug/l for algae and trout-pellet
fed Daphnia, respectively. LC-50 (72 hrs) values were not
different due to diet, ranging from 81.4 to 88.8 ug Cull.
Applicatioo factors of MATC to LC-50 (72 hrs) value ratios were
0.47 for animals on algae food and 0.12 on trout food. Authors
suggested that the mechanism of toxic actioo is different for
acute and chronic toxicity and that, if so, the ratio between
chronic and acute toxicity would not be a constant under
different environmental conditions.
2812.
Anderson, L.W.J. and B.M. Sweeney. 1978. Role of
inorganic ions in controlling sedimentation rate of a
marine centric diatom Di tylum brightwelli. Jour.
Phycol. 14:204-214.
279
-------
Settling rates and intracellular levels of ~,
Na+, CI-, Mi+ and Ca2+ were measured in Di tylum grown
axenically in an enriched seawater medium at 20 C at 4000 lux on
an 8:16 LD schedule. Cells at the end of the dark period have
high Na+ (2700 mg/kg), low r<+ (2500 mg/kg) and low CI-
(4100 mg/kg) relative to levels at the end of the light period
when l(f" (4910 mg/kg) and CI- (5400 mg/kg) are high and Na+
(2320 mg/kg) is low. There is no significant change in Mg2+
(380 to 430 mg/kg) or Ca2+ (120 to 160 mg/kg) with time. The
net result of ion changes during the light period is to increase
cell density by about 3.4 mg/ml. This change can account for
the increase in settling rate of ca. 0.3/day during the same
interval. The density of cell contents, calculated from
observed ion concentrations, is 15 to 18 mg/ml less than
seawater medium. Ion and settling rate changes are
light-dependent and do not persist in the dark or under constant
light (ca. 850 lx), but cells do exhibit a free-running
circadian rhythm in cell division under continuous dim
illumination. The cell vacuole expands during the light period
and contracts during the dark, apparently in response to net ion
fluxes. Q. brightwelli appears to regulate its density by
active ion selectivity accompanied by trans-vacuolar water
movement.
2813.
Anderson, M.A., F.M.M. Morel, and R.R.L. Guillard.
1978. Growth limitation of a coastal diatom by low
zinc ion activity. Nature 276 :70-71.
Zinc ion activity, rather than total Zn
concentration, can limit the growth rate of Thalassiosira
weissflogii. Laboratory studies demonstrated that this
limitation occurs at zinc ion activities which would be present
in unpolluted seawater if any organic complexation of zinc were
taking place.
2814.
Archibald, F.S. and I.W. DeVoe. 1978. Iron in Neisseria
meningitidis: minimum requirements, effects of
limitation, and characteristics of uptake. Jour.
Bacteriology ,136: 35-48.
A simple defined medium was devised that does not
require iron extraction to produce iron-limited growth of N.
meningitidis. The defined medium was used in batch cultures to
determine the disappearance of iron from the medium and its
uptake by cells. To avoid a number of problems inherent in
batch culture, acontinuous culture in which iron and dissolved
280
-------
oxygen were varied independently was used. Most of the cellular
iron \as found to be nonheme and associated with the particulate
fracticn in sonically disrupted cells. Nonheme and
catalase-heme iron were reduced by iron starvation far more than
cytochromes b and c and N,N,N',N'-tetramethylphenylenediamine-
oxidase. Ttie respIration rate and efficiency also decreased
under irm limitation, whereas generatioo times increased. The
iron-starved meningococcus took up iron by an energy-independent
system operating in the first minute after an irm pulse and a
sl~er energy-dependent system inhibited by respiratory poisons
and an uncoupler. The energy-dependent system showed saturation
kinetics and was stimulated nearly fourfold by iron privation.
2815.
Berland, B.R., D.J. Bonin, O.J. Guerin-Ancey, V.I.
Kapkov, and D.P. Arlhac. 1977. Action de metaux
lourds a des doses subletales sur les
caracteristiques de la croissance chez la diatomee
Skeletonema costatum. Marine Biology 42:17-30. (In
French, English surrmary).
Sublethal effects of mercury (5 to 10 ug/l), cadmium
(25 to 100 ug/l), and copper (51 to 200 ug/l) salts on the
marine diatom S. costatum grown in batch and bacteria-free
culture were studied. Division rate, maximum yield, growth,
mean cell volume, particulate carbon and nitrogen, and
C-14-bicarbonate uptake over a period of 7 days were used as
toxic impairment criteria. Division rate was the first-affected
and IIDSt sensitive parameter, but algal resPOllSes varied
according to the metal. Hg produced an acute decrease in
division rate, foll~ed by a temporary recovery of growth
capacity within 48 hrs after metal addition. Cadmium, on the
other hand, increased division rate, followed by an obvious
decrEBse. Copper reduced division rate slowly or quickly,
depending on metal concentration. Cell synthesis capacity
(culture biovollllle, particulate carbm and nitrogen, carbon
assimilation) \as less affected than division rate, especially
with Hg. The C:N cell ratio was unchanged at sublethal
concentrations, even when production \as reduced. The mean cell
volume was slightly affected; variations were not greater than
those of controls during its growth phases. Markedly
teratological fonDS were never observed. Authors concluded that
many parameters and growth kinetic aspects must be considered in
evaluating the effects of sublethal concentrations of heavy
retals.
281
-------
2816.
Betzer, S.B. 1972. Copper metabolism, copper toxicity,
and a review of the function of hemocyanin in Busycon
canaliculatum L. Ph.D. thesis, Univ. Rhode Island,
Kingston, RI: 133 pp.
The marine gastropod, Busycon canaliculatum, was
captured at all seasons of the year and dissected for analysis
of copper content of individual tissues. Despite a high degree
of individual variation in tissue Cu concentrations (mg/kg fresh
wt), seasonal trends were evident. Generally, concentrations
were low in winter and early spring, increasing 5- to 10-fold in
ear ly sumner, and decreasing in autumn. The early sumner
increases correlated with time of emergence from the sediment
and corrmencement of feeding. The average Cu concentration in
whole soft tissues of whelks captured in sumner was 76 mg/kg
with digestive gland accounting for 60% of total Cu.
Radioactive Cu-64 was used to trace uptake from seawater by
whelks. Uptake by whole animals followed a smooth curve which
slowed with time; about 2/3 of the available labeled Cu was
absorbed by 48 hrs. The rate of Cu uptake was generally
proportional to Cu concentration in medium. Shell accounted for
about 30% of the accumulated Cu. Among soft tissues, Cu-64
appeared at 1 hr on gills, in blood, and in kidney. By 6 hrs
Cu-64 appeared in gut and digestive gland, and continued to
accumulate in the digestive gland, so that by 48 hrs it
contained 50% of the total Cu taken up by gills and organs of
the visceral mass. Transfer of absorbed Cu-64 to the digestive
gland continued even when exposed whelks were removed to
unlabeled water for 24 hrs. Separations carried out on blood
labeled with Cu-64 indicated that absorbed Cu was
nonspecifically bound to hemocyanin. Excretion rates for Cu by
Busycon were found to average about 70 ug/24 hrs per kg tissue
wt in spring and sumner. Rates did not appear to be affected by
Cu concentration of the medium. Under normal environmental Cu
concentrations, rates of dissolved Cu uptake and Cu excretion
are probably about eq ual. A calculation of the amount of Cu
shed at spawning in the autumn (based on determinations of the
Cu concentration of Busycon egg capsules, averaging 23
ug/capsule) showed that this could be a significant route for Cu
loss. A possible increase in Cu excretion in autumn,
correlating with observed increases in kidney Cu concentration,
is also suggested as an explanation for the drop in Cu
concentrations of other tissues at this season. Whelks were
exposed to high concentrations of ionic Cu in seawater (up to
1000 ug/l), and effects were followed histologically, by
determination of tissue Cu concentrations, and by tracing uptake
with Cu-64. The whelk showed a high degree of resistance to
282
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ionic Cu. At lethal concentrations, Cu was accumulated at the
gill and osphradium. These tissues also showed progressive
histopathologic changes, including swelling of gill fimaments,
amebocytic infiltration of connective tissue, and necrosis and
swelling of mucosa.
2817 .
Bitton, G. and V. Freihofer. 1978. Influence of
extracellular polysaccharides on the toxicity of
copper and cadmium toward Klebsiella aerogenes.
Microbial Ecology 4:119-125.
Expos~e of various bacterial strains of Klebsiella
to 10 mg/l of Cuf+ for 7 hours reduced survival by a 4 to 5
log reduction factor. Cadmium at 10 mg/l was less toxic than
copper, with a 0.5 to 2.0 log reduction factor in 7 hours. In
all cases, capsular strains were more resistant than
non-capsulated strains. This was attributed to complexing
properties of capsular polysaccharides.
2818.
Brenner, F.J. and W.L. Cooper. 1978. Effect of
suspended iron hydroxide on the hatchability and
embryonic develoPment of the coho salmon. Ohio Jour.
Sci. 78:34-38.
Oncorhynchus kisutch eggs were fertilized and fry
incubated at 10 C in the presence and absence of suspended
iron. Suspended ferric hydroxide at 3.0 mg/l had no apparent
effect on hatchability, embryonic development, or survival and
maturation of newly hatched coho salmon. Eggs exposed to iron
hatched within 51 days, with 96% survival, vs 53 days with 99%
survival for controls. Total mortality among alevins after 90
days was 6.1% in 3.0 mg Fe/I, and 4.0% without Fe.
2819.
Carlsson, S. and K. Liden. 1978. 137Cs and potassium
in fish and littoral plants from a humus-rich
oligotrophic lake 1961-1976. Oikos 30:126-132.
Resul ts of a 15-year study on concentrations of
Cs-137 from fallout in some species of fish and littoral plants
in a humus-rich oligotrophic lake are presented. High
concentrations of Cs-137 were detected in the different species
studied. This is in agreement with the general observation that
organisms in oligotrophic lakes have higher concentrations of
the radionuclide than lakes of other limnological types. The
283
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maxllnum values of Cs-137 were found in 1964 or 1965, depending
on the species studied. Concentrations have decreased 20 to 30%
of the maxllnum value by 1975. A seasonal variation in
concentration of Cs-137 in fish (pike, Esox lucius; perch, Perca
fluviatilis; roach, Rutilus rutilus; rudd, Scardinius
erythrophtalmus) was noted with the highest value occurring
during the first quarter of the year. This is explained by the
strong temperature dependence of excretion of Cs-137. No
seasonal variation in the concentration of potassium is seen in
fish. The plant species Equisetum fluviatile and Carex rostrata
have seasonal variations in concentration of both Cs-137 and
potassium, with highest values at the beginning of the growing
season. In various species of fish studied a relationship was
derived between the concentration of Cs-137 and the size of the
fish. The results are discussed in terms of changes in feeding
habits and changes in excretion of the radionuclide. The
concentration of Cs-137 in fish was observed to follow a trophic
level increase. The concentration is increased by a factor of
two between each level.
Carrano, C.J. and K.N. Raymond. 1978. Coordination
chemistry of microbial iron transport compounds:
rhodotorulic acid and iron uptake in Rhodotorula
pilimanae. Jour. Bacteriology 136:69-74.
The mechanism by which iron uptake is facilitated by
the siderophore rhodotorulic acid (RA) in the yeast Rhodotorula
pilimanae was investigated with radioactively labeled Fe and RA
and chromic-substituted RA complexes. The evidence supports a
model in which RA mediates iron transport to the cell but does
not actually transport iron into the cell. It is proposed that
RA exchanges the ferric ion at the cell surface with a
membrane-bound chelating agent that completes the active
transport of iron into the cell. Uptake of Fe-55 ferric
rhodotorulate was much more rapid than uptake of RA itself. Two
exchange-inert chromic complexes of RA showed no uptake.
2820.
2821 .
Carter, J.G.T. and W.L. Nicholas. 1978. Uptake of zinc
by the aquatic larvae of Simulium ornati~ (Diptera:
Nematocera). Austral. Jour. Marine Freshwater Res.
29:299-309.
Uptake and loss of zinc by aquatic larvae of blackfly,
S. ornatipes, was investigated using radioactive Zn-65. Larvae
284
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absorbed zinc from solution, up to 11 mg Zn/kg wet wt in 0.1 mg
Zn/l after 24 hrs. A substantial proportion of Zn remained in
the body when larvae were transferred to zinc-free water.
Insects contained 2.0 mg/kg after 32 hrs in clean water. Uptake
was assisted by metabolism, but an increase of calcium ion
concentration, although reducing toxicity, had no effect on
uptake, exchange, or loss of zinc. In the cuticle and
high-molecular-weight fractions of larvae, two pools were
identified; one in which zinc is weakly held and exchanges
rapidly with zinc in solution; and one where zinc is held and
exchanges slCMly. Exposure time, temperature, and external
concentration influenced the quantity of zinc entering these
pools. High molecular fractions contained 60% of Zn-65 in whole
larvae after 60 hr exposure. Zinc was probably bound by
phenolic groups in the cuticle fraction, and by phosphonic acids
in the high-molecular-weight fraction. Sulfhydryl groups did
not bind a major portion of the zinc.
2822.
Chalker, B.E. 1976. Calcium transport during
skeletogenesis in hermatypic corals. Compo Biochem.
Physiol. 54A:455-459.
Light-enhanced calcification in the hermatypic corals
Acropora cervicornis and!. formosa results from the active
transport of calcium ions. Dark calcification results from
enzyme mediated isotopic exchange. Strontium is a competitive
inhibitor of both light-enhanced and dark calcification. The
data refutes the diffusional model for calcium movement in
hermatypic corals.
2823.
Decleir, W., A. Vlaeminck, P. Geladi and R. Van Grieken.
1978. Determination of protein-bound copper and zinc
in some organs of the cuttlefish ~ officinalis
L. Compo Biochem. Physiol. 60B:~50.
The copper, zinc and iron content of blood and water
soluble extracts from several organs of Sepia officinalis were
determined by atomic absorption spectrometry. The relatively
high concentration of copper (up to 70 mg/kg dry wt) and zinc
(up to 124 mg/kg dry wt) in the branch ial gland po ints to its
probable role in trace element metabolism. After gel filtration
a low molecular weight copper and zinc containing fraction can
be isolated from the gland. A possible role of this fraction in
hemocyanin biosynthesis is postulated.
285
-------
2824.
Findley, A.M. and W.B. Stickle. 1978. Effects of
salinity fluctuation on the hemolymph composition of
the blue crab Callinectes sapidus. Marine Biology
46:9-15.
Crab hemolymph was hyperosmotic during 20-10-20 0/00
S and 30-10-30 0/00 S diurnal cycles. The hemolymph became
isomotic at 26 0/00 S and hyposmotic at 28 0/00 S in the
10-30-10 0/00 S diurnal cycle. Hemolymph Na+ was hyperionic
to seawater throughout all cycles. Hemolymph Cl- was
hyperionic below 24 0/00 S and either isionic or hypoionic from
24 to 30 0/00 S. Hemolymph ~ concentrations were hyperionic
below 26 0/00 S and e~ther isionic or hypoionic from 26 to 30
0/00 S. Hemolymph MgL+ values were hypoionic over the
experimental salinity range of 10 to 30 0/00. Hemolymph
ninhydrin-positive substances levels were directly related to
ambient salinity.
2825.
Foster, R.B. and J.M. Bates. 1978. Use of freshwater
mussels to monitor point source industrial
discharges. Environ. Science Technol. 12:958-962.
In-stream monitoring techniques were used to evaluate
effects of copper electroplating wastes on mussel fauna of the
Muskingum River, Ohio. Laboratory effluent bioaccumulation
tests were conducted with freshwater mussels and copper, the
major effluent constituent. Mussels were also exposed in cages
at various distances from the electroplating plant outfall and
analyzed for copper content after 14, 30 and 45 days.
Indigenous mussels were also analyzed for copper. Copper
accumulation in the species tested, Quadrula quadrula, was
inversely related to body weight. Mortalities during effluent
exposures occurred after 11 days and were associated with body
burdens approaching 20 mg Cu/kg wet wt. Analysis of caged
mussel specimens when correlated with Muskingum River population
surveys and natural background content of copper in freshwater
mussels demonstrated an adverse impact of the electroplating
plant within 21 km of the outfall. Mussels caged 0.1 km from
the outfall accumulated 20.64 mg/kg Cu in 14 days, 10X the
normal body burden of mussels at control stations upstream. The
copper content of caged mussels at stations located 5 to 53 km
downstream declined as the distance from the outfall increased.
The impact of the electroplating plant effluent on the Muskingum
River mussel fauna was significant, causing population
mortalities of 60% within 5 km and 39% within 21 km.
286
-------
2826.
Fukai, R., B. Oregioni, and D. Vas. 1978.
Interlaboratory comparability of measurements of
trace elements in marine organisms: results of
intercalibration exercise on oyster homogenate.
Oceanologica Acta 1:391-396.
An intercalibration exercise of trace element
measurements was organized by using an oyster (Ostrea edulis)
homogenate sample to examine the state of the art of measurement
performance, with the aim of improving the comparability of
results; 87 laboratories, on a world-wide basis, participated in
this operation. The results of analyses on 12 selected trace
elements (Cr, Mn, Fe, Co, Cu, Zn, As, Se, Ag, Cd, Hg, and Pb)
were treated statistically to deduce the "consensus values" of
these elements in the sample. The results of selected
laboratories were treated similarly to estimate "probable
concentrations". The "probable concentrations" agree with
"consensus values" for most elements. On the basis of "probable
concentrations", ranges for acceptable values were estimated for
each element. More than 80% of the resul ts reported were wi thin
estimated acceptable ranges for Mn and CUi more than 70% for Cr,
Zn, Se, Cd, and Hg; more than 60% for Fe, Co and Ag; while 59%
were acceptable for Pb and only 43% for As. General
observations made on analytical methods used, presentation of
data, and other aspects are also given.
28zr .
Fyhn, H.J. 1976. Holeuryhalinity and its mechanisms in a
cirriped crustacean, Balanus improvisus. Compo
Biochem. Physiol. 53A:19-30.
Euryhalinity of barnacles depends partly on
hyperosmotic regulation of hemolymph and partly on cell volume
regulation. ~. improvisus osmoconform in water above 500 mOsm
and osmoregulate in more dilute seawaters, showing strict
homoiosmoticity below 100 mOsm. Hemolymph and maxillary gland
fluid are isomotic and have equal chloride concentrations.
Seventeen free amino acids are found in thorax muscle tissue in
amounts varying with hemolymph osmolality. Proline reaches
unique values of 0.7 M at hypersaline seawater. The relative
water content of muscle tissue varies little with changes in
hemolymph osmolality pointing to a regulation of cell volume.
Adjustments of intracellular amino acids, especially proline,
assist in this regulation. The intermoult cycle does not
significantly influence measured parameters.
287
-------
2828.
Gertz, S.M. and I.H. Suffet. 1977. The biological fate
of radionuclides in aquatic environments. In: Suffet,
I.H. (ed.). Fate of pollutants in the air and water
environments. Advan. Environ. Sci. Technol. 8:223-238.
Three levels were presented to describe algal uptake of
radioactivity. Level I described radionuclide uptake in terms of
concentration factors. This level is basic to the study of
radionuclide uptake but it is not complete. Level II considered
algal radionuclide uptake in terms of concentration factors and
those environmental stresses which may affect an organism's
biomagnification potential. This level, while a higher level of
understanding than Level I, is still not complete, for while the
phenomenon is better quantified, the reason for the phenomenon is
still not known. Level III, the highest level, considers the
biological mechanisms that permit and cause an organism to
accumulate radioactivity. Algal accumulation of cesium and
strontium and modifications by magnesium, calcium, sodium,
potassium, and temperature are presented as examples.
2829.
Goldman, M., R.D. Dillon, and R.M. Wilson. 1977.
Thyroid function in Pekin ducklings as a consequence of
erosion of ingested lead shot. Toxicol. Appl.
Pharmacol. 40:241-246.
Young ducklings received three or six lead shot which
were dropped down the throat of each bird. Lead shot recovered
from gizzards at necropsy were smaller and more irregular in shape
than when introduced. Although erosion rate was similar in both
groups receiving lead shot, total amount of lead eroded was
greater in birds receiving the greater number of shot. After 16
days, the 3 shot group accumulated 360 mg Pb and the 6 shot group
accumulated 670 mg Pb from pellets. Body weight gain was
significantly lower in waterfowl receiving 6 shot. Birds fed 6
shot showed major signs of lead poisoning such as green diarrhea,
weakness, and lethargy. Thyroid weight and 24 hr thyroidal uptake
of 1-125 were increased while serum protein-bound 1-125 was
reduced in contaminated birds. Chromatographic analyses of
thyroid hydrolysates revealed a depression in iodothyronine
labeling.
2830.
Grimanis, A.P., D. Zafiropoulos, and M. Vassilaki-Grimani.
1978. Trace elements in the flesh and liver of two
fish species from polluted and unpolluted areas of the
Aegean Sea. Environ. Sci. Technol. 12:723-726.
288
-------
Concentrations of As, Cd, Co, Cu, Fe, Hg, Rb, Sb, Se,
and Zn were determined in flesh and liver of two edible fishes,
Sargus annularis and Gobius nig~r, caught from polluted and
unpolluted areas of the Aegean ea. Increased levels of arsenic
were found in flesh of Sargus from polluted areas at 6.4 to 9.1
rng/kg dry wt (vs. 2.4 for unpolluted area). Arsenic levels were
also increased-rn flesh and liver, 18 to 140 and 8.4 to 17 mg/kg
dry wt, respectively, of Gobius from the Athens sewage outfall
area. Elevated concentrations to 1.9 mg/kg mercury were found in
flesh of Sargus and up to 0.33 in flesh and 0.72 in liver of
Gobius from a sea area close to Mytelene Harbor in the island of
Lesvos. Elevated levels of arsenic and mercury found in these two
species of edible fish from polluted areas were not high enough to
render them dangerous for human consumption. No significant
differences were found for all the other elements measured.
Maximum metal concentrations, in mg/kg dry wt, in flesh of Sargus
were <0.3 for Cd, 1.7 for Cu, 0.04 for Sb, 1.4 for Se, 71 for Zn,
40 for Fe, 0.04 for Co, and 2.9 for Rb; in liver of sarrs maximum
levels were <0.3, 35, <0.02, 6.6, 111, 530, 0.6, and 2. ,
respectively; in flesh of Gobius, <0.3, 1.3, <0.02, 1.4, 58, 25,
0.02, and 2.6; and in liver of Gobius, 0.91, 8.1, 0.03, 2.6, 22,
240, 0.05, and 0.78, respectively.
2831.
Guary, J.C. and A. Fraizer. 1977. Etude comparee des
teneurs en plutonium chez divers mollusques de quelques
sites littoraux fransais. Marine Biology 41:263-267.
(In French, English summary).
Plutonium contents of 4 species of gastropods:
Crepidula fornicata, Patella vulgata, Littorina littoralis,
Nucella lapillus; and 5 species of bivalve molluscs: Venerupis
decussata, Ensis ensis, Mytilus edulis, Ostrea edulis, Crassostrea
gigas, from several sites along the French coast were measured to
determine distributional patterns of plutonium levels. The
influence of the La Hague nuclear fuel reprocessing plant was
apparent in the ilnmediate proximity of the waste-disposal outfall
(Ecalgrain Bay), and to a lesser degree in an oyster farming
center situated about 50 km east of the Bay of Ecalgrain (St.
Vaast-la-Hougue). Plutonium concentrations in molluscs from the
remaining sites were quite comparable to levels that have been
measured in similar species subject only to plutonium from
atmospheric fallout. All molluscs, except those from Ecalgrain
Bay, displayed higher levels of plutonium in the shell than soft
parts, a finding in agreement with similar studies. Individuals
sampled from the vicinity of the outfall consistently displayed
shell:soft parts plutonium ratios of less than 1.0. This
289
-------
difference may reflect different physico-chemical forms of the
isotope at the various sampling stations. With the exception of
Crepdidula shell, the tissues of filter-feeding molluscs do not
appear to concentrate plutonium above the level found in other
types of molluscs.
2832.
Guary, J.-C., M. Masson, and A. Fraizier. 1976. Etude
prelllninaire, in situ, de la distribution du plutonium
dans differentS-tissues et organes de Cancer pagurus
(crustacea:decapoda) et de Pleuronectes platessa
(pisces:pleuronectidae). Marine Biology 36:13-17 (In
French, English summary).
Plutonium distribution was determined in tissues and
organs of the crab, Cancer pagurus, and the plaice (flatfish),
Pleuronectes platessa, collected inshore near the La Hague fuel
reprocessing plant, France. There is an observed transfer of
plutonium from seawater to gills (102 pCi/kg wet wt) and
exoskeleton (2.2 pCi/kg wet wt) of the crab, these organs
representing a large surface adsorption. In plaice, only gut
strongly accumulated plutonium (64 pCi/kg wet wt), indicating
contamination by feeding. The edible parts of these two marine
species, particularly the flesh, do not constitute, for man, an
llnportant source of contamination by environmental plutonium.
2833.
Hattula, M.L., J. Sarkka, J. Janatuinen, J. Paasivirta, and
A. Roos. 1978. Total mercury and methyl mercury
contents in fish from Lake Paijanne. Environ.
Pollution 17:19-29.
Total mercury and methylmercury in freshwater fishes
from Lake Paijanne, Finland, were determined!- This is the second
largest lake in Finland and has been heavily contaminated by
mercury from pulp and paper industries, chlor-alkali plants, and
other sources. Twelve species of fish were ana lysed during a
4-year period. The average mercury concentration for all fish was
0.65 mg/kg on a fresh wt basis, of which 98.7% was in a methylated
form. The concentration of mercury in fish differed in different
parts of the lake and also depended on the weight of the fish.
Maximum values recorded for total mercury, in mg/kg wet wt
(presumably fish axial musculature), were 2.94 for smelt, 3.96 for
pike, 1.13 for roach, 4.34 for burbot, 1.57 for ruffe, 2.98 for
pikeperch, 4.68 for perch, and <1.0 for whitefish, vendace, bream,
and carp.
290
-------
2834.
Hoyaux, J., R. Gilles, and C. Jeuniaux. 1976.
Osmoregulation in molluscs of the intertidal zone.
Compo Biochem. Physiol. 53A:361-365.
Gastropods, Littorina littorea, Purpura lapillus,
Patella vulgata, and bivalves, Mytilus edulis, Scrobicularia
plana, Glycymeris glycymeris, of the littoral area behave as
poikilosmotic animals when acclimated gradually to diluted media.
However, when transferred directly to the more diluted medium,
these molluscs react by shell-closing, leading to a transitory
hyperosmotic state of the blood and perivisceral fluids. In the
euryhaline molluscs studied, osmoregulation is achieved by
isomotic regulation of the intracellular medium. Free amino acids
and taurine playa significant part as osmotic effectors in this
regulation, except in the case of the chiton Acanthochitona
discrepans. The part played by the amino-acid pool as well as the
nature of the prominent acids at work in the regulation of the
intra-cellular osmolarity varies from species to species with no
single general pattern emerging.
2835.
Huner, J.V.~ J.G. Kowalczuk, and J.W. Avault, Jr. 1976.
Calcium and magnesium levels in the intermolt (C4)
carapaces of three species of freshwater crawfish
(Cambaridae:Decapoda). Compo Biochem. Physiol.
55A: 183-185.
Mean calcium (25.1, 24.9 and 25.4%) and magnesium
(0.408, 0.428 and 0.421%) concentrations in the carapaces of
intermolt (C4) Orconectes virilis, Procambarus alIeni, and
Procambarus clarkii did not differ significantly. Mature
(sexually active) crawfish apparently have much thicker cuticles
than rapidly growing mature (sexually inactive) and juvenile
crawfish of the same size.
Iordachescu, D., I.F. Dumitru and S. Niculescu. 1978.
Activation by copper ions of mytilidases - acid
proteolytic enzymes obtained from Mytilus
~~~;~~~~~~~~ialis. Compo Biochem. Physiol.
Cu2+ ions, at 3810 ug/l as CuC12' strongly
activated acid proteases purified from the hepatopancreas of
mussels Mytilus galloprovincialis. Tyrosine liberation peaked at
90 nmoles/ml/min at 50 C with copper, compared to 50 nmoles for
controls. In the presence of the effector, the first optimal pH
2836.
291
-------
was displaced from 1.5 to 1.85. Inhibition occurred at high
hemoglobin concentrations. Copper ions did not protect acid
proteases from the denaturing effect of temperature, while
hemoglobin had a heat-protector effect.
2837.
Kwasnik, G.M., Jr., R.J. Vetter, and G.J. Atchison.
The uptake of manganese-54 by green algae
(Protococcoidal chlorella), Daphnia magna, and
minnows (Pimephales promelas). Hydrobiologia
59 : 181 -185 .
1978.
fathead
Concentration factors (CF) of Mn-54 for freshwater
algae, daphnids, and minnows were determined following direct
exposure to the isotope in solution. The maximum accumulation
(CF=911) in P. chlorella was reached at 48 hrs of exposure; the
maximum uptake ( CF=65) in Daphnia was reached at 8 hrs of
exposure; and the max imum accumula ti on (CF=22. 6) in fathead
minnows was at 128 hrs of exposure. The data indicate that Mn-54
accumulation decreases with ascent within a theoretical aquatic
food chain when water is the only source of contamination.
2838.
Larochelle, J. and A. Gagnon. 1976. Osmoregulation in
Acanthamoeba castellanii - II. variations of the
concentrations of some intracellular ions. Compo
Biochem. Physiol. 54A:275-279.
The free-living soil amoeba A. castellanii undergoes
changes in water content when incubated-in media of different
osmotic pressures. In this study the intracellular concentrations
of K, Na, Mg, Ca, and Cl were determined following incubation in
media having different salt contents but the same osmotic
pressures, namely 40, 200, and 500 mOsm. The intracellular K
concentration changes as a function of the osmotic pressure of the
medium and is independent of its salt content. The amoeba Cl
concentration is affected by both the osmotic pressure and the
composition of the media. The intracellular Na concentration
depends upon the levels of the Na and Ca in the external media.
2839.
Man ly, R. and W.O. George. 1977 . The occurrence 0 f some
heavy metals in populations of the freshwater mussel
Anodonta anatina (L.) from the River Thames. Environ.
Pollution 14:139-154.
Concentrations of Zn, Ni, Pb, Cd, Cu and Hg in Anodonta
292
-------
anatina from three urban and four rural localities along the River
Thames were determined. The apparent influence of urban sewage
outfalls was reflected by the relatively higher concentrations of
Zn, Ni, Pb and Cd in mussels from the former areas, while Cu and
Hg, metals which have more diffuse inputs, showed no such
relationship. The maximum concentrations recorded in this study,
in mg metal/kg dry wt soft parts, were Zn 3226, Ni 46, Pb 79, Cd
21, Cu 222 and Hg 12 exceeded those previously observed in
Anodonta spp. and many marine 1amellibranchs from the British
Isles. Considerable differences were observed in the
concentrations of all metals in mussels from the same locality,
particularly among imnature individuals. Except for Ni, these
differences were variously correlated with the dry body weight of
mussels in the more highly contaminated populations. None of the
metals was evenly distributed throughout the tissues of mussels.
Generally, the mantle, ctenidia and kidneys contained the highest
concentrations. An evaluation is made of the potential of the
species as an indicator organism.
2840.
Milne, R.S. and D.J. Randall. 1976. Regulation of
arterial pH during fresh water to sea water transfer in
the rainbow trout Salmo gairdneri. Compo Biochem.
Physiol. 53A:157-160.
Plasma Cl-, H003; arterial blood p002' and pH
and 002 excretion were not affected by transfer of trout from
freshwater to seawater. Carbonic anhydrase activity in trout gill
epithelium is low compared with that for goldfish and seawater
coho salmon, but similar to that in freshwater coho salmon. The
results are discussed in relation to various models for ion
transport across the fish gill. It is concluded that a
C1-/H00~ exchange mechanism is reduced in gill epithelium
of trout compared with goldfish.
2841 .
Morel, N.M.L., J.G. Rueter, and F.M.M. Morel. 1978.
Copper toxicity to Skeletonema costatum
(Baci11ariophyceae). Jour. Phyco1ogy 14 :43-48.
This marine alga is relatively insensitive to cupric
ion activity under controlled laboratory conditions. Cultures
inoculated from stationary phase stocks exhibit a prolongation of
the lag phase with increasing copper concentrations near and above
the point of precipitation of the copper. The toxicity of copper
is a function of the silicic acid concentration in the medium.
This effect is observed in a range of Si(OH)4 concentrations
293
-------
(10-5 M to 10-4 M) above known values for the saturation of
silicon uptake kinetics, thus suggesting an influence of copper on
silicate metabolism.
2842.
Nordlie, F.G. 1976. Influence of environmental
temperature on plasma ionic and osmotic concentrations
in Mugil cephalus Lin. Compo Biochem. Physiol.
55A: 379-381.
Plasma Na+ in mullet ranged from a concentration of
159 meq/l in fish acclimated to 10 C to 178 meq/l in fish at 30 C;
plasma Cl- ranged from 139 meq/l at 10 C to 158 meq/l at 30 C;
plasma osmotic concentration ranged from 323 mOsm/kg to 378
mOsm/kg for the same acclimation temperature range. Plasma r<+
remained roughly constant. These patterns of response in
inorganic ions and total osmotic concentrations to environmental
temperature are opposite to that expected in fishes acclimated to
seawater and infers an additional metabolic expenditure for
regulation at lowered temperatures.
2843.
Penrose, W.R., H.B.S. Conacher, R. Black, J.C. Meranger, W.
Miles, H.M. Cunningham and W.R. Squires. 1977.
Implications of inorganic/organic interconversion on
fluxes of arsenic in marine food webs. Environ. Health
Perspec. 19:53-59.
An organic form of arsenic is commonly encountered in
marine organisms. In greysole Glyptocephalus cynoglossus and
shrimp, organoarsenic accounted for all arsenic found in muscle
tissue. It has been isolated from flounder tissue by two
independent procedures and found to be hydrophilic, cationic, and
not decomposed to inorganic arsenic by hot nitric and sulfuric
acids. Nuclear magnetic resonance spectroscopy indicated all
nonexchangeable protons to be equivalent, with behavior more
similar to N-methyl protons than As-methyl protons.
High-resolution mass spectroscopy from a heated probe yielded a
spectrum corresponding to tetramethylarsonium (AsMelf). The
authentic ion, however, had thin-layer chromatography and
ion-exchange behavior different from that of the natural product.
Infrared spectrometry likewise produced conflicting or
uninterpretable data. Decomposition of the compound for
analytical purposes was accomplished by dry ashing under oxidizing
conditions. Sea urchins, Strongylocentrotus droebachiensis, like
trout, converted arsenic to an organic form, but to a more limited
degree. Arsenic found naturally in sea urchins and in a species
294
-------
of macroalga Fucus vesiculosus was also organic. In individual
containers, sea urchins were fed on the alga for 7 weeks. During
this time they consumed 0.203 mg total As and excreted only 0.036
mg as feces. Measurement of inorganic As in the seawater did not
account for the discrepancy, but measurements of total As did
(0.202 mg). Sea urchins, like humans, appear to be able to
rapidly excrete these organic forms of arsenic.
2844.
Pentreath, R.J. 1977. The accumulation of 110mAg by the
plaice, Pleuronectes platessa L. and the thornback ray,
Raja clavata L. Jour. Exp. ~ine BioI. EcoI.
29:315-325.
Accumulation of stable Ag and Ag-110m from both food
and water by a marine fish (plaice) and elasmobranch (thornback
ray) has shown that metabolism of silver by these two species is
markedly different. Silver levels, in mg/kg wet wt, in plaice
exposed to 0.04 mg Ag/l for 2 months ranged from 0.01 in muscle to
about 0.05 in liver and heart, with concentration factors (CF) up
to 1200. In contrast, the elasmobranch had tissue concentrations
ranging from 0.008 mg Ag/kg wet wt in blood cells to 0.56 in
kidney and 1.47 in liver; CF reached 14,000 and 37,000 in kidney
and liver. Direct accumulation of Ag-110m from seawater was low
for both species, but higher for rays. CF values rose to about 15
for whole body accumulation in rays over 63 days, and to 2 for
plaice. Ag-110m concentrations in tissues of plaice over blood
plasma ranged from 0.3 in blood cells to 1.6 in gill filaments,
1.8 in liver and 2.3 in brain. After depuration for 43 days,
maximum radionuclide levels over plasma were 3.6, 3.8, and 4.0 in
spleen, liver, and bladder, and 14.4 in brain. Ag-110m
accumulations over plasma after 63 days in rays were up to 117 in
stomach, 138 in gill filaments, and 1900 in liver; after 43 days
loss, CF over plasma were 89 to 285, 52 to 118, and 4200 to 4600
in respective tissues. Retention of Ag-110m from labelled worms,
Nereis, by plaice was poor: only 4% after 3 days, with a very
short biological half-time. In contrast, rays retained 48% of the
radionuclide from labelled food, with a long biological half-time
and with very high concentrations in liver. Livers from rays
caught near a nuclear fuel reprocessing plant contained Ag-110m,
but this isotope could not be detected in plaice liver.
2845.
Pesch, C.E. and D. Morgan. 1978. Influence of sediment in
copper toxicity tests with the polychaete Neanthes
arenaceodentata. Water Research 12:747-751.
295
-------
Adult male marine worms were exposed to measured
concentrations of 0.04, 0.06,0.10,0.16 and 0.26 mg Cull in a
continuous-flow bioassay system, with and without a clean sand.
The 28-day LC-50 was lower (0.044 mg Cull) for polychaetes exposed
without sand than those with sand (0.100 mg Cull). Neanthes
surviving exposure for 28 days at various Cu concentrations in a
sand substrate consistently contained lower whole body Cu residues
than Neanthes in a sand-free substrate.
2846.
Planas, D. and F.P. Healey. 1978. Effects of arsenate on
growth and phosphorus metabolism of phytoplankton.
Jour. Phycology 14:337-341.
The response to arsenate in growth and phosphate uptake
by five species of algae in culture varied considerably. The
growth rates of Melosira granulata and Ochromonas vallesiaca were
depressed by 1.0 uM arsenate. Chlamydomonas reinhardtii required
10 uM for the same degree of depression, while the growth rates of
Cryptomonas erosa and Anabaena variabilis were unaffected up to
100 uM. However, following depletion of phosphate, cultures of
the latter two algae began to die at the higher concentrations of
arsenate tested. Growth of C. reinhardtii in the presence of 35
uM arsenate resulted in characteristics of P deficiency.
Comparison of rates of photosynthesis, respiration, and phosphate
uptake between cultures of C. reinhardtii grown in the presence
and absence of arsenate showed little evidence after 16 doublings
that it had adapted to arsenate.
2847.
Prusch, R.D., D.J. Benos, and M. Ritter. 1976.
Osmoregulatory control mechanisms in freshwater
coelenterates. Compo Biochem. Physiol. 53A:161-164.
Contraction rate of the body column of Hydra littoralis
is affected by Na+, CN and ouabain added to the external
medium. The electrical potential across the hydra body wall is
decreased by a decrease in the external Na+, and by decreased
temperature. Enteron Na+ and r<+ levels are influenced by a
variety of exper imental concU tions. Osmoregulation in freshwater
coelenterates is influenced by both external Na+ and total
external osmolality.
2848.
Reiniger, P. 1977. Concentration of cadmium in aquatic
plants and algal mass in flooded rice culture.
Environ. Pollution 14:297-301.
296
-------
Concentrations of Cd in aquatic plants Elatine
hexandra, Althenia filiformis and Monita rivularis on a flooded
rice soil contanrlnated with up to 24 mg Cd/kg largely exceeded
cadmium concentrations found in leaves and roots of rice plants.
The accumulation of Cd by the algal mass was considerable, with a
concentration factor of around 10,000 relative to the surface
water. The quantity of Cd accumulated by the algal mass in a rice
field may be comparable to that in leaves of rice plants. Mean Cd
concentrations, in mg/kg wet wt, for rice leaves (roots) grown in
soil containing 2, 8, or 24 mg/kg of added Cd were 6(0.2),
20(0.3), and 50(0.5), respectively-
2849.
Reish, D.J., C.E. Pesch, J.H. Gentile, G. Bellan, and D.
Bellan-Santini. 1978. Interlaboratory calibration
experiments using the polychaetous annelid Capitella
capitata. Marine Environ. Res. 1:109-118.
An interlaboratory calibration experiment was conducted
at installations in California, Rhode Island, and France in order
to test two sources of variation associated with toxicity bioassay
experiments: variation due to the experimenter, and variations
due to the natural seawater. Twenty-eight day static (with
frequent media renewal) bioassays with polychaetes Capitella
capitata and cadmium salts were conducted with synthetic and
natural seawaters. Test results varied between the 3
laboratories, with LC-50 (28 day) values extending from 0.40 to
1.50 mg Cd/I. However, variations might be attributable to
extreme temperatures experienced by worms during some air
transshipments.
2850.
Robertson, D.R. 1976. Diurnal and lunar periodicity of
intestinal calcium transport and plasma calcium in the
frog, Rana pipiens. Compo Biochem. Physiol.
54A:225'=231.
Calcium transport in frog duodenum displayed wide
amplitude diurnal changes with maximum transport at night, while
diurnal changes were of low magnitude in the jejunum and ileum.
Diurnal patterns at four major lunar phases throughout the
synodical lunar month show peaks of activity that correspond to
times of high and low lunar transit. Maximal plasma calcium
levels are coincident with maximal periods of duodenal calcium
transport.
297
-------
2851.
Rossi, L.C., G.F. Clemente, and G. Santaroni. 1976.
Mercury and selenium distribution in a defined area and
in its population. Arch. Environ. Health 31:160-165.
In the Amiata Mountain area of Tuscany, Italy,
concentrations of mercury and selenium were examined in the
environment, in the food chain, and in human blood, urine, and
hair. This area has large mineral deposits and concentrations of
iron, copper, silver, antimony, and particularly mercury.
Subjects consisted of a group with high occupational exposure to
mercury vapor, a group randomly exposed to mercury dust, and a
group nonoccupationally exposed to mercury. Maximum mean Hg
concentrations were found in humans with high exposure: 59 ug
Hg/l in whole blood, 93 ug/l in serum, 44 ug/l in blood cells, 251
ug/l in urine, and 25 mg/kg in hair. Selenium content in these
subjects was 133 ug Sell in whole blood, 60 in serum, 19 in blood
cells, 8.2 in urine, and 7.6 mg/kg in hair. Autopsies of 3 miners
showed maximum mercury, at 240 to 3000 ug/kg wet wt, and selenium,
at 267 to 680 ug/kg, in kidney. Edible freshwater fishes Barbus
barbus plebejus, Leuciscus cephalus cabeda, Rutilus rubilio, and
Salmo trutta fario contained mean values of 1 SO to 524 ug Hg/kg
wet wt and 192 to 284 ug Se/kg, the highest concentrations in
foodstuffs examined. Aquatic plants and mosses contained 400 and
4000 ug Hg/kg dry wt, respectively, and 100 and 750 ug Se/kg dry
wt. Freshwater concentrations were about 0.8 ug Hg/l and 0.7 ug
Sell. Sediments contained 500 ug Se/kg dry wt. Results showed
that human metabolism of mercury is different from selenium
metabolism and that selenium retention in man could be influenced
by mercury intake. A great Part of selenium introduced through
the diet passes into the blood, where it is mainly associated with
blood cells.
2852.
Schell, W.R. and A. Nevissi. 1977. Heavy metals from
waste disposal in Central Puget Sound. Environ. Sci.
Technol. 11 :887-893.
One source of Pb, Cd, Zn, Hg, Cu and Ni in the Puget
Sound is liquid effluent from the Metropolitan Seattle sewage
treatment facility which is discharged through diffusers at West
Point, Seattle, Washington. Heavy metals were measured in water,
biota, and sediments collected at various distances from the
sewage treatment plant. There were few seasonal differences
between amounts and kinds of metals in samples collected near the
outfall and at control stations. Concentrations of metals in
Puget Sound water, except Pb and Cd, were similar to reported
values for open ocean. Metal levels in Puget Sound were 0.1 to
298
-------
0.8 ug Cd/I, 0.03 to 1.3 ug Pb/l, 0.5 to 2.0 ug Cull, 5.0 to 15.0
ug Ni/l, and 1.5 to 3.0 ug Zn/l. Intertidal and benthic biota
showed only 3I1all increases in concentrations at control
stations. Mercury and lead content were 3.0 to 7.0 ug Hg/kg dry
wt and 1.0 to 1.5 mg Pb/kg in seaweed, Fucus; 5.0 to 10.0 ug Hg/kg
and 1.0 to 2.0 mg Pb/kg in seaweed, Ulva; 6.0 to 12.0 ug Hg/kg and
1.5 to 2.2 mg Pb/kg in mussels, MytilUSedulis; and 5.0 to 12.0 ug
Hg/kg and 1.2 to 2.2 mg Pb/kg in clams. Mean metal
concentrations, in mg/kg dry wt, in surface sediments were 12 to
21 for Co, 42 to 60 for Cr, 30 to 52 for Cu, 0.27 to 0.70 for Hg,
35 to 50 for Ni, 10 to 50 for Pb, and 90 to 130 for Zn. Sediment
cores dated by Pb-210 techniques provided information on the
history of metal accumulation in Puget Sound over the past 100
years. Concentrations of several metals at the surface are 1-3.6X
greater than in sediments deposited 50 years ago, notably Pb and
Hg near West Point.
2853.
Schipp, R. and F. Hevert. 1978. Distribution of copper
and iran in some central organs of Sepia officinalis
(cephalopoda). A comparative study by flameless atomic
absorption and electron microscopy. Marine Biology
47 : 391-399 .
In juvenile and adult S. officinalis (a decapod
mollusc) of the Bassin d' Arcachon~ France, copper and iron
contents of blood, hepatopancreas, branchial gland, branchial
heart, branchial heart appendages, heart ventricle, and pancreatic
appendages were determined. Despite significant differences
between the absolute values of Cu and Fe concentrations in
different organs, a certain parallelism can be demonstrated in
ability to concentrate both metals. The hepatopancreas, as the
most important storage organ, shows the highest concentrations of
copper (100 mg/kg wet wt) and iron (152 mg/kg), followed by the
branchial heart system with distinctly lower values (20 Cu, 46
Fe). The cytolysosome-like dense bodies in these tissues of S.
officinalis and of Octopus vulgaris can be characterized as the
cellular sites of storage by histochemistry and electron
microscopy. The low copper content of branchial gland (22 mg
Cu/kg wet wt) does not disprove hemocyanin synthesis in this
organ; biochemical experiments indicate a subsequent incorporation
of copper released by the endoplasmic reticulum of the gland.
2854.
Schulz, D. 1975. Salinitatspraferenzen bei Glasaalen und
jungen Gelbaalen (Anguilla anguilla). Helgol. wiss.
299
-------
Meeresunters.
sunmary) .
27: 199-210.
(In German, English
Preference experiments have been carried out on elvers
and young eels to assess locomotory responses to different
salinity conditions. It was established that elvers preferred
freshwater to water of 18 0/00 and 36 0/00 S. There was no
significant difference between responses to water of 18 0100 and
36 0/00 S. When young yellow eels were offered different
salinities (freshwater, 18 0100 and 36 0100 S) in tubes, a
preference for water of 18 0/00 S was noted. This preference was
not influenced by the different salinities in which the eels had
previously been kept.
2855.
Shephard, K. and K. Simkiss. 1978. The effects of heavy
metal ions on Ca2+ ATPase extracted from fish gills.
Compo Biochem. Physiol. 61B:69-72.
Gills of the freshwater fish Rutilus rutilus cont~in a
subcellular membrane fraction which is rich in t~e enzym~ Ca +
ATPase. The enzyme is maximally activated by Ca + or ~+
ions at a concentration of about 2 roM but is not affected by Na+
or ~ io~s or ~y ouabaiq. In vitro the enzyme is inhibited by
Cu2+, Pb +, Zn + and Hgc+ ions at concentrations below 10
uM. Copper ions at concentrations below 0.2 uM appear to induce
the formation of additional enzyme units when applied to fish
gills in vivo.
2856.
Singer, P.C. 1977. Influence of dissolved organics on the
distribution, transport, and fate of heavy metals in
aquatic systems. In: Suffet, I.H. (ed.). Fate of
pollutants in the air and water environments. part I.
mechanism of interaction between environments and
mathematical modeling and the physical fate of
pollutants. Advan. Environ. Sci. Tech. 8:155-182.
The influence of dissolved organic matter on
distribution, transport, reactivity, and fate of metals in natural
aquatic systems is discussed, with examples of AI, Ca, Cd, Co, Cu,
Fe, Mg, Mn, Ni, Pb, Po, Si, Zn, and Zr in water, sediments, and
algal species. Water quality literature is reviewed using field
observations of occurrence and distributions of metals and
organics in aqueous environments and phenomenological studies of
metal-organic interactions.
300
-------
2857.
Sunda, W.G., D.W. Engel, and R.M. Thuotte. 1978. Effect
of chemical speciation on toxicity of cadmium to grass
shrimp, Palaemonetes pugio: importance of free cadmium
ion. Environ. Sci. Technol. 12:409-413.
Seawater at salinities of 4 to 29 0/00, with different
concentra ti ons of the chela tor n i tr ilotr iacetic ac id (NTA), were
used to determine relationships between chemical speciation of
cadmium and Cd toxicity to grass shrimp. After 4 days exposure to
a given CdC12 concentration, shrimp mortality decreased with
increasing salinity and increasing NTA concentration. The
protecti ve effect of NTA was attributable to complexation of
cadmium. In seawater at 4.4 0/00 S, only 0 to 10% of shrimp
survived in 246 to 997 ug Cd/l, while 90% survived in 997 ug/l at
29 0/00 S. At 5.2 0/00 S, survival dropped below 50% in 224 ug
Cd/l with no NTA, in 448 ug Cd/l with 10 uM NTA, and in 3360 ug
Cd/l with 100 uM NTA. Mortality was related to measured free Cd
ion concentration, which was determined by total Cd concentration
and level of complexation by either Cl ion or NTA. Fifty percent
mortali ty occurred at a free Cd ion concentration of 44.8 ug/l.
2858.
Vlasblom, A.G., K.F. Vaas, and W. Rozing. 1977. The
osmotic concentration of the blood plasma of plaice
(Pleuronectes platessa) from three habitats of
different salinity. Netherlands Jour. Sea Research
11 :168-183.
Between August 1971 and December 1973, osmotic
concentrations of blood plasma of plaice from Lake Grevelingen and
Lake Veere, Netherlands, were compared with plaice from the North
Sea. Salinity of the sea was always higher than the lakes, of
which Lake Veere v;as lowest. Plaice were hyposmotic to
surrounding sea or brackish water. Blood 03ll0tic concentration
usually decreased with increasing length of plaice. Influence of
temperature on osmotic concentration was stronger in plaice from
the North Sea than from either lake. Seasonal fluctuations in
pla3lla osmolarity are more pronounced in North Sea plaice although
temperature at sea fluctuated less. Interaction of temperature
and salinity changed with fish body length and was strongest in
fish from North Sea and weakest from Lake Verre. Authors
concluded that plaice that have lived for a longer time in an
unusual environment of abnormal salinity (Lake Veere) show the
weakest reaction to environmental changes.
2859.
Wentsel, R., A. McIntosh, and V. Anderson.
1977.
Sediment
301
-------
contamination and benthic rnacroinvertebrate
distribution in a metal-llnpacted lake. Environ.
Pollution 14: 187 -193.
Sedllnent contamination and distribution of benthic
annelids and insects were studied in Palestine Lake, Indiana, a
public 80-ha system contaminated by effluents from a nearby
electroplating plant. Trace metal levels in the upper 3 cm of
sed llnent ranged from a high of 969 rng/kg cadmium, 14,032 rng/kg
zinc and 2106 mg/kg chromium (dry wt basis) near the influent
ditch, to a low of 4 rng/kg Cd, 139 Zn and 38 Cr in the
uncontaminated eastern basin of the lake. The midge Chironomus
tentans was absent from areas of highest contamination; however,
midge numbers increased to an average of 28 individuals/grab
sample in the eastern basin. Specllnens of the aquatic oligochaete
Lirnnodrilus sp. were abundant (89/sample) in the most heavily
llnpacted areas of the lake and scarce <3.4/sample) in the eastern
basin.
2860.
Wickes, M.A. and R.P. Morgan, II. 1976. Effects of
salinity an three enzymes involved in amino acid
metabolism from the American oyster, Crassostrea
virginica. Compo Biochem. Physiol. 53B:339-343.
Adductor muscle and gill tissue from oysters raised in
various salinities were assayed for glutamate dehydrogenase (GDH),
pyruvate kinase (PK) and glutarnate-oxaloacetate transaminase
(GOT). GOT increases linearly with salinity in both muscle and
gill tissue. GDH increases with salinity in muscle. Little GDH
activity is present in gill. No relationship between PK activity
and salinity was evident.
2861 .
Witte-Maas, E.L.M. and D.H. Spaargaren. 1977. Some lethal
and sub-lethal effects in Crangon crangon at
experimental ~ enrichment of their environment.
Netherlands Jour. Sea Research 11:316-324.
Sudden changes in environmental potassium levels were
harmful to shrimps, ~. crangon. In 30 0/00 S and 20 C, survival
dropped below 50% under the following conditions: 24 hrs in 630
rng [T/l as KCl; 7 days in 320 rng ~/l; and 11 days in 160 rng
[T/l. Lethal half-times (LT-50) of Crangon at 5 C decreased
from 20 days with no added ~ at salinities from 10 0/00 to 35
0/00 to 1-5 days in 630 rng ~/l. Lowest LT-50's were at 10-15
0/00 S, and 30 0/00. LT-50 values in 20 C were 10-15 days at
302
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10-15 0/00 S and 30 0/00 in 0.0 mg ~/l, and below 2 days at all
salinities in 630 mg ~/l. Expected LT-50 values calculated
from 30 combinations of salinity and potassium concentrations
showed shrimps were more sensitive at salinities below 15 0/00 and
above 30 0/00 in given ~ levels in 5 C and 20 C water.
Potassium concentrations in blood of shrimps closely paralleled
external ~ levels above 500 mg/l in 20 C, but were hypoosmotic
in 5 C. No clear response in heart beat rate of Crangon due to
~ concentration was observed; heart beat increased slightly in
crabs, Carcinus maenas, in raised ~ water levels.
2862.
Yeo, A.R. and T.J. Flowers. 1977.
halophyte Suaeda maritima (L.)
between aluminum and salinity.
Salt tolerance in the
Dum.: interaction
Ann. Bot. 41:331-339.
Growth of the estuarine plant Suaeda maritima was
stimulated. by lCM aluminum concentrations of 1.35 mg/l in saline
solution culture containing 19,700 mg NaCl/l. Number and extent
of lateral roots increased over 5 days under the same conditions.
Under non-saline conditions the same Al concentration inhibited
growth and led to an abnormal lateral root initiation. Increasing
the level of Al up to 16 mg/l led to growth inhibition under both
culture conditions. Salinity reduced the uptake of Al into plan.t
tissue at all levels of Al exposure, and there was no evidence
that Al was tolerated internally. Plants in 1.0 mg Al/l
accumulated 0.75 mg AI/kg in roots and 0.081 mg Ag/kg in shoots
under saline conditions, compared to 1.59 and 0.24, respectively,
when grown without NaCl. Although short-term P-32 influx was
increased by AI, there were no long-term effects on levels of Na,
K, Ca or P in the shoots. Mechanisms of Al toxicity and
interaction between Al and salt toxicities are discussed. An
explanation is proposed for both stimulatory and inhibitory
effects of Al as a quantitative expression of a single primary
effect upon the root system.
2863.
Yousef, Y.A. and E.F. GloYna. 1977. A transport model for
long term release of low level radionuclide solutions
into a stream ecosystem. In: Suffet, I.H. (ed.).
Fate of pollutants in the arr and water environments.
Part 2. chemical and biological fate of pollutants in
the environment. Advan. Environ. Sci. Tech. 8:239-259.
Processes of radionuclide transport in flowing water
bodies were simulated in 3Dall scale ecosystems. Stratification,
deposition, erosion, and relocation indicate the complexity of a
real river system. Under continuous release of cesium-134 and
303
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strontium-85, bottom sediments and plants concentrated
radioactivity until an equilibrium state was reached. Transfer
coefficients per day from water to sediments were 0.033 to 0.043
for Cs-134 and 0.030 to 0.036 for Sr-85. In rooted plants
Potamogeton, Vallisneria, MyrioghYllum, Utricularia, and Chara;
transfer coefficients were 0.69 for Cs-134 and 0.912 for Sr-85.
Plants reached equilibrium faster than sediments. Uptake rate was
proportional to the differences between saturation level and
concentration in sediments or plants at a given time. Release of
radioactivity was observed after cessation of exposure. Cyclical
diurnal uptake of Cs-134 by phytoplankton was linearly correlated
with photosynthetic 02 production. Suspended phytoplankton
tends to deposit on plant leaves, stems and bottom sediments,
suggesting increases in surface concentration attributable to area
of sorbing surfaces.
2864.
Augier, H., G. Gilles and G. Ramonda. 1978. Studies on
the mercury content in the thallus and in a commercial
product of agricultural use of the brown algae
Ascophyllum nodosum (Linne) Le Jolis manufactured in
Brittany. Botanica Marina XXI:413-416. (In French,
English abstract).
Whole brown algae collected in 1977 from Brittany
contained 0.07 to 0.11 mg Hg/kg wet wt; concentrations in
different sections of the thallus of Ascophyllum ranged from 0.07
to o. 14 mg Hg/kg. Conmercially prepared algal products had a mean
mercury level of 0.08 mg/kg. Looal seawater contained 0.0002 mg
Hg/1.
2865.
Bacci, E., C. Leonzio, and A. Renzoni. 1978. Mercury
decontamination in a river of Mount Amiata. Bull.
Environ. Contamin. Toxicol. 20:577-581.
Since 1970, there has been a drastic reduction in
mining of mercury-bearing minerals around Mount Amiata, Italy. In
1969, by comparison, a total of 1680 metric tons of mercury were
produced. Freshwater mussels, Unio elongatulus, collected in 1973
contained 0.75 to 1.60 mg Hg/kg wet wt in abductor muscle, with
highest concentrations in larger animals. By 1974, mercury levels
of abduc tor muscle had dropped to 0.5 to 0.8 mg/kg; and by 1975
and 1976 concentrations were 0.05 to 0.25 mg/kg. These latest
values determined are only about twice that of background levels
in control site mussels (0.03 to 0.07 mg Hg/kg wet wt).
304
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2866.
Boggess, W.R. (ed.). 1977. Lead in the environment. Nat.
Science Foun. Rept. NSF 1RA-770214 :272 pp. Avail. from
Supt. Documents U.S. Govt. Print. Off., Washington,
D.C. 20402.
This study of lead in the environment sUITInarizes data
on characteristics, monitoring, and analysis of lead; transport
and distribution in atmosphere, soil, biota, watersheds, and
around mines and snelters; effects of lead on microorganisms,
plants, animals, and humans; and recomnendations for control.
Several studies of freshwater ecosystems deal with lead levels in
sediments, fish, benthic invertebrates (including insects,
crustaceans, molluscs, annelids, and nematodes), bacteria, algae,
and higher plants and effects of Pb on biota.
2867 .
Christensen, G., E. Hunt, and J. Fiandt. 1977. The effect
of methylmercuric chloride, cadmium chloride, and lead
nitrate on six biochemical factors of the brook trout
(Salvelinus fontinalis). Toxicol. Appl. Pharmacol.
42:523-530.
Brook trout were exposed to methylmercuric chloride at
concentrations from 0.01 to 2.93 ug of Hg/I, to cadmium chloride
from 0.06 to 6.35 ug of Cd/I, and to lead nitrate from 0.90 to
474.0 ug of Pb/l, for 2- or 8-week periods. Fish weight and
length, hemoglobin, and blood plasma sodium, chloride, glucose,
glutamic oxalacetic transaminase (GOT), and lactic dehydrogenase
(LOO) were measured. The following observed changes were
significant: increases in plasna sodium and chloride and
decreases in hemoglobin and GOT activity caused by Pb at a
threshold of 58 or 235 ug/l; increases in plasma chloride and LHD
and a decrease in plasma glucose caused by Cd at a minimum of 6.35
ug/l; and increases in hemoglobin and plasna sodium and chloride
caused by 2.9 ug/l of methylmercury. Comparisons were made
between these biochemical findings and published data from
bioassay and tissue-residue studies regarding the determination of
threshold indices of toxicity. Maximum acceptable concentration
indices, in ug/l, for brook trout were: molecular index for no
biochemical change in adults, 0.94 (2 wk) and 2.9 (8 wi< exposure)
for Hg, 6.4 and 0.5, respectively, for Cd, and 0.5 and 34.0 for
Pb. Maximum acceptable concentrations bioassay index for no
mortality, growth change, or deformities for alevin-fry and adults
exposed for 38 wks, were: 0.29 Hg, 1.7 Cd, and 58.0 Pb. The
residue index showing no increasing deposition in body for adults
exposed 38 wks; 0.01 Hg, 0.5 Cd, and 0.9 Pb. Maximum allowable
water concentrations for freshwater biota, in ug/l, as suggested
Qy the U.S. Environmental Protection Agency, are 0.05 Hg, 0.4 Cd
and 50.0 Pb.
305
-------
2868.
D'Itri, F.M., A.W. Andren, R.A. Doherty and T.M. Wood.
1977. An assessment of mercury in the environment.
Panel on Mercury Coord. Comm. Sci. Tech. Assessments
Environ. Pollutants. Nat. Acad. Sciences, Nat.
Research Coun., Washington, D.C.:183 pp.
This report summarizes data on the global cycle of
mercury, forms and occurrence of mercury in the environment,
chemical and biochemical mechanisms for methylation and
demethylation, ecological effects to biota, and exposure, uptake,
and effects of mercury on humans. Ecological effects reviewed
include uptake, retention, and elimination in freshwater and
marine species of algae, higher plants, zooplankton, insects,
crustaceans, molluscs, fish, amphibians, birds, and marrmals. Data
on exposure and uptake of mercury in humans via food, including
fish and other seafood, drinking water, and air, and various
effects of methylmercury to adult populations, fetuses, and human
biological processes are also presented. A bibliography of
approximately 400 references is appended.
2869.
Fahy, W.E. and R.K. O'Hara. 1977. Does salinity influence
the number of vertebrae developing in fishes? Jour.
Conseil Int. Explor. Mer 37:156-161.
Embryos of the cyprinodontid fish, Fundulus majalis,
were reared from gastrulation to hatching in a controlled
temperature room at five different salinities (16, 21, 26, 31, and
36 0/00). Compar isons of mean vertebral counts show no
statistically significant differences occurring between groups;
thus no salinity influence upon vertebral number is indicated.
Literature on salinity influence upon vertebral number in fishes
is reviewed. It is concluded that there is little evidence, from
field or laboratory studies, to support the view that salinity can
modify vertebral number in developing fishes.
2870.
Fowler, S.W. and M.Y. Unlu. 1978. Factors affecting
bioaccumulation and elimination of arsenic in the
shrimp Lysmata seticaudata. Chemosphere 9:711-720.
Concentration factors (CF) of radioarsenic-74 as sodium
arsenate in tissues of shrimp following 8 days exposure in media
containing 2 to 100 ug As/I were: 2.6 to 2.7 in whole animal, 5.2
to 8.0 in exoskeleton, 1.3 to 4.4 in muscle, and 3.0 to 4.2 in
viscera. In general, snaller individuals had the largest CF.
Exoskeleton and muscle contained most of the As-74 accumulated in
306
-------
tissues. Exoskeleton and muscle contained 41% and 42%,
respectively, of body total after 8 days; and 52% and 31% after 14
days. After 7 days depuration following 6 day exposure,
exoskeleton contained 34% of total As-74 and muscle 42%. After 35
days loss following single ingestion of As from labelled Artemia,
30% of As was in exoskeleton and 48% in muscle. Molting caused
large variations in As accumulation: shrimp lost about 60% of
incorporated As-74 at each molt. Arsenic accumulation decreased
with increasing salinity from 16 to 38 0/00. Molting masked any
temperature effects since shrimp molted faster at higher
temperatures. Loss of As-74 was slower when accumulated from food
than water, being slightly faster at 20 C than 10 C. Exposure
salinity had little effect on As retention.
2871.
Hamelink, J.L., R.C. Waybrant, and P.R. Yant. 1977.
Mechanisms of bioaccumulation of mercury and
chlorinated hydrocarbon pesticides by fish in lentic
ecosystems. In: Suffet, I.H. (ed.). Fate of
pollutants in-rhe air and water environments. part 2.
chemical and biological fate of pollutants in the
environment. Adv. Environ. Sci. Tech. 8:261-281.
Bioaccumulation of mercury, lindane, and DDE by rainbow
trout, Salmo gairderi, in a flooded limestone quarry in southern
Indiana has been studied for over 3 yrs since additions of 5.0 ug
Hg/l as mercuric nitrate and 0.05 ug/l of both pesticides in
sumner 1972. Water concentration of mercury dropped to 0.15 ug/l
by 120 days, about the time trout were added. Fish accumulated
mercury faster than DDE over 350 days; lindane body burden
increased ooly slightly. Uptake efficiency from water by fish for
organic methylmercury approached 20%, while for inorganic forms it
was ooly 0.2%. Another source of mercury for trout was via
zooplankton diet, primarily Daphnia, which contained 360 ug
Hg/kg. Total mercury available to trout from water and food was
94 ug organic Hg/l or kg and 62 ug inorganic, of which 39 and 26
ug/kg, respectively, were retained by fish during 350 days of
exposure.
2872.
Hammons, A.S., J.E. Huff, H.M. Braunstein, J.S. Drury, C.R.
Shriner, E.B. Lewis, B.L. Whitfield, and L.E. Towill.
1978. Reviews of the environmental effects of
pollutants: IV. cadmium. U.S. Environ. Protect.
Agency Rept. EPA-600/1-78-026:253 pp. (also listed as
Oak Ridge Nat. Lab. Rept. ORNL/EIS-106). Avail. from
Nat. Tech. Inform. Serv., Springfield, VA 22161.
307
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Health and environmental effects of cadmium and
specific cadmium derivatives are reviewed. More than 500
references are cited. Background levels of cadmium are typically
low. The highest concentrations are most likely to be found near
smelters or industrialized urban areas. Cadmium is introduced
into the environment mainly during extraction, refining, and
production of metallic cadmium, zinc, lead, and copper; through
wastes generated during other metallurgical processes such as
electrolytic plating; through reprocessing of scrap metal such as
cadmium-plated steel; following disposal by combustion; or as
solid wastes from consumer items such as paints, nickel-cadmium
batteries, and plastics. Other sources of cadmium in the
environment are cadmium-containing fungicides, phosphate
fertilizers, and municipal sewage sludges. The cadmium body
burden in animals and humans results mainly from diet. In the
United States, the normal intake of cadmium for adult humans is
estimated at about 50 ug/day. Tobacco smoke is a significant
additional source of cadmium exposure. The kidneys and liver
together contain about 50% of the total cadmium body burden.
Acute cadmium poisoning is primarily an occupational problem,
generally from inhalation of cadmium fumes or dusts. In the
general population, poisoning by inhaled or ingested cadmium or
its compounds are relatively rare. Biological aspects of uptake,
metabolism, distribution, and effects of cadmium in aquatic
bacteria, algae, higher plants, protozoans, crustaceans, molluscs,
annelids, fish, and birds, and interactions with copper, zinc, and
salinity are reviewed. The major concern about environmental
cadmium is the potential effects on the general population. There
is no substantial evidence of hazard from current levels of
cadmium in air, water, or food. However, because cadmium is a
cumulative poison and because present intake provides a relatively
small safety margin, authors believe there are adequate reasons
for concern over possible future increases in background levels.
2873.
Jones, J.B. and T.C. S tad tman. 1977. Methanococcus
vanniellii: culture and effects of selenium and
tungsten on growth. Jour. Bacteriology 130: 1404-1406.
Reisolation, culture, and method of preservation of the
methane-producing anaerobe Methanococcus vannielii isolated from
mud of San Francisco Bay is described. Growth of the organism on
formate was markedly stimulated by selenium and tungsten.
Turbidity of the bacterial culture, as a measure of growth, was 3X
higher in 79 ug Sell as selenite than controls at 100 hrs, and 5X
higher in 79 ug Sell plus 18,380 ug Wil as tungstate. Cell yields
were 760 mg wet wtll in controls, 1000 mg/l in Se, and 1100 mgll
in Se plus W.
308
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2874.
Jones, R.M. and S.S. Hillman. 1978.
in the salamander Batrachoseps.
76:1-10.
Salinity adaptation
Jour. Exp. BioI.
Relatively few species of amphibians can tolerate
salinites above 300 m-osmol on a sustained basis. However,
Batrachoseps attenuatus and~. major were successfully acclimated
to 600 m-osmol NaCl and 400 m-osmol sucrose solutions.
Accumulation of sodium over 5290 mg/l and an increased rate of
urea synthesis in excess of 200 roM provided substantial increases
in plasma concentrations of these solutes; these are probably the
two major solutes (plus anions) responsible for elevation of
osmotic concentration in Batrachoseps. Batrachoseps exhibits a
water balance response upon dehydration. Urine production was
significantly reduced in salamanders acclimated to sucrose
solutions compared to those acclimated to tap water or saline of
equivalent osmotic concentration. Plasma urea concentration was
equivalent to urine urea concentration when Batrachoseps was kept
in tap water and during short-term saline acclimation. After
long-term saline acclimation, urine urea concentration was
one-fourth the plasma urea concentration.
2875. Karpevich, A.F. and A.T. Shurin. 1977. Manganese in the
metabolic processes of mollusks of the Baltic Sea.
Soviet Jour. Marine Biology 3:437-442.
The effect of Mn2+, as MnCI2' on metabolic
processes of Macoma baltica, ~ arenaria, and Dreissena
polymorpha, in the Gulf of Riga, was studied. In concentrations
of 2-5 mg/l, acclIDlUlation of manganese in gonad, liver, and heart
of molluscs was low. Oxygen consumption rose sharply in 17-20 mg
Mn/l. After 30-50 days in 30 to 50 mg Mn/l, average tissue
contents rose to 1000-19,300 mg Mn/kg dry wt in mantle (vs.
1.0-270.0 in controls), 50-13,000 in gills (1.0-20.0 controls),
120-1000 in liver (5.0-50.0 controls), and 30-290 in foot (1.0-3.0
controls). As Mn concentration was increased to 140 mg/l, oxygen
consumption gradually declined, the animals became moribund and
died. After about 2 months in solutions of 2-17 mg Mn/l,
molluscs' shells became overgrown with bacteria and blackened as
the result of excretions of grains containing manganese.
2876.
Levander, O.A. (Chmn.). 1976. Arsenic. Subcomm. Arsenic,
Comm. Med. BioI. Eff. Environ. Pollutants, Nat. Res.
Coun. Nat. Acad. Sciences, Washington, D.C.:480 pp.
309
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A review of arsenic is presented with emphasis on
chemistry, distribution in the environment (air, water, soil,
sediments, and biota), metabolism, and biologic effects on plants,
animals, and man. Control recorrmendations are made by the
authors. Arsenic concentrations in plants, plant products, and
animals are listed, including data on algae and aquatic plants,
mammals (humans and whales), crustaceans (shrimps, crawfish,
lobsters, crabs, and plankton), molluscs (bivalves, shelled
gastropods, squid, and octopus), echinoderms (starfish), and a
variety of freshwater and marine fishes. Authors conclude that
environmental contamination of arsenic and subsequent human
exposure to various arsenic compounds has resulted from air
pollution from smelters, improper use of arsenic pesticides, and
episodes of tainted food and drink. Water supplies generally
contain negligible quantities of As, although some cases of
endemically poisoned waters are reported. A bibliography of over
800 references is included.
2877.
MacInnes, J.R. and A. Calabrese. 1978. Response of the
embryos of the American oyster, Crassostrea virginica,
to heavy metals at different temperatures. In:
McLusky, D. S. and A. J. Berry (eds.). Physiology and
behaviour of marine organisms. Pergaroon Press, New
York: 195-202.
LC-50 (48 hr) values of mercury, silver, zinc, and
copper salts to Crassostrea embryos at 20, 25, and 30 C were 10.2
to 12.6 ug Hg/I, 24.2 to 35.3 ug Ag/I, 205 to 324 ug Zn/l, and
15.1 to 18.7 ug Cull. All metals, added either individually or in
combination, were less toxic at 25 C than 20 or 30 C, suggesting
that oyster embryos are more susceptible to metal toxicity at
either 20 or 30 C. Less-than-additive effects were observed at 20
and 25 C with mercury and silver in combination. Simple additive
effects were noted at 30 C for the mercury-silver mixture and at
20, 25, and 30 C for the copper-zinc mixture.
2878.
Middaugh, D.P. and G. Floyd. 1978. The effect of prehatch
and posthatch exposure to cadmium on salinity tolerance
of larval grass shrimp, Palaemonetes pugio. Estuaries
1:123-125.
Exposure to 0.1 or 0.3 mg/l cadmium at 30 0/00 salinity
for 1, 4, or 8 days prior to hatching had no additive effects on
sensitivity of larval shrimp to subsequent Cd exposure and
salinity stress for 14 days after emergence. Only larvae exposed
310
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to o. 1 mg Cd/l for 4 days before hatching and transferred to 10
0100 S water with O. 1 mg Cdll after hatching had significantly
decreased survi val. No decreases were observed for larvae
transferred to 15 and 30 0100 at a pre- and posthatch cadmium
concentration of 0.1 mg/l. At a pre- and posthatch concentration
of 0.3 mg Cdll, survival was reduced for all larvae transferred to
10 and 15 0100 S after hatching. Significant mortality occurred
for only 2 groups exposed before hatching and transferred to 30
0/00 S and 0.3 mg Cdll during 14 days after hatching.
2879.
Moller, V.W. 1978. Lead contents of freshwater snails in
the Upper Rhine Valley. Arch. Hydrobiol. 83:405-418.
(In German, English abstract).
Lead in gastropods collected from the northern Upper
Rhine Valley in spring and sumner 1975 was analyzed. Mean
concentrations, in mg Pblkg dry wt, in whole animals were 66. 1 for
~aea ovata, 72.8 for L. st~alis, 93.6 for Galba truncatula,
.1 for Planorbis corne'Us, 75. for f. planorbis, 70.0 for Physa
acuta, 71.6 for Anisus vortex, and 59.0 for Bithynia tentaculata.
Highest tissue concentrations were registered in shells, averaging
54.3 to 81.0 mg Pb/kg. The lead content of snails collected near
busy roads was exceptionally high, when compared to an isolated
district far from heavy traffic. Increased lead was observed in
summer 1975, and was apparently related to increased traffic
activity. There was no obvious correlation between Pb content and
body size or species. In general, shell contained more than half
the total body content followed by viscera, foot, and mantle in
that order.
2880.
Moraitou-Apostolopoulou, M. 1978. Acute toxicity of
copper to a copepod. Marine Poll. Bull. 9:278-280.
Acute toxicity of copper to the marine copepod, Acartia
clausi, from two locations, one polluted with industrial effluents
and domestic wastes and another from a relatively uncontaminated
area, were compared. LC-50 (48 hr) value for uncontaminated
copepods was 0.034 mg Cull, while for contaminated populations it
was 0.082 mg Cull. All copepods from the uncontaminated area died
within 24 hrs in 1.0 mg Cull; all from the contaminated area died
after 72 hrs. No copepods died within 24 hrs in up to 0.05 mg
Cull from contaminated populations. However, 15 to 28% from
uncontaminated populations died in 0.01 to 0.05 mg Cull.
311
-------
2881 .
Olsson, M. 1976. Mercury levels in biota from Morrum
River during a 10 year clean-up period. Rep. Inst.
Freshwater Res. Drottningholm 55:71-90.
Mercury levels in biota from 11 localities along the
Morrum River, Sweden, after mercury discharge from a paper mill
had ceased, were analyzed each year since 1965. Mean mercury
levels, in ug/kg dry wt, in organisms collected above the mill
since 1969 were: 90 to 125 in alderfly larvae Sialis lutaria,
watermoss Fontinalis antipyretica, and caddisfly larvae
Hydropsyche pelucidula and~. instabilis; 140 to 160 in dragonfly
larvae Agrion splendens and adult!. imagines, leeches belonging
to Erpobdellidae, and fry of fishes, Gobis gob is, roach Rutilus
rutilus, and pike Esox lucius; and 275 in isopods Asellus
aquaticus. Mercury concentrations, in ug/kg wet wt, in these
organisms at sites below the mill decreased from about 500-11,000
in 1965 to 20-200 in 1974. Generally, Hg levels dropped
exponentially and the maximum decrease was seen in biota closest
to the mill. Mercury content in muscle of roach below the paper
mill decreased from 1250 to 350 ug/kg wet wt during 1968 to 1974;
maximum levels in 1971 were found in fish furthest downstream from
the mill. Concentrations in breast muscle of birds, white
wagtail, were <200 ug/kg upstream and 300 to 800 downstream from
the mill. Author concluded that mercury levels were not
correlated with food or habitat of the different species; that
ratios between Hg levels in 8 species was the same in contaminated
and uncontaminated areas; that invertebrate Hg levels depend on
intake of water and possibly metabolic rate; that decrease in Hg
concentration below the mill was exponential with time; that time
for 50% decrease varied from 1 to 2.5 years in invertebrates and
fish; that during discharge, highest levels were found close to
the mill, while after discharge ceased, high levels were further
downstream possibly due to sediments becoming the pollution
source; and that elevated Hg levels in birds downstream showed the
influence on terrestrial organisms from aquatic insects.
2882.
Roth, I., and H. Hornung. 1977 . Heavy metal
concentrations in water, sediments, and fish from
Mediterranean coastal area, Israel. Environ. Sci.
Techno 1. 11:265-269.
Water, sediment, and biota were collected along the
northern part of the Mediterranean coast of Israel in 1974 and
analyzed for cadmium, lead, copper, zinc, nickel, and chromium.
Values showed no significant heavy metal pollution in the studied
area, compared with values found in literature for metal
312
-------
concentrations in other parts of the world. Mean water metal
levels off Israel, in ug/l, were 0.7 to 0.9 for Cd, 2.0 to 2.8 for
Cu, 2.8 to 3.6 for Ni, 6.8 to 7.2 for Pb, and 30 to 44 for Zn.
Metal concentrations in particulate matter were 0.2 ug Cd/I, 0.4
Cr, 0.4 Cu, 0.5 Ni, 2.4 Pb, and 5.7 Zn. Average sediment
concentrations were 0.7 mg Cd/kg dry wt, 4.2 for Cr, 1.6 for Cu,
4.8 for Ni, 8.4 for Pb, and 7.0 for Zn. Marine chlorophytic and
rhodophytic algae contained 0.9 to 2.1 mg Cd/kg dry wt, 2.6 to 6.7
for Cr, 2.9 to 7.6 for Cu, 5.2 to 5.8 for Ni, 1.9 to 22.2 for Pb,
and 117 to 218 for Zn. Commercial fishes Sardinella aurita,
Saurida undosquamis, Merluccius merluccius, Epinephelus ~aza,
Mullus barbatus, Upeneus moluccensis, Diplodus vulgaris, phyraena
sphyraena, Siganus rivulatus, and Solea solea contained means of
0.1 to 0.7 mg Cd/kg dry wt, 0.6 to 4.9 for Cr, 0.7 to 8.3 with a
high of 23.5 for Cu, 0.1 to 10.8 for Ni. 0.04 to 5.3 for Pb, and
0.5 to 40.2 with highs of 61 to 84 for Zn.
2883.
Towle, D.W., M.E. Gilman and J~D. Hempel. 1977. Rapid
modulation of gill Na++~-dependent ATPase activity
during acclimation of the killifish Fundulus
heteroclitus to salinity change. Jour. Exp. Zoology
202: 179-186.
Enzymatic properties of membrane-bound
Na++~-ATPase from gills of killifish acclimated to
freshwater, to 16 0/00 seawater, or to 30 0/00 seawater appeared
to be identical, indicating that the same enzyme may function to
absorb Na+ in low salinities and excrete Na+ at the gills in
high salinities. Specific activities of Na++~-ATPase in the
three salinities were consistent with expected Na+ pumping
rates; activity was higher in freshwater and 30 0/00 S than in 16
0/00 S. Within 30 min after transfer of killifish from one
salinity to another, gill Na++~-ATPase activities reached
equilibrium. Rapid increase in Na++~-ATPase activity in gill
microsomes of fish acclimating from freshwater to 30 0/00 was
accompanied by a sloo decrease in the number of binding sites for
ouabain, supporting the idea that acclimation to short-term
salinity changes may involve modifications in the catalytic rate
rather than the number of Na++~-ATPase molecules.
2884.
Amiard-Triquet, C. and L. Foulquier. 1978. Modalites de
la contamination de deux chaines trophiques
dulcaquicoles par Ie cobalt 60: I: contamination
directe des organismes par l'eau. Water, Air, Soil
Pollution 9:475-489. (In French, English abstract).
313
-------
Cobalt-60 transfer through two freshwater food chains
were investigated using Chlorella (algae) -+- ~
(cladoceran) -+- carp (fish); and Elodea (macrophyte) -+- L~aea
(gastropod) -+- crayfish (crustacean). Peak values for Co- 0
accumulation (mean concentration factor from water) was 24 hrs
(565) for Chlorella, 32 days (3.4) for carp, 30 days (4200) for
Elodea, about 5 wks (about 7(0) for Lymnaea, and about 6 wks
(about 220) for crayfish. In general, the most highly
contaminated species were the primary elements in the food chain.
Authors concluded that concentration factors obtained under
laboratory conditions were of limited worth for extrapolation to
field situations.
2885.
Anderson, R. V. 1978. The effects of lead on oxygen uptake
in the crayfish, Orconectes virilis (Hagen). Bull.
Environ. Contamin. Toxicol. 20:394-400.
Increased Pb concentrations (from 0.0 to 0.5, 1.0, or
2.0 mg Pb/l) caused some decrease in oxygen consumption of
crayfish over a period of 40 days when compared to controls.
Crayfish compensated for decreased gill efficiency by increased
ventilation volume. MaxllDwm concentrations of Pb recorded, in
mg/kg dry wt, were observed at 2.0 mg Pb/l after exposure for 40
days: 52 in exoskeleton, 50 in gill, 12 in viscera, and about 8
in muscle.
2886.
Bengtsson, B.E. 1978. Use of a harpacticoid copepod in
toxicity tests. Marine Poll. Bull. 9:238-241.
The harpacticoid copepod, Nitocra spinipes, was tested
for acute toxicity of 12 metal chlorides ~n brackish wat~r. LC-50
(96 hr) va~ues, in mg/l, were 0.23 for Hgc:+, 1.45 f02 Zn +,
1.8 for Cd +.t. 1.8 for Cu2+, 4.5 for C~2+, 6.0 for Ni +,
10.0 f~r Al3 , 21 for Fe3+, 70 for Mn +, 450 for ~, 580
for Ca +, and 720 for ~+. Their order of toxicity,
expressed as 96 hr LC-50, was in agreement with other
investigations performed in freshwater and seawater. Brackish
water LC-50 (96 hr) values were intermediate to those for fish and
seawater environments. Author concludes that~. spinipes is a
suitable assay organism for brackish water toxicity tests.
2887.
Bloom, H., and G.M. Ayling. 1977. Heavy metals in the
Derwent Estuary. Environ. Geology 2 :3-22.
Analyses of heavy metal concentrations in filtered
314
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waters, suspended particulates, sediments, shellfish, fish,
airborne particulates, and sewage have confirmed work of other
investigators showing that the Derwent Estuary, Tasmania, is
heavily contaminated, particularly with mercury, cadmium, lead,
and zinc. Analyses also have added information about the
distribution of each metal. Apparently, most of the contamination
originated from the operation of a zinc refining plant. More than
20 species of molluscs and barnacles growing in contaminated
regions were listed in order of their respective abilities to
accumulate each heavy metal. Mussels, Mytilus edulis, were good
indicators of cadmium and mercury contamination, but not zinc.
Surf barnacles, Catophra~s pOI~erus, were one of the most
sensitive biological indIcators 0 cadmium contamination. An
indication of the steps by which a waste metal is eventually
accumulated at high and even toxic concentrations in seafoods, may
be seen from a comparison of the relative concentrations of
cadmium, lead, mercury, and zinc found in mussels, sediments,
suspended particulates, and filtered waters. High concentrations
recorded for metals include: 1100 mg Hg/kg, 10,000 mg Zn/kg, and
862 mg Cd/kg in dried sediments; 1500 mg Cd/kg in airborne dust
fallout; and 16 ug Hg/I, 15 ug Cd/I, and 1500 ug Zn/l in filtered
water. M3.ximum levels in organisms were 200 mg Cd/kg dry wt in
oyster Ostrea angasi; 152 to 452 mg Pb/kg in~. edulis and chiton
Sypharochiton pellis-serpentis; 3500 to 100,000 mg Zn/kg in Q.
angasi, barnacle ~. polymerus, and winkle Dicathais tertilosa; and
8.2 to 14.6 mg Hg/kg in the molluscs~. edulis, Q. angasi,
Anapella cycladea, Percanassa pauperata, and Salinator fragilis.
Among 10 local fish species, Platycephalus bassensis, Ruboralgu
ergastulorum, and sharks Mustilus antarcticus and Squalus sp.
contained 0.50 to 0.76 mg Hg/kg wet wt, equal to or above the
Tasmanian Public Health Regulations maximum allowable
concentration of 0.50 mg Hg/kg.
2888.
Bloom, H.D., A. Perlmutter, and R.J. Seeley. 1978. Effect
of a sublethal concentration of zinc on an aggregating
pheromone system in the zebrafish, Brachydanio rerio
(Hamilton-Buchanan). Environ. Pollution 17:127-131.
Adult female zebrafish maintained in water containing a
sublethal level of 5.0 mg/l zinc for 9 days showed no preference
for pheromone-containing donor water at a concentration of
pheromone shown to attract non-zinc treated females. The possible
effect of Zn interference with the pheronomal sex attractant is
discussed.
2889.
Boney, A.D. 1978. Marine algae as collectors of iron ore
dust. Marine Poll. Bull. 9:175-180.
315
-------
Five species of intertidal marine algae (Porphyra
umbilicalis, Plumaria elegans, Pol si honia lanosa, Cladophora
rupestris, Pelvetia canaliculata when s~~ken in iron ore dust
suspensions in seawater (5 g Fe/I) take up appreciable quantities
of the dust load. Weight of ore dust retained per kg fresh wt of
plant after shaking for 6 hrs was 192 to 198 g for Plumaria, 208
to 210 g for Cladophora, 50 to 64 g for Polysiphonia, and 48 to 49
g for Pelvetia. The quantities taken up vary with the modes of
thallus construction. Considerable quantities of ore dust are
retained by the plants after shaking for up to 15 hrs in dust-free
seawater. Marine algae can be used as a monitoring system for ore
dust loading of seawater due to accidental spillages in the
vicinity of ore unloading terminals.
2890.
Brodwick, M.S. and D.C. Eaton. 1978. Sodium channel
inactivation in squid axon is removed by high internal
pH or tyrosine-specific reagents. Science
200:1494-1496.
In squid axon, internal alkalinization from pH 7.1 to
pH 10.2 results in a reversible decrease of the maximum inward
current and the steady state sodium channel inactivation. Similar
effects were observed after treatment of the axon with
tetranitromethane or after iodination with lactoperoxidase. These
results suggest that a tyrosine residue is an essential component
of the inactivation process in this nerve.
2891.
Burgess, B.A., N.D. Chasteen, and H.E. Gaudette. 1975/76.
Electron paramagnetic resonance spectroscopy: a
suggested approach to trace metal analysis in marine
environments. Environ. Geology 1:171-180.
Electron paramagnetic resonance (EPR) spectroscopy
analysis of marine samples from different environments apQears to
differentiate between adsorbed and structural Mn2+ and Fe~+
sites in sediment. This suggests that EPR may provide a means of
distinguishing different environmental influences on sediment.
Acid extract solutions from sediment samples exhibit clearly
defined EPR spectra due to various metals, which are amenable to
qualitative and quantitative analysis at concentrations below 1.0
mg/kg. Spectra of several shellfish vary considerably, both
between species, and within a s~ecies~ dependin~ on sampling
localities. Resonances from Mn +, Mo?+, and Fe3+ were
obtained from shells of barnacles Balanus balanoides, mussels
Mytilus edulis, brain corals Maeandrina, sea urchins
316
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Strongylocentrotus drobackiensis, sea fans Gorgonia flabellum,
clams ~ arenaria, and periwinkles Littorina littorina. Mytilus
shells from New Hampshire contained approximately 20 mg Mn/kg
based on EPR e~amination; higher level~ than reported from other
locations. Mn + is substituted for Ca + in the calcite
structure of some shells, such as Balanus.
2892.
Davies, I.M. and J.M. Pirie. 1978. The mussel Mytilus
edulis as a bio-assay organism for mercury in
seawater. Marine Poll. Bull. 9:128-132.
Surveys of natural populations of mussels have
identified areas of mercury contamination in the Firth of Forth,
Scotland. A field bioassay technique has been devised which
accurately reflects the mean total mercury concentration in the
surrounding seawater. The detection limit of the technique is
estimated at 5 to 20 ng Hg/I; consequently, the method can detect
comparatively small enhancements over background mercury
concentrations in estuarine and seawater.
2893.
Deitmer, J.W. 1977. Effects of cobalt and manganese on
the calcium-action potentials in larval insect muscle
fibres (Ephestia kuhniella). Compo Biochem. Physiol.
58A: 1-4.
In either cobalt- or manganese-(5-25 mM) containing
solutions, action potentials could be elicited by direct
stimulation. The maximal rates of rise and fall of these action
potentials were, however, considerably reduced. The
repolarization phase of the action potentials was delayed by Co
and Mn. The membrane input resistance increased in the presence
of Co and Mn (25 mM) by a factor of 2-4, while the membrane
rectification was abolished. It is suggested that Co and Mn ions
reduced both the inward and outward current of the muscle
membrane. Effects of Co and Mn are compared with those described
for other excitable cells.
2894.
Dickman, M.D. and M.B. Gochnauer. 1978. Impact of sodium
chloride on the microbiota of a small stream. Environ.
Pollution 17:109-126.
The addition of 1000 mg/l NaCI to a small stream to
simulate road salt loading resulted in a reduction in algal
density and an increase in bacterial density on artificial
substrates left in the stream over a 4-week period. Algal
317
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diversity was lower at the salt stressed station, 1.88 compared
with 2.49 in week 3, and 2.61 compared with 2.91 at the fourth
week. Phytophagous grazers were far more abundant at the
salt-free control station. These grazers increased algal
diversity by preventing Cocconeis placentula (the dominant alga)
from overgrowing and out-competing the other major algal species.
Bacterial densities, principally Hyphomicrobium, were
significantly higher at the salt-treated station while algal
densities on the salt-exposed substrates were significantly lower
than on the control slides.
2895.
D'Silva, C. and T.W. Kureishy. 1978. Experimental studies
on the accumulation of copper and zinc in the green
mussel. Marine Poll. Bull. 9:187-190.
Toxicity of copper and zinc to green mussel, ~tilUS
viridis, was evaluated by short-term bioassays. LC-50 ( hr)
values were 0.14 mg/l for Cu and 2.31 mg/l for Zn. The rates of
copper and zinc accumulation were determined by analyzing metal
content in soft parts of mussels at fixed intervals of time.
Maximum accumulation of Zn (60 mg/kg wet wt) was observed after 5
wks immersion in 0.2 mg Zn/l; for Cu this was ~3.2 mg/kg wet wt
after immersion for 5 wks in 0.01 mg Cull. Bioaccumulation was
determined as a function of metal concentration in the
experimental medium. The correlations for the regression lines
indicate that uptake of metal is linear at least for the first 5
weeks.
2896.
EIFAC Working Party on Water Quality Criteria for European
Freshwater Fish with the cooperation of the United
Nations Environment Prograrrme (UNEP). 1978. Report on
cadmium and freshwater fish. Water Research
12:281-283.
Cadmium is widely used in industry and small quantities
are discharged to surface freshwaters. Natural background
concentrations are usually below 1.0 ug/l, but higher levels have
been found in polluted waters. A substantial proportion of the Cd
in river water is adsorbed onto solids in suspension, but only
soluble forms of Cd are toxic to fish. Little is known of the
toxic action of cadmium to fish. The metal is accumulated
predominantly in gills, liver, and kidney. The significance of Cd
residues is not clear although there is some evidence that
osmoregulatory role of gills and kidney may be impaired. Cadmium
is slowly lost from tissues when fish previously exposed to
318
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cadmium are returned to clean water; however, loading can occur in
a short period of time causing death several days later. Acute
and chronic toxicity tests with sensitive species of fish have
given conflicting results which may have been caused by the
variable and unusual concentration-response curve or errors in
measuring concentrations of soluble cadmium. Concentrations
lethal after at least 10 days exposure can be up to 100X less than
those lethal in 2 to 4 days, and if a threshold lethal
concentration exists, it is ill defined. Several environmental
factors influence the position and shape of the
concentration-response curve. A decrease in water hardness and
dissolved oxygen, and possibly in pH value, produces a lower
LC-50; changes in temperature and salinity may also affect cadmium
toxicity. The sensitivity of different species of fish is more
variable for cadmium than. for other common pollutants but
comparisons between data are difficult to make because of
differences in water quality and exposure times. However, of the
few species tested, salmonids are more sensitive than cyprinids
(with the possible exception of carp), with pike occupying an
intermediate position. Juvenile stages appear to be the more
sensitive. Few sublethal effects of cadmium have been observed.
Minnows have been shown to develop spinal deformities and in
rainbow trout the development of ova can be impaired. Increased
activity of male brook trout dur'ing spawning in low concentrations
of cadmium has led to increased mortality. Salmonid fish appear
to be more sensitive than other aquatic biota species which have
been tested. Some species of invertebrates such as Daphnia magna
and Gammarus fossarum appear to be as sensitive as salmonids, but
most others are much more resistant. Some species of aquatic
plants grow more slowly in concentrations of cadmium which are
close to the limits for the survival of fish, but the majority of
plants appear to be very resistant. Few data exist on the status
of fish fauna in surface waters polluted with cadmium, although
there is some evidence that brown trout were absent from waters
where cadmium concentration was predicted to be harmful on the
basis of laboratory experiments. Minnows were also found at
concentrations predicted to be harmless to trout. However, rivers
polluted with cadmium also contain other pollutants, especially
heavy metals, and although some of these have been shown to be
additive with cadmium in their joint toxic action, there is some
evidence that zinc may have an antagonistic effect. On the basis
of a critical examination of the available data, tentative
criteria for dissolved cadmium can be proposed as follows. Values
for common carp should be taken to be the same as those for
rainbow trout pending further data on long-term effects. The
corresponding values for brown trout and pike appear to be about
twice as high as those for rainbow trout while those for the more
insensitive non-salmonid fish such as perch and minnow would be
319
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about 38X higher; allowances should be made for low concentration
of dissolved oxygen and for the presence of other poisons. There
is a need for reliable field data from polluted and unpolluted
rivers and from semi-artificial experimental aquatic ecosystems,
to reinforce these criteria. Such studies are particularly
necessary to establish the maximum concentrations associated with
flourishing populations of resistant coarse fish species, and the
modifying effects of other pollutants, especially zinc, in the
water. The concentration of cadmium in muscle of fish exposed for
long periods to low concentrations of cadmium in the water under
either laboratory or field conditions is highly variable. The
reasons for these differences are not clear. A bibliography of 82
references is appended.
2897.
EIFAC Working Party on Water Quality Criteria for European
Freshwater Fish with the cooperation of the United
Nations Environment Progranme (UNEP). 1978. Report on
copper and freshwater fish. Water Research 12:277-280.
Copper's mode of action on aquatic or~nisms is not
clear but toxicity is largely attributable to Cu +. The cupric
form of copper, the species conmonly found, is readily complexed
by inorganic and organic substances and is adsorbed onto
particulate matter. For this reason, the free ion rarely occurs
except in pure acidic soft waters. Analytical techniques commonly
used to distinguish between toxic ionic copper and non-toxic
soluble copper complexes are not accurate at low concentrations,
making interpretation of field data difficult; where possible,
copper concentrations are expressed herein as "soluble copper",
i.e., that which passes through a millipore filter of average
porosity 0.45 u. Toxicity is increased by reduction in water
hardness, temperature, dissolved oxygen, chelating agents such as
EDTA and NTA, humic acids, amino acids, and suspended solids but
little is known of the effect of pH. Acutely lethal
concentrations of copper to European species of fish in hard water
range over 1.5 orders of magnitude. No reliable comparative data
are available for different species in soft water, for the young
stages, or for sublethal effects. Significant adverse effects on
growth of some species, including rainbow trout, occur at about
0.1 of the LC-50 (96 hr) value. Aquatic plants and algae and
invertebrates are generally more resistant than fish and there is
no evidence that fisheries in waters containing copper have been
adversely affected because of a reduction in food organisms. The
toxicity of copper in natural waters, except soft water free from
organic matter and suspended solids, is less than that predicted
from laboratory tests in clean water, probably because of the
320
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presence of non-toxic complexes and insoluble precipitates.
Sewage effluents containing copper are also less toxic than would
be predicted from laboratory data. The presence of non-toxic
complexes may partly explain the existence of brown trout
populations where the annual 50 and 95 percentile values of
soluble copper were 0.17 and 0.38 of the LC-50 (48 hr) value to
rainbow trout, and some non-salmonid species where the
corresponding values were 0.17 and 0.66, respectively. Only
tentative water quality criteria can be formulated at present
because there are virtually no field observations that indicate
unequivocally the concentrations of copper that are not inimical
to fish populations or fisheries. Also, quantitative data on size
and structure of fish populations are not available, and other
poisons are frequently present with copper. Only meager
qualitative data are available for non-salmonid species. In the
absence of data on the precise effects of copper on natural fish
populations, considerable reliance has to be placed on laboratory
data. It is suggested that the maximum safe concentrations should
be based on annual 50 and 95 percentile values of soluble copper
of 0.05 and 0.2, repspectively, of the threshold LC-50 to rainbow
trout, taking into account the effect of water hardness. A
bibliography of 111 references is appended.
2898.
Eversole, A.G. 1978. Marking clams with rubidium.
Natl. Shellfish. Assn. 68:78. (Abstract).
Proc.
Hard shelled clams, Mercenaria mercenaria, were
successfully marked with rubidium by rearing seed clams in
artificial seawater containing rubidium chloride. Clams exposed
for 48 and 96 hrs to 10,000, 1000, 100, and 10 mg/l RbCI contained
levels of Rb+ significantly higher than controls. Siphon
extension and survival of clams was not affected by RbCI at
concentrations less than 10,000 mg/l. Also, significantly higher
levels of Rb+ were present in tissue for up to 3 wks after clams
were exposed to 1000 mg/l RbCI for 96 hrs and transferred to
uncontaminated water. Diatoms, Phaedactylus tricornutum, exposed
for 24, 48, and 96 hrs to 10,000, 1000, and 100 mg/l RbCI had
significantly higher levels of Rb+ than controls. Clams
cultured for 96 hrs in vessels containing diatoms exposed to 1000
mg/l RbCI had significantly more Rb+ than clams grown with
unlabelled diatoms. Clams exposed to 1000 mg RbCI/1 solutions
with and without diatoms contained levels of Rb+ significantly
higher than clams reared only with labelled diatoms. No
significant difference was detected between clams grown with and
without diatoms at 1.0 g/l RbCI. Mud crabs, Panopeus herbstii,
were offered Rb+-labelled clams for 96 hrs then sacrificed or
321
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transferred to containers with unlabelled clams for 7 days.
Control crabs were fed unlabelled clams and sacrificed at 96 hrs,
and at 7 days. Fecal strands of experimental crabs had evelated
levels of Rb+ with peak values at approximately 132 hrs. Four
tissues dissected from control and experimental crabs were
analyzed. Highest levels of Rb+ were found in hepatopancreas of
experimental crabs after 96 hrs, with no apparent difference after
7 days.
2899.
Fales, R.R. 1978. The influence of temperature and
salinity on the toxicity of hexavalent chromium to the
grass shrimp Palaemonetes pugio (Holthuis). Bull.
Environ. Contamin. Toxicol. 20:447-450.
Chromium was more toxic to shrimp at higher
temperatures and lower salinities. In 10 0/00 S water, the LC-50
(48 hr) values were 81 mg Cr/l at 10 C, 39 at 15 C, 37 at 20 C,
and 21 at 25 C. In 20 0/00 S, LC-50 (48 hr) levels were 147, 107,
78, and 77 mg Cr/l at respective temperatures.
2900.
Georgiadis, G. 1977. Die auswirkung verschiedener
temperatur- und salinitatskombinationen auf Gammarus
fossarum Kock, 1835. Crustaceana Suppl. 4:112-119.
(In German, English summary).
Data are given on tolerance, preference, concentration
of hemolymph, and oxygen consumption of Gammarus fossarum exposed
to different combinations of NaCl (500 to 3000 mg/l) and
temperature (6, 12, 20, 26 C). Observations on Gammarus pulex and
Q. roeselii are included for comparison.
2901 .
Hamriy, M.K. and S.R. Wheeler. 1978. Inhibition of
bacterial growth by mercury and the effects of
protective agents. Bull. Environ. Contamin. Toxicol.
20:378-386.
Mercury-sensitive clones of Bacteroides and Clostridium
were isolated and utilized to ascertain effects of mercury in
combination with tryptone, ground rubber, and various sediment
types. Ground rubber and organic-SH clay sands protected
bacterial cells, apparently by chemi-sorptive behavior.
2902.
Hasnain, A.D., I. Kimura, K. Arai, and T. Yasui. 1978.
Comparative studies on the tryptic digestion of
322
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actomyosins and my~sins from several fish species -
11. changes in Ca + and EDTA-ATPases. Bull. Japan.
Soc. Sci. Fish. 44:143-147.
Ca2+- and EDTA-ATPase of actomyosins from several
fish species and rabbit were a~sayed during digestion with
trypsin. During digestion, Ca +-ATPase of heat denatured
samples of bigeye tuna and Cill~p actomyosins showed patterns which
were identical with those of their respective fresh preparations.
A higher initial activation wa~ a general feature of the tuna
actomyosins if the assay of ea +-ATPase was performed in 60 roM
KCl. The initial activation of tilapia actomyosin ea2+ -ATPase
was of a lesser extent, and was absent from carp, yellowtail and
flatfish actomyosins. At the higher KCl concentration (500 raM) in
the ATPase assay, the response of Ca2+-ATpase was altogether
monophasic, i.e. devoid of any initial activation, even in the
case of rabbit actomyosin. EDTA-ATPase pattern of actomyosin
di~estion by trypsin closely resembled the pattern of
ea +-ATPa~e at the higher KCl concentration. The activation of
myosin ea +-ATPase of tuna species occurred to a lesser extent
than that of actomyosin ATPase, and the reversal of the order of
stability observed in case of actomyosin ATPase of tilapia and
skipjack tuna was no longer noted. The reasons for these
discrepancies are discussed.
2903.
Hodson, P.V., B.R. Blunt, and D.J. Spry. 1978. Chronic
toxicity of water-borne and dietary lead to rainbow
trout (Salmo ~airdneri) in Lake Ontario water. Water
Research 12: b9-~78.
Rainbow trout exposed to lead in Lake Ontario water
demonstrated an LC-50 (21 day) value of 2400 ug Pb/l. At lead
concentrations ranging from 3 to 120 ug/l, the log of Pb
concentrations in most tissues of exposed fish appeared linearily
related to the log of Pb concentrations in water. Highest
concentrations in trout exposed to 100 ug Pb/l for 16 to 32 wks
occurred in opercular bone at 100 mg/kg followed by gill and
kidney at 15 mg/kg. Lead accumulation by brain was not clearly
demonstrated. Exposure over 32 wks to Pb in water at
concentrations as low as 13 ug/l caused significant increases in
red blood cell (REC) numbers, decreases in REC volumes, decreases
in REC cellular iron content and decreases in REC <5 -amino
levulinic acid dehydratase activity. No changes were observed in
hematocrit or whole blood iron content. The changes indicated
increased erythropoiesis to compensate for inhibition of
hemoglobin production and increased mortality of mature red blood
323
-------
cells. After 32 wks exposure to 120 ug Pb/l, 30% of remaining
fish exhibited black tails, an early indication of spinal
deformities. Lead added to food was not available for Pb uptake
by fish. Lead content of fish exposed to dietary lead was not
elevated above control levels. The majority of lead consumed
could be accounted for in feces. Dietary lead may have slightly
inhibited the uptake of dietary iron.
2904.
Hughes, M.R. 1976. The effects of salt water adaptation
on the Australian black swan, Cygnus atratus (Latham).
Compo Biochem. Physiol. 55A:271-277.
Body weight, plasma and tear concentrations,
hematocrit, tissue sizes and Na, K, and CI excretion in salt gland
secretion (SGS) and cloacal fluid (CF) were studied in freshwater
(FW) and saltwater (SW) adapted Australian black swan, ~
atratus, cygnets and adults. FW cygnet plasma Na 119, K-~S--
m-equiv/l were significantly different from adult FW swan plasma
of Na 142; K 1.0. Salt adaptation increased cygnet plasma Na, 136
and salt and Harderian gland sizes, but plasma K, hematocrit, tear
ion concentration, heart, kidney and adrenal gland size were
unaffected. Hematocrit and plasma Na, K, and CI of adults swans
were unaffected by saltwater adaptation. The Na and K content of
spontaneously formed SGS of FW and SW adapted cygnets were the
same. A SW cygnet stomach loaded with Na, 500; K, 25 m-equiv/l
produced SGS at 0.35 ml/min/kg, an unusually high rate; adults
secreted at about 1/3 this rate. FW adults eliminated ~ the
imposed salt loads in SGS (Na, 548 m-equiv/l) and 1/5 in CF (Na,
137 m-equiv/l). SW swans secreted only 1/3 of the load
extrarenally (Na, 656 m-equiv/l) while cloacal excretion (Na, 266
m-equiv/l) increased to ~ the load given. In FW adult swans the
first CF sample was obtained 90 min after the salt loading and in
SW adults 4 min after loading, suggesting the FW swans absorbed
the salt loads more completely and produced more SGS, but that SW
swans allowed the loading solution to pass through the gut to be
excreted as CF.
2905.
Huguenin, J.E. 1977. The reluctance of the oyster drill
(Urosalpinx cinerea) to cross metallic copper. Proc.
Natl. Shellfish. Assn. 67:80-84.
The predatory snail, U. cinerea, is extremely reluctant
to cross metallic copper, and thIs is due to some characteristic
of the metal rather than to effects of physical obstruction. It
was also shown that the width of copper strip is an important
324
-------
parameter in preventing crossings. Copper barriers at least as
wide as the largest animals are recommended for maximum
effectiveness.
2906.
Yamamoto, Y., T. Ishii, and S. Ikeda. 1978. Studies on
copper metabolism in fishes - III. existence of
metallothionein-like protein in carp hepatopancreas.
Bull. Japan. Soc. Sci. Fish. 44:149-153. (In
Japanese, English sLIDlllary).
The appearance of copper-bound metallothionein in
hepatopancreas of carp kept in an O. 1 mg/l copper solution for 2
weeks was determined. Hepatic soluble fractions from controls and
copper-exposed fish showed that: copper as well as zinc was
eluted in two fractions and most of the copper appeared in the
second fraction (F-2) in controls; copper and free SH-group
contents in F-2 from copper-exposed fish significantly increased
when compared to controls; copper, zinc and free SH-groups were
diminished in F-2 from copper-exposed fish; soluble fractions from
control and copper-exposed fish on incubation in copper
incorporated the additive copper into F-2 fractions at a level
much higher in experimentals than controls. In addition, the zinc
in F-2 was replaced by copper and the free SH-groups in this
fraction disapp~red. The molecular weight of F-2 was estimated
to be about 10,000. These findings indicate that, in carp,
hepatopancreas copper induces the synthesis of a copper-binding
protein which can be identified as a metallothionein-like protein.
2907.
Karapetian, J. V. and A.M. Shahmoradi. 1978. Arsenic
concentration in canned tuna fish and sardine. Bull.
Environ. Contamin. Toxicol. 20:602-605.
Canned tuna fish from the Persian Gulf and canned
sardines from the Caspian Sea were analyzed for arsenic. Tuna
contained a mean of 0.78 mg As/kg, ranging from 0.65 to 1.00;
sardines contained 1.0 mg As/kg, ranging from 0.9 to 1.2.
2908.
Kikuchi, T., H. Honda, M. Ishikawa, H. Yamanaka, and K.
Amano. 1978. Excretion of mercury from fish. Bull.
Japan. Soc. Sci. Fish. 44:217-222. (In Japanese,
English sLIDlllary).
The possibility of removing mercury from fish heavily
contaminated by methylmercury was examined in two series of
325
-------
rearing experiments using two marine species of fish: conger eel
(Astroconger myriaster) and sea bream (Chrysophrys major). In the
first series, conger eel from Kagoshima Bay, with natural levels
of mercury of 1.0 mg/kg wet wt in muscle, 0.67 mg/kg in spleen,
and 1.8 mg/kg in liver, were kept in Hg-free seawater and fed raw
fish flesh for 7 weeks. Mercury levels were reduced by 50% in 5
wks for muscle and spleen, and in 3 wks for liver. In the second
series, sea bream were fed for 7 wks with pellets containing
either methylmercury or mercuric chloride at a level of 1.0 mg/kg
and subsequently fed with either commercial pellet feed or pellets
impregnated by a mixture of cysteine, pectin, and chitosan for
another 7 wks. Mercury concentrations at the end of the first
feeding period were 0.9 mg/kg in kidney and 0.25-0.40 in muscle,
liver, brain, and spleen. During the subsequent feeding period,
the mercury level was reduced to less than 0.2 mg/kg in every
tissue examined, with best results in the group fed pellets
supplemented by the mixture mentioned. When fed pellets
containing mercuric chloride, the mercury level in any tissue
never reached 0.2 mg/kg, even after 7 weeks, and suggests that
mercury in this chemical form will excrete readily.
2909.
Koli, A.K. and W.T. Canty. 1978. Determination of
methylmercury in fish of South Carolina. Bull.
Environ. Contamin. Toxicol. 20:537-543.
It was concluded that mercury in muscle tissue from
brown trout containing 1.75 mg total Hg/kg wet wt was in the form
of mono- and dimethylmercury.
2910.
Koli, A.K., S.S. Sandhu, W.T. Canty, K.L. Felix, R.J. Reed,
and R. Whitmore. 1978. Trace metals in some fish
species of South Carolina. Bull. Environ. Contamin.
Toxicol. 20:328-331.
Six species of freshwater and marine fishes of South
Carolina were collected and analyzed for Cu, Fe, Zn, Mn, Cd, and
Hg. Values, in mg/kg whole body wet wt, ranged from 0.01 to 0.20
for Cu, 0.30 to 7.4 for Fe, 0.02 to 5.2 for Zn, 0.02 to 0.25 for
Mn, <0.01 to 0.03 for Cd, and 0.12 to 0.63 for Hg. In general,
marine fishes contained higher levels of all metals than
freshwater species, and larger fish have higher residue levels
than small fish of the same species.
326
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2911.
Kremling, K., J. Piuze, K. von Brockel, and C.S. Wong.
1978. Studies on the pathways and effects of cadmium
in controlled ecosystem enclosures. Marine Biology
48:1-10.
Two experiments were conducted in which cadmium was
added to seawater and its plankton, primarily Chaetoceros spp.,
enclosed in plastic containers moored in Saanich Inlet (Vancouv~r
Island, Canada). In both experiments, two enclosures (ca. 68 mj
each) were used. One was spiked with about 1.3 ug/l cadmium,
while the other served as a control (0.075 ug/l) to assess the
fate of the added metal and its effect on marine phytoplankton.
In both experiments, the pattern of biological events was similar
in the cadmium-treated bag and the control. Furthermore, there
were no marked differences in phytoplankton species composition,
indicating that, at this concentration, cadmium did not affect the
ecosystem. The rate of removal of cadmium by biological processes
was relatively slow. The fraction of metal accumulated (for 2 and
4 weeks, respectively) in the settling material was less than 1%
for the cadmium-treated bags. Experiments on the mechanism of
cadmium binding indicated that the major part of the particulate
metal is loosely bound to outer cell membranes.
2912.
Lasserre, P., G. Boeuf and Y. Harache. 1978. Osmotic
adaptation of Oncorhnychus kisutch Walbaum. I.
seasonal variations of gill NaT-~ ATPase activity
in coho salmon, O+-age and yearling, reared in fresh
water. Aquaculture 14:365-382.
An eventual improvement in salmonid production in
seawater will depend on a fundamental understanding of the natural
osmotic behavior, which demands, in turn, seaward migration of
young salmonids and development of osmoregulatory processes.
Seasonal changes in gill Na+-~ ATPase of coho salmon were
studied on two successive broods, O+-age and yearling, of the
same origin reared under natural conditions in a freshwater
hatchery off the Brittany coast (France). Gill ATPase changes are
of a rhythmical nature, showing that a seasonal activation of the
branchial Na+-~ ATPase affects one part of the population
only. Both age groups, O+-age and yearlings, present two peaks
of Na+-~ ATPase activity during the year, in spring and in
autumn, separated by a law activity period in summer and in
winter. Peaks of ATPase activity in autumn (both groups) and
spring (yearlings) correspond, roughly, with the equinox.
However, the spring activity rise of O+-age fish starts later.
Levels of gill ATPase activity are probably a function of fish
327
-------
size at a given season. Duration of Na+-~ ATPase activation
may be affected by high temperatures of late spring and thus may
fl~ctuate from year to year. Yearly variations in branchial
MgL+ ATPase were evidenced in both groups; at present these
variations are impossible to correlate with the smolting process.
Spring and autumn rises in gill Na+ -~ ATPase of coho salmon
in freshwater indicate changes in osmoregulatory physiology
preparatory to seaward migration. Authors conclude that gill
ATPase activity gives aquaculturists some indication of the
migratory tendencies in young freshwater salmon and thus the
euryhalinity possibilities of the species at a given time.
2913.
Longstreth, D.J. and B.R. Strain. 1977. Effects of
salinity and illumination on photosynthesis and water
balance of Spartina alterniflora Loisel. Oecologia
31:191-199.
Salt marsh grass, Spartina alterniflora, was collected
from North Carolina and grown under controlled nutrient,
temperature, and photoperiod conditions. Plants were grown at two
different illumination levels under variable substrate
salinities. Leaf photosynthesis, transpiration, total
chlorophyll, leaf xylem pressure, and specific leaf weight were
measured. Growth at low illumination and high salinity (30 0/00)
resulted in a 50% reduction in photosynthesis. The reduction in
photosynthesis of plants grown at low illumination was correlated
with an increase in gaseous resistance. Photosynthetic rates of
plants grown at high salinity and high illumination were reduced
only slightly compared to rates in plants grown in 10 0/00. Both
high salinity and high illumination were correlated with increases
in specific leaf weight. Chlorophyll data indicate that specific
leaf weight differences were the result of increases in leaf
thickness. It is therefore hypothesized that photosynthetic
response can be strongly influenced by salinity-induced changes in
leaf structure. Similarities in photosynthetic rate on an area
basis at high illumination were apparently the result of increases
in leaf thickness at high salinity. Photosynthetic rates were
generally high, even at salinities close to open ocean water. It
is concluded that salinity rarely limits photosynthesis in S.
alterniflora.
2914.
Madrid, E., I.P. Zanders and F.C. Herrera. 1976. Changes
in coelomic fluid and intracellular ionic composition
in holothurians exposed to diverse sea water
concentrations. Compo Biochem. Physiol. 54A:167-174.
328
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Ionic concentrations, including Na, K, Cl, Ca, and Mg,
of coelomic fluid of Isostichopus badionotus equilibrated with 80
and 120% seawater in 4-6 hr. With increasing external medium
concentration, intestinal albumin space remained constant whereas
intracellular space decreased; in muscle, total water and
intracellular space decreased and extracellular space increased.
Non-albumin space ionic content per unit dry weight, with the
exception of intestinal sodium, remains practically unchanged in
intestine and muscle in passing from 80 to 120% seawater.
Intracellular ionic concentrations rise proportionately to that of
external medium. Adjustment of intracellular osmolality is due
mainly to water movements into and out of the cells.
2915.
Papadopoulou, C., G.D. Kanias, and E.M. Kassimati. 1978.
Zinc content in otoliths of mackerel from the Aegean.
Marine Poll. Bull. 9:106-108.
Zinc content in otoliths of the mackerel, Scomber
japonicus colias, ranged from 7.2 mg/kg dry wt to 43.6 mg/kg dry
wt. In general, zinc content decreased linearly with fish age and
body length.
2916.
Pentreath, R.J. and M.B. Lovett. 1978. Transuranic
nuclides in plaice (Pleuronectes platessa) from the
north-eastern Irish Sea. Marine Biology 48:19-26.
Concentrations of a number of alpha-emitting nuclides,
Pu-238, Pu-239/240, Am-241, Cm-242, and Cm-243/244 were determined
in organs of flatfish caught in the vicinity of a nuclear fuel
reprocessing plant. Fish were taken for analysis every 3 months
for 2 years. Highest concentrations of plutonium and americium
nuclides were found in kidney, and lowest in muscle. In all
organs analysed, concentrations of americium were greater than
plutonium. Am values were also greater than plutonium when
related to rates of discharge of these two elements, and gave
higher concentration factors over samples of filtered shore-line
seawater taken from the area.
2917 .
Robinson, K.R. 1977. Reduced external calcium or sodium
stimulates calcium influx in Pelvetia eggs. Planta
136: 153-158.
Effect of external Ca and Na ion concentrations on Ca
fluxes in eggs of the marine brown alga Pelvetia fastigiata was
329
-------
measured. Decreasing exte2nal Ca2+ greatly increas2d
permeability of eggs to Ca +; at 1.0 mM external Ca + th~s
permeability was 60x greater than at the normal 10 mM Ca +.
Lowering external Na+ also increased Ca2+ influx; at 2 mM
Na+, the Ca2+ influx was 2-3X greater than normal Na+ if
choline was used as a Na+ substitute. Lithium was less
effectiv~ as a Na+ substitute in increasing Ca2+ influx. The
extra Ca + influx in low Na+ seemed to be dependent on
internal Na+. Ca2+ efflux increased transiently and then
declined in low Na+ media.
2918.
Sakamoto, S. and Y. Yone. 1978.
bream for dietary iron - II.
Fish. 44:223-225.
Requirement of red sea
Bull. Japan. Soc. Sci.
In order to determine amount of dietary iron required
by the marine teleost Chrysophrys major, the effect of dietary
iron on some biological and chemical characteristics of blood were
examined using diets with different levels of iron over a 90-day
feeding trial. Fish fed dietary iron levels lower than 150 mg
Fe/kg diet showed lower values for mean corpuscular constants of
blood and iron content and iron saturation index of blood serum,
and higher values for total iron binding capacity and unsaturated
iron binding capacity of blood serum than those found for fish
receiving higher dietary iron levels. It is concluded that the
dietary iron requirement of ~ed sea bream is approximately 150
mg/kg.
2919.
Sarkka, J., M.L. Hattula, J. Janatuinen, and J.
Paasivirta. 1978. Chlorinated hydrocarbons and
mercury in aquatic vascular plants of Lake Paijanne,
Finland. Bull. Environ. Contamin. Toxicol. 20:361-368.
Mercury had been discharged into L. Paijanne until 1968
as slimicidal agents of a wood-processing industry. Between
1972-74, a total of 23 species of aquatic plants were analyzed for
Hg and chlorinated hydrocarbons. Mercury, in ug/kg dry wt, for
all species ranged from 8 to 122 with a mean of 54 ug/kg (standard
deviation 51). Elodeids and Helophytes contained highest mean
levels (62-65 ug/kg dry wt) and Nymphaeids the lowest (14 ug/kg).
2920.
Sasayama, Y. and C. Oguro. 1976. Effects of
ultimobranchialectomy on calcium and sodium
concentrations of serum and coelomic fluid in bullfrog
330
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tadpoles under high calcium and high sodium
environment. Compo Biochem. Physiol. 55A:35-37.
The role of the ultimobranchial gland of bullfrog
tadpoles on the regulation of Ca and Na levels in serum and
coelomic fluid was studied. Calcium levels in serum and coelomic
fluid in the ultimobranchialectomized tadpoles increased markedly
after 48 hr treatment with high Ca and Na media, although no
changes were found in these levels untreated in tap water. The
tendency to hyponatremia was more pronounced in the
ultimobranchialectomized tadpoles than in the sham-operated. It
is concluded that one function of the ultimobranchial gland of
anuran larva is to suppress acute rise of calcium levels in body
fluid.
2921.
Sastry, K.V. and P.K. Gupta. 1978. Effect of mercuric
chloride on the digestive system of a teleost fish,
Channa punctatus. Bull. Environ. Contamin. Toxicol.
20:353-360.
The LC-50 (96 hr) value of mercuric chloride was
determined as 1.8 mgll for ~. punctatus. Various tissues from
survivors were analyzed for activities of alkaline phosphatase,
acid phosphatase, glucose-6-phosphatase, amylase, pepsin, trypsin,
tripeptidase glycyl-glycine dipeptidase and carnosinase. The
three phosphatases were inhibited in liver, but showed increased
activities in pyloric caeca and intestine. Amylase, pepsin, and
trypsin also exhibited a slight increase in activity. There was
no significant alteration in peptidase activites. Authors
conclude that mercury inhibits liver phosphatase activities, but
not digestive enzymes.
2922.
Somero, G.N., T.J. Chow, P.H. Yancey, and C.B. Snyder.
1977. Lead accumulation rates in tissues of the
estuarine teleost fish, Gillichthys mirabilis:
salinity and temperature effects. Arch. Environ.
Contamin. Toxicol. 6:337-348.
Tissue-specific lead accumulation rates were determined
in Gillichthys as a function of seawater lead concentration
(50-2650 ug Pb/l), duration of exposure to lead acetate (up to 130
days), salinity (25%-100% seawater), and temperature (10 and 20
C). Distinct tissue-specific accumulation rates were found.
Spleen, gill, fin, and intestine accumulated the greatest amounts
of lead; liver and muscle the least. Maximum Pb values, in mg
Pb/kg dry wt, of control fish were 11.6 for spleen, 11.8 for gill,
331
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15.7 for fin, 6.6 for intestine, 2.9 for skin, 7.9 for vertebrae,
2.6 for liver and 1.9 for muscle. After exposure for 8 days to
265 ug Pb/l, maximum values recorded were 31.2 mg/kg dry wt for
spleen, 28.8 for gill, 13.9 for intestine, 8.4 for skin, 18.0 for
vertebrae, 3.4 for liver, 0.7 for muscle and 6.2 for brain. After
130 days in 265 ug Pb/l, maximum values recorded were 100-125 mg
Pb/kg dry wt for spleen, fin, and gill. Exposure for 100 days to
50 ug Pb/l produced values in the 20-30 mglkg dry wt range for
spleen, intestine and gill; lower values were recorded for fin,
skin, liver, vertebrae, and muscle in that order. A similar
pattern was observed at 2650 ug Pb/l after 90 days, with maximum
values recorded approaching 1000 mg Pb/kg dry wt in spleen. Decay
of lead from tissues of lead-exposed fish was observed only for
gill, fin, and intestine, tissues which all possess an outer or
inner covering of mucus. It is suggested that the rapid turnover
of lead in these mucus-covered tissues is a result of lead
complexing with mucus and subsequent loss of lead when the mucus
layer is sloughed off. In spleen and vertebrae, lead levels
continued to rise in fish returned to natural (unspiked) seawater
from lead-spiked seawater. The rate of lead accumulation was
dependent on both salinity and the temperature. Fish held at high
temperature accumulated lead more rapidly than fish held at low
temperature. The rate of lead accumulation was inversely
proportional to the salinity of the medium. Both of these
environmental effects on lead accumulation rates could be
significant in estuarine habitats where lead concentrations,
salinity, and temperature vary seasonally.
2923.
Somero, G.N., P.H. Yancey, T.J. Chow, and C.B. Snyder.
1977. Lead effects on tissue and whole organism
respiration of the estuarine teleost fish, Gillichthys
mirabilis. Arch. Environ. Contamin. Toxicol.
6:349-354.
Oxygen consumption rates of whole fish and isolated
gill tissue were measured in Gillichthys exposed to lead-dosed
seawater for varying periods of time. Whole organism oxygen
consumption was significantly higher in fish exposed to media
containing 2,650 ug Pb/l for up to 60 min at 20 C and 33 0/00 S
than in those held for equivalent periods of time in non-leaded
seawater. In vitro gill respiration rates were virtually
identical for control and lead-exposed fish (exposure to 265 ug
Pb/l for up to 2 hrs at 25 C and 33 0100 S). Lead-exposed fish
were also extremely more active in the aquaria than controls.
These findings suggest that lead-induced metabolic changes may
derive more from lead effects on central nervous system
332
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coordination of activity and metabolism than from direct effects
of lead on intermediary metabolism enzymes in each cell.
2924.
Spehar, R.L., E.N. Leonard, and D.L. DeFoe. 1978. Chronic
effects of cadmium and zinc mixtures on flagfish
(Jordanella floridae). Trans. Amer. Fish. Soc.
107 :354-360.
J. floridae, a freshwater cyprinodont, were exposed to
cadmium and-zinc as individual metals and as mixtures (4.3-8.5 ug
Cd/l and 73.4-139.0 ug Zn/l) through one complete life cycle in
Lake Superior water (45 mg/l total hardness). Cadmium and zinc
did not act additively at sublethal concentrations when combined
as mixtures; however, a joint action of the metals was indicated.
Effects on survival showed that toxicity of Cd and Zn mixtures was
little if any greater than toxicity of zinc alone. Mechanisms of
zinc toxicity in this test were similar to those in previous
chronic tests of individual metals, indicating that presence of
cadmium did not influence mode of action of zinc. Comparisons
between metal residues in fish exposed to each individual metal or
to the metal mixtures showed that uptake of one metal was not
influenced by the presence of the other.
2925.
Thomson, A.J., J.R. Sargent, and J.M. Owen. 1977.
Influence of acclimatization temperature and salinity
on (Na+ + ~)-dependent adenosine triphosphatase
and fatty acid composition in the gills of the eel,
(Anguilla anguilla). Compo Biochem. Physiol.
56B:223-22e.
Microsomal Na/K-ATPase from gills of freshwater eels
had an Arrhenius plot (log specific activity vs. temperature)
discontinuity at 20 C. The corresponding enzyme from seawater
eels had a discontinuity at 12 C. Fatty acids from total lipids
of the gills of freshwater and seawat.er eels were rich in (n-6)
and (n-3) fatty acids, respectively. Freshwater eels adapted to
seawater for 3 months without a temperature change had an
unchanged Arrhenius plot discontinuity and an unchanged fatty acid
composition. The situation was unchanged after a further 3 months
in seawater at low temperature. Seawater eels adapted to a higher
temperature in seawater for 3 months yielded an Arrhenius plot
discontinuity at 20 C and their gills fatty acid were now more
saturated. These changes were reversed by re-adapting the eels
for a further 3 months in seawater at a lower temperature. It is
concluded that temperature and not salinity determines the degree
333
-------
of unsaturation of gill lipids. The position of discontinuity in
the Arrhenius plot of a biomembrane enzyme can be correlated with
the degree of unsaturation of membrane lipids under natural
conditions, reflecting the fluidity of the biomembrane. The (n-3)
and not the (n-6) polYunsaturated fatty acids yield fluid
biomembranes at low temperatures.
2926.
Tromballa, H.W. 1978. Influence of permeant acids and
bases on net potassium uptake by Chlorella. Planta
138 :243-248.
Salts of membrane-permeant acids and bases strongly
influence net K uptake by Chlorella fusca. Na phenylacetate,
acetate, isobutyrate, propionate, and butyrate added to buffered
algal suspensions containing 0.1-0.2 mM KCl increasingly
stimulated net K uptake. In contrast, K release was induced by
the chlorides of imidazole, ammonia and methylamine. All these
effects were found in the light and, less pronounced, in the
dark. The dependence of net K movements on concentrations of
salts added and on pH of medium suggests that free acids or bases
are the effective agents. Between net uptake of K and uptake of
labelled propionate a molar ratio close to 1 was found. It is
concluded that internal pH of the cell is changed by the
permeants. Acidification of the cytoplasm stimulates extrusion of
protons coupled to uptake of K. Alcalization brings about proton
uptake and K extrusion. Apparently, K/H exchange serves as a
pH-stat of the cell.
2927 .
Tucker, C.S. and C.E. Boyd. 1977. Relationships between
potassium permanganate treatment and water quality.
Trans. Amer. Fish. Soc. 106:481-488.
Addition of 2, 4, and 8 mg/l KMn04 slightly decreased
chemical oxygen demand of fish pond water. Treatment of samples
with 4 and 8 mg/l KMn04 decreased biochemical oxygen demand but
did not prevent depletion of dissolved oxygen within the 4-day
test period. Addition of 4 and 8 mg/l KMn04 to water in plastic
pools decreased phytoplankton abundance and gross photosynthesis
and did not prove beneficial in increasing dissolved oxygen
concentrations when oxygen concentrations were near ° mg/l.
Potassium permanganate was also highly toxic to bacteria in
laboratory studies (LC-100 after 4 hrs = 4 mg/l). However, pond
waters often contain large amounts of organic matter which express
a KMn04 demand, rendering the chemical less effective as a
bactericide. This implies that in treating bacterial fish
334
-------
diseases, enough KMn04 should be added to satisfy the KMn04
demand plus a bactericidal residual. The amount of KMn04 per
application can be increased without harm to fish as toxicity to
fish also decreased with increasing KMn04 demand. For example,
the LC-l00 (48 hr) values for KMn04 to bluegill sunfish, and
fathead minnows decreased from about 5.0 mg/l in waters with a
KMn04 demand of 0.1 mg/l to about 9.0 mg/l in waters with a
KMn04 demand of 1.0 mg/l.
2928.
Walker, R.L. and P.O. Fromm. 1976. Metabolism of iron by
normal and iron deficient rainbow trout. Compo
Biochem. Physiol. 55A:311-318.
Iron metabolism in normal and iron deficient trout was
studied after intraperitoneal injection of Fe-59. In both groups
most of the Fe-59 was absorbed from the peritoneal cavity within
24 hr. Equilibrium between plasma Fe-59 pool and tissues was
attained 8 days after injection. Liver iron, the main storage
pool in trout, was reduced from the control level of 185 mg/kg wet
wt to < 100 mg/kg 16 days after bleeding whereas splenic iron
stores were unaffected. In iron deficient fish the RBC Fe-59
content increased to 70-80% of the injected dose by day 16
compared to 50% in controls. This was attributed to the
difference in reticulocyte count, which was 10-20% for bled fish
and 2-3% in controls. Some iron accumulated by erythrocytes is
temporarily stored as non-heme iron by these cells. An average of
15% of the injected Fe-59 was taken up by hepatic tissue of
controls and remained there throughout the 30-day study. In iron
deficient trout, liver radioiron was reduced from a high of 15% on
day 2 to <1% of the initial dose by day 16 post bleeding. There
was essentially no detectable loss of Fe-59 in the urine or feces
of either normal control or iron deficient fish.
Walter, A. and M.R. Hughes. 1978. Total body water volume
and turnover rate in fresh water and sea water adapted
glaucous-winged gulls, Larus glaucescens. Compo
Biochem. Physiol. 61A:233-237.
Total body water (TBW) volume and TBW turnover rate
were measured by tritiated water disappearance rate in
glaucous-winged gulls drinking either freshwater or seawater over
2 weeks. TBW volume was 79% BW and TBW turnover 0.064 ml/g/day in
birds given freshwater; these values did not change when adapted
to seawater. TBW volume is large in gulls compared to other
species, but TBW turnover is similar to that of other birds.
2929.
335
-------
2930.
Wentsel, R., A. McIntosh, and G. Atchison. 1978. Evidence
of resistance to metals in larvae of the midge
Chironomus tentans in a metal contaminated lake. Bull.
Environ. Contamin. Toxicol. 20:451-455.
Chironomid larvae removed from the west basin of
Palestine Lake, Indiana, which received Cd, Cr, and Zn from
electroplating plant wastes for at least 25 years, and chironomids
from the relatively clean east basin were exposed to various lake
sediments. In water for 96 hrs with contaminated sediments
containing 1070 mg Cd/kg, 1680 mg Cr/kg, and 15,100 mg Zn/kg, only
48% of east basin chironomids survived while 75% of west basin
insects survived. With uncontaminated sediments of 6.0 mg Cd/kg,
39.0 mg Cr/kg, and 184 mg Zn/kg, 76% of east basin and 33% of west
basin populations survived 96 hrs. During exposure to heavily
contaminated sediments, larval length increased 9% in east basin
insects and 18% in west basin insects.
2931 .
Yamamoto, Y., T. Ishii, and S. Ikeda. 1977. Studies on
copper metabolism in fishes - II. the site of copper
accumulation in the tissues of carp. Bull. Japan. Soc.
Sci. Fish. 43:1327-1332. (In Japanese, English
sunmary) .
Carp, Cyprinus carpio, were exposed to solutions
containing 0.1 mg Cull for 2 weeks. Ceruloplasmin and
direct-reacting copper contents in the serum of copper-exposed
carp increased significantly compared to controls. By copper
loading, a statistically apparent increase of copper content was
observed in the hepatopancreas, gills, intestine and kidney.
Hepatopancreas contained the highest copper content (28 mg/kg wet
wt) with more than 70% of the copper in the supernatant fraction.
Little, or no, copper was found in ultrafiltrate from the
supernatant fraction. Analysis of the supernatant fraction
demonstrated that most of the copper accumulated in hepatopancreas
was bound to relatively low molecular weight proteins.
2932.
Anderson, W.L. and K.E. Smith. 1977. Dynamics of mercury
at coal-fired power plant and adjacent cooling lake.
Environ. Sci. Technol. 11:75-80.
Mercury in coal, slag, fly ash, airborne particulate
matter, soil, lake sediment, fish, macrophytes, and ducks, was
determined at the Kincaid Power Plant-Lake Sangchris complex in
central Illinois. Of 546 kg of mercury calculated to be in the
2.7 million metric tons of coal burned by the power plant from
336
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September 1973 to August 1974, an estimated 97% was vaporized and
emitted into the air. Mean concentrations of total mercury in
soil were 0.022 mg/kg northeast of the power plant in the
direction of prevailing winds, and 0.015 mg/kg to the southwest.
Mean concentrations in lake sediment were 0.049 mg/kg in deposits
that occurred after the power plant began operating in 1967, and
0.037 in earlier years. Seven species of fishes from Lake
Sangchris (largemouth bass, black bullhead, green sunfish,
bluegill, white crappie, white bass, channel catfish) contained
low amounts of mercury. Mean Hg values for largemouth bass was
0.07 mg/kg wet wt compared to means of 0.16-0.56 for bass from
three other Illinois lakes. Mean levels for other fish from Lake
Sangchris ranged from 0.07 to 0.17 mg Hg/kg wet wt. Some, as yet,
unidentified factor at Lake Sangchris has apparently suppressed
mercury accumulation in the fishes. Total mercury concentrations,
in mg/kg wet wt, in mallard, American wigeon, and blue-winged teal
ducks ranged from 0.035 to 0.053 in breast muscle and 0.025 to
0.140 in liver; maximum individual level found was 0.37 in liver
of a teal. Pondweed contained 0.04 mg Hg/kg dry wt in stems and
0.062 in leaves.
2933.
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. volume II. indium.
U.S. Environ. Protect. Agen. Rept. EPA-560/2-75-005b.
Avail. as PB-245 985 from Nat. Tech. Inform. Serv.,
U.S. Dept. of Corom., Springfield, VA 22151:38 pp.
Indium production in the United States is probably less
than 20 metric tons per year. The American Conference of
GovernmeQtal Hygienists recommend a Threshold Limiting Value of
0.1 mg/m:; (air) based on experiments with mammals. Data
involving humans are limited and as a result, possibly too much
weight is given to a Russian report that individuals exposed to
indium compounds during production complained of pains in joints
and bones, tooth decay, nervous and gastrointestinal disorders,
heart pains and general debility. This has not been reported in
comparable U.S. activities. Since compounds of various
radionuclides of indium are organ-specific, radioactive compounds
of indium are used in diagnostic organ scanning. Toxicity of
radioactive indium compounds is slight, only 3 of 770 patients
exposed to indium showed effects. Stable indium and its compounds
may cause local irritation en contact with the skin. Indium is
poorly absorbed through intestine, with the result that oral
levels of toxicity are quite high. Cells of the
reticuloendothelial system phagocytize indium compound particles,
337
-------
with indium toxicity apparently due to concentration by these
cells. Distribution of indium in the body can be controlled by
the chemical form of indium, suspension medium, and mode of
injection. Some indium salts apparently exert antitumor activity,
but toxic side effects make treatment difficult. Effects of
indium on lower animals, plants (cucumbers), and microorganisms
(alga Chlorella vulgaris and bacterial strains of Azotobacter) are
little known. Although there appears to be potential for
occupational hazards to personnel in industries producing or
utilizing indium, significant detrimental effects have not been
reported in this country. A list of 79 references is appended.
2934.
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. vol. VI. vanadium.
U.S. Environ. Protect. Agen. Rept. EPA-560/2-75-005f.
Avail. as PB-245 989 from Nat. Tech. Inform. Serv.,
U.S. Dept. of Comm., Springfield, VA 22151:84 pp.
The United States is the largest world producer and
consumer of vanadium. Release of vanadium to the environment from
man's activities is estimated to exceed 30,000 metric tons per
year; about two-thirds arises from combustion of residual fuel
oil. In view of the solubility of vanadium oxide, much of the
vanadium in wastes can be considered to enter the waters over a
finite period of time. Natural sources of vanadium include wind
erosion of rocks and transport from soils. Toxicity of vanadium
and its compounds to humans varies from moderate to acute. There
has been little apparent adverse effect of vanadium in the
environment, but occupational hazards exist and are
well-documented. The Threshold Limiting Value in air for
concentration of vanadiuw compounds has been set: vanadium ~
pentoxide dust, 1.5 mg/m.:S; vanad~um pentoxide fume, 0.1 mg/m-';
and ferrovanadium dust, 1.0 mg/mJ. Vanadium has marked effects
an human metabolism, including a reduction in chloresterol,
various enzymes, and sulfur-containing amino acids. Vanadium
ingested by humans appears to be excreted largely unabsorbed. No
evidence was found of teratogenicity, carcinogenicity or
mutagenicity occasioned by vanadium. Some apparent allergic
response was observed to develop after occupational exposures.
Vanadium compounds may be absorbed through lungs, and, to a small
extent, by intestine. Most orally ingested vanadium is excreted
in the feces. Elevated urinary vanadium levels reflect vanadium
exposure, and systemic vanadium is rapidly eliminated from the
body by the kidneys. Vanadium interferes with sulfhydryl group
metabolism and reduces hypercholesterolemia. Presumably, man and
338
-------
the higher animals do not accumulate vanadium in hazardous
amounts. Toxicity in lower animals is greater than in humans and
other mammals, and greatly dependent on exposure, mode of
administration, and valence of vanadium ion. The order of V
toxicity is 5+ > 3+ > 2+. The green blood pigment of
tunicates, primitive marine chordates, contains vanadium and these
organisms effectively accumulate V from seawater and silts. Some
holothurians (sea cucumbers) also contain high levels of
vanadium. Vanadium plays a role in the absorption and reduction
of nitrogen by plants and possibly growth. Information on
toxicity of plants to vanadium is relatively limited, particularly
long-term effects. Plants accumulate and trans locate vanadium,
particularly at acidic pH. Phytotoxicity may involve interference
with iron uptake by plants. Relatively little information is
available concerning effects of vanadium on organisms, including
algae, bacteria, molluscs, echinoderms, tunicates, and mammals.
Since some of these species accumulate vanadium and some exhibit
detrimental effects for acute exposure, potential environmental
hazards from vanadium may exist if environmental vanadium levels
increase. Eighty-four references are appended.
2935.
Aoyama, I., Y.(oshinobu) Inoue, and Y.(oriteru) Inoue.
1978. Experimental study on the concentration process
of trace element through a food chain from the
viewpoint of nutrition ecology. Water Research
12:831-836.
Using Cs-137 in water as a tracer, authors evaluated
predation of the freshwater teleost Astronotus ocellatus on top
minnows, Oryzias latipes, as a function of feeding frequency,
ration size per day, and weight change in Astronotus. Over a
period of 120 days, the concentration of Cs-137 in Astronotus
increased with ration size; the feeding interval had no effect on
uptake of Cs-137; and the concentration in growing fish was
suppressed, increasing in value with increase in weight.
2936.
Badsha, K.S. and M. Sainsbury. 1978. Some aspects of the
biology and heavy metal accumulation of the fish
Liparis liparis in the Severn Estuary. Estuar. Coast.
Marine Sci. 7:381-391.
Tissue levels of heavy metals, feeding habits, rates of
growth, fecundity, and other aspects of general biology of L.
li~aris from the Severn estuary are reviewed. Concentrations, in
mg kg dry wt of whole fish minus guts, in~. liparis from Oldbury
339
-------
in September to March for 1973 through 1976 were 84 to 150 for
zinc, 18 to 32 for lead, and 2.5 to 10.4 for cadmium. Lowest
levels were generally in 1975-1976. Whole dried fish less guts
from Berkeley in October to February for 1974 through 1976
contained 80 to 195 mg Zn/kg dry wt, 17 to 31 mg Pb/kg, and 3.1 to
7.1 Cd, with lowest values in 1975-76. At Hinkley Point, fish
collected in September 1975 to March 1976 contained 94 to 160 mg
Zn/kg dry wt, 12 to 18 Pb, and 2.4 to 4.4 Cd. In similarly sized
fish from the same area, L. liparis contained higher levels of
these metals, as much as 2X more, than a related species,
five-bearded rocklings, Ciliata mustela.
2937.
Bottino, N.R., R.D. Newman, E.R. Cox, R. Stockton, M.
Hoban, R.A. Zingaro and K.J. Irgolic. 1978. The
effects of arsenate and arsenite on the growth and
morphology of the marine unicellular algae Tetraselmis
chui (Chlorophyta) and Hymenomonas carterae
(Chrysophyta). Jour. Exper. Marine BioI. EcoI.
33: 153-168.
The effects of arsenic on marine phytoplanktonic algae
varied with oxidation state of As, its concentration, and degree
of illumination. Arsenate affected mainly algal growth but also
morphology, whereas arsenite caused only morphological changes.
When grown in modified seawater from the Gulf of Mexico, cell
number of T. chui reached 0.04/1 under the following time-arsenate
concentratIon regimes: 2 days, 1.0 mg As/I; 5 days, 20 mg As/I; 8
days, 50 mg As/I. Differences in growth rates of H. carterae was
not as pronounced. Studies on the incorporation of As-74 as
arsenate into cells grown in artificial seawater indicated that
arsenate was incorporated and later partially released by both T.
chui and H. carterae. Both arsenate influx and efflux seemed to
be energy=dependent phenomena since they varied with degree of
illumination. Differences between rates of uptake and release of
arsenic suggested that arsenate undergoes chemical changes after
transport into algal cells.
2938.
Brehm, P., and R. Eckert. 1978. Calcium entry leads to
inactivation of calcium channel in Paramecium.
Science 202:1203-1206.
Under depolarizing voltage clamp of Paramecium an
inward calcium current developed and subsequently relaxed within
10 milliseconds. The relaxation was substantially slowed when
most of the extracellular calcium was replaced by either strontium
340
-------
or barium. The relaxation is not accounted for by a drop in
electromotive force acting on calcium, or by activation of a
delayed potassium current. Relaxation of the current must,
therefore, result from an inactivation of the calcium channel.
This inactivation persisted after a pulse, as manifested by a
reduced calcium current during subsequent depolarization.
Inactivation was retarded by procedures that reduce net entry of
calcium, and was independent of membrane potential. The calcium
channel undergoes inactivation as a consequence of calcium entry
during depolarization. In this respect, inactivation of the
calcium channel departs qualitatively from the behavior described
in the Hodgkin-Huxley model of the sodium channel.
2939.
Buzinova, N.S. 1978. Dynamics of activity of digestive
enzymes in fish under the influence of pollutants.
Jour. Ichthyology 17:805-808.
Toxicity of an organic tin compound, triethyl stannic
chloride (TESC), was determined on digestive enzymes of yearling
mirror carp, Cyprinus carpio. Over a period of 60 days, amylase
activity in gut decreased in 0.003 mg TESC/l administered via both
water and food but not by water alone. Hepatopancreas amylase
decreased in 0.003 mg/l from water but not water and food.
Amylase activity of gut and hepatopancreas decreased in 0.1 mg
TESC/I :'rom water and from water, and f cod by 60 days and in O. 5
mg/1 by 5 days. Activity of gut and hepatopancreas trypins
declined in 30 days in 0.003 mg TESC/l when given via water and
food, but not significantly when from water alone.
2940.
Charbonneau, S.M., K. Spencer, F. Bryce, and E. Sandi.
1978. Arsenic excretion by monkeys dosed with
arsenic-containing fish or with inorganic arsenic.
Bull. Environ. Contamin. Toxicol. 20:470-477.
Four female Cynomologus monkeys were fed a single dose
of fish homogenate of grey sole, Glypocephalus cynoglossus, which
contained 77 mg As/kg. The homogenate dose was administered at
approximately 1.0 mg fish-As/kg monkey body wt. Monkey chow food
and drinking water contained 0.1 mg/kg and 0.01 mg/l total arsenic
respectively. Sixty-seven percent of the arsenic was excreted
with the urine and 10% with the feces within 5 days. The monkeys
were later administered inorganic arsenic; 76% was excreted with
urine and practically none with feces over 14 days.
341
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2941 .
Clark, D.L., A.A. Weiss, and S. Silver. 1977. Mercury and
organomercurial resistances determined by plasmids in
Pseudomonas. Jour. Bacteriology 132:186-196.
Mercury and organomercurial resistance determined by
genes an ten Pseudomonas aeruginosa plasmids and one Pseudomonas
putida plasmid have been studied with regard to the range of
substrates and the range of inducers. Th~ plasmidless strains
were sensitive to gro~h inhibition by H~+ and did not
volatilize Hg from HgC+. A strijin with plasmid RP1 (which
does not confer resistance to Hg;+) similarly did not volatilize
mercury. All 10 plasmids deter~ine mercury resist5Bce by way of
an inducible enzyme system. Hg;+ was reduced to Hg , which is
insoluble in water and rapidly volatilizes from the growth
medium. Other plasmids in~. aeruginosa and~. putida confe~red
resistance to, and the ability to volatilize mercury from Hg;+,
but strains with these plasmids were sensitive to and could not
volatilize mercury from the organomercurials methylmercury,
ethylmercury, phenylmercury, and thimerosal. These plasmids, in
addition, conferred resistance to the organomercurials merbromin,
p-hydroxymercuribenzoate, and fluorescein mercuric acetate by a
mechanism not involving degradation. In all cases,
organomercurial decomposi~ion and mercury volatilization were
induced by exposure to HgC+ or organomercurials. Ahe plasmids
differed in the relative efficacy of inducers. HgC+ resistance
with strains that are organ~ercurial sensitive appeared to be
induced preferentially by Hg;+ and only poorly by
organomercurials to which the cells are sensitive. However, the
organomercurials p-hydroxymercuribenzoate, merbromin, and
fluorescein mercuric ijcetate were strong inducers but not
substrates for the H~+ volatilization system. With strains
resistant to phenylmercury and thimerosal, these organomercurials
were both inducers and substrates.
2942.
Crowther, R.A. and H.B. N. Hynes. 1977. The effect of road
deicing salt on the drift of stream benthos. Environ.
Pollution 14:113-126.
The three major ions in common road salts (Cl-,
Na+, ea2+) were monitored in Laurel Creek from December 1973
to February 1975 to determine whether levels of salt from road
runoff affect the drift of benthic invertebrates of urban streams
in southern Ontario. Maximum salt concentrations occurred during
the winter, with high~st levels being 1770 mg Cl-/l, 9550 mg
Na+ /1, and 4890 mg Ca +/1. Since most of the salt was
entering the creek as NaCl, this chemical was used to test the
342
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drift response of two insects, Hydropsyche betteni and
Cheumatopsyche anal is, and one amphipod, Gammarus pseudolimnaeus.
Pulses of salt to BOO mg CI-/I had no effect on drift patterns.
Several experiments were conducted in Lutteral Creek which had
been longitudinally divided. As much as 750 mg CI-/I produced
no differences in drift between salted and unsalted channels.
However, a pulse of 2165 mg CI-/I increased drift of all
organisms in the salted channel; this became apparent only when
the concentration exceeded about 1000 mg/l.
2943.
Cutshall, N.H., J.R. Naidu, and W.G. Pearcy. 1978.
Mercury concentrations in Pacific hake, Merluccius
productus (Ayres), as a function of length and
latitude. Science 200:1489-1491.
Mercury concentrations in hake increased with fish size
and with the latitude of collection. Mercury levels in hake about
300 nm in I ength were < O. 1 to 0.2 mg/kg wet wt, wh ile
concentrations in fish 600 mm in length were 0.4 to 0.5 ~/kg.
Mean Hg concentrations rose from 0.085 mg/kg wet wt at 32 51 'N
latitude to 0.383 mg/kg at 48000'-48o28'N. While the
mercury-size trend is consistent with data for other species, the
latitudinal trend is opposite to that reported for other fishes
over the same geographical area. Authors conclude that
latitudinal trends of mercury concentrations in fishes do not
necessarily indicate trends of mercury concentrations in water.
Instead, food habits and metabolism may cause the observed
variations.
2944.
Davenport, J. and A. Manley. 1978. The detection of
heightened sea-water copper concentrations by the
mussel ~tiluS edulis. Jour. Marine BioI. Assn. U.K.
58:843- 50.
An acute toxicity threshold of 0.09-0.10 mg/l added
copper was determined for mussels from the Menai Strait which were
exposed to CUS04 in a flowing seawater system. Median lethal
times (50% mortality) was 255 hrs in 0.09 mg Cull, 242 hrs in 0.10
mg Cull, and 169 hrs in 0.18 mg Cull; MLT was not reached in 0.07
mg Cull by 12 days. The closure response of the mussel to added
copper was shown to be a three-part process. First, a sharp
adduction of shell valves is seen at a mean total copper
concentration of only 0.021 mg/l. Then as the concentration
rises, "testing" behavior is observed. Finally, shell valves
close to isolate the mussel from its environment. The complete
343
-------
valve closure mechanism operates at copper concentrations of 0.2
mg/l or more. The initial valve adduction reaction occurred at a
significantly higher mean total copper concentration of 0.1"6 mg/l
in mussels which had been acclimated to 0.02 mg Cull for 10 days.
2945.
Dorgelo, J. 1977. Comparative ecophysiology of gammarids
(Crustacea:Amphipoda) from marine, brackish- and
fresh-water habitats exposed to the influence of
salinity-temperature combinations. IV. blood sodium
regulation. Netherlands Jour. Sea Res. 11:184-199.
Blood sodium regulation as a function of salinity (0 to
45% SW) and temperature (5, 15, and 25 C) was determined for
garmnarids from marine littoral (Chaetogammarus marinus),
oligohaline (Gammarus tigrinus) and freshwater (Q. fossarum)
environments. All three species were hyperosmotic over the
salinity range at each temperature, except G. fossarum in
supranormal, potentially lethal salinities.- Gammarids showed
hyperregulation at homoiosmotic levels that decreased from coastal
to brackish water to freshwater origin. Generally, new steady
state levels of blood sodium were reached within 48 hrs; Na
alterations were rapid during the first hours. When placed in
extreme salinities at 25 C, all animals died within 2 days.
Temperature had no influence on regulation level of the 3
species. Q. tigrinus resembled ~. marinus in osmotic regulation
more than G. fossarum, which may be linked to great salt
tolerance. - Small male C. marinus, averaging 9.2 mg dry wt, had
higher blood Na content-at 457 mM than large males of 27.5 mg at
431 roM Na; no differences were noted in other species.
2946.
Ernst, W.H.O. and M. Marquenie-van der Werff. 1978.
Aquatic angiosperms as indicators of copper
contamination. Arch. Hydrobiol. 83:356-366.
Effluents of pig bioindustries cause copper
contamination of water, mud and aquatic plants in ditches in the
Netherlands. Aquatic angiosperms and algae, Elodea nuttallii,
Spirodela polyrhiza, Ceratophyllum demersum, Nuphar luteum,
Vaucheria sp., and Oedogonium sp., accumulate Cu to 33 to 4390
mg/kg dry wt at the effluent source and 5. 1 to 42.0 mg/kg one km
from the outfall. Plants from a control ditch contained 4.4 to
17 . 8 mg Cu/kg dry wt. Copper uptake by leaves of Elodea is active
and can be described by a multiphasic system. Uptake depends on
Cu concentration in the medium, temperature, pH, time, and ratio of
344
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biomass and water volume. Median lethal times in 6.4 mg Cull
range from 2 to 3 wks for Elodea and Lemna minor, and to >4 wks
for Callitriche platycarpa. This difference in copper resistance
is discussed in relation to uptake and cellular localization of
copper. The possibilities for transplant of hydrophtyes for
biological monitoring are discussed in view of chemical analysis
of water and mud.
2947.
Findley, A.M., B.W. Belisle, and W.B. Stickle. 1978.
Effects of salinity fluctuations on the respiration
rate of the southern oyster drill Thais haemastoma and
the blue crab Callinectes sapidus. Marine Biology
49 :59-67.
Respiration rates of Thais and Callinectes were
determined as a function of salinity at 20 C in animals acclimated
to 10, 20, and 30 0/00 S. Effects of 10-5-10 0/00, 20-10-20 0/00,
30-10-30 0/00 S, and 10-30-10 0/00 S semidiurnal cycles (12 hr) of
fluctuating salinity on respiration of the oyster drill and
effects of diurnal (24.8 hr) salinity cycles on oyster drills and
blue crabs were also studied. Respiration rate of 30 0/00 S
acclimated oyster drills (679 ul 02/g dry wt/hr) was
significantly higher than individuals acclimated to 10 0/00 S (534
ul). Blue crab respiration was 170 ul 02/g dry wt/hr at 30 0/00
S, but was significantly higher at 10 and 20 0/00 S. With the
exception of the 20-10-20 0/00 S semidiurnal cycle, respiration
rate of oyster drills declined as salinity fluctuated in either
direction from the acclimation salinity and increased as salinity
returned to the acclimation salinity. Semidiurnal salinity cycles
produced greater changes in respiration rate of snails than
analogous diurnal cycles. A 10-30-10 0/00 S pattern of
fluctuation caused a greater percentage reduction in steady state
respiration rate of drills than the 30-10-30 0/00 S pattern.
Respiration rate of crabs varied slightly and inversely with
fluctuating salinity. Crab respiration dropped during the initial
phase of declining salinity at a rate directly proportional to
rate of salinity decrease, perhaps representing a metabolic
adjustment period by the crabs. The respiratory response of T.
haemastoma to salinity is consistent with its incomplete volume
regulation, while the response of .Q. sapidus is compatible with
its ability to regulate extracellular fluid and osmotic and ionic
composition.
345
-------
2948.
Fraser, J., D.T. Parkin and E. Verspoor. 1978. Tolerance
to lead in the freshwater isopod Asellus aquaticus.
Water Research 12:637-641.
Isopods from 3 sites in the River Trent basin were
subjected to different amounts of lead pollution. Differential
survival was recorded between size classes and sites that could be
explained in terms of genetic adaptation. Mean lead levels in
river water at Lea Marston were 0.05 to 0.06 mg/l between 1973 and
1975; levels at Rochester and Great Haywood were 0.03 mg Pbll
during this period. Of 40 isopods from Lea Marston held in 1500
mg Pbll, as lead nitrate, for 24 hrs, 4 animals < 4.0 rrm length and
8 > 4.0 nm survived. None and 1 small isopod, and 4 and 2 large
isopods from Rochester and Great Haywood, respectively, survived
in 1500 mg Pb/l. Survival differences in small specimens from the
3 sites were seen in concentrations as low as 500 mg Pb/l; size
differences were apparent in a minimum of 250 mg Pbll in isopods
from all locations. Significance of the results is discussed in
terms of adaptation to environmental pollution.
Fuhrman, J.A., S.W. Chisholm, and R.R.L. Guillard. 1978.
Marine alga Platymonas sp. accumulates silicon without
apparent requirement. Nature 272:244-246.
Intracellular concentrations of total Si(OH)4 acid in
PI(t~on<:s could be as high as 500 mM with more than 100 mM
Si OH 4 In the dissolved fraction. Despite this significant
accumulation, authors were unable to demonstrate a silicon
requirement in this alga. Because natural waters are often low in
Si(OH)4 relative to the requirements of diatoms, uptake of this
element by organisms such as Platymonas sp. could represent a
mechanism by which they limit the growth of other species without
affecting themselves, a relationship known as amensalism.
2949.
2950.
Fujiki, M(otto), M. Fujiki, S. Yamaguchi, R. Hirota, S.
Tajima, N. Sh imojo , and K. Sano. 1978. Accumulation
of methyl mercury in red sea bream (Chrysophrys major)
via the food chain. In: Peterson, S.A. and K.K.
Randolph (eds.). Management of bottom sediments
containing toxic substances. Proc. 3rd U.S.-Japan
Experts' Meeting, November 1977, Easton, Maryland.
U.S. Environ. Proto Agen. Rept. 600/3-78-084:87-94.
Accumulation of methylmercury in the marine teleost, C.
346
-------
major, can result from food chain accumulations--from diatoms,
Skeletonema costatum, to copepods, Acartia clausi, or brine
shrimp, Artemia salina, to the juvenile bream. Diatoms, reared
for 24 hrs in seawater containing 5.0 ug/l methylmercury,
accumulated 3.45 mg/kg. The diatoms containing methylmercury were
fed to copepods for 4 days, at which time the concentration of
methylmercury in Acartia reached 3.14 mg/kg. Copepods were then
fed to juvenile red sea bream for 10 days. Methylmercury level in
fish was 3.10 mg/kg after feeding. The concentration of
methylmercury in diatoms and copepods was about 2000X that of
culture solution. The increase of metal from food to fish was
about 2X. However, the amount of methylmercury accumulated by the
juvenile bream was about 120X that of controls.
2951 .
Fujiki, M., R. Hirota, and S. Yamaguchi. 1977. The
mechanism of methylmercury accumulation in fish. In:
Management of bottom sediments containing toxic
substances. Proc. 2nd U.S.-Japan Experts' Meeting,
October 1976, Tokoyo, Japan. U.S. Environ. Proto Agen.
Rept. 600/3-77-083:89-95.
The factors contributing to methylmercury accumulation
in red sea bream, Chrysophrys major, were investigated by using
seawater containing 0.5 ug/l methylmercury, bottom sediment from
Minamata Bay, Japan, methylmercury of 0.015 mg/kg dry wt, total
mercury of 192 mg/kg dry wt, and prawns, Penaeus japonicus, bait
containing 0.133 mg/kg methylmercury. Fish placed in contaminated
seawater accumulated methylmercury from 0.012 mg/kg wet wt to
0.033 in muscle tissue over 10 days. Fish fed methylmercury-
contaminated prawns accumulated methylmercury in muscle increased
from 0.012 to 0.020 mg/kg. Mercury levels were elevated within 2
days in fish in contaminated water and sediment. Fish raised in a
tank containing sediment from Minamata Bay did not show an
effective accumulation of methylmercury. During 10 days exposure,
fish weight was higher in all three contaminated conditions than
controls; there was no difference in length.
2952.
Gadd, G.M. and A.J. Griffiths. 1978. Microorganisms and
heavy metal toxicity. Microbial Ecology 4:303-317.
The environmental and microbiological factors that can
influence toxicity of Ag, Cd, Co, Cu, Fe, Hg, Mg, Mn, TI, and'Zn
are discussed with a view to understanding the mechanisms of
microbial metal tolerance. Metal toxicity can be heavily
influenced by environmental conditions: binding of metals to
347
-------
organic materials, precipitation due to alkaline pH, complexation,
and ionic interactions with other metals. Organisms including
bacteria, yeast, fungi, algae, and protozoans possess a range of
tolerance mechanisms, most featuring some kind of detoxification.
These include H2S and organic compound production to form
organometallic compounds or sulfides, transformation of metal
valences, and intercellular detoxification after uptake and
accumulation of metals. Some strains have a genetically-
determined metal resistance. Many detoxification mechanisms occur
widely in the microbial world and are not only specific to
microbes growing in metal-contaminated environments. A
bibliography of 120 references is appended.
2953.
Gardner, D. 1978. Mercury in fish and waters of the Irish
Sea and other United Kingdom fishing grounds. Nature
272:49-51.
Mean mercury concentrations in surface waters from
various UK fishing grounds ranged from 16.6 ng/l to 57.8 ng/l
(range for all stations was 0.0 to 443.0 ng/l). Mean mercury
concentrations in fish flesh ranged from 0.10 to 0.64 mg/kg wet
wt. Concentration factors of Hg from water to fish in different
areas ranged from 2900 in unpolluted distant fishing grounds to
10,600 within Liverpool and Morecambe Bay. A concentration factor
of 20,500 was obtained from water to fish in the central Irish Sea
and around the Isle of Man; this anomaly is probably attributable
to low Hg levels found throughout the year in this area, to
current patterns, and to migratory habits of fish stocks.
2954.
Glooschenko, W.A. and J.A. Capobianco. 1978. Metal
content of Sphagnum mosses from two northern Canadian
bog ecosystems. Water, Air, Soil Poll. 10:215-220.
Samples of 6 species of Sphagnum moss collected from
Kinoje Lake, northern Ontario, and Porter Lake, Northwest
Territories, Canada, were analyzed for 10 elements. On a dry
weight basis, Ca was highest in concentration followed by Mg, Fe
and Mn; other elements were lower by an order of magnitude or
greater. Average metal concentrations, in mg/kg dry wt, in moss
from Kinoje and Porter Lqkes, respectively, were 1860 and 2220 for
Ca, 530 and 1440 for Mg, 270 and 1020 for Fe, 290 and 270 for Mn,
61 and 83 for Hg, 37 and 35 for Zn, 23 and 7.0 for Pb, 14 and 13
for Cu, 3.5 and 2.8 for Cr, and 1.0 and 0.3 for Cd. The two
Canadian sites were similar in elemental composition except that
the Ontario site was higher in Cd ana Pb, while the N.W.T. site
348
-------
was higher in Mg and Hg. These differences could be due to a
combination of regional geochemical and human activity
differences.
2955.
Glover, H. 1977. Effects of iron deficiency on
Isochrysis galbana (Chrysophyceae) and Phaeodactylum
tricornutum (Bacillariophyceae). Jour. Phycol.
13:205-212.
Cultures of marine algae were grown in iron-limited
chemostats containing between 0.5 and 15.9 ug atoms Fell. With
increasing iron deficiency, photosynthetic rate per cell and
assimilation number decreased. The pattern of photosynthesis was
also altered. In Fe deficient cells the proportion of C-14 fixed
in glycine and serine decreased with an accompanying increase into
alanine after 3 min assimilation. Although there was no
significant effect of Fe deficiency on the proportion of C-14
incorporated into total amino acids and amides, the percentage of
total C-14 fixed in protein increased with increasing Fe
deficiency. Cellular levels of chlorophyll a, carotenoids,
cytochromes and protein also decreased with increasing Fe
deficiency. However, the reduction in chlorophyll alcell was not
as great as that of cytochrome f l' with the result that Fe
deficient cells showed a marked increase in the ratio of
chlorophyll a to cytochrome f1.
2956.
Gogate, S.S., S.M. Shah, and C.K. Unni. 1975. Strontium,
calcium and magnesium contents of some marine algae
from the west coast of India. Jour. Marine BioI. Assn.
India 17:28-33.
Algae collected from the west coast of India in 1964
and 1965 were analyzed for strontium, calcium, and magnesium.
Mean concentrations, in mg/kg dry wt, ranged from 19 to 646, with
a high of 1460, for Sr; 1860 to 25,000 for Ca; and 2950 to 74,500,
with a high of 118,400, for Mg. Strontium to calcium ratio in 2
species of brown algae varied between 0.022 and 0.030. In 4
species of green algae and 4 species of red algae Sr:Ca was 0.005
to 0.009 and 0.005 to 0.006, respectively. Brown algae
accumulated Sr in pre ference to Ca from seawater.
2957.
Greig, R.A. and D.R. Wenzloff. 1978. Metal accumulation
and depuration by the American oyster, Crasssostrea
349
-------
v6rH~9i~~.
2: - 4.
Bull. Environ. Contamin. Toxicol.
Oysters from Beaufort, North Carolina, were held under
various conditions in natural seawater from Milford Harbor,
Connecticut. Natural Beaufort populations contained <0.16 mg
Ag/kg wet wt, <0.28 for Cd, 8.4 for Cu, and 515 for Zn. After 11
days, oysters contained <0.15 to 0.36 mg Ag/kg wet wt, 0.43 to
0.66 mg Cd/kg, 10.7 to 29.3 mg Cu/kg, and 281 to 563 mg Zn/kg;
metal concentrations after 22 days were 0.49 to 1.00 Ag, 1.0 to
1.5 Cd, 18.4 to 41.6 Cu, and 346 to 410 Zn. Lowest Ag, Cd, and Cu
levels were found in tanks with muddy sediments; these sediments
contained <2.5 mg Cd/kg dry wt, 180 Cu, and 108 Zn. Maximum metal
levels in oysters were from tanks with unfiltered seawater.
Oysters transferred to Milford Harbor water for 42-48 weeks did
not depurate metals. Cu decreased in unfiltered water and Ag
decreased in filtered water, but most metals stayed constant or
increased. Only Cu at week 27 was significantly lowered in
oysters transferred to uncontaminated water at Beaufort, N.C., for
40 weeks, indicating that specimens retained their metal content
even when in relatively unpolluted water.
2958.
Gupta, A.B. and A. Arora. 1978. Morphology and physiology
of Lyngbya nigra with reference to copper toxicity.
Physiol. Plant. 44:215-220.
Effect of copper sulphate exposure for up to 8 days on
morphology and physiology of the alga, ~. nigra, was studied.
Growth was inhibited in all treatments of 0.1 to 20.0 mg/l copper
sulphate. There were no apparent morphological changes to 0.2
mg/l or during the first two days of treatment in higher
concentrations of copper sulphate. In concentrations >0.2 mg/l,
the first symptom of toxicity was the formation of many separation
discs. Trichomes contracted longitudinally and cells became
swollen and constricted at the cross walls. Cells also became
yellowish due to loss of photosynthetic pigments. In 2.0 mg/l and
above, vacuoles appeared in large numbers, indicating the moribund
state of cells. Copper sulphate increased respiration at 0.5
mg/l, with greatest effect observed in 2.0 mg/l after 96 hrs.
Inhibition of photosynthesis was detectable in 0.2 mg/l, and 100%
inhibition took place in 2.0 mg/l after 96 hrs. In higher
concentrations a conspicuous inhibition of photosynthesis was
observed within 10 min. Copper content of the alga increased with
increased concentration of copper sulphate while potassium content
decreased over 192 hrs. Copper concentration rose from 8.0 to
12.7 mg/kg dry wt and K declined from 19.7 to 17.4 mg/kg dry wt as
350
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CuS04 exposure increased to 20.0 mg/l from controls. Greatest
comparative increase of Cu absorption from water was in 0.5 and
1.0 mg/l. Authors concluded that changes in physiological
activity of the alga under treatment were closely linked with
marked changes in morphology.
2959.
Hamada, M., Y. Inamasu, and T. Ueda. 1977. On mercury and
selenium in tuna fish tissues - III. mercury
distribution in yellowfin tuna. Jour. Shimonoseki
Univ. Fisheries 25:213-220. (In Japanese, English
abstract and table subtitles).
Distribution of mercury in various tissues of Thunnus
albacares was investigated. Mean concentrations of total mercury
in muscle from all parts of tuna ranged from 0.14 to 0.37 mg/kg
wet wt and methylmercury ranged from 0.13 to 0.34 mg/kg. Total
mercury concentration was low in fins, scales, vertebrae, and
cartilage; maximum level in these tissues was 0.04 mg Hg/kg.
Tissues containing ;:0.10 mg/kg total Hg in some samples included
gills, heart, liver, spleen (with a maximum of 2.1 mg Hg/kg),
kidney, stomach, intestine, pyloric caeca, sinew, skin, and
intestinal content of sardine, shrimp and squid. The ratio of
methylmercury to total Hg in muscle was nearly 1: 1.
2960.
Helmy, M.M., A.E. Lemke, P.G. Jacob, and B.L. Oostdam.
1978. Effects of some trace elements on the blood of
Kuwait mullets, Liza macrolepis (Smith). Jour. Exp.
Marine BioI. Eco~34:151-161.
Hemopathological changes attributed to heavy metal
poisoning were observed in blood smears of ~. macrolepis taken
after exposures of 96 hrs to graded doses, in mg/l, of copper
(0.11-1.80), lead (1.15-18.36), or mercury (0.04-0.59) in a
flow-through marine bioassay system. In general, changes in
leucocytic profile, of increasing eosinophil but not lymphocyte
percentage, appeared to be correlated with pathological changes
caused by increasing copper and mercury concentrations. In
contrast, blood samples of fish exposed to lead showed significant
polychromasia and anisocytosis regardless of concentrations. Red
blood cell count, hemoglobin content, and hematocrit were less
valuable in diagnosis of copper and mercury effects. LC-50 (q6
hr) values, in mg/l, were 1.43 for Cu, 14.61 for Pb, and 0.38 for
Hg. The manifestations of poisoning by trace elements resemble
pathological changes shown clinically and experimentally in
mammals. Consequently, blood measurements on marine organisms may
351
-------
be diagnostic of undesirably high levels of copper and mercury and
may constitute useful indicators of marine pollution.
2961.
Hetherington, J.A., D.F. Jefferies, N.T. Mitchell, R.J.
Pentreath, and D.S. Woodhead. 1976. Environmental and
public health consequences of the controlled disposal
of transuranic elements to the marine environment.
In: Transuranium nuclides in the environment. Int.
Atom. Energy Agen., Vienna. IAEA-S~199/11:139-154.
Experience from the controlled disposal of liquid
radioactive wastes from the nuclear power program of the United
Kingdom has shown that the only releases of transuranic elements
of potential environmental significance occur following fuel
reprocessing. In this context, plutonium, because of its long
half-life and high radiotoxicity, and the next most important
transuranic, americium, have been studied. Radiological
significance of these radionuclides following discharge to the
marine environment, in terms of both dose to man and to
environmental resources is reviewed. Both plutonium and americium
are found in each of the three compartments: water, seabed
sediment, and biota. The highest concentrations were found in
particularly fine mud in estuaries close the the Windscale
outfall. Radionuclide concentrations, in pCi/g wet wt, in 1974,
were 10 for Pu-238,239,240 and 5.0 for Am-241 in sediment, 1.0 and
1.0 in seaweed Porphyra, and 0.004 and 0.003 in fish muscle;
seawater contained 0.0002 pCi Pu/ml. Levels decreased in deeper
sediment and in biota further from the sources. Tissue levels in
the flatfish, Pleuronectes platessa, ranged from 0.0004 pCi
Pu-239,240/g wet wt in muscle to 0.088 in kidney, and from 0.002
pCi Am-241/g in muscle to 0.59 in liver. In crabs, Cancer
pagurus, concentrations ranged from 0.1 in muscle to 2.8 in gill
for Pu and from 0.6 in muscle to 7.9 in gill for Am. In mussels,
Mytilus edulis, levels were 1.6 for Pu and 3.9 for Am in visceral
mass. The public health significance of those biota which
represent potential human exposure pathways was evaluated and
estimates of the dose rate to critical groups from current
discharges were made. In parallel studies, attention was focused
on exposure of fish and shellfish stocks. Dose rates were
estimated by use of environmental data on contamination levels
combined with simple dosimetry models.
2962.
Hrs-Brenko, M., C. Claus, and S. Bubic. 1977. Synergistic
effects of lead, salinity and temperature on embryonic
development of the mussel Mytilus galloprovincialis.
Marine Biology 44:109-115.
352
-------
Combined effects of lead, salinity and temperature on
embryonic development of mussels were studied under laboratory
conditions. The basic experimental design was a 4 x 6 factorial
e~eriment using 4 lead concentrations (100, 250, 500 and 1000 ug
Pb +/1) and 6 salinity levels (from 25 to 37.5 0/00 with 2.5
0/00 intervals). These factorial studies were conducted at 3
constant temperatures (15, 17.5 and 20 C). Statistical analysis
indicated that salinity changes have more effect on embryonic
development than temperature. Optimal development was observed at
34.8 0/00 and 15.6 C, which is in accordance with observations in
the field. The effect of lead was minimal in optimal salinity and
temperature conditions. The deleterious effect of lead on
embryonic development was especially conspicuous at 20 C. Since
in nature spawning occurs at temperatures lower than 20 C, lead
will probably not drastically decrease the potential recruitment
of mussel spat in littoral populations of the northern Adriatic
Sea, where salinity of the water is relatively stable. Under
experimental conditions, lead caused a delay or inhibition of
embryonic development with occurrence of a large number of
abnormal larvae.
2963.
Ireland, M.P. 1977. Lead retention in toads Xenopus
laevis fed increasing levels of lead-con~nated
earthworms. Environ. Pollution 12:85-92.
Toads were fed, at a fixed rate, live earthworms
containing 10, 308, and 816 mg/kg wet wt lead. All six toads in
each group were killed after 4 or 8 weeks and the tissues analyzed
for lead. The highest concentration of dietary lead had no
significant effect on growth rate, hemoglobin, hematocrit or
reticulocyte values, but it did significantly affect levels of
delta-aminolevulic acid dehydrase. There was significantly less
lead in bone, skin, kidney, and liver in toads on a low lead diet
compared with toads on higher lead diets; there was no significant
difference in muscle lead. Individual organ analysis, within
groups, showed high levels of lead in kidney, bone and liver, but
ICM lead values in skin and muscle. The ratio of bone lead
concentration to kidney, liver and muscle lead, compared with deer
mice, showed more lead was deposited in soft tissues of toads.
Author suggests that toads present a relatively high lead
pollution hazard in the food chain.
2964.
Ireland, M.P. and R.J. Wootton. 1977. Distribution of
lead, zinc, copper and manganese in the marine
gastropods, Thais lapillus and Littorina littorea,
353
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around the coast of Wales.
12: 27 -41.
Environ. Pollution
Two species of marine gastropods were taken in August
1974 from 9 sites around the coast of Wales and analyzed for Pb,
Zn, Cu, and Mn. Significant species and site differences could be
detected and are discussed in relation to known polluted areas and
species specificity for metals. Site X species interactions were
inconsistent. Metal content of whole bodies, in mg/kg dry wt, of
Thais from each site ranged from 492 to 2355 for Zn, 166 to 458
for Cu, 5.9 to 17.3 for Mn, and 3.9 to 19.6 for Pb; in Littorina,
levels ranged from 92 to 186 for Zn, 43 to 249 for Cu, 19 to 60
for Mn, and 4.0 to 15.0 for Pb. Tissue metal analysis of
specimens from selected areas showed high levels of zinc and
copper in digestive gland/gonad of Thais (up to 761 mg Zn/kg zinc
and 554 mg Cu/kg) compared with Littorina (134 Zn, 92 Cu), and
high levels of manganese in digestive gland/gonad of Littorina (up
to 104 mg/kg) compared with Thais (8.5 mg/kg). Highest level of
lead in both species was found in shell, at 45 mg Pb/kg for Thais
and 42 for Littorina. Manganese was greater in shells of
Littorina (up to 8.3 mg/kg) than in Thais (4.2 mg/kg). Results
are discussed in relation to possible food source and mineralogy
of shell, together with the presence of specific enzyme systems.
2965.
Itazawa, Y. and J. Koyama. 1978. Effects of oral
administration of cadmium on fish - III comparison of
the effects on the porgy and the carp. Bull. Japan.
Soc. Sci. Fish. 44:891-895. (In Japanese, English
abstract) .
Porgy, Pagurus major, of 73 g, were fed for 113 days
diets containing 0.0, 37.5, 150, or 375 mg/kg dry wt of cadmium.
There was no decrease in serum calcium and vertebrae Ca, or of
scoliosis, all of which were noticed in carp fed diets containing
~140 mg Cd/kg for 30 days. Alkaline phosphatase activity and
magnesium concentration in serum, and phosphorus and magnesium in
vertebrae all increased slightly in porgy fed 375 mg Cd/kg. Total
amount of Cd administered per 100 g of fish through the feeding
period was 42.4 mg for porgy on 375 mg/kg Cd-feed, and 3.8-5.6 mg
for carp fed on 140 mg/kg. Cd contents, in mg/kg, in porgy fed
375 mg Cd/kg were 0.0 in muscle and gills, 64 in digestive tract,
146 in hepatopancreas, and 164 in kidney. Cd levels in carp fed
150 mg Cd/kg were 0.0 muscle, 0.6 spleen, 139 digestive tract, 14
hepatopancreas, and 52 kidney. That porgy, a marine teleost, did
not suffer from low calcium and vertebral abnormalities even when
administered 7 to 11X more Cd than carp, is considered to be
354
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due partly to calcium that carp derived from the environmental
medium.
2966.
Jasper, P. and S. Silver. 1978. Divalent cation transport
systems of Rhodopseudomonas capsulata. Jour.
Bacteriology 133:1323-1328.
~.-? Sep~rate transport systems for energy-dependent uptake
of ~~+ and Mn + were found with aerobically,
heterotrophically, and photosynthe~ically grown cells of B.
capsulata. The maximum rate of ~+ uptake differed be~w~en
photosynthetic and aerobic cells, while the Km for the MgC+
transport system was constant. Photosynthekic midlog-phase cells
eXHibited Km's for uptake of about 55 uM ~+ and 0.5 uM
Mn +. The Vmax's also differed between the tw~ systems: 0.6
to 1.8 umol/min per g2(dry wt) of cells for ~+, but only 0.020
umol/min per g for Mn +, distinguishing between a
"macro-requirement" system and a system functioning at trace
nutrient levels. Calcium was not normally taken up by intact
cells of B. capsulata. However, ch~matophore membranes isolated
from photosynthetic cells took up Ca + by an energy-dependent
process.
2967.
Johnson, D.L. and R.M. Burke. 1978. Biological mediation
of chemical speciation. II. arsenate reduction during
marine phytoplankton blooms. Chemosphere 8:645-648.
The thermodynamically unfavorable arsenite form,
As3+, occurs in seawater to a much greater extent than can be
accounted for by thermodynamic equilibrium. Accordingly, authors
formulated a temporal steady state model balancing chemical,
biological, and physical forces to explain its existence there.
Since elements, including As, with sufficient biological
involvement change in chemical speciation due to changes in
"suitable" biological parameters of an ecosystem, authors
determined chemical speciation of arsenic in water column during a
winter-spring diatom bloom in Narragansett Bay, R.I. Populations
of phytoplankton, Skeletonema costatum, had a peak of 10,000
cells/ml in November 1976 and a higher peak of 30,000 cells/ml in
March 1977. Total arsenic in water remained relatively constant
at about 975 ng/l from Nov. to April. Arsenite water levels
in~reas~ relative to arsenate during the winter-spring bloom;
As +:As + ratios generally increased from 0.02 to 0.08. Ratio
of orthophosphate to arsenate ~d corresponding decreases at algal
blooms, showing a decrease in P +. Rate of arsenate transport
355
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by uptake systems in algae will increase as P/As5+ ratio falls,
since arsenate competitively inhibits phosphate uptake. Arsenite
production reached 2.25 to 3.38 ug/l between days 10 and 40 for
Skeletonema grown with 3.98 ug/l arsenate and phosphate
concentrations of 370 to 1580 ug/l; higher As3+ peaks appeared
sooner in higher P levels.
2968. Kallqvist, T. and B.S. Meadows. 1978. The toxic effect of
copper on algae and rotifers from a soda lake (Lake
Nakuru, East Africa). Water Research 12:771-775.
The effect of Cu2+ ions on the photosynthetic oxygen
production of phytoplankton, the growth rate of the blue-green
algae Spirulina platensis and the population of rotifers
Brachionus sp. in water from Lake Nakuru in Kenya was
investigated. Within 8 days, the photosynthetic production was
reduced to 80% of control by addition of 0.1 mg Cull and 50% by
0.15-0.20 mg Cull. Growth rate of Spirulina was more affected by
copper than photosynthesis of phytoplankton. Addition of 0.05 mg
Cull reduced growth rate to about 40% of control. Rotifers were
less sensitive to copper than the algae; but after 8 days exposure
to 0.5 mg Cull or more the population was reduced to 0-4
specimens/ml compared to 35-51/ml in lesser Cu concentrations.
2969.
Korda, R.J., T.E. Henzler, P.A. Helmke, M.M. Jimenez, L.A.
Haskin, and E.M. Larsen. 1977. Trace elements in
samples of fish, sediment and taconite from Lake
Superior. Jour. Great Lakes Res., Internat. Assn.
Great Lakes Res. 3:148-154.
Concentrations of Cu, Zn, Mn, Na, As, Hg, Co, Sc, Cd,
Se, Fe, Cr, and 15 rare-earth elements were determined in samples
of flesh and liver from two species of sculpin, sediment, and
taconite tailings. The samples were from areas of Lake Superior
with high and low concentrations of taconite tailings. Sediment
from the top 2 cm to a depth of 41 cm contained metal
concentrations, in mg/kg, ranging from 6 to 109 for As, 60 to 115
for Ce, 18 to 25 for Co, 70 to 150 for Cr, 40 to 72 for Cu, 51,000
to 202,000 for Fe, 12 to 24 for Ga, 635 to 2300 for Mn, 7250 to
14,300 for Na, 28 to 49 for Nd, 9 to 17 for Sc, and 80 to 160 for
Zn; Dy, Er, Eu, Gd, Hf, Ho, Lu, Sm, Tb, and Yb levels were all <10
rng/kg. Concentrations of all elements, except Mn, in 0-2 em
sediment samples were lower than samples at 16-17.5 cm and 37-41
cm; samples at 3.5-3.7 cm had lowest concentrations for all metals
except As, Fe, and Mn. Only As and Mn concentrations in taconite
356
-------
tailings were higher than in sediment. The low concentrations of
most trace elements in taconite and the similarity of their
concentration ratios show that no elements measured in taconite
are suitable for use as tracers to determine movement and
distribution of taconite tailings in Lake Superior. No
significant differences were found in trace element concentrations
in sculpin from the site affected by taconite tailings compared to
those not affected. Maximum metal concentrations, in mg/kg wet
wt, in sculpins Cottus cognatus and Myoxocephalus quadricornis
from all sites were, in flesh, 0.02 for Co, 0.76 for Cu, 0.63 for
Mn, 790 for Na, 12.3 for Zn, 0.12 for As, 0.02 for Cd, 0.35 for
Hg, 0.59 for Se, and between 0.0002 to 0.0027 for Ga, La, Sb, Sc,
and Sm. Sculpin liver contained maximum levels, in mg/kg wet wt,
of 0.14 for Co, 3.7 for Cu, 1.4 for Mn, 1360 for Na, 39 for Zn,
0.59 for As, 0.81 for Cd, 0.28 for Hg, 1.7 for Se, and between
0.0007 to 0.0045 for Ga, La, Sb, Se, and Sm.
2970.
Kotani, H., A. Shinmyo and T. Enatsu. 1977. Killer toxin
for sake yeast: properties and effects of adenosine
5'-diphosphate and calcium ion on killing action.
Jour. Bacteriology 129:640-650.
The killer character of a strain isolated from the main
mash of sake brewing which produces a killer substance for sake
yeast was transmitted to hybrids of the strain and a standard
strain of Saccharomyces cerevisiae. The character was eliminated
at 41 C by incubation followed by growth at 30 C. The killer
strain produced the killer toxin in a growth-associated manner. A
preparation of crude killer toxin extract showed first-order
inactivation and a linear Arrhenius plot between 25 and 40 C, with
an activation energy of 55.0 kcal/mol. Addition of 1% of
synthetic polymer protected the toxin from inactivation by
agitation but not by heat. Enhancement of the killer action
toward sensitive yeast cells by only the nucleotide adenosine
5'-diphosphate (ADP) was observed after plating on agar medium as
well as after incubation in liquid medium. The addition of
CaCl2 reversed the enhancing effect of ADP on killing activity.
This action of CaCl2 was inhibited by cycloheximide, suggesting
the protein synthesis is required for recovery of toxin-induced
cells in the presence of CaCI2. Further, CaCl2 overcame the
decrease in the intracellular level of adenosine 5'-triphosphate
(ATP) enhanced by ADP in killer-treated cells and also inhibited
leakage of ATP from the cells with iITlnediate response. The mode
of killing action is discussed in terms of a transient state of
the cells and the action of ADP and CaCI2.
357
-------
2971 .
Kumagai, H. and K. Saeki. 1978. Contents of total
mercury, alkyl mercury and methyl mercury in some
coastal fish and shells. Bull. Japan. Soc. Sci. Fish.
44:807-811. (In Japanese, English summary).
Average total mercury levels, in mg/kg wet wt, in
edible portions of marine organisms collected near Yamaguchi were
0.069 for 30 species of fish, 0.078 for 4 species of crustaceans,
0.058 for 3 species of cephalopod molluscs, and 0.041 for 5
species of bivalve and gastropod molluscs. Wide within-group
variation occurred for total mercury. No lower alkylmercuric
compounds were detected, except methylmercury. Authors suggest
that content of lower alkylmercury coincides with methylmercury in
uncontaminated coastal water samples. Mean concentrations of
methylmercury in edible portions were 0.046 mg/kg for fish, 0.009
for crustaceans, 0.025 for cephalopods, and 0.008 for bivalves and
gastropods. Ratios of methylmercury to total mercury were 0.67,
0.46,0.70, and 0.18 for respective groups.
2972.
Labat, R., C. Roqueplo, J.~. Ricard, P. Lim and M.
Burgat. 1977. The ecotoxicological action of some
metals (Cu, Zn, Pb, Cd) on freshwater fish in the river
Lot. AnnIs. Limnol. 13:191-207. (In French, English
abstract) .
Poisoning of fish by heavy metals (Cu, Zn, Pb, and Cd)
is most common in populations downstream from the source of
pollution. In downstream zones, there is a passive accumulation
of metals by fish related to the low concentration of these metals
in water. Water at 9 stations along the river contained trace to
0.03 mg Cull, 0.03 to 3.1 mg Zn/l, trace to 0.09 mg Pb/l, and
trace to 0.24 mg Cd/l. Metal concentrations in muscle of 15
fishes (Lucio~erca lucioperca, Esox lucius, Micropterus salmoides,
Perca fluviatllis, Lepomis gibbosus, Leuciscus leuciscus, L.
cephalus, Rutilus rutilus, Scardinius erythrophtalmus, -
Chondrostoma toxostoma, Alburnus alburnus, Gabio gobio, Ciprinus
carpio, Barbus barbus, and Tinca tinca) at these stations ranged
from 2. 0 to 7i. 0 mg Cu/kg, 15 . 8 to 75.5 for Zn, O. 1 to 1. 6 for Pb,
and 0.04 to 18.0 for Cd. Maximum values were found at the 5 sites
furthest downstream from the contamination source. Because fish
accumulate metals from water, authors suggest that there should be
three critical thresholds for the content of metals in water, each
one affecting a different physiological process. Contamination
with metals affected absorption through gills and food absorption
with a gradient through the gut.
358
-------
2973.
Lande, E. 1977. Heavy metal pollution in
Trondheimsfjorden, Norway, and the recorded effects on
the fauna and flora. Environ. Pollution 12:187-198.
During 1972-73, molluscs (Mytilus ~dulis, Patella
vulgata), crustaceans (Carcinus maenas) and seaweeds (Ascophyllum
nodosum, Fucus vesiculosus, Pelvetia canaliculata) from the
intertidal zone, and pelagic and bottom-dwelling fishes (Gadus
spp., Anarchichas lupus, Clupea harengus, Macrurus rupestris,
Chimaera monstrosa, Glyptocephalus cynoglossus, Galeus melastomus,
Ar entina silus, Etmoterus spinax) were sampled. Seabirds
Somateria mollissima, Larus fuscus fuscus) were collected in the
fjord and from adjacent areas. Kidneys, liver, pectoral
musculature and eggs (white and yolk) of these birds were
analyzed. All samples were analyzed for cadmium, copper, iron,
nickel, chromium, silver, zinc and mercury. Heavy metal pollution
was found in two distinct areas of the fjord. Qualitative and
quantitative changes in the faunal assemblages of these two areas
are described.
2974.
Livingston, H.D. and V.T. Bowen. 1976. Americium in the
marine environment - relationships to plutonium. In:
Miller, M. W. and J .N. Stannard (eds.). Environmental
toxicity of aquatic radionuclides: models and
mechanisms. Ann Arbor Sci. PubIs., Inc. :107-130.
The behavior of Am-241 in the marine environment, and
by analogy other transplutonium nuclides, is compared and
contrasted with that of Pu-239,240. Radiochemical data for these
nuclides in seawater, sediments, and organisms contaminated mostly
by global fallout, are used to generate the ratio
Am-241/Pu-239,240, used as an index of fractionation between
plutonium and americium. The average value for this ratio, 0.20,
found in shallow nearshore sediments is proposed as representative
of integrated, unfractionated fallout at mid-latitudes in the
Northern Hemisphere by mid-1973. No fractionation between Am and
Pu has been found in these sediments, even under conditions when
they are being lost from the sediment following upward vertical
migration. Higher ratios in deep ocean water and sediments
suggest that americium sinks more quickly than plutonium in the
water column. Data reported for some marine organisms, mostly
algae but also plankton, corals, clams, and fish, suggest that
while americium may frequently be concentrated to a degree similar
to plutonium, some organisms may discriminate against, and others
in favor of, americium relative to plutonium. Authors measured
ratios of Am-241/Pu-239,240 ranging from 0.04 to 0.23 in the algae
359
-------
Sargassum sp., Fucus vesiculosa, Desmaidetta sp., Daisia sp., and
Chondrus crispus from the Massachusetts coast, and 0.10 in
starfish, Asterias forbesi, 0.15 in urchin (Strongylocentrotus
drobachiensis) spines, and 0.29 in winkle (Buccinum undatum)
shells.
2975.
Luoma, S.N. and G.W. Bryan. 1978. Factors controlling the
availability of sediment-bound lead to the estuarine
bivalve Scrobicularia plana. Jour. Marine BioI. Assn.
U.K. 58:793-~02.
Concentrations of lead in soft tissues of the
deposit-feeding clam, ~. plana, were canpared with physicochemical
characteristics of sediments in 20 estuaries in southern and
western England and one in northwest France. Biological
availability of lead in sediment is controlled mainly by the
concentration of iron. Lead concentration in bivalves may be
predicted from the Pb/Fe ratio in 1 N HCl acid extracts of surface
sediments. Maximum tissue lead of 1000 mg/kg dry wt was found in
clams collected from sediments containing maximum Pb at slightly
over 1000 mg/kg, high Fe at 6000 mg/kg, and maximum
Pb(mg/kg)/Fe(g/kg) ratio of almost 200.
2976.
Matthiessen, P. and A.E. Brafield. 1977. Uptake and loss
of dissolved zinc by the stickleback Gasterosteus
aculeatus L. Jour. Fish Biology 10:399-410.
Uptake and loss by sticklebacks of both stable zinc and
Zn-65 in hard and soft water were studied for periods up to 400
hr. In calcium-free water, the Zn-65 uptake curve is
approximately asymptotic over a period of 24 hr, while in hard
water internal Zn-65 levels begin to drop by 24 hr. Over 5 hr,
however, fish in hard tapwater absorb about 3.5 times more Zn-65
than those in calcium-free water. There is a positive linear
relationship between log Zn-65 uptake and log wet wt of fish.
Whole body concentration factors (CF) at 16 hr reach a maximum of
12.2 (mean = 2.9), with the highest concentrations of Zn-65 found
in the gills (mean CF = 5.1) and the lowest concentrations in
gonads (mean CF = 0.8). Over longer periods (400 hr), ~nternal
stable zinc levels of fish exposed to 1.0 and 4.0 mg Zn +/1
remain slightly higher (max 28%) than controls. Zn-65 efflux into
zinc-free water falls to zero after 5 hr, more zinc (78%) being
lost after uptake in tapwater than in Ca-free water (56%).
360
-------
2977.
Maxbnov, V.N. 1977. Specific problems in studyies (sic)
of pollutants combined action on biological systems.
Gidrobiologicheskii Zhurnal 13(4):34-45. (In Russian,
English summary).
Problems associated with toxicity of mixtures of
ZnC12 and ~cr04 to marine alga, including Skeletonema
costatum, CEaetoceros wighamii, Dynobrion pellucidum, GYmnodinium
arcticum, and diatoms Nitzschia spp. were investigated.
2978.
Merlini, M. and G. Pozzi. 1977- Lead and freshwater
fishes: part I - lead accumulation and water pH.
Environ. Pollution 12:167-172.
The accumulation of lead-203 by the sunfish, Lepomis
gibbosus, an edible freshwater teleost, was investigated at pH 7.5
and pH 6.0. At the lower pH, fish concentrated almost 3X more
lead than at the higher pH. Maxbnum Pb-203 accumulations were
observed in gills, fins and liver; minimal accumulations in
muscle; and intermediate accumulations in skin and scales, head,
and bone. The sites of lead concentration, however, were not
al tered by change in water pH.
2979.
Mitchell, N.T. 1977. Radioactivity in surface and coastal
waters of the British Isles, 1976. part I. the Irish
Sea and its environs. Tech. Rep. Fish. Radiobiol.
Lab., MAFF Direct. Fish. Res., (FRL 13) Lowestoft:15
pp.
Measurements of radioactivity of Am-241, Ce-144,
Cs-134, Cs-137, Pa-234m, Pu-239+240, Ru-106, and Zr-95/Nb-95 were
recorded in seawater, sedbnents and biota including algae,
crustaceans, bivalve and gastropod molluscs, and fish from various
locations in the Irish Sea in 1976. Maximum individual public
radiation exposures from disposals of liquid radioactive wastes,
as % of ICRP-recommended dose limit of 33 millirem/person/yr,
were: 44% from fish and shellfish at Windscale Nuclear Fuel
Limited, 8% from external dose at Windscale, 0.2% from Porphyra
seaweed-laverbread pathway at Windscale, and <1.0% of exposure
limits at Springfields and Chapelcross Nuclear Fuel Limited
outfalls. Wylfa Electricity Generating Board discharge accounted
for < 0.1% of dose limit.
361
-------
2980.
Mitra, R.S. and I.A. Bernstein. 1978. Single-strand
breakage in DNA of Escherichia coli exposed to Cd2+.
Jour. Bacteriology 33 :75-80. -
When a growing culture of E. coli was exposed to 3 x
10-6 M Cd2+ (about 0.34 mg Cd/I), 85 to 95% of the cells lost
their ability to form colonies on agar plates. Loss of viability
was accompanied by considerable single-strand breakage in the DNA,
with no detectable increase in double-strand breaks. A direct
correlation exists b~tween number of single-strand breaks and the
concentrations of Cd + to which ~he cells were exposed.
Exposure of DNA in vitro to a Cd + concentration of 3 x 10-6M
or higher, followed by sedimentation in alkaline sucrose
gradients, demonstrated no single-strand break~. Cadmium-exposed
cells recovered viability when incubated in Cd +-free liquid
medium containing 10 mM hydroxyurea. During the early period of
recovery, there was a lag in the incorporation of labeled
thymidine, but cellular DNA, at least in part, appeared to be
repaired.
2981 .
Muller, G. 1978. Strontium uptake in shell aragonite from
a freshwater gastropod. Naturwissenschaften 65:434.
Mean distribution coefficients relating Sr/Ca ratios in
shell aragonite to Sr/Ca ratios in water ranged from 0.233 to
0.282 for gastropod molluscs of the genera Lymnaea, Planorbis,
Bithynia, and Valvata in Lake Constance, Germany. Distribution
coefficients ranged from 0.307 to 0.378 in pelecypod molluscs
Anodonta, Sphaerium, and Pisidium. Coefficients of Sr/Ca ratios
averaged 0.252 in all gastropods and 0.348 in all pelecypods.
2982.
Murphy, B.R., G.J. Atchison, A.W. McIntosh and D.J. Kolar.
1978. Cadmium and zinc content of fish from an
industrially contaminated lake. Jour. Fish Biology
13: 327 -335.
Eleven species of fish from the industrially-
contaminated Palestine Lake were analyzed for whole body cadmium
and zinc. Species were bluegill Lepomis macrohirus, redear L.
microlophus, warmouth~. gulosus, orangespot sunfish~. humilus,
largemouth bass Micropterus salmoides, black crappie Pomoxis
nigromaculatus, golden shiner Notemigonus crysoleucas, white
sucker Catostomus commersoni, brown bullhead Ictalurus nebulosus,
bowfin Amia calva, and yellow perch Perca flavescens. Most
species accumulated Cd and Zn to levels significantly higher
362
-------
than background. At the electroplating plant discharge, water
levels were 17.3 ug/l dissolved Cd, 30.3 ug/l suspended Cd, and
293 and 270 ug/l dissolved and suspended Zn. Sediment contained
800 mg Cd/kg dry wt and 12,800 mg Zn/kg. Mean metal content in
fish collected near the discharge ranged from 0.06 to 8.0 mg Cd/kg
dry wt, with an individual maximum of 13.6 in bluegill, and from
80 to 477 mg Zn/kg dry wt, with a maximum of 820 in redear. Away
from the discharge, water levels, in ug/l, were 0.9 dissolved Cd,
0.3 suspended Cd, 52.4 dissolved Zn, and 5.2 suspended Zn.
Concentrations in sediments, in mg/kg dry wt, were 4.4 Cd and 320
Zn; and body levels in fish, in mg/kg dry wt, ranged from below
detection to 0.21 for Cd, and 79 to 139 for Zn. Cadmium content
was much more variable than zinc. Distributions of concentrations
of both cadmium and zinc in fish were lognormal, and
concentrations of both metals tended to decrease in higher trophic
levels. Zinc concentrations significantly decreased as total
length increased in three species.
2983.
Ociepa, A. and M. Protasowicki. 1976. A relationship
between total mercury content and a kind of food in
some chosen Pacific fish species. Marine Fishing Food
Technol. 60:83-87. (In Russian, English Summary).
Mercury determinations in 5 species of Pacific
foodfish: Trachurus sYmmetricus, Theragra chalcogramma,
Merluccius productus, Hypomesus pretiosus, and Sebastes sp.,
caught off the western coast of the USA are presented. Mercury
content varied in flesh of the species examined, from 0.0 to 1.9
mg/kg, but the average never exceeded 0.3 mg/kg wet wt for
individual species. Mercury in planktophagous and predatory
fishes were different and suggests an increasing accumulation of
Hg in consecutive links of trophic chains.
2984.
Pascoe, D. and P. Cram. 1977.
the toxicity of cadmium to
Gasterosteus aculeatus L.
10:4b7-472.
The effect of parasitism on
the three-spined stickleback
Jour. Fish Biology
Toxicity of cadmium to sticklebacks was determined over
a wide range of concentrations. LC-50 (96 hr) was 6.5 mg Cd/I.
The shape of the time-concentration curve suggests that cadmium
may have two toxic mechanisms. The median period of survival for
fish infected with the plerocercoids of the cestode,
Schistocephalus solidus, was found to be considerably shorter than
for non-parasitized fish. This observation is considered in the
363
-------
light of known effects of S. solidus on its host.
2985.
Paul, A.C. and K.C. Pillai. 1978.
river. Water, Air, Soil Poll.
Pollution profile of a
10:133-146.
A host of chemical industries subject the Periyar River
in south India to pollutants such as acids, bases, trace metals
and radionuclides. Proximity of different outfalls and poor
lateral mixing in the river are responsible for high local aquatic
concentrations. Scavenging reactions, in situ, and sedimentation
of suspended matter result in accumulation-or-radionuclides near
the outfall area. Monsoon rains flush the river into the
backwater area, with translocation of sediments being the major
factor in pollutant transport. Relative concentration values of
metal concentrations at outfalls compared to background levels in
1974-75 were: Ra-288, 15 water and 500 sediment; Cd, >400 water
and >8750 sediment; Cu, 6.0 and 1.0; Hg, >23 and >3600; Mn, 180
and 4.0; and Zn, >3750 and 220, respectively. Sediment
concentrations of Ca, Co, Cr, Fe, K, Mg, and Ni were determined at
various sites before and after monsoons. Ra-228, Cd, and Hg are
preferentially concentrated in sediments, whereas Zn, Cu, and Mn
are concentrated in water. Levels of Ra-228, in uCi/kg, and Hg,
in mg/kg, in fish flesh were 0.15 and 0.1, respectively, in Aries
sp.; 0.14 and 0.2 in Clupea longicents; and 0.05 and 0.1 in
Etroplus sp. Etroplus viscera contained 2.2 uCi Ra-228/kg.
2986.
Pentreath, R.J. 1977. The accumulation of cadmium by the
plaice, Pleuronectes platessa L., and the thornback
ray, Raja clavata L. Jour. Exp. Marine BioI. Ecol.
30:223-232.
Accumulation of cadmium-115m from both food (polychaete
worms Nereis sp.) and seawater by a flatfish, Pleuronectes
platessa, and thornback ray, Raja clavata, was studied in relation
to measured cadmium concentrations. Plaice accumulated cadmium
from seawater at a faster rate than rays, although concentration
factors attained by both species as a result of such direct
accumulation were very low. CF factors for plaice tissues after
59 days were 125 for gill filament, 115 for upper intestine, 46
for lower intestine, 16 for liver, 6 for stomach and <1 for skin,
muscle, and bone. CF for rays after 70 days were 9 for gill
filament, 3 for liver, and <1 for all other tissues. Both species
retained cadmium from food and accumulated it in the liver, with
rays accumulating more than plaice. Some evidence was found for a
positive linear relation between concentrations of cadmium in
364
-------
plaice liver and age, but not weight, of the fish.
2987.
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.
Highest concentrations of plutonium (Pu-238,-239,-240)
in the internal organs of fish (Pleuronectes platessa) collected
in February 1975 from the vicinity of a nuclear fuel reprocessing
facility was in kidneys. Fish caught later in the year exhibited
higher values for gut, and this was attributed to the low feeding
frequency in winter. Concentrations of Am-241 in the internal
organs were generally higher than those of plutonium. In any
event, the concentrations of Pu and Am isotopes measured in fish
muscle are equivalent to less than 0.01% of the derived working
limit, based on calculations using a dose limit to the public of 3
rem/year and maximum consumption rate of 300 g fish/day.
2988.
Rho, S. and C.K. Park. 1976. Studies on the propagation
of blue crab, Portunus trituberculatus (Miers) (1) the
survival of larvae stages to various salinities. Bull.
Fish. Res. Dev. Agency 15:43-56. (In Japanese,
English sunmary).
Survival of blue crab larval stages in different
salinity concentrations was observed. In salinity lower than 9
0/00 all zoeal larvae were dead after 48 hrs incubation. Survival
increased as salinity increased from 9 to 33 0/00. Above 21 0/00
S, approximately 70% of zoeae survived. Survival rates of
megalopa larvae were similar to zoeal larvae. The lowest survival
of 15 percent was observed at 12 0/00 S. Survival of young crab
stage 5 (ecdysis) was 90% at 9 0/00 salinity.
2989.
Rodsaether, M.C., J. Olafsen, J. Raa, K. Myhre, and J.B.
Steen. 1977. Copper as an initiating factor of
vibriosis (Vibrio anguillarum) in eel (Anguilla
anguilla) Jour. Fish Biology 10:17-21.
Eels (Anguilla anguilla) which were exposed to
copper-contaminated freshwater (30-60 ug Cull) died with symptoms
of vibriosis (Vibrio anguillarum). Eels kept in non-contaminated
365
-------
freshwater «6 ug Cull) remained healthy. V. anguillarum was
present in eels with symptoms of vibriosis.- Authors suggest that
Y... anguillarum is a common inhabitant of eels and that copper can
change a commensal association between fish and bacterium to one
of pathogenicity. Maximum concentrations of copper recorded in
tissues of eels surviving exposure to copper-contaminated water
for 50 days at 2 to 4 C were about 50 mg/kg wet wt in liver and
about 140 mg/kg wet wt in brain.
2990.
Schmidt, R.L. 1978. Copper in the marine environment -
part I. CRC Critical Rev. Environ. Control 8:101-152.
This compendium of the literature describing the
biogeochemistry of copper in the marine environment examines
abiotic and biotic factors that affect distribution and cycling of
copper in the marine ecosystem. Emphasis is placed on
transformations of copper by physicochemical processes and its
transfer between components within the ecosystem. The inorganic
and organic chemistry of copper in the marine environment are
discussed. A summary is presented of techniques for extracting
and concentrating copper from environmental samples and of
procedures for analytical measurement. Sources of copper to the
sea are identified and the concentrations and forms of copper are
given for seawater, suspended particulates, detritus, sediments,
and some marine organisms, such as plankton and molluscs,
collected throughout the world's oceans. A bibliography of about
870 titles is appended.
2991.
Schmidt, R.L.
part II.
1978. Copper in the marine environment -
CRC Critical Rev. Environ. Control 8:247-291.
This compendium of the literature (a bibliography of
about 400 articles is appended) describing the biogeochemistry of
copper in the marine environment, examines abiotic and biotic
factors that affect distribution and cycling of copper and
ecological implications of this metal in the marine ecosystem.
Emphasis is placed on transformations of copper by physicochemical
and biological processes; its transfer between components within
the ecosystem; and the availability, uptake and effect of copper
on marine biota. The inorganic and organic chemistry of copper in
the marine environment are discussed. Sources of copper to the
sea are identified and the concentrations and forms of copper are
given for seawater, suspended particulates, sediments, and some
marine organisms, including bacteria, phytoplankton, algae,
annelids, echinoderms, crustaceans, molluscs, and fish collected
366
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throughout the world's oceans. Seaweeds, polychaete worms,
mussels, and oysters appear to have fairly consistent Cu
accumulation factors and reflect environmental concentrations. Cu
is generally concentrated in digestive organs of most animals
except molluscs and arthropods, whose blood contains hemocyanin, a
Cu-protein. Uptake of copper by phytoplankton is probably an
active process, whereas seaweeds simply absorb metals. Dietary
uptake is the most important means of Cu accumulation for most
marine animals. Polychaetes directly adsorb Cu from sediment
interstitial water. Oysters bind the metal in gill mucous
sheets. Complexation of copper by nonviable cellular materials
reduces toxicity to bacteria and phytoplankton, and may regulate
Cu seawater levels. Some animals, particularly polychaetes and
fish, may influence the biogeochemistry of Cu in shallow estuaries.
2992.
Schulz-Baldes, M. and R.A. Lewin. 1976.
two marine phytoplankton organisms.
150: 118-127.
Lead uptake in
BioI. Bull.
Uptake of lead by diatoms, Phaeodactylum tricornutum,
and flagellate algae, Platymonas subcordiformis, exposed to lead
concentrations ranging from 0.02 to 0.8 mg/l occurs in two
phases. The first phase, completed within 10 minutes after
addition of lead, can be described by a Freundlich adsorption
isotherm. The number of binding sites per cell seems to be
limited. Cells of Phaeodactylum become "saturated" when lead
bUg den reaches 11,640 mg/kg dry wt, equivalent to about 6.7 x
10 Pb atoms per cell. In the second phase, lead content of
Platymonas cells continues to rise slowly, whereas that of
Phaeodactylum declines after two or three days. Addition of
0.000002 M EDTA to a solution containing 1.0 mg Pb/l completely
inhibits metal uptake by Phaeodactylum. When diatom cells,
pre-treated with lead, are resuspended in a higher concentration
of 0.01 M EDTA, much of the adsorbed lead is eluted. The longer
the pre-treatment period with lead, the less readily is the metal
removed from cells in this way. Since content of bound lead, i.e.
residual lead burden after EDTA extraction, increases with time in
both species, authors suggest that, during prolonged exposure to
lead solutions, metal ions are first adsorbed to the cell surface
and then translocated to within the cell wall, to plasma membrane,
and eventually to cytoplasm.
2993.
Shcherban, E.P. 1977. Toxicity of some heavy metal ions
for Daprmia magna Straus depending on temperature.
Gidrobiologisheskii Zhurnal 13(4):86-91. (In Russian,
English summary).
367
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Effect of cadmium, copper, manganese, nickel, and zinc
sulphates on 3- to 5-day fry and puberal females of Q. magna was
studied for 24, 48, and 72 hours at temperatures of 10, 15, 25,
and 30 C. Toxicity of each ion increased with increasing
temperature and length of exposure. Between 25 and 30 C, Cd
toxicity rose 3-4 orders of magnitude and Cu and Zn by 2 orders,
while Ni and Mn were only slightly more toxic.
2994.
Sheffy, T.B. 1978.
Wisconsin River.
Mercury burdens in crayfish from the
Environ. Pollution 17:219-225.
Mercury in abdominal muscle of crayfish, Orconectes
virilis, from the Wisconsin River ranged from 0.07 to 0.56 mg/kg
wet wt. Elevated Hg concentrations did not correspond with the
industrialized zone along the river. The pattern of mercury
accumulation in crayfish was similar to that of sediment, fish,
and mammals previously recorded along the Wisconsin River.
Crayfish, therefore, seem to be a useful indicator species of
mercury contamination along a river system, since crayfish are
easily obtained and provide a basis for organic mercury
accumulation for other species from the same area.
2995.
Shiber, J.G. and T.A. Shatila. 1978. Lead, cadmium,
copper, nickel and iron in limpets, mussels and snails
from the coast of Ras Beirut, Lebanon. Marine Environ.
Res. 1:125-134.
Limpets Patella coerulea, mussels Brachydontes
variabilis, snails Monodonta turbinata, and surface seawater were
collected at eight locations along the coast of Ras Beirut,
Lebanon, and analyzed for lead, cadmium, copper, nickel, and
iron. With the exception of cadmium, metal levels found in the
three molluscs appear to be high in relation to levels reported by
investigators from other coastal areas. Average values for lead,
cadmium, and nickel in these animals were quite similar, although
Patella had higher iron and lower copper content. Average metal
concentrations, in mg/kg dry wt, in soft parts of Patella were
37.8 for Pb, 2.5 for Cd, 22.8 for Cu, 40.1 for Ni, and 2685.0 for
Fe; concentrations in Brachydontes were 53.0, 1.6, 98.4, 37.0, and
517.0, respectively, and in Monodonta 31.8, 1.1, 87.1, 27.4, and
737.0, respectively. Average seawater levels were 0.36 mg Pb/l,
0.02 for Cd, 0.15 for Cu, 0.27 for Ni, and 8.1 for Fe.
368
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2996.
Singh, S.M. and P.N. Ferns. 1978. Accumulation of heavy
metals in rainbow trout Salmo gairdneri (Richardson)
maintained on a diet containing activated sewage
sludge. Jour. Fish Biology 13:277-286.
Trout were fed for 10 weeks with a nutritionally
balanced diet containing 30% by weight of activated sewage
sludge. The experimental diet contained 9.2 mg Cr/kg dry wt,
171.0 Mn, 2340.0 Fe, 5.4 Co, 61.0 Ni, 61.0 Cu, 167.0 Zn, 1.1 Cd,
38.0 Pb, 10,700.0 Ca, 1780.0 Mg, 798.0 Na, and 1690.0 K. Whole
body concentrations were determined at the beginning and end of
the experiment and at three intermediate stages. Fish fed the
diet containing sewage sludge had significantly elevated levels of
Cr, Fe, Ni, Pb, and reduced levels of Na and K after 70 days,
though the values obtained for all groups fell within the range
reported for uncontaminated fish. Chromium concentration in fish
was 3.6 mg/kg dry wt compared to 2.8 in controls, iron was 45.9
compared to 37.3, nickel was 0.63 vs. 0.33, and Pb was 0.78
compared to 0.45. Nickel and Zn showed a marked increase towards
the end of the experiment, suggesting that they might have
continued to rise after 70 days. Weight gain was 7.6% in
contaminated fish compared to 11.6% in uncontaminated fish.
2997.
Sodergren, S. 1976. Ecological effects of heavy metal
discharge in a salmon river. Fish. Bd. Sweden, Inst.
Freshwater Res., Drottningholm 55:91-131.
In the Ricklea River in northern Sweden, salmon Salmo
salar and to a lesser extent, trout Salmo trutta popoulations have
decreased since 1965, possibly due to pollution or failure of
spawning. Simultaneously, there was a decrease in abundance of
invertebrate fauna, especially winter nymphs of mayflies Baetis
rhodani and Ephemerella mucronata, and backfly larvae. A diamond
factory began operation in the upper river in 1963; nickel was
used from 1963 to 67 and cobalt since 1967. Lime addition did not
prevent metals from dissociating in the acidic river water. Heavy
metal consumption and discharge has increased each year; a
purification plant was installed i.n 1973. An electroplating plant
was in operation from 1964 to 69. Decreases in Salma populations
and invertebrate fauna were synchronous with activities at the
diamond factory. In 1972 and 73, cobalt water levels were highest
in autumn and winter, at 10 to 43 ug/l. Surficial sediment
concentrations of Co were 14 to 24 mg/kg below the discharge where
Fontinalis mass accumulated 770 to 820 mg Co/kg dry wt in 1973.
When 470 or 3950 ug/l cobalt nitrate was added to water, all
Ephemerella nymphs living on their natural substrate (Fontinalis),
369
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died within 2 wks. Mortality was also high and subimagine
emergence retarded in 32.6 ug Coil. In 5.2 ug Coil, weight of
subimaginates decreased and development was slightly retarded.
2998.
Speranza, A.W., R.J. Seeley, V.A. Seeley and A.
Perlmutter. 1977. The effect of sublethal
concentrations of zinc on reproduction in the
zebrafish, Brachydanio rerio Hamilton-Buchanan.
Environ. Pollution 12:217-222.
Adult zebrafish, when held in water containing a
threshold concentration (5 mg/l) of zinc for a 9-day period during
which the gametes were maturing, showed a delay in spawning. When
spawning did occur, experimental pairs of fish produced an average
of 165 eggs of which only 21% were viable. In contrast, controls
produced an average of 434 eggs of which 90% were viable. In
addition, survival of eggs to hatching was significantly lower in
exposed groups than in controls, survival rate for the
experimentals being 0.9%, vs. 63% in controls. Adverse effects of
zinc on zebrafish can be reversed by returning the fish to a
zinc-free environment.
Stahl, S. 1978. Calcium uptake and survival of Bacillus
stearothermophilus. Arch. Microbiol. 119:17-24.
Calcium transport in resting vegetative cells of B.
stearothermophilus was studied by determining retention of Ca-45,
in a membrane filter assay. Kinetics of death by vegetative cells
suspended in buffer at 55 C was also investigated. Calcium influx
required an energy source of glucose-1-phosphate and the system
exhibited saturation kinetics. Bacteria accumulated 40.1 mg Calkg
in one min in 240 mg Call. Requirements for survival of
thermophilic cells reflected those of the calcium transport
system. Cells treated with nitrogen gas showed an increased
thermal stability and a decreased efflux of calcium. The initial
velocity of calcium influx correlated linearly with survival of
cells after 1 min at 55 C. Lanthanum, and to a lesser extent
manganese and strontium, inhibited calcium influx and reduced
survival. Magnesium did not inhibit calcium influx, but could
replace calcium as a stabilizing agent. Results suggest that the
thermophilic cells are not intrinsically heat stable but survive
due to a high cellular concentration of divalent ions.
2999.
370
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3000.
Stancyk, S.E. and P.L. Shaffer. 1977. The salinity
tolerance of Ophiothrix an~lata (Say)
(Echinodermata:Ophiuroidea in latitudinally separate
populations. Jour. Exper. Marine BioI. Ecol. 29:35-43.
Q. angulata from an estuary in South Carolina were less
tolerant of reduced salinity than those from an estuary in
Florida. Animals from North Inlet, South Carolina, became
incapacitated more rapidly after exposure to a reduced salinity,
and were less able to recover after return to normal salinity.
This difference probably results from the more severe selection
for salinity tolerance at Cedar Key, Florida. The Florida estuary
has a lower average salinity (25 0100) than that in South Carolina
(30 0100), and has more frequent extended periods of reduced
salinity. The two populations are of different color varieties
and size, and there may be differences in breeding seasons as
well. The South Carolina and Florida populations of O. angulata
may, therefore, represent different races.
3001 .
Sunda, W.G. and J.A.M. Lewis. 1978. Effect of
complexation by natural organic ligands on the toxicity
of copper to a unicellular alga, Monochrysis lutheri.
Limnol. Oceanogr. 23:870-876.
The effect of copper on division rate of M. lutheri was
tested in media with different concentrations of natural organic
ligands from filtered river water. Increased binding of copper by
natural ligands was associated with decreased toxicity of a given
concentration of added CuS04' In 10% river water, algal cell
division rate decreased from 1.5 doublingslday with 0.5 ug Cull to
0.09 doublingslday with 210 ug Cull. However, in 90% river water,
division rate was 0.14 doublings/day in up to 635 ug Cull. The
decrease in copper toxicity with increasing complexation could be
explained quantitatively in terms of a dependency of toxicity on
the concentration of free cupric ion. Sixty-one to 99% of total
CuS04 added to river water was in the form of Cu-natural organic
complexes. These results indicate that complexation of copper by
organic ligands influences the toxicity of copper in natural
waters by complexing with free cupric ions.
3002.
Tagatz, M.E. and M. Tobia. 1978. Effect of barite
(BaS04) on development of estuarine communities.
Estuarine Coastal Marine Sci. 7:401-407.
Barite (BaS04)' the primary component of oil drilling
371
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muds, affected the composition of estuarine communities developed
from planktonic larvae in aquaria which contained sand and flowing
estuarine water. Various experimental aquaria contained: sand
only; a mixture by volume of 1 part barite and 10 parts sand; 1
part barite and 3 parts sand; or sand covered by 0.5 cm of
barite. For all environments, annelids and molluscs were the
numerically dominant phyla collected after 10 weeks exposure. A
total of 59 species of annelids, crustaceans, coelenterates,
echinoderms, molluscs, nemerteans, sipunculids, and tunicates were
collected. Significantly fewer animals and species developed in
aquaria with sand covered by barite than in aquaria unexposed or
exposed to 1 barite: 10 sand. Number of animals in aquaria
containing 1 barite:3 sand also differed from control aquaria.
Annelids were particularly affected and significantly fewer were
found in all exposures than controls. Molluscs decreased markedly
in number only in barite-covered aquaria. Barite, however, did
not impede growth (as height) of the abundant clam, Laevicardium
mortoni, or decrease abundance of other groups. It was concluded
that large quantities of barite discharged during offshore oil
drilling, may adversely affect colonization of benthic animals.
3003.
Takeda, M., Y. Inamasu, T. Koshikawa, T. Ueda, M. Nakano,
T. Tomida, and M. Hamada. 1976. On mercury and
selenium contained in tuna fish tissues - II. total
mercury level in muscles and viscera of yellowfin
tuna. Jour. Shimonoseki Univ. Fish. 25:47-65. (In
Japanese, English abstract).
Total mercury level and lipid content of 39 yellowfin
tuna, Thunnus albacares, from the Middle Pacific, the West
Pacific, and the East Indian Ocean were determined. Total mercury
in dark muscle and abdominal muscle was correlated to that in
dorsal muscle. Average levels in these tissues were almost the
same at 0.21 to 0.25 mg Hg/kg wet wt. Stomach contained an
average of 0.12 mg Hg/kg, liver contained 0.13, spleen 0.64, and
kidney 0.33; contents of stomach averaged 0.06 and intestine
0.05. Mercury in muscle, liver, stomach, and intestine contents
increased almost exponentially with body length. Relatively high
Hg concentrations of 0.40 to 0.59 mg/kg wet wt in muscle, 0.45 in
stomach, 0.50 in liver, 2.06 in spleen, and 0.53 in kidney were
recorded in tuna caught off Brisbane, Australia, or Lombok,
Indonesia. The major kinds of food species found in tuna stomach,
in quantitative order, were squid, sardine, horse mackerel, and
shrimp. Total mercury of each prey species was < O. 1 mg/kg, except
a sardine (0.17) and octopus (0.13) in a tuna from Lombok Island.
372
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3004.
Tevlin, M.P. 1978. An improved experimental medium for
freshwater toxicity studies using Daphnia magna. Water
Research 12:1027-1034.
Difficulties in formulating experimental media for use
in toxicity studies are indicated, with particular reference to
heavy metals and their possible chelation by agents in the media.
Physiological responses by Daphnia with green alga, Chlorella sp.,
to sublethal cadmium poisoning were investigated. The synthetic
media included labile Fe-EDTA complex as a source of soluble iron
which is essential for growth of both Daphnia and Chlorella.
Attention is drawn to the almost universal complexing ability of
EDTA with metal ions, and to mechanisms whereby EDTA may be
released from the Fe-EDTA complex under experimental conditions.
Synthesis of a ferri-gluconate complex as an alternative source of
soluble iron is described. This complex is theoretically more
iron-specific than Fe-EDTA, while providing equally well for
Chlorella growth and Daphnia growth and fecundity. Restriction of
pH variation in the experimental medium, within its chemically
stable range of 6.0-9.0, is difficult over 10 days. Most buffers
with a suitable pKa value (rv7.5) were toxic or had some
complexing ability. HEPES buffer at 0.001 M restricted pH
variation to within 0.5 pH units without adversely affecting
Chlorella growth or Daphnia growth and fecundity. Chemical
estimation of cadmium-complexing by each iron source and each
buffer was not possible since the presence of chelating agents
imposes restrictions on the methods available, particularly at low
cadmium concentrations. Instead, a 48-hr acute toxicity bioassay
of the reduction of Daphnia due to cadmium in media containing
each potential chelating agent was used. These data indicate that
0.001 M HEPES buffer does not complex cadmium at 0.1 mg/l, and
that ferri-gluconate is less likely to do so than ferri-EDTA. In
1.0 mg Cd/I, addition of 0.001 M or 0.002 M HEPES did not improve
Daphnia survival from 0%; with 0.002 M TES and 0.005 M TES,
respectively, about 25% and 60% of the specimens survived.
Survival in ferri-gluconate in 1.0 mg Cd/l was 30% and with
ferri-EDTA 50%.
3005.
Tucker, C.S. and C.E. Boyd. 1978. Consequences of
periodic applications of copper sulfate and simazine
for phytoplankton control in catfish ponds. Trans.
Amer. Fish. Soc. 107:316-320.
Treatment of channel catfish, Ictalurus punctatus,
production ponds with biweekly applications of 0.84 kg/hectare
copper sulfate was ineffective in reducing phytoplankton density
373
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over 5 months. Three days after each addition, Cu pond levels
were 10-18 ug/l; concentrations were 4.0-9.0 ug Cull after 10
days. Three periodic applications of simazine totaling 1.3 mg/l
drastically reduced phytoplankton density. However, extended
periods of low dissolved oxygen concentrations following simazine
applications resulted in decreased fish yields and poor conversion
ratios compared to control ponds. Catfish yield, in kg/hectare,
was 2640 for controls, 2720 for Cu-treated, and 2100 for
simazine-treated ponds.
3006.
Voyer, R.A., C.E. Wentworth, Jr., E.P. Barry and R.J.
Hennekey. 1977. Viability of embryos of the winter
flounder Pseudopleuronectes americanus exposed to
combinations of cadmium and salinity at selecte&
temperatures. Marine Biology 44: 117 -124.
Developing eggs of winter flounder were exposed to 9
combinations of cadmium (range 0.1 to 2.1 mg Cd/I) aDd salinity
(10, 20, 30 0/00) at 5 and 10 C. Overall mean times to 50% hatch
ranged from 7.7 days at 10 C, to 17.9 days at 5 C. Mean
percentages of total hatches ranged from 50 to 100% for all
treatment combinations. Percentages of viable hatches were
generally lowest at 10 0/00 S and highest in the 25 to 30 0/00 S
range. At both temperatures, cadmium significantly influenced
viable hatch in all experiments. Viable hatch was also
significantly influenced by salinity in both tests at 5 C and in 2
of 3 tests at 10 C. The interaction between cadmium and salinity
also significantly affected viable hatch at 10 C.
3007.
Waiwood, K.G. and F.W.H. Beamish. 1978. Effects of
copper, pH and hardness on the critical swimming
performances of rainbow trout (Salmo ~airdneri
Richardson). Water Research 12:611- 19.
Critical swimming velocities of trout at 12 C were
determined in different combinations of copper, pH and hardness
after exposure for 0.5, 5.0, 10.0, and 30.0 days. When copper was
not applied, hardness, pH and exposure time had no appreciable
effect an critical performance. Copper had the greatest effect on
swimming performance at 5 days of exposure at up to 200 ug Cull.
At pH 7.5-8.0, recovery from the initial depression was complete
after 10 days of exposure. However, critical swimming performance
did not return to control levels in pH 6.0 treatments. For any
given hardness, copper had a greater effect on critical speed at
low pH. A given copper treatment had a more pronounced effect at
374
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low hardness. LC-20 (240 hrs) values ranged from 22 to 330 ug
Cull between conditions of lowest hardness of 30 mg/l and pH 6,
and highest hardness of 360 mgll and pH 8. No distinction could
be made among total, soluble, or extractable copper, but predicted
concentrations of 6 specific cupric ions va2ied with pH and
hardness. Of these copper species, only Cu + and CuO~ were
significantly related to critical performance. In the presence of
25 or 40 ug Cull, maximum oxygen consumption decreased and energy
expenditure for a given swimming speed increased.
3008.
Weiss, A.A., S.D. Murphy, and S. Silver. 1977. Mercury
and organomercurial resistances determined by plasmids
in Staphylococcus aureus. Jour. Bacteriology
132:197-205.
Penicillinase plasmids of Staphylococcus aureus oAten
contain genes conferring resistance to inorganic mercury (HgC+)
and the organomercurial phenylmercury acetate. The mechanism of
resistance was the enzymatic hydrolysis of phenylmercury to
benzene plus inorganic ionic mercury, which was then enzymatically
reduced to metallic mercury (Hgo). The HgO was rapidly
volatilized from the medium into the atmosphere. After the
mercurial was degraded and the mercury was volatilized, the
resistant cells were able to grow. These plasmids also conferred
the ability to volatilize mercury from thimerosal, although the
plasmid-bearing strains were equally as thimerosal sensitive as
the S. aureus without plasmids. None of the plasmids conferred
the ability to volatilize mercury from several other
organomercurials. Although mercury was not volatilized from
p-hydroxymercuribenzoate or fluoresceine mercuric acetate, the
plasmid-bearing strains were resistant to these organomercurials.
The ability to volatilize mercury from Hg2+ and pqenylmercury
was inducible. The range of inducers included H~+,
phenylmercury, and several organomercurials that were not
substrates for the degradation system. Mercury-sensitive mutants
have been isolated from the parental plasmids. Thirty-one such
mercury-sensitive strains fall into three classes: 1)
mercury-sensitiv~ strains totally devoid of the phenylmercury
hydrolase and H~+ reductase activites; 2) mutants with normal
hydrolase levels and no detectable reductase; and 3) mutants with
essentially normal hydrolase levels and low variable (5 to 25%)
levels of reductase activites. The mercury-sensitive strains were
also sensitive to phenylmercury, including those with the
potential for hydrolase activity.
375
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3009.
Woodrow, G.C., L. Langman, I.G. Young, and F. Gibson.
1978. Mutations affecting the citrate-dependent iron
uptake system in Escherichia coli. Jour. Bacteriology
133: 1524-1526.
Isolation of six strains of E. coli carrying mutations
affecting the citrate-dependent iron uptake system is described.
Genetic analysis of these mutants showed that mutations affecting
the citrate system are clustered together at one locus on the E.
coli chromosome.
3010.
Yamada, M., T. Koyama, and M. Matsuhashi. 1977.
Interconversion of large packets and small groups of
cells of Micrococcus rubens: dependence upon magnesium
and phosphate. Jour. Bacteriology 129:1513-1517.
M. rubens, a gram-positive coccus, usually forms large
cubic packets of more than 500 cells regularly arranged in
three-dimensional ce~l groups. In medium with extremely low
concentrations of ~+ and phosphate, in which the cells can
only grow on an agar surface, M. rubens formed small groups of 2
to 20 cells. Irregularly arranged cell groups of intermediate
size were obtained iq culture media containing intermediate
concentrations of MgL+ and phosphate.
3011.
Young, A.M. and T.L. Hazlett, III. 1978. The effect of
salinity and temperature on the larval development of
Clibanarius vittatus (Bosc) (Crustacea:Decapoda:
Diogenidae). Jour. Exp. Marine BioI. Ecol. 34:131-141.
Hermit crab, C. vittatus, larvae were reared in 20
combinations of 4 salinities (15, 20, 25, and 30 0/00) and 5
temperatures (15, 20, 25, 30, and 35 C). No development was
observed in any salinity at 15 C, but partial development occurred
in all other test conditions. Metamorphosis to juvenile crabs was
noted only at salinities of 25 and 30 0/00 in combination with
temperatures of 25 and 30 C. In general, development times were
decreased at higher temperatures; no trend was evident for
salinity.
3012.
Young, M.L. 1977. The roles of food and direct uptake
from water in the accumulation of zinc and iron in the
tissues of the dogwhelk Nucella lapillus (L.). Jour.
Exp. Marine BioI. Ecol. 30:315-325.
376
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A description of zinc and iron accumulation in the
tissues of Nucella lapillus, a predatory gastroPOd, has been
obtained with the aid of seawater and barnacles, Balanus
balanoides~ labelled with Zn-65 and Fe-59. The food chain is the
major source of Zn and Fe in tissues, input being approximately
two orders of magnitude greater than that from seawater. Neither
metal is accumulated up the food chain. The fractions of zinc and
iron assimilated from food are similar, as are their rates of
excretion from tissues of N. lapillus. The relative
concentrations of zinc and-iron in tissues reflect their relative
concentrations in food. Results are discussed with reference to
zinc and iron accumulation by the herbivorous winkle, Littorina
littoralis.
3013.
Aarkrog, A. 1977. Environmental behaviour of plutonium
accidentally released at Thule, Greenland. Health
Physics 32:271-284.
Plutonium contamination resulting from a B-52 airplane
accident in 1968 at Thule, Greenland, was studied in 1968, 1970,
and 1974. Contamination was confined mainly to the marine
environment, where plutonium was preferentially accumulated in
sediment and benthic fauna. Radioactive plutonium levels of
sediments decreased with depth and distance from point of impact.
Pu-239,240 in the marine environment from the accident was
estimated at 25-30 Ci, and Pu-238 about 0.5 Ci. Surface sediment
concentrations within 1 km of impact were 23,000 pCi/kg ash wt in
1968, 13,000 in 1970, and 17,000 in 1974. Benthic anilnals showed
a horizontal distribution of radioactivity similar to sediment.
From 1968 to 1970, Pu-239,240 concentrations in biota decreased by
an order of magnitude; since 1970 the decrease has been less
evident. Plutonium concentrations in worms within 1 km of the
accident were 230,000 pCi/kg ash wt in 1968, 3.4 in 1970, and 5.7
in 1974. Seven species of bivalve molluscs within one km of the
site contained 4600, 390, and 240 pCi/kg fresh wt, and
brittlestars and seastars contained 380, 140, and 81 pCi/kg fresh
wtin respective years. There were no indications of increased Pu
in surface seawater or marine plants and zooplankton. Algae,
Fucus and Laminaria, contained 2.0 to 19.0 pCi Pu-239,240/kg wet
wt and shrimp contained 35 to 72 pCi/kg fresh wt during the three
surveys. Vertebrates showed no tendencies to increase plutonium
levels after the accident. Pu content in 6 species of fish ranged
from 1.0 to 40.0 pCi/kg fresh wt in collections of 1968 to 1974,
entrails of 2 species of birds contained 0.3 to 2.2, and entrails,
liver, stomach, and intestine of 3 species of seals and walrus
contained 0.5 to 1.0 pCi/kg.
377
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Babich, H. and G. Stotzky. 1978. Toxicity of zinc to
fungi, bacteria, and coliphages: influence of chloride
ions. Appl. Environ. Microbiology 36:906-914.
A 65.4 mg/l concentration of Zn2+, as znS04'
decreased survival of Escherichia coli, enhanced survival of
Bacillus cereus, did not significantly affect survival of
Pseudomonas aeruginosa, Nocardia corallina, and selected
coliphages, completely inhibited mycelial growth of Rhizoctonia
solani, and reduced mycelial growth of Fusarium solani,
Cunninghamella echinulata, Aspergillus niger, and Trichoderma
viride. Toxicity of zinc to fungi, bacteria, and coliphages was
influenced by 0.5 and 1.0 M NaCl. Increased toxicity of zinc in
the presence of high N~Cl was not a result of a synergistic
interaction between Zn + and elevated osmotic pressures, but of
the formation of complex anionic Zn-Cl species that exerted
greater toxicities than cationic Zn2+. Conversely, decrease in
zinc toxicity with increasing concentrations of NaCl probably
reflected the decrease in levels of Zn~+ due to the formation of
Zn-Cl species, which was less inhibitory to these microbes than
Zn2+. ~. n2g~~ tolerated higher concentrations of zinc with
NaCl at 37 an 25 C.
3014.
3015.
Berk, S.G., A.L. Mills, D.L. Hendricks, and R.R. Colwell.
1978. Effects of ingesting mercury-containing bacteria
on mercury tolerance and growth rates of ciliates.
Microbial Ecology 4:319-330.
A marine protozoan ciliate, Uronema nigricans, acquired
tolerance to mercury within one generation after being fed
mercury-laden bacteria, Pseudomonas sp., followed by exposure of
these ciliates to various concentrations of mercury (10 to 100
ug/l) in solution. After 14.5 hours in 10 ug Hg/l, 26% of
ciliates fed Hg-free bacteria died, compared to 8.4% of those fed
Hg-laden bacteria. Ciliates fed Hg-free bacteria and subsequently
exposed to increasing levels of mercury in solution showed an
elevated tolerance to concentrations which, on initial testing,
resulted in mortality of 83% of the ciliate population. Ingestion
of mercury-laden bacteria had no effect on growth rates of
ciliates that had been fed Hg-laden and Hg-free bacteria, based on
measurements at 3 and 14 days.
3016.
Briand, F., R. Trucco, and S. Ramamoorthy.
Correlations between specific algae and
binding in lakes. Jour. Fish. Res. Bd.
35 : 1482 -1485 .
1978.
heavy metal
Canada
378
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Four-month experllnents conducted at Hen~y Lake, Quebec,
in summer 19~6, showed the binding capacity for Cu +, Hg2+,
Pb2+, and Cd + to be related to algal species composition
rather than to total algal biomass or to physicochemical
parameters. Most of the metal binding could be accounted for by
certain species of green algae, diatoms, and chrysomonads that
usually constituted only a minor fraction of total algal volume.
3017.
Brown, B.E. 1978. Lead detoxification by a copper-
tolerant isopod. Nature 276:388-390.
Copper and lead uptake was studied in two populations
of isopods, Asellus meridans: one Cu and Pb tolerant group from
Hayle River, with Cu water levels between 0.10 and 0.25 mg/l and
Pb < 0.01 mg/l, and one Pb tolerant but not Cu tolerant group from
Gannel River, with Pb water levels of 0.19 to 0.35 mg/l and Cu of
0.01 to 0.04 mg/l. After exposure for 14 days to constant copper
(0.25 mg/l) and increasing lead concentrations (0.0 to 0.4 mg/l),
isopods from the Hayle showed decreasing Cu body levels, from 3500
to 1500 mg/kg dry wt and increasing Pb from 500 to 4500 mg/kg,
while isopods from Gannel had slight changes, from 800 to 400 mg
Cu/kg dry wt and from 1800 to 3000 mg Pb/kg. With constant lead
(0.25 mg/l) and increasing copper (0.0 to 0.4 mg/l), Hayle isopods
decreased body Pb from 2500 to 1500 mg/kg dry wt and increased Cu
from 2500 to 4000 mg/kg. Gannel isopods body levels varied from
2000 to 2500 mg Pb/kg regardless of increasing Cu, and increased
from 1200 to 2000 mg Cu/kg dry wt. Hayle populations of isopods
accumulated more Cu and Pb and were able to "detoxify" lead by
storing the metal in cuprosomes in the hepatopancreas at the
expense of copper. CU and Pb appeared to compete for the same
sites in the hepatopancreas.
3018.
Brown, D.A., C.A. Bawden, K.W. Chatel, and T.R. Parsons.
1977. The wildlife community of Iona Island jetty,
Vancouver, B.C., and heavy-metal pollution effects.
Environmental Conservation 4:213-216.
Marine and terrestrial organisms (algae and higher
plants, bivalve molluscs, crabs, ducks and raptorial birds, and
rats) abundant in a community associated with a marine sewer
outfall from Vancouver, B.C., are contaminated with high levels of
heavy metals, but are apparently protected from their toxic
effects by production of metallothionein protein. Amount of
metallothionein and heavy metal loading appears to depend
379
-------
primarily on degree of pollution and secondly on species of animal
and its position in the food web. As total quantity of cadmium,
copper, and zinc in animal tissue increased from 0.1 to 0.4 mmole
metals/kg, ratio of metals on metallothionein to enzyme protein
fractions rose from 0.25 (bivalves tilus edulis, Macoma
incons icua, and crYrtomya californica to 0.40 (rats Rattus
norvegicus to 0.45 mussels closer to outfall) to 0.70 (ducks).
3019.
Carlr~fn, S. 1978. A model for the movement and loss of
Cs in a small watershed. Health Physics 34:33-37.
The mathematical model describing turnover of fallout
Cs-137 in a small lake is based on the assumption that water
receives Cs-137 from deposition on the lake surface and from
removal from the drainage-area. Loss of Cs-137 from lake water is
assumed to occur through outflow and sedimentation. Based on
observed concentrations of Cs-137 in water and sediment, the model
determined that 1.9% of freshly deposited Cs-137 and 0.56% per
year of the accumulated Cs-137 in the drainage-area is transported
to the lake and that 38% of Cs-137 is accumulated in lake
sediment. This indicates that the radionuclide is strongly bound
to soil and vegetation in the drainage-area and that movement of
Cs-137 in the watershed is small and mainly consists of a
transport to sediment. Loss of Cs-137 from the watershed is
small; the dominant pathway is through physical decay.
3020.
Carlsson, S. 1978. A model for the turnover of 137Cs
and potassium in pike (Esox lucius). Health Physics
35:549-554. ----
A mathematical model for turnover of cesium-137 and
potassium in pike is described. It is assumed that the change in
body burden of the elements is the difference between intake and
excretion, which in turn are functions of metabolic rate. The
model, quantitatively based on existing data on food (other fish)
of pike and its concentrations of Cs-137 and K, has been applied
to calculate biological half-times in pike from Lake Ulkesjon,
Sweden. Turnover was estimated as 1.3 yr for Cs and 0.55 yr for
K, for a pike weighing 500 g at a water temperature of 8-10 C.
Half-times were longer in larger pike. Maximum whole-body Cs-137
concentrations measured between 1961 and 1973 were 8.5 nCi/kg in
pike and 5.0 nCi/kg in their prey. Influences of various
assumptions about intake and elimination of Cs-137 and K on these
calculations are discussed.
380
-------
3021 .
Chapman, G.A. 1978. Effects of continuous zinc exposure
on sockeye salmon during adult-to-smolt freshwater
residency. Trans. Amer. Fish. Soc. 107:828-836.
Adults of sockeye salmon, Oncorhynchus nerka, were
chronically exposed to zinc for 3 months then spawned. The
resultant embryonic through smolt stages were also subjected to
various concentrations of zinc for 18 months. Zinc concentrations
were 30 to 112 ug/l during adult-to-smolt exposure period, and an
addi tional 242 ugll for embryo-to-smolt expsoure. No adverse
effects were observed, on survival, fertility, fecundity, growth,
or on subsequent survival of smol ts transferred to seawater.
Fertility was above 97% in adults exposed to up to 120 ug Zn/l.
Survi val was >90% in all but 3 cases for adults, eggs, and
juveniles in up to 242 ug Zn/l. Acclimatization to 242 ug Zn/l
markedly decreased mortality at Zn levels that were lethal to
unacclimated salmon juveniles. The 112- and 242-ug/1
concentrations were 0.15 and 0.32, respectively, of the 749 ug/l,
LC-50 (96-hr) value for 8-month-old sockeye salmon. An
application factor relating LC-50 (96 hr) and "safe"
concentrations of zinc to anadromous sockeye salmon in soft water
appears to be >0.15, at least 15X larger than the often
recommended 0.01 application factor for zinc based on studies with
other species.
3022.
Chapman, G.A. 1978. Toxicities of cadmium, copper, and
zinc to four juvenile stages of chinook salmon and
steelhead. Trans. Amer. Fish. Soc. 107:841-847.
Continuous-flow toxicity tests were conducted to
determine relative tolerances of newly hatched alevins, swim-up
alevins, parr, and smolts of chinook salmon, Oncorhynchus
tshawytscha, and steelhead, Salmo gairdneri, to cadmium, copper,
and zinc. Newly hatched alevins were much more tolerant to
cadmium, and to a lesser extent zinc, than later juvenile forms.
However, developmental progression from swtm-up alevin, through
parr, to smolt was accompanied by a slight increase in metal
tolerance. LC-50 (96 hr) values for all 4 life stages ranged from
1.0 (steelhead parr) to >27 ug Cd/I (steelhead alevins); 17
(steelhead swtm-up) to 38 ug Cull (salmon parr); and 93 (steelhead
parr) to 815 ug Zn/l (steelhead alevins). LC-50 (200 hr) values
ranged for all groups from 0.9 to >27 ug Cd/I, 15 to 30 ug Cull,
and 93 to > 661 ug Zn/l. Steelhead were consistently more
sensitive to Cd, Cu and Zn than chinook salmon. The author
suggests that when a sensitive life stage for acute toxicity tests
with metals is sought, the more resistant newly hatched alevins
should be avoided. Although tolerance may increase with age, all
381
-------
late juvenile life stages are more sensitive than newly-hatched
alevins and should give replicable results.
3023.
Chapman, G.A. and D.G. Stevens. 1978.
levels of cadmium, copper, and zinc
salmon and steelhead. Trans. Amer.
107:837-840.
Acutely lethal
to adult male coho
Fish. Soc.
Flow-through acute toxicity tests of cadmium, copper,
and zinc were conducted with adult male coho salmon, Oncorrgchus
kisutch and adult male steelhead, Salmo gairdneri. LC-50 96 hr)
values for copper were 46 ug/l for salmon and 57 ug/l for
steelhead. LC-50 (96 hr) values for zinc were 905 and 1755 ug/l
for salmon and steelhead, respectively. Mortality induced by
cadmium was slow at onset, but 50% mortality occurred after more
than a week at 3.7 ug/l for salmon and 5.2 ug/l for steelhead.
Hardness and alkalinity of water supply were higher during tests
with steelhead, complicating direct comparisons between the two
species.
3024.
Chin, B., G.S. Lesowitz, and I.A. Bernstein. 1978. A
cellular model for studying accommodation to
environmental stressors: protection and potentiation
by cadmium and other metals. Environmental Research
16 :432-442.
Exposure of bacteria, Physarum polycephalum, to low
concentrations of cadmium insufficient to delay mitosis, elicited
a protective response against a mitotic delay resulting from
subsequent exposure to higher Cd concentrations. The
concentration gf Cd2+ in the subthreshold challenge could be
lowered to 10- M (about 1.12 mg/l) and maintain comple~e
pr~tection against a suprathreshold e:Il0sure of 5 x 10- M
Cd +. A subthreshold cha14enge ~f 10- M provided full
protec~ion ~ainst 7 x 10- M Cd +. A subthreshold challenge
of 10- M Cd + could be placed anywhere in the cell cycle
apP40aching but not abutting a suprathreshold challenge of 5 x
10- M Cd2+ in late G2 stage and still provide complete
protection with4the e~ception of one point in early S stage. At
that point, 10- M Cd + was toxic to the cell; however,
partial protection developed. Other responses developed when
oth~r metals were subs~ituted f~r cadmium. Cd2+ protected
agal~t exp~sure ~o Hg::+ ~d Ni +, but potenqated exposures
to Co +, Cu +, Pb +, or Zn +. Exp~ure to Hg<-+ and
N~~~ protected bacteria ag~inst ~d + (as ~ell as Hg2+ and
Nl 'h while exposure to Co +, Pb +, or Zn + potentiated
toxicity of Cd2+.
382
-------
3025.
Cough trey , P.J. and M.H. Martin. 1978. Cadmium uptake and
distribution in tolerant and non-tolerant populations
of Holcus lanatus grown in solution culture. Gikos
30 :555-560.
Cadmium uptake and distribution between roots and
shoots of a tolerant and a non-tolerant population of plant,
Holcus lanatus, grown in culture solution were studied with
reference to both concentration and total cadmium content. Mean
concentrations, in mg Cd/kg dry wt, after 7 days in 1.0 mg Cd/l
were: in nan-tolerant plants, 145 in shoots, 1211 in roots, and
545 in whole plants; in tolerant plants, 43 shoots, 1799 roots,
and 538 whole plants. When exposed to 2.0 mg Cd/l, non-tolerant
plants contained 191, 2229, and 1099 mg/kg, respectively, and
tolerant plants contained 89, 2349, and 738. In normal
non-tolerant plants, as much as 90% of whole plant Cd remains in
roots. In tolerant plants translocation of Cd to shoots is
reduced with a concomitant increase of cadmium concentration in
roots. Translocation differences are shown to be related to
differences in biomass and rates of metal uptake between tolerant
and non-tolerant populations.
3026.
Davis, J.A. and C.E. Boyd. 1978. Concentrations of
selected elements and ash in bluegill (Lepomis
macrochirus) and certain other freshwater fish.
Amer. Fish. Soc. 107:862-867.
Trans.
Bluegills and 16 other species of freshwater fish
collected from southeastern U.S. were found to differ in
concentrations of calcium, magnesium, potassium, sodium, nitrogen,
phosphorus, sulfur, and ash depending upon species, size, and
collecting site. Mean elemental concentrations, as percent dry
wt, in bluegill from 24 ponds were: 5.65 for Ca, 1.20 for K, 0.42
for Na, and 0.19 for Mg. Range of concentrations in all species
of fish collected from West Point Reservoir, Georgia, were: 2.36
to 10.30% dry wt for Ca, 0.91 to 1.30 for K, 0.26 to 0.62 for Na,
and 0.13 to 0.23 for Mg. Authors conclude that elemental
composition of fish fauna in a body of water is a function of
species and size.
3027.
Delhaye, W. and D. Cornet. 1975. Contribution to the
study of the effect of copper on Mytilus edulis during
reproductive period. Compo Biochem. Physiol.
50A:511-518.
383
-------
Mortality, respiration, and copper accumulation in
mussels are exponential functions of the initial copper
co~centration with a critical value between 0.3 and 1.0 mg
Cu +/1. An acceleration of mortality occurs during the
reproducti ve period. Respiration is similarly affected. Oxygen
consumption rates obtained at different copper concentrations show
that more than one mechanism is disrupted. Most of the copper
accumulated is bound to organic molecules. Cu accumulation is
comparatively high in gills, mantle and foot. After 48 hrs,
copper levels decreased in all organs, with no major organ
respository observed. Critical concentrations seem to exist which
inhibit some mechanisms; higher Cu concentrations have no markedly
greater effects. The spawning period corresponds with an
acceleration of copper uptake and consequently the critical
concentration is reached more rapidly. The final result of these
studies seems to be that the increase in copper toxicity during
reproductive period is primarily attributable to a seasonal
increase in mussel metabolism, engendering faster absorption of
Cu, rather than a real increase of sensitivity.
3028.
Deshimaru, 0., K. Kuroki, S. SakamoEg, and Y. Yone. 1978.
Absorption of labelled calcium- Ca by prawn from sea
water. Bull. Japan. Soc. Sci. Fish. 44:975-977.
Absorption of labelled calcium from surrounding
seawater by prawns, Penaeus japonicus, fed a diet without
supplemental calcium was compared to that of prawns fed diets
supplemented with calcium. Prawns were fed each diet in ordinary
seawater, then one hour after the final feeding, transferred to
seawater with Ca-45 CaC12. Prawns not fed supplemental calcium
exhibited faster absorption and higher activity of Ca-45 over 23
hours than those fed calcium. Calcium content was 830 mg/kg in
prawns not fed Ca and 710 mg/kg in those fed Ca.
3029.
De Wolf, P. 1975. Mercury content of mussels from West
European coasts. Marine Poll. Bull. 6:61-63.
Mytilus edulis and ~. galloprovincialis were collected
from the east side of the North Sea from Arcachon in France to
Cape Skagen in Denmark and on the west side from Lands End in
England to Edinburgh, Scotland. Mercury content, in mg/kg wet wt
soft parts, of intertidal mussels ranged from 0.053 to 0.830 and
varied with season of year. Values were high at all sampling
stations in March and diminished until September, after which they
increased again until March. The rapid decrease in Hg content
384
-------
from March to May is attributed to spawning, part of the Hg
leaving with the gametes. In general, subtidal mussels contained
less Hg than mussels collected from the intertidal zone. Highest
Hg levels occurred in mussels taken from the vicinity of the Rhine
and Eems Dollard and may reflect environmental contamination.
Mercury values on the British coast were generally higher than
values from the east side of the North Sea.
3030.
Domby, A.H., D. Paine, and R.W. McFarlane. 1977.
Radiocesium dynamics in herons inhabiting a
contaminated reservoir system. Health Physics
33:523-532.
Blue heron, Florida caerulea, and green heron,
Butorides virescens, nest at a radionuclide-contaminated reservoir
on the Savannah River Plant site near Aiken, South Carolina.
Green herons distributed their nests singly along the periphery of
the reservoir but fed their nestlings exclusively upon amphibians
from adjacent uncontaminated Carolina bays. Radiocesium burdens
in green heron nestlings did not exceed 5.0 nCi/kg wet wt; 12
regurgitated food pellets averaged 0.2 nCi/kg. Twelve pairs of
blue herons established a heronry upon a small island and fed
their nestlings fish and amphibians foraged from within the
radionuclide-contaminated reservoir system. Recently-hatched
birds within the same nest did not exhibit significant differences
in body burdens; maximum radiocesium burden determined was 27.4
nCi/kg wet wt. Substantial differences were found between
nestlings from different nests. Radiocesium level of 43
regurgitated food pellets had a high correlation with observed
levels in nestlings. Variation in food contamination is believed
to be the major factor in observed variation between blue and
green heron nestlings. Radiocesium levels in bluegill fish,
Lepomis macrochirus, ranged from 2.3 to 52.3 nCi/kg wet wt, with
highest values occurring nearest to the original Cs source.
Variable contamination of primary prey species was correlated with
differentially contaminated foraging sites, and indicates that
adult blue herons tend to spatially partition available foraging
areas.
3031.
Establier, R., M. Gutierrez and A. Arias. 1978.
Accumulation and histopathological effects of organic
and inorganic mercury to the lisa (~ auratus
Risso). Investigacion Pesquera 42:55=80. (In
Spanish, English sunrnary).
385
-------
Inorganic (HgC~2) and. organic (CH3Hg~l) me~cury .
uptake in flesh, blood, llver, kldney, spleen, lntestlne, .pylorlc
caeca, and gills by M. auratus exposed to O. 1 mg/l HgCl2 ln
seawater for 57 days-and 0.008 mg/l CH3HgCI for 45 days was
determined. Fish in natural seawater contained concentrations of
0.47 mg total Hg/kg (presumably dry wt) in dorsal muscle and 0.92
in intestine. After 57 days in 0.1 mg Hg/I, levels were 10.3
mg/kg in muscle and 93.3 in intestine, and after 45 days in 0.008
mg Hg/I, 11.8 mg/kg in muscle and 41.8 in intestine.
Histopathological effects of inorganic Hg on liver and intestine
and organic Hg on gills, stomach muscle, liver, kidney, and
intestine were also investigated.
3032.
Eyman, L.D. and T.R. Trabalka. 1977. Plutonium-237:
comparative uptake in chelated and non-chelated form by
channel catfish (Ictalurus punctatus). Health Physics
32 :475-478.
Chelation can either enhance or reduce uptake of
ingested plutonium relative to PuOH (monomer) in channel catfish.
Uptake was 10.5% in Pu-237 citrate, 6.2% in Pu-237 hydroxide, and
1.6% in Pu-237 fulvate. Biological half-lives for respective
compounds were 30, 13, and 24 days. Reduced uptake of Pu-237
fulvate was due either to molecular weight of the complex or its
stability in metabolic systems. Increased uptake of Pu-237
citrate was attributable to instability of the complex in
metabolic systems.
3033.
Frank, R., M.V.H. Holdrinet, R.L. Desjardine, and D.P.
Dodge. 1978. Organochlorine and mercury residues in
fish from Lake Simcoe, Ontario 1970-76. Environ. BioI.
Fish 3:275-285.
Lake Simcoe in the central Ontario plain has four major
streams draining the watershed. Persistent organochlorine
insecticides were used in the basin for mosquito control and
agricultural production until restricted: methylmercury compounds
have been phased out and a voluntary restriction was imposed for
polychlorinated biphenyls. Ten species of fish (Perca flavescens,
Ambloplites rupestris, Micropterus dolomieui, M. salmoides,
Catostomus commersoni, Stizostedion vitreum vitreum, Esox lucius,
Lota Iota, Salvenius namaycush, and Coregonus clupeaformIs) were
collected between 1970 and 1976 for organochlorine and mercury
analysis. Mercury residues showed no change from 1970 to
386
-------
1975-76 in five species; residues declined in two species, and
increased in small specimens of S. v. vitreum from 0.20 to 0.25
mg/kg wet wt. Mercury residues ,-in-mg/kg , in 1970 ranged from
0.01-0.04 in small f. clupeaformis, f. commersoni, and ~.
ruprestris to 0.32-0.48 in large L. Iota and M. dolomieui. In
1975-76, concentrations ranged from 0.01-0.04-mg/kg in large and
small f. clupeaformis, and small~. dolomieui and f. commersoni to
0.49-0.73 in large~. namaycush, ~. Iota, and~. ~. vitreum.
Among tissues analyzed, L. Iota in 1971 contained 0.39 mg Hg/kg in
liver and 0.22 in other tissues, eggs of ~. namaycush in 1975-76
contained 0.09-0.12 mg Hg/kg. Correlations were observed between
lipid content of fish and organic contamination, but not mercury
residues.
3034.
Fujita, M., K. Iwaskai, and E. Takabatake. 1977.
Intracellular distribution of mercury in freshwater
diatom, Synedra cells. Environmental Research 14:1-13.
Intracellular distribution of mercury in Synedra cells
was investigated by measuring amounts of radioactive Hg
incorporated into various subcellular components. Mercury
initially accumulated in the chloroplast fraction and then
translocated to the soluble fraction. Mercury levels reached 8000
cpm/l of cell culture in one fraction after 22 hr exposure (100
cpm = 0.6 ng Hg). When dead cells were used, no Hg accumulation
was observed in any fraction.
3035.
Guary, J.-C. and S.W. Fowler. 1978. Uptake from water and
tissue distribution of neptunium-237 in crabs, shrimp
and mussels. Marine Poll. Bull. 9:331-334.
Uptake of Np-237 was monitored in tissues of mussel
Mytilus galloprovincialis, shrimp Lysmata seticaudata, and crab
Cancer pagurus, exposed to the actinide in seawater under
controlled conditions. Bioaccumulation was observed in all
tissues examined, with highest concentration factors found in
external shells of the three species. Concentration factors of
Np-237 levels in exoskeleton or shell over water were 60 in crabs
after 50 days, 15 in shrimp after 50 days, and 20 in mussels after
60 days. Muscle tissue of each organism had CF's of 1.0, 0.25,
and 2.0, respectively. Despite some incorporation of Np-237 into
internal tissues, 92-98% of the organisms' total Np-237 content
was associated with non-edible shell or exoskeleton. Authors
concluded that neptunium accumulation patterns in invertebrate
tissues are very similar to those of plutonium.
387
-------
3036.
Gutierrez, M., R. Establier and A. Arias. 1978. Uptake
and histopathological effects of cadmium and mercury to
the sapo (Halobatrachus didactylus). Investigacion
Pesquera 42:141-154. (In Spanish, English summary).
Accumulation of cadmium in flesh, blood, liver, kidney,
and intestine of the marine teleost H. didactylus exposed to 50 mg
Cd/l in seawater for 4 days, and accumulation of mercury in flesh
and liver in fish exposed to 0.1 mg Hg/I for 49 days was
determined. Cadmium concentrations in fish from natural seawater
were 0.2 mg/kg dry wt in dorsal muscle and 1.5 in intestine.
After 4 days exposure to 50 mg/l Cd, levels were 0.7 mg/kg in
muscle and 289.9 in intestine. Cytohematological and
histopathological effects of Cd and Hg on blood, liver, kidney,
and intestine were also investigated.
3037.
Hartung, R. 1973. Biological effects of heavy metal
pollutants in water. In: Dhar, S.K. (ed.). Metal
ions in biological systems. Studies of some
biochemical and environmental problems. Advances
Exper. Medicine Biology 40:161-172.
A brief review is presented of effects of cadmium,
chromium, copper, lead, mercury, and zinc to freshwater species of
algae and higher plants, crustaceans, molluscs, fish, waterfowl
and fish-eating birds, and mammals. The author points out
difficulties in evaluating heavy metal effects to aquatic
organisms, including the resolution of chemical and physiological
conditions during exposure, correctly predicting absorbed dose and
effects, and the need to study subtle effects of growth,
reproduction, and behavior.
3038.
Hess, C.T., C.W. Smith, and A.H. Price. 1977. A
mathematical model of the accumulation of radionuclides
by oysters (~. virginica) aquacultured in the effluent
of a nuclear power reactor to include major biological
parameters. Health Physics 33:121-130.
Uptake, accumulation, and loss of radionuclides by
Crassostrea virginica in the effluent of a nuclear power reactor
was measured monthly for 3 years at four field stations in the
Montsweag Estuary of the Sheepscot River and at a control station
in nearby Damariscotta River Estuary, Maine. A mathematical model
for time variation of the specific activity of oysters was
developed to include physical and biological half-lives of various
388
-------
radionuclides, water temperature (oyster hibernation), and shell
growth. The equation is driven by the liquid radionuclide
effluent release schedule of Maine Yankee Nuclear Reactor.
Comparison of monthly measurements of labelled cobalt, manganese,
and cesium in oysters with model calculations show close agreement
over all ranges of variation observed. Maximum radionuclide
levels in oysters measured between 1973 and 1976 were 850 pCi/kg
for Co-58, 135 for Co-60, 130 for Mn-54, 50 for Cs-134, and 100
for Cs-137. Biological half-lives, in days, were 35 for Co-58 and
-60, 1500 for Mn-54, and 250 for Cs-134 and -137.
3039.
Hidu, H. and H.H. Haskin. 1978. Swimming speeds of oyster
larvae Crassostrea virginica in different salinities
and temperatures. Estuaries 1:252-255.
Swimming speeds of oyster larvae, f. virginica, were
determined in constant and increasing salinities. Normal
non-directed swimming speeds in 25 0/00 S ranged from <1 cm/min
for early veligers to 5 cm/min for eyed veligers. Temperature was
an important variable. When subjected to hourly salinity
increases of 0.5 0/00, most larvae swam upward or downward at
approximately 3X normal speeds. Larvae, with valves closed in
response to traces of formalin, sank at speeds of 5 to 50 cm/min,
depending on larval stage, regardless of salinity of 15, 20, or 25
0/00.
3040.
Holden, A.V. 1973. International cooperative study of
organochlorine and mercury residues in wildlife,
1969-71. Pesticides Monitoring Jour. 7:37-52.
A two-part collaborative study of organochlorine
pesticides, polychlorinated biphenyls (PCB's), and mercury
residues was conducted by 26 laboratories in 12 countries. The
first part involved analysis of 3 test samples containing
organochlorine residues and one group containing mercury.
Freeze-dried homogenates of muscle of pike, Esox lucius, contained
mean values, in mg/kg, of 0.152 methylmercury and 0.165 total
mercury before Hg-spiked solutions were added. Samples and
analyses of several species of wildlife from both terrestrial and
aquatic environments were also taken from areas considered free of
pesticide usage and from areas seriously polluted. Results
demonstrated difficulties in selecting species appropriate for
international monitoring programs, in identifying areas of high
contamination before analysis, and in relating concentrations to
measurable biological effects. Mercury levels, in mg/kg, in
389
-------
marine mussels, Mytilus edulis, from 10 countries ranged from 0.03
to 0.23 in unpolluted areas, 0.08 to 0.31 in slightly polluted
areas, and 0.02 to 0.46 in polluted areas. Concentrations in
marine herring, Clupea harengus, (and freshwater pike) from 8
countries were <0.01 to 0.12 (0.27 to 0.68) unpolluted, 0.05 to
0.19 (0.08 to 2.12) slightly polluted, and <0.01 to 0.07 (0.65 to
3.85) polluted. Freshwater eel, Anguilla vulgaris, from 2
countries contained 0.24 to 0.35 unpolluted and 0.22 to 0.72 mg/kg
polluted. Mercury concentrations in eggs from 6 species of
aquatic birds, (eider Somateria mollissima, pelican Pelicanus
occidentalis carolinensis, terns Thalasseus maximus, Sterna
hirundo, and S. sandvicensis) from 6 countries were 0.33 mg/kg
freeze-dried homogenate from unpolluted areas, O. 12 from slightly
polluted areas, and 0.50 to 0.87 from polluted areas.
3041 .
Huckabee, J. W., S.A. Janzen, B.G. Blaylock, Y. Talmi, and
J.J. Beauchamp. 1978. Methylated mercury in brook
trout (Salvelinus fontinalis): absence of an in vivo
--
methylating process. Trans. Amer. Fish. Soc.
107:848-852.
The possibility of in vivo conversion of inorganic
mercury to methylated mercury TMe~in trout was tested by
chronically exposing fish to 1.0 ug/l mercury, as Hg(N03)2'
for 56 days, and then maintaining them at background levels for
294 days. Inorganic mercury levels in test fish increased rapidly
during exposure, reaching, at 116 days, 0.49 mg/kg wet wt in
muscle, 11.3 in liver, 9.0 in gills, and 3.5 in intestine. MeHg
concentrations in both control and test fish increased slowly at
the same rate. Final 350-day concentrations, in mg/kg wet wt,
were 0.04 in muscle, 0.03 in liver, 0.02 in gills, and 0.01 in
intestine. These values were comparable to those found in wild
brook trout from an uncontaminated area. This information
indicates that fish do not methylate inorganic mercury in vivo,
and that approximately one-half of the MeHg body burdens wa:s-
acquired via food.
3042.
Huisman, J. and J.H.G.T. Hoopen. 1978. A mercury buffer
for toxicity experiments with green algae. Water, Air,
30il Poll. 10:325-333.
Mercury toxicity experiments with green algae are
complicated by the fast reduction and evaporation of Hg. A Hg
buffer system is described, which considerably stabilizes the
Hg2+ concentration in test solutions. The Hg buffer consists of
390
-------
mercuric chloride and N-methyliminodiacetic acid (MIDA).
Dissociation of Hg~IDA complex compensates for loss of some
mercury; however, 50% of experimental Hg was lost over 3 days in
spite of MIDA addition. Green alga, Scenedesmus acutus, exposed
to Hg2+ concentrations between 0.02 and 2.0 mg/l at 15 to 30 C
showed no change in algal density during the first day of addition
of Hg-MIDA, but generation time (measured by density) increased
from 17 to 180 hrs. Different initial algal concentrations had
similar results. In unbuffered medium, Hg was no longer in
solution after 1 day, and algae lost Hg adsorbed onto cell walls
by 2 days. With low initial algal concentrations, growth was
inhibited initially, but resumed 2 days after Hg disappearance.
Growth was not affected with a large initial algal concentration.
No effect of MIDA on growth of algae was detected.
3043.
Jackson, T.A. 1978. The biogeochemistry of heavy metals
in polluted lakes and streams at Flin Flon, Canada, and
a proposed method for limiting heavy-metal pollution of
natural waters. Environ. Geology 2: 173-189.
The biogeochemistry of Zn, Cd, Cu, Hg, and Fe in lakes
and streams polluted by mine and smelter wastes emitted at Flin
Flon, Canada, was investigated. In Schist Lake, a repository for
both tailings-pond drainage and sewage, green algal blooms
generated by nutrients from sewage promote entrapment of metals in
sediments by: 1) accumulation of metals from solution by algal
seston, with preferential uptake of Zn, the most abundant metal,
followed by sinking of seston; and 2) production of H2S during
decomposition of dead algae, resulting in sulfide precipitation.
Metals are partially resolubilized from seston as it decomposes
while sinking. Preferential retention of Cu by sinking seston and
by mud promotes Cu enrichment in mud, but the Cu/Zn ratio of mud
varies with the Cu/Zn ratio of surface water seston. In bottom
muds, partitioning of a metal between sulfide and organic matter
is strongly dependent on the stability of the metal sulfide, the
proportion of sulfide-bound metal decreasing in the order of
Hg>Cd>Cu>Fe>Zn. Sulfide was much more effective than organic
matter in suppressing remobilization of metals from bottom
sediments. Authors concluded that introduction of sewage together
with heavy-metal effluents into settling ponds could be an
effective and economic method for limiting heavy-metal pollution
of natural waters.
3044.
Jorgensen, K.F., and K. Jensen. 1977. Effect of copper
(II) chloride on the hatching rate of Artemia salina
391
-------
(L. ).
Chemosphere 6:287-291.
Average hatching rates of Artemia eggs exposed to
coPpe2 chloride, as fractions of control rate, were 0.79 in 0.001
mg Cu +/1, 0.55 in 0.01 mg/l, 0.27 in 0.1 mg/l, and 0.03 or
lower in 1.0 mg/l or greater. Medium hatching rate in 48 hrs was
observed at 0.014 mg Cu2+/l. Minimum effect level for Cu was
below 0.001 mg/l.
3045.
Khandekar, R.N. 1977. Polonium-210 in Bombay diet.
Health Physics 33:148-150.
Polonium-210 concentrations in foodstuffs in Bombay,
India, were assessed to estimate Po-210 intake by man. Local fish
contained 4.25 pCi/kg, which was relatively high compared to
cereal, vegetables, and milk products. Drinking water contained
0.05 pCi/l. Food items accounted for a daily intake of 1.40 pCi
Po-210 in humans. Water and air accounted for intakes of 0.15 and
0.07 pCi, respectively. Polonium reaching blood was 0.084, 0.009,
and 0.019 pCi Po-210/day from food, water and air.
3046.
Kilham, S.S., C.L. Kott, and D. Tilman. 1977.
and silicate kinetics for the Lake Michigan
Diatoma elongatum. Jour. Great Lakes Res.,
Assn. Great Lakes Res. 3:93-99.
Phosphate
diatom
Internat.
Growth rates and uptake rates by a clone of freshwater
Diatoma elongatum isolated from Lake Michigan were measured under
silicate and phosphate limitation. Under silicate limited
conditions, the half saturation constant for growth, K, was 1.51
uM Si02-Si, and maximum growth rate was 1.2 doublings/day.
Results agreed with steady state kinetic information obtained for
a two-step (uptake and utilization) growth model. Authors
observed a dependence of the coefficient of luxury consumption on
steady state growth rate. D. elongatum can store up to 28x more
phosphate, and up to 4.4x more silicate than needed.
3047.
Lorch, D.W. 1978. Desmids and heavy metals II.
manganese: uptake and influence on growth and
morphogenesis of selected species. Arch. Hydrobiol.
84: 166-179.
Effect of manganese was investigated on cell morphology
of 5 species of Desmidiaceae algae, Closterium ehrenbergii,
392
-------
Gonatozygon aculeatum, Micrasterias rotata, Netrium digitus, and
Penium spirostrilatum. In 7.0 mg Mn/l, yield was reduced in 4
species, down to 19% and 33% for Netrium and Micrasterias,
respectively, and was increased to 141% for Penium. Manganese
accumulation followed saturation kinetics, with saturation levels
of 2000 to 12,550 mg/kg, except Closterium which did not reach
saturation at the highest level tested of 7.0 mg Mn/l. Uptake at
saturation level of the 4 species was 1.5 to 5.1% of available
manganese. Mn uptake by isolated cell walls reached saturation
levels of 18% of intact cells for Micrasterias, 90% for
Closterium, and 184 to 504% for the other 3 species.
3048.
Macka, W., H. Wihlidal, G. Stehlik, J. Washuttl, and E.
Bancher. 1978. Metabolic studies of Hg-203 on
Chlamydomonas reinhardi. Experientia 34:602-604.
Sterile cultures of algae, Chlamydomonas reinhardi,
were treated with Hg-203 at 25 C to identify possible formation of
volatile mercury compounds. Experiments were performed with
living and dead cells under aerobic or anaerobic conditions.
Mercury content in the system algae/nutrient medium decreased from
0.35 ug Hg to 0.15 ug in 12 hrs in the living cell suspension
under aerobic and anaerobic conditions, and remained at that level
for 48 hrs. Mercury in the cell-free nutrient medium decreased
slightly to 30 ug Hg and in controls (newly prepared nutrient
medium) showed no decline over the test period. The decrease in
mercury concentration was due to a reduction of Hg2+ to HgO,
probably caused by extracellular enzymes. Monomethyl or dimethyl
mercury could not be detected as intermediate compounds.
3049.
Manson, J.M. and E.J. o 'Flaherty. 1978. Effects of
cadmium on salamander survival and limb regeneration.
Environmental Research 16:62-69.
Salamanders, Notophthalmus viridescens, with amputated
forelimbs, were held in water with 0.0, 2.25, 4.50, or 6.75 mg
Cd/l as cadmium acetate. After 51 days, survival had been
linearly reduced by about 35% in salamanders in 2.25 mg Cd/I, 45%
in 4.50 mg/l, and 80% in 6.75 mg/l. Limb regeneration was begun
in 40% of controls by day 22, but in <5% of any surviving
Cd-exposed animals. Regeneration had started in all groups except
6.75 mg Cd/l Qy day 36, and some regeneration was observed in 70
to 100% of all Cd-exposed salamanders and controls on day 51.
Amount of regeneration of each limb decreased with increasing Cd
concentration. Effects of cadmium on formation of abnormal limb
skeletal structures was also noted.
393
-------
3050.
Martin, P.H. 1978. On the radioactivity in the marine
environment of the Straits of Malacca. Health Physics
35:574-575.
Average concentrations of uranium-238 and thorium-232
(mg/kg dry wt), and cesium-137 (pCi/kg dry wt) in the Straits of
Malacca off Malaysia were: near-shore topsoils, 5.1, 10.6, and
41.0, respectively; marine sediments, 0.5, 2.6, and below
quantitative determination; and prawns, Penaeus sp., detectable
but below quantitative levels for all three elements.
3051 .
Miramand, P. and M. Unsal. 1978. Acute toxicity of
vanadium to some marine benthic and phytoplanktonic
species. Chemosphere 10:827-832. (In French, English
abstract) .
Acute toxicity of vanadium, as sodium metavanadate, to
three benthic species (crabs Carcinus maenas, mussels Mytilus
galloprovincialis, and annelids Nereis diversicolor) and three
phytoplanktonic species (Dunaliella marina, Prorocentrum micans,
and Asterionella japonica) were studied. In general,
phytoplankton were more sensitive than benthic organisms. From
LC-50 (9 day) values, the species studied can be classified in the
following decreasing order of sensitivity: D. marina (0.5 mg
V/I), A. ja onica (2.0), P. micans (3.0), N.-diversicolor (10.0),
f. maenas 35.0 , ~. galloprovincialis (65~0).
3052.
Moss, J.L. 1978. Toxicity of selected chemicals to the
fairy shrimp, Streptocephalus seali, under laboratory
and field conditions. Prog. Fish-Cult. 40:158-160.
Laboratory toxicity tests were conducted with six
chemicals, including potassium permanganate, to determine effect
on survival of fairy shrimp. Potassium permanganate (0.5 to 4.0
mg/l) produced 100% mortality in less than 24 hrs. Pond
treatments with potassium permanganate (1.0 and 2.0 mg/l) produced
more rapid mortality than Dylox (0.25 mg/l). Neither chemical
completely eliminated all fairy shrimp from ponds, except in
isolated cases.
3053.
Mudroch, A. and J. Capobianco. 1978. Study of selected
metals in marshes on Lake St. Clair, Ontario. Arch.
Hydrobiol. 84:87-108.
394
-------
Relationship between concentration of Cd, Co, Cr, Cu,
Ni, Pb, and Zn in sediments and marshwater, and uptake by plants
(Typha latifolia, Carex laucustris, Pontederia cordata, Lythrum
salicaria, Nymphaea odorata, and Myriophyllum heterophyllum) and
algae (Chara sp.) from the east shore of Lake St. Clair, Ontario,
was investigated over the 1976 growing season. Accumulation of
metals varied between plant species and was affected by metal
concentrations in sediments and water in a complex way.
Variations occurred in metal uptake by the same species growing in
different plant communities. Average concentrations in plants, in
mg/kg dry wt, ranged from <1.0 to 3.2 for Cd, 1.1 to 12.8 for Co,
1.3 to 6.0 for Cr, 1.9 to 5.3 for Cu, 1.2 to 10.9 for Ni, 3.6 to
35.1 for Pb, and 11.5 to 25.5 for Zn. Carex accumulated the
largest amount of zinc, while Myriophyllum and Chara contained
maximum concentrations of the other metals. Metal content of
roots of Typha, Lythrum, and Pontederia were higher than above
ground biomass. Metal levels in the top 20 cm of sediment, in
mg/kg dry wt, were 1.0 to 1.3 for Cd, 5.6 to 9.6 Co, 5.0 to 24.9
Cr, 7.0 to 43.7 Cu, 9.2 to 24.1 Ni, 18.2 to 63.7 Pb, and 29.0 to
123.4 Zn. Maxilnum marshwater concentrations, in mg/l, were 1.0
Cd, 0.001 Co, 1.0 Cr, 9.0 Cu, 0.001 Ni, 50 Pb, and 54 Zn.
3054.
Newkirk, G. 1978. Interaction of genotype and salinity in
larvae of the oyster Crassostrea virginica. Marine
Biology 48:227-234.
Adult oysters were obtained from 4 populations and
spawned in the laboratory. Larvae from within-population crosses
and hybrid crosses raised at 4 salinities between 12 and 30 0/00
showed no significant differences in survival. However, one set
of hybrids did show dominance in survival. There were significant
genotype-environment interaction differences between populations
in growth rate, which depended upon salinity. Non-additive
genetic effects in the hybrid crosses were observed, but direction
and magnitude was dependent upon salinity. There was as much
difference between populations from the same estuary as between
populations from geographically isolated populations.
3055.
Nielsen, S.A. 1974. Vertical concentration gradients of
heavy metals in cultured mussels. New Zealand Jour.
Marine Freshwater Res. 8:631-636.
Cultured mussels, Perna canaliculus, from two widely
separated locations in N.Z. were analysed for variations in content
395
-------
of selected metals with water depth. Perna, which are grown on
vertically suspended ropes to a depth of 9 m, were analysed for
Cd, Pb, Fe and Zn at 1 m intervals. At one location (Kenepuru
Sound), Cd, Pb, and Fe increased with depth, Zn decreased. At the
second location (Waiheke I.), concentrations of all 4 metals
remained essentially constant with depth. Author attributes
differences in vertical concentration gradients to differences in
mixing of the water column at the two locations. This may also
cause variations in the type of food organisms with depth, or in
variations in the ratio of particulate:dissolved metal levels with
depth. Either or both of these conditions could result in
differences in the bioavailability of metals with depth.
3056.
Nielsen, S.A. and A. Nathan. 1975. Heavy metal levels in
New Zealand molluscs. New Zealand Jour. Marine
Freshwater Res. 9:467-481.
Cadmium, lead, copper, mercury, zinc, and iron
concentrations were determined in 13 species of edible molluscs,
including all species normally found in N.Z., from 199 sites.
Average concentrations, in mg/kg wet wt soft parts, were:
Crassostrea glomerata
Ostrea lutaria
Perna canaliculus
Mytilus edulis
Pecten novaezelandiae
stomach
gonad
adductor muscle
Haliotis iris
Paphies ventricosa
Paphies australis
Paphies subtriangulata
Aulacomya maoriana
Anomia walteri
Chione stutChburyi
Modiolus neozelanicus
Cd
13
3.9
0.3
0.6
0.2
137
1.5
0.5
0.2
O. 1
O. 1
0.3
0.9
2.0
0.2
0.04
Pb
0.9
0.7
1.8
0.7
1.1
1.2
0.3
0.5
0.5
0.8
0.4
0.7
0.5
0.4
1.8
Zn
337
66
21
14
21
24
27
16
13
10
13
7
8
19
10
Cu
"""TiC')
11
2
8
1
10
2
7
2
1
5
9
14
Iron was relatively high in most species; values up to 280 mg/kg
wet wt soft parts were found in Perna canaliculus. For all .
metals, wide variations occurred between locations; explanations
for some of these variations are presented.
396
-------
3057 .
Ogino, C. and H. Takeda. 1978. Requirements of rainbow
trout for dietary calcium and phosphorus. Bull. Japan.
Soc. Sci. Fish. 44:1019-1022. (In Japanese, English
abstract) .
Trout were fed purified diets for 6 weeks containing
from 300 to 3400 mg Ca/kg and from 650 to 10,900 mg P/kg. The
rearing water contained 20 to 23 mg Call and 0.002 mg P/l.
Dietary P levels greatly affected growth, body composition, and
mineral composition (Ca, P, and Mg) of the body and vertebrae.
Dietary calcium levels did not influence growth or body
composition. The available phosphorus level required to maintain
a nomal growth of experimental fish was estimated to be 0.7 to
0.8% of their diet.
3058.
Ogino, C. and G.-Y. Yang. 1978. Requirement of rainbow
trout for dietary zinc. Bull. Japan. Soc. Sci. Fish.
44: 1015-1018.
Trout were fed diets containing from 1.0 to 30.0 mg/kg
of zinc. Zinc was an essential trace element in the diet of trout
though rearing water contained a low concentration (11 ug/l) of
this element. Fish fed a diet low in zinc content (1.0 mg/kg)
showed an extremely low growth rate, high mortality, and suffered
from cataracts in the eyes and erosion of fins and skin. Dietary
zinc levels also influenced digestibility of protein and, to a
lesser degree, carbohydrates. Proximate body composition and
contents of Cu, Fe, and Zn in different organs varied according to
dietary zinc. Judging from the growth rate, an adequate zinc
content in the diet of rainbow trout was estimated to be 15 to 30
mg/kg.
3059.
Payton, P.H., S.B. Hild, C.U. Oertti, and A.D. Suttle, Jr.
1977. Strontium-90 in the western Gulf of Mexico.
Health Physics 33:143-145.
Strontium-90 concentrations, nomalized to calcium
content, in marine invertebrates collected in 1972 from the
western Gulf of Mexico were: 4.22 nCi Sr-90/kg Ca in coral
Montastrea cavernosa, 0.68 in hermit crab Clibanarius vittatus,
0.06 in two bivalve molluscs Amusium papyraceum and Laevicardium
laevigatum, and ranged from 0.02 to 0.57 in 9 species of gastropod
molluscs. The freshwater clam, Cyrtonaias tampicoensis, contained
0.04 nCi Sr-90/kg Ca. Gulf seawater contained 0.0001 nCi/l, or
1.37 nCi Sr-90/kg Ca.
397
-------
3060.
Pentreath, R.J. 1978. 237pu experiments with the plaice
Pleuronectes platessa. Marine Biology 48:327-335.
Metabolism of Pu-237 (a high Rpecific activity,
gamma-emitting isotope of plutonium) by plaice, f. platessa, was
studied. Very little of the isotope was incorporated into fish
after 2 months exposure to labelled water or sediment. Oral
retention from labelled foods, annelids Nereis diversicolor, or
hepatopancreas of crabs Carcinus maenas, was also poor. Apart
from the gut itself, no incorporation of Pu-237 could be
demonstrated. Injected Pu-237 was eliminated very slowly; rate of
Pu-237 loss was inversely related to growth rate of fish. Growing
fish incorporated a relatively larger fraction of Pu-237 body
burden into skeletal material at the expense of the isotopic
content of liver. Very little Pu-237 was incorporated into muscle.
Pentreath, R.J. 1978. 237pu experiments with the
thornback ray Raja clavata. Marine Biology 48:337-342.
Metabolism of Pu-237 (a high specific activity,
gamma-emitting isotope of plutonium) by R. clavata was studied.
Unlike plaice, Pleuronectes platessa, thornback rays absorbed
plutonium across the gut wall. Liver accumulated up to 0.2% of
Pu-237 given in a single labelled meal of annelid, Nereis
diversicolor, or hepatopancreas of crab, Carcinus maenas, after 12
days. Direct injection of the isotope into muscle resulted in
extremely slow rates of elimination from rays. Highest internal
concentrations were: spleen, to 935 cpm/g wet wt; liver, to 446;
and gill, to 278. The largest fractions of Pu-237 whole-body
burden, however, were in liver, 12-27%, and skeleton, 10-26%.
3061 .
3062.
Phillips, G.R. and D.R. Buhler. 1978. The relative
contributions of methylmercury from food or water to
rainbow trout (Salmo gairdneri) in a controlled
laboratory environment. Trans. Amer. Fish. Soc.
107 :853-861.
Trout accumulated methylmercury linearly during 24 days
when continually exposed to methylmercury. Exposure was by means
of water solutions (0.07-1.33 ug Hg/l), food consumption
(8.0-380.5 ug Hg/kg fish/day) or both. Methylmercury accumulated
from one source had no influence on rate of uptake from the second
source. Accumulation from both sources was quantitatively
398
-------
additive, which validates a frequently used assumption. Trout
exposed to 1. 33 ug Hg/I and fed 3080 ug Hg/kg had methylmercury
accumulation rate of 4120 ug Hg/kg wet wt/day and consumption rate
of 379 ug Hg/kg/day. Maximum body burdens reached 8630 ug Hg/kg
wet wt under these conditions. Food consumption rate and
therefore growth rate had no influence on rate of mercury
accumulation from water. Nearly 70% of methylmercury ingested and
10% of methylmercury passed over gills was assimilated.
3063.
Roberts, E., R. Spewak, S. Stryker, and S. Tracey. 1975.
Compilation of state data for eight selected toxic
substances, vols. 1-5. U.S. Environ. Protect. Agency
Repts. EPA 560/7-75-001-1 through EPA 560/7-75-001-5.
Avail. as PB-248-660 through PB-248-664 from Nat. Tech.
Inform. Serv., U.S. Dept. of Comm., Springfield, VA
22151 .
Compilation of monitoring data from agencies in 20
states on biological effects of arsenic, beryllium, cadmium,
chromium, lead, mercury, and other compounds was completed.
Emphasis was on residue concentrations in plants, fish, shellfish,
ducks, terrestrial wildlife, humans, water, and sediment.
Summaries of state agency data and monitoring capabilities, are
discussed. Volumes also include a directory on each monitoring
agency and a bibliography of 129 citations.
3064.
Sidwell, V.D., A.L. Loomis, K.J. Loomis, P.R. Foncannon,
and D.H. Buzzell. 1978. Composition of the edible
portion of raw (fresh or frozen) crustaceans, finfish,
and mollusks. III. microelements. Marine Fish. Rev.
40 ( 9) : 1-20 .
This report summarizes data from 224 publications on
trace metal contents in flesh of commonly eaten species of marine
and freshwater crustaceans, elasmobranchs, finfishes, molluscs,
echinoderms, mammals, and waterfowl. Data are presented on the
following elements: copper, iron, zinc, manganese, mercury,
organic mercury, lead, arsenic, silver, cadmium, cobalt, selenium,
chromium, vanadium, tin, aluminum, nickel, barium, and molybdenum.
3065.
Sikes, C.S. 1977. Calcium and cation sorption by
Cladophora from the Great Lakes. Jour. Great Lakes
Res., Internat. Assn. Great Lakes Res. . 3: 100-105.
399
-------
Sorption of calcium and strontium was studied in the
alga Cladophora glomerata. Total calcium uptake was directly
proportional to concentration in the medium at low levels (2-20 mg
Call). However, algae became saturated at high Ca levels after 4
weeks (13,000 mg Ca/kg at 20-100 mg Call). Uptake was largely an
ion-exchange reaction favoring polyvalent cations of small
hydrated radius. Strontium uptake mimicked that of calcium, but
the alga preferentially adsorbed Sr over Ca by 1.25X. Maximum
concentration factors were 775 for Ca and 1070 for Sr. Calcium
and Sr sorption by Cladophora from each of the Great Lakes had the
same cationic sorptive capacity. Results of experiments with a
Lake Michigan isolate should, therefore, be applicable to natural
populations of the alga. Turbulence and pH contributed to the
variability of calcium sorption by Cladophora by affecting
diffusion gradients and solubility of calcium, respectively.
3066.
Singh, H. and J.S. Mar~@5II. 1977. A preliminary
assessment of 239, Pu concentrations in a stream
near Argonne National Laboratory. Health Physics
32 : 195 -198 .
Low level radioactive wastes empty into Sawmill Creek,
Illinois, from Argonne's nuclear facilities following clean-up and
dilution in the Argonne National Laboratory sewage plant.
Plutonium-239 concentrations detected in the creek were:
unfiltered water, upstream 0.41 fCi/1 and at discharge 102;
sediment, upstream 1490 fCi/kg wet wt and downstream 8900; algae
Cladophora sp., upstream 314 fCi/kg wet wt and downstream 5160;
isopods, upstream 2880 fCi/kg wet wt and downstream 3920;
sunfishes (Centrarchidae), downstream 142 fCi/kg wet wt in gill
and 1040 in gastrointestinal tract. Pu-239 ratios of downstream
concentration to upstream were 16 in Cladophora, 1.4 in isopods,
6.3 in fish gills, 46 in fish G.I. tract, 246 in unfiltered water,
and 6.0 in sed iments.
3067.
Smart, R.M. and J.W. Barko. 1978. Influence of sediment
salinity and nutrients on the physiological ecology of
selected salt marsh plants. Estuarine Coastal Marine
Science 7:487-495.
Influence of salinity and nutrients on Spartina
alterniflora, ~. foliosa, ~. patens, and Distichlis spicata was
400
-------
studied under sllnulated tidal inundation. Growth differences were
attributed to differences in sedllnent salinity and nutrients.
Relative salinity tolerances of the four species were comparable
to field results reported in literature. Salinity tolerance, in
decreasing order, was: D. spicata, S. alterniflora, S. foliosa,
and S. patens. The specIes studied are known to be salt
secreting, and were shown to be capable of ion exclusion which, in
some cases, resulted in increased sediment salinity. Selective
uptake of potassium was demonstrated; tissue potassium was
linearly related to sediment salinity. Importance of salinity on
plant growth in natural marshes is discussed in relation to other
environmental factors.
3068.
Sosnowski, S.L. and J.H. Gentile. 1978. Toxicological
comparison of natural and cultured populations of
Acartia tonsa to cadmium, copper, and mercury. Jour.
Fish. Res. Bd. Canada 35:1366-1369.
Cultured copepods, A. tonsa, manifested a reproducible
toxicological response through-six generations, with no
significant differences in responses of F1 and F6 generations
to salts of cadmium, copper, and mercury. Cultured and field
populations (parental) exposed to cadmium showed similar
toxicological effects. The response variability of cultured
populations was less than in field populations. LC-50 (96 hr)
concentrations for cultured (F1) populations were go ug Cd/I, 31
ug Cull, and 10 ug Hg/l. Presence and abundance of ova, and
unicellular glands in the circumesophogeal region were useful as
criteria for evaluating the nutritional condition of test
populations.
3069.
Tamura, Y., T. Maki, H. Yamada, Y. Shimamura, S. Ochiai, S.
Nishigaki, and Y. Kllnura. 1975. Studies on the
behavior of accumulation of trace elements in fishes.
III. accumulation of selenium and mercury in various
tissues of tuna. Tokyo Toritsu Eisei Kenkyusho Nenpo
26(1):200-204. (Translated by Translation Bur.,
Multilingual Servo Div., Dept. Seer. State Canada,
Fish. Mar. Servo No. 3994, 1977:11 pp).
Bluefin tuna, albacore, bigeye tuna, yellowfin tuna,
and bonito from a Tokyo market were analyzed for selenium, total
mercury and methylmercury. Maximum tissue levels of Se were
between 10 and 15 mg/kg wet wt in liver, spleen, and kidney and
ranged from 0.5 to 1.3 mg/kg in white muscle. Maximum
concentrations of total Hg ranged from 0.1 to 0.7 mg/kg wet wt in
401
-------
spleen, liver, and muscle, and were 0.3 mg/l in blood. Percentage
of methyl-Hg of' total Hg averaged 93% in white muscle of tuna, but
was lower, about 55%, in red muscle and liver. Levels of Se
exceeded Hg in all tissues; the least molar ratio was 5.8:1 in
muscle and >100:1 in other organs. No correlation between Se and
total Hg accumulation was observed. Higher levels of Se in muscle
tissues were found on the side of the abdomen, while total Hg
tended to be located higher in back muscle. Accumulation of Se in
red muscle was 7X higher than in white muscle.
3070.
Townes, M.M. 1978. The Participation of ionic strength
and pH in the contraction induced in Vorticella by
calcium and magnesium. Compo Biochem. Physiol.
61A:555-558.
Glycerinated stalks of the protozoan, Vorticella
co~valla~+ can be induced to contract by application of either
Ca T or . Contractions varied as a function of pH and
ionic strength (NaCI) of bat~ing fluids. Coiling in the presence
of ~+ is atypical while Ca +-contractions are typical of
living vort;cellid coiling. Increasing ionic strength prevented
~+ coiling. Ca2+ coiling at pH 6.8 and 7.0 was inhibited by
low ionic strength a~d enhanced by high ionic strength. High
concentrations of Ca + prevented the ionic strength repression
of contractions.
Umehara, S. and M. Oguri. 1978. Effects of environmental
calcium content on plasma calcium levels in goldfish.
Bull. Japan. Soc. Sci. Fish. 44:827-833.
Plasma Ca2+ level increased markedly, up to about 5.0
meq/l, in goldfish, Carassius auratus, within 7 days of transfer
to 1/3 strength seawater, and remained high for 21 days. Plasma
K+ and Na+ also increased to about 5.0 and 180 meq/l,
resP8?tively, in 1/3 seawa~er. Cation levels did not change in
goldflSh transferred to Ca +-rich freshwater. In goldfish in
1/3 seawater, histological changes in the corpuscle of Stannius
oc~urred, water movement rate in intestine increased, and
Ca +-activated ATPase activity in gill i~creased. These changes
were not observed in goldfish held in Ca +-rich freshwater.
307 1 .
3072.
Weis, J.S. 1978. Interactions of methylmercury, cadmium,
and salinity on regeneration in the fiddler crabs Uca
pugilator, U. pugnax and U. minax. Marine Biology---
"49:119-124.-
402
-------
After multiple autotomy in 3 species of fiddler crabs,
methylmercury at 0.5 mg/l, or cadmium at 2.0 mg/l, retarded limb
regeneration and ecdysis. When crabs in seawater were exposed to
a mixture of both metals, the retardation effect was increased,
indicating additive interaction. In 50% seawater (15 0/00 S),
effects of cadmium were greatly intensified so that growth of limb
buds was extremely slow, or nil. When methylmercury was present
at the same time, severe effects of Cd were somewhat lessened,
indicating an antagonistic interaction. Adding additional calcium
to 50% seawater also decreased severity of cadmium effect, thus
supporting the idea of a calcium-cadmium competition.
3073.
Westerman, A.G. and W.J. Birge. 1978. Accelerated rate of
albinism in channel catfish exposed to metals. Progr.
Fish-Culturist 40:143-146.
Salts of As, Cd, Cu, Hg, Se, and Zn were shown to
increase the incidence of albinism during 5 years of experiments
with channel catfish, Ictalurus punctatus. Metal-induced albinism
resulted from exposure of both adult fish and eggs. In egg
bioassays, exposed populations consistently exhibited higher
percentages, up to 6.3%, of albinos in fry than controls; however
frequencies did not vary significantly among the six metals or
among exposure concentrations which ranged from 0.5 to 250 ug/l.
Metal contamination in a hatchery water supply yielded frequencies
of albinos corresponding directly with those observed for
metal-exposed laboratory populations. Since albinism is
deleterious to fish survival and production, caution is
recommended when using metallic compounds in hatcheries. Tests
for albinism may prove useful in screening aquatic contaminants
for mutagenic potential.
3074.
Willis, J.N. and N.Y. Jones. 1977. The use of uniform
labeling with zinc-65 to measure stable zinc turnover
in the mosquito fish, Gambusia affinis - I.
retention. Health Physics 32:381-387.
Juveniles of G. affinis, were reared for about 100 days
in water uniformly labelled with 1.0 mCi Zn-65 Cl2 plus znS04
(for a total concentration of 200 ug Zn/l), until they attained
the specific activity of the environment. Specific activities of
zinc, in nCi Zn-65/ug Zn, after 100 days were 1.7 in filtered
water, 1.1 in particulate water, 1.3 in algae, and 1.2 in
mosquitofish. Retention of Zn-65 in these fish was monitored over
120 days in a non-labeled zinc environment. Analysis of the
403
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retention curve yielded three mathematical reservoirs of stable Zn
each containing 8.7,4.3 and 91.1% of the element with measured
rate constants of 0.280, 0.051 and 0.003/day, respectively.
3075.
Wrench, J.J. 1978. Selenium metabolism in the marine
phytoplankters Tetraselmis tetrathele and Dunaliella
minuta. Marine Biology 49:231-236.
Radioactive selenite-75 was used to investigate
metabolic transformation of inorganic selenium by 2 species of
marine algae. The majority of radioselenium taken up from culture
media during growth became associated with cellular protein. A
small quantity of this protein-bound Se could be volatilized by
treatment with strong acid, suggesting the presence of hydrogen
selenide. However, the principal fraction of selenium was
integrated into the primary protein structure, as revealed by the
presence of seleno-analogues of the sulphur amino acids. Selenium
amino acids were also detected in non-protein extracts.
3076.
Yannai, S. and K. Sachs. 1978. Mercury compounds in some
eastern Mediterranean fishes, invertebrates, and their
habitats. Environmental Research 16:408-418.
Total mercury content of the cornmon edible species of
fishes and invertebrates taken along the Mediterranean coast of
Israel was determined. Size (reflecting age) and position in the
food chain were the factors which most affected concentration of
total mercury in fish. In most cases, carnivorous fish had higher
mercury levels than herbivorous and omnivorous species. Among the
fishes with highest mercury content in edible tissues (i.e.,
Upeneus moluccensis with 0.44 to 0.56 rng Hg/kg wet wt, Merluccius
merluccius with 0.88, Saurida undosquamis with 0.51, and Sphyraena
sphyraena with 0.62 rng/kg), methylmercury concentrations accounted
for 77 to 100% of total mercury. Barnacles Balanus eburnus and B.
amphitrite, tunicate Ciona intentinalus, plus serpulid worms,
other tunicates, crustaceans, molluscs, and bryozoan species
collected along the northern Mediterranean coast of Israel
contained total mercury concentrations of 0.02 to 0.38 rng/kg wet
wt. These benthic invertebrates reflected concentrations in their
habitat, being with tissue concentrations higher in animals from
the more heavily polluted Haifa Bay and environs. Sediment
mercury concentrations were 0.04 to 0.05 mg/kg dry wt in sites
with no pollution and 0.01 to 0.70 rng/kg in sites with industrial
or domestic pollution or both. Water concentrations ranged from
0.01 to 0.07 ug Hg/l in unpolluted and 0.02 to 1.90 ug/l in
404
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polluted environments. Only in the immediate vicinity of a
chemical plant outfall were concentrations of mercury in water and
sednnent significantly greater than in other sampling stations
along the northern coast.
3077.
Akesson, B. and J.D. Costlow. 1978. Effects of
temperature and salinity on the life cycle of
Ophryotrocha diadema (Polychaeta, Dorvilleidae).
Ophelia 17:215-229.
Mortality, maturation, and reproductive success of
various life stages of a stenohaline polychaete worm was observed
in salinities from 15 to 45 0/00 at temperatures of 15 to 25 c.
At 15 and 20 0/00 S, all larvae and adults died within 2 days.
Optimum conditions for survival were obtained at 35 0/00 S and 18
C. Optllnum egg production was at 35 0/00 Sand 25 C. Maximum
growth rate and shortest development time to sexual maturity were
at 30 and 35 0/00 Sand 25 C. The number of eggs per egg mass was
salinity dependent, with a maximum at 35 0/00. At low
temperatures of 15 and 18 C, survival was better at 40 than at 25
0/00 S; at 21 and 25 C, that pattern was reversed. Growth rate
indicated a snnilar change, which occurred between 15 and 18 C.
At 15 C, larvae maintained at 40 0/00 S exhibit superior survival,
but at higher temperatures, greater survival was observed among
larvae reared at 25 0/00.
3078.
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. volume 1. boron. U.S.
Environ. Protect. Agen. Rept. EPA-560/2-75-005a.
Avail. as PB-245 984 from Nat. Tech. Inform. Serv.,
U.S. Dept. Commerce, Springfield, VA 22151:111 pp.
A comprehensive review of 225 articles was conducted on
the physical and chemical properties of boron, environmental
exposure factors related to its consumption and use, health and
environmental effects resulting from B exposure, and applicable
regulations and standards governing its use. Boron is found at
concentrations of 10 to 30 mg/kg in soils, about 0.1 mg/l in
surface waters, and 4.5 mg/l in seawater. It enters the
environment at a rate of approximately 32,000 metric tons B/year
for the United States; most ends up in the waters. About one-half
enters water directly from laundry products and sewage. Effects
of B have been studied with bacteria, protozoans, insects, fish,
birds, and mammals. Boron compounds are absorbed by intestine,
mucous membranes, and skin. Excretion is mainly via urine, but
405
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complete excretion is slow and boron may accumulate. Inorganic
borates are toxic, apparently complexing hydroxy compounds and
interfering with protein synthesis. Organoborate compounds exert
physiological effects on the peripheral and central nervous
system, acting a~ spasmolytics, sedatives and convulsants,
depending upon the structure. Boranes produce toxic effects by
creating embolisms of hydrogen gas as they react with tissue. No
boron carcinogenicity has been reported. Erythema and swelling
may develop in individuals sensitive to boron. Boric acid is a
potent teratogen when applied directly to frog or chick embryo.
Its compounds are selectively accumulated by some types of
tumors. Boron is a growth requirement for plants and not animals,
but excess amounts are phytotoxic. Plant species vary greatly in
sensitivity to B toxicity. Long-range effects of boron compounds
on birds, fish, and other aquatic organisms have not been
investigated. Medical and household use of boric acid solutions
as antiseptics has led to numerous accidental poisonings through
ingestion or absorption through skin, particularly in infants.
Contamination of air with boron compounds does not appear to pose
an environmental problem. Future build-up of boron in ground
waters could cause detrimental effects to aquatic and other
species of plants and animals. Plant toxicity effects could
become generalized if boron-containing cleansing agents become
more widely used. Acute toxicity of humans to boric acid has led
to poisonings which could probably have been prevented by minimal
use of warning labels or substitution.
3079.
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. volume III. nickel.
U.S. Environ. Protect. Agen. Rept. EPA-560/2-75-005c.
Avail. as PB-245 986 through Nat. Tech. Inform. Serv.,
U.S Dept. Commerce, Springfield, VA 22151:89 pp.
A comprehensive review of 244 articles was conducted on
the physical and chemical properties of nickel, environmental
exposure factors related to its consumption and use, health and
environmental effects resulting from Ni exposure, and regulations
and standard~ governing its use. Of the estimated 4895 metric
tons/year of nickel entering the environment for the United
States, over 90% arises from combustion of fuel oil and enters the
abmosphere as oxides. A significant amount of nickel waste
(15,000 kg Ni/year) arises from the electroplating industry.
Waste effluents from nickel sulfate production are insignificant
in comparison to other sources. Toxic concentrations of nickel in
soil and waters occur both naturally and as a result of man's
406
-------
activities in foreign countries (including Canada), but have not
been reported in the United States except as local effects of
plating bath and similar effluents. Many persons exhibit allergic
reactions to nickel and nickel compounds. The concentration at or
below which no contact allergic reaction occurs in
nickel-sensitive persons is 1.0 umole Ni/l (about 59 ug/l).
Sensitivity to nickel often occurs concurrently with sensitivity
to cobalt and chromium. Various nickel compounds, particularly
sulfide and carbonyl, are known carcinogens, and various
environmental exposures to nickel in other countries seem to
correlate with increased incidence of tumors in man. Effects of
Ni have been observed with bacteria and yeasts, algae and higher
plants, fungi, protozoans, annelids, crustaceans, echinoderms,
molluscs, insects, fish, amphibians, birds, and mammals. Nickel
is absorbed through intestines, lungs, and abraded skin; urinary
excretion is the principal mode of elimination. Nickel is present
in both an ultrafiltrable and a protein-bound form in blood. A
dietary requirement for Ni has not been established. Nickel ions
can replace calcium ions in the generation of action potentials in
muscle, but duration of the potential is increased. Nickel is
absorbed by plants through roots, and phytotoxicity occurs with
excessive nickel levels. Nickel ions inhibit growth of various
microorganisms and produce a progressive narcosis in Paramecium.
Although Ni-containing industrial wastes are probably
insignificant except on a very localized basis, nickel content of
petroleum has caused a continuing world-wide increase in
atmospheric levels of nickel. This source of nickel could pose
future health and environmental hazards if the increase continues.
3080.
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. volume IV. selenium.
U.S. Environ. Protect. Agen. Rept. EPA-560/2-75-005d.
Avail. as PB-245 987 from Nat. Tech. Inform. Serv.,
U.S. Dept. Commerce, Springfield, VA 22151:92 pp.
A total of 63 articles were reviewed on physical and
chemical properties of selenium, environmental exposure factors
related to its consumption and use, health and environmental
effects resulting from Se exposure, and applicable regulations and
standards governing its use. Selenium is beneficial or essential
in amounts from trace to mg/kg or mg/l concentrations for humans,
animals, and plants, but toxic to animals at concentrations which
may exist in the environment. Sensitivity to Se and its compounds
is extremely variable in all classes of organisms~ Selenium is
407
-------
widely distributed in nature, and is found in greater
concentrations associated with sulfide minerals of lead, iron,
copper and other metals. The major source of Se is from
weathering of natural rock. Selenium entering the environment
from activities of man is estimated at 3500 metric tons/year, of
which most is attributed to combustion of coal. These
contributions are small in comparison to natural sources.
Selenium and its compounds are moderately toxic to man; effects
disappear when exposure ceases. A number of cases of accidental
human poisoning by selenium in well water and by selenium sulfide
(dandruff treatment) have been reported. Effects of Se have been
observed in algae and higher plants, bacteria and yeasts,
crustaceans, molluscs, insects, fish, birds, and mammals.
Selenium compounds are absorbed through small intestine and
excreted in urine, feces, exhaled air and perspiration. Inorganic
selenium salts become tightly bound to protein, binding with free
sulfhydryl groups. Organoselenium'compounds are metabolized like
their sulfur analogs. Selenium is a growth requirement in some
animals. Plants are efficient accumulators of selenium,
especially organoselenium, but tolerance of plants to selenium
varies greatly. Selenium "indicator" plants can accumulate
thousands of mg Se/kg without ill effects, and in these plants, Se
promotes growth. Concentrations of 25 to 50 mg/kg may produce
phytotoxicity in crop plants. Plants and waters high in Se are
significant dangers to livestock in seleniferous zones due to the
extreme toxicity. Urinary Se levels appear higher in humans
ingesting foods raised in seleniferous areas, and chronic and
acute cases of poisoning have been reported. Selenium is
transmitted from the mother to the fetus. Reduced reproduction
rates and weakened offspring occur in selenium-deficient mothers.
Excessive selenium may act as teratogens and antitumor agents
rather than carcinogens. Selenium compounds inhibit growth in
many microorganisms. Animals, plants, and microorganisms reduce
selenium, but metabolic oxidation has not been clearly established
in any species.
308 1 .
Anon. 1975. Preliminary investigation of effects on the
environment of boron, indium, nickel, selenium, tin,
vanadium and their compounds. volume V. tin. U.S.
Environ. Protect. Agen. Rept. EPA-560/2-75-005e.
Avail. as PB-245 988 from Nat. Tech. Inform. Serv.,
U.S. Dept. Commerce, Springfield, VA 22151:80 pp.
A total of 67 articles were reviewed on the physical
and chemical properties of tin, environmental exposure factors
related to consumption and use, health and environmental effects
408
-------
resulting from Sn exposure, and on applicable regulations and
standards governing use of tin. There is almost no contamination
of the environment from processing of tin or its compounds because
of recovery and reprocessing of tin wastes. The significant
source of environmental contamination is scrap tin cans and tin
plate disposal. This tin quickly enters the soil and surface
water. One source of contamination of tin is from food stored in
tin cans. Although serious health problems from this appear to be
unusual, ingestion by humans of tin from cans is continually under
surveillance. An unofficial limit in foods of 300 mg Sn/kg has
been set. Effects of Sn have been observed in algae and higher
plants, fungi, bacteria, protozoans, zooplankton, coelenterates,
annelids, echinoderms, molluscs, nematodes, fish, and mammals.
Seawater contains about 3.0 ug Sn/l. Tin has been found in algae,
but not in most other marine organisms. Inorganic tin compounds
are relatively nontoxic. Inorganic tin compounds are poorly
absorbed by intestine, and most ingested Sn is excreted in feces.
Tin is essential for normal growth in rats. Some Sn may be
absorbed through lungs, but inhaled tin oxide particles produce
only benign lesions in lung tissue. Tin does not appear to be a
carcinogen, teratogen or allergen. Organotin compounds may be
absorbed through intestine and skin, and are relatively toxic,
depending upon type of organic groups present, and degree of
substitutioo on the Sn. Trialkyl tins are the most toxic to
mammals, producing cerebral edema and hepatic degeneration.
Tetraalkyltins are converted to trialkyltins in liver; thus
toxicity symptoms are the same. Dialkytins are excreted in bile,
and fatal peritonitis or liver damage may occur. Monoalkyltins
produce gastric irritation. Organotins have proven effective as
insecticides, molluscides, vermicides, and fungicides. Tin
accumulation by plants varies with species. Lichens and mosses
contain relatively high levels of Sn. Phytotoxicity can result
from excessive applications, but actions of tin on plants are not
clearly established.
3082.
Anon. 1978. Criteria (dose/effect relationships) for
cadmium. Report of a Working Group of Experts prepared
for the Commission of the European Communities,
Directorate-General for Social Affairs, Health and
Safety Directorate. Pergamon Press, N.Y.:202 pp.
Concern for chronic toxicity of cadmium to humans has
been raised in part because of the outbreak of Itai-Itai disease
in J~pan. Cadmium levels in air are verY3low: 0.0001 to 0.043
ug/m in rural areas and 0.002-0.700 ug/m in cities, reaching
5.0 ug/~ near Cd emission sources. Drinking water usually
409
-------
contains <5.0 ug Cd/I. Concentrations of cadmium in most
foodstuffs from non-contaminated areas are below 0.1 mg/kg, but
liver, kidney, and shellfish can contain much higher levels of
cadmium. In general, there is little evidence for Cd
concentration in marine food chains; however, oysters, which have
a remarkable ability to accumulate cadmium above low levels in
seawater, are an exception. For human populations in non-polluted
areas, food constitutes the most important source of cadmium
(median 43.0 ug/day). Airborn cadmium may be an important source
of exposure for human populations close to Cd emission sources or
heavy smokers. Total daily absorption of Cd for
non-occupationally exposed adults range from 0.36 to 9.80 ug. The
main targets of cadmium in humans are the gastrointestinal tract
after acute ingestion, and lungs after inhalation during
short-term exposure. After long-term exposure, lungs and kidneys
are the target organs. The Subcommittee on Toxicity of Metals
under the Permanent Commission and International Association of
Occupational Health has proposed 200 mg Cd/kg wet wt as the
tentative critical concentration in human kidney cortex. The
threshold effect level of cadmium by absorption is calculated to
be 10-12 ug/day. A list of 560 references is appended.
3083.
Augier, H., G. Gilles, and G. Ramonda. 1978. Recherche
sur la pollution mercurielle du milieu maritime dans la
region de Marseille (Mediterranee, France): partie 1.
degre de contamination par Ie mercure de la phanerogame
marine Posidonia oceanica delile a proximite du
complexe portuaire et dans la zone de rejet due grand
collecteur d'egouts de la ville de Marseille. Environ.
Pollution 17:269-285.
Concentrations of mercury were determined in roots,
rhizomes and leaves of the marine plant Posidonia oceanica
collected from the western Mediterranean Sea in the first half of
1976. Results revealed serious mercury contamination of this
plant in the main bay and adjoining small bays of Marseilles,
France, with a particularly high level near the outrlow of Cortiou
sewer, where sediment contained 15.1 mg Hg/kg. Maximum mercury
concentrations in Posidonia from 7 sites ranged from 0.14 to 1.07
mg/kg dry wt in roots, 0.12 to 2.50 in rhizomes, and 0.07 to 51.50
in leaves.
3084.
Beattie, J.H. and D. Pascoe. 1978. Cadmium uptake by
rainbow trout, Salmo ~airdneri eggs and alevins. Jour.
Fish Biology 13:631- 37.
410
-------
Uptake of cadmium by trout zygotes and alevins from
water at concentrations between 0.01 and 50.0 mg Cd/l was
investigated. Cadmium content of zygotes and alevins increased
with time and exposure concentration. Lower Cd levels were
detected in alevins than eggs. Cadmium concentrations, in mg/kg
dry wt, after 100 hrs exposure to 10 mg Cd/I, were 570 in zygotes
and 8 in alevins. In 50 mg Cd/I, zygotes contained 506 mg Cd/kg
dry wt by 10 hrs; all zygotes were dead by 32 hrs. All alevins
died within 100 hrs at 50 mg Cd/I. Most cadmium (98%) in zygotes
was associated with chorion, which may explain the considerable
reduction in cadmium concentration observed in alevins after
hatching. Alevins hatching from zygotes exposed to cadmium
survived longer in cadmium solutions than alevins with no previous
exposure as zygotes. This suggests that pretreatment of zygotes
with Cd serves some protective function. Behavioral and
pathological signs of cadmium poisoning such as erratic swimming
and blood clotting in alevins were observed.
3085.
Benoit, D.A. and G.W. Holcombe. 1978. Toxic effects of
zinc on fathead minnows Pimephales promelas in soft
water. Jour. Fish Biology 13:701-708.
A fathead minnow life-cycle exposure to zinc
concentrations from 2.0 to 577.0 ug/l was conducted. The most
sensitive indicators of zinc toxicity were egg adhesiveness and
fragility, which were significantly affected at 145 ug Zn/l and
higher, but were not affected at 78 ug Zn/l and lower. These
effects occurred shortly after eggs were spawned (during water
hardening) and, therefore, were not related to effects on parental
fish. Hatchability and survival of larvae were significantly
reduced, and deformities at hatching were significantly increased
at 295 ug Zn/l and above. Acclimated and unacclimated groups of
larvae exposed to identical zinc concentrations for 8 weeks after
hatch showed only slight differences in sensitivity.
3086.
Bhan, S. and A.P. Mansuri. 1978. Adaptations to osmotic
stress in the marine-euryhaline teleost Periophthalmus
dipes: tissue water and mineral content. Indian Jour.
Marine Sci. 7:134-136.
Water, sodium, potassium, calcium, and phosphorus
contents were estimated in white muscle, red muscle, gills, liver,
heart, and kidney of P. dipes after adaptation to various
concentrations of seawater from full strength to freshwater.
Water content did not vary significantly in any tissue after
411
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adaptation to various salinities. Sodium, K, Ca, and P levels of
different tissues showed a decreasing trend in lowered salinities
and absolute freshwater. Authors conclude that this fish has the
ability to regulate the mineral status of its tissues according to
salinity and becomes acclimatized gradually to different
salinities without a significant increase of body water.
3087.
Bochenin, V.F., M.Y. Chebotina, and N.V. Kuli~8v. 1978.
Seasonal dynamics in the distribution of Sr and Ca
between the alga Chara tomentosa and the aqueous
medium. Soviet Jour. Ecology 9(1):39-43.
Between 1974 and 1976, water from Lake B. Miassovo,
South Urals, before ice formation contained 4.0 pCi Sr-90/1.
Water below ice in winter contained 5.4 to 14.3 pCi/l, and water
from melted ice contained 0.2 to 0.7 pCi/l. Concentration of
Sr-90, calcium, and total ash in the alga Chara tomentosa
decreased during winter and increased during spring and summer.
Concentrations in alga were 2000 to 7000 pCi Sr-90/kg in winter
and 11,000 to 13,000 pCi/kg in summer. Algae contained 30,000 to
80,000 mg Ca/kg winter and 90,000 to 130,000 mg/kg summer. At all
times of the year, algae accumulated relatively more Ca than
Sr-90.
3088.
Carlsson, S. an93~. Liden. 1977. Observed concentration
factors of Cs and potassium in some species of
fish and littoral plants from an oligotrophic lake.
Soviet Jour. Ecology 8(6):492-495.
Concentration factors of cesium-137 and potassium in
some species of fish (Esox lucius, Perca fluviatilis, Rutilus
rutilus, Scardinius erythropthalmus, Abramis brama, and Tinca
tinca) and aquatic plants (Carex rostrata, Equisetum fluviatile,
and Nuphar luteum) from the oligotrophic Lake Ulkesjon, Sweden,
were determined during 1961 to 1976. Equilibrium concentration
factors of Cs-137 followed a trophic level increase among fish,
with 810 for bream (Abramis) and 3055 for pike (Esox). In plants,
concentration factors were high and varied from 255 for Carex to
2135 for Equisetum growing on soft sediment. Concentration
factors of K ranged from 2400 to 2900 in fish and 2800 to 3360 in
plants. Time dependence, both between years and between seasons,
affected observed concentration factors.
3089.
Cember, H., E.H. Curtis, and B.G. Blaylock.
1978.
Mercury
412
-------
bioconcentration in fish: temperature and
concentration effects. Environ. Pollution
17:311-319.
Mercury bioconcentration factors in bluegill sunfish,
Lepomis macrochirus, were investigated over 688 hours by exposing
fish to CH3Hg-203 Cl at water temperatures of 9, 21, and 33 C
and Hg concentrations of 0.0002, 0.0005, 0.005, and 0.05 mg/l.
Bioconcentration factor increased exponentially with water
temperature at a rate of 0.066 per degree C. Mercury
concentration in water did not influence the bioconcentration
factor; but total uptake by fish increased with increasing water
Hg levels. At 33 C, bioconcentration was 680 to 1144x over water
after 240 hrs, and 2294 to 2454X after 688 hrs exposure to all Hg
concentrations. Mercury concentration in whole fish in 0.005 mg
Hg/l at 33 C for 688 hrs was about 1.3 mg Hg/kg wet wt. Mortality
exceeded 50% under the following conditions during 0.05 mg Hg/l
exposure: 360 hrs at 9 C; 240 hrs at 21 C; and 300 hrs at 33 C.
3090.
Chang, L. W.
review.
1977. Neurotoxic effects of mercury - a
Environmental Research 14:329-373.
Neurotoxic effects of mercury, mainly involving
mammalian and domesticated aviary systems, are reviewed from
approximately 150 references. Pathological findings on Minamata
Bay disease are summarized. A working hypothesis on the mechanism
of mercury action on nervous system is proposed, based on results
of biochemical, physiological, and pathological studies of mercury
intoxication.
3091 .
Chin, B., G.S. Lesowitz, I.A. Bernstein, and B.D. Dinman.
1978. A cellular model for studying accommodation to
environmental stressors: a protective response to
subtoxic exposure to cadmium. Environmental Research
16 :423-431.
Effects of cadmium exposure on the normal cell cycle of
slime mold, Physarum polycephalum, were tested. Periodic exposure
to 56 mg Cd2.,. /1 for 30 min throughout the cell cycle showed two
peaks of sensitivity resulting in mitotic delay of almost 200 min,
one i~ early S stage and one in late G2 stage. Exposure to 11.2
mg Cd +/1 for 30 min in early ~ (0.45 cycle), which does not
delay mitosis, "protected" phKsarum a~inst a mitotic delay of 105
min from 30 min exposure to 4 .~ mg Cd +/1 in late ~ (0.75
cycle). This protection persisted for at least two cell cycles.
413
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3092.
Davies, A.G. 1978. Pollution studies with marine
plankton. part II. heavy metals. Adv. Marine
Biology 15:381-508.
Effects of heavy metals (including Ag, As, Cd, Co, Cr,
Cu, Hg, Mn, Na, Ni, Pb, Po, Se, Si, Sr, Zn, and Zr) and influences
of salinity, temperature, and other compounds on marine
phytoplankton and zooplankton are reviewed. Natural metal
concentrations in water and organisms, sublethal and lethal
toxicity, and metal turnover in laboratory and natural populations
are discussed. Author concludes that if toxicity is determined by
levels of uptake in organisms rather than ambient water
concentrations, differences between laboratory experiments and
natural water conditions disappear and experimental results can be
used to determine the extent of pollution effects in the natural
environment. A list of about 225 references is appended.
3093.
EI-Hawawi, A.S.N. and P.E. King. 1978. Salinity and
temperature tolerance by Nymphon gracile (Leach) and
Achelia echinata (Hodge) (Pycnogonida). Jour. Exp.
Marine BioI. Ecol. 33:213-221.
Tolerance of two species of pycnogonids, Achelia
echinata and Nymphon racile, to a range of salinities (0.0 to
70.0 0/00), temperatures 15 and 25 C), and relative humidities
has been examined. In most instances N. gracile was more
resistant than A. echinata, and is found higher in the littoral
zone during warmer summer months and thus likely to be subjected
to greater environmental fluctuation. At 15 C, mortality reached
50 percent in less than a day for adults of both species in 3.4
0/00 S, and by 12 days for A. echinata and 15 days for N. gracile
in 17.0 0/00 S. No specimens from either group died over 20 days
in 34.0 0/00 S. At higher salinities, mortality reached 50
percent by 13 days for both species in 50 0/00 S, and by 3 and 4
days for !. echinata and~. gracile, respectively, in 70 0/00 S.
Survi val was greater for both species in < 34 0/00 S at 5 C than at
15 C. Adult~. gracile were more tolerant to lowered salinity
than larvae.
3094.
Emery, R.M., D.C. Klopfer and M.C. McShane. 1978. The
ecological export of plutonium from a reprocessing
waste pond. Health Pnysics 34:255-269.
A reprocessing waste pond at Hanford near Richland,
Washington, has been inventoried to determine quantities of
414
-------
plutonium that have accumulated since its formation in 1944. The
ecological behavior of Pu in this pond is similar to that in other
contaminated aquatic systems having widely differing limnological
characteristics. Since its creation, this pond has received about
1.0 Ci of Pu-239,240 and Pu-238, practically all of which has been
retained by sediments. Submerged plants, mainly diatoms and
Potarnogeton, accumulate> 95% of Pu contained in biota. Total
plutonium contained in all biota is about 5.0 mCi. Emergent
insects are the only direct biological route of export, mobilizing
about 5.0 uCi Pu annually, which is the estimated maximum quantity
of Pu exported by waterfowl, other birds, and mammals
collectively. Pu concentrations were also determined for lower
invertebrates, gastropods, and goldfish. There is no apparent
significant export by wind, and it is not likely that Pu has
migrated to ground water via percolation. Although this pond has
a rapid flushing rate, a eutrophic nutrient supply with a diverse
biotic profile, and is in contact with an active terrestrial
environment, it appears to effectively bind Pu and prevent it from
entering pathways to man and other life.
3095.
Fendley, T.T., M.N. Manlove, and I.L. Brisbin, Jr. 1977.
The accumulation and elimination of radiocesium by
naturally contaminated wood ducks. Health Physics
32 :415-422.
Accumulation of radiocesium was studied in hand-reared
ducks released into a South Carolina swamp habitat which had been
contaminated with production reactor effluents. Uptake of
radiocesium by the ducks was described as: In nCi Cs/kg live body
wt = 0.36 + 0.18 (days). Sex of bird had no effect on Cs uptake
rate. The average estimated time required to attain practical
equilibrium was 17.3 days, with a range of 10.2 to 26.8 days.
Ducks which were recaptured after attaining equilibrium
concentrations in the field, averaging 16.6 nCi Cs/kg live body
wt, showed single-component elimination rate curves. Radiocesium
elimination under penned conditions was described as: In %
initial body burden = 4.60 - 0.13 (days). Elimination rate and
body weight showed a negative linear correlation for penned birds
and there was no effect of sex on loss rate. Radiocesium
biological half-times averaged 5.6 days with a range of 3.2 to 9.3
days. Calculations based on biological half-times determined from
studies with penned birds were successful in accurately predicting
both levels and rates of radiocesium accumulation by free-living
birds in the field.
415
-------
3096.
Gardner, G.R. 1978. A review of histopathological effects
of selected contaminants on some marine organisms.
Marine Fisheries Review 40:51-52.
Histological assessment of effects of environmental
pollutants, including copper, mercury, silver, and cadmium, to
selected marine organisms are briefly reviewed. Vascular and
neurosecretory responses are discussed for fish, bivalve molluscs,
and crustaceans.
3097 .
Glickstein, N. 1978. Acute toxicity of mercury and
selenium to Crassostrea gigas embryos and Cancer
magister larvae. Marine Biology 49:113-117.
Possible modification of mercury toxicity by selenium
in embryos of the Pacific oyster, ~. gigas, and larvae of the
crab, C. magister, was investigated. Mercury concentration
elicitIng abnormal development in 50% of oyster embryos (EC-50)
was 5.7 ug/l (48 hr). Mortality in 50% of crab larvae (LC-50)
occurred at 6.6 ug/l (96 hr). EC-50 (48 hr) for selenium was
~O,OOO ug/l for oyster embryos and LC-50 (96 hr) for crab zoeae
was 1040 ug Sell. A high level of selenium l:5000 ug/l) increased
mercury toxicity for both species. Moderate selenium
concentrations of 10 to 1000 ug/l decreased mercury toxicity,
although no statistical verification could be made. The order of
administration of toxicants had no effect on~. gigas embryos.
Early developmental stages ~8 hours of oyster embryos were most
sensitive to dissolved Hg. Toxicant administration 24 hrs after
fertilization resulted in no apparent abnormalities in development.
3098.
Hart, B.A. and B.D. Scaife. 1977. Toxicity and
bioaccumulation of cadmium in Chlorella pyrenoidosa.
Environmental Research 14:401-413.
Cultures of green alga, ~. pyrenoidosa, grown at pH 7
in the presence of 0.0, 0.25, 0.5, and 1.0 mg Cd/l had doubling
times of 11, 21, 22, and 35 hours, respectively. Similarly
exposed cultures grown at pH 8 had doubling times of 11, 16, 17,
and 25 hrs, respectively. C. pyrenoidosa concentrated cadmium up
to 3600 mg Cd/kg protein over 35 hrs in 0.5 mg Cd/l at pH 7. The
amount of Cd accumulated was directly proportional to initial
concentration of metal and was dependent upon pH of the medium.
No accumulation occurred in the dark, at 4 C, or in dead cells.
Cadmium uptake was not affected by calcium, magnesium, molybdenum,
copper, zinc, or cobalt in growth medium, but manganese at 0.2
416
-------
mgll canpletely blocked accrnnulation. Il"on may also playa role
in regulating Cd accumulation. Cells which bad accumulated
cadmium fixed atmospheric CO2 at reduced rates and oxygen
evoluticn was slightly inhibited. The ability of C. pyrenoidosa
to accumulate large concentrations of Cd before shOwing adverse
effects may be related to the presence of cadmium-sequestering
agent(s) within the cell. Concentration of Cd by this alga could
pose a hazard to organisms higher in the freshwater food chain.
Hughes, G.M. and R. Flas. 1978. Zinc content of the gills
of rainbow trout (S. gairdneri) after treatment with
zinc solutions under normoxic and hypoxic conditions.
Jour. Fish Biology 13:117-728.
Forty trout (54-127 g) were divided into 4 groups and
treated as follows: normoxic (oxygen level at 150 um Hg) clean
~ter; hypoxic (oxygen at 60 rII1l Hg) clean water; normoxic water
with 10 DIg zinc/l for 10 hrs; or hypoxic water with 10 DIg zinc/l
for 10 hrs. Zinc content was determined separately for each of
the 4 gill arches en each side of the fish. Zinc concentrations
were greater following Zn treatments, but no significant
difference between hypoxia and normoxia was observed. Gills
contained mean levels of 342 mg Znlkg dry wt with normoxic
conditions, 292 mg/kg with hypoxic, 669 mg/kg with normoxic and 10
DIg Znl1, and 528 mg/kg with hypoxic and 10 mg Zn/l. Mean Zn
content in individual arches ranged frem 597 to 779 mg/kg dry wt
with normoxia and 10 mg Znl1 and from 447 to 587 mg/kg with
hypoxia and 10 mg Zn/l. Differences in concentrations of zinc
were found in different arches whether expressed per gram dry
~ight or per unit surface area of the secondary lamellae. The
first arch bad the lowest and the third arch the highest Zn levels
under all conditions.
3099.
3100.
Inman, C.B.E. and A.P.M. Lockwood. 1977. Sane effects of
methylmercury and lindane an scxiium regulaticn in the
amphipod ~fTlTI~'I1'''us duebeni during changes in the
salinity of its medium. Compo Biochem. Physiol.
58C:67-75.
Ganmarus exposed to sublethal concentrations of
methylmercury ( up to 320 ug/l) , or lindane in 2% seawater for 1 to
4 days showed reductions in hemolymph sodium concentration from
about 250 mM to as low as 210 mH. Lindane-treated animals still
bad larered Na concent.rations after a subsequent period of 7 days
in clean ~ seawater. Prior t.reatment with sublethal
concentrations of methylmercury or lindane resulted in delays
417
-------
of 80 and 120 min, respectively, in the time required for
amphipods to increase active Na uptake when transferred from 100
to 2% seawater. Prior treatment also depressed maximal and
steady-state sodium transport rates.
3101.
Kariya, T., H. Haga, Y. Haga and Y. Kawasaki. 1978.
Studies on the post-mortem identification of the
pollutant in fish killed by water pollution - XII.
cadmium. Bull. Japan. Soc. Sci. Fish. 44:1065-1072.
Toxicity and accumulation of cadmium in goldfish,
Carassius auratus, were investigated. Cd-plating solution I
contained 50,000 mg Cd(CN)2/1 and 100,000 mg NaCI/I, solution II
40,000 mg CdO/1 and 130,000 mg NaCN/I, and solution III 208,000 mg
CdS04.H20/1. LC-50 (48 hr) values for CdCl2 and solution
III were 3.0 to 7.0 mg Cd/I. For Cd-plating solutions I and II it
was 0.3 mg Cd/I. The latter solutions had toxicities greater than
indicated by CN concentration. Of experimentals held in 0.1 mg
Cd/I, higher mortality and higher body cadmium content were
observed for non-feeding groups than feeding groups. Almost all
non-feeding fish were dead by 70 days, with over 0.2 mg Cd/kg in
whole bodies. About half of feeding fish had died by 70 days and
contained less than 0.2 mg Cd/kg. After 30 days in 0.1 mg Cd/I,
as CdCI2' non-feeding fish contained 0.94 mg Cd/kg in kidney and
0.61 mg/kg in hepatopancreas; feeding fish contained 0.31 mg/kg in
kidney and 0.51 in hepatopancreas; and controls had 0.04 and 0.03
mg/kg, respectively. Bone, ovary, and muscle concentrations were
lower than other tissues examined for all 3 groups. High cadmium
residues were observed in fishes killed with CdCI2' Cd(CN)2'
and solution III; in fishes killed with solutions I and II, high
cadmium content was observed only in elevated cadmium
concentrations. Maximum whole body Cd levels in dead fishes from
different solutions were: 4.52 mg Cd/kg in 10 mg Cd/I, as
Cd(CN)2' for 6 hrs; 10.7 mg/kg in 684 mg Cd/I, as soln I, for
0.5 hr; 11.4 mg/kg in 700 mg Cd/I, as soln II, for 0.5 hr; and
13.5 mg/kg in 72.4 mg Cd/I, as soln III, for 15 hrs.
3102.
Kulikov, N.V., M.Y. ~8ebotina1 rnd V.F. Bochenin. 1977.
Accumulation of Sr and 3 Cs by components of a
charophyte biocenose. Soviet Jour. Ecology 8(1):34-40.
Accumulation of strontium-90 by live charophyte algae
(Chara spp., Nitella hialina, Nitellopsis obtusa, Tolipella
prolifera) was higher than in dead plants or bottom deposits.
Coefficients of accumulation (CA) of Sr-90 on a dry wt basis by
418
-------
live algae ranged from 700 to 1700 after 16 days; CA by dead
specimens was 200 to 800; and of bottom deposits of algae from 100
to 400. Cesium-137 was accumulated to a greater degree by bottom
deposits than by live and dead algae. CA of Cs-137 of both algal
groups after 16 days ranged from 100 to 400, and of bottom
deposits from 500 to 7000. Coefficients of accumulation of Sr-90
and Cs-137 for all components of charophyte biocenoses were
several times higher in natural conditions than in laboratory
experiments. For algae and bottom deposits, a positive linear
relationship was observed between Sr-90 accumulation and calcium
content, and between Cs-137 accumulation and potassium content.
Concentrations of Ca in 8 species of algae ranged from 61,000 to
170,000 mg/kg dry wt with a mean of 123,600, and K ranged from
4400 to 24,100 mg/kg dry wt with a range of 9700.
3103.
Kuli~8v, N.V. ~d V.G. Kulikova. 1977. Acclmrulation of
Sr and 1 Cs by certain freshwater fish under
natural conditions. Soviet Jour. Ecology 8(5):416-420.
Accumulation of Sr-90 and Cs-137 by freshwater fish is
influenced by diet and water chemical composition, in particular
the content of Ca and K. The direct dependence of Cs-137
accumulation on fish age is demonstrated with pike. No
differences in radionuclide accumulation due to sex were found in
any species studied. Specimens of Esox lucius, Percus
fluviatilis, Coregonus lavaretus, RUtIIus rutilus, Leuciscus idus,
Carassius carassius, Tinca tinea, and Cyprinus carpio from twO---
lakes in the South Urals contained Sr-90 concentrations in whole
body minus viscera ranging from 340 to 1329 pCi/kg wet wt and
Cs-137 from 170 to 2490 pCi/kg. Coefficients of accumulation in
fish over water were 155 to 600 for Sr-90 and 100 to 1465 for
Cs-137. As age of pike (Esox) increased, average Cs-137 level
increased from 1111 to 3353 pCi/kg wet wt, while Sr-90, Ca, and K
did not change. Accumulation of calcium and potassium in whole
pike is related to the chemical composition of water. Ca
concentrations in pike ranged from 7200 to 12,300 mg/kg wet wt and
for K from 1700 to 2900 mg/kg.
3104.
Lavrova, E.A. and Y.V. Natochin. 1978. Sodium and
magnesium concentration of environmental water and the
water-salt exchange in fish. Soviet Jour. Ecology
9(2): 135-140.
A relation between sodium concentrations of
environmental water and blood serum from 64 species of fish and
elasmobranchs was observed. Sodium concentrations in waters
419
-------
ranged from O. 14 to 465.0 meq/l, and was divided into four groups
for this study: I - Na below 0.25 meq/l, II - from 0.48 to 1.1
meq Nail, III - close to osmotic concentration of blood serum of
bony fish, and IV - from 227 to 465 meq Nail. Lowest blood Na
levels were in fish from the least saline waters. Sodium in blood
serum of fish collected from group I waters averaged 121 meq/l,
aDd 141 meq/l in blood from group II. Fish from the Baltic,
Caspian, Black, White, and Barents Seas contained 159 to 184 meq
Nail. Maximum blood concentrations of 240 meq Nail were obtained
from sharks and rays from the Black Sea. Kidneys are the
principal organs which eliminate excess magnesium from blood.
After ingestion of magnesium salt, excess Mg was eliminated by a
secretory process characteristic of kidneys of fish able to
migrate to the sea or marine species. This mechanism was not
present in stenohaline freshwater fish. Kidney regulation
maintenance of calcium and potassium balance is also discussed.
3105.
Lewis, M. 1978. Acute toxicity of copper, zinc
manganese in single and mixed salt solutions
juvenile longfin dace, Agosia chrysogaster.
Fish. Biology 13:695-700.
and
to
Jour.
Acute toxicity of copper, zinc, manganese, and
copper-zinc and copper-manganese mixtures were determined for
juvenile longfin dace in hard water bioassays (mean = 218 mg
CaCO~/I). Copper-zinc was the most lethal toxicant (LC-50 96 hr
= 0.21 mg Cull and 0.28 mg Zn/l) and exhibited more than additive
toxicity, which was in contrast to additive toxicity of
copper-manganese mixtures (LC-50 96 hr = 0.45 mg Cull and 64.0 mg
Mn/l). Toxicity of copper (LC-50 96 hr = 0.86 mg/l) and zinc
(0.79 mg/l) to fish was similar. Both were considerably more
lethal than manganese (LC-50 96 hr = 130 mg/l).
3106.
Li, W.K.W. 1978. Kinetic analysis of interactive effects
of cadmium and nitrate on growth of Thalassiosira
fluviatilis (Bacillariophyceae). Jour. Phycology
14:454-460.
Effect of cadmium, from 0.0 to 1.0 mg/l, on growth
rates of 2 algal species, Thalassiosira fluviatilis and Isochrysis
galbana, at non-limiting nutrient concentrations is described. At
limiting nitrate concentrations, effect of Cd on growth rate of T.
fluviatilis is described by analogy to the general equation of -
enzyme inhibition in which the reaction involves a single
intermediate. When cells are stressed by Cd, not only is maximum
420
-------
growth rate reduced, but half-saturation growth parameter is
increased. The value of log(k1/k2) can be used to describe
the type and degree of interaction between a nutrient and an
inhibitor. k1 and k2 are the inhibitor concentrations
resulting in 50% growth inhibition as nutrient concentration
approaches zero and an infinitely large value, respectively.
Results show that for T. fluviatilis, degree of inhibition by Cd
is more severe at low than high N03- levels, but difference in
severity diminishes as Cd concentration increases.
3107.
Marais, J.F.K. 1978. Routine oxygen consumption of
Mugil cephalus, Liza dumerili and~. richardsoni at
different temperatures and salinities. Marine Biology
50:9-16.
Metabolic rate in fish may be described by the equation
M = awO; where M = metabolic rate, a = intensity of metabolism,
W = body weight, and b = the exponent of W. Oxygen consumption
studies were undertaken with 3 mullet species to determine the
indices b and a. This was done under 5 experimental temperatures
(13, 18, 23, 28, 33 C) for M. cephalus and L. dumerili at 1.0 and
35 0/00 S, and for L. richardsoni at 35 0/00 S only. Mean b
values were approxiIDately o. 85. The value of a depended on
temperature, and increased according to Van't Hoff's Law, except
for L. dumerili at 1 0/00 S and L. richardsoni at 35 0/00 S for a
temperature increase from 23 to 28 C. Handling of fish influenced
metabolic rate and led to increased consumption rates during the
first 8 hrs after introduction into respiration chambers. Fasting
in L. dumerili resulted in a drop of 27% in oxygen consumption
over 6 days, of which 10% occurred over the first 24 hrs. Oxygen
consumption of fish displayed diurnal rhythms, with lowest
consumption rates at midday and midnight and highest just after
sunrise and sunset.
3108.
Marchyulenene, E. -D. P. 1978. Exchange of certain
radionuclides between the environment and fresh-water
algae. Soviet Jour. Ecology 9(2):163-165.
Order of level of accumulation of 4 radionuclides by
freshwater algae after 16-day exposure was Ce-144> Ru-106 >Sr-90
>Cs-137. Coefficients of accumulation of Cladophora glomerata,
Nitella syncarpa, Nitellopsis obtusa, Chara rudis, and C. vulgaris
over water ranged from 900 to 4374 for Ce-144, 110 to 1598 for
Ru-106, 16 to 57 for Sr-90, and 4 to 78 for Cs-137. Calcium
content in algae ranged from 40,500 to 100,000 rng/kg ash wt, and
421
-------
potassium from 9000 to 47,500 mg/kg ash wt. After 16 days in
clean water, Cladophora and Nitella retained 72 to 83% of
accumulated Ce-144, ~3% Ru-106, 60 to 70% Sr-90, and 23 to 75%
Cs-137. Algal uptake of radionuclides of strontium and cesium
depended on season, decreasing 3 to 14X from spring to autumn;
cerium and ruthenium uptake did not change during the vegetative
season.
3109.
Martin, D.F. and M.H. Gonzalez. 1978. Effects of salinity
on synthesis of DNA, acidic polysaccharide, and growth
in the blue-green alga, Gomphosphaeria aponina. Water
Research 12:951-955.
Gomphosphaeria was grown in artificial seawater at
salinities of 20 to 36 0/00. Fair to good growth was obtained at
all salinities. Highest growth constant was 1.178/day in 30 0/00
S, with an algal doubling time of 0.588 days. Rate of DNA
synthesis increased linearly with growth constant gbove Ke =
0.95/day. Maximum growth rate was 31.88 ug DNA/10 cells/day in
30 0/00 S. Linear correlation coefficients were obtained for rate
of polysaccharide synthesis and rate of DNA synthesis, as well as
for rate of DNA synthesis and synthesis rate of aponin. Aponin is
a material isolated from G. aponina which has cytolytic activity
toward the Florida red tide organism, GYmnodinium breve.
3110.
Murphy, B.R., G.J. Atchison, and A.W. McIntosh. 1978.
Cadmium and zinc in muscle of bluegill (Lepomis
macrochirus) and largemouth bass (Micropterus
salmoides) from an industrially contaminated lake.
Environ. Pollution 17:253-257.
Cadmium and zinc analyses of 44 largemouth bass and 29
bluegill indicated that fish in an ecosystem heavily contaminated
by trace metals accumulate significantly more metal in edible
muscle tissue than fish from an uncontaminated ecosystem. Average
metal concentrations near an industrial effluent in Palestine
Lake, Indiana, were: in water, 17.3 ug Cd/l/ (dissolved) and 30.3
Cd (suspended), and 293 ug Zn/l (dissolved) and 270 Zn
(suspended); and in top 5 em of sediment, 800 mg Cd/kg dry wt and
12,800 mg Zn/kg. Concentrations detected in fish muscle ranged
from 0.01 to 1.31 mg Cd/kg dry wt and 18.2 to 158.2 mg Zn/kg dry
wt. Bluegill contained significantly greater concentrations of Cd
and Zn than bass. Mean levels were 0.431 Cd (bluegill) and 0.075
mg Cd/kg (bass) and 67.8 Zn (bluegill) and 43.3 mg Zn/kg (bass).
Small bass contained significantly more Cd than large bass.
422
-------
Authors concluded that human consumption of these fish is probably
not a health hazard unless such fish constitute a major portion of
the diet.
3111.
Nifontova, M.G. 1977. Effect of iSQ&opic an~3Donisotopic
carriers on the accumulation of IJ Sr and 'r Cs from
aqueous solutions by lichens. Soviet Jour. Ecology
8(6) :533-535.
Chlorides of stable strontium and cesium, at O. 1 mM to
0.1 M concentrations, and Sr-90 and Cs-137, at 10 uCi/l and 6
uCi/l, respectively, were added to water to follow accumulation in
lichen, Cladonia amaurocraea, over 4 days. Effect of nonisotopic
carriers, calcium and potassium, was also deter'mined. Strontium
and cesium isotope accumulation by lichen was directly
proportional to water concentrations; Ca and K followed a similar
pattern. Lichen content of both stable elements rose from 0.001 M
to 1.0 M then plateaued as concentrations in solutions increased.
Accumulation coefficients (AC) of radionuclides remained almost
constant at 1000 as solution concentrations of Sr and Cs increased
to 1.0 mM, then AC dropped gradually to about 10-50 with higher
concentrations. As Ca and K levels in solution rose above O. 1 mM
to highest concentrations used, AC of Sr-90 and Cs-137 decreased
linearly to about 10 to 50.
3112.
Noel-Lambot, F., C. Gierday, and A. Disteche. 1978.
Distribution of Cd, Zn and Cu in liver and gills of the
eel Anguilla anguilla with special reference to
metallothioneins. Compo Biochem. Physiol. 61C:177-187.
Distribution of cadmium, zinc, and copper in the
soluble fraction of liver and gills of eels adapted to seawater
and submitted to chronic or acute Cd exposure was studied. Metal
concentrations, in mg/kg wet wt, in whole livers of control eels
were 0.9 for Cd, 17.7 for Cu, and 41.3 for Zn. Liver of eels in
200 mg Cd/l for 5 hrs contained 11.7 mg Cd/kg, 13.3 Cu, and 42.7
Zn. Eels in 13 mg Cd/l for 180 days contained 331 Cd, 15 Cu, and
82 Zn in liver. During chronic intoxication, most of the Cd that
accumulated in liver and gills is bound to metallothioneins. In
the case of acute intoxication, only liver accumulated Cd as
Cd-thioneins. Metallothioneins were present in livers of
non-Cd-exposed eels, but in lower amounts than in chronically
intoxicated specimens. Metallothioneins were principally in the
form of Zn and Cu derivatives. In gills, metallothioneins did not
exist in detectable amounts. The overall characteristics of
423
-------
metallothioneins isolated from eel liver are very similar to those
obtained from mammalian tissues.
3113.
Ogino, C., F. Takashima, and J.Y. Chiou. 1978.
Requirement of rainbow trout for dietary magnesium.
Bull. Japan. Soc. Sci. Fish. 44:1105-1108. (In
Japanese, English abstract and tables).
Trout weighing 0.9 g were fed diets containing
different amounts of Mg (46 to 779 mg/kg) for 6 weeks.
Concentration of Mg in rearing water was 3. 1 mg/l. Dietary Mg
levels affected appetite, growth, movement of fish, and contents
of ash, Mg, and Ca in whole body and vertebrae. Phosphorus levels
did not change significantly. With increasing magnesium in diet,
whole body Ca decreased from 3.5 to 2.7% of dry wt, Mg increased
from 0.08 to 0.15%, and Ca/Mg ratio decreased from 41 to 18.
Vertebrae content of Ca decreased from 13.8 to 11.1% of dry wt, Mg
increased from 0.10 to 0.27%, and Ca/Mg ratio decreased from 141
to 40, as dietary magnesium increased. Vertebral curvature and
histological changes were observed in muscle, pyloric caeca, and
gill filaments were observed in Mg-deficient fish. Requirement of
trout for dietary Mg was estimated to be 0.06-0.07% of a dry diet
or 12-16 mg/kg body wt per day under experimental conditions.
3114.
Ostrom, K.M. and T.L. Simpson. 1978. Calcium and the
release from dormancy of freshwater sponge gemmules.
Developmental Biology 64:332-338.
Salts of barium, manganese, strontium, and zinc at 1
mM, and magnesium at 8 mM, inhibit development of dormant gemmules
of the freshwater sponge Spongilla lacustris. This inhibition is
overcome by 1 mM calcium, so it can be interpreted that Ca
divalent ion is essential for germination (cell division).
Inhibitory cations have different effective concentrations which
indicate differing binding affinities for sites which may normally
bind Ca. Ethylene glycol bis (s-aminoethyl ether),
N,N-tetraacetic acid does not effect gemmule development at 15 C
but stimulates it at 4 C, indicating that a dislocation of
endogenous Ca stimulates release from dormancy. Magnesium will
only partially substitute for calcium in overcoming inhibition,
implying a different specificity for Mg in gemmule development.
Calcium is also essential for hatching (cell motility) in this
sponge.
424
-------
3115.
Paschoa, A.S. and G.B. Baptista. 1978. Method for
calculation of upper limit internal alpha dose rates to
aquatic organisms with application to plutonium-239 in
plankton. Health Physics 35:404-409.
Estimations were calculated for upper limits of the
internal alpha-radiation dose rates received by plankton due to
bioaccumulation of plutonium-239. Authors assumed uniform
distribution of alpha-emitter throughout the body, constant
concentration, and complete absorption of the mean alpha energy.
Reported Pu-239 content in marine and freshwater plankton from
selected references ranged from 1.9 to 8.4 uCi/kg wet wt in
phytoplankton and 1.0 to 9.0 uCi/kg in zooplankton. Upper limit
alpha dose rates ranged from 2. 1 to 9. 1 urad/hr in phytoplankton
and 1.1 to 9.8 urad/hr in zooplankton.
3116.
Patel, B., S. Patel, M.C. Balani, and S. Pawar. 1978.
Flux of certain radionuclides in the blood-clam Anadara
granosa Linneaus under environmental conditions. Jour.
Exp. Marine BioI. Ecol. 35:177-195.
Flux of cesium-137, cerium-144, and ruthenium-106, in
the Bombay Harbor, India, ecosystem was measured over six years
(1970-1976), during which input of controlled low level
radioacti ve waste was gradually reduced by more than 20X. Of the
pelagic and benthic species studied, the arcid clam Anadara
granosa, showed a specific affinity for all three radionuclides;
degree of bioaccumulation was Ce2Ru> Cs. Concentrations of these
nuclides in tissues varied with levels in sediment, which in turn
were related to inputs into seawater, maintaining some kind of
equilibrium. Highest concentrations in whole bodies of clams were
38 nCi Ru-106/kg dry wt, 36 nCi Ce-144/kg, and 10 nCi Cs-137/kg,
at sediment levels of 75, 140, and 260 nCi/kg dry wt, for
respective elements. Individual tissue concentrations were also
determined. On reaching maximum accumulation, nuclides in the
clam population decreased exponentially with time although
radioactivity was still available in sediment. Ecological
half-times for Ce-144 and Ru-106 were about 3 to 6X longer, and
for Ce-137 significantly shorter, than their respective physical
half-lives. Ecological half-times were predominantly influenced
by environment rather than by biological half-lives, indicating
that biological half-lives were much shorter than respective
ecological half-lives. Biological half-time of Cs-137 was
biphasic; the short-lived component had a half-time of about 3
days and long-Ii ved component about 15 days. Bioaccumulation of
cobalt-60 in A. granosa increased with time of exposure and
425
-------
reached a level significantly higher than Cs-137, but was
independent of ambient concentrations and temperature.
Strontium-90 was preferentially deposited in clam shell at higher
concentrations (0.10 nCi/kg after 34 days) under higher
temperatures of 30-35 C. Generally, clams maintained tissue
concentrations of Ce-144, Ru-106, and Cs-137, but not Co-60,
through adjusting physiological flux rates, in equilibrium with
changing levels in the environment.
3117.
Paul, M. and R.N. Johnston. 1978. Absence of a Ca
response following ammonia activation of sea urchin
eggs. Developmental Biology 67:330-335.
Following insemination of eggs of sea urchins,
Strongylocentrotus purpuratus and S. drobachiensis, rate of Ca
uptake and efflux from eggs increase. Both of these components of
the egg's Ca response are absent following partial activation with
arrmonia. This suggests that the "late events" of fertilization,
which are activated by ammonia treatment, are not mediated
directly by changes in egg Ca. Uptake of calcium from water
reached 2.0 nmoles Ca2+/egg sample after 15 minutes following
insemination, but was only 0.3 nmoles/egg sample with addition of
NH4CI. Efflux of Ca-45 from pre loaded eggs was lower with
ammonia activation, at 1300 cpm/ml in control seawater vs. 700
cpm/ml with NH4CI after 40 minutes.
3118.
Rajendran, A., Sumitra-Vijayaraghavan, and M. V.M. Wafar.
1978. Effect of some metal ions on the photosynthesis
of microplankton and nannoplankton. Indian Jour.
Marine Sci. 7:99-102.
Photosynthesis in larger algae (microplankton) and
smaller algae (nannoplankton) collected from Dona Paula Bay, Goa,
in the East Indies, was affected after 3 hours by higher
concentrations of cobalt, copper, iron, manganese, molybdenum, and
zinc. Response of each group varied with metal. Copper enhanced
micro- and nannoplankton photosynthesis at low levels of 8.0 and
4.0 ug/l, but decreased rates to 90% of controls in microplankton
and 63% in nannoplankton in 20 ug/l. Photosynthetic rate of
nannoplankton increased in up to 16 ug Zn/l, then decreased
slightly in higher concentrations. Microplankton production
gradually decreased as Zn levels rose to 60 ug/l. Both groups of
algae showed a decreasing photosynthesis rate due to iron
exposure, from 90% to 50% as concentrations rose from 4.5 to 45.0
ug Fell. Molybdenum increased photosynthesis at 20 ug Moll, and
426
-------
did not significantly reduce rates at higher concentrations.
Manganese and cobalt, which increased photosynthetic rate slightly
at low levels (8.0 ug Mn/l or 1.0 ug Co/I), did not appear to be
toxic to either size group of algae at concentrations up to 40 ug
Mo/l or 4.0 ug Co/I.
3119.
Sakamoto, S. and Y. Yone. 1978. Iron deficiency symptoms
of carp. Bull. Japan. Soc. Sci. Fish. 44:1157-1160.
Cyprinus carpio were fed diets with and without
supplemental iron (199 mg Fe/kg diet vs. 10 mg Fe/kg) over a 105
day period. No significant differences were recognized between
groups in: growth rate; condition factor; feed efficiency; ratio
of liver, spleen and heart weight to body weight; blood serum
levels of total protein, total cholesterol, total bilirubin,
urea-N, glucose, calcium, inorganic phosphorus; and activities of
enzymes such as glutamic oxalacetic transaminase, glutamic pyruvic
transaminase, alkaline phosphatase, lactic dehydrogenase, and
leucine aminopeptidase. However, in the group without the iron
supplement, blood specific gravity, hemoglobin, hematocrit, mean
corpuscular constants, and mean corpuscular diameter of minor
length were lower; and percentage of imnature erythrocytes was
higher. These findings show that carp fed a diet without iron
supplement manifested a hypochromic microcytic anemia.
3120.
Sankaranarayanan, V.N., K.S. Purushan, and T.S.S. Rao.
1978. Concentration of some of the heavy metals in the
oyster, Crassostrea madrasensis (Preston), from the
Cochin Region. Indian Jour. Marine Sci. 7:130-131.
Concentrations of zinc, copper and iron were measured
in C. madrasensis collected from the Cochin backwaters during 1975
and-1976. High concentrations in adult specimens, in mg/kg dry wt
soft parts, of 150 to 200 for Cu, 500 to 1600 for Fe, 35 to 90 for
Mn, and 7500 to 12,500 for Zn, were observed during December to
M3.y. Low values were confined to June to November, when
freshwater discharge through the rivers was maxllnum. Metal levels
in oysters were below 150 mg Cu/kg, 500 for Fe, 30 for Mn, and
4000 for Zn during this period. Juvenile oysters generally
contained lower concentrations than adults. The high levels of
Zn, Cu, and Fe were considered to be due to industrial and
domestic pollution.
3121.
Shiber, J. and E. Washburn.
1978.
Lead, mercury, and
427
-------
certain nutrient elements in Ulva lactuca (Linnaeus)
from Ras Beirut, Lebanon. Hydrobiologia 61:187-192.
Algae collected from nine locations along the coast of
Ras Be irut, Lebanon, were analyz ed for lead, mercury, phospha te,
calcium, magnesium, iron, copper, and zinc. Low lead
concentrations of 0.14 mg/kg dry wt in all samples, suggest that
U. lactuca controls Pb uptake and toxicity. Phosphate levels may
be a contributing factor to this process. Concentrations of all
other elements seemed relatively uniform. With few exceptions,
average metal levels in algae from all sites, in mg/kg dry wt,
were 2.9 Hg, 100.5 Ca, 0.54 Mg, 2.7 Fe, 0.22 Cu, and 0.53 Zn.
This uniformity suggests that U. lactuca is subject to similar
environmental conditions and element exposure at each collecting
site and that this species might be capable of maintaining
biochemical stability under high levels of stress.
3122.
Sivalingam, P.M. 1978. Effects of high concentration
stress of trace metals on their biodeposition modes in
Ulva reticulata Forskal. Japan. Jour. Phycol.
26: 157 -160.
Studies on algal biodeposition of Cd, Cr, Co, Pb, Zn,
Mn, and Ni, at concentrations of 50, 100, 200, 300, and 500 mg/l
over 48 hours, indicated that bioconcentration factors for 50 and
500 mg/l concentrations were 36 and 21X for Cd, 18 and llX for Cr,
136 and 23X for Co, 124 and 24X for Pb, 48 and 4X for Zn, 144 and
35X for Mn, and 146 and lOX for Ni, respectively. Time course
studies indicated different patterns of biodeposition for each
metal, reflecting possible different physiological and biochemical
interactions of these trace metals in Ulva.
3123.
Spear, P.A. and P.D. Anderson. 1978. Pharmacokinetics in
relation to toxicity assessment. In: Davis, J.C.,
G.L. Greer, and I.K. Birtwell (eds:}. Proc. Fourth
Annual Aquatic Toxicity Workshop, Vancouver, B.C., Nov.
8-10, 1977. Fish. Mar. Servo Canada, Tech. Rept. No.
818:168-185.
Sunfish, Lepomis gibbosus, were exposed to ambient
solutions of copper sulfate. Rate of copper accumulation in gills
and LC-50 (96 hr) concentrations approximated an inverse
relationship as magnitudes of the two variables changed with
sunfish body weight. For rainbrn trout, Salmo gairdneri, both
428
-------
variables were independent of body weight. LC-50 (96 hr) values
for sunfish increased from 1.24 to 1.85 mg Cull as body wt
increased, and values for trout were 0.19 to 0.21 mg Cull
regardless of size. Accumulation rate in gills in sunfish
decreased from 8.2 to 6.6 mg Cu/kg fish/hr as size increased.
Accumulation rates in trout gills ranged from 1.2 to 1.6 mg Cu/kg
fish/hr regardless of weight. Results are discussed in relation
to metabolic rate and prediction of the tolerance of fish exposed
to metal toxicants.
3124.
Till g.E. 1978. The effect of chronic exposure to
23 Pu (IV) citrate on the embryonic development of
carp and fathead minnow eggs. Health Physics
34 :333-343.
Quantitative analysis of uptake of Pu-238 citrate by
carp (Cyprinus carpio) eggs indicated that plutonium is
accumulated in egg and reaches a concentration factor of about 4
by hatching (72 hr after exposure began). Although some plutonium
was concentrated on egg chorion, Pu-238 that penetrated the
chorion was uniformly distributed throughout perivitelline fluid,
embryo, and yolk sac. Conversion factors for eggs exposed to
Pu-238 during embryological development were 2100 and 7500
rad/uCi/ml for carp and fathead minnows (Pimephales promelas),
respectively. Eggs were exposed to Pu-238 in solution during
embryogenesis. Percentage of eggs hatching, number of abnormal
larvae produced, and survival of larvae were used as indicators of
radiation toxicity. Concentrations in excess of 1.0 mCi/l
prevented both species of eggs from hatching. Fish eggs
developing in natural aquatic ecosystems contaminated with Pu-238
probably do not receive a significant dose from plutonium alpha
radioactivity.
3125.
Trabalka, J.R. and M.L. Frank. 1978. Trophic transfer by
chironomids and distribution of plutonium-239 in simple
aquatic microcosms. Health Physics 35:492-494.
Larval insects, Chironomus riparius, were analyzed 73
days after two additions of 0.1 uCi Pu-239/ml had been added to
rearing water. Plutonium-239 concentrations were 8.2 mCi/kg wet
wt in gut contents, 7.7 mCi/kg in sediment, and 0.66 uCi/l in
water. Trophic transfer factors for Chironomus over water were
7.1 in whole animal, 0.79 in animal without gut contents, and 0.40
in an imal without gut.
429
-------
3126.
Van Horn, W. 1975. Materials balance and technology
assessment of mercury and its compounds on national and
regional bases. U.S. Environ. Protect. Agen. Rept.
EPA-560/3-75-007. Avail. as PB-247 000 from Nat. Tech.
Inform. Serv., U.S. Dept. Commerce, Springfield, VA
22151:293 pp.
The role of mercury and its compounds in the
environment and economy of the United States was studied from 164
references. A detailed material balance for mercuric compounds
was developed on a national basis and for selected geographical
regions, including estimates of the environmental fate of all
emissions. About 80% of the almost 1900 tons of mercury used each
year in the U.S. is ultimately discharged to the environment; an
additional 8% is recycled, and the remainder is permanently in
place. Mercury discharges enter the environment at a number of
points. Of particular concern is the characteristic of mercurials
to move, after discharge, from one environmental medium to another
and to enter man's foodchain through various mechanisms. Present
monitoring capabilities for determining Hg concentration in the
environment are inadequate; therefore available data on ambient
mercury levels do not provide a complete picture of either natural
or elevated levels. Percent distribution of mercury discharges
from man-related sources in the U.S. is: 31% to air; 6% to water;
and 63% to land. About 13% of man-related discharges to water are
from regulated industries, currently chlor-alkali and mercurials
manufacturing. Natural sources, primarily runoff, contribute
about 2X as much Hg to water as man-related discharges. Some
mercury is removed from water in sewage treatment processes as
sludge and is either returned to land or incinerated and returned
to air. Solid wastes incorporated in regulated landfills (which
currently receive about one-third of all solid wastes) do not
discharge appreciable amounts of mercury to water. Most mercury
discharged to water is incorporated rapidly into sediments and may
be released by biological and mechanical action over a period of
time. Effects of Hg have been studied with organisms in man's
foodchain, including fish, molluscs, and other mammals. The
author believes that the "threat to man" associated with current
rates of man-related mercury discharges to the environment has not
been conclusively demonstrated. Similarly, there is no conclusive
evidence to indicate that a long-term buildup of mercury in the
biosphere is occurring. Nonetheless, potential consequences of a
mercury buildup are of such magnitude that efforts should continue
to decrease the quantities of mercury discharged each year.
Current and projected process technologies for mercury products
were examined, and estimates of environmental losses for 1973 and
1983 presented. A set of regulatory alternatives was developed
430
-------
for the major technologies involving substantial losses of mercury
to the environment, and economic impact of these alternatives was
examined.
3127. Varanasi, U. and D.J. Gmur. 1978. Influence of
water-borne and dietary calcium on uptake and retention
of lead by coho salmon (Oncorhynchus kisutch).
Toxicol. Appl. Pharmacol. 46:65-75.
Coho salmon in freshwater (2.6 mg Ca2+/1) were
exposed to sublethal concentrations (0.13 and 0.21 mg/l) of
water-borne lead in the presence of increased concentrations of
water-borne or dietary calcium. Uptake of lead was greatly
reduced in gills, blood, liver, brain, skin, skeleton, and kidney
of fish fed 8.4 mg of calcium. Lead uptake was also reduced
significantly in gills, blood, skin, and skeleton of fish exposed
to higher concentrations of 6.2 mg/l water-borne calcium; however,
liver and kidney did not show signifi~t reduction in lead levels
compared to fish exposed to 2.6 mg Ca +/1. Bioconcentration
factors were highest in gills and kidney and lowest in brain in
both groups. An increased concentration of Ca in gastrointestinal
tract was more effective than an increased concentration of Ca in
surrounding water in reducing uptake of water-borne Pb. Retention
of Pb administered via caudal vein was not significantly affected
by increasing Ca concentrations in water from 2.6 to 11.9 mg/l.
Increase in dietary or water-borne Ca had a less pronounced effect
in reducing Pb retention in most tissues than reducing Pb uptake;
nevertheless, an increase in water-borne or dietary Ca
significantly reduced both uptake and retention of Pb in skin and
skeleton. Turnover of Pb, and perhaps Ca, in salmon is greater in
skin than in skeleton. It is concluded that, in salmonids,
biological fate and, presumably, toxicity of lead is influenced by
the calcium status of the fish.
3128.
Waiwood, K.G., and F.W.H. Beamish. 1978. The effect of
copper, hardness and pH on the growth of rainbow trout,
Salmo gairdneri. Jour. Fish Biology 13:591-598.
Trout held on a fixed ration and activity regime were
exposed to a number of copper (0.0 to 200.0 ug/l), pH, and
hardness combinations. Growth rate, appetite, and gross
conversion efficiency were determined over three consecutive
10-day exposure periods. Growth rate was most affected during the
first 10 days of exposure; partial or complete recovery was
observed thereafter. For a given pH, less copper was required to
431
-------
reduce growth by a given amount at low levels of hardness. At a
given hardness, copper-induced depressions in growth rate were
more pronounced and recovery slower in a low pH. No distinction
could be made among total soluble or extractable copper, but
predicted concentrations of six specific cupric ions varied with
pH and hardness. Regression analysis indicated that only Cu2+
and CuOH+ could be significantly correlated with growth rate.
3129.
Weinstein, N.L., and P.D. Anderson. 1978. Lethal and
sublethal toxicities of copper-nickel mixtures to the
zebra fish Brachydanio reria. In: Davis, J.C., G.L.
Greer, and I.K. Birtwell (eds.~ Proc. Fourth Annual
Aquatic Toxicity Workshop, Vancouver, B.C., Nov. 8-10,
1977. Fish. Mar. Servo Canada, Tech. Rept. No.
818: 153-167.
Zebrafish were exposed to mixtures of copper and nickel
at sublethal and lethal concentrations to assess their multiple
toxicities. The response variable of lethal bioassays was
percentage mortality, a quantal factor, while sublethal response
was graded in terms of fecundity. Lethal and sublethal mixtures
evoked supra-additive effects which proved to be substantially
greater in magnitude than the effects predicted according to a
hypothesis of toxicant additivity. Authors propose that the
apparent enhancement of potency in mixtures may be attributable to
alterations in kinetics of toxicant absorption, distribution,
depositi~l, degradation, or excretion.
3130.
White, A.W. 1978. Salinity effects on growth and toxin
content of Gonyaulax excavata, a marine dinoflagellate
causing paralytic shellfish poisoning. Jour.
Phycology 14:475-479.
The optllnum salinity for growth of G. excavata from
Cape Ann, Massachusetts, was 30.5 0/00. It grew well over a range
of 20 to 40 0/00 S, and tolerated salinities from 11 to 43 0/00.
Growth rates at 24 and 20 0/00 S were only 10 and 20% lower,
respectively, than the maxllnum of 0.36 divisions/day. It is
unlikely that salinity fluctuations in coastal areas where diatoms
occur would significantly alter growth. The paralytic toxin
content of Gonyaulax increased with increasing salinity up to 37
0/00. Toxicity of Gonyaulax in nature may, th~refore, be
influenced by changes in salinity.
432
-------
3131.
Williams, D.R. and J.P. Giesy, Jr. 1978. Relative
importance of food and water sources to cadmium uptake
by Gambusia affinis (Poeciliidae). Environmental
Research 16:326-332.
Relative importance of food and water as cadmium
sources to mosquitofish, G. affinis, was studied in a factorially
designed exper iment with O. 1 and 1.0 mg Cd/kg dry wt in food and
0.00002 and 0.01 mg Cd/l in water after 2 to 8 weeks of
exposure. There was significant Cd uptake from water, but no
significant uptake from food, except after 8 weeks in the presence
of Cd in water. Fish exposed to high Cd levels in water contained
46.9 mg Cd/kg dry wt with low Cd diet and 71.5 mg/kg with high Cd
diet. When exposed to a continuous flow of 10 ug Cd/l in water,
G. affinis did not reach equilibrium Cd concentration before 8
weeks.
3132.
Zaba, B.N. and E.J. Harris. 1978. Accumulation and
effects of trace metal ions in fish liver
mitochondria. Compo Biochem. Physiol. 61C:89-93.
Uptake and effects of calcium, copper, manganese, and
zinc in liver mitochondria of the freshwater fishes Salmo
gairdneri and Esox lucius, and the marine t~leosts G~dUS morhua
and Pleuronectes platessa were studied. Ca + and Mn T were
taken up by an energy-dependent2~rocess si~ilar to that described
for rat liver mitochondria. Cu , however, was taken up by an
en~rgy-independent process which stimulated potass~um uptake.
Zn + was accumulated to a very limited extent. Zn + and
Mn2+ caused very strong inhibition of respiration. Implications
of these findings are discussed.
433
-------
SECTION III
INDEX
Three indices to this volume are presented: INDEX-METALS,
INDEX-TAXA, and INDEX-AUTHORS. Cumulative indices to the first
three volumes in this series are located on pages 361 to 486 of
EPA Report 600/3-78-005 (Third Annotated Bibliography on
Biological Effects of Metals in Aquatic Environments).
434
-------
INDEX - METALS
ALUMINUM
ALGAE: 2283, 2288, 2395, 2452, 2528, 2570, 2595, 2676, 2856
ANNELIDA: 2283, 2570, 2595
AVES: 2283, 2570, 3064
BACTERIA AND YEAST: 2283, 2288, 2349, 2570, 2595, 2728, 2764
BIBLIOGRAPHY: 2570, 2595, 3064
BRYOPHYTA: 2570
CHAETOGNATHA: 2604
CDELENTERATA : 2283, 2570, 2604, 2721
CRUSTACEA: 2283, 2288, 2570, 2591, 2595, 2604, 2730, 2886, 3064
CTENOPOORA: 2604
DETRITUS: 2283
ECHINODERMATA: 2283, 2570, 2595, 3064
ELASMOBRANCHII: 2283, 3064
FISH: 2281, 2283, 2288, 2570, 2595, 2604, 2730, 3064
HIGHER PLANTS: 2288, 2452, 2570, 2862
INSECTA: 2570, 2591, 2730
MAMMALIA: 2283, 2570, 2595, 3064
MISCELLANEOOS: 2570
MOLLUSCA: 2283, 2285, 2288, 2289, 2375, 2444, 2570, 2595, 2730,
3064
NEMATODA: 2570
PLANKTON: 2452, 2570, 2573, 2604
PORIFERA: 2283
PROTOZOA: 2283, 2288, 2570
SEAWATER: 2288, 2570, 2573, 2604, 2676
SEDIMENTS: 2283, 2452, 2570, 2591, 2604, 2856
SIPUNCULOIDEA: 2595
TUNICATA: 2283, 2604
AMERICIUM
ALGAE: 2961, 2974, 2979
AMPHIBIA: 2542
ANNELIDA: 27 4 3
BIBLIOGRAPHY: 2542
CDELENTERATA: 2974
CRUSTACEA: 2542, 2743, 2961, 2979
ECHINODERMATA: 2542, 2974
FISH: 2542, 2588, 2916, 2961, 2974,
2979, 2987
435
-------
MAMMALIA: 2979, 2987
MOLLUSCA: 2542, 2674, 2961,
PLANKTON: 2974
PROTOZOA: 2542
SEAWATER: 2961, 2974, 2979
SEDIMENTS: 2961, 2974, 2979
2974, 2979
ANTIM)NY
ALGAE: 2283, 2328, 2534, 2570
ANNELIDA: 2283, 2570
AVES: 2283, 2570, 2596
BACTERIA AND YEAST: 2283, 2570, 2764
BIBLIOGRAPHY: 2570
BRYOPHYTA: 2570
CHAETOGNATHA: 2328
COELENTERATA: 2283, 2570
CRUSTACEA: 2283, 2328, 2530, 2534, 2570
DETRITUS: 2283, 2328
ECHINODERMATA: 2283, 2570, 2707
ELASMOBRANCHII: 2283
FISH: 2281, 2283, 2534, 2541, 2570, 2588, 2830, 2969
HIGHER PLANTS: 2476, 2570
INSECTA: 2570
MAMMALIA: 2283, 2570
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2375, 2534, 2570
NEMATODA: 2570
PLANKTON: 2570
PORIFERA: 2283
PROTOZOA: 2283, 2570
SEAWATER: 2570
SEDIMENTS: 2283, 2541, 2570, 2969
TUNICATA: 2283
ARSENIC
ALGAE: 2283, 2447, 2486, 2534, 2543, 2546, 2570, 2595, 2644, 2645,
2694, 2720, 2843, 2846, 2876, 2937, 2967, 3092
AMPHIBIA: 2542
ANNELIDA: 2283, 2443, 2447, 2486, 2556, 2570, 2595, 2645, 2720
AVES: 2283, 2486, 2556, 2570, 2645, 2809, 3063, 3064
BACTERIA AND YEAST: 2283, 2486, 2570, 2595, 2728, 2746, 2764,
436
-------
2795
BIBLIOGRAPHY: 2542, 2570, 2595, 2876, 3063, 3064, 3092
BRYOPHYTA: 2570, 2655
CHAEl'OGNATHA: 2604
COELEN1ERATA: 2283, 2570, 2604
CRUSTACEA: 2283, 2441, 2447, 2486, 2530, 2534, 2542, 2543, 2570,
2591, 2595, 2604, 2632, 2646, 2656, 2720, 2730, 2843,
2870, 2876, 3063, 3064
C1ENOPHORA: 2604
DETRITUS: 2283
ECHINODERMATA: 2283, 2542, 2543, 2570, 2595, 2843, 2876, 3064
ELASMOBRANCHII: 2283, 2441, 2443, 3064
FISH: 2263, 2281, 2283, 2351, 2441, 2443,
2534, 2541, 2542, 2543, 2555, 2556,
2632, 2645, 2646, 2656, 2657, 2730,
2907, 2940, 2969, 3063, 3064, 3073
HIGHER PLANTS: 2570, 2645, 2876, 3063
INSECTA: 2555, 2556, 2570, 2591, 2645, 2720, 2730
MAMMALIA: 2283, 2378, 2486, 2570, 2595, 2843, 2876, 2940, 3063,
3064
MISCELLANEOUS: 2570
MJLLUSCA: 2283, 2289,
2570, 2595,
2876, 3063,
NEMATODA: 2570, 2720
PLANKTOO: 2556, 2570, 2604, 2632, 2644, 3092
PORIFERA: 2283
PROTOZOA: 2283, 2542, 2570, 2720
ROTIFERA: 2720
SEAWATER: 2447,2570,2604,2632,2937,2967,3092
SEDIMENTS: 2283, 2447, 2486, 2541, 2543, 2555, 2556, 2570, 2591,
2604, 2644, 2645, 2646, 2876, 2969, 3063
SIPUNCULOIDEA: 2595
TUNICATA: 2283, 2604
2447, 2466, 2486, 2512,
2570, 2588, 2595, 2604,
2770, 2830, 2843, 2876,
2375, 2441, 2447, 2486, 2534, 2542, 2543,
2632, 2644, 2646, 2656, 2720, 2730, 2826,
3064
BARIUM
ALGAE: 2452, 2464, 2534, 2587,2620,2676,2749
ANNELIDA: 3002
AVES: 2596, 3064
BAC1ERIA AND YEAST: 2764
BIBLIOGRAPHY: 3064
COELEN1ERATA: 3002, 3114
CRUSTACEA: 2534, 2553, 2591, 2730, 3002, 3064
ECHINODERMATA: 3002, 3064
437
-------
ELASMOBRANCHII: 3064
FISH: 2440, 2534, 2541, 2587, 2588, 2730, 3064
HIGHER PLANTS: 2452
INSECTA: 2591, 2730
MAMMALIA: 2378, 2749, 3064
MISCELLANEOUS: 3002
MOLLUSCA: 2375, 2534, 2587, 2730, 3002, 3064
PLANKTON: 2452, 2573
PROTOZOA: 2938
SEAWATER: 2573, 2587, 2676
SEDIMENTS: 2452, 2541, 2591, 3002
SIPUNCULOIDEA: 3002
TUNICATA: 3002
BERYLLI UM
ALGAE: 2283, 2534, 2570
ANNELIDA: 2283, 2570
AVES: 2283, 2570, 2596, 3063
BACTERIA AND YEAST: 2283, 2570, 2764
BIBLIOGRAPHY: 2570, 3063
BRYOPHYTA: 2570
COELENTERATA: 2283, 2570
CRUSTACEA: 2283, 2534, 2570, 2591, 3063
DETRITUS: 2283
ECHINODERMATA: 2283, 2570
ELASMOBRANCHII: 2283
FISH: 2283, 2534, 2570, 3063
HI GHER PLANTS: 2570 , 3063
INSECTA: 2570, 2591
MAMMALIA: 2283, 2570, 3063
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2534, 2570, 3063
NEMATODA: 2570
PLANKTOO: 2570
PORIFERA: 2283
PROTOZOA: 2283, 2570
SEAWATER: 2570
SEDIMENTS: 2283, 2570, 2591, 3063
TUNICATA: 2283
BIBLIOGRAPHY
438
-------
ALGAE: 2570
ANNELIDA: 2562, 2570
AVES: 2562, 2570
BACTERIA AND YEAST: 2562, 2570
BRYOPHYTA: 2570
COELENTERATA: 2562, 2570
CRUSTACEA: 2562, 2570, 2632
ECHINODERMATA: 2570
FISH: 2562, 2570, 2588, 2632
HIGHER PLANTS: 2570
INSECTA: 2562, 2570
MAM1ALIA: 2570
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2375, 2562, 2570, 2632
NEMATODA: 2570
PLANKTOO: 2570, 2632
PLATYHELMINTHFS: 2562
PORIFERA: 2562
PROTOZOA: 2562, 2570
ROTIFERA: 2562
SEAWATER: 2570, 2632
SEDIMENTS: 2570
BISMUTH
ALGAE: 2534, 2570
ANNELIDA: 2570
AVES: 2570
BACTERIA AND YEAST: 2570, 2764
BIBLIOGRAPHY: 2570
BRYOPHYTA: 2570
COELENTERATA: 2570
CRUSTACEA: 2534, 2570
ECHINODERMA TA: 2570
FISH: 2281, 2534, 2570, 2588
HIGHER PLANTS: 2570
INSECTA: 2570
MAMMALIA: 2570
MISCELLANEOOS: 2570
MOLLUSCA: 2375, 2534, 2570
NEMATODA: 2570
PLANKTON: 2570
PROTOZOA: 2570
SEAWATER: 2570
SEDIMENTS: 2570
439
-------
BORON
ALGAE: 2452, 2570, 3078
AMPHIBIA: 3078
ANNELIDA: 2570
AVES: 2570, 3078
BAC1ERIA AND YEAST: 2570, 3078
BIBLIOGRAPHY: 2570, 3078
BRYOPHYTA: 2570
COELEN1ERATA: 2570
CRUSTACEA: 2570, 2591
ECHINODERMA TA : 2570
FISH: 2570, 3078
HIGHER PLANTS: 2452, 2570, 2613, 3078
INSECTA: 2570, 2591, 3078
MAMMALIA: 2378, 2570, 3078
MISCELLANEOUS: 2570
M:JLL USCA: 2570
NEMATODA: 2570
PLANKTON: 2452, 2570
PROTOZOA: 2570, 3078
SEAWATER: 2570, 3078
SEDIMENTS: 2452, 2570, 2591, 3078
CAIMIUM
ALGAE: 2267,2283,2284,2296,2328,2343, 2389,2393,2404,2415,
2447, 2467, 2469, 2470, 2486, 2509, 2513, 2516, 2534, 2546,
2570, 2595, 2608, 2616, 2645, 2647, 2648, 2676, 2683, 2694,
2744, 2749, 2757, 2759, 2815, 2848, 2852, 2856, 2872, 2882,
2911, 2952, 2973, 3004, 3016, 3018, 3037, 3043, 3053, 3092,
3098, 3106, 3122
AMPHIBIA: 2542, 2679, 3049
ANNELIDA: 2250, 2276, 2277, 2283, 2284, 2318,2393, 2447,2456,
2463, 2486, 2509, 2521, 2556, 2562, 2570, 2595, 2645,
2849, 2859, 2872, 2986
AVES: 2283, 2486, 2556, 2562, 2570, 2645, 2706, 2809, 2810, 2872,
2973, 3018, 3037, 3063, 3064
BAC1ERIA AND YEAST: 2283, 2323, 2415, 2429, 2459, 2486, 2497,
2562, 2570, 2595, 2677, 2746, 2764, 2817,
2872, 2952, 2980, 3024
BIBLIOGRAPHY: 2542, 2562, 2570, 2595, 2952, 3063, 3064, 3082,
440
-------
3092
BRYOPHYTA: 2404, 2570, 2655, 2954
CHAETOONATHA: 2328, 2604
COELENTERATA: 2283, 2389, 2562, 2570, 2580, 2604
CRUSTACEA: 2250, 2283, 2292, 2306, 2311, 2317, 2318, 2326, 2328,
2337, 2339, 2343, 2363, 2389, 2427, 2429, 2441, 2447,
2486, 2504, 2513, 2514, 2521, 2525, 2526, 2527, 2530,
2534, 2542, 2562, 2564, 2570, 2582, 2591, 2595, 2602,
2604, 2608, 2610, 2624, 2632, 2646, 2647, 2656, 2661,
2669, 2680, 2698, 2709, 2730, 2739, 2755, 2757, 2769,
2799, 2857, 2872, 2878, 2886, 2887, 2896, 2973, 2993,
3004, 3018,3037,3063, 3064, 3068, 3072, 3096
CTENOPHORA: 2343, 2604
DETRITUS: 2283, 2328
ECHINODERMATA: 2283, 2318, 2379, 2389, 2513, 2542, 2570, 2579,
2595, 3064
ELASMOBRANCHII: 2283, 2345, 2389 2441 2887 2986, 3064
FISH: 2253, 2254, 2263, 2280, 2281, 2282, 2283, 2290, 2292, 2306,
2309, 2312, 2317, 2318, 2322, 2337, 2338, 2341, 2342, 2343,
2344, 2345, 2351, 2362, 2382, 2383, 2389, 2393, 2394, 2402,
2403, 2408, 2412, 2413, 2425, 2428, 2429, 2438, 2441, 2447,
2459, 2477, 2486, 2498, 2505, 2512, 2519, 2521, 2534, 2541,
2542, 2549, 2550, 2551, 2555, 2556, 2558, 2562, 2570, 2584,
2588, 2594, 2595, 2604, 2608, 2610, 2624, 2627, 2628, 2632,
2645, 2646. 2647, 2651, 2656, 2678, 2686, 2688, 2699, 2700,
2715, 2730, 2739, 2757, 2769, 2770, 2779, 2830, 2867, 2872,
2882, 2887,2896, 2910, 2924, 2936, 2965, 2969,2972, 2973,
2982, 2984, 2985, 2986, 2996, 3006, 3022, 3023, 3036, 3037,
3063, 3064, 3073, 3084, 3096, 3101, 3110, 3112, 3131
FUNGI: 2952, 3091
HIGHER PLANTS: 2401,2523, 2529,2570,2579,2607,2608,2645,
2783, 2848, 2872, 2896, 3018, 3025, 3037, 3053,
3063
INSECTA: 2250, 2297, 2300, 2301, 2322, 2393, 2520, 2555, 2556,
2562, 2570, 2591, 2610, 2624, 2629, 2630, 2645, 2706,
2730, 2859, 2930
MAM1ALIA: 2283, 2315, '2378, 2486, 2558, 2570, 2595, 2639, 2739,
2749, 2807, 2872, 3018, 3037, 3063, 3064, 3082
MISCELLANEOOS: 2562, 2570
MOLLUSCA: 2250, 2251, 2275, 2283, 2284, 2285,
2317, 2318, 2322, 2326, 2334, 2371,
2429, 2434, 2441, 2444, 2445, 2446,
2486, 2513, 2521, 2534, 2542, 2557,
2579, 2580, 2584, 2595, 2608, 2610,
2646, 2647, 2656, 2658, 2666, 2669,
2725, 2730, 2734, 2739, 2757, 2760,
2852, 2872, 2887, 2957, 2973, 2995,
4L~1
2289, 2292, 2316,
2375, 2389, 2426,
2447, 2463, 2478,
2558, 2562, 2570,
2624, 2632, 2639,
2674, 2704, 2705,
2803, 2826, 2839,
3018, 3055, 3056,
-------
3063, 3064, 3082, 3096
NEMATODA: 2570
PLANKTON: 2389,2556, 2570, 2573, 2604, 2632, 2647,2771, 2911,
3092
PLATYHELMINTHES :
PORIFERA: 2283,
PROTOZOA: 2283,
ROTIFERA : 2562
SEAWATER: 2389, 2447, 2570, 2573, 2584, 2604, 2608, 2616, 2632,
2676, 2759, 2771, 2852, 2882, 2887, 2995, 3092
SEDIMENTS: 2251, 2253, 2282, 2283, 2284, 2322, 2389, 2401, 2415,
2447, 2477, 2486, 2509, 2520, 2541, 2555, 2556, 2570,
2579, 2591, 2604, 2608, 2610, 2629, 2630, 2645, 2646,
2704, 2705, 2759, 2783, 2848, 2852, 2856, 2859, 2882,
2887,2930, 2969,2982, 2985, 3043, 3053, 3063
SESTON: 2389, 2516, 3043
SIPUNaJLOIDFA : 2595
TUNICATA: 2283, 2604
2438, 2562, 2984
2389, 2562
2542, 2562, 2570, 2872, 2952
CALCIUM
ALGAE: 2283, 2356, 2373, 2389, 2452,
2570, 2572, 2587, 2595, 2620,
2759, 2812, 2828, 2856, 2917,
3108, 3111, 3121
AMPHIBIA: 2542, 2850, 2920
ANNELIDA: 2276, 2283, 2480, 2570, 2595
AVES: 2283, 2570
BACTERIA AND YEAST: 2283, 2349,2570,2595, 2677, 2764, 2966,
2970, 2999
BIBLIOGRAPHY: 2542, 2570, 2595
BRYOPHYTA: 2570, 2954
COELENTERATA: 2259, 2283, 2304~ 2389, 2570, 2721, 2822, 2891,
3059 , 3114
CRUSTACFA: 2265, 2283, 2317,2388, 2389, 2416,
2525, 2526, 2527, 2534, 2536, 2542,
2595, 2610, 2626, 2730, 2774, 2835,
3028 , 3059, 3072
DETRITUS: 2283, 3102
ECHINODERMATA: 2283, 2332, 2389, 2457, 2475, 2481, 2542, 2570,
2595, 2707, 2751, 2891, 2914, 3117
ELASMJBRANCHII: 2283 2389 2481, 3104
FISH: 2249, 2258, 2281, 2283, 2317, 2382, 2383, 2388,
2440, 2471, 2481, 2512, 2534, 2536, 2542, 2551,
2570, 2583, 2585, 2587, 2588, 2595, 2610, 2718,
2469, 2470, 2491, 2534, 2540,
2663, 2676, 2747, 2748, 2749,
2956, 3065, 3087, 3098, 3102,
2457,2481, 2515,
2553, 2570, 2591,
2886, 2891, 2942,
2389, 2430,
2552, 2568,
2730, 2776,
442
-------
2787,2790, 2855, 2902, 2965,2976, 2985, 2996, 3026, 3057,
3071, 3086, 3103, 3104, 3113, 3119, 3127, 3132
FUNGI: 2692, 3111
HIGHER PLANTS: 2262, 2268, 2366, 2452, 2523, 2570, 2618, 2783,
2862
INSECTA: 2570, 2591, 2610, 2626, 2730, 2821, 2893, 2942
MAMMALIA: 2283, 2481, 2570, 2595, 2749
MISCELLANEOOS: 2570
M)LLUSCA: 2283, 2285,
2457, 2475,
2595, 2610,
NEMATODA: 2570
PLANKTON: 2388, 2389, 2452, 2570, 2573
PORIFERA: 2283, 2389
PROTOZOA: 2283, 2542, 2570, 2838, 2938, 3070
SEAWATER: 2389, 2475, 2570, 2573, 2587, 2676, 2759, 3059, 3104
SEDIMENTS: 2283, 2389, 2452, 2570, 2591, 2610, 2759, 2783, 2856,
2985
SESTON: 2389
SIPUNCULOIDEA: 2457, 2595
TUNICATA: 2283
2286, 2317, 2347, 2355, 2375, 2388, 2389,
2479, 2481, 2534, 2542, 2570, 2576, 2587,
2730, 2733, 2891, 2981, 3059
CERIUM
ALGAE: 2328, 2979, 3108
AVES: 2596
CHAETOGNATHA: 2328
CRUSTACEA: 2328, 2979
DETRITUS: 2328
FISH: 2588, 2969, 2979
HIGHER PLANTS: 2398
MAM1ALIA: 2979
MOLLUSCA: 2375, 2398, 2979, 3116
SEAWATER: 2979, 3116
SEDIMENTS: 2969, 2979, 3116
CESIUM
ALGAE: 2328, 2421, 2510, 2565,
2979, 3102, 3108, 3111
AMPHIBIA: 2542, 3030
ANNELIDA: 2510, 2570, 2605
AVES: 2570, 2596, 3030, 3095
2570, 2572, 2605, 2620, 2828, 2863,
443
-------
BACTERIA AND YEAST: 2570
BIBLIOGRAPHY: 2542, 2570
BRYOPHYTA: 2570
CHAETOGNA THA : 2328
COELENTERATA: 2570
CRUSTACEA: 2328, 2542, 2565, 2570, 2632, 2979, 3050
DETRITUS: 2328, 3102
ECHINODERMATA: 2542, 2570
ELASMOBRANCHII: 2360
FISH: 2256, 2360, 2370, 2440, 2542, 2565, 2570, 2588, 2632, 2723,
2786, 2819, 2935, 2979, 3020, 3030, 3088, 3103
FUNGI: 3111
HIGHER PLANTS: 2398, 2570, 2819, 2863, 3019, 3088
INSECTA: 2570
MAMMALIA: 2570, 2979
MISCELLANEOUS: 2570
MOLLUSCA: 2375, 2398, 2542, 2565, 2570, 2603, 2605, 2632, 2674,
2979,3038,3116
NEMATODA: 2570
PLANKTON: 2570, 2632
PROTOZOA: 2542, 2570
SEAWATER: 2421, 2570, 2605, 2632, 2979, 3116
SEDIMENTS: 2421, 2510, 2570, 2605, 2863, 2979, 3019, 3050, 3116
SOILS: 3050
CHROMIUM
ALGAE: 2283, 2284,
2534, 2570,
2852, 2882,
AMPHIBIA: 2542
ANNELIDA: 2276, 2277, 2283, 2284, 2318, 2406, 2447, 2455, 2456,
2486 2562, 2570, 2575, 2595, 2801, 2859
AVES: 2283, 2486, 2562, 2570, 2973, 3037, 3063, 3064
BACTERIA AND YEAST: 2283, 2323, 2349, 2415, 2429, 2439, 2486,
2562, 2570, 2595, 2696, 2728, 2801
BIBLIOGRAPHY: 2542, 2562, 2570, 2595, 3063, 3064, 3092
BRYOPHYTA: 2570, 2954
CHAEfOGNATHA: 2328, 2604
COELENTERATA: 2283, 2389, 2562, 2570, 2604
CRUSTAC~: 2283, 2317, 2318, 2328, 2343, 2389,
2486, 2530, 2534, 2542, 2562, 2570,
2632, 2646, 2647, 2662, 2730, 2899,
3064
CTENOPHORA: 2343, 2604
2328, 2343, 2374, 2389,2415,2447,2452, 2486,
2586, 2595, 2647, 2676, 2694, 2736, 2749, 2759,
2973, 2977, 3037, 3053, 3092, 3122
2429, 2441, 2447,
2591, 2595, 2604,
2973, 3037, 3063,
1+44
-------
DETRITUS: 2283, 2328
ECHINODERMATA: 2283, 2318, 2332, 2389, 2542, 2570, 2579, 2595,
3064
ELASMOBRANCHII: 2283, 2345, 2389, 2441, 3064
FISH: 2253, 2283, 2287, 2314, 2317, 2318, 2338, 2343,
2389, 2403, 2407,2408, 2429, 2441, 2447,2477,
2541, 2542, 2551, 2562, 2570, 2575, 2588, 2595,
2646, 2647, 2715, 2730, 2801, 2882, 2969, 2973,
3037, 3063, 3064
FUNGI: 2314
HIGHER PLANTS:
2345, 2351,
2486, 2534,
2604, 2632,
2985, 2996,
INSECTA: 2422,
2930
MAMMALIA: 2283, 2378,2486, 2570, 2595, 2749, 3037, 3063, 3064
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2283, 2284, 2285, 2289, 2294, 2317,
2407, 2429, 2434, 2441, 2444, 2447,
2557, 2562, 2570, 2575, 2579, 2595,
2704, 2705, 2730, 2803, 2826, 2852,
NEMATODA: 2570
PLANKTGI: 2389 ,
PLATYHELMINTHES :
PORIFERA: 2283,
PROTOZOA: 2283,
ROTIFERA: 2562
SEAWATER: 2389, 2447, 2570, 2575, 2604, 2632, 2662, 2676,2759,
2852, 2882, 3092
SEDIMENTS: 2253, 2283, 2284, 2294, 2389, 2415, 2422,
2452, 2477, 2486, 2520, 2541, 2570, 2575,
2604, 2629, 2630, 2646, 2704, 2705, 2759,
2882, 2930, 2969, 2985, 3053, 3063
SESTON: 2389
SIPUNCULOIDEA: 2595
TUNICATA: 2283, 2604
2439, 2452, 2476, 2529, 2570, 2579, 3037, 3053,
3063
2520, 2562, 2570, 2591, 2629, 2630, 2730, 2859,
2452, 2570, 2604,
2562
2389, 2562
2542, 2562, 2570
2318, 2375, 2389,
2486, 2534, 2542,
2632, 2646, 2647,
2973, 3063, 3064
2632, 2647, 3092
2439,2447,
2579, 2591,
2852, 2859,
COBALT
ALGAE: 2283, 2284,
2534, 2565,
2797,2852,
AMPHIBIA: 2542
ANNELIDA: 2283, 2284, 2447, 2510, 2562, 2570,2595
AVES: 2283, 2562, 2570~ 2596, 3064
BACTERIA AND YEAST: 22tj3, 2349, 2354, 2415, 2562, 2570, 2595,
2328, 2389,2415,2421, 2447,2452, 2491, 2510,
2570, 2572, 2595, 2620, 2676, 2697, 2741, 2749,
2856, 2884, 2952, 3053, 3092, 3098, 3118, 3122
445
-------
2636, 2728, 2764, 2952, 3024
BIBLIOGRAPHY: 2542, 2562, 2570, 2595, 2952, 3064, 3092
BRYOPHYTA: 2570, 2997
CHAETOGNATHA: 2328, 2604
COELENTERATA: 2283, 2389, 2562, 2570, 2604
CRUSTACEA: 2283, 2328, 2389, 2447, 2530, 2534, 2542, 2562, 2565,
2570, 2591, 2595, 2604, 2610, 2730, 2884, 2886, 3064
CTENOPHORA: 2604
DETRITUS: 2283, 2328, 2571
ECHINODERMATA: 2283, 2389, 2542, 2570, 2595, 3064
ELASMJBRANCHII: 2283 2389, 3064
FISH: 2283, 2370, 2389, 2447, 2534, 2542, 2551, 2562, 2565, 2568,
2570, 2588, 2595, 2604, 2610, 2651, 2730, 2731, 2830, 2884,
2969,2985, 2996, 2997, 3064
FUNGI: 2952
HIGHER PLANTS: 2452, 2476, 2522, 2523, 2570, 2783, 2884, 3053
INSECTA: 2562, 2570, 2591, 2610, 2730, 2893, 2997
MAM1ALIA: 2283, 2570, 2595, 2749, 3064
MISCELLANEOUS: 2562, 2570
MJLLUSCA: 2283, 2284, 2285, 2375, 2389, 2444, 2447, 2449, 2534,
2542, 2562, 2565, 2570, 2571, 2595, 2610, 2704, 2705,
2730, 2797, 2826, 2852, 2884, 3038, 3064, 3116
NEMATODA: 2570
PLANKTON: 2389, 2452, 2570, 2604, 3092
PLATYHELMINTHES: 2562
PORIFERA: 2283, 2389, 2562
PROTOZOA: 2283, 2542, 2562, 2570, 2952
ROTIFERA: 2562
SEAWATER: 2389,2421, 2447,2570, 2604, 2676, 2852, 3092, 3116
SEDIMENTS: 2283, 2284, 2354, 2389, 2415, 2421, 2447, 2452, 2510,
2570, 2571, 2591, 2604, 2610, 2704, 2705, 2783, 2852,
2856, 2969, 2985, 2997, 3053, 3116
SESfON: 2389
SIPUNCULOIDEA : 2595
TUNICATA: 2283, 2604
COPPER
ALGAE:
2267,2283,
2359, 2373,
2469, 2473,
2543, 2548,
2660, 2673,
2759, 2773,
2946, 2952,
2284, 2296, 2327,
2374, 2389, 2393,
2486, 2491, 2502,
2565, 2570, 2595,
2676, 2683, 2689,
2811, 2815, 2841,
2958, 2968, 2973,
2328, 2331, 2340, 2343, 2346,
2404, 2433, 2447, 2452, 2461,
2503, 2508, 2511, 2516, 2534,
2597, 2616, 2631, 2645, 2647,
2694, 2697, 2741, 2749, 2757,
2852, 2856, 2872, 2882, 2897,
2991, 3001, 3005, 3016, 3018,
446
-------
3037, 3043, 3053, 3092, 3098, 3118, 3121
AMPHIBIA: 2542
ANNELIDA: 2250, 2266, 2276, 2277, 2279, 2283, 2284, 2336, 2393,
2447, 2456, 2463, 2486, 2521, 2556, 2562, 2570, 2595,
2645, 2716, 2801, 2845, 2872, 2991
AVES: 2283, 2486, 2556, 2562, 2570, 2592, 2645, 2809, 2872, 2973,
3018, 3037, 3064
BACTERIA AND YEAST: 2283,
2511 ,
2765,
3024
2562, 2570, 2595, 2952, 2990, 2991, 3064,
2349, 2429, 2439, 2483, 2486, 2488,
2562, 2570, 2595, 2696, 2763, 2764,
2801, 2817,2872, 2952, 2989, 2991,
BIBLIOGRAPHY: 2542,
3092
BRYOPHYTA: 2404, 2570, 2954
CHAETOGNATHA: 2328, 2336, 2604
COELENTERATA: 2283, 2336, 2389, 2562, 2570, 2580, 2604
CRUSTACEA: 2250, 2252, 2266, 2278, 2279, 2283, 2317, 2326, 2328,
2336, 2343, 2358, 2380, 2389, 2429, 2441, 2447, 2453,
2454, 2460, 2486, 2502, 2515, 2521, 2526, 2530, 2534,
2536, 2542, 2543, 2562, 2565, 2570, 2581, 2591, 2595,
2604, 2610, 2614, 2615, 2632, 2646, 2647, 2656, 2661,
2662, 2698, 2716, 2730, 2757, 2774, 2811, 2872, 2880,
2886,2973, 2991, 2993, 3017, 3018, 3037, 3044, 3064,
3068, 3096
CTENOPHDRA: 2336, 2343, 2358, 2453, 2604
DETRITUS: 2283, 2328, 2508, 2990
ECHINODERMATA: 2266, 2283, 2332, 2336, 2379, 2389, 2475, 2507,
2542, 2543, 2570, 2579, 2595, 2991, 3064
ELASMOBRANCHII: 2283, 2345, 2389 2441 3064
FISH: 2258, 2263, 2271, 2280, 22A1, 2282, 2283, 2293,
2338, 2343, 2345, 2351, 2362, 2364, 2380, 2387,
2403, 2407, 2408, 2418, 2429, 2441, 2447, 2448,
2488, 2512, 2521, 2534, 2535, 2536, 2541, 2542,
2547, 2551, 2552, 2555, 2556, 2562, 2565, 2570,
2588, 2595, 2604, 2610, 2631, 2632, 2634, 2645,
2656, 2665, 2678, 2686, 2718, 2730, 2753, 2757,
2801, 2830, 2855, 2872, 2882, 2897,2906, 2910,
2969, 2972, 2973, 2985, 2989, 2991, 2996, 3005,
3023, 3037, 3058, 3064, 3073, 3096, 3105, 3112,
3129, 3132
FUNGI: 2692, 2952
HIGHER PLANTS: 2257,2439,2452,2529,
2645, 2783, 2872, 2897,
INSECTA: 2250, 2279, 2297, 2393, 2422,
2591, 2610, 2645, 2730
MAMMALIA: 2283, 2315, 2378, 2486, 2570, 2595, 27'49, 2872, 2960,
3018, 3037, 3064
2317, 2336,
2389, 2393,
2477, 2486,
2543, 2545,
2574, 2584,
2646, 2647,
2770, 2787,
2931, 2960,
3007, 3022,
3123, 3128,
2570, 2579, 2607, 2609,
2946, 3018, 3037, 3053
2555, 2556, 2562, 2570,
447
-------
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2250, 2251, 2266, 2275, 2279, 2283, 2284, 2285, 2289,
2291, 2298, 2316, 2317, 2326, 2331, 2334, 2336, 2375,
2389,2399,2407, 2429, 2431, 2434, 2441, 2444, 2445,
2447, 2461, 2463, 2475, 2486, 2494, 2521, 2534, 2542,
2543, 2557, 2562, 2565, 2570, 2579, 2580, 2584, 2595,
2610, 2632, 2646, 2647, 2656, 2658, 2671, 2674, 2704,
2705, 2708,2710, 2730, 2732, 2734, 2757,2803, 2816,
2823, 2825, 2826, 2836, 2839, 2852, 2853, 2872, 2877,
2895, 2905, 2944, 2957, 2964, 2973, 2990, 2991, 2995,
3018, 3027, 3056, 3064, 3096, 3120
NEMATODA: 2570
PHORONIDEA: 2266, 2336
PLANKTON: 2389,2452, 2556, 2570, 2573, 2604,2632, 2647,2665,
2990, 3092
PLATYHELMINTHES: 2279, 2562
PORIFERA: 2283, 2389, 2562
PROTOZOA: 2266, 2283, 2460, 2542, 2562, 2570, 2872, 2952
ROTIFERA: 2266, 2562, 2968
SEAWATER: 2389, 2447, 2475, 2508, 2570, 2573, 2584, 2604, 2616,
2632, 2662, 2676, 2759, 2852, 2882, 2990, 2991, 2995,
3092
SEDIMENTS: 2251, 2279, 2282, 2283,
2439, 2447, 2452, 2477,
2570, 2579, 2591, 2604,
2716, 2759, 2783, 2852,
2990, 2991, 3043, 3053
SESTON: 2358, 2389, 2516, 3043
SIPUNCULOIDEA: 2595
TUNICATA: 2266, 2283, 2336, 2604
CURIUM
FISH: 2588, 2916
DYSPROSIUM
FISH: 2969
SEDIMENTS: 2969
ERBIUM
448
2284, 2331,
2486, 2541,
2610, 2645,
2856, 2882,
2346, 2389, 2422,
2543, 2555, 2556,
2646, 2704, 2705,
2946, 2969, 2985,
-------
FISH: 2969
SEDIMENTS: 2969
EUROPIUM
ALGAE: 2328, 2570
ANNELIDA: 2570
AVES: 2570, 2596
BAC1ERIA AND YEAST: 2570
BIBLIOGRAPHY: 2570
BRYOPHYTA: 2570
CHAETOGNATHA: 2328
COELEN1ERATA: 2570
CRUSTACEA: 2328, 2570
DETRITUS: 2328
ECHINODERMATA: 2570
FISH: 2570, 2588, 2969
HIGHER PLANTS: 2570
IN~CTA: 2570
MAM1ALIA: 2570
MISCELLANEOUS: 2570
MOIL USCA: 2375, 2570
NEMATODA: 2570
PLANKTCN: 2570
PROTOZOA: 2570
SEAWATER: 2570
SEDIMENTS: 2570, 2969
GAroLINIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
449
-------
CRUSTACEA: 2319
CTENOPOORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MM-t1ALIA: 2319
MOI1...USCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTOO: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESTON: 2319
SIPUNaJLOIDEA: 2319
TUNICATA: 2319
GALLIUM
ALGAE: 2319, 2452, 2528, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BAC1ERIA AND YEAST: 2319, 2763, 2764
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534
CTENOPOORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2969
FUNGI: 2319
450.
-------
HIGHER PLANTS: 2319, 2452
INSECTA: 2319
MAMv1ALIA: 2319
MOLLUSCA: 2319, 2375, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319, 2452
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2452, 2969
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
GERMANIUM
ALGAE: 2319, 2493, 2534, 2570, 2668
AMPHIBIA: 2319
ANNELIDA: 2319, 2570
ARACHNOIDEA: 2319
AVES: 2319, 2570
BACTERIA AND YEAST: 2319, 2570
BIBLIOGRAPHY: 2319, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2570
CRUSTACEA: 2319, 2534, 2570
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMA TA : 2319, 2570
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2570
FUNGI: 2319
HIGHER PLANTS: 2319, 2570
INSECTA: 2319, 2570
MAMMALIA: 2319, 2570
MISCELLANEOUS: 2570
MOLLUSCA: 2319, 2375, 2534, 2570
NEMATODA: 2319, 2570
POORONIDEA: 2319
451
-------
PLANKTON: 2319, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570
SEDIMENTS: 2319, 2570
SESTON: 2319
SIPUNCULOIDEA: 2319
TUmCATA: 2319
GOLD
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 27 64
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588
FUNGI: 2319
HIGHER PLANTS: 2319, 2476, 2523
INSECTA: 2319
MAMMALIA: 2319, 2378
MOLLUSCA: 2319, 2375
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTaJ: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
452
-------
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
HAFNIUM
ALGAE: 2319, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 2764
BIBLIOORAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOONATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHI I: 2319
FISH: 2319, 2534, 2969
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
M:>U,USCA: 2319, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTCN: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
HOLMIUM
453
-------
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATIIA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MlMW.IA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONID EA : 2319
PLANKTOO: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESI'ON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
INDIUM
ALGAE: 2319, 2534, 2933
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
454
-------
BACTERIA AND YEAST: 2319, 2933
BIBLIOGRAPHY: 2319, 2933
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHI I: 2319
FISH: 2319, 2534
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319, 2933
MOLLUSCA: 2319, 2534
NEMATOOA: 2319
PHORONIDEA: 2319
PLANKTCN: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
IRIDIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST:
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
2319, 2764
455
-------
CRUSTACEA: 2319
C1ENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
~IA: 2319
MJLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
IRON
ALGAE: 2255, 2283, 2284, 2319, 2320, 2321, 2328, 2346, 2374, 2389,
2404, 2447, 2452, 2491, 2516, 2528, 2543, 2565, 2570, 2590,
2595, 2620, 2647, 2672, 2676, 2694, 2697, 2749, 2759, 2798,
2856, 2889, 2952, 2955, 2973, 3004, 3043, 3098, 3118, 3121
AMPHIBIA: 2319, 2542, 2623
ANNELIDA: 2279, 2283, 2284, 2319, 2447, 2562, 2570, 2595, 2801
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2562, 2570, 2973, 3064
BAC1ERIA AND YEAST: 2255, 2283, 2319, 2349, 2429, 2439, 2562,
2570, 2595, 2763, 2764, 2801, 2814, 2820,
2952, 3009
2542, 2562, 2570, 2595, 2952, 3064
BIBUOGRAPHY: 2319,
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2404, 2570, 2954
CHAETOGNATHA: 2319, 2328, 2372, 2604
COELENTERATA: 2283, 2319, 2389, 2562, 2570, 2604, 2721, 2891
CRUSTACEA: 2279, 2283, 2317, 2319, 2326, 2328, 2372, 2388, 2389,
2429, 2447, 2515, 2530, 2542, 2543, 2562, 2565, 2570,
456
-------
2591, 2595, 2604, 2610, 2614, 2647, 2730, 2886, 2891,
2973, 3004, 3064
C'IENOPHORA: 2319, 2604
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2319, 2389, 2542, 2543, 2570, 2595, 2891,
3064
ELASMOBRANCHII: 2283, 2319, 2389, 3064
FISH: 2258, 2281, 2283, 2317, 2319, 2338, 2388,
2447,2512, 2541, 2542, 2543, 2547,2551,
2588, 2595, 2604, 2610, 2647, 2678, 2730,
2903, 2910, 2918, 2928, 2969, 2973, 2985,
3119
FUNGI: 2319, 2692, 2952
HIGHER PLANTS: 2257, 2260, 2268, 2319, 2333, 2439, 2452, 2476,
2523, 2570, 2607, 2777, 2783
INSECTA: 2279, 2297, 2319, 2562, 2570, 2591, 2610, 2730
MAMMALIA: 2283, 2319, 2570, 2595, 2749, 3064
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2275, 2279, 2283,
2375, 2388, 2389,
2565, 2570, 2589,
2823, 2826, 2853,
3064, 3120
NEMATODA: 2319, 2570
PIDRONIDEA : 2319
PLANKTON: 2319,2388,2389,2452, 2570, 2573, 2604, 2647,2789
PLATYHELMINTHES: 2279, 2319, 2562
PORIFERA: 2283, 2319, 2389, 2562
PROTOZOA: 2283, 2319, 2542, 2562, 2570, 2952
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2447, 2570, 2573, 2604, 2672, 2676, 2759, 2789,
2995
SEDIMENTS: 2279,2283, 2284, 2319, 2346, 2389, 2439, 2447, 2452,
2541, 2543, 2570, 2591, 2604, 2610, 2704, 2705, 2759,
2783, 2856, 2969, 2975, 2985, 3043
SESTON: 2319, 2389, 2516, 3043
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2283, 2319, 2604
2389, 2408, 2429,
2562, 2565, 2570,
2801, 2818, 2830,
2996, 3058, 3064,
2284, 2285, 2317, 2319,
2429, 2444, 2447, 2542,
2595, 2610, 2647,2704,
2891, 2973, 2975, 2995,
2326, 2334,
2543, 2562,
2705, 2730,
3055, 3056,
LANTHANUM
ALGAE: 2283, 2319, 2534
AMPHIBIA: 2319, 2542
ANNELIDA: 2283, 2319
l.~57
-------
ARACHNOIDEA.: 2319
AVES: 2283, 2319
BACTERIA AND YEAST: 2283, 2319, 2677, 2764, 2999
BIBLIOGRAPHY: 2319, 2542
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319
CRUSTACEA.: 2283, 2319, 2534, 2542
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2542
ELASMOBRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2542, 2588, 2969
FUNGI: 2319
HIGHER PLANTS: 2319, 2476
INSECTA: 2319
MAMMALIA: 2283, 2319
MOLLUSCA: 2283, 2319, 2375, 2534, 2542
NEMATODA: 2319
PHORONIDEA.: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2542
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2283, 2319, 2969
SESTON: 2319
SIPUNaJLOIDEA : 2319
TUNICATA: 2283, 2319
LEAD
ALGAE: 2267,2283, 2284, 2296, 2319, 2328, 2343, 2389,2393, 2404,
2415, 2433, 2447, 2452, 2469, 2473, 2486, 2489, 2516, 2524,
2532, 2534,2570,2587,2595,2616,2645,2647,2676,2694,
2697, 2737, 2744, 2749, 2757, 2759, 2806, 2852, 2856, 2866,
2872, 2882, 2992, 3016, 3037, 3053, 3092, 3121, 3122
AMPHIBIA: 2319, 2542, 2679, 2963
ANNELIDA: 2250, 2283, 2284, 2319, 2393, 2405,2447, 2456, 2463,
2486, 2521, 2556, 2562, 2570, 2595, 2645, 2716, 2801,
2866, 2872, 2963
ARACHNOIDEA: 2319
458
-------
AVES: 2283, 2308, 2319, 2329, 2486, 2556, 2562, 2570, 2640, 2645,
2809, 2810, 2829, 2872, 3037, 3063, 3064
BACTERIA AND YEAST: 2283, 2319, 2415, 2429, 2439, 2486, 2497,
2562, 2570, 2595, 2636, 2696, 2728, 2737,
2746, 2764, 2801, 2866, 2872, 3024
2542, 2562, 2570, 2595, 2866, 3063, 3064,
BIBLIOORAPHY: 2319,
3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2404, 2570, 2655, 2954
CHAETOONATHA: 2319, 2328, 2604
COELENTERATA: 2283, 2319, 2389, 2562, 2570, 2604
CRUSTACEA: 2250, 2278, 2283, 2317, 2319, 2328, 2343,
2441, 2447, 2486, 2521, 2534, 2538, 2542,
2591, 2595, 2604, 2610, 2624, 2632, 2646,
2661, 2662, 2716,2730,2737,2739,2754,
2872, 2885, 2887, 2948, 3017, 3037, 3063,
CTENOPHORA: 2319, 2343, 2604
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2319, 2389, 2475, 2542, 2570, 2579, 2595,
3064
ELASMOBRANCHII: 2283, 2319 2345 2389 2441, 2887, 3064
FISH: 2254, 2258, 2263, 2281, 2282, 2283, 2317, 2319, 2322, 2343,
2345, 2351, 2361, 2362, 2389, 2393, 2403, 2405, 2411, 2429,
2440, 2441, 2447, 2477, 2486, 2512, 2519, 2521, 2534, 2541,
2542, 2549,2555, 2556, 2562, 2570, 2584, 2587, 2588, 2593,
2594, 2595, 2599, 2601, 2604, 2610, 2624, 2632, 2645, 2646,
2647,2656, 2675, 2699, 2700, 2730, 2737, 2739, 2754, 2757,
2770, 2801, 2855, 2866, 2867, 2872, 2882, 2887, 2903, 2922,
2923, 2936, 2960, 2972, 2978, 2996, 3037, 3063, 3064, 3127
FUNGI: 2319
HIGHER PLANTS:
2389, 2429,
2562, 2570,
2647, 2656,
2757, 2866,
3064
2319, 2401, 2439, 2452, 2523, 2529, 2570, 2579,
2645, 2754, 2783, 2866, 2872, 3037, 3053, 3063
INSECTA: 2250, 2297, 2319, 2322, 2393, 2405, 2422, 2539, 2555,
2556, 2562, 2570, 2591, 2610, 2624, 2645, 2730
MAMMALIA: 2283, 2315, 2319, 2378, 2486, 2570, 2595, 2739, 2749,
2866, 2872, 2960, 2963, 3037, 3063, 3064
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2250, 2251, 2275,
2319, 2322, 2375,
2447, 2463, 2475,
2562, 2570, 2579,
2632, 264( , 2647,
2730, 2739, 2754,
2866, 2872, 2879,
3056, 3063, 3064
NEMATODA: 2319, 2570, 2866
2283, 2284, 2285, 2289, 2316, 2317,
2389, 2405, 2429, 2434, 2441, 2444,
2486, 2492, 2521, 2534, 2542, 2557,
2584, 2587, 2589, 2595, 2610, 2624,
2656, 2664, 2674, 2704, 2705, 2725,
2757, 2760, 2803, 2826, 2839, 2852,
2887, 2962, 2964, 2975, 2995, 3055,
459
-------
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2452, 2556, 2570, 2573, 2604, 2632, 2647,
3092
PLATYHELMINTHES: 2319, 2562
PORIFERA: 2283, 2319, 2389, 2562
PROTOZOA: 2283, 2319, 2468, 2542, 2562, 2570, 2872
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2447, 2475, 2538, 2570, 2573, 2584, 2587, 2604,
2616, 2632, 2662, 2676, 2759, 2852, 2882, 2887, 2995,
3092
SEDIMENTS: 2251, 2282, 2283, 2284,
2415, 2422, 2439, 2447,
2555, 2556, 2570, 2579,
2704, 2705, 2716, 2754,
2882, 2887, 2975, 3053,
SESTON: 2319, 2389, 2516
SIPUNCULOIDEA : 2319, 2595
TUNICATA: 2283, 2319, 2604
2319, 2322,
2452, 2477,
2591, 2604,
2759, 2783,
3063
2389, 2401, 2405,
2486, 2539, 2541,
2610, 2645, 2646,
2852, 2856, 2866,
LITHIUM
ALGAE: 2283, 2319, 2389, 2493, 2570,2572, 2747,2917
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2570
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2570
BACTERIA AND YEAST: 2283, 2319, 2570, 2652, 2677
BIBLIOGRAPHY: 2319, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2389, 2570
CRUSTACEA: 2283; 2319, 2389, 2570
CTENOPIDRA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2389, 2570
ELASMOBRANCHII: 2283, 2319, 2389
FISH: 2283, 2319, 2389, 2570, 2723
FUNGI: 2319
HIGHER PLANTS: 2319, 2570
INSECTA: 2319, 2570
MAMMALIA: 2283, 2319, 2570
MISCELLANEOUS: 2570
460
-------
MOLLUSCA: 2283, 2319, 2375, 2389, 2570
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319, 2389
PROTOZOA: 2283, 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389, 2570
SEDIMENTS: 2283, 2319, 2389, 2570
SESTON: 2319, 2389
SIPUNaJLOIDEA : 2319
TUNICATA: 2283, 2319
LUTETIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOID FA : 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACFA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONIDFA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
461
-------
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESI'ON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
MAGNESIUM
ALGAE: 2283, 2319, 2356, 2389, 2452, 2469, 2470, 2491, 2534, 2540,
2570, 2572, 2595, 2676, 2748, 2759, 2812, 2856, 2952, 2956,
3098, 3121
AMPHIBIA: 2319, 2542, 2679
ANNELIDA: 2276, 2283, 2319, 2480, 2570, 2595
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2570
BACTERIA AND YEAST: 2283, 2319,
2764, 2785,
BIBLIOGRAPHY: 2319, 2542, 2570,
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570, 2954
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2389, 2570, 2721, 3114
CRUSTACEA: 2265, 2283, 2317, 2319, 2389, 2457, 2481, 2515, 2525,
2534, 2536, 2542, 2570, 2591, 2595, 2610, 2730, 2824,
2835, 2886
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2389, 2457, 2475, 2481, 2542, 2570,
2595, 2914
ELASMOBRANCHII: 2283, 2319, 2389, 2481, 3104
FISH: 2281, 2283, 2317, 2319, 2341, 2389, 2471, 2481, 2512, 2534,
2536, 2542, 2551, 2552, 2570, 2583, 2585, 2595, 2610, 2718,
2730, 2738, 2855, 2912, 2965, 2985, 2996, 3026, 3057, 3104,
3113
FUNGI: 2319, 2952
HIGHER PLANTS: 2262, 2268, 2319, 2366, 2452, 2523, 2570
INSECTA: 2319, 2570, 2591, 2610, 2730
MAMMALIA: 2283, 2319, 2481, 2570, 2595
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2285, 2317, 2319, 2355, 2375, 2389, 2457, 2475,
2479, 2481, 2534, 2542, 2570, 2595, 2610, 2701, 2730,
2733
2349, 2570,2595, 2677, 2728,
2952, 2966, 2999, 3010
2595, 2952
462
-------
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2452, 2570, 2573
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319, 2389
PROTOZOA: 2283, 2319, 2542, 2570, 2838, 2952, 3070
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389, 2475, 2570, 2573, 2676, 2759, 3104
SEDIMENTS: 2283, 2319, 2389, 2452, 2570, 2591, 2610,
2985
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2457, 2595
TUNICATA: 2283, 2319
2759, 2856,
MANGANESE
ALGAE: 2283, 2284, 2319, 2328, 2346, 2365, 2374,
2452, 2464, 2534, 2565, 2570, 2572, 2595,
2660, 2676, 2697, 2741, 2749, 2756, 2759,
2927, 2952, 3047, 3092, 3098, 3118, 3122
AMPHIBIA: 2319, 2542, 2679
ANNELIDA: 2283, 2284, 2319,2447, 2556, 2570, 2595, 2645, 2801
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2556, 2570, 2596, 2645, 3064
BACTERIA AND YEAST: 2283, 2319, 2349, 2439, 2570, 2595, 2801,
2875, 2927,2952, 2966, 2999
BIBLIOGRAPHY: 2319, 2542, 2570, 2595, 2952, 3064, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2404, 2570, 2954
CHAETOGNATHA: 2319, 2328, 2604
COELENTERATA: 2283, 2319, 2389, 2570, 2604, 2891, 3114
CRUSTACEA: 2283, 2317, 2319, 2326, 2328, 2388, 2389, 2447, 2460,
2526, 2530, 2534, 2542, 2553, 2565, 2570, 2591, 2595,
2604, 2610, 2632, 2646, 2647, 2730, 2774, 2837, 2886,
2891, 2993, 3052, 3064
CTENOPHORA: 2319, 2604
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2319, 2389, 2542, 2570, 2595, 2891, 3064
ELASMOBRANCHII: 2283, 2319, 2345, 2389, 3064
FISH: 2281, 2283, 2317, 2319, 2345, 2388, 2389,
2541, 2542, 2547, 2551, 2555, 2556, 2565,
2604, 2610, 2632, 2645,2646,2647, 2678,
2837, 2910, 2927, 2969, 2985, 2996, 3064,
2389, 2404, 2447,
2620, 2645, 2647,
2798, 2837, 2856,
2408, 2447, 2534,
2570, 2588, 2595,
2730, 2731, 2801,
31 05, 3132
463
-------
FUNGI: 2319, 2692, 2952
HIGHER PLANTS: 2257,2260, 2262, 2268, 2319, 2439, 2452, 2476,
2523, 2529, 2570, 2607, 2645
INSECTA: 2319, 2555, 2556, 2570, 2591, 2610, 2645, 2730, 2893
MAMMALIA: 2283, 2319, 2570, 2595, 2749, 3064
MISCELLANEOUS: 2570
MOLLUSCA: 2275, 2283, 2284,
2375, 2388, 2389,
2570, 2589, 2595,
2730, 2826, 2875,
NEMATODA: 2319, 2570
POORONIDEA: 2319
PLANKTON: 2319, 2388, 2389, 2452, 2556, 2570, 2573, 2604, 2632,
2647, 3092
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319, 2389
PROTOZOA: 2283, 2319, 2460, 2542, 2570, 2952
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389, 2447, 2570, 2573, 2604, 2632, 2676, 2759, 3092
SEDIMENTS: 2283, 2284, 2319, 2346, 2389, 2439, 2447, 2452, 2541,
2555, 2556, 2570, 2591, 2604, 2610, 2645, 2646, 2704,
2705, 2759, 2856, 2969, 2985
SESTON: 2319, 2389
SIPUNCULOIDEA : 2319, 2595
TUNICATA: 2283, 2319, 2604
2285, 2289, 2316, 2317, 2319, 2326,
2444, 2447, 2449, 2534, 2542, 2565,
2610, 2632, 2646,2647,2704, 2705,
2891, 2964, 3038, 3064, 3120
MERCURY
ALGAE: 2269, 2272, 2283, 2319, 2328, 2415, 2447, 2482, 2486,2487,
2501, 2534, 2570, 2595, 2608, 2619, 2621, 2645, 2670, 2676,
2683, 2694, 2703, 2711, 2744, 2749, 2780, 2784, 2804, 2808,
2815, 2852, 2864, 2868, 2950, 2952, 2973, 3016, 3034, 3037,
3042, 3043, 3048, 3092, 3121
AMPHIBIA: 2319, 2542, 2679, 2868
ANNELIDA: 2276, 2277, 2283, 2318, 2319, 2390, 2391, 2392, 2442,
2447, 2456, 2463, 2486, 2521, 2531, 2556, 2562, 2570,
2595, 2645, 2881, 3076
ARACHNOIDFA: 2319
AVES: 2283, 2319, 2486, 2490, 2556, 2562, 2570, 2606, 2612, 2643,
2645, 2761, 2809, 2810, 2868, 2881, 2932, 2973, 3037, 3040,
3063, 3064, 3090
BACTERIA AND YEAST: 2283,
2483,
272~ ,
2319, 2349, 2354, 2415, 2450, 2451,
2486, 2559, 2562, 2570, 2595, 2636,
2746, 2764, 2765, 2780, 2784, 2792,
464
-------
2795, 2901, 2941, 2952, 3008, 3015, 3024
BIBLIOGRAPHY: 2319, 2542, 2562, 2570, 2595, 2868, 2952, 3063,
3064, 3092, 3126
BRACHIOPODA: 2319
BRYAZOA: 2319, 3076
BRYOPHYTA: 2319, 2570, 2851, 2881, 2954
CHAETOGNATHA: 2319, 2328, 2604
COELENTERATA: 2283, 2319, 2562, 2570, 2580, 2604
CRUSTACEA: 2283, 2292, 2318, 2319, 2328, 2377, 2390, 2391, 2392,
2437, 2447, 2454, 2486, 2487, 2501, 2504, 2517, 2521,
2530, 2531, 2534, 2542, 2562, 2563, 2570, 2591, 2595,
2604, 2608, 2611, 2621, 2632, 2635, 2642, 2646, 2654,
2656, 2662, 2670, 2680, 2703, 2730, 2768, 2780, 2791,
2868, 2871, 2881, 2886, 2887, 2950, 2951, 2959, 2971,
2973, 2994, 3003, 3037, 3063, 3064, 3068, 3072, 3076,
3096, 3097, 3100
CTENOPHORA: 2319, 2604
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2318, 2319, 2542, 2570, 2595, 2642, 3064
ELASMOBRANCHII: 2264, 2283, 2319, 2345, 2410, 2442, 2722, 2887,
3064
FISH: 2248, 2263, 2264, 2270, 2274,
2310, 2318, 2319, 2335, 2345,
2381, 2386, 2400, 2403, 2410,
2472, 2474, 2486, 2487, 2496,
2519, 2521, 2531, 2534, 2541,
2556, 2559, 2560, 2562, 2563,
2595, 2604, 2606, 2608, 2619,
2645, 2646, 2654, 2656, 2659,
2713, 2724, 2727, 2729, 2730J
2830, 2833, 2851, 2855, 2867,
2909, 2910, 2921, 2932, 2943,
2969, 2971, 2973, 2983, 2985,
3037, 3040, 3041, 3062, 3063,
3096, 3126
FUNGI: 2319, 2952
HIGHER PLANTS: 2319,2476, 2570, 2607, 2608, 2619, 2645, 2851,
2868, 2919, 2932, 3037, 3063, 3083
INSECTA: 2319, 2450, 2482, 2539, 2555, 2556, 2559, 2562, 2563,
2570, 2591, 2645, 2730, 2868, 2881
MAMMALIA: 2283, 2315, 2319, 2377, 2378, 2462,
2566, 2570, 2595, 2606, 2685, 2687,
2761, 2807,2851, 2868, 2960, 2994,
3090, 3126
MISCELLANEOOS: 2562, 2570
MOLLUSCA: 2264, 2283, 2289, 2291, 2292, 2305, 2313, 2318, 2319,
2368, 2375, 2423, 2434, 2447, 2463, 2465, 2486, 2501,
2281, 2282, 2283, 2292, 2309,
2351, 2352, 2353, 2362, 2376,
2428, 2432, 2447, 2450, 2471,
2499, 2500, 2501, 2512, 2518,
2542, 2544, 2551, 2554, 2555,
2566, 2570, 2584, 2588, 2594,
2622, 2628, 2632, 2635, 2642,
2665, 2682, 2687, 2690, 2691,
2761, 2780, 2791, 2794, 2805,
2868, 2871, 2881, 2887, 2908,
2950, 2951, 2953, 2959, 2960,
2994, 3003, 3031, 3033, 3036,
3064, 3069, 3073, 3076, 3089,
2486, 2499, 2554,
2713, 2727, 2749,
3037, 3063, 3064,
L~65
-------
2521, 2531, 2534, 2542,
2584, 2595, 2608, 2632,
2656, 2670, 2674, 2695,
2826, 2839, 2852, 2865,
2971, 2973, 3003, 3029,
3097, 3126
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2556, 2570, 2604, 2632, 2665, 2703, 2768, 2780,
2784, 2808, 2868, 2871, 3092
PLATYHELMINTHES: 2319, 2562
PORIFERA: 2283, 2319, 2562
PROTOZOA: 2283, 2319, 2468, 2542, 2562, 2570, 2952, 3015
REPTILIA: 2319
ROTIFERA: 2319, 2562, 2621
SEAWATER: 2400, 2447,2570, 2584, 2604, 2608, 2632, 2662, 2676,
2703 2852, 2864, 2887, 2892, 2953, 3076, 3092, 3126
SEDIMENTS: 2248, 2282, 2283, 2319,2354, 2368,2415, 2447, 2451,
2486, 2500, 2531, 2539, 2541, 2555, 2556, 2563, 2570,
2591, 2604, 2608, 2642, 2645, 2646, 2703, 2729, 2851,
2852, 2881, 2887, 2932, 2951, 2969, 2985, 2994, 3043,
3063, 3076, 3083, 3126
SESTON: 2319, 2325, 3043
SIPUNaJLOIDEA : 2319, 2595
TUNICATA: 2283, 2319, 2604, 3076
2544, 2557, 2562, 2570, 2580,
2635, 2641, 2642, 2646, 2654,
2712, 2714, 2725, 2730, 2734,
2868, 2877, 2887, 2892, 2959,
3040, 3063, 3064, 3076, 3096,
t-DLYBDENUM
ALGAE: 2283, 2319, 2452, 2486, 2534, 2570, 2788, 3098
AMPHIBIA: 2319, 2542
ANNELIDA: 2283, 2319, 2486, 2570
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2486, 2570, 3064
BACTERIA AND YEAST: 2283, 2319, 2486, 2570, 2636
BIBLIOGRAPHY: 2319, 2542, 2570, 3064
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570, 2891
CRUSTACEA: 2247, 2283, 2319, 2441, 2486, 2534, 2542, 2570, 2591,
2891, 3064
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2247, 2283, 2319,2542, 2570, 2891, 3064
466
-------
ELASMOBRANCHII: 2283, 2319, 2441, 3064
FISH: 2283, 2319, 2441, 2486, 2534, 2541, 2542, 2570, 2588, 3064
FUNGI: 2319
HIGHER PLANTS: 2319, 2452, 2570
INSECTA: 2319, 2570, 2591
MAMMALIA: 2283, 2319, 2486, 2570, 3064
MISCELLANEOUS: 2570
MOLLUSCA: 2247, 2283, 2319, 2375, 2441, 2486, 2534, 2542, 2570,
2891, 3064
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2452, 2570
PLA TYHELMINTHE'3 : 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2542, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570
SEDIMENTS: 2283, 2319, 2452, 2486, 2541, 2570, 2591
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2283, 2319
NEOOYMIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HI GHER PLANTS: 2319
467
-------
INSECTA: 2319
MAMMALIA: 2319
MJu...USCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
NEPTUNIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 3035
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAfvMALIA: 2319
MJu...USCA: 2319, 3035
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTCN: 2319
PLATYHELMINTHES: 2319
468
-------
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
NICKEL
ALGAE: 2283, 2284, 2296, 2319, 2328, 2343,
2447, 2452, 2486, 2491, 2534, 2565,
2676, 2694, 2697, 2749, 2852, 2856,
3053, 3079, 3092, 3122
AMPHIBIA: 2319, 2542, 3079
ANNELIDA: 2276, 2277, 2283, 2284, 2318, 2319, 2393, 2447, 2463,
2486, 2562, 2570, 2595, 2872, 3079
ARACHNOIDFA: 2319
AVES: 2283, 2319, 2486, 2562, 2570, 2592, 2872, 2973, 3064, 3079
BACTERIA AND YEAST: 2283, 2319, 2486, 2562, 2570, 2595, 2764,
2872, 2952, 3024, 3079
2542, 2562, 2570, 2595, 2952, 3064, 3079,
2346, 2374, 2389, 2393,
2570, 2572, 2595, 2647,
2872, 2882, 2952, 2973,
BIBLIOGRAPHY: 2319,
3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570, 2997
CHAETOGNATHA: 2319, 2328, 2604
COELENTERATA: 2283, 2319, 2389, 2562, 2570, 2604
CRUSTACEA: 2283, 2317, 2318, 2319, 2326, 2328, 2343,
2447, 2486, 2534, 2542, 2562, 2565, 2570,
2604, 2610, 2632, 2647,2730, 2872, 2886,
3064, 3079
CTENOPHORA: 2319, 2343, 2604
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2318,2319,2379,2389,2475,2507,2542,
2570, 2579, 2595, 3064, 3079
ELASMOBRANCHII: 2283, 2319, 2345, 2389, 2441, 3064
FISH: 2281, 2283, 2317, 2318, 2319, 2343, 2345, 2351,
2403, 2408, 2441, 2447, 2486, 2512, 2534, 2535,
2551, 2562, 2565, 2570, 2595, 2604, 2610, 2632,
2872, 2882, 2973, 2985, 2996, 2997, 3064, 3079
FUNGI: 2319, 2952, 3079
HIGHER PLANTS: 2319, 2452, 2523, 2529, 2570, 2579, 2783, 2872,
3053, 3079
2389, 2441,
2591, 2595,
2973, 2993,
2389, 2393,
2541, 2542,
2647, 2730,
469
-------
INSECTA: 2297,2319,2393, 2562, 2570,2591, 2610,2730,2997,
3079
MAMMALIA: 2283, 2319, 2486, 2570, 2595, 2749, 2872, 3064, 3079
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2275, 2283, 2284,
2319, 2326, 2330,
2463, 2475, 2486,
2579, 2595, 2610,
2839, 2852, 2872,
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2452, 2570, 2573, 2604, 2632, 2647, 3092
PLATYHELMINTHES: 2319, 2562
PORIFERA: 2283, 2319, 2389, 2562
PROTOZOA: 2283, 2319, 2542, 2562, 2570, 2872, 2952, 3079
REPTILIA: 2319
ROTlFERA: 2319, 2562
SEAWATER: 2389, 2447, 2475, 2570, 2573, 2604, 2632, 2676, 2852,
2882, 2995, 3079, 3092
SEDIMENTS: 2283, 2284, 2319, 2346, 2389, 2447, 2452, 2486, 2541,
2570, 2579, 2591, 2604, 2610, 2704, 2705, 2783, 2852,
2856, 2882, 2985, 2997, 3053
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2595
SOILS: 3079
TUNICATA: 2283, 2319, 2604
2285, 2289,
2375, 2389,
2534, 2542,
2632, 2647,
2973, 2995,
2291, 2316,
2434, 2441,
2557, 2562,
2674, 2704,
3064, 3079
2317,2318,
2444, 2447,
2565, 2570,
2705, 2730,
NIOBIUM
ALGAE: 2319, 2421, 2510, 2534, 2979
AMPHIBIA: 2319
ANNELIDA: 2319, 2510
ARACHNOIDEA: 2319
AVES: 2319, 2596
BACTERIA AND YEAST: 2319, 2764
BIBUOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNA THA : 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534, 2979
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMA TA : 2319
4]0
-------
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2588, 2979
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319, 2979
MOLLUSCA: 2319, 2375, 2534, 2979
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2421, 2979
SEDIMENTS: 2319, 2421, 2510, 2979
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
OSMIUM
ALGAE: 2534
BACTERIA AND YEAST: 2764
CRUSTACEA: 2534
FISH: 2534
MOLLUSCA: 2534
PALLADIUM
ALGAE: 2319, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST:
BIBLIOORAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
2319, 2764
LJ71
-------
CRUSTACEA: 2319, 2534
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2534
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTOO: 2319
PLATYHELMINTH~: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
PLATINUM
ALGAE: 2319, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 2764
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534, 2730
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2730
FUNGI: 2319
472
-------
HIGHER PLANTS: 2319
INSECTA: 2319, 2730
MAMMALIA: 2319
MOLLUSCA: 2319, 2534, 2730
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
PLUTONIUM
ALGAE: 2319, 2346, 2570, 2961, 2974, 2979, 3013, 3066, 3094, 3115
AMPHIBIA: 2319, 2542
ANNELIDA: 2319, 2570, 3013, 3060, 3061
ARACHNOIDEA: 2319
AVES: 2319, 2570, 2596, 3013, 3094
BAC1ERIA AND YEASI': 2319, 2570
BIBLIOGRAPHY: 2319, 2542, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELEN1ERATA: 2319, 2570, 2974
CRUSTACEA: 2319, 2542, 2570, 2632, 2832, 2961, 2979, 3013, 3060,
3061, 3066
C1ENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2542, 2570, 2974, 3013
ELASMOBRANCHII: 2319, 3061
FISH: 2319, 2542, 2570, 2588, 2632, 2832, 2916, 2961, 2974, 2979,
2987, 3013, 3032, 3060, 3061, 3066, 3094, 3124
FUNGI: 2319, 2458
HIGHER PLANTS: 2319, 2570, 3094
INSECTA: 2319, 2570, 3094, 3125
MAMMALIA: 2319, 2570, 2979, 2987, 3013, 3094
MISCELLANEOOS: 2570
MOLLUSCA: 2319,2375,2542, 2570,2617,2632,2674,2831, 2961,
473
-------
2974, 2979, 3013, 3094
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2570, 2632, 2974, 3115
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2542, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570, 2617, 2632, 2961, 2974, 2979, 3013
SEDIMENTS: 2319, 2346, 2570, 2617, 2961, 2974, 2979,
3066, 3094, 3125
SESfON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
POLONIUM
ALGAE: 2319, 2856, 3092
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2538
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588, 3045
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319, 3045
MOLLUSCA: 2319, 2375
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319, 3092
PLATYHELMINTHES: 2319
474
3013, 3060,
-------
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2538, 3092
SEDIMENTS: 2319 , 2856
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
POTASSIUM
ALGAE: 2319, 2373, 2389, 2452, 2493, 2540, 2570, 2572, 2595, 2650,
2676, 2747, 2759, 2812, 2828, 2926, 2958, 3102, 3108, 3111
AMPHIBIA: 2319, 2542
ANNELIDA: 2319, 2480, 2562, 2570, 2595, 2778
ARACHNOIDEA: 2319
AVES: 2319, 2562, 2570, 2596, 2904
BACTERIA AND YEAST: 2319, 2349, 2562, 2570, 2595, 2652, 2677,
2764
BIBLIOGRAPHY: 2319, 2542, 2562, 2570, 2595
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2389, 2562, 2570, 2847
CRUSTACEA: 2265, 2317, 2319, 2389, 2457, 2481, 2542, 2553, 2562,
2570, 2595, 2730, 2774, 2824, 2861, 2886
CTENOPHORA: 2319
DETRITUS: 2319, 3102
ECHINODERMATA: 2319, 2389, 2457, 2475, 2481, 2542, 2570, 2595,
2914
ELASMOBRANCHII: 2319, 2389, 2481, 3104
FISH: 2249, 2274, 2281, 2317, 2319, 2389, 2440,
2562, 2570, 2583, 2588, 2595, 2600, 2723,
2819, 2842, 2855, 2883, 2902, 2912, 2925,
3026, 3071, 3086, 3088, 3103, 3104, 3132
FUNGI: 2319, 3111
HIGHER PLANTS: 2262, 2319, 2366, 2452, 2476, 2523, 2570, 2819,
2862, 3067, 3088
INSECTA: 2319, 2562, 2570, 2730
MAMMALIA: 2319, 2481, 2570, 2595
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2317,2319,2355,2375,2389,2457,2475,2481, 2542,
2562, 2570, 2595, 2695, 2701, 2730
2471, 2481, 2542,
2730, 2738, 2782,
2985, 2996, 3020,
475
-------
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2452, 2570, 2573
PLATYHELMINTHES: 2319, 2562
PORIFERA: 2319, 2389, 2562
PROTOZOA: 2319, 2542, 2562, 2570, 2838, 2938
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2475, 2570, 2573, 2676, 2759, 3104
SEDIMENTS: 2319, 2389, 2452, 2570, 2759, 2985, 3067
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2457, 2595
TUNICATA: 2319
PRASEODYMI UM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
476
-------
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
PROMETHIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
477
-------
PROTACTINIUM
ALGAE: 2319, 2919
AMPIDBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACIDOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2919
CTENOPHORA: 2319
DETRITUS: 2319
ECIDNODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588, 2919
FUNGI: 2319
ID GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319, 2919
MOLLUSCA: 2319, 2919
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2919
SEDIMENTS: 2319, 2919
SESTCN: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
RADIUM
ALGAE: 2319
478
-------
AMPHIBIA: 2319, 2542
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319, 2542
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2542
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2542
ELASMOBRANCHII: 2319
FISH: 2319, 2542, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319, 2375, 2542
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2542
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESI'ON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
RHENIUM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST:
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
2319, 2764
479
-------
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPOORA : 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
RHODIUM
ALGAE: 2319, 2421, 2510, 2605
AMPHIBIA: 2319
ANNELIDA: 2319, 2510, 2605
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 2764
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
480
-------
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
MOLLUSCA: 2319, 2605
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2421, 2605
SEDIMENTS: 2319, 2421,
SESTCN: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
2510, 2605
RUBIDIUM
ALGAE: 2319, 2389, 2565, 2570, 2572, 2898
AMPHIBIA: 2319
ANNELIDA: 2319, 2570
ARACHNOIDEA: 2319
AVES: 2319, 2570
BACTERIA AND YEAST: 2319, 2570, 2652, 2764
BIBLIOGRAPHY: 2319, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2389, 2570
CRUSTACEA: 2319, 2389, 2565, 2570, 2898
CTENOPOORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2389, 2570
ELASMOBRANCHII: 2319, 2389
FISH: 2319, 2389, 2440, 2565, 2570, 2588, 2723, 2830
FUNGI: 2319
HIGHER PLANTS: 2319, 2476, 2570
INSECTA: 2319, 2570
4Rl
-------
MAMMALIA: 2319, 2570
MISCELLANEOUS: 2570
MOLLUSCA: 2319, 2375, 2389, 2565, 2570, 2898
NEMATODA: 2319, 2570
PIDRONIDEA: 2319
PLANKTON: 2319, 2389, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2319, 2389
PROTOZOA: 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389, 2570
SEDIMENTS: 2319, 2389, 2570
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319
TUNICATA: 2319
RUTHENI UM
ALGAE: 2319, 2346, 2421, 2510, 2534, 2605, 2979, 3108
AMPHIBIA: 2319
ANNELIDA: 2319, 2510, 2562, 2605
ARACHNOIDEA: 2319
AVES: 2319, 2562, 2596
BACTERIA AND YEAST: 2319, 2562, 2764
BIBLIOGRAPHY: 2319, 2562
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2562
CRUSTACEA: 2319, 2534, 2562, 2979
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2562, 2588, 2979
FUNGI: 2319
HIGHER PLANTS: 2319, 2398
INSECTA: 2319, 2562
MAMMALIA: 2319, 2979
MISCELLANEOUS: 2562
MOLLUSCA: 2319, 2375, 2398, 2534, 2562, 2605, 2979, 3116
NEMATODA: 2319
PHORONIDEA: 2319
482
-------
ALGAE: 2283, 2319, 2419, 2420, 2570, 2649, 2650, 2741, 2742, 2806,
2894, 3092, 3109, 3130
AMPHIBIA: 2319, 2542, 2874
ANNELIDA: 2283, 2319, 2392, 2480, 2485, 2570, 2740, 2758, 2778,
3077
ARACHNOIDEA: 2319, 3093
AVES: 2283, 2319, 2570, 2904, 2929
BACTERIA AND YEAST: 2283, 2319, 2488, 2570, 2750, 2894, 3014
BIBLIOGRAPHY: 2319, 2542, 2570, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570
CRUSTACEA: 2265, 2283, 2319, 2385, 2392,
2526, 2527, 2542, 2569, 2570,
2740, 2755, 2766, 2767, 2769,
2861, 2870, 2878, 2886, 2899,
2988, 3011, 3039, 3072
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2542, 2570, 2914, 3000
ELASMOBRANCHII: 2283, 2319
FISH: 2249, 2283, 2299, 2319, 2324, 2387, 2396,
2488, 2495, 2542, 2570, 2583, 2598, 2600,
2702, 2717, 2719, 2735, 2740, 2745, 2769,
2854, 2858, 2869, 2883, 2912, 2922, 2925,
FUNGI: 2319, 3014
HIGHER PLANTS: 2319, 2424, 2570, 2862, 2913, 3067
INSECTA: 2319, 2570, 2942
MAMMALIA: 2283, 2319, 2570
PLANKTON: 2319
PLATYHELMINTHES :
PORIFERA: 2319,
PROTOZOA: 2319 ,
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2421, 2605, 2979, 3116
SEDIMENTS: 2319, 2346, 2421, 2510,
SESI'ON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
2319, 2562
2562
2562
2605, 2979, 3116
SALINITY
2417, 2514,
2602, 2637,
2772, 2824,
2900, 2942,
483
2517, 2525,
2667, 2709,
2827, 2857,
2945, 2947,
2397, 2413, 2430,
2628, 2653, 2686,
2781, 2782, 2840,
3006, 3071, 3107
-------
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2319, 2355, 2369, 2423, 2445, 2479, 2537, 2542,
2570, 2589, 2625, 2641, 2701, 2710, 2712, 2834, 2860,
2947, 2962, 3054
NEMATODA: 2319, 2570, 2740
POORONIDEA : 2319
PLANKTON: 2319, 2570, 3092
PLATYHELMINTHES: 2319, 2740
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2542, 2570, 2838
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570, 3092
SEDIMENTS: 2283, 2319, 2570, 3067
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2283, 2319
SAMARIUM
ALGAE: 2319, 2389
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2389
CRUSTACEA: 2319, 2389
CTENOPOORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2389
ELASMOBRANCHII: 2319, 2389
FISH: 2319, 2389, 2969
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MOLLUSCA: 2319, 2375, 2389
NEMATODA: 2319
PHORONIDEA: 2319
~4
-------
PLANKTON: 2319, 2389
PLATYHELMINTHES: 2319
PORIFERA: 2319, 2389
POOTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389
SEDIMENTS: 2319, 2389, 2969
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319
TUNICATA: 2319
SCANDIUM
ALGAE: 2319, 2328, 2389, 2534, 2570
AMPHIBIA: 2319, 2542
ANNELIDA: 2319, 2570
ARACHNOIDEA: 2319
AVES: 2319, 2570, 2596
BAC1ERIA AND YEAST: 2319, 2570
BIBLIOGRAPHY: 2319, 2542, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNA TIIA : 2319, 2328
COELENTERATA: 2319, 2389, 2570
CRUSTACEA: 2319, 2328, 2388, 2389, 2530, 2534, 2542, 2570
CTENOPHORA: 2319
DETRITUS: 2319, 2328
ECHINODERMATA: 2319, 2389, 2542, 2570
ELASmBRANCHII : 2319 2389
FISH: 2319, 2388, 2389, 2534, 2542, 2570, 2588, 2969
FUNGI: 2319
HIGHER PLANTS: 2319, 2570
INSECTA: 2319, 2570
MAMMALIA: 2319, 2570
MISCELLANEOUS: 2570
MOLLUSCA: 2319, 2375, 2388, 2389, 2534, 2542, 2570
NEMATODA: 2319, 2570
POORONIDEA: 2319
PLANKTON: 2319, 2388, 2389, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2319, 2389
PROTOZOA: 2319, 2542, 2570
REPTILIA: 2319
485.
-------
ROTIFERA: 2319
SEAWATER: 2389, 2570
SEDIMENTS: 2319, 2389,
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319
TUNICATA: 2319
2570, 2969
SELENIUM
ALGAE: 2283, 2319, 2328, 2486, 2534, 2570, 2586, 2595, 2694, 3075,
3080, 3092
AMPHIBIA: 2319, 2542
ANNELIDA: 2283, 2319, 2486, 2570, 2595
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2486, 2570, 2809, 3064, 3080
BACTERIA AND YEAST: 2283, 2319, 2486, 2570, 2595, 2764, 2873,
3080
BIBLIOGRAPHY: 2319, 2542, 2570, 2595, 3064, 3080, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570, 2851
CHAETOGNATHA: 2319, 2328
COELENTERATA: 2283, 2319, 2570
CRUSTACEA: 2283, 2319, 2328, 2486, 2530, 2534, 2542, 2570, 2595,
2632, 2730, 2739, 3064, 3080, 3097
CTENOPHORA: 2319
DETRITUS: 2283, 2319, 2328
ECHINODERMATA: 2283, 2319, 2542, 2570, 2595, 3064
ELASMOBRANCHII: 2283, 2319, 3064
FISH: 2263, 2283, 2319, 2376, 2474, 2486, 2534, 2541, 2542, 2554,
2566, 2570, 2595, 2632, 2638, 2687, 2730, 2739, 2830, 2851,
2969, 3064, 3069, 3073, 3080
FUNGI: 2319
HIGHER PLANTS: 2319, 2570, 2851, 3080
INSECTA: 2319, 2570, 2730, 3080
Mm11ALIA: 2283, 2319, 2486, 2554, 2566, 2570, 2595, 2687, 2739,
2807, 2851, 3064, 3080
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2319, 2375, 2486, 2534, 2542, 2570, 2595, 2632,
2730, 2739, 2826, 3064, 3080, 3097
NEMATODA: 2319, 2570
POORONIDEA : 2319
PLANKTON: 2319, 2570, 2632, 3092
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
48fi
-------
PROTOZOA: 2283, 2319, 2542, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570, 2632, 3080, 3092
SEDIMENTS: 2283, 2319, 2486, 2541,
SESTON: 2319
SIPUNCULOIDEA: 2319, 2595
SOILS: 3080
TUNICATA: 2283, 2319
2570, 2851, 2969
SILIOON
ALGAE: 2273, 2302, 2303,
2493, 2534, 2546,
2856, 2949, 3046,
AMPHIBIA: 2319
ANNELIDA: 2319, 2570, 2595
ARACHNOIDEA: 2319
AVES: 2319, 2570
BACTERIA AND YEAST: 2319, 2349, 2570, 2595, 2764
BIBLIOGRAPHY: 2319, 2570, 2595, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
OOELENTERATA: 2319, 2570
CRUSTACEA: 2319, 2534, 2570, 2595
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2570, 2595
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2570, 2595
FUNGI: 2319
HIGHER PLANTS: 2319, 2366, 2452, 2570
INSECTA: 2319, 2570
MAMMALIA: 2319, 2570, 2595
MISCELLANEOUS: 2570
MOLLUSCA: 2319, 2375, 2534, 2570, 2595
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2452, 2570, 2573, 3092
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2570
REPTILIA: 2319
2319, 2340, 2357,2395, 2435, 2436, 2452,
2570, 2595, 2668, 2676, 2681, 2773, 2841,
3092
4'J]
-------
ROTIFERA: 2319
SEAWATER: 2570, 2573, 2676, 2681, 3092
SEDIMENTS: 2319, 2452, 2570, 2856
SESTON: 2319
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2319
SILVER
ALGAE: 2283, 2284, 2319, 2328, 2343, 2389, 2447, 2501, 2570, 2595,
2676, 2952, 2973, 3092
AMPHIBIA: 2319, 2542
ANNELIDA: 2283, 2284, 2319, 2447, 2562, 2570, 2595, 2844
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2562, 2570, 2973, 3064
BACTERIA AND YEAST: 2283, 2319, 2562, 2570, 2595, 2762, 2764,
2952
BIBLIOGRAPHY: 2319, 2542, 2562, 2570, 2595, 2952, 3064, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319, 2328
COELENTERATA: 2283, 2319, 2389, 2562, 2570
CRUSTACEA: 2283, 2292, 2319, 2326, 2328, 2343, 2389, 2441, 2447,
2501, 2542, 2562, 2570, 2591, 2595, 2632, 2646, 2973,
3064, 3096
CTENOPHORA: 2319, 2343
DETRITUS: 2283, 2319, 2328, 2571
ECHINODERMATA: 2283, 2319, 2389, 2542, 2570, 2595, 3064
ELASMOBRANCHII: 2283, 2319, 2345, 2389, 2441, 2844, 3064
FISH: 2283, 2292, 2319, 2342, 2343, 2345, 2351, 2389, 2441, 2447,
2501, 2506, 2541, 2542, 2549, 2562, 2570, 2588, 2595, 2632,
2646, 2776, 2844, 2973, 3064, 3096
FUNGI: 2319, 2952
HIGHER PLANTS: 2319, 2476, 2522, 2523, 2529, 2570, 2783
INSECTA: 2319, 2562, 2570, 2591
MAMMALIA: 2283, 2319, 2378, 2570, 2595, 3064
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2283, 2284, 2285, 2289,
2389, 2441, 2444, 2447,
2571, 2595, 2632, 2646,
2957, 2973, 3064, 3096
NEMATODA: 2319, 2570
POORONIDEA : 2319
PLANKTON: 2319, 2389, 2570, 2573, 2632, 3092
2291, 2292, 2319, 2326, 2375,
2501, 2542, 2557, 2562, 2570,
2674, 2704, 2705, 2826, 2877,
48R
-------
PLATYHELMINTHES :
PORIFERA: 2283,
PROTOZOA: 2283,
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2447, 2570, 2573, 2632, 2676, 3092
SEDIMENTS: 2283, 2284, 2319, 2389, 2447, 2541, 2570,
2646, 2704, 2705, 2783
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2283, 2319
2319, 2562
2319, 2389, 2562
2319, 2542, 2562, 2570, 2952
2571, 2591,
SODIUM
ALGAE: 2283, 2319, 2373, 2389, 2452, 2470, 2493, 2534, 2540, 2570,
2572, 2595, 2676, 2747, 2759, 2812, 2828, 2894, 2917
AMPHIBIA: 2319, 2542, 2633, 2796, 2874, 2920
ANNELIDA: 2283, 2319, 2480, 2485, 2562, 2570, 2595, 2758, 2778
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2562, 2570, 2596, 2904
BACTERIA AND YEAST: 2283, 2319, 2349, 2562, 2570, 2595, 2652,
2677,2750, 2764,2894, 3014
BIBLIOGRAPHY: 2319, 2542, 2562, 2570, 2595
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2389, 2562, 2570, 2847
CRUSTACEA: 2265, 2283, 2317, 2319, 2389, 2457, 2481, 2534, 2542,
2553, 2562, 2570, 2591, 2595, 2626, 2730, 2766, 2767,
2774, 2824, 2900, 2942, 2945, 3100
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2389, 2457, 2475, 2481, 2542, 2570,
2595, 2914
ELASMOBRANCHII: 2283, 2319, 2389, 2481, 3104
FISH: 2249, 2274, 2281, 2283, 2317, 2319, 2389,
2542, 2562, 2570, 2583, 2595, 2600, 2653,
2738, 2745, 2782, 2790, 2842, 2855, 2867,
2969, 2996, 3026, 3071, 3086, 3104
FUNGI: 2319, 3014
HIGHER PLANTS: 2262, 2319, 2366, 2452, 2476, 2523, 2570, 2862
INSECTA: 2319, 2562, 2570, 2591, 2626, 2730, 2942
MAMMALIA: 2283, 2319, 2481, 2570, 2595
MISCELLANEOUS: 2562, 2570
2471, 2481, 2534,
2717, 2723, 2730,
2883, 2912, 2925,
~9
-------
MOLLUSCA: 2283, 2317, 2319, 2355, 2375, 2389, 2457, 2475, 2479,
2481, 2534, 2542, 2562, 2570, 2595, 2701, 2730, 2890
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2389, 2452, 2570, 2573
PLATYHELMINTHES: 2319, 2562
PORIFERA: 2283, 2319, 2389, 2562
PROTOZOA: 2283, 2319, 2542, 2562, 2570, 2838, 2938, 3070
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2475, 2570, 2573, 2676, 2759, 3104
SEDIMENTS: 2283, 2319, 2389, 2452, 2570, 2591, 2759, 2969
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2457, 2595
TUNICATA: 2283, 2319
STRONTI UM
ALGAE: 2319, 2328, 2389, 2452, 2484, 2534, 2587,2595,2620, 2676,
2749, 2828, 2863, 2956, 3065, 3087, 3092, 3102, 3108, 3111
AMPHIBIA: 2319, 2542
ANNELIDA: 2319, 2595
ARACHNOIDEA: 2319
AVES: 2319, 2596
BACTERIA AND YEAST: 2319, 2595, 2677, 2764, 2999
BIBLIOGRAPHY: 2319, 2542, 2595, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319, 2328
COELENTERATA: 2319, 2389, 2721, 2822, 3059, 3114
CRUSTACEA: 2317, 2319, 2326, 2328, 2388, 2389, 2534, 2542, 2553,
2595, 2632, 2730, 3059
CTENOPHORA: 2319
DETRITUS: 2319, 2328, 3102
ECHINODERMATA: 2319, 2389, 2542, 2595
ELASMOBRANCHII: 2319, 2389
FISH: 2256,2317,2319, 2384, 2388, 2389, 2440, 2534, 2542, 2587,
2588, 2595, 2632, 2730, 3103
FUNGI: 2319, 3111
HIGHER PLANTS: 2319, 2398, 2452, 2522, 2523, 2618, 2863
INSECTA: 2319, 2730
MAMMALIA: 2319, 2595, 2749
MOLLUSCA: 2286, 2317, 2319, 2326, 2375, 2388, 2389, 2398, 2534,
2542, 2587, 2595, 2632, 2730, 2981, 3059, 3116
1+90
-------
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319, 2388, 2389, 2452, 2573, 2632, 3092
PLATYHELMINTHES: 2319
PORIFERA: 2319, 2389
PROTOZOA: 2319, 2542, 2938
REPTILIA: 2319
ROTIFERA : 2319
SEAWATER: 2389, 2573, 2587, 2632, 2676, 3059, 3092, 3116
SEDIMENTS: 2319, 2389, 2452, 2863, 3116
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2319
TANTALUM
ALGAE: 2319, 2389, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 2764
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
OOELENTERATA: 2319, 2389
CRUSTACEA: 2319, 2389, 2534
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2389
ELASMOBRANCHII: 2319, 2389
FISH: 2319, 2389, 2534
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MOLLUSCA: 2319, 2389, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319, 2389
PLATYHELMINTHES: 2319
PORIFERA: 2319, 2389
PROTOZOA: 2319
491
-------
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2389
SEDIMENTS: 2319, 2389
SESTON: 2319, 2389
SIPUNCULOIDEA: 2319
TUNICATA: 2319
TECHNElI UM
ALGAE: 2319, 2346
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAElOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPOORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MOLLUSCA: 2319, 2375
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2346
SESfON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
492
-------
TELLURIUM
ALGAE: 2319, 2534
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319, 2728, 2764
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATIfA : 2319
CDELENTERATA: 2319
CRUSTACEA: 2319, 2534
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2534, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MJLLUSCA: 2319, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESI'ON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
TERBIUM
ALGAE: 2319
493
-------
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BAC1ERIA AND YEAST: 2319
BIBLIOORAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOONATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HI GHER PLANTS: 2319
llJSECTA: 2319
MM-t1ALIA: 2319
MOLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTIJES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SEsrON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
THALLIUM
ALGAE: 2283, 2319, 2534, 2570, 2595, 2952
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2570, 2595
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2570
BAC1ERIA AND YEAST: 2283, 2319, 2570, 2595, 2764, 2952
BIBLIOORAPHY: 2319, 2570, 2595, 2952
BRACHIOPODA: 2319
494
-------
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570
CRUSTACEA: 2283, 2319, 2534, 2570, 2595
CTENOPOORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2570, 2595
ELASMOBRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2570, 2588, 2595
FUNGI: 2319, 2952
HIGHER PLANTS: 2319, 2570
INSECTA: 2319, 2570
MAMMALIA: 2283, 2319, 2570, 2595
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2319, 2534, 2570, 2595
NEMATODA: 2319, 2570
POORONIDEA : 2319
PLANKTON: 2319, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2570, 2952
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570
SEDIMENTS: 2283, 2319, 2570
SESTON: 2319
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2283, 2319
THORIUM
ALGAE: 2319, 2570
AMPHIBIA: 2319
ANNELIDA: 2319, 2570
ARACHNOIDEA: 2319
AVES: 2319, 2570
BACTERIA AND YEAST: 2319, 2570
BIBLIOGRAPHY: 2319, 2570
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2319, 2570
CRUSTACEA: 2319, 2570, 3050
495
-------
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2570
ELASMJBRANCHII: 2319
FISH: 2319, 2570, 2588
FUNGI: 2319
HIGHER PLANTS: 2319, 2570
INSECTA: 2319, 2570
MAMMALIA: 2319, 2570
MISCELLANEOUS: 2570
MOLLUSCA: 2319, 2375, 2570
NEMATODA: 2319, 2570
PHORONIDEA : 2319
PLANKTON: 2319, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570
SEDIMENTS: 2319, 2570, 3050
SESTON: 2319
SIPUNCULOIDEA: 2319
SOILS: 3050
TUNICATA: 2319
THULl UM
ALGAE: 2319
AMPHIBIA: 2319
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
496
-------
FISH: 2319
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAM1ALIA: 2319
MJLLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2319
TIN
ALGAE: 2283, 2319, 2534, 2570, 2804, 3081
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2570, 3081
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2570, 3064
BACTERIA flJID YEAST: 2283, 2319, 2570, 2728, 2764, 3081
BIBLIOGRAPHY: 2319, 2570, 3064, 3081
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570, 3081
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570, 3081
CRUSTACEA: 2283, 2319, 2534, 2570, 2591, 2730, 3064
C1ENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2570, 3064, 3081
ELASMOBRANCHII: 2283, 2319, 3064
FISH: 2283, 2319, 2534, 2541, 2570, 2730, 2775, 2939, 3064, 3081
FUNGI: 2319, 3081
HIGHER PLANTS: 2319, 2570, 3081
INSECTA: 2319, 2570, 2591, 2730
MAMMALIA: 2283, 2319, 2570, 3064, 3081
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2319, 2375, 2534, 2570, 2730, 3064, 3081
497
-------
NEMATODA: 2319, 2570, 3081
PHORONIDEA: 2319
PLANKTON: 2319, 2570, 3081
PLATYHELMINTH~ : 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2570, 3081
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570, 3081
SEDIMENTS: 2283, 2319, 2541, 2570, 2591
SESTON: 2319
SIPUNCULOIDEA : 2319
SOILS: 3081
TUNICATA: 2283, 2319
TITANIUM
ALGAE: 2283, 2319, 2452, 2534, 2570, 2595
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2570, 2595
ARACHNOID FA: 2319
AVES: 2283, 2319, 2570
BACTERIA AND YEAST: 2283, 2319, 2349, 2570, 2595, 2764
BIBLIOGRAPHY: 2319, 2570, 2595
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570
CRUSTACEA: 2283, 2319, 2326, 2534, 2570, 2591, 2595
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2570, 2595
ELASMOBRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2570, 2595
FUNGI: 2319
HIGHER PLANTS: 2319, 2452, 2570
INSECTA: 2319, 2570, 2591
MAMMALIA: 2283, 2319, 2570, 2595
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2319, 2326, 2375, 2444, 2534, 2570, 2595
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2452, 2570
PLATYHELMINTHES: 2319
498
-------
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2570
SEDIMENTS: 2283, 2319, 2452, 2570, 2591
SESTON: 2319
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2283, 2319
TUNGSTEN
ALGAE: 2283, 2319, 2534
AMPHIBIA: 2319
ANNELIDA: 2283, 2319
ARACHNOIDEA: 2319
AVES: 2283, 2319
BACTERIA AND YEAST: 2283, 2319, 2764, 2873
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
CDELENTERATA: 2283, 2319
CRUSTACEA: 2283, 2319, 2534
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319
ELASMOBRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2588
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2283, 2319
M)LLUSCA: 2283, 2319, 2534
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTOO: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2283, 2319
SESTON: 2319
499
-------
SIPUNCULOIDEA: 2319
TUNICATA: 2283, 2319
URANIUM
ALGAE: 2283, 2319, 2534, 2752
AMPHIBIA: 2319, 2542
ANNELIDA: 2283, 2319
ARACHNOIDFA: 2319
AVES: 2283, 2319
BACTERIA AND YEAST: 2283, 2319
BIBLIOGRAPHY: 2319, 2542
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319
CRUSTACEA: 2283, 2319, 2534, 2542, 3050
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2542
ELASM)BRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2542, 2588
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2283, 2319
M)LLUSCA: 2283, 2319, 2534, 2542
NEMATODA: 2319
PIDRONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES :
PORIFERA: 2283,
PROTOZOA: 2283,
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2283, 2319, 3050
SESTON: 2319
SIPUNCULOIDEA: 2319
SOILS: 3050
TUNICATA: 2283, 2319
2319
2319
2319, 2542
VANADIUM
50.0
-------
ALGAE: 2283, 2295, 2319, 2409, 2452, 2534, 2570, 2577, 2578, 2586,
2934, 3051
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2570, 3051
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2570, 3064
BACTERIA AND YEAST: 2283, 2319, 2570, 2934
BIBLIOGRAPHY: 2319, 2570, 2934, 3064
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2570
CHAETOGNATHA: 2319
COELENTERATA: 2283, 2319, 2570
CRUSTACEA: 2283, 2317, 2319, 2534, 2570, 2591, 3051, 3064
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319, 2570, 2934, 3064
ELASMOBRANCHII: 2283, 2319, 3064
FISH: 2283, 2317, 2319, 2534, 2541, 2570, 3064
FUNGI: 2319 .
HIGHER PLANTS: 2319, 2452, 2570
INSECTA: 2319, 2570, 2591
MAMMALIA: 2283, 2319, 2570, 2934, 3064
MISCELLANEOUS: 2570
MOLLUSCA: 2283, 2317, 2319, 2375, 2444, 2534, 2570, 2934, 3051,
3064
NEMATODA: 2319, 2570
PHORONIDEA: 2319
PLANKTON: 2319, 2452, 2570
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319, 2570
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2295, 2570
SEDIMENTS: 2283, 2295, 2319, 2452, 2541, 2570, 2591
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2283, 2319, 2934
YTTERBIUM
ALGAE: 2319
AMPHIBIA: 2319
501
-------
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319
CTENOPIDRA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319
ELASMOBRANCHII: 2319
FISH: 2319, 2969
FUNGI: 2319
HIGHER PLANTS: 2319
INSECTA: 2319
MAMMALIA: 2319
M)LLUSCA: 2319
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTHES: 2319
PORIFERA: 2319
PROTOZOA: 2319
REPTILIA: 2319
ROTIFERA: 2319
SEDIMENTS: 2319, 2969
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
YTTRIUM
ALGAE: 2319, 2534, 2620, 2800
AMPHIBIA: 2319, 2542
ANNELIDA: 2319
ARACHNOIDEA: 2319
AVES: 2319
BACTERIA AND YEAST: 2319
BIBLIOGRAPHY: 2319, 2542
BRACHIOPODA: 2319
BRYAZOA: 2319
.102
-------
BRYOPHYTA: 2319
CHAETOGNATHA: 2319
COELENTERATA: 2319
CRUSTACEA: 2319, 2534, 2542
CTENOPHORA: 2319
DETRITUS: 2319
ECHINODERMATA: 2319, 2542
ELASMOBRANCHII: 2319
FISH: 2319, 2384, 2534, 2542, 2588
FUNGI: 2319
HI GHER PLANTS: 2319
INSECTA: 2319
MAt+1ALIA: 2319
MOLLUSCA: 2319, 2534, 2542
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319
PLATYHELMINTEES: 2319
PORIFERA: 2319
PROTOZOA: 2319, 2542
REPTILIA: 2319
ROTIFERA: 2319
SEDI MENTS : 2319
SESTON: 2319
SIPUNCULOIDEA : 2319
TUNICATA: 2319
ZINC
ALGAE: 2261, 2283, 2284, 2296,
2389, 2393, 2404, 2414,
2486, 2491, 2508, 2513,
2572, 2595, 2616, 2620,
2694, 2697, 2741, 2744,
2856, 2872, 2882, 2952,
3074, 3092, 3098, 3118,
AMPHIBIA: 2319, 2542
ANNELIDA: 2250, 2276, 2277, 2279, 2283, 2284, 2318, 2319, 2393,
2447, 2456, 2463, 2486, 2521, 2556, 2562, 2570, 2595,
2645, 2716, 2801, 2859, 2872
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2486, 2556, 2562, 2570, 2592, 2596, 2645, 2809,
2872, 2973, 3018, 3037, 3064
BACTERIA AND YEAST: 2283, 2319, 2349, 2429, 2439, 2486, 2497,
2562, 2570, 2595, 2696, 2764, 2801, 2872,
2319, 2328,
2447, 2452,
2516, 2534,
2645, 2647,
2749, 2757,
2973, 2977,
3121, 3122
2343, 2350, 2356, 2374,
2461, 2469, 2470, 2484,
2561, 2565, 2567, 2570,
2648, 2660, 2676, 2683,
2759, 2800, 2813, 2852,
3018, 3037, 3043, 3053,
503
-------
2952, 3014, 3024
BIBLIOGRAPHY: 2319, 2542, 2562, 2570, 2595, 2952, 3064, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319, 2404, 2570, 2954
CHAETOGNATIlA: 2319, 2328, 2604
COELENTERATA: 2259, 2283, 2319, 2389, 2562, 2570, 2604, 3114
CRUSTACEA: 2250, 2261, 2279, 2283, 2306, 2317, 2318, 2319, 2326,
2328,2343, 2388, 2389, 2429, 2447, 2486, 2513, 2515,
2521, 2530, 2534, 2542, 2562, 2565, 2570, 2591, 2595,
2604, 2610, 2615, 2632, 2646, 2647, 2656, 2661, 2684,
2698, 2716, 2730, 2739, 2757, 2774, 2872, 2886, 2887,
2973, 2993, 3012, 3018, 3037, 3064
CTENOPHORA: 2319, 2343, 2604
DETRITUS: 2283, 2319, 2328, 2508, 2571
ECHINODERMATA: 2283, 2318, 2319, 2332, 2379, 2389, 2475, 2507,
2513, 2542, 2570, 2579, 2595, 3064
ELASMOBRANCHII: 2283, 2319, 2345, 2389, 2887, 3064
FISH: 2254,2258,2263, 2280,2281, 2282, 2283,2306,2307,2317,
2318, 2319, 2338, 2343, 2345, 2351, 2362, 2367, 2387, 2388,
2389,2393,2408,2429,2447,2472, 2477,2486,2512, 2521,
2533, 2534, 2535, 2541, 2542, 2547, 2551, 2552, 2555, 2556,
2558, 2562, 2565, 2570, 2584, 2585, 2588, 2595, 2604, 2610,
2632, 2645, 2646, 2647, 2656, 2665, 2678, 2684, 2699, 2700,
2715, 2718, 2726, 2730, 2731, 2739, 2757, 2770, 2801, 2802,
2830, 2855, 2872, 2882, 2887, 2888, 2906, 2910, 2915, 2924,
2936, 2969, 2972, 2973, 2976, 2982, 2985, 2996, 2998, 3021,
3022, 3023, 3037, 3058, 3064, 3073, 3074, 3085, 3099, 3105,
3110, 3112, 3129, 3132
FUNGI: 2319, 2692, 2693, 2952, 3014
HIGHER PLANTS: 2319, 2439, 2452, 2476, 2523, 2529,
2609, 2645, 2783, 2872, 3018, 3037,
INSECTA: 2250,2279,2297, 2319, 2393, 2422, 2520,
2562, 2570, 2591, 2610, 2629, 2630, 2645,
2859, 2930
MAMMALIA: 2283, 2315, 2319, 2378, 2486, 2558, 2570, 2595, 2739,
2749, 2872, 3018, 3037, 3064
MISCELLANEOUS: 2562, 2570
MOLLUSCA: 2250, 2251, 2261,
2291, 2316, 2317,
2375, 2388, 2389,
2461, 2463, 2475,
2558, 2562, 2565,
2632, 2646, 2647,
2730, 2739, 2757,
2877, 2887, 2895,
3056, 3064, 3120
2570, 2579,
3053
2555, 2556,
2730, 2821,
2275, 2279, 2283,
2318, 2319, 2326,
2429, 2434, 2444,
2486, 2513, 2521,
2570, 2571, 2579,
2656, 2658, 2671,
2802, 2823, 2826,
2957, 2964, 2973,
2284, 2285, 2289,
2334, 2348, 2371,
2445, 2446, 2447,
2534, 2542, 2557,
2584, 2595, 2610,
2674, 2704, 2705,
2839, 2852, 2872,
3012, 3018, 3055,
104
-------
NEMATODA: 2319, 2570
POORONIDEA : 2319
PLANKTON: 2319, 2388, 2389, 2452, 2556, 2570, 2573, 2604, 2632,
2647, 2665, 3092
PLATYHELMINTHES: 2279, 2319, 2348, 2562
PORIFERA: 2283, 2319, 2389, 2562
PROTOZOA: 2283, 2319, 2468, 2542, 2562, 2570, 2872, 2952
REPTILIA: 2319
ROTIFERA: 2319, 2562
SEAWATER: 2389, 2447, 2475, 2508, 2570, 2573, 2584, 2604, 2616,
2632, 2676, 2759, 2852, 2882, 2887, 3092
SEDIMENTS: 2251, 2261, 2279, 2282, 2283, 2284, 2319,
2439, 2447, 2452, 2477, 2486, 2520, 2541,
2570, 2571, 2579, 2591, 2604, 2610, 2629,
2646, 2704, 2705, 2716, 2759, 2783, 2852,
2882, 2887, 2930, 2969, 2982, 2985, 3043,
SESTON: 2319, 2389, 2516, 3043
SIPUNCULOIDEA: 2319, 2595
TUNICATA: 2283, 2319, 2604
2389, 2422,
2555, 2556,
2630, 2645,
2856, 2859,
3053
ZIRCONIUM
ALGAE: 2283, 2319, 2421, 2452, 2510, 2534, 2793, 2856, 2979, 3092
AMPHIBIA: 2319
ANNELIDA: 2283, 2319, 2510
ARACHNOIDEA: 2319
AVES: 2283, 2319, 2596
BACTERIA AND YEAST: 2283, 2319, 2764
BIBLIOGRAPHY: 2319, 3092
BRACHIOPODA: 2319
BRYAZOA: 2319
BRYOPHYTA: 2319
CHAETOGNA TRA : 2319
COELENTERATA: 2283, 2319
CRUSTACEA: 2283, 2319, 2534, 2979
CTENOPHORA: 2319
DETRITUS: 2283, 2319
ECHINODERMATA: 2283, 2319
ELASMOBRANCHII: 2283, 2319
FISH: 2283, 2319, 2534, 2588, 2793, 2979
FUNGI: 2319
HIGHER PLANTS: 2319, 2452
INSECTA: 2319
MAMMALIA: 2283, 2319, 2979
MOLLUSCA: 2283, 2319, 2375, 2534, 2979
505
-------
NEMATODA: 2319
PHORONIDEA: 2319
PLANKTON: 2319, 2452, 3092
PLATYHELMINTHES: 2319
PORIFERA: 2283, 2319
PROTOZOA: 2283, 2319
REPTILIA: 2319
ROTIFERA: 2319
SEAWATER: 2421, 2979, 3092
SEDIMENTS: 2283, 2319, 2421,
SESTON: 2319
SIPUNCULOIDEA: 2319
TUNICATA: 2283, 2319
2452, 2510, 2856, 2979
506
-------
INDEX - TAXA
ALGAE
ALUMINUM: 2283, 2288, 2395, 2452, 2528, 2570, 2595, 2676, 2856
AMERICIUM: 2961, 2974, 2979
ANTIMONY: 2283, 2328, 2534, 2570
ARSENIC: 2283, 2447, 2486, 2534, 2543, 2546, 2570, 2595, 2644,
2645, 2694, 2720, 2843, 2846,2876,2937, 2967, 3092
BARIUM: 2452, 2464, 2534, 2587, 2620, 2676, 2749
BERYLLIUM: 2283, 2534, 2570
BIBLIOGRAPHY: 2570
BISMUTH: 2534, 2570
BORON: 2452, 2570, 3078
CADMIUM: 2267,2283, 2284, 2296, 2328, 2343, 2389, 2393, 2404,
2415, 2447, 2467, 2469, 2470, 2486, 2509, 2513, 2516,
2534, 2546, 2570, 2595, 2608, 2616, 2645, 2647, 2648,
2676, 2683, 2694, 2744, 2749, 2757, 2759, 2815, 2848,
2852, 2856, 2872, 2882, 2911, 2952, 2973, 3004, 3016,
3018, 3037, 3043, 3053, 3092, 3098, 3106, 3122
CALCIUM: 2283, 2356, 2373, 2389, 2452, 2469, 2470, 2491, 2534,
2540, 2570, 2572, 2587, 2595, 2620, 2663, 2676, 2747,
2748,2749, 2759, 2812, 2828, 2856, 2917, 2956, 3065,
3087, 3098, 3102, 3108, 3111, 3121
CERIUM: 2328, 2979, 3108
CESIUM: 2328, 2421, 2510, 2565, 2570, 2572, 2605, 2620, 2828,
2863, 2979, 3102, 3108, 3111
CHROMIUM: 2283, 2284, 2328, 2343, 2374, 2389, 2415, 2447, 2452,
2486, 2534, 2570, 2586, 2595, 2647, 2676, 2694, 2736,
2749, 2759, 2852, 2882, 2973, 2977, 3037, 3053, 3092,
3122
COBALT: 2283, 2284, 2328,
2510, 2534, 2565,
2741, 2749, 2797,
3098,3118,3122
COPPER: 2267,2283, 2284, 2296, 2327,
2346, 2359, 2373, 2374, 2389,
2452, 2461, 2469, 2473, 2486,
2511, 2516, 2534, 2543, 2548,
2616, 2631, 2645, 2647, 2660,
2694, 2697, 2741, 2749, 2757,
2841, 2852, 2856, 2872, 2882,
2968, 2973, 2991, 3001, 3005,
3053, 3092, 3098, 3118, 3121
EUROPIUM: 2328, 2570
2389, 2415, 2421, 2447, 2452, 2491,
2570, 2572, 2595, 2620, 2676, 2697,
2852, 2856, 2884, 2952, 3053, 3092,
')07
2328, 2331,
2393, 2404,
2491, 2502,
2565, 2570,
2673, 2676,
2759, 2773,
2897, 2946,
3016, 3018,
2340, 2343,
2433, 2447,
2503, 2508,
2595, 2597,
2683, 2689,
2811, 2815,
2952, 2958,
3037, 3043,
-------
GADOLINIUM: 2319
GALLIUM: 2319, 2452, 2528, 2534
GERMANIUM: 2319, 2493, 2534, 2570, 2668
GOLD: 2319
HAFNIUM: 2319, 2534
HOLMIUM: 2319
INDIUM: 2319, 2534, 2933
IRIDIUM: 2319
IRON: 2255, 2283, 2284, 2319, 2320, 2321,
2404, 2447, 2452, 2491, 2516, 2528,
2595, 2620, 2647, 2672, 2676, 2694,
2856, 2889, 2952, 2955, 2973, 3004,
LANTHANUM: 2283, 2319, 2534
LEAD: 2267, 2283, 2284, 2296, 2319, 2328, 2343, 2389, 2393, 2404,
2415, 2433, 2447, 2452, 2469, 2473, 2486, 2489, 2516, 2524,
2532, 2534, 2570, 2587, 2595, 2616, 2645, 2647, 2676, 2694,
2697, 2737, 2744, 2749, 2757, 2759, 2806, 2852, 2856, 2866,
2872, 2882, 2992, 3016, 3037, 3053, 3092, 3121, 3122
LITHIUM: 2283, 2319, 2389, 2493, 2570, 2572, 2747, 2917
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2356, 2389, 2452, 2469, 2470, 2491, 2534,
2540, 2570, 2572, 2595, 2676, 2748, 2759, 2812, 2856,
2952, 2956, 3098, 3121
MANGANESE: 2283, 2284, 2319, 2328, 2346, 2365,
2447,2452, 2464,2534,2565,2570,
2645, 2647, 2660, 2676, 2697, 2741,
2798,2837,2856,2927,2952, 3047,
3122
MERCURY: 2269, 2272, 2283, 2319, 2328, 2415, 2447, 2482, 2486,
2487, 2501, 2534, 2570, 2595, 2608, 2619, 2621, 2645,
2670, 2676, 2683, 2694, 2703, 2711, 2744, 2749, 2780,
2784, 2804, 2808, 2815, 2852, 2864, 2868, 2950, 2952,
2973, 3016, 3034, 3037, 3042, 3043, 3048, 3092, 3121
MOLYBDENUM: 2283, 2319, 2452, 2486, 2534, 2570, 2788, 3098
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2284, 2296, 2319, 2328, 2343,
2393, 2447, 2452, 2486, 2491, 2534,
2595, 2647, 2676, 2694, 2697, 2749,
2882, 2952, 2973, 3053, 3079, 3092,
NIOBIUM: 2319, 2421, 2510, 2534, 2979
OSMIUM: 2534
PALLADIUM: 2319, 2534
PLATINUM: 2319, 2534
PLUTONIUM: 2319, 2346, 2570, 2961, 2974, 2979, 3013, 3066, 3094,
3115
POLONIUM: 2319, 2856, 3092
2328, 2346, 2374, 2389,
2543, 2565, 2570, 2590,
2697, 2749, 2759, 2798,
3043, 3098, 3118, 3121
2374, 2389, 2404,
2572, 2595, 2620,
2749, 2756, 2759,
3092, 3098, 3118,
2346, 2374, 2389,
2565, 2570, 2572,
2852, 2856, 2872,
3122
508
-------
POTASSIUM: 2319, 2373, 2389, 2452, 2493, 2540, 2570, 2572, 2595,
2650, 2676, 2747, 2759, 2812, 2828, 2926, 2958, 3102,
3108, 3111
PRASEODYMIUM: 2319
PROMElHIUM: 2319
PROTACTINIUM: 2319, 2979
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319, 2421, 2510, 2605
RUBIDIUM: 2319, 2389, 2565, 2570, 2572, 2898
RUTHENIUM: 2319, 2346, 2421, 2510, 2534, 2605, 2979, 3108
SALINITY: 2283, 2319, 2419, 2420, 2570, 2649, 2650, 2741, 2742,
2806, 2894, 3092, 3109, 3130
2319, 2389
2319, 2328, 2389, 2534, 2570
2283, 2319, 2328, 2486, 2534, 2570, 2586, 2595, 2694,
3075, 3080, 3092
SILICON: 2273, 2302, 2303, 2319, 2340, 2357, 2395, 2435,2436,
2452, 2493, 2534, 2546, 2570, 2595, 2668, 2676, 2681,
2773, 2841, 2856, 2949, 3046, 3092
SILVER: 2283, 2284, 2319, 2328, 2343, 2389, 2447, 2501, 2570,
2595, 2676, 2952, 2973, 3092
SODIUM: 2283, 2319, 2373, 2389, 2452, 2470, 2493, 2534, 2540,
2570, 2572, 2595, 2676, 2747, 2759, 2812, 2828,2894,
2917
STRONTIUM: 2319, 2328,2389, 2452, 2484, 2534, 2587,2595, 2620,
2676, 2749, 2828, 2863, 2956, 3065, 3087, 3092, 3102,
3108, 3111
TANTALUM: 2319, 2389, 2534
TECHNETIUM: 2319, 2346
TELLURIUM: 2319, 2534
TERBIUM: 2319
THALLIUM: 2283, 2319, 2534, 2570, 2595, 2952
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2534, 2570, 2804, 3081
TITANIUM: 2283, 2319, 2452, 2534, 2570, 2595
TUNGSTEN: 2283, 2319, 2534
URANIUM: 2283, 2319, 2534, 2752
VANADIUM: 2283, 2295, 2319, 2409, 2452, 2534, 2570, 2577, 2578,
2586, 2934, 3051
YTTERBIUM: 2319
YTTRIUM: 2319, 2534, 2620, 2800
ZINC: 2261, 2283, 2284, 2296, 2319, 2328, 2343,
2389, 2393, 2404, 2414, 2447, 2452, 2461,
2486, 2491, 2508, 2513, 2516, 2534, 2561,
2572, 2595, 2616, 2620, 2645, 2647, 2648,
SAMARIUM:
SCANDIUM:
SELENIUM :
2350, 2356, 2374,
2469, 2470, 2484,
2565, 2567, 2570,
2660, 2676, 2683,
509
-------
2694, 2697, 2741, 2744, 2749, 2757, 2759, 2800, 2813, 2852,
2856, 2872, 2882, 2952, 2973, 2977, 3018, 3037, 3043, 3053,
3074, 3092, 3098, 3118, 3121, 3122
ZIRCONIUM: 2283, 2319, 2421, 2452, 2510, 2534, 2793, 2856, 2979,
3092
AMPHIBIA
AMERICIUM: 2542
ARSENIC: 2542
BORON: 3078
CADMIUM: 2542, 2679, 3049
CALCIUM: 2542, 2850, 2920
CESIUM: 2542, 3030
CHROMIUM: 2542
COBALT: 2542
COPPER: 2542
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2542, 2623
LANTHANUM: 2319, 2542
LEAD: 2319, 2542, 2679, 2963
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319, 2542, 2679
MANGANESE: 2319, 2542, 2679
MERCURY: 2319, 2542, 2679, 2868
M:>LYBDENUM: 2319, 2542
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2542, 3079
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2542
POLONIUM: 2319
POTASSIUM: 2319, 2542
PRASEODYMIUM: 2319
PROMETHIUM: 2319
5J,0
-------
PROTACTINIUM: 2319
RADIUM: 2319, 2542
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319, 2542, 2874
SAMARIUM: 2319
SCANDIUM: 2319, 2542
SELENIUM: 2319, 2542
SILICON: 2319
SILVER: 2319, 2542
SODIUM: 2319, 2542, 2633,
STRONTIUM: 2319, 2542
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319, 2542
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319, 2542
ZINC: 2319, 2542
ZIRCONIUM: 2319
2796, 2874, 2920
ANNELIDA
ALUMINUM: 2283, 2570, 2595
AMERICIUM: 2743
ANTIMONY: 2283, 2570
ARSENIC: 2283, 2443, 2447,2486,
BARIUM: 3002
BERYLLIUM: 2283, 2570
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570
CAIMIUM: 2250,
2463,
2849,
2556, 2570, 2595, 2645, 2720
2276, 2277, 2283, 2284, 2318,2393, 2447,2456,
2486, 2509, 2521, 2556, 2562, 2570, 2595, 2645,
2859, 2872, 2986
511
-------
CALCIUM: 2276, 2283, 2480, 2570, 2595
CESIUM: 2510, 2570, 2605
CHROMIUM: 2276, 2277, 2283, 2284, 2318, 2406, 2447, 2455, 2456,
2486, 2562, 2570, 2575, 2595, 2801, 2859
COBALT: 2283, 2284, 2447, 2510, 2562, 2570, 2595
COPPER: 2250, 2266, 2276, 2277, 2279, 2283, 2284, 2336, 2393,
2447, 2456, 2463, 2486, 2521, 2556, 2562, 2570, 2595,
2645, 2716, 2801, 2845, 2872, 2991
EUROPIUM: 2570
GAIOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2279,2283, 2284, 2319, 2447, 2562, 2570,2595,2801
LANTHANUM: 2283, 2319
LEAD: 2250, 2283, 2284, 2319, 2393, 2405, 2447, 2456, 2463, 2486,
2521, 2556, 2562, 2570, 2595, 2645, 2716, 2801, 2866, 2872,
2963
LITHIUM: 2283, 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2276, 2283, 2319, 2480, 2570, 2595
MANGANESE: 2283, 2284, 2319, 2447, 2556, 2570, 2595, 2645, 2801
MERCURY: 2276, 2277, 2283, 2318, 2319, 2390, 2391, 2392, 2442,
2447, 2456, 2463, 2486, 2521, 2531, 2556, 2562, 2570,
2595, 2645, 2881, 3076
MOLYBDENUM: 2283, 2319, 2486, 2570
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2276,2277,2283, 2284, 2318, 2319, 2393, 2447, 2463,
2486, 2562, 2570, 2595, 2872, 3079
NIOBIUM: 2319, 2510
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2570, 3013, 3060, 3061
POLONIUM: 2319
POTASSIUM: 2319, 2480, 2562, 2570, 2595, 2778
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319, 2510, 2605
RUBIDIUM: 2319, 2570
51?
-------
RUTHENIUM: 2319, 2510, 2562, 2605
SALINITY: 2283, 2319, 2392, 2480, 2485, 2570, 2740, 2758, 2778,
3077
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2283, 2319, 2486, 2570, 2595
SILICON: 2319, 2570, 2595
SILVER: 2283, 2284, 2319, 2447, 2562, 2570, 2595, 2844
SODIUM: 2283, 2319, 2480, 2485, 2562, 2570, 2595, 2758, 2778
STRONTIUM: 2319, 2595
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570, 2595
THORIUM: 2319, 2570
THUliUM: 2319
TIN: 2283, 2319, 2570, 3081
TITANIUM: 2283, 2319, 2570, 2595
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2570, 3051
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2250, 2276, 2277,2279, 2283, 2284, 2318, 2319, 2393, 2447,
2456, 2463, 2486, 2521, 2556, 2562, 2570, 2595, 2645, 2716,
2801, 2859, 2872
ZIRCONIUM: 2283, 2319, 2510
ARACHNOIDEA
GArOliNIUM: 2319
GALliUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319
LANTHANUM: 2319
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
5D
-------
MANGANESE: 2319
MERCURY: 2319
MJLYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319, 3093
SAMARIUM: 2319
SCANDIUM: 2319
SELENI UM: 2319
SILICON: 2319
SILVER: 2319
SODIUM: 2319
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
Y'ITERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319
ZIRCONItM: 2319
AVES
.514
-------
ALUMINUM: 2283, 2570, 3064
ANTIMONY: 2283, 2570, 2596
ARSENIC: 2283, 2486, 2556, 2570, 2645, 2809, 3063, 3064
BARIUM: 2596, 3064
BERYLLIUM: 2283, 2570, 2596, 3063
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570, 3078
CADMIUM: 2283, 2486, 2556, 2562, 2570, 2645, 2706, 2809, 2810,
2872, 2973, 3018, 3037, 3063, 3064
CALCIUM: 2283, 2570
CERIUM: 2596
CESIUM: 2570, 2596, 3030, 3095
CHROMIUM: 2283, 2486, 2562, 2570, 2973, 3037, 3063, 3064
COBALT: 2283, 2562, 2570, 2596, 3064
COPPER: 2283, 2486, 2556, 2562, 2570, 2592, 2645, 2809, 2812,
2973, 3018, 3037, 3064
EUROPIUM: 2570, 2596
GAOOUNIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
OOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2562, 2570, 2973, 3064
LANTHANUM: 2283 2319
LEAD: 2283, 2308, 2319, 2329, 2486, 2556, 2562, 2570, 2640, 2645,
2809, 2810, 2829, 2872, 3037, 3063, 3064
LITHIUM: 2283, 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2570
MANGANESE: 2283, 2319, 2556, 2570, 2596, 2645, 3064
MERCURY: 2283, 2319, 2486, 2490, 2556, 2562, 2570, 2606, 2612,
2643, 2645, 2761, 2809, 2810, 2868, 2881, 2932, 2973,
3037, 3040, 3063, 3064, 3090
MOLYBDENUM: 2283, 2319, 2486, 2570, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2486, 2562, 2570, 2592, 2872, 2973, 3064,
3079
NIOBIUM: 2319, 2596
PALLADIUM: 2319
PLATINUM: 2319
515
-------
PLUTONIUM: 2319, 2570, 2596, 3013, 3094
POLONIUM: 2319
POTASSIUM: 2319, 2562, 2570, 2596, 2904
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIUM: 2319, 2562, 2596
SALINITY: 2283, 2319, 2570, 2904, 2929
SAMARIUM: 2319
SCANDIUM: 2319, 2570, 2596
SELENIUM: 2283, 2319, 2486, 2570, 2809, 3064, 3080
SILICON: 2319, 2570
SILVER: 2283, 2319, 2562, 2570, 2973, 3064
SODIUM: 2283, 2319, 2562, 2570, 2596, 2904
STRONTIUM: 2319. 2596
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 3064
TITANIUM: 2283, 2319, 2570
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2570, 3064
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2319, 2486, 2556, 2562, 2570, 2592, 2596, 2645, 2809,
2872, 2973, 3018, 3037, 3064
ZIRCONIUM: 2283, 2319, 2596
BACTERIA AND YEAST
ALUMINUM: 2283, 2288, 2349, 2570. 2595, 2728, 2764
ANTIMONY: 2283, 2570, 2764
ARSENIC: 2283, 2486, 2570, 2595, 2728, 2746, 2764, 2795
BARIUM: 2764
BERYLLIUM: 2283, 2570, 2764
BIBLIOGRAPHY: 2562, 2570
51h
-------
BISMUTII: 2570, 2764
BORON: 2570, 3078
CADMIUM: 2283, 2323,
2595, 2677,
CALCIUM: 2283, 2349,
CESIUM: 2570
CHROMIUM: 2283, 2323, 2349, 2415, 2429, 2439, 2486, 2562, 2570,
2595, 2696, 2728, 2801
COBALT: 2283, 2349, 2354, 2415, 2562, 2570, 2595, 2636, 2728,
2764, 2952, 3024
COPPER: 2283, 2349, 2429,
2570, 2595, 2696,
2952, 2989, 2991,
EUROPIUM: 2570
GAIDLINIUM: 2319
GALLIUM: 2319, 2763, 2764
GERMANIUM: 2319, 2570
GOLD: 2319, 2764
HAFNIUM: 2319, 2764
HOLMIUM: 2319
INDIUM: 2319, 2933
IRIDIUM: 2319, 2764
IRON: 2255, 2283, 2319, 2349, 2429, 2439, 2562, 2570, 2595, 2763,
2764, 2801, 2814, 2820, 2952, 3009
LANTHANUM: 2283, 2319, 2677, 2764, 2999
LEAD: 2283, 2319, 2415, 2429, 2439, 2486, 2497, 2562, 2570, 2595,
2636, 2696, 2728, 2737, 2746, 2764, 2801, 2866, 2872, 3024
LITIIIUM: 2283, 2319, 2570, 2652, 2677
LUTETIUM: 2319
MAGNESIUM: 2283, 2319,2349, 2570, 2595, 2677, 2728, 2764, 2785,
2952, 2966, 2999, 3010
MANGANESE: 2283, 2319, 2349, 2439, 2570, 2595, 2801, 2875, 2927,
2952, 2966, 2999
MERCURY: 2283, 2319, 2349, 2354, 2415, 2450,
2559, 2562, 2570, 2595, 2636, 2728,
2780, 2784, 2792, 2795, 2901, 2941,
3024
MOLYBDENUM: 2283, 2319, 2486, 2570, 2636
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2486, 2562, 2570, 2595, 2764, 2872, 2952,
3024, 3079
NIOBIUM: 2319, 2764
OSMIUM: 2764
PALLADIUM: 2319, 2764
PLATINUM: 2319, 2764
PLUTONIUM: 2319, 2570
2415, 2429, 2459, 2486, 2497, 2562, 2570,
2746, 2764, 2817, 2872, 2952, 2980, 3024
2570, 2595, 2677, 2764, 2966, 2970, 2999
2439, 2483, 2486, 2488, 2511, 2562,
2763, 2764, 2765, 2801, 2817, 2872,
3024
2451, 2483, 2486,
2746, 2764, 2765,
2952, 3008, 3015,
S17
-------
POLONIUM: 2319
POTASSIUM: 2319, 2349, 2562, 2570, 2595, 2652, 2677, 2764
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319, 2764
RHODIUM: 2319, 2764
RUBIDIUM: 2319, 2570, 2652, 2764
RUTHENIUM: 2319, 2562, 2764
SALINITY: 2283, 2319, 2488, 2570, 2750, 2894, 3014
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2283, 2319, 2486, 2570, 2595, 2764, 2873, 3080
SILICON: 2319, 2349, 2570, 2595, 2764
SILVER: 2283, 2319, 2562, 2570, 2595, 2762, 2764, 2952
SODIUM: 2283, 2319, 2349, 2562, 2570, 2595, 2652, 2677, 2750,
2764, 2894, 3014
STRONTIUM: 2319, 2595, 2677, 2764, 2999
TANTALUM: 2319, 2764
TECHNETI UM: 2319
TELLURIUM: 2319, 2728, 2764
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570, 2595, 2764, 2952
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 2728, 2764, 3081
TITANIUM: 2283, 2319, 2349, 2570, 2595, 2764
TUNGSTEN: 2283, 2319, 2764, 2873
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2570, 2934
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2319, 2349, 2429, 2439, 2486, 2497, 2562, 2570, 2595,
2696, 2764, 2801, 2872, 2952, 3014, 3024
ZIRCONIUM: 2283, 2319, 2764
BIBLIOORAPHY
ALUMINUM: 2570, 2595, 3064
AMERICIUM: 2542
ANTItvDNY: 2570
ARSENIC: 2542, 2570, 2595, 2876,
BARIUM: 3064
BERYLLIUM: 2570, 3063
3063, 3064, 3092
518
-------
BISMUTH: 2570
BORON: 2570, 3078
CADMIUM: 2542, 2562, 2570, 2595, 2952, 3063, 3064, 3082, 3092
CALCIUM: 2542, 2570, 2595
CESIUM: 2542, 2570
CHROMIUM: 2542, 2562, 2570, 2595, 3063, 3064, 3092
COBALT: 2542, 2562, 2570, 2595, 2952, 3064, 3092
COPPER: 2542, 2562, 2570, 2595, 2952, 2990, 2991, 3064, 3092
EUROPIUM: 2570
GAroLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319, 2933
IRIDIUM: 2319
IRON: 2319, 2542, 2562, 2570, 2595, 2952, 3064
LANTHANUM: 2319, 2542
LEAD: 2319, 2542, 2562, 2570, 2595, 2866, 3063, 3064, 3092
LITHIUM: 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2319, 2542, 2570, 2595, 2952
MANGANESE: 2319, 2542, 2570, 2595, 2952, 3064, 3092
MERCURY: 2319, 2542, 2562, 2570, 2595, 2868, 2952, 3063, 3064,
3092, 3126
MOLYBDENUM: 2319, 2542, 2570, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2542, 2562, 2570, 2595, 2952, 3064, 3079, 3092
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2542, 2570
POLONIUM: 2319, 3092
POTASSIUM: 2319, 2542, 2562, 2570, 2595
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319, 2542
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIUM: 2319, 2562
SALINITY: 2319, 2542, 2570, 3092
SAMARIUM: 2319
SCANDIUM: 2319, 2542, 2570
519
-------
SELENIUM: 2319, 2542, 2570, 2595, 3064, 3080, 3092
SILICON: 2319, 2570, 2595, 3092
SILVER: 2319, 2542, 2562, 2570, 2595, 2952, 3064, 3092
SODIUM: 2319, 2542, 2562, 2570, 2595
STRONTIUM: 2319, 2542, 2595, 3092
TANTALUM: 2319
TECHNETIUM: 2319
TELL URI ill'1 : 2319
TERBIUM: 2319
THALLIUM: 2319, 2570, 2595, 2952
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2319, 2570, 3064, 3081
TITANIUM: 2319, 2570, 2595
TUNGSTEN: 2319
URANIUM: 2319, 2542
VANADIUM: 2319, 2570, 2934, 3064
YTTERBIUM: 2319
YTTRIUM: 2319, 2542
ZINC: 2319, 2542, 2562, 2570, 2595, 2952, 3064, 3092
ZIRCONIUM: 2319, 3092
BRACHIOPODA
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319
LANTHANUM: 2319
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319
MERCURY: 2319
M)LYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319
NIOBIUM: 2319
520
-------
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIlli: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319
SODIUM: 2319
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBHM: 2319
THALLIUM: 2319
THORIlM: 2319
THUUUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTIERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319
ZIRCONItM: 2319
BRYAZOA
GAroUNIUM: 2319
GALUUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
521
-------
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319
LANTHANUM: 2319
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESI UM: 2319
MANGANESE: 2319
MERCURY: 2319, 3076
M)LYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNI liM: 2319
NICKEL: 2319
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319
SAMARIlM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319
SODIUM: 2319
STRONTIUM: 2319 '
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIlM: 2319
THALLIUM: 2319
THORIlM: 2319
THUUUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
522
-------
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YITRI lM: 2319
ZINC: 2319
ZIRCONItM: 2319
BRYOPHYTA
ALUMINUM: 2570
ANTIMONY: 2570
ARSENIC: 2570, 2655
BERYLLIUM: 2570
BIBLIOGRAPHY: 2570
BISMUTH: 2570
BORON: 2570
CArnIUM: 2404, 2570, 2655, 2954
CALCIUM: 2570, 2954
CESIUM: 2570
CHRCMIUM: 2570, 2954
caBAL T : 2570, 2997
caPPER: 2404, 2570, 2954
EUROPIUM: 2570
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDHM: 2319
IRIDIUM: 2319
IRON: 2319, 2404, 2570, 2954
LANTIIANlM: 2319
LEAD: 2319, 2404, 2570, 2655, 2954
LITHIUM: 2319, 2570
LUTETIUM: 2319
MAGNESIlM: 2319, 2570, 2954
MANGANESE: 2319, 2404, 2570, 2954
MERCURY: 2319, 2570, 2851, 2881, 2954
MJLYBDENUM: 2319, 2570
NEODYMIlM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2570, 2997
NIOBIUM: 2319
PALLADItM: 2319
523
-------
PLATINUM: 2319
PLUTONIUM: 2319, 2570
POLONIUM: 2319
POTASSIUM: 2319, 2570
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIUM: 2319
SALINITY: 2319, 2570
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2319, 2570, 2851
SILICON: 2319, 2570
SILVER: 2319, 2570
SODIUM: 2319, 2570
STRONTI LM: 2319
TANTALUM: 2319
TECHNETIlli: 2319
TELLURIUM: 2319
TERBILM: 2319
THALLIUM: 2319, 2570
THORIUM: 2319, 2570
THUliUM: 2319
TIN: 2319, 2570, 3081
TITANIUM: 2319, 2570
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319, 2570
YTTERBIUM: 2319
YTTRILM: 2319
ZINC: 2319, 2404, 2570, 2954
ZIRCONIUM: 2319
CHAETOGNA THA
ALUMINUM: 2604
ANTIMJNY: 2328
ARSENIC: 2604
CADMIUM: 2328, 2604
CERIUM: 2328
CESIUM: 2328
524
-------
CHROMIUM: 2328, 2604
COBALT: 2328, 2604
COPPER: 2328, 2336, 2604
EUROPIUM: 2328
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANILM: 2319
GOLD: 2319
HAFNHM: 2319
HOLMIUM: 2319
INDILM: 2319
IRIDIUM: 2319
IRON: 2319, 2328, 2372, 2604
LANTHANUM: 2319
LEAD: 2319, 2328, 2604
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319, 2328, 2604
MERCURY: 2319, 2328, 2604
M)LYBDENUM: 2319
NEODYMIlM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2328, 2604
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHILM: 2319
PROTACTINIUM: 2319
RADHM: 2319
RHENIUM: 2319
RHODILM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319
SAMARILM: 2319
SCANDIUM: 2319, 2328
SELENILM: 2319, 2328
SILICON: 2319
SILVER: 2319, 2328
SODIUM: 2319
STRONTIUM: 2319, 2328
TANTALUM: 2319
525
-------
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THU1I UM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIU1: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2328, 2604
ZIRCONIUM: 2319
COELENTERATA
ALUMINUM: 2283, 2570, 2604, 2721
AMERICIUM: 2974
ANTIMONY: 2283, 2570
ARSENIC: 2283, 2570, 2604
BARIUM: 3002, 3114
BERYLLIUM: 2283, 2570
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570
CADMIUM: 2283, 2389, 2562, 2570, 2580, 2604
CALCIUM: 2259, 2283, 2304, 2389, 2570, 2721, 2822, 2891, 3059,
3114
CESIU1: 2570
CHROMIUM: 2283, 2389, 2562, 2570, 2604
COBALT: 2283, 2389, 2562, 2570, 2604
COPPER: 2283, 2336, 2389, 2562, 2570, 2580, 2604
EUROPIUM: 2570
GADOLINIUM: 2319
GALLIU1: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
OOLMIlli: 2319
INDIUM: 2319
IRIDIlli: 2319
IRON: 2283, 2319, 2389, 2562, 2570, 2604, 2721, 2891
LANTHANUM: 2283, 2319
526
-------
LEAD: 2283, 2319, 2389, 2562, 2570, 2604
LITHIUM: 2283, 2319, 2389, 2570
LU1ETIUM: 2319
MAGNESIUM: 2283, 2319, 2389, 2570, 2721, 3114
MANGANESE: 2283, 2319, 2389, 2570, 2604, 2891, 3114
MERCURY: 2283, 2319, 2562, 2570, 2580, 2604
MOLYBDENUM: 2283, 2319, 2570, 2891
NEODYMIUM: 2319
NEPTUNI 11-1: 2319
NICKEL: 2283, 2319, 2389, 2562, 2570, 2604
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2570, 2974
POLONIUM: 2319
POTASSIUM: 2319, 2389, 2562, 2570, 2847
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389, 2570
RUTHENIUM: 2319, 2562
SALINITY: 2283, 2319, 2570
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2389, 2570
SELENIUM: 2283, 2319, 2570
SILICON: 2319, 2570
SILVER: 2283, 2319, 2389, 2562, 2570
SODIUM: 2283, 2319, 2389, 2562, 2570, 2847
STRONTIUM: 2319, 2389, 2721, 2822, 3059, 3114
TANTALUM: 2319, 2389
TECHNETI UM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 3081
TITANIUM: 2283, 2319, 2570
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2570
YTTERBIUM: 2319
YTIRIUM: 2319
ZINC: 2259, 2283, 2319, 2389, 2562, 2570, 2604, 3114
527
-------
2283, 2288, 2570, 2591, 2595, 2604, 2730, 2886, 3064
2542, 2743, 2961, 2979
2283, 2328, 2530, 2534, 2570
2283, 2441, 2447, 2486, 2530, 2534, 2542, 2543, 2570,
2591, 2595, 2604, 2632, 2646, 2656, 2720, 2730, 2843,
2870, 2876, 3063, 3064
BARIUM: 2534, 2553, 2591, 2730, 3002, 3064
BERYLLIUM: 2283, 2534, 2570, 2591, 3063
BIBLIOGRAPHY: 2562, 2570, 2632
BISMUTH: 2534, 2570
BORON: 2570, 2591
CADMIUM: 2250, 2283, 2292,
2337, 2339, 2343,
2486, 2504, 2513,
2534, 2542, 2562,
2604, 2608, 2610,
2669, 2680, 2698,
2799,2857, 2872,
3004, 3018, 3037,
CALCIUM: 2265, 2283, 2317,
2525, 2526, 2527,
2595, 2610, 2626,
3028, 3059, 3072
CERIUM: 2328, 2979
. CESIUM: 2328, 2542, 2565, 2570, 2632, 2979, 3050
CHROMIUM: 2283, 2317, 2318, 2328, 2343, 2389, 2429,
2486, 2530, 2534, 2542, 2562, 2570, 2591,
2632, 2646, 2647, 2662, 2730, 2899, 2973,
3064
COBALT: 2283, 2328, 2389,
2570, 2591, 2595,
COPPER: 2250, 2252, 2266,
2336, 2343, 2358,
2454, 2460, 2486,
2536, 2542, 2543,
2604, 2610, 2614,
2662, 2698, 2716,
2886, 2973, 2991,
3068, 3096
EUROPIUM: 2328, 2570
GAOOLINIUM: 2319
ZIRCONIUM: 2283, 2319
CRUSTACEA
AL UMINUM:
AMERICIUM:
ANTI MJNY :
ARSENI C :
2306, 2311, 2317,
2363, 2389, 2427,
2514, 2521, 2525,
2564, 2570, 2582,
2624, 2632, 2646,
2709, 2730, 2739,
2878, 2886, 2887,
3063, 3064, 3068,
2388, 2389, 2416,
2534, 2536, 2542,
2730, 2774, 2835,
2318, 2326, 2328,
2429, 2441, 2447,
2526, 2527, 2530,
2591, 2595, 2602,
2647, 2656, 2661,
2755, 2757, 2769,
2896, 2973, 2993,
3072, 3096
2457, 2481, 2515,
2553, 2570, 2591,
2886, 2891, 2942,
2441, 2447,
2595, 2604,
3037, 3063,
2447, 2530, 2534, 2542, 2562, 2565,
2604, 2610, 2730, 2884, 2886, 3064
2278, 2279, 2283, 2317, 2326, 2328,
2380, 2389, 2429, 2441, 2447, 2453,
2502, 2515, 2521, 2526, 2530, 2534,
2562, 2565, 2570, 2581, 2591, 2595,
2615, 2632, 2646, 2647, 2656, 2661,
2730, 2757, 2774, 2811, 2872, 2880,
2993, 3017, 3018, 3037, 3044, 3064,
128
-------
GALLIUM: 2319, 2534
GERMANIUM: 2319, 2534, 2570
GOLD: 2319
HAFNIUM: 2319, 2534
HOLMIUM: 2319
INDIUM: 2319, 2534
IRIDIUM: 2319
IRON: 2279,2283, 2317, 2319, 2326,
2447, 2515, 2530, 2542, 2543,
2604, 2610, 2614, 2647, 2730,
LANTHANUM: 2283, 2319, 2534, 2542
LEAD: 2250, 2278, 2283, 2317, 2319,
2447, 2486, 2521, 2534, 2538,
2604, 2610, 2624, 2632, 2646,
2730, 2737, 2739, 2754, 2757,
3017, 3037, 3063, 3064
LITHIUM: 2283, 2319, 2389, 2570
LUTETIUM: 2319
MAGNESIUM: 2265, 2283, 2317, 2319, 2389, 2457, 2481, 2515, 2525,
2534, 2536, 2542, 2570, 2591, 2595, 2610, 2730, 2824,
2835, 2886
MANGANESE: 2283, 2317,2319,2326,
2526, 2530, 2534, 2542,
2604, 2610, 2632, 2646,
2891, 2993, 3052, 3064
MERCURY: 2283, 2292, 2318, 2319, 2328, 2377, 2390, 2391, 2392,
2437, 2447, 2454, 2486, 2487, 2501, 2504, 2517, 2521,
2530, 2531, 2534, 2542, 2562, 2563, 2570, 2591, 2595,
2604, 2608, 2611, 2621, 2632, 2635, 2642, 2646, 2654,
2656, 2662, 2670, 2680, 2703, 2730, 2768, 2780, 2791,
2868, 2871, 2881, 2886, 2887, 2950, 2951, 2959, 2971,
2973, 2994, 3003, 3037, 3063, 3064, 3068, 3072, 3076,
3096, 3097, 3100
MOLYBDENUM: 2247, 2283, 2319, 2441, 2486,2534, 2542, 2570, 2591,
2891, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319, 3035
NICKEL: 2283, 2317, 2318,2319,
2447, 2486, 2534, 2542,
2604,2610,2632, 2647,
3064, 3079 .
NIOBIUM: 2319, 2534, 2979
OSMIUM: 2534
PALLADIUM: 2319, 2534
PLATINUM: 2319, 2534, 2730
PLUTONIUM: 2319, 2542, 2570, 2632, 2832, 2961, 2979, 3013, 3060,
3061, 3066
2328, 2372, 2388, 2389, 2429,
2562, 2565, 2570, 2591, 2595,
2886, 2891, 2973, 3004, 3064
2328, 2343,
2542, 2562,
2647, 2656,
2866, 2872,
2389, 2429, 2441,
2570, 2591, 2595,
2661, 2662, 2716,
2885, 2887, 2948,
2328, 2388, 2389, 2447, 2460,
2553, 2565, 2570, 2591, 2595,
2647, 2730, 2774, 2837, 2886,
2326, 2328, 2343, 2389, 2441,
2562, 2565, 2570, 2591, 2595,
2730, 2872, 2886, 2973, 2993,
529
-------
POLONIUM: 2319, 2538
POTASSIUM: 2265, 2317, 2319, 2389, 2457,2481, 2542, 2553, 2562,
2570, 2595, 2730, 2774, 2824, 2861, 2886
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319, 2979
RADIUM: 2319, 2542
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389, 2565, 2570, 2898
RUTHENIUM: 2319, 2534, 2562, 2979
SALINITY: 2265, 2283, 2319, 2385, 2392,
2526, 2527, 2542, 2569, 2570,
2740, 2755, 2766, 2767, 2769,
2861, 2870, 2878, 2886, 2899,
2988, 3011, 3039, 3072
2319, 2389
2319, 2328, 2388, 2389, 2530,
2283, 2319, 2328, 2486, 2530,
2632, 2730, 2739, 3064, 3080,
SILICON: 2319, 2534, 2570, 2595
SILVER: 2283, 2292, 2319, 2326, 2328, 2343, 2389, 2441, 2447,
2501, 2542, 2562, 2570, 2591, 2595, 2632, 2646, 2973,
3064, 3096
SODIUM: 2265, 2283, 2317,2319, 2389, 2457, 2481, 2534, 2542,
2553, 2562, 2570, 2591, 2595, 2626, 2730, 2766, 2767,
2774, 2824, 2900, 2942, 2945, 3100
STRONTIUM: 2317, 2319, 2326, 2328, 2388, 2389, 2534, 2542, 2553,
2595, 2632, 2730, 3059
TANTALUM: 2319, 2389, 2534
TECHNETIUM: 2319
TELLURIUM: 2319, 2534
TERBIUM: 2319
THALLIUM: 2283, 2319, 2534, 2570, 2595
THORIUM: 2319, 2570, 3050
THUUUM: 2319
TIN: 2283, 2319, 2534, 2570, 2591, 2730, 3064
TITANIUM: 2283, 2319, 2326, 2534, 2570, 2591, 2595
TUNGSTEN: 2283, 2319, 2534
URANIUM: 2283, 2319, 2534, 2542, 3050
VANADIUM: 2283, 2317,2319,2534,2570, 2591, 3051, 3064
YTTERBIUM: 2319
YTTRIUM: 2319, 2534, 2542
ZINC: 2250, 2261, 2279, 2283,
2343, 2388, 2389, 2429,
2534, 2542, 2562, 2565,
2632, 2646, 2647, 2656,
SAMARIU1:
SCANDIUM:
SELENI UM:
2417, 2514,
2602, 2637,
2772, 2824,
2900, 2942,
2517, 2525,
2667, 2709,
2827, 2857,
2945, 2947,
2534, 2542, 2570
2534, 2542, 2570, 2595,
3097
2306,2317,2318,2319,
2447, 2486, 2513, 2515,
2570, 2591, 2595, 2604,
2661, 2684, 2698, 2716,
530
2326, 2328,
2521, 2530,
2610,2615,
2730, 2739,
-------
2757, 2774, 2872, 2886, 2887, 2973, 2993, 3012, 3018, 3037,
3064
ZIRCONIUM: 2283, 2319, 2534, 2979
CTENOPHORA
ALUMINUM: 2604
ARSENIC: 2604
CADMIUM: 2343, 2604
CHROMIUM: 2343, 2604
COBALT: 2604
COPPER: 2336, 2343, 2358,
GAOOLINIU1: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2604
LANTHANUM: 23 19
LEAD: 2319, 2343, 2604
UTHIUM: 2319
LUTETItM: 2319
MAGNESIUM: 2319
MANGANESE: 2319, 2604
MERCURY: 2319, 2604
MOLYBDENU1: 2319
NEODYMIUM: 2319
NEPTUNIU1: 2319
NICKEL: 2319, 2343, 2604
NIOBIUM: 2319
PALLADIUM: 2319
PLATINU1: 2319
PLUTONIUM: 2319
POLONIU1: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENILM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
2453, 2604
531
-------
RUTHENIUM: 2319
SALINITY: 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319, 2343
SODIUM: 2319
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2343, 2604
ZIRCONIUM: 2319
DETRITUS
ALUMINUM: 2283
ANTIMONY: 2283, 2328
ARSENIC: 2283
BERYLLIUM: 2283
CADMIUM: 2283, 2328
CALCIUM: 2283, 3102
CERIUM: 2328
CESIUM: 2328, 3102
CHROMIUM: 2283, 2328
COBALT: 2283, 2328, 2571
COPPER: 2283, 2328, 2508, 2990
EUROPIUM: 2328
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
532
-------
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2328
LANTHANUM: 2283, 2319
LEAD: 2283, 2319, 2328
LITHIUM: 2283, 2319
LUTETIUM: 2319
MAGNE3IlM: 2283, 2319
MANGANESE: 2283, 2319, 2328
MERCURY: 2283, 2319, 2328
M)LYBDENUM: 2283, 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2328
NIOBIUM: 2319
PALLADIlM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319, 3102
PRASEODYMIUM: 2319
PROMETHIlM: 2319
PROTACTINIUM: 2319
RADIlM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIlM: 2319
SALINITY: 2283, 2319
SAMARHM: 2319
SCANDIUM: 2319, 2328
SELENIlM: 2283, 2319, 2328
Sll,I CON: 2319
Sll,VER: 2283, 2319, 2328, 2571
SODIUM: 2283, 2319
STRONTIUM: 2319, 2328, 3102
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIU1: 2319
TERBIUM: 2319
THALLIlM: 2283, 2319
THORIUM: 2319
THULILM: 2319
TIN: 2283, 2319
TITANILM: 2283, 2319
533
-------
TUNGSTEN: 2283, 2319
URANIU1: 2283, 2319
VANADIUM: 2283, 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2319, 2328,
ZIRCONIUM: 2283, 2319
2508, 2571
ECHINODERMATA
ALUMINUM: 2283, 2570, 2595, 3064
AMERICIUM: 2542, 2974
ANTIMJNY: 2283, 2570, 2707
ARSENIC: 2283, 2542, 2543, 2570, 2595, 2843, 2876, 3064
BARIUM: 3002, 3064
BERYLLIUM: 2283, 2570
BIBLIOGRAPHY: 2570
BISMUTH: 2570
BORON: 2570
CADMIUM: 2283, 2318, 2379, 2389, 2513, 2542, 2570, 2579, 2595,
3064
CALCIUM: 2283, 2332, 2389, 2457, 2475, 2481, 2542, 2570, 2595,
2707, 2751, 2891, 2914, 3117
CESIUM: 2542, 2570
CHROMIUM: 2283, 2318, 2332, 2389, 2542, 2570, 2579, 2595, 3064
COBALT: 2283, 2389, 2542, 2570, 2595, 3064
COPPER: 2266, 2283, 2332, 2336, 2379, 2389, 2475, 2507, 2542,
2543, 2570, 2579, 2595, 2991, 3064
EUROPIUM: 2570
GAroLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
OOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2389, 2542, 2543, 2570, 2595, 2891, 3064
LANTHANUM: 2283, 2319, 2542
LEAD: 2283, 2319, 2389, 2475, 2542, 2570, 2579, 2595, 3064
LITHIUM: 2283, 2319, 2389, 2570
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2389, 2457, 2475, 2481, 2542, 2570, 2595,
2914
534
-------
MANGANESE: 2283, 2319, 2389, 2542, 2570, 2595, 2891, 3064
MERCURY: 2283, 2318, 2319, 2542, 2570, 2595, 2642, 3064
MOLYBDENUM: 2247, 2283, 2319, 2542, 2570, 2891, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2318, 2319, 2379, 2389, 2475, 2507, 2542, 2570,
2579, 2595, 3064, 3079
NIOBIUM: 2319
PALLADIUM: 2319
PLATINtJ1: 2319
PLl~ONIUM: 2319, 2542, 2570, 2974, 3013
POLONI UM: 2319
POTASSIUM: 2319, 2389, 2457, 2475, 2481, 2542, 2570, 2595, 2914
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINItJ1: 2319
RADIUM: 2319, 2542
RHENHM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389, 2570
RUTHENIUM: 2319
SALINITY: 2283, 2319, 2542, 2570, 2914, 3000
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2389, 2542, 2570
SELENIUM: 2283, 2319, 2542, 2570, 2595, 3064
SILICON: 2319, 2570, 2595
SILVER: 2283, 2319, 2389, 2542, 2570, 2595, 3064
SODIUM: 2283, 2319, 2389, 2457, 2475, 2481, 2542, 2570, 2595,
2914
STRONTIUM: 2319, 2389, 2542, 2595
TANTALUM: 2319, 2389
TECHNE1'I UM: 2319
TEli..URIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570, 2595
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 3064, 3081
TITANIUM: 2283, 2319, 2570, 2595
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319, 2542
VANADIUM: 2283, 2319, 2570, 2934, 3064
YTTERBIUM: 2319
YTTRIUM: 2319, 2542
ZINC: 2283, 2318, 2319, 2332, 2379, 2389, 2475, 2507, 2513, 2542,
2570, 2579, 2595, 3064
ZIRCONIUM: 2283, 2319
535
-------
ELASMOBRANCHII
ALUMINUM: 2283, 3064
ANTIMONY: 2283
ARSENIC: 2283, 2441, 2443, 3064
BARIUM: 3064
BERYLLIUM: 2283
CADMIUM: 2283, 2345, 2389, 2441, 2887, 2986, 3064
CALCIUM: 2283, 2389, 2481, 3104
CESIUM: 2360
CHROMIUM: 2283, 2345, 2389, 2441, 3064
COBALT: 2283, 2389, 3064
COPPER: 2283, 2345, 2389, 2441, 3064
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2389, 3064
LANTHANUM: 2283, 2319
LEAD: 2283, 2319, 2345, 2389, 2441, 2887, 3064
LITHIUM: 2283, 2319, 2389
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2389, 2481, 3104
MANGANESE: 2283, 2319, 2345, 2389, 3064
MERCURY: 2264, 2283, 2319, 2345, 2410, 2442, 2722, 2887, 3064
MOLYBDENUM: 2283, 2319, 2441, 3064
NEODYMIUM: 2319
NEPTUNIlM: 2319
NICKEL: 2283, 2319, 2345, 2389, 2441, 3064
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 3061
POLONIUM: 2319
POTASSIUM: 2319, 2389, 2481, 3104
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
536
-------
RHODIUM: 2319
RUBIDIUM: 2319, 2389
RUTHENIUM: 2319
SALINITY: 2283, 2319
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2389
SELENIUM: 2283, 2319, 3064
SIUCON: 2319
SILVER: 2283, 2319, 2345, 2389, 2441, 2844, 3064
SODIUM: 2283, 2319, 2389, 2481, 3104
STRONTIUM: 2319, 2389
TANTALUM: 2319, 2389
TECHNETIUM: 2319
TELLURIlM: 2319
TERBIUM: 2319
THALUUM: 2283, 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2283, 2319, 3064
TITANIUM: 2283, 2319
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 3064
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2319, 2345, 2389, 2887, 3064
ZIRCONIUM: 2283, 2319
FISH
ALUMINUM: 2281, 2283, 2288, 2570, 2595, 2604, 2730, 3064
AMERICIUM: 2542, 2588, 2916, 2961, 2974, 2979, 2987
ANTIMONY: 2281, 2283, 2534, 2541, 2570, 2588, 2830, 2969
ARSENIC: 2263, 2281, 2283, 2351, 2441, 2443, 2447, 2466, 2486,
2512, 2534, 2541, 2542, 2543, 2555, 2556, 2570, 2588,
2595, 2604, 2632, 2645, 2646, 2656, 2657, 2730, 2770,
2830, 2843, 2876, 2907, 2940, 2969, 3063, 3064, 3073
BARIUM: 2440, 2534, 2541, 2587, 2588, 2730, 3064
BERYLLIUM: 2283, 2534, 2570, 3063
BIBLIOGRAPHY: 2562, 2570, 2588, 2632
BISMUTH: 2281, 2534, 2570, 2588
BORON: 2570, 3078
CADMIUM: 2253, 2254, 2263,
2306, 2309, 2312,
2342, 2343, 2344,
2280, 2281, 2282, 2283, 2290, 2292,
2317, 2318, 2322, 2337, 2338, 2341,
2345, 2351, 2362, 2382, 2383, 2389,
537
-------
2393, 2394, 2402, 2403, 2408, 2412, 2413, 2425, 2428,
2429, 2438, 2441, 2447, 2459, 2477, 2486, 2498, 2505,
2512, 2519, 2521, 2534, 2541, 2542, 2549, 2550, 2551,
2555, 2556, 2558, 2562, 2570, 2584, 2588, 2594, 2595,
2604, 2608, 2610, 2624, 2627, 2628, 2632, 2645, 2646,
2647, 2651, 2656, 2678, 2686, 2688, 2699, 2700, 2715,
2730, 2739, 2757, 2769, 2770, 2779, 2830, 2867, 2872,
2882, 2887, 2896, 2910, 2924, 2936, 2965, 2969, 2972,
2973, 2982, 2984, 2985, 2986, 2996, 3006, 3022, 3023,
3036, 3037, 3063, 3064, 3073, 3084, 3096,3101, 3110,
3112, 3131
CALCIUM: 2249, 2258, 2281,
2430, 2440, 2471,
2552, 2568, 2570,
2718, 2730, 2776,
2985, 2996, 3026,
3119, 3 127, 3132
CERIUM: 2588, 2969, 2979
CESIUM: 2256, 2360, 2370, 2440, 2542, 2565, 2570, 2588, 2632,
2723, 2786, 2819, 2935, 2979, 3020, 3030, 3088, 3103
CHROMIUM: 2253, 2283, 2287, 2314, 2317, 2318, 2338, 2343, 2345,
2351, 2389, 2403, 2407, 2408, 2429, 2441, 2447, 2477,
2486, 2534, 2541, 2542, 2551, 2562, 2570, 2575, 2588,
2595, 2604, 2632, 2646, 2647, 2715, 2730, 2801, 2882,
2969, 2973, 2985, 2996, 3037, 3063, 3064
COBALT: 2283, 2370, 2389, 2447, 2534, 2542, 2551, 2562, 2565,
2568, 2570, 2588, 2595, 2604, 2610, 2651, 2730, 2731,
2830, 2884, 2969, 2985, 2996, 2997, 3064
COPPER: 2258, 2263, 2271, 2280, 2281, 2282, 2283, 2293, 2317,
2336, 2338, 2343, 2345, 2351, 2362, 2364, 2380, 2387,
2389,2393, 2403, 2407,2408,2418,2429,2441, 2447,
2448, 2477, 2486, 2488, 2512, 2521, 2534, 2535, 2536,
2541, 2542, 2543, 2545, 2547, 2551, 2552, 2555, 2556,
2562, 2565, 2570, 2574, 2584, 2588, 2595, 2604, 2610,
2631, 2632, 2634, 2645, 2646, 2647, 2656, 2665, 2678,
2686, 2718, 2730, 2753, 2757, 2770, 2787, 2801, 2830,
2855, 2872, 2882, 2897, 2906, 2910, 2931, 2960, 2969,
2972, 2973, 2985, 2989, 2991, 2996, 3005, 3007, 3022,
3023, 3037, 3058, 3064, 3073, 3096, 3105, 3112, 3123,
3128, 3129, 3132
CURIUM: 2588, 2916
DYSPROSIUM: 2969
ERBIUM: 2969
EUROPIUM: 2570, 2588, 2969
GAOOLINIUM: 2319, 2969
GALLIUM: 2319, 2534, 2969
GERMANIUM: 2319, 2534, 2570
2283, 2317,2382,
2481, 2512, 2534,
2583, 2585, 2587,
2787, 2790, 2855,
3057, 3071, 3086,
2383, 2388, 2389,
2536, 2542, 2551,
2588, 2595, 2610,
2902, 2965, 2976,
3103, 3104, 3113,
538
-------
GOLD: 2319, 2588
HAFNIUM: 2319, 2534, 2969
HOLMIUM: 2319, 2969
INDIUM: 2319, 2534
IRIDIUM: 2319
IRON: 2258, 2281, 2283,
2447, 2512, 2541,
2588, 2595, 2604,
2903, 2910, 2918,
3119
LANTHANUM: 2283, 2319, 2534, 2542, 2588, 2969
LEAD: 2254, 2258, 2263, 2281, 2282, 2283, 2317, 2319, 2322, 2343,
2345, 2351, 2361, 2362, 2389, 2393, 2403, 2405, 2411, 2429,
2440, 2441, 2447, 2477, 2486, 2512, 2519, 2521, 2534, 2541,
2542, 2549, 2555, 2556, 2562, 2570, 2584, 2587, 2588, 2593,
2594, 2595, 2599, 2601, 2604, 2610, 2624, 2632, 2645, 2646,
2647, 2656, 2675, 2699, 2700, 2730, 2737, 2739, 2754, 2757,
2770, 2801, 2855, 2866, 2867, 2872, 2882, 2887, 2903, 2922,
2923, 2936, 2960, 2972, 2978, 2996, 3037, 3063, 3064, 3127
LITHIUM: 2283, 2319, 2389, 2570, 2723
LUTETIUM: 2319, 2969
MAGNESIUM: 2281, 2283, 2317, 2319, 2341,
2534, 2536, 2542, 2551, 2552,
2610, 2718, 2730, 2738, 2855,
3026, 3057, 3104, 3113
MANGANESE: 2281, 2283, 2317,2319, 2345,
2534, 2541, 2542, 2547, 2551,
2588, 2595, 2604, 2610, 2632,
2730, 2731, 2801, 2837, 2910,
3064, 3105, 3132
MERCURY: 2248, 2263, 2264, 2270, 2274, 2281, 2282, 2283, 2292,
2309, 2310, 2318, 2319, 2335, 2345, 2351, 2352, 2353,
2362, 2376, 2381, 2386, 2400, 2403, 2410, 2428, 2432,
2447, 2450, 2471, 2472, 2474, 2486, 2487, 2496, 2499,
2500, 2501, 2512, 2518, 2519, 2521, 2531, 2534, 2541,
2542, 2544, 2551, 2554, 2555, 2556, 2559, 2560, 2562,
2563, 2566, 2570, 2584, 2588, 2594, 2595, 2604, 2606,
2608, 2619, 2622, 2628, 2632, 2635, 2642, 2645, 2646,
2654, 2656,2659,2665, 2682, 2687,2690, 2691, 2713,
2724, 2727, 2729, 2730, 2761, 2780, 2791, 2794, 2805,
2830, 2833, 2851, 2855,2867, 2868, 2871, 2881, 2887,
2908, 2909, 2910, 2921, 2932, 2943, 2950, 2951, 2953,
2959, 2960, 2969, 2971, 2973, 2983, 2985, 2994, 3003,
3031, 3033, 3036, 3037, 3040, 3041, 3062, 3063, 3064,
3069, 3073, 3076, 3089, 3096, 3126
MOLYBDENUM: 2283, 2319, 2441, 2486, 2534, 2541, 2542, 2570, 2588,
3064
2317,2319,
2542, 2543,
2610, 2647,
2928, 2969,
2338, 2388,
2547, 2551,
2678, 2730,
2973, 2985,
2389, 2408, 2429,
2562, 2565, 2570,
2801, 2818, 2830,
2996, 3058, 3064,
2389, 2471, 2481, 2512,
2570, 2583, 2585, 2595,
2912, 2965, 2985, 2996,
2388, 2389,
2555, 2556,
2645, 2646,
2927, 2969,
2408, 2447,
2565, 2570,
2647, 2678,
2985, 2996,
539
-------
NEODYMI UM: 2319, 2969
NEPTUNIUM: 2319, 2588
NICKEL: 2281, 2283, 2317,2318,2319,2343,
2393, 2403, 2408, 2441, 2447, 2486,
2541, 2542, 2551, 2562, 2565, 2570,
2632, 2647, 2730, 2872, 2882, 2973,
3064, 3079
NIOBIUM: 2319, 2534, 2588, 2979
OSMI UM : 2534
PALLADIUM: 2319, 2534
PLATINUM: 2319, 2534, 2730
PLUTONIUM: 2319, 2542, 2570, 2588, 2632, 2832, 2916, 2961, 2974,
2979, 2987, 3013, 3032, 3060, 3061, 3066, 3094, 3124
POLONIUM: 2319, 2588, 3045
POTASSIUM: 2249,2274, 2281, 2317,2319, 2389, 2440,
2542, 2562, 2570, 2583, 2588, 2595, 2600,
2738, 2782, 2819, 2842, 2855, 2883, 2902,
2985, 2996, 3020, 3026, 3071, 3086, 3088,
3132
PRASEODYMIUM: 2319, 2588
PROMETHIUM: 2319
PROTACTINIUM: 2319, 2588, 2979
RADIUM: 2319, 2542, 2588
RHENIUM: 2319
RHODIUM: 2319, 2588
RUBIDIUM: 2319, 2389, 2440, 2565, 2570, 2588, 2723, 2830
RUTHENIUM: 2319, 2534, 2562, 2588, 2979
SALINITY: 2249, 2283, 2299, 2319, 2324, 2387, 2396,
2430, 2488, 2495, 2542, 2570, 2583, 2598,
2653, 2686, 2702, 2717, 2719, 2735, 2740,
2781, 2782, 2840, 2854, 2858, 2869, 2883,
2925, 3006, 3071, 3107
2319, 2389, 2969
2319, 2388, 2389, 2534, 2542, 2570, 2588, 2969
2263, 2283, 2319, 2376, 2474, 2486, 2534, 2541, 2542,
2554, 2566, 2570, 2595, 2632, 2638, 2687, 2730, 2739,
2830, 2851, 2969, 3064, 3069, 3073, 3080
SILICON: 2319, 2534, 2570, 2595
SILVER: 2283, 2292, 2319, 2342, 2343, 2345, 2351, 2389, 2441,
2447, 2501, 2506, 2541, 2542, 2549, 2562, 2570, 2588,
2595, 2632, 2646, 2776, 2844, 2973, 3064, 3096
SODIUM: 2249,2274,2281,2283,2317,2319,2389,2471, 2481,
2534, 2542, 2562, 2570, 2583, 2595, 2600, 2653, 2717,
2723, 2730, 2738, 2745, 2782, 2790, 2842, 2855, 2867,
2883, 2912, 2925, 2969, 2996, 3026, 3071, 3086, 3104
STRONTIUM: 2256, 2317, 2319, 2384, 2388, 2389, 2440, 2534, 2542,
2587, 2588, 2595, 2632, 2730, 3103
2345, 2351, 2389,
2512, 2534, 2535,
2595, 2604, 2610,
2985, 2996, 2997,
2471, 2481,
2723, 2730,
2912, 2925,
3103, 3104,
2397, 2413,
2600, 2628,
2745, 2769,
2912, 2922,
SAMARIUM:
SCANDIUM:
SELENI T.M:
540
-------
TANTALUM: 2319, 2389, 2534
TECHNETIU1: 2319, 2588
TELLURIUM: 2319, 2534, 2588
TERBIUM: 2319, 2969
THALLIUM: 2283, 2319, 2534, 2570, 2588, 2595
THORIUM: 2319, 2570, 2588
THULIUM: 2319
TIN: 2283, 2319, 2534, 2541, 2570, 2730, 2775, 2939, 3064, 3081
TITANIUM: 2283, 2319, 2534, 2570, 2595
TUNGSTEN: 2283, 2319, 2534, 2588
URANIUM: 2283, 2319, 2534, 2542, 2588
VANADIUM: 2283, 2317,2319,2534,2541, 2570, 3064
YTTERBIUM: 2319, 2969
YTTRIUM: 2319, 2384, 2534, 2542, 2588
ZINC: 2254, 2258, 2263, 2280, 2281, 2282, 2283,
2318, 2319, 2338, 2343, 2345, 2351, 2362,
2389, 2393, 2408, 2429, 2447, 2472, 2477,
2533, 2534, 2535, 2541, 2542, 2547, 2551,
2558, 2562, 2565, 2570, 2584, 2585, 2588,
2632, 2645, 2646, 2647, 2656, 2665, 2678,
2715, 2718, 2726, 2730, 2731, 2739, 2757,
2830, 2855, 2872, 2882, 2887, 2888, 2906,
2936, 2969, 2972, 2973, 2976, 2982, 2985,
3022, 3023, 3037, 3058, 3064, 3073, 3074,
3110, 3112, 3129, 3132
ZIRCONIUM: 2283, 2319, 2534, 2588, 2793, 2979
FUNGI
CADMIUM: 2952, 3091
CALCIUM: 2692, 3111
CESIUM: 3111
CHROMI UM: 2314
COBALT: 2952
COPPER: 2692, 2952
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
IDLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2692, 2952
LANTHANLM: 2319
5L~1
2306, 2307, 2317,
2367, 2387, 2388,
2486, 2512, 2521,
2552, 2555, 2556,
2595, 2604, 2610,
2684, 2699, 2700,
2770, 2801, 2802,
2910, 2915, 2924,
2996, 2998, 3021,
3085, 3099, 3105,
-------
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319, 2952
MANGANESE: 2319, 2692, 2952
MERCURY: 2319, 2952
M)LYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2952, 3079
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIm~: 2319, 2458
POLONIUM: 2319
POTASSIUM: 2319, 3111
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319, 3014
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319, 2952
SODIUM: 2319, 3014
STRONTIUM: 2319, 3111
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2952
THORIUM: 2319
THUUUM: 2319
TIN: 2319, 3081
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2692, 2693, 2952, 3014
542
-------
ZIRCONIUM: 2319
HIGHER PLANTS
ALUMINUM: 2288, 2452, 2570, 2862
ANTIMONY: 2476, 2570
ARSENIC: 2570, 2645, 2876, 3063
BARIUM: 2452
BERYLLIUM: 2570, 3063
BIBLIOGRAPHY: 2570
BISMUTH: 2570
BORON: 2452, 2570, 2613, 3078
CADMIUM: 2401, 2523, 2529, 2570,
2848, 2872, 2896, 3018,
CALCIUM: 2262, 2268, 2366, 2452,
CERIUM: 2398
CESIUM: 2398, 2570, 2819, 2863, 3019, 3088
CHROMIUM: 2439, 2452, 2476, 2529, 2570, 2579, 3037, 3053, 3063
COBALT: 2452, 2476, 2522, 2523, 2570, 2783, 2884, 3053
COPPER: 2257, 2439, 2452, 2529, 2570, 2579, 2607, 2609, 2645,
2783, 2872, 2897, 2946, 3018, 3037, 3053
EUROPIUM: 2570
GJUX)LINIUM: 2319
GALLIUM: 2319, 2452
GERMANIUM: 2319, 2570
GOLD: 2319, 2476, 2523
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2257, 2260, 2268,2319, 2333, 2439, 2452, 2476, 2523, 2570,
2607, 2777, 2783
LANTHANUM: 2319, 2476
LEAD: 2319, 2401, 2439, 2452, 2523, 2529, 2570, 2579, 2645, 2754,
2783, 2866, 2872, 3037, 3053, 3063
LITHIUM: 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2262, 2268, 2319, 2366, 2452, 2523, 2570
MANGANESE: 2257, 2260, 2262, 2268, 2319, 2439, 2452, 2476, 2523,
2529, 2570, 2607, 2645
MERCURY: 2319, 2476, 2570, 2607, 2608, 2619, 2645, 2851, 2868,
2919, 2932, 3037, 3063, 3083
MOLYBDENUM: 2319, 2452, 2570
NEODYMIUM: 2319
NEPTUNIUM: 2319
2579, 2607, 2608, 2645, 2783,
3025, 3037, 3053, 3063
2523, 2570, 2618, 2783, 2862
543
-------
NICKEL: 2319, 2452, 2523, 2529, 2570, 2579, 2783, 2872, 3053,
3079
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2570, 3094
POLONIUM: 2319
POTASSIUM: 2262, 2319, 2366, 2452, 2476, 2523, 2570, 2819, 2862,
3067, 3088
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2476, 2570
RUTHENIUM: 2319, 2398
SALINITY: 2319, 2424, 2570, 2862, 2913, 3067
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2319, 2570, 2851, 3080
SILICON: 2319, 2366, 2452, 2570
SILVER: 2319, 2476, 2522, 2523, 2529, 2570, 2783
SODIUM: 2262, 2319, 2366, 2452, 2476, 2523, 2570, 2862
STRONTIUM: 2319, 2398, 2452, 2522, 2523, 2618, 2863
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2570
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2319, 2570, 3081
TITANIUM: 2319, 2452, 2570
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319, 2452, 2570
YTTERBIUM: 2319
YTTRHM: 2319
ZINC: 2319, 2439, 2452, 2476, 2523, 2529, 2570, 2579, 2609, 2645,
2783, 2872, 3018, 3037, 3053
ZIRCONIUM: 2319, 2452
INSECTA
544
-------
ALUMINUM: 2570, 2591, 2730
ANTIMONY: 2570
ARSENIC: 2555, 2556, 2570, 2591, 2645, 2720, 2730
BARIUM: 2591, 2730
BERYLLIUM: 2570, 2591
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570, 2591, 3078
CADMIUM: 2250, 2297,2300, 2301, 2322, 2393, 2520, 2555, 2556,
2562, 2570, 2591, 2610, 2624, 2629, 2630, 2645, 2706,
2730, 2859, 2930
CALCIUM: 2570, 2591, 2610, 2626, 2730, 2821, 2893, 2942
CESIl11: 2570
CHROMIUM: 2422, 2520, 2562, 2570, 2591, 2629, 2630, 2730, 2859,
2930
COBALT: 2562, 2570,
COPPER: 2250, 2279,
2591, 2610,
EUROPIUM: 2570
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2279,2297, 2319, 2562, 2570,2591, 2610, 2730
LANTHANUM: 2319
LEAD: 2250, 2297, 2319, 2322, 2393, 2405, 2422, 2539, 2555, 2556,
2562, 2570, 2591, 2610, 2624, 2645, 2730
LITHIUM: 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2319, 2570, 2591, 2610, 2730
MANGANESE: 2319, 2555> 2556, 2570, 2591, 2610, 2645, 2730, 2893
MERCURY: 2319, 2450, 2482, 2539, 2555, 2556, 2559, 2562, 2563,
2570, 2591, 2645, 2730, 2868, 2881
MOLYBDENUM: 2319, 2570, 2591
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2297, 2319, 2393, 2562, 2570, 2591, 2610, 2730, 2997,
3079
NIOBIU1: 2319
PALLADIlJr-1: 2319
PLATINUM: 2319, 2730
PLUTONIUM: 2319, 2570, 3094, 3125
POLONIUM: 2319
2591, 2610, 2730, 2893, 2997
2297, 2393, 2422, 2555, 2556, 2562, 2570,
2645, 2730
545
-------
POTASSIUM: 2319, 2562, 2570, 2730
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIUM: 2319, 2562
SALINITY: 2319, 2570, 2942
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2319, 2570, 2730, 3080
SILICON: 2319, 2570
SILVER: 2319, 2562, 2570, 2591
SODIUM: 2319, 2562, 2570, 2591, 2626, 2730, 2942
STRONTIUM: 2319, 2730
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2570
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2319, 2570, 2591, 2730
TITANIUM: 2319, 2570, 2591
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319, 2570, 2591
YT1ERBIUM: 2319
YTI'RIUM: 2319
ZINC: 2250, 2279, 2297, 2319, 2393, 2422, 2520, 2555, 2556, 2562,
2570, 2591, 2610, 2629, 2630, 2645, 2730, 2821, 2859, 2930
ZIRCONIUM: 2319
MAMMALIA
ALUMINUM: 2283, 2570, 2595, 3064
AMERICIUM: 2979, 2987
ANTIMONY: 2283, 2570
ARSENIC: 2283, 2378, 2486, 2570,
3064
BARIUM: 2378, 2749, 3064
BERYLLIUM: 2283, 2570, 3063
BIBLIOGRAPHY: 2570
2595, 2843, 2876, 2940, 3063,
546
-------
BISMUTH: 2570
BORON: 2378, 2570, 3078
CADMIUM: 2283, 2315, 2378, 2486, 2558, 2570, 2595, 2639, 2739,
2749, 2807, 2872, 3018, 3037, 3063, 3064, 3082
CALCIUM: 2283, 2481, 2570, 2595, 2749
CERIUM: 2979
CESIUM: 2570, 2979
CHROMIUM: 2283, 2378,2486, 2570, 2595,2749. 3037, 3063, 3064
COBALT: 2283, 2570, 2595, 2749, 3064
COPPER: 2283, 2315, 2378, 2486, 2570, 2595, 2749, 2872, 2960,
3018, 3037, 3064
EUROPIUM: 2570
GA1X)LINIUM: 2319
GALULM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319, 2378
HAFNIUM: 2319
IDLMIUM: 2319
INDIUM: 2319, 2933
IRIDIUM: 2319
IRON: 2283, 2319, 2570, 2595, 2749, 3064
LANTHANlM: 2283, 2319
LEAD: 2283, 2315, 2319, 2378, 2486, 2570, 2595, 2739, 2749, 2866,
2872, 2960, 2963, 3037, 3063, 3064
LITHIUM: 2283, 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2481, 2570, 2595
MANGANESE: 2283, 2319, 2570, 2595, 2749, 3064
MERCURY: 2283, 2315, 2319, 2377, 2378, 2462, 2486,
2566, 2570, 2595, 2606, 2685, 2687, 2713,
2761, 2807,2851, 2868, 2960, 2994, 3037,
3090, 3126
MOLYBDENUM: 2283, 2319, 2486, 2570, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2486, 2570, 2595, 2749, 2872, 3064, 3079
NIOBIUM: 2319, 2979
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2570, 2979, 2987, 3013, 3094
POLONIUM: 2319, 3045
POTASSIUM: 2319, 2481, 2570, 2595
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319, 2979
RADIUM: 2319
RHENIUM: 2319
2499, 2554,
2727, 2749,
3063, 3064,
547
-------
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIUM: 2319, 2979
SALINITY: 2283, 2319, 2570
SAMARIUM: 2319
SCANDIUM: 2319, 2570
SELENIUM: 2283, 2319, 2486, 2554, 2566, 2570, 2595,2687, 2739,
2807, 2851, 3064, 3080
SILICON: 2319, 2570, 2595
SILVER: 2283, 2319, 2378, 2570, 2595, 3064
SODIUM: 2283, 2319, 2481, 2570, 2595
STRONTIUM: 2319, 2595, 2749
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570, 2595
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 3064, 3081
TITANIUM: 2283, 2319, 2570, 2595
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2570, 2934, 3064
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2315, 2319, 2378, 2486, 2558, 2570, 2595, 2739, 2749,
2872, 3018, 3037, 3064
ZIRCONIUM: 2283, 2319, 2979
MISCELLANEOUS
ALUMINUM: 2570
ANTIMONY: 2570
ARSENIC: 2570
BARIUM: 3002
BERYLLIUM: 2570
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570
CADMIUM: 2562, 2570
CALCIUM: 2570
CESIUM: 2570
CHROMIUM: 2562, 2570
COBALT: 2562, 2570
548
-------
COPPER: 2562, 2570
EUROPIUM: 2570
GERMANIUM: 2570
IRON: 2562, 2570
LEAD: 2562, 2570
LITHIUM: 2570
MAGNESHM: 2570
MANGANESE: 2570
MERCURY: 2562, 2570
M)LYBDENUM: 2570
NICKEL: 2562, 2570
PLUTONIUM: 2570
POTASSIUM: 2562, 2570
RUBIDIUM: 2570
RUTHENIUM: 2562
SALINITY: 2570
SCANDIUM: 2570
SELENIUM: 2570
SIliCON: 2570
SILVER: 2562, 2570
SODIUM: 2562, 2570
THALLIUM: 2570
THORIUM: 2570
TIN: 2570
TITANIUM: 2570
VANADIUM: 2570
ZINC: 2562, 2570
M:JLLUSCA
ALUMINUM: 2283, 2285, 2288, 2289, 2375, 2444, 2570, 2595, 2730,
3064
AMERICIUM: 2542, 2674, 2961, 2974, 2979
ANTIMONY: 2283, 2375, 2534, 2570
ARSENIC: 2283, 2289, 2375, 2441, 2447, 2486, 2534, 2542, 2543,
2570, 2595, 2632, 2644, 2646, 2656, 2720, 2730, 2826,
2876, 3063, 3064
BARIUM: 2375, 2534, 2587, 2730, 3002, 3064
BERYLLIUM: 2283, 2534, 2570, 3063
BIBLIOGRAPHY: 2375, 2562, 2570, 2632
BISMUTH: 2375, 2534, 2570
BORON: 2570
CADMIUM: 2250, 2251,
2317, 2318,
2429, 2434,
2275, 2283, 2284, 2285, 2289, 2292, 2316,
2322, 2326, 2334, 2371, 2375, 2389, 2426,
2441, 2444, 2445, 2446, 2447, 2463, 2478,
549
-------
2486, 2513, 2521, 2534, 2542, 2557,
2579, 2580, 2584, 2595, 2608, 2610,
2646, 2647, 2656, 2658, 2666, 2669,
2725, 2730, 2734, 2739, 2757, 2760,
2852, 2872, 2887, 2957, 2973, 2995,
3063, 3064, 3082, 3096
CALCIUM: 2283, 2285, 2286, 2317, 2347, 2355,
2457,2475, 2479, 2481, 2534, 2542,
2595, 2610, 2730, 2733, 2891, 2981,
CERIUM: 2375, 2398, 2979, 3116
CESIUM: 2375, 2398, 2542, 2565, 2570, 2603, 2605, 2632, 2674,
2979, 3038, 3116
CHROMIUM: 2283, 2284, 2285, 2289, 2294, 2317,2318, 2375, 2389,
2407, 2429, 2434, 2441, 2444, 2447, 2486, 2534, 2542,
2557, 2562, 2570, 2575, 2579, 2595, 2632, 2646, 2647,
2704, 2705, 2730, 2803, 2826, 2852, 2973, 3063, 3064
COBALT: 2283, 2284, 2285, 2375, 2389, 2444, 2447, 2449, 2534,
2542, 2562, 2565, 2570, 2571, 2595, 2610, 2704, 2705,
2730, 2797,2826, 2852, 2884, 3038, 3064, 3116
COPPER: 2250, 2251, 2266, 2275, 2279, 2283, 2284, 2285, 2289,
2291, 2298, 2316, 2317, 2326, 2331, 2334, 2336, 2375,
2389, 2399, 2407, 2429, 2431, 2434, 2441, 2444, 2445,
2447, 2461, 2463, 2475, 2486, 2494, 2521, 2534, 2542,
2543, 2557, 2562, 2565, 2570, 2579, 2580, 2584, 2595,
2610, 2632, 2646,2647, 2656, 2658, 2671, 2674, 2704,
2705, 2708, 2710, 2730, 2732, 2734, 2757, 2803, 2816,
2823, 2825, 2826, 2836, 2839, 2852, 2853, 2872, 2877,
2895, 2905, 2944, 2957, 2964, 2973, 2990, 2991, 2995,
3018, 3027, 3056, 3064, 3096, 3120
EUROPIUM: 2375, 2570
GAroUNIUM: 2319
GALLIUM: 2319, 2375, 2534
GERMANIUM: 2319, 2375, 2534, 2570
GOLD: 2319, 2375
HAFNIUM: 2319, 2534
OOLMIUM: 2319
INDIUM: 2319, 2534
IRIDIUM: 2319
IRON: 2275, 2279, 2283, 2284, 2285, 2317, 2319,
2388, 2389, 2429, 2444, 2447, 2542, 2543,
2589,2595, 2610, 2647, 2704, 2705, 2730,
2891, 2973, 2975, 2995, 3055, 3056, 3064,
LANTHANUM: 2283, 2319, 2375, 2534, 2542
LEAD: 2250, 2251, 2275, 2283, 2284, 2285, 2289, 2316, 2317, 2319,
2322, 2375, 2389, 2405, 2429, 2434, 2441, 2444, 2447, 2463,
2475, 2486, 2492, 2521, 2534, 2542, 2557, 2562, 2570, 2579,
2584,2587,2589,2595,2610,2624,2632,2646,2647,2656,
2558, 2562, 2570,
2624, 2632, 2639,
2674, 2704, 2705,
2803, 2826, 2839,
3018, 3055, 3056,
2375, 2388, 2389,
2570, 2576, 2587,
3059
2326, 2334, 2375,
2562, 2565, 2570,
2823, 2826, 2853,
3120
550
-------
2664, 2674, 2704, 2705, 2725, 2730, 2739, 2754, 2757, 2760,
2803, 2826, 2839, 2852, 2866, 2872, 2879, 2887, 2962, 2964,
2975, 2995, 3055, 3056, 3063, 3064
LITHIUM: 2283, 2319, 2375, 2389, 2570
LUTETItM: 2319
MAGNESIUM: 2283, 2285, 2317,2319, 2355, 2375, 2389, 2457, 2475,
2479, 2481, 2534, 2542, 2570, 2595, 2610, 2701, 2730,
2733
MANGANESE: 2275, 2283, 2284, 2285, 2289, 2316, 2317, 2319, 2326,
2375, 2388, 2389, 2444, 2447, 2449, 2534, 2542, 2565,
2570, 2589, 2595, 2610, 2632, 2646, 2647, 2704, 2705,
2730, 2826, 2875, 2891, 2964, 3038, 3064, 3120
MERCURY: 2264, 2283, 2289, 2291, 2292, 2305, 2313, 2318, 2319,
2368, 2375, 2423, 2434, 2447, 2463, 2465, 2486, 2501,
2521, 2531, 2534, 2542, 2544, 2557, 2562, 2570, 2580,
2584, 2595, 2608, 2632, 2635, 2641, 2642, 2646, 2654,
2656, 2670, 2674, 2695, 2712, 2714, 2725, 2730, 2734,
2826, 2839, 2852, 2865, 2868, 2877, 2887, 2892, 2959,
2971, 2973, 3003, 3029, 3040, 3063, 3064, 3076, 3096,
3097, 3126
MOLYBDENUM: 2247, 2283, 2319, 2375, 2441, 2486, 2534, 2542, 2570,
2891, 3064
NEODYMIUM: 2319
NEPTUNIUM: 2319, 3035
NICKEL: 2275, 2283, 2284, 2285, 2289, 2291, 2316,
2319, 2326, 2330, 2375, 2389, 2434, 2441,
2463, 2475, 2486, 2534, 2542, 2557, 2562,
2579, 2595, 2610, 2632, 2647, 2674, 2704,
2839, 2852, 2872, 2973, 2995, 3064, 3079
NIOBIUM: 2319, 2375, 2534, 2979
OSMIUM: 2534
PALLADIUM: 2319, 2534
PLATINUM: 2319, 2534, 2730
PLUTONIUM: 2319, 2375, 2542, 2570, 2617, 2632, 2674, 2831, 2961,
2974, 2979, 3013, 3094
POLONIUM: 2319, 2375
POTASSIUM: 2317, 2319, 2355, 2375, 2389, 2457, 2475, 2481, 2542,
2562, 2570, 2595, 2695, 2701, 2730
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319, 2979
RADIUM: 2319, 2375, 2542
RHENIUM: 2319
RHODIUM: 2319, 2605
RUBIDIUM: 2319, 2375, 2389, 2565, 2570, 2898
RUTHENIUM: 2319, 2375, 2398, 2534, 2562, 2605, 2979, 3116
SALINITY: 2283, 2319, 2355, 2369, 2423, 2445, 2479, 2537, 2542,
2317, 2318,
2444, 2447,
2565, 2570,
2705, 2730,
551
-------
2570, 2589, 2625, 2641, 2701, 2710, 2712, 2834, 2860,
2947, 2962, 3054
2319, 2375, 2389
2319, 2375, 2388, 2389, 2534, 2542, 2570
2283, 2319, 2375, 2486, 2534, 2542, 2570, 2595, 2632,
2730, 2739, 2826, 3064, 3080, 3097
SILICON: 2319, 2375, 2534, 2570, 2595
SILVER: 2283, 2284, 2285, 2289, 2291, 2292,
2389, 2441, 2444, 2447, 2501, 2542,
2571, 2595, 2632, 2646, 2674, 2704,
2957, 2973, 3064, 3096
SODIUM: 2283, 2317, 2319, 2355, 2375, 2389, 2457, 2475, 2479,
2481, 2534, 2542, 2562, 2570, 2595, 2701, 2730, 2890
STRONTIUM: 2286, 2317, 2319, 2326, 2375, 2388, 2389, 2398, 2534,
2542, 2587, 2595, 2632, 2730, 2981, 3059, 3116
TANTALUM: 2319, 2389, 2534
TECHNETIUM: 2319, 2375
TELLURIUM: 2319, 2534
TERBIUM: 2319
THALLIUM: 2283, 2319, 2534, 2570, 2595
THORIUM: 2319, 2375, 2570
THULIUM: 2319
TIN: 2283, 2319, 2375, 2534, 2570, 2730, 3064, 3081
TITANIUM: 2283, 2319, 2326, 2375, 2444, 2534, 2570, 2595
TUNGSTEN: 2283, 2319, 2534
URANIUM: 2283, 2319, 2534, 2542
VANADIUM: 2283, 2317, 2319, 2375, 2444, 2534, 2570, 2934, 3051,
3064 '
YTTERBIUM: 2319
YTTRIUM: 2319, 2534, 2542
ZINC: 2250, 2251, 2261, 2275, 2279, 2283,
2316, 2317, 2318, 2319, 2326, 2334,
2389, 2429, 2434, 2444, 2445, 2446,
2486, 2513, 2521, 2534, 2542, 2557,
2571, 2579, 2584, 2595, 2610, 2632,
2671, 2674, 2704, 2705, 2730, 2739,
2839,2852, 2872, 2877,2887,2895,
3018, 3055, 3056, 3064, 3120
ZIRCONIUM: 2283, 2319, 2375, 2534, 2979
SAMARIUM:
SCANDI UM:
SELENIUM:
2319, 2326, 2375,
2557, 2562, 2570,
2705, 2826, 2877,
2284, 2285, 2289, 2291,
2348, 2371, 2375, 2388,
2447, 2461, 2463, 2475,
2558, 2562, 2565, 2570,
2646, 2647, 2656, 2658,
2757, 2802, 2823, 2826,
2957,2964, 2973, 3012,
NEMATODA
ALUMINUM: 2570
ANTIMONY: 2570
ARSENIC: 2570, 2720
552
-------
BERYLLIUM: 2570
BIBLIOGRAPHY: 2570
BISMUTH: 2570
BORON: 2570
CAOO UM: 2570
CALCIUM: 2570
CESIUM: 2570
CHROMIUM: 2570
COBALT: 2570
COPPER: 2570
EUROPIUM: 2570
GAroLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2570
LANTHANUM: 2319
LEAD: 2319, 2570, 2866
LITHIUM: 2319, 2570
LUTETIUM: 2319
MAGNESIUM: 2319, 2570
MANGANESE: 2319, 2570
MERCURY: 2319, 2570
M)LYBDENUM: 2319, 2570
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2570
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONItM: 2319, 2570
POLONIUM: 2319
POTASSItM: 2319, 2570
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIlM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RUTHENIlM: 2319
SALINITY: 2319, 2570, 2740
SAMARIUM: 2319
553
-------
SCANDIUM: 2319, 2570
SELENIUM: 2319, 2570
SILICON: 2319, 2570
SILVER: 2319, 2570
SODIUM: 2319, 2570
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2570
THORIUM: 2319, 2570
THUliUM: 2319
TIN: 2319, 2570, 3081
TITANIUM: 2319, 2570
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319, 2570
YTIERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2570
ZIRCONIUM: 2319
PHORONIDEA
COPPER: 2266, 2336
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319
LANTHANUM: 2319
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319
MERCURY: 2319
MOLYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
554
-------
NICKEL: 2319
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMElHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319
SODILM: 2319
STRONTIUM: 2319
TANTALU1: 2319
TECHNETIUM: 2319
TElLURIlli: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319
ZIRCONIUM: 2319
PLANKTON
ALUMINUM: 2452, 2570, 2573, 2604
AMERICIUM: 2974
ANTIMJNY: 2570
555
-------
ARSENIC: 2556, 2570, 2604, 2632, 2644, 3092
BARIUM: 2452, 2573
BERYLLIUM: 2570
BIBLIOGRAPHY: 2570, 2632
BISMUTH: 2570
BORON: 2452, 2570
CADMIUM: 2389,2556,2570, 2573, 2604, 2632, 2647,2771, 2911,
3092
CALCIUM: 2388, 2389, 2452, 2570, 2573
CESIUM: 2570, 2632
CHROMIUM: 2389, 2452, 2570, 2604, 2632, 2647, 3092
COBALT: 2389, 2452, 2570, 2604, 3092
COPPER: 2389, 2452, 2556, 2570, 2573, 2604, 2632, 2647, 2665,
2990, 3092
EUROPIUM: 2570
GAroLINIUM: 2319
GALLIUM: 2319, 2452
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2388, 2389, 2452, 2570, 2573, 2604, 2647, 2789
LANTHANUM: 2319
LEAD: 2319, 2389, 2452, 2556, 2570, 2573, 2604, 2632, 2647, 3092
LITHIUM: 2319, 2389, 2570
LUTETIUM: 2319
MAGNESIUM: 2319, 2389, 2452, 2570, 2573
MANGANESE: 2319, 2388, 2389, 2452, 2556, 2570, 2573, 2604, 2632,
2647, 3092
MERCURY: 2319, 2556, 2570, 2604, 2632, 2665, 2703, 2768, 2780,
2784, 2808, 2868, 2871, 3092
MOLYBDENUM: 2319, 2452, 2570
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2389, 2452, 2570, 2573, 2604, 2632, 2647, 3092
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2570, 2632, 2974, 3115
POLONIUM: 2319, 3092
POTASSIUM: 2319, 2389, 2452, 2570, 2573
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
556
-------
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389, 2570
RUTHENIUM: 2319
SALINITY: 2319, 2570, 3092
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2388, 2389, 2570
SELENIUM: 2319, 2570, 2632, 3092
SILICON: 2319, 2452, 2570, 2573, 3092
SILVER: 2319, 2389, 2570, 2573, 2632, 3092
SODIUM: 2319, 2389, 2452, 2570, 2573
STRONTIUM: 2319, 2388, 2389, 2452, 2573, 2632, 3092
TANTALUM: 2319, 2389
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2570
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2319, 2570, 3081
TITANIUM: 2319, 2452, 2570
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319, 2452, 2570
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2388, 2389, 2452, 2556, 2570, 2573, 2604, 2632, 2647,
2665, 3092
ZIRCONIUM: 2319, 2452, 3092
PLATYHELMINTHES
BIBLIOGRAPHY: 2562
CADMIUM: 2438, 2562, 2984
CHROMIUM: 2562
COBALT: 2562
COPPER: 2279, 2562
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
557
-------
IRON: 2279, 2319, 2562
LANTHANUM: 2319
LEAD: 2319, 2562
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319
MERCURY: 2319, 2562
MOLYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2562
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319, 2562
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319, 2562
SALINITY: 2319, 2740
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319, 2562
SODIUM: 2319, 2562
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIlM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIU1: 2319
VANADIUM: 2319
YTTERBIUM: 2319
558
-------
YTI'RIUM: 2319
ZINC: 2279, 2319, 2348, 2562
ZIRCONIUM: 2319
PORIFERA
ALUMINUM: 2283
ANTIMONY: 2283
ARSENIC: 2283
BERYLLIUM: 2283
BIBLIOGRAPHY: 2562
CADMIUM: 2283, 2389, 2562
CALCIUM: 2283, 2389
CHROMIUM: 2283, 2389, 2562
COBALT: 2283, 2389, 2562
COPPER: 2283, 2389, 2562
GADJLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
IDLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2389, 2562
LANTHANUM: 2283, 2319
LEAD: 2283, 2319, 2389, 2562
LITHIUM: 2283, 2319, 2389
LUTETIUM: 2319
MAGNESIUM: 2283, 2319, 2389
MANGANESE: 2283, 2319, 2389
MERCURY: 2283, 2319, 2562
M:JLYBDENUM: 2283, 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2389, 2562
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319, 2389, 2562
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
559
-------
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389
RUTHENIUM: 2319, 2562
SALINITY: 2283, 2319
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2389
SELENIUM: 2283, 2319
SILICON: 2319
SILVER: 2283, 2319, 2389, 2562
SODIUM: 2283, 2319, 2389, 2562
STRONTIUM: 2319, 2389
TANTALUM: 2319, 2389
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319
lliORI UM: 2319
THULIlM: 2319
TIN: 2283, 2319
TITANIUM: 2283, 2319
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319
YTTERBIUM: 2319
YTIRIUM: 2319
ZINC: 2283, 2319, 2389, 2562
ZIRCONIUM: 2283, 2319
PROTOZOA
ALUMINUM: 2283, 2288, 2570
AMERICIUM: 2542
ANTIMONY: 2283, 2570
ARSENIC: 2283, 2542, 2570, 2720
BARIUM: 2938
BERYLLIUM: 2283, 2570
BIBLIOGRAPHY: 2562, 2570
BISMUTH: 2570
BORON: 2570, 3078
CADMIUM: 2283, 2542, 2562, 2570, 2872, 2952
CALCIUM: 2283, 2542, 2570, 2838, 2938, 3070
CESIUM: 2542, 2570
CHROMIUM: 2283, 2542, 2562, 2570
560
-------
COBALT: 2283, 2542, 2562, 2570, 2952
COPPER: 2266, 2283, 2460, 2542, 2562, 2570, 2872, 2952
EUROPIUM: 2570
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2542, 2562, 2570, 2952
LANTHANUM: 2283, 2319, 2542
LEAD: 2283, 2319, 2468, 2542, 2562, 2570, 2872
LITHIUM: 2283, 2319, 2570
LU1ETIUM: 2319
MAGNESIUM: 2283, 2319, 2542, 2570, 2838, 2952, 3070
MANGANESE: 2283, 2319, 2460, 2542, 2570, 2952
MERCURY: 2283, 2319, 2468, 2542, 2562, 2570, 2952, 3015
MOLYBDENUM: 2283, 2319, 2542, 2570
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2542, 2562, 2570, 2872, 2952, 3079
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2542, 2570
POLONIUM: 2319
POTASSIUM: 2319, 2542, 2562, 2570, 2838, 2938
PRASEODYMHM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319, 2542
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2570
RU'IHENIUM: 2319, 2562
SALINITY: 2283, 2319, 2542, 2570, 2838
SAMARIUM: 2319
SCANDIUM: 2319, 2542, 2570
SELENIUM: 2283, 2319, 2542, 2570
SILICON: 2319, 2570
SILVER: 2283, 2319, 2542, 2562, 2570, 2952
SODIUM: 2283, 2319, 2542, 2562, 2570, 2838, 2938, 3070
STRONTIUM: 2319, 2542, 2938
TANTALUM: 2319
TECHNETIUM: 2319
561
-------
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319, 2570, 2952
THORIUM: 2319, 2570
THULIUM: 2319
TIN: 2283, 2319, 2570, 3081
TITANIUM: 2283, 2319, 2570
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319, 2542
VANADIUM: 2283, 2319, 2570
YTTERBIUM: 2319
YTTRIUM: 2319, 2542
ZINC: 2283, 2319, 2468, 2542, 2562, 2570, 2872, 2952
ZIRCONIUM: 2283, 2319
REPTILIA
GAJX)LINIUM: 2319
GALLIU1: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDILM: 2319
IRON: 2319
LANTHANUM: 2319
LEAD: 2319
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319
MERCURY: 2319
M)LYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLCNIUM: 2319
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMEI'HILM: 2319
562
-------
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319
SODIUM: 2319
STRONTI UM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319
Z IRCONI UM: 2319
ROTIFERA
ARSENIC: 2720
BIBLIOGRAPHY: 2562
CAIMIUM: 2562
CHROMIUM: 2562
COBALT: 2562
COPPER: 2266, 2562, 2968
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
563
-------
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2562
LANTHANUM: 2319
LEAD: 2319, 2562
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319
MANGANESE: 2319
MERCURY: 2319, 2562, 2621
M)LYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2562
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONI UM: 2319
POLOOIUM: 2319
POTASSIUM: 2319, 2562
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIa1: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319, 2562
SALINITY: 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2319
SILICON: 2319
SILVER: 2319, 2562
SODIUM: 2319, 2562
STRONTIUM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319
THORIUM: 2319
THUliUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
564
-------
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2562
ZIRCONIUM: 2319
SEAWATER
ALUMINUM: 2288, 2570, 2573, 2604, 2676
AMERICIUM: 2961, 2974, 2979
ANTIMJNY: 2570
ARSENIC: 2447,2570,2604,2632, 2937,2967,3092
BARIUM: 2573, 2587, 2676
BERYLLIUM: 2570
BIBLIOGRAPHY: 2570, 2632
BISMUTH: 2570
BORON: 2570, 3078
CADMIUM: 2389, 2447, 2570,
2676, 2759, 2771,
CALCIUM: 2389, 2475, 2570,
CERIUM: 2979, 3116
CESIUM: 2421, 2570, 2605, 2632, 2979, 3116
CHROMIUM: 2389, 2447, 2570, 2575, 2604, 2632, 2662, 2676, 2759,
2852, 2882, 3092
COBALT: 2389, 2421, 2447, 2570,
COPPER: 2389, 2447, 2475, 2508,
2632, 2662, 2676, 2759,
3092
EUROPIUM: 2570
GERMANIUM: 2570
IRON: 2389,2447, 2570,
LEAD: 2389, 2447, 2475,
2632, 2662, 2676,
LITHIUM: 2389, 2570
MAGNESIUM: 2389, 2475, 2570, 2573, 2676, 2759, 3104
MANGANESE: 2389, 2447, 2570, 2573, 2604, 2632, 2676, 2759, 3092
MERCURY: 2400, 2447, 2570, 2584, 2604, 2608, 2632, 2662, 2676,
2703, 2852, 2864, 2887, 2892, 2953, 3076, 3092, 3126
MOLYBDENUM: 2570
NICKEL: 2389, 2447, 2475, 2570, 2573, 2604, 2632, 2676, 2852,
2882, 2995, 3079, 3092
NIOBIUM: 2421, 2979
PLUTONIUM: 2570, 2617, 2632, 2961, 2974, 2979, 3013
POLONIUM: 2538, 3092
POTASSIUM: 2389, 2475, 2570, 2573, 2676, 2759, 3104
2573, 2584, 2604, 2608, 2616, 2632,
2852, 2882, 2887, 2995, 3092
2573, 2587, 2676, 2759, 3059, 3104
2604, 2676, 2852, 3092, 3116
2570, 2573, 2584, 2604, 2616,
2852, 2882, 2990, 2991, 2995,
2573, 2604, 2672, 2676, 2759, 2789, 2995
2538, 2570, 2573, 2584, 2587, 2604, 2616,
2759, 2852, 2882, 2887, 2995, 3092
565
-------
PROTACTINIUM: 2979
RHODIUM: 2421, 2605
RUBIDIUM: 2389, 2570
RUTHENIUM: 2421, 2605, 2979, 3116
SALINITY: 2570, 3092
SAMARIUM: 2389
SCANDIUM: 2389, 2570
SELENIUM: 2570, 2632, 3080, 3092
SILICON: 2570, 2573, 2676, 2681, 3092
SILVER: 2389, 2447, 2570, 2573, 2632, 2676, 3092
SODIUM: 2389, 2475, 2570, 2573, 2676, 2759, 3104
STRONTIUM: 2389, 2573, 2587, 2632, 2676, 3059, 3092, 3116
TANTALUM: 2389
THALLIUM: 2570
THORIUM: 2570
TIN: 2570, 3081
TITANIUM: 2570
VANADIUM: 2295, 2570
ZINC: 2389, 2447, 2475, 2508, 2570, 2573, 2584, 2604, 2616, 2632,
2676, 2759, 2852, 2882, 2887, 3092
ZIRCONIUM: 2421, 2979, 3092
SEDIMENTS
ALUMINUM: 2283, 2452, 2570, 2591, 2604, 2856
AMERICIUM: 2961, 2974, 2979
ANTIMONY: 2283, 2541, 2570, 2969
ARSENIC: 2283, 2447, 2486, 2541, 2543, 2555, 2556, 2570, 2591,
2604, 2644, 2645, 2646, 2876, 2969, 3063
BARIUM: 2452, 2541, 2591, 3002
BERYLLIUM: 2283, 2570, 2591, 3063
BIBLIOGRAPHY: 2570
BISMUTH: 2570
BORON: 2452, 2570, 2591, 3078
CADMIUM: 2251, 2253, 2282, 2283,
2447, 2477, 2486, 2509,
2579, 2591, 2604, 2608,
2704, 2705, 2759, 2783,
2887, 2930, 2969, 2982,
CALCIUM: 2283, 2389, 2452, 2570,
2985
CERIUM: 2969, 2979, 3116
CESIUM: 2421, 2510, 2570, 2605, 2863, 2979, 3019, 3050, 3116
CHROMIUM: 2253, 2283, 2284, 2294, 2389, 2415, 2422, 2439, 2447,
2452, 2477, 2486, 2520, 2541, 2570, 2575, 2579, 2591,
2284, 2322,
2520, 2541,
2610, 2629,
2848, 2852,
2985, 3043,
2591, 2610,
2389, 2401, 2415,
2555, 2556, 2570,
2630, 2645, 2646,
2856, 2859, 2882,
3053, 3063
2759, 2783, 2856,
566
-------
2604, 2629, 2630, 2646, 2704, 2705, 2759, 2852, 2859,
2882, 2930, 2969, 2985, 3053, 3063
COBALT: 2283, 2284, 2354, 2389, 2415, 2421, 2447, 2452, 2510,
2570, 2571, 2591, 2604, 2610, 2704, 2705, 2783, 2852,
2856, 2969, 2985, 2997, 3053, 3116
COPPER: 2251, 2279, 2282, 2283, 2284, 2331, 2346, 2389, 2422,
2439, 2447, 2452, 2477, 2486, 2541, 2543, 2555, 2556,
2570, 2579, 2591, 2604, 2610, 2645, 2646, 2704, 2705,
2716, 2759, 2783, 2852, 2856, 2882, 2946, 2969, 2985,
2990, 2991, 3043, 3053
DYSPROSIUM: 2969
ERBIUM: 2969
EUROPIUM: 2570, 2969
GAOOLINIUM: 2319, 2969
GALLIUM: 2319, 2452, 2969
GERMANIUM: 2319, 2570
GOLD: 2319
HAFNIUM: 2319, 2969
HOLMItJ1: 2319, 2969
INDIUM: 2319
IRIDIUM: 2319
IRON: 2279, 2283, 2284, 2319, 2346, 2389, 2439, 2447, 2452, 2541,
2543, 2570, 2591, 2604, 2610, 2704, 2705, 2759, 2783, 2856,
2969, 2975, 2985, 3043
LANTHANUM: 2283, 2319, 2969
LEAD: 2251, 2282, 2283, 2284,
2422, 2439, 2447, 2452,
2570, 2579, 2591, 2604,
2754, 2759, 2783, 2852,
3063
LITHIUM: 2283, 2319, 2389, 2570
LUTETIUM: 2319, 2969
MAGNESIUM: 2283, 2319, 2389, 2452, 2570, 2591, 2610, 2759, 2856,
2985
MANGANESE: 2283, 2284, 2319, 2346, 2389, 2439, 2447, 2452, 2541,
2555, 2556, 2570, 2591, 2604, 2610, 2645, 2646, 2704,
2705, 2759, 2856, 2969, 2985
MERCURY: 2248, 2282, 2283, 2319, 2354, 2368, 2415,
2486, 2500, 2531, 2539, 2541, 2555, 2556,
2591, 2604, 2608, 2642, 2645, 2646, 2703,
2852, 2881, 2887, 2932, 2951, 2969, 2985,
3063, 3076, 3083, 3126
MOLYBDENUM: 2283, 2319, 2452, 2486, 2541, 2570, 2591
NEODYMIUM: 2319, 2969
NEPTUNIUM: 2319
NICKEL: 2283, 2284, 2319, 2346, 2389, 2447, 2452, 2486, 2541,
2570, 2579, 2591, 2604, 2610, 2704, 2705, 2783, 2852,
2319, 2322,
2477, 2486,
2610, 2645,
2856, 2866,
2389, 2401,
2539, 2541,
2646, 2704,
2882, 2887,
2405, 2415,
2555, 2556,
2705, 2716,
2975, 3053,
2447, 2451,
2563, 2570,
2729, 2851,
2994, 3043,
567
-------
2856, 2882, 2985, 2997, 3053
NIOBIUM: 2319, 2421, 2510, 2979
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319, 2346, 2570, 2617, 2961, 2974, 2979, 3013, 3060,
3066, 3094, 3125
POLONIUM: 2319, 2856
POTASSIUM: 2319, 2389, 2452, 2570, 2759, 2985, 3067
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319, 2979
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319, 2421, 2510, 2605
RUBIDIUM: 2319, 2389, 2570
RUTHENIUM: 2319, 2346, 2421, 2510, 2605, 2979, 3116
SALINITY: 2283, 2319, 2570, 3067
SAMARIUM: 2319, 2389, 2969
SCANDIUM: 2319, 2389, 2570, 2969
SELENIUM: 2283, 2319, 2486, 2541, 2570, 2851, 2969
SILICON: 2319, 2452, 2570, 2856
SILVER: 2283, 2284, 2319, 2389, 2447, 2541, 2570, 2571, 2591,
2646, 2704, 2705, 2783
SODIUM: 2283, 2319, 2389, 2452, 2570, 2591, 2759, 2969
STRONTIUM: 2319, 2389, 2452, 2863, 3116
TANTALUM: 2319, 2389
TECHNETIt}1: 2319, 2346
TELLURIUM: 2319
TERBIUM: 2319, 2969
THALLIUM: 2283, 2319, 2570
THORIUM: 2319, 2570, 3050
THULIUM: 2319
TIN: 2283, 2319, 2541, 2570, 2591
TITANIUM: 2283, 2319, 2452, 2570, 2591
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319, 3050
VANADIUM: 2283, 2295, 2319, 2452, 2541, 2570, 2591
YTTERBIUM: 2319, 2969
YTTRIUM: 2319
ZINC: 2251, 2261, 2279, 2282, 2283, 2284,
2447, 2452, 2477, 2486, 2520, 2541,
2579, 2591, 2604, 2610, 2629, 2630,
2716, 2759, 2783, 2852, 2856, 2859,
2982, 2985, 3043, 3053
ZIRCONIUM: 2283, 2319, 2421, 2452, 2510, 2856, 2979
2319, 2389, 2422, 2439,
2555, 2556, 2570, 2571,
2645, 2646, 2704, 2705,
2882, 2887, 2930, 2969,
568
-------
SESTON
CADMIUM: 2389, 2516, 3043
CALCIUM: 2389
CHROMIUM: 2389
COBALT: 2389
COPPER: 2358, 2389, 2516, 3043
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2389, 2516, 3043
LANTHANUM: 2319
LEAD: 2319, 2389, 2516
LITHIUM: 2319, 2389
LUTETIUM: 2319
MAGNESIUM: 2319, 2389
MANGANESE: 2319, 2389
MERCURY: 2319, 2325, 3043
MJLYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2389
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLOOIUM: 2319
POTASSIUM: 2319, 2389
PRASEODYMIUM: 2319
PROMEI'HIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319, 2389
RUTHENIUM: 2319
SALINITY: 2319
SAMARIUM: 2319, 2389
SCANDIUM: 2319, 2389
SELENIUM: 2319
SILICON: 2319
569
-------
SILVER: 2319, 2389
SODIUM: 2319, 2389
STRONTIUM: 2319, 2389
TANTALUM: 2319, 2389
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLI UM: 2319
THORIUM: 2319
THULIUM: 2319
TIN: 2319
TITANIUM: 2319
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2389, 2516, 3043
ZIRCONIUM: 2319
SI PUNCULOIDEA
ALUMINUM: 2595
ARSENIC: 2595
BARIUM: 3002
CAIMIUM: 2595
CALCIUM: 2457, 2595
CHROMIUM: 2595
COBALT: 2595
OOPPER: 2595
GADOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HOLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2319, 2595
LANTHANUM: 2319
LEAD: 2319, 2595
LITHIUM: 2319
LUTETIUM: 2319
MAGNESIUM: 2319, 2457, 2595
MANGANESE: 2319, 2595
570
-------
MERCURY: 2319, 2595
MOLYBDENUM: 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2319, 2595
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
POTASSIUM: 2319, 2457, 2595
PRA.::EODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIlM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTIIEIUUM: 2319
SALINITY: 2319
SAMARIUM: 2319
SCANDILM: 2319
SELENIUM: 2319, 2595
SILICON: 2319, 2595
SILVER: 2319, 2595
SODIUM: 2319, 2457, 2595
STRONTIUM: 2319, 2595
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2319, 2595
TIIORIUM: 2319
THUUUM: 2319
TIN: 2319
TITANIUM: 2319, 2595
TUNGSTEN: 2319
URANIUM: 2319
VANADIUM: 2319
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2319, 2595
ZIRCONIUM: 2319
SOILS
571
-------
CESIUM: 3050
NICKEL: 3079
SELENIU1: 3080
TIIORIUM: 3050
TIN: 3081
URANIUM: 3050
TUNICATA
ALUMINUM: 2283, 2604
ANTIMONY: 2283
ARSENIC: 2283, 2604
BARIUM: 3002
BERYLLIUM: 2283
CADMIUM: 2283, 2604
CALCIUM: 2283
CHROMIUM: 2283, 2604
COBALT: 2283, 2604
COPPER: 2266, 2283, 2336, 2604
GAOOLINIUM: 2319
GALLIUM: 2319
GERMANIUM: 2319
GOLD: 2319
HAFNIUM: 2319
HJLMIUM: 2319
INDIUM: 2319
IRIDIUM: 2319
IRON: 2283, 2319, 2604
LANTHANlJ.1: 2283, 2319
LEAD: 2283, 2319, 2604
LITHIUM: 2283, 2319
LUTETIUM: 2319
MAGNESIUM: 2283, 2319
MANGANESE: 2283, 2319, 2604
MERCURY: 2283, 2319, 2604, 3076
M)LYBDENUM: 2283, 2319
NEODYMIUM: 2319
NEPTUNIUM: 2319
NICKEL: 2283, 2319, 2604
NIOBIUM: 2319
PALLADIUM: 2319
PLATINUM: 2319
PLUTONIUM: 2319
POLONIUM: 2319
5]2
-------
POTASSIUM: 2319
PRASEODYMIUM: 2319
PROMETHIUM: 2319
PROTACTINIUM: 2319
RADIUM: 2319
RHENIUM: 2319
RHODIUM: 2319
RUBIDIUM: 2319
RUTHENIUM: 2319
SALINITY: 2283, 2319
SAMARIUM: 2319
SCANDIUM: 2319
SELENIUM: 2283, 2319
SILICON: 2319
SILVER: 2283, 2319
SODIUM: 2283, 2319
SI'RONTILM: 2319
TANTALUM: 2319
TECHNETIUM: 2319
TELLURIUM: 2319
TERBIUM: 2319
THALLIUM: 2283, 2319
THORIUM: 2319
TIfULIUM: 2319
TIN: 2283, 2319
TITANIUM: 2283, 2319
TUNGSTEN: 2283, 2319
URANIUM: 2283, 2319
VANADIUM: 2283, 2319, 2934
YTTERBIUM: 2319
YTTRIUM: 2319
ZINC: 2283, 2319, 2604
ZIRCONIUM: 2283, 2319
573
-------
INDEX - AUTHORS
Aarkro~, A. 3013
Abbott, O.J. 2247
Abde1ma1ik, ioJ. E. Y. 2370
Abernathy, A. R. 2248
Achituv, Y. 2625
Adams, A. 2343, 2344, 2646
Adams, C.E., Jr. 2696
Adamska, 11. 2614
Adeney, R.J. 2367
Agadi, V.V. 2697
Ahsanu11ah, M. 2698
Akesson, B. 3077
Al-Daham, N.K. 2249
Alexander, G. V . 2297
Allen, D.A. 2636
Alvarado, R.H. 2796
lrnano, K. 2908
Amiard-Triquet, C. 2884
Arrrnann, B. D. 2555, 2645
Anderson, A. 2308
Anderson, D.M. 2660
Anderson, J J'J, 2581
Anderson, L.H.J. 2812
Anderson, M.A. 2591, 2813
Anderson, P.D. 2535, 3123,
3129
2624
2250, 2251,
2661, 2885
Anderson, V. 2520, 2859
Anderson, V.L. 2401
Anderson, H.L. 2932
Andren, A. riJ. 2563, 2868
Andrew, R.W. 2252, 2536
Annett, C.8. 2499
Anon. 2635, 2933, 2934, 3078,
3079, 3080, 3081, 3082
Antonovics, J. 2609
Aoyama, I. 2935
Arai, K. 2902
Archibald, F. 8. 2814
Arias, A. 3031, 3036
Ar1hac, D.P. 2815
Armstrong, F .A.J. 2687
Arnott, G.H. 2698
Anderson, R.L.
Anderson, R. V .
2958
2729
2324
2520, 2629, 2930
2253, 2627,
2648, 2688, 2699,
2837, 2982, 3110
Angier, H. 28M-, 3083
Austen, K. 2362
Austin, B. 2636
Auty, E.H. 2263
Avau1t, J.1-1., Jr. 2835
Averett, R.C. 2331
AyLing, G.H. 2887
Azam, F. 2502, 2511, 2668,
2765
Arora, A.
Asell, B.
Ashfie1d, D.
Atchison, G.
Atchison, G.J.
Babich, H.
Bacci, E.
Badsha, Y.:. S .
3014
2865
2254, 2700,
2936
2255
2427, 2582
2256
3116
2766, 2767
3048
2257
23M.
3115
2662
2719
2631
3067
2258
2259. 2304
2388
2377
3006
2260
Bagnyuk, V.H.
Bahner J L. H.
Bakunov, N.A.
Ba1ani, 11. C.
BalchtJin, G.F.
Banchf'x, E.
Banus, H.D.
Baptist, J.P.
Baptista, G.B.
Barbaro, A.
Barbour, 8.E.
Barica, J.
Barko, J.H.
Bar1rnv, D.J.
Barnes, D.J.
Barnes, 8.8.
Barron, G.P.
Barry, E.P.
Bas iouny , F .M.
Bass, E.L. 2537
Bates, J.M. 2825
Baudm, J.-P. 2261
Bauer, J. 2577
Bffi..uen, C.A. 3018
574
-------
Bayley, I.L. 2262
Beruner, P. 2281
Beamish, F.W.H. 3007, 3128
Beamish, R.J. 2512
Beasley, T.M. 2538
Beattie, J.R. 3084
Beauchamp, J.J. 3041
Bebbington, G.N. 2263
Beckett, J.S. 2264
Bedford, J.J. 2265
Beers, J.R. 2266, 2768
Belisle, B.H. 2947
Bellan, G. 2849
Bel1an-Santini, D.
Bende.r, ~f.L. 2733
Bengtsson, B.-E. 2769, 2886
Benoit, D.A. 3085
Benos, D.J. 2847
Bentley-Hmvat, J .A.
Benzonana, G. 2774
Benzschawel, H. 2409, 2578
Berger, If. Y. 2701
Berk, S.G. 3015
Berland, B. R. 2815
Bernstein, I.A. 2980, 3024,
3091
Besselievre, H.L. 2388
Best, E.P.H. 2268
Betz, 11. 2269
Betzer, S.B. 2816
Beuchat, L.R. 2785
Beyers, R. J. 2482
Bhan, S. 3086
Bhattacharya, S. 2418
Bhatti, M. N. 2249
Bhosle, N.B. 2697
Bielig, H.-J. 2409
Biesinger, K.E. 2252
Bilio, M. 2662
Billard, R. 2702
Birge, W.J. 3073
Birks, E. 2376
Bishop, J.N. 2270
Bishop, W.E. 2699
Bissonnette, P. 2539
Bitton, G. 2817
Black, J .A. 2545
Black, R. 2843
2849
2267
Blair, W. 2728
Blair, iJ.R. 2703
Blankespoor, H.D. 2348
Blaxter, J.H.S. 2271
Blaylock, B.G. 3041, 3089
Blinn, D.H. 2272
Bloam, R. 2887
Bloam, H.D. 2888
Blunt, ~.R. 2362, 2675, 2903
Bochenin, V.F. 30S7, 3102
Beeuf, G. 2912
"Bof,gess, ~T.R.
BolTI, L. 2663
Bohn, A. 2770
Boisseau, D. 2340
Boney, A.D. 2889
Bonin, D.J. 2815
Borgr18J1Tl, U. 2664
Berowitzka, L.J. 2273
Boswell, F.C. 2785
Bottino, N.R. 2937
Bouquegneau, J .11. 2274, 2428
Bo~ven, V.T. 2674, 2974
Boyd, C.E. 2927, 3005, 3026
Boyden, C.R. 2275, 2610
Bradley, B.P. 2637
Brafield, A.E. 2976
Braunstein, R.11. 2872
Brehe, J. 2782
Brehm, P. 2938
Brenner, F. J . 2818
Briand, F. 3016
Brinckman, Ii'. E . 2703, 277.8
Brisbin, 1.1..., Jr. 3095
Brkovic-Popovic, I. 2276,
2277
2890
2573
2661
2278, 2279, 2610,
3017
2280, 2665, 3018
2281
2282
2540
2633
2541
2.173
Brc:xTIvick, M. S .
Broenkmv, H. H.
Brmver, J. E .
Brmvn, B.E.
Brown, D.A.
&mvn, E.R.
Brmvn, J .R.
BrmJIl, L.M.
Brmvn, S.C.
Bro~vn, V.M.
Bruland, K.M.
575
2866
-------
Bruland, K. W.
Brungs, ~v.
Brungs, W.A.
Bruns, H.
Bryan, G.W.
2771
2448
2542
2490
2283, 2284, 2285,
2704, 2705, 2975
Bryce, F. 2940
Bubic, S. 2962
Buchardt, B. 2286
Buckley, M. 2631
Buhler, D.R. 2287, 3062
Buhringer, H. 2568
Bull, K.R. 2706
Bulnhe:irr.., H. -P. 2753
Ihrgat, M. 2972
Burgess, B.A. 2891
Burke, R.M. 2967
Burlakava, Z.P. 2800
Purnett, H. 2587
Burrell, J.M. 2381
Burrows, 'i..l. D. 2288
Bursey, C.R. 2772
Putton, K.S. 2773
Buzinova, N. S. 2939
Buzzell, D.H. 2481, 3064
2348
2289, 2290, 2291,
2292, 2309, 2423,
2504, 2877
Calamari, D. 2293
Caldwell, R.S. 2287
Call, D.J. 2645
Callaghan, O. 2281
Canty, W.T. 2909, 2910
Capobianco, J. 3053
Capobianco, J.A. 2954
Capuzzo, J.M. 2294
Cardasis, C.A. 2707
Cardwell, R.D. 2638, 2666
Carlsson, S. 2819, 3019, 3020,
3088
Carney, G. 2478
Carr, M.1. 2666
Carr, R.S. 2456
Carrano, C.J. 2820
Carson, ~J.G. 2533
Carstensen, ~.L. 2677
Cairns, J., Jr.
Calabrese, A.
r~ter, J.G.T. 2821
C--arter, '-l.ll. 2554
rXlsterline, J .L., Jr.
Castilla, J.C. 2543
Caviglia, A. 2544
Ca'\Vthorne, D.F. 2667
Ceccaldi, H.J. 2615
Ceccanti, 11. 2810
CEffiber, ll. 3089
Chalker, B.E. 2822
Chan, KJ1. 2295
Chang, L.H. 3090
Chaplina, AJ1. 2618
Chapman, G.A. 3021, 3022,
3023
Charbonneau, S.M. 2940
Chasteen, N.D. 2891
Chatel, K. H. 3018
Chau, Y.K. 2296, 2694
Chebotina, H.Y. 3087, 3102
Cheng, L. 2297, 2706
Cheng, T.C. 2298, 2494, 2708
Cherry, D. S . 2349
Cherry, R.D. 2538
Cherv:mski, J. 2299
Cheyne, A.R. 2671
ChiD, B. 3024, 3091
Chiou, J. Y. 3113
Chisholm, S,Iv. 2365, 2663,
2949
Chou, C.L. 2669
ChovJ, L. Y. 2282
Chmv, T. J . 2601, 2922, 2923
Christensen, G. 2867
ern, R.C. 2377
Chvojv..a, R. 2263
Chynmveth, D.P. 2545
Cieleszky, V. 2335
Clark, D.L. 2941
Clarke, H.C. 2745
Claus, C. 2962
Clemente, G.F. 2851
Clements, L.C. 2726
Clubb, R.W. 2300, 2301
Collier, R.S. 2290, 2506
C~hvell, R.R. 2415, 2636, 3015
Conacher, H. B . S . 2843
Connell, D.H. 2757
2639
576
-------
Conway, H.L.
2302, 2303, 2357,
2435, 2436, 2546
Coanbs, R. L. 2334
Coanbs, T.L. 2671
Cooper, W.L. 2818
Cornet, D. 3027
Costlow, J.D. 3077
Costlrn~, J.D., Jr.
Coston, L.C. 2304
Couch, J.A. 2709
Coughtrev, P. J. 3025
Cousins, R.J. 2682
Cox, E.R. 2937
Cox, J.A. 2774
Cram, P. 2984
Crear, D. 2805
Cross, F.A. 2547, 2797
Crossland, C.J. 2259, 2304
Crowther, R.A. 29/+2
Cruz, L. L. 2579
Cugurra, F. 2544
Cumbie, P.H. 2248
O.mningham, H.M. 2843
Cunningham, P.A. 2305, 2611
Curtis, E.H. 3089
Cutshall, N.H. 2306, 2307, 2684,
2943
2755
Dane 11 , K. 2308
Danil'chenko, O.P.
Darcy, K. 2454
Davenport, J. 2480, 2710, 2944
Davey, E. H. 2548
Davies, A.G. 3092
Davies, 1. H. 2892
Davies, J.M. 2358
Davies, P.H. 2549, 2776
Davis, C.O. 2357
Davis, J.A. 3026
Davis, R. 2388
Davis, H.R. 2412
Dawson, H.A. 2309, 2504, 2505
Dean, J .M. 2413
de Castro, G.L. 2579
Decleir, H. 2823
DeCoursey, P.J. 2514, 2680
DeFeo, D.L. 2924
2775
defreitas, A.S.H. 2310, 2622
Deitmer, J. H. 2893
Del Carratore, G. 2433
Delcourt, A. 2711
Deldormo, M. 2471
Delhaye, H. 3027
Deshlinaru, O. 3028
Desjardine, R.L. 3033
Dethlefsen, V. 2311, 2312
DeVoe, I JrJ. 2814
De Holf, P. 3029
Diaz, B.H. 2469
Dic1
-------
2473
2795
2642, 2714
Edwards, P.
Edwards, T.L.
Eganhouse, R. P.
Eide, I. 2744
EIFAC 2896, 2897
Eisler, R. 2316, 2317, 2318,
2319, 2408
Elder, J.F. 2320, 2321
El-lIawa\.7i, A.S.N. 3093
Ellgaard, E.G. 2715
Emery, R.M. 3094
Enatsu, T. 2970
Engel, D.W. 2364, 2857
Enk, H. D. 2322
Epplev, R.W. 2359, 2668, 2784
F.rdelvi, L. 2335
Ernst~ W.H.O. 2946
Escalera, R.M. 2388, 2389
Establier, R. 3031, 3036
Eversole, A.G. 2898
Ewell, H.S. 2501
Evman, L. D. 3032
Eynor, L.a. 2255
Eyres, J.P. 2716
Fahy, H.E. 2869
Fales, R. R. 2899
Fallis, B. H. 2770
Fargo, L. L. 2323
Fanner, G.J. 2324
Farrell, M. P. 2811
Farrin..g;ton, J .10!. 2674
FeLix, K.L. 2910
Fendley, T.T. 3095
Ferns, P.N. 2996
Ferrara, ~. 2433
Fiandt, J. 2867
Fiandt, J. T. 2624
Filice, F.P. 2330
Findley, A.H. 2824, 2947
Finley, M. T. 2612
Fischer, P. V . 2499
Flegal, A.R. 2325, 2326
Flaning, R. W. 2323
Flaning, W.R. 2782
Fletcher, G.L. 2551, 2552, 2717,
2718
2551
Fletcher, P.E.
Flos, R. 3099
Flowers, T.J. 2862
2878
2723
2L~8l, 3064
2638
2285
Jr . 2385
2327
2825
2884
2328, 2538, 2670,
2870, 3035
Fox, F .R. 2553
Frazier, A. 2831, 2832
Prancescon, A. 2662
Franco, P.J. 2297
Frank, H.L. 3125
Frank, R. 2642, 2643, 3033
Franzin, H.G. 2678
Fraser, J. 2948
Frederick, R.B. 2329
Freeman, E.A. 2262
Freeman, H.C. 2264, 2462
Freeman, R.F.Il. 2778
Freihofex, V. 2817
Friedman, M.A. 2554
Friedrich, A.R. 2330
Fritz, P. 2286
Fr~, P.O. 2928
Fuhnnan, J.A. 2949
Fujiki, H. 2950, 2951
Fujiki, M. Cotoo) 2950
Fuj inaga, K. 2379
Fujita, H. 3034
Fukai, R. 2617, 2826
Fuller, R.Il. 2331
Punk, w.n. 2476
Fylm, H.J. 2827
Cadd, G.11. 2952
Gagnon, A. 2838
r,aines, L. 2736
Galtsoff, P. S. 2332
Gamble, E. 2674
Gamble, J. C . 2453
Garanina, S.N. 2256
Gardner, D. 2953
Gardner, G. R. 3096
Gardner, H. S . 2608
Garland, T .R. 2458
Flovd, r,.
FolsOI:l, T.R.
Foncannon, P. R.
ForA'1aJ1, D.G.
Forster, G .R.
Forivard, R. B. ,
Foster, P.L.
Foster, R. B.
Foulquier, L.
Fmvler, S.W.
578
-------
Garrard, L.A.
Garrasi, C.
Garside, E.T.
Gast, H. 2448
Gaudette, H.E. 2891
Gaufin, A.R. 2300, 2301
Gauglitz, E.J., Jr. 2352, 2353,
2722
2260
2742
2719
Geddes, H. e. 2417
Geladi, P. 2823
Gentile, J.H. 2849, 3068
Gentner, S.-R. 2333
George, S.G. 2334, 2671
George, H.O. 2839
Georgiadis,~. 2900
Gergely, A. 2335
Gertz, S.H. 2828
Gibson, F. 3009
Gibson, V.R. 2336
Giddings, J. 2720
Giddings, J .1'1. 2644
Gidnev, H.A.J. 2310
Gierd8.y, C. 3112
Giesy, - J.P., Jr. 2337, 2338, 3131
Gilles, G. 2864, 3038
Gilles, R. 2834
Gillespie, P.A. 2765
Gillespie, R. 2339
Gilman, 1'1. F. . 2883
Glandon, R.D. 2613
Glass, G.E. 2252
Glickstein, N. 3097
Glooschenko, H.A. 2954
Glover, H. 2955
Glover, H.E. 2672
Glovna, E.F. 2863
GrouT, D.J. 3127
Gnassi-Barelli, H. 2673
Godmauer, H. B. 2894
Goering, J.J. 2340, 2681, 2792
Gogate, S.S. 2956
Goldberg, E.D. 2674
C,oldman, H. 2829
Gondko, R. 2614
Gonzalez, M.H. 3109
Goodman, B.L. 2696
Gordan, A.G. 2388
(',oreau, T.J.
('-.auld, E.
2721
2292, 2309, 2341,
2342, 2394, 2504,
2779
2671
2414
2555, 2556,
2645
2555, 2556,
2645
2343, 2344, 2345,
2394, 2504, 2557,
2646, 2957
Greve, H. 2487
Grice, G.D. 2336, 2768, 2780
Griffiths, A.J. 2952
Griggs, K.S. 2513
Grj~is, A.~. 2530, 2830
Groroov, \.T. V . 2346
Grosch, D.S. 2611
iliarv, .I.-C. 2831, 2832, 3035
Guerin-Ancev - O. J . 2815
QuAst, H. r,." 2460
Guillard, R.R.L, 2813, 2949
Gupta, A.B. 2958
nuDta, A.S. 2347
nttjJta, P .K. 2599, 2921
Guth, D.J. 2348
ilithrie, R.K. 2349, 2483
rJutierrez, 11. 3031, 3036
Gutknecht, J. 2350
Haga, H. 3101
Haga, Y. 3101
Ham, J .HJJ. 2781
11ale, J.G. 2351
Ha1e'l, L.E. 2369
Hall', A. S. 2352, 2353, 2722
Haller, H. T . 2260
Hamada, H. 2959, 3003
Hamana1~, T. 2558
Hamdy, H.K. 2354, 2450, 2559, 2901
Hamelink, J .1.. 2871
Harrrnan, D.r; ,D. 2645
Hanmons, A. S . 2872
Hand, S.C. 2355
Hansen, N. 2723
Grant, P.T.
Greene, J.e.
Greichus, A.
Greichus, Y.A.
Greig, R.A.
579
-------
Hanson, ~.e. 2782
Harac~e, Y. 2912
Harding, J.p.e. 2356, 2783
Hardman, H.H. 2353
Hardy, L. H. 2547
Hardy, R. 2632
Harms, U. 2568
Harmon, P. 2495
Harms, n. 2315
Harris, E.J. 3132
Harrison, F.L. 2513, 2753
Harrison, P.J. 2303, 2357
Harrison, W.G. 2358, 2359, 2784
Hart, B.A. 3098
Hartman, A.H. 2724
Hartung, R. 2560, 3037
Harvey, E.J., Sr. 2725
Harvey, G. 2674
Hasanen, E. 2761
Haskin, H.H. 3039
Haskin, L.A. 2969
Basnain, A. U. 2902
Hattori, A. 2340, 2792
Hattu1a, H. - L. 2621, 2833, 2919
Haug, A. 2484, 2572
Hazara, J. J. 2281
Hazlett, T.L., III 3011
Healey, F. P . 2846
Heinis, J.J. 2785
Heinze, D.G. 2719
Heisinger, J. F. 2376
He11ebust, J.A. 2540, 2649,
2650
He1mke, P .A. 2969
Helmy, 11. H. 2960
Hemp1e, J.D. 2883
Hendricks. A. e. 2561
Hendricks, D. L. 3015
Hennekev. R. J. 2318, 3006
Henrv- fA.e. 2402
Henzl~r, T.E. 2969
Herman, L. 2707
Herrera, F.e. 2914
l{erricks, E.E. 2562
Hess, C.T. 2449. 3038
Hethe1"ington, J .A. 2961
Hettler, W.F. 2726
Hevert, F. 2853
Hewett, C.J. 2360, 2786
Heyraud, H. 2538, 2670
Hicin, H. 3039
Higgo, J.J.H. 2538
Hilde, S.B. 3059
HildebrAnd, S.G. 2563
Hillman, S. S. 2874
llirota, R. 2950, 2951
Hoar, lv.S. 2745
Hoban, H. 2937
Hodson, P.". 2361, 2362,
2675, 2903
Hodson, R. 2502
HOdson, R.E. 2511, 2765
Holcombe, G.W. 2550, 2574, 3085
Holden, A. V. 2632, 3040
Ho1drinet, H.V.H. 2643, 3033
Ho1m-Hanse, O. 2502
Holmes, R. W. 2357
Holmes, R. H. 2357
Honda, H. 2908
Eoopen, J )I.G.T. 3042
!{Gpcraft, J. 2555
Hoppenheit, !f. 2363, 2564,
2743
Home, A.J. 2321
Hornung, H. 2882
HorO'ivl.tz, A. 2647
Hoskins, K. D . 22fifi
I{oss, D.E. 2364, 2726
Hostetter, H.P. 2773
Houston, A.H. 2402, 2738
HO'ivard, H.B. 2365
HO'ivard-HilliaP1S, e.
HO'iVarth, R. S. 2787
Howse, R.D. 2569
Hoyaux, J. 2834
Hrs- Brenko, l1. 2962
Hud:abee, J.H. 2563, 2728
:fuey, e. 2703, 2728
Huff, J.E. 2872
HU8uenin, J.E. 2905
Hughes, GJ1. 2367, 3099
Hughes, M,R. 290L~, 2929
Huisman, J. 3042
Humnerstone, L.G. 2284, 2704
Humphrey, H.E.B. 2727
Htmer, J .V. 2835
Htmg, T. -c. 2368
Htmt, E. 2867
Huschenbeth, E.
Hutchinson, T.e.
580
2366
2315
2491
-------
Hynes, H.B.N. 2942
Ikeda, S. 2634, 2906, 2931
Ikeda, T. 245L~
Inamasu, Y. 2959, 3003
Inman, C.B.E. 3100
Innes, D.J. 2369
Inoue, Y. (oriteur) 2935
Inoue, Y.(oshino1ai) 2935
Iordachescu, D. 2836
Ireland, H. P. 2963, 2964
Irgo1ic, K.J. 2937
Ishak, H.H. 2370
Ishii, T. 2565, 2634, 2906,
2931
Ishika'V\B, H. 2908
Iskiwawa, T. 2746
Itazawa, Y. 2382, 2383, 2965
Iverson, T.tJ. P. 2703, 2728
Iwaskai, K. 3034
Jackirn, E. 2371
Jackson, G.A. 2676
Jackson, T .A. 3034
Jacob, P.G. 2960
Jacobs, R. 2788
Jan, T.-K. 2529
Janatuinen, J. 2621, 2833, 2919
Janzen, S.A. 3041
Jasper, P. 2966
Jeffries, D.F. 2360, 2786, 2961
Jerme, E.A. 2571
Jermet, J.C. 2754
Jennings, C.D. 2372, 2789
Jensen, K. 304L~
Jerne1av, A. 2729
Jeuniaux, C. 2834
Jewett, K.L. 2703, 2728
Jimenez, M.M. 2969
Jolms, D.M. 2514
Jams on , D.L. 2967
Jolmson, G.D. 2648
Jolmston, R. 2632
Jomston, R.N. 2751, 3117
Jones, A. K. 2404
Jones, J.B. 2873
Jones, N.Y. 2547, 3074
Jones, R.M. 2874
Jorgensen, K. F . 3044
Junk, \.J.J. 2366
Kallqvist, T. 2968
Kania, H.J. 2482
I~ias, G.D. 2915
Kapkav, V. I . 2373, 2815
Y--arapetian, J.". 2907
F:ari, T. 2566
Kariva, T. 3101
Karo1us, J.J. 2341
Karpevich, A.F. 2875
Kassirnata, E.M. 2915
Kato, H. 2558
Katz, H. 2730
Kauranen, P. 2566
Kauw1ing, T.J. 2595
!(ffivasaki, Y. 3101
Kayser, II. 2567
Kazmierczak, A. 2614
Ke3ting, J. 2626
lZeckes , 5 . 2584
Keeling, T. 2811
lZeith, L. 2281
Kelley, E. 2594
Kelly, 11. 2514
Khailav, I~J1. 2800
Khalil, S.P.. 7370
Khandekar, R.N. 3045
I\hlebovich, "'iT.", 2701, 2790
Khobot 'vev. V.G. 2373
Khristofor~va, n.K. 2374
Y-idder, G.B. 2375
Kikuchi, T. 2908
Kil~, S.5. 3046
yJrrt, J .H. 2376
villn, K.C. 2377
Kimura, I. 2902
Kimura, Y. 3069
King,11.J. 2552, 2718
Kirscmer, L.B. 2766, 2767
Ki tarruri , 5. 2606
Klein, A.E. 2378
Kling, H. 2631
Klopfer, D.C. 3094
Knauer, G.A. 2771
Knight, L.A., Jr. 2725
Knowles, S.C. 2799
Kobayashi, N. 2379
Koeller, P. 2380
Koeller, P.A. 2791
581
-------
Kohler, L. 277 4
Koike, I. 2792
Kolar, D.J. 2688, 2982
Ko1i, A.K. 2381, 2909, 2910
Kondo, I. 2746
Korda, R. J. 2969
Y-J)rvakova, H. D. 2374
Koshikawa, T. 3002
Kotani, H. 2970
Kott, C.L. 3046
Kova1eva, N.M. 2701
Kowa1czuk, J.G. 2835
Koyama, J. 2382, 2383, 2965
T
-------
L'vova, T.G. 2790
L'vovskaya, N.R. 2255
MacFarlane, L.R.
Hac Innes , J. R.
2495
2291, 2342, 2194,
2423, 2877
Macka, w. 3048
Hackay, N. J . 2263
NacKenzie, C. L., Jr. 2557
l'1ackenzie, F.T. 2395
MacLean, S. A. 2425
MacLeod, M.G. 2396, 2397, 2735
Madgwick, J. 2572
Madrid, E. 2914
Magee, R.J. 2658
~fuki, T. 3069
Malizia, A.A., Jr. 2715
lfuncy, K.H. 2467, 2545
Mangi, J. 2736
Manley, A. 2944
Manlove, M.N. 3095
Manly, R. 2839
Hanson, J.M. 3049
Mansuri, A. P. 3086
lfurais, J.F.K. 3107
Marchetti, R. 2293, 2737
1vfarchyulenene, D. P . 2398
Marchyulenene, E.-D.P. 3108
Marcs tran , V. 2308
Marquenie-van der Werff, !'f.
113.rquis, R. E . 2677
~~rshall, B. 2556
l~shall, J.S. 3066
Martin, D.F. 2777, 3109
Martin, J.H. 2326, 2388, 2399,
2573, 2674, 2771
Martin, J. -L.M. 2615
Martin, M. 2399
Martin, M. H. 3025
Martin, P.H. 3050
Marvan, P. 2752
Massaro, E.J. 2339
Hasson, H. 2832
Mastrianni, vI. 2594
Mathis, B.J. 2322
Matsuhashi, M. 3010
Matsunaga, K. 2400
2946
}1attey, D.L. 2438
Hatthiessen, P. 2976
Maximov, V.N. 2977
Hay, 1{.C. 2598
~~yes, R.A. 2401, 2699
11avzel, K. 2677
HcBride, B.C:;. 2795
McCafferty, H. P . 2520, 2630
McCanless, J.B. 2388
HcCarty, L. S. 2402, 2738
IfcClary, E.B. 2381
I1cComick, J. H. 2542
l1cDanald, R. C . 2522, 2523
11cFarlane, ~.A. 2678
!1cFarlane, R.H. 3030
l1cIntosh, A. 2520. 2629,
2630, 2859.
2930
2401, 2627,
2648, 2688,
2699. 2982,
3110
25U
2403, 2550, 2574
2310, 2622
2689
2490
2404
2613
2405
2387
3094
2968
2406, 2407,
2477, 2575,
2595
Hears, H. C. 2408
Heier-Brook, C. 2576
Meisch, H.-V. 2409, 2577,
2578
Helhuus, A. 2616
Hellinger, J).L. 2302
HelsCJ['1, S. 2744
!1enasveta, P. 2410
Henzel, D.H. 2780
Her anger, J. C . 2843
Herlini, H. 2411, 2651, 28QZ,
29]8
IfcIntosh, A. T,T.
HcIntyre, D.R.
HcKim, J .11.
HcY-innon, A.E.
~1cJ~iLrl.8ht, D.H.
HcLane, }1.A.R.
McLean, R.O.
McNabb, C.D.
HcNurney, J.M.
McPhPISon, B.P.
HcShRne, H.C.
Headows, B.S.
Hearns, A.J.
5~3
-------
2557
2711
2412, 2413, 2878
2739
Merrill, A. S.
Mestre, J.C.
Hiddaugh, D. P.
Miett:inen, J .K.
Hiles, \'1. 2843
Miller, D. S. 2471
Hiller, J. C. 2679
Miller, J.E. 2290, 2291
Miller, H. E. 2414
Hills, A. L. 2415, 2636, 3051
Hills, B.J. 2416
l1ilne, R. S. 2840
Hirarnand, P. 3051
Mirkes, D..z. 2680
Hisra, B.N. 2619
Mitchell, B.D. 2417
~litchell, N.T. 2961, 2979
Hitra, R.S. 2980
Mitshashi, S. 2746
t'fiyama, T. 2/+96
Hol-Krijnen, J. C.M.
Holler, H. 2740
MOller, V.W. 2879
Montganery, J. R. 2579
Moore, 11. N. 2580
Hoore, W., Jr. 2749
furaitOll-ApostolopOlllOll, M.
2880
M:>rel, F .H.M.
2809
2660, 2689,
2813, 2841
Morel, N.M.L. 2689, 2841
Morgan, D. 2845
Morgan, J.J. 2676
tbrgan, R.P., II 2860
Horgan, W.S.G. 2258
Morishita, H. 2652
Morrison, G. 2371
~bss, J.L. 3052
~DUssal1i, E.L. 2765
Hudroch, A. 3053
Hukherj ee, S. 2418
fulhern, B.H. 2640
Mullen, T.L. 2796
M.1ller, G. 2981
MUnda, I.M. 2419, 2420, 2741,
2742
2627, 2699.
tm-phy, B.R.
2982, 3110
ttITphy, P.J. 2501
lfurphy, S.D. 3008
lfurrav, C.N. 2617, 2743
lUTton, R.K. 2706
~1urz:ina, T .A. 2618
Hyhre, 1(. 2989
t1ylclestad, S. 2616, 2744
Nagahama,Y. 2744, 2745
Naidu,J .R. 2306, 2307, 2943
Nair, \T. 2281
Nakahara, H. 2746
Nakahara, H. 2603, 2797
Nabmura, R. 2421, 2509,
2510, 2603,
2605
1~akano, M. 3003
Nakazmva, S. 2747
Narrminga, H. 2422
Nathan, A. 3056
Natoch:in, Y.V. 2701, 3104
!~ealler, E. 2543
Neary. B.P. 2270
Neff', . J .11. 2581, 2712
Neiheisel, 'I',(J. 2542
Nelson, B. 2646
Nelson, B.A. 2344
Nelson, D.A. 2291, 2423
Nelson, D .M. 2681
Nestler, J. 2424
Nevissi, A. 2852
N~vkirlc, G. 3054
Nev.raan, H. IV. 2425
Nei'InaIl, R.D. 2937
Nicholas, vJ. L. 2821
Nichols, KJ1. 2748
Niculescu, S. 2836
Nieboer, E. 2592
Nielsen, S.A. 2426, 3055,
3056
Nifontova, ~tG. 3111
Nimno, D . R. 2427, 2582
Nishigaki, S. 3069
Nitkrnvski, H.F. 2459
Noel-Lambot, F. 2428, 3112
Nordlie, F. G . 2842
584
-------
Noro, r. 2798
NorstrOOl, R.J. 2310
Noyes, n.R. 2354
Nuorteva, P. 2761
Ochiai, S. 3069
Ociepa, A. 2983
O'Conner, J.S. 2429
Oduleye, S.O. 2430
Oertti, C. U. 3059
o 'Flaherty, E.J. 3049
Ogino, C. 3057, 3058, 3113
~i, H. 2653, 3071
Oguro, C. 2920
0' Hara, R. K. 2869
Oikari, A. 2583
Okabe, H. 2499
Okazaki, R.K. - 2431
01afsen, J. 2989
Oleynik, T. L. 2255
Olson, K.R. 2682
Olsson, M. 2432, 2881
O'Neill, D.J., Jr. 2319
OoshiIna, Y. 2653
Oostdam, B.L. 2960
Oregioni, n. 2826
Osborn, D. 2706
Oshida, p.S. 2406, 2595
Osterberg, C. 2584
Ostrom, KJ1. 3114
Otsuka, Y. 2528
Overnel1, J. 2683
Owen, J )1. 2925
Ozhegov, L. N . 2384
Paasivirta, J.
2621, 2833,
2919
2608, 2799
2585
Pace, F. 2433
Paffenhofer, r;.A.
Pagenkopf, G. K.
Paine, D. 3030
Pa1mer, J. B. 2434
Panigrahi, A.K. 2619
Pankow, J. 2736
Papadopou1ou, C.
Parchevskii, V. P .
Park, C K. 2988
Parker, J.1. 2302, 2435, 2436
2915
2800
Parker, P .1.. 2671~
Parkin, D. T . 2948
Parsons, J.R. 2380
Parsons, Y.R. 2665, 3018
Parvaneh, IT. 2437
Paschoa, A.S. 3115
Pascoe, D. 2438, 2984, 3084
Paskins-Hllr1burt, A.J. 271+9
Patel, B. 3116
Patel, G.B. 2750
Patel, S. 3116
Patrick, F .11. 21~39. 2801
Patrick, R. 2586
Patterson, C. 2440, 2587
Paul, A.C. 2985
Paul, H. 2751, 3117
Pawar, S. 3116
Pavne, T.R. 2638
Payton, P .n. 3059
Pearcy, IV. r;. 2306, 2307,
2684, 2731,
2943
2441
2843
2442, 2443.
2588, 2632,
2844, 2916,
2961, 2986,
2987, 3060,
3061
PerLmutter, A. 2888, 2998
Perrv, H.C. 2640
Pesando, D. 2673
Pesch, C.E. 2845, 2849
Pesch, G. 2444
Peters, D.S. 2726
Phelps, D.K. 2389
Phillips, D.J.H. 2445, 2446,
2447, 2589
3062
2448
2985
2671
2892
2388
2590
2911
2846
Pearse, J.B.
Penrose, H. Jl.
Pentreath, R.J.
Phillips, G.R.
Pickering, Q.
Pil1ai, K.C.
Pirie, B.J.S.
Pirie, JJL
Pirie, R.G.
Pirt, S.J.
Piuze, J.
Planas, D.
5~5
-------
Po 1 ikarpov, r:;.G.
Polo, B. 2662
Popovic, M. 2276, 2277
Pott, RJ1. 2645
Potts, G.W. 2285
Pozzi, G. 2411, 2802, 2978
Prabhu, N.V. 2450, 2559
Prater, B.L. 2591
Presley; B.J. 2604, 2647, 2656
Pribil, S. 2752
Price, A.H. 3038
Price, H.B., II 2449
Price, M. 2579
Protasowicki, M. 2983
Prosch, R.D. 2847
Pugh-Thanas, H. 2716
Purushan, K. S . 3120
Raa, J. 2989
Rade, H. 2743
P~i, L.C. 2793
Rajendran, A. 3118
Ramamoorthi, K. 2732
Ramamoorthy, S. 2451, 3016
Ramonda, G. 2864, 3083
Ramprashad, F. 2685
Rand, G.t1. 2434
Randall, D. J . 2840
Ranta, W. B. 2592
Rao, K. R. 2553
Rao, T.S.S. 3120
Rapley, H.A. 2643
Ravera, O. 2803
Rawlence, D.J. 2452
Ray, S. 2593
Raymond, K.N. 2820
Reed, R.J. 2910
Reeve, M.R. 2453, 2454, 2768
Remvoldt, R.E. 2594
Reid, S.H. 2267
Re:imer, A.A. 2654
Remer, R. D. 2654
Reiniger, P. 2848
Reish, D.J. 2406, 2455, 2456,
2595, 2849
2339
2359, 2784
Reisine, T.
Renger, E.H.
2398
Renzoni, A. 2865
Reynolds, B. 2444
Pillo, S. 2988
Pd.card, J.-7'1. 2972
Rice, D.H., Jr. 2753
lUc1~rd, H.H. 2596
Rigby, R.A. 2582
Ri.kr1enspoel, R. 2748
Riley, J.P. 2295
Pd.sebraugh, R.W. 2674
Pitter, J.A. 2324
Pitter, H. 2847
FDald, T. 2484
"Roberts, E. 3063
Robertson, D.R. 2850
Rohertson, J.D. 2457
Robertson, \IT. 2674
~obinson, A.V. 2458
Robinson, K.R. 2917
RDbohn, R.A, 2459
Rodsaether, !1.C. 2989
Roegge, 1'1. Ao 2460
Rogerson, P. 2444
Rolfe, G.L. 2754
Reneo, M. 2673
Raneril, H.G. 2461
Ronald, K. 2462, 2685
Roos, A. 2822
Roqueplo, C. 2972
Rosenber~, B. 2762
Rosenberg, R. 2463, 2755
Rosenthal, H. 2312
%ssi, L.C. 2851
Rossi, 8.S. 2595
Roth, I. 2882
Roth, L.A. 2750
Rozhanskaya, L. I .
Razing, N. 2858
Rueter, J.G. 2841
Rukhadze, Y.G. 2373
Rutledge, W.P. 2460
Ryndina, D. D. 2464, 2620
Saboski, E.M. 2804
Sachs, K. 3076
Saeki, K. 2971
Saenko, G.N. 2374
2464
5R6
-------
Saifullah, S.~f. 2597
Sainsburv, H. 2254, 2700, 2936
Sakamoto, S. 2918, 3028, 3119
Saliba, L. J . 2465
Sanborn, E. 2666
Sanders, J .G. 2756
Sandi, E. 2940
Sandu, S.-S. 2466, 2910
Sankaranarayanan, V.N. 3120
Sano, K. 2950
Santaroni, G. 2851
Santerre, H. T. 2598
Santiago, R.J. 2388
Sarai, Y. 2746
Sargent, J.R. 2925
Sarkka, J. 2621, 2833, 2919
Sarsfield, L.J. 2467
Sartory, D. P . 2468
Sasayama, Y. 2920
Sasner, J. J . 2294
Sastry, K.V. 2599, 2921
Sato, M. 2634
Say, P.J. 2469, 2470
Scaife, B.D. 3098
Schau1e, B. 2587
Schell, W.R. 2852
Schipp, R. 2853
Schmidt, K. 2736
Schmidt, R.L. 2990, 2991
Schmidt-Nielsen, B. 2471, 2474
Sclmeider, E. 2674
Schneiderman, G.S. 2458
Schreck, C.B. 2686
Schrenk, W. T . 2386
Schue 1 , H. 2707
Schu1z, D. 2854
Schu1z-Ba1des, M.
Scott, J.S. 2472
Seeley, R.J. 2888, 2998
Seeley, V.A. 2998
See1fuger, V. 2473
Seibert, D.L.R. 2502, 2503,
2808
2388
2616
2616
2440, 2587
2992
Sei.ss1ie, G.A.
Seip, H.H.
Seip, K.L.
Settle, D.
Shaffer, P. L. 3000
Shah, S.11. 2956
Shahmoradi, A.H.
Shanks, V. 2809
Shapiro, M.A. 2757
Sharpe, ~1.A. 2622
Shati1a, T.A. 2995
Sheffy, T. B. 2994
Shcherban, E. P . 2993
Sheline, J. 2471, 2474
She1puk, C. 2646
Shen, A.C.Y. 2600
Shephard, K. 2855
Sheppard, C.R.C. 2475
Sheppard, .I.e. 2476
Sheppard, J .M. 2582
She~od, H. J . 2406, 2407,
2477
Shiber, J. 3121
Shiber, J .G. 2995
Shid1ovsklYa, N .A. 2373
Shimamura,. Y. 3069
Sh:imojo, N. 2950
Shirmyo, A. 2970
Shiroyama, T . 241!+
Shore-, R. 2478
Shriner, C.R. 2872
Shultz, C.D. 2805
ShlUTIWay, S.E. 2479, 2480
Shurin, A. T. 2875
Shutt1ev~rth, T.J. 2778
Sidwell, V.D. 2481, 3064
Siebers, D. 2758
Si~, C.F. 2482
Sikes, C.S. 3065
Silver, S. 2941, 2966,
3008
Sllrikiss, K. 2855
Snno1a, L.R. 2655
Slinpson, T.L. 3114
S:ims, R.R., Jr. 2656
Sinclair, T. 2281
Singer, P. C . 2856
Sinp,h, H. 3066
Singh, K. 2623
Singh, S .H. 2996
Singleton, F. L. 2349. 2!~83
2907
SP, 7
-------
Sin'kov, N.A. 2374
Sin1ey. J.R. 2776
Siriyong, R. 2410
Sivalingam. P.H. 2759. 3122
Sivieri, S. 2810
Skipnes, O. 2484
Skoryna, S.C. 2749
Smart, RJ1. 3067
STLi..th, A. L. 2481
anith, C. H. 2449. 3038
anith, K.E. 2932
Smith, R.I. 2485
Smith, T.G. 2687
Snyder, C.B. 2922, 2923
Sodergren, S. 2997
Solly, S.R.B. 2809
Saner, E. 2487
Somero, G.N. 2601, 2922, 2923
Sormtag, N. C. 2487
Soos, K. 2335
Sorenson, E.M.B.
Sosnowski, S.L.
Spaargaren, D.H.
Spear, P.A. 3123
Spehar, R.L. 2542. 2624, 2924
Spencer, K. 2940
Speran, z3. A. H. 2998
Sperling, K.-R. 2363
Spewak. R. 3063
Sprague. J.B. 2787
Spr~gthorpe. S. 2451
Spry, D.J. 2362. 2675, 2903
Squibb. K.S. 2682
Squires, H. R. 2843
Stadtman. T. C. 21373
Stahl, S. 2999
Stall. J. 2594
Stancyk, S.E. 3000
Stara. J.F. 2749
Steele. R. 2371
Steen, J.B. 2989
Stehlik, G. 3048
Stendell, R.C. 2612
Stephan, C.E. 2542
Stephenson, H. D. 2399
Stern, S. 2625
Stevens, D.G. 2488. 3023
2657
3068
2861
SteIVart, G. L. 2266
Stewart, J. 2806
StBvart, J'G' 2489
Stickel, L.F. 2tj.90
Stickel, 'J.B. 2490
Stickle. ~'J. B. 2355, 2824~ 2947
Stobbart, R.B. 2626
Stockton, R. 2937
Stoffer. J.O. 2386
StO-FfWl, H. 2395
Stokes, G . N . 2542
Stokes, P. 2491
Stokes. R.}1. 2287
St:oneburn.er, n.L.
Stotzkv, G. 3QJ.4
Strain, B.R. 2913
Strvker, S. 3063
Sturesson, U. 2492, 2760
St~1gall, T. 2478
Suckcharoen, S. 2761
Suffet, I.H. 2828
.,
Sullivan', r:.TJ. 2493
Stlllivan, J.F. 2627, 2688
Sullivan. J .K. 2602
Sullivan, J. T. 2tj.94 , 2708
Sumitra-Vij ay~aghavan 3U8
Sumnerfelt, Tpt. 2498
Stmda, 1V.~. 2857, 3001
Suter, P. 2416
Sutterlhl, A.NT.
Suttle, A.D., Jr.
Suzuki, H. 2565
Suzuki, 1. 2692, 2693
Suzuki, 'T'. 2496
SUzWci, Y. 2421, 250Q, 2510,
2603, 2605
2689
2596
21312
2188
2L~97
2807
2495
3Q59
Sl"vallmv, K. C.
S1:veany, H. A.
~veenev, BJ1.
".
Swift, D .J?
S~Tlvester, A.J.
Tabata, T.
Tafnnelli, R.
Tap.;atz, ~1. Eo
Tami, Y.
Ta.iima, S.
2500
2498
3002
3041
2950
588
-------
Takabatal~e, E. 3034
Takada, II. 2652
Takahashi, 1'1. 2502, 2808
Takashima, F. 3113
Takeda, H. 3057
Takeda, n. 2659, 3003
Takeuchi, '"r. 2499
Talbot, V. 2658
Tarmra, Y. 3069
Tanaka, Y. 2749
Tarao, R. 2500
Teeny, F.H. 2352, 2353, 2722
Telek, r;. 2388
Ter~ar, r;. J . 2501
Terho, K. 2794
Tessaro, S.V. 2462
Tevlin, H.P. 3004
Thomas, W.R. 2502, 2503, 2808
Thanpson, r;.~v. 2319
Thanson, A. J. 2925
'Thuotte, R.U. 2857
Thurberg, F.P. 2292, 2309, 2394,
2504, 2505, 2506
Thurston, J. 2579
Till, J.E. 3124
TiL~, D. 3046
Tilton, R.C. 2762
Timourian, H. 2507
Ting, R.Y. 2388, 2389
Tobia, }1. 3002
Tomassini, F .D.
Tanida, T. 3003
Tompkins, T. 2272
Topping,~. 2508
Tonna, A.E. 2763
Towill, L.E. 2872
Towle, D.Tv. 2883
Tmvnes, 1-1.1'1. 3070
Toyama, C. 2496
Trabalka, J .R. 3125
Traba1ka, '"r .R. 3032
Tracev, S. 3063
Trefrv, J.R. 2604
Tranbal1a, H.H. 2926
Ttucco, R. 3016
Tsujita, T. 2558
Tucker, C. S . 2927, 3005
2592
'::l1clcer, P. . T~ . 2504
TuŁt, S .,1. 2610
Turner, J. C . 2809
Turner, p. 2736
'I'11runina, N.". 2.173
'Pasa, ,T .F:. 2715
Ueda, T.
2421, 2509, 2S10,
2605, 2659, 2959,
3003
TJEmJra, K. 2528
Ui, J. 2606, 2713
lbehara, S. 3071
TInIn, H.Y. 2870
TJTIni, C.K. 2956
TJnsa1, M. 3051
TJntaltVa1e, A.G. 2697
TTthe, .T.F. 2462, 2669
Uysal, R. 2705
TT2T1atl11, J .R. 2734
Vaas, K.:r. 2858
vaccaro, R.F. 2511, 2765
Van Den Brock, TI.L.F. 2521
Van lirieken,~. 2823
Van Horn, H. 3126
VanLoon, J .C. 2512
I larmuc chi , C. 2810
Van Hormhoudt, A. 2615
Varanasi, U. 3127
'las, D. 2876
lJassilaki-Gr:i.mani, H.
Vattuone, r;.1'1. 2513
'le11a, H.r;. 2tf65
Venkataramiah, A. 2569
Vernherg, H.B. 2514, 2680
Ilersnoor, E. 2948
\Tetter, R.J. 2837
~linogradrnr, r; .A. 2790
,naoonck, A. 2823
vlasb1C111, A.G. 2858
,lo1cani, B.E. 2273
von Brockel, K. 2911
'lover, R.A. 3003
2830
Hafar, H.\l.H.
Hai,;~ocl, K. G .
3118
3007, 3128
589
-------
Wa1ach, M. 2590
Walker, G. 2515
Walker, R. L. 2791
Wa11acp-, G.T. 2791
Walter, A. 2929
Walter, KA. 2453, 2454
Ward, P. 2706
Ware, G.C. 2497
Hashburn, E. 3121
Washutt1,- J. 3048
Hatchmaker, G. 2507
Haybrant, R.C. 2871
Weber, L.J. 2535
Heige1, H.P. 2516
Weinstein, N.L. 3129
Iveis, J.8. 2517, 2518, 2519,
2528, 3072
Heis, P. 2518, 2519, 2628
Heiss, A.A. 2941, 3008
l>Jeitz, W.E., Jr. 2723
Wentse1, R. 2520, 2629, 2630,
2859. 2930
HentwJrth, C. E., Jr. 3006
Wenz1off, D.R. 2343, 2345, 2557,
2646, 2957
2689
3073
2312
Westall, J.C.
\ves tennan, A. G.
Westernhagen, H. V.
Wetzel, M.J. 2405
Wharfe, J.R. 2521
Wheeler, S.R. 2354, 2901
vlliitaker, J. 2631
White, A.W. 3130
Whi te , W. \-1; 2501
Whitfield, B.L. 2872
1,,1hitmore, R. 2910
Whittle, K.J. 2732
1
-------
Young, A.M.
Yaung, T).R.
3011
2406, 2529, 2575,
2642, 2714
3009
3012
2863
Young, r.r;.
Young, H.L.
Yousef, Y.A.
Zaba, B.N. 3132
7afiropou1os, n. 2510, 2830
Zaleski, L. 2272
Zanders, I. P . 2914
&~uke, G.-P. 2531
Zavodnik, N. 2532
Zdanowicz, V. S . 2557
ZllnneDman, D.D. 2579
Zingaro, TJ...A. 2937
Zitko, IT. 2533, 2534
Zook, E.G. 2669
591
-------
TECHNICAL REPORT DATA
(Please read b~s.lructions on the reverse before completing)
1. REPORT NO. 12. 3. RECIPIENT'S ACCESSIO~NO.
EPA-600/3-79-084
4. TITLE AND SUBTITLE 5. REPORT DATE
Fourth Annotated Bibliography on Biological Effects of August 1979 issuing date
Metals in Aquatic Environments (No. 2247- 3132) 6. PERFORMING ORGANIZATION CODE
7. AUTHOR IS) 8. PERFORMING ORGANIZATION REPORT NO.
Ronald Eisler, Richard M. Rossoll, and Gloria A. Gabour
9. PERFORMING ORGANIZATION NAME AND ADDRESS 10. PROGRAM ELEMENT NO.
Environmental Research Laboratory-Narragansett, RI 18 A022; l6AAT!3l
Office of Research and Development 11. CONTRACT/GRANT NO.
U. S. Environmental Protection Agency
Narragansett, Rhode Island 02882
12. SPONSORING AGENCY NAME AND ADDRESS 13. TYPE OF ~EPORT AND PERIOD COVERED
Environmental Research Laboratory-Narragansett. RI in-holise
Office of Research and Development 14. SPONSORING AGENCY CODE
U.S. Environmental Protection Agency EPA!600/05
Narragansett, Rhode Island 02882
15. SUPPLEMENTARY NOTES
16. ABSTRACT
Ti tles of 886 technical articles are listed on the subject at toxicological i'
physiological and metabolic effects of stable and radio-labelled chemical speci~s
of metals and metalloids to marine, estuarine, and freshwater flora and fauna.
Each reference is annotated and subsequently indexed by metal, by taxa, and. by
author.
17. KEY WORDS AND DOCUMENT ANAL YSIS
a. DESCRI PTORS b.IDENTIFIERS/OPEN ENDED TERMS c. COSATI Field/Group
Metals, Cations, Salinity, Water Pollution, Aquatic Invertebrates, 6F
Toxicity, Metabolism, Bibliographies, Aquatic Vertebrates, 8A
Radioactive Isotopes, Fishes, Aquatic Heavy Metals, Trace 8E
Animals Metals, Elemental 13B
Composition
18. DISTRIBUTION STATEMENT 19. SECURITY CLASS (This Report} 21. NO. OF PAGES
Release to public Unclassified 598
20. SECURITY CLASS (This page) 22. PRICE
Unclassified
EPA Form 22211-1 (9-7J)
592
- us GQVERNMENTPRINTINGOFFICE 1979 -657-060/5377
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