Microcosms aquatic

Correll, D.L. and T.L. Wu. 1982. Atrazine toxicity to submersed vascular plants in simulated estuarine microcosms. Aquat. Bot. 14 151-158. 

Traas TP, Janse JH, Aldenberg T, Brock TCM. 1998. A food web model for fate and direct and indirect effects of Dursban 4E (active ingredient chlorpyrifos) in freshwater microcosms. Aquat Ecol 179-190. 

Wellman P, Ratte H-T, Heimbach F. 1998. Primary and secondary effects of methabenz-thiazuron on plankton communities in aquatic outdoor microcosms. Aquat Ecol 32 125-134. 

Altmann, D., Stief, P., Amann, R., and de Beer, D. (2004). Distribution and activity of nitrifying bacteria in natural stream sediment versus laboratory sediment microcosms. Aquatic Microbial Ecology... 

Schwalbach, M. S., Hewson, L, and Fuhrman, J. A. (2004). Viral effects on bacterial community composition in marine plankton microcosms. Aquat. Microb. Ecol. 34, 117—127. 

Holm HW, Kollig HP, Pa5me WR Jr, et al. 1983. Fate of methyl parathion in aquatic channel microcosms. Environ Toxicol Chem 2 169-176. 

In the quest for better methods of establishing the environmental safety (or otherwise) of chemicals, interest has grown in the use of microcosms and meso-cosms—artificial systems in which the effects of chemicals on populations and communities can be tested in a controlled way, with replication of treatments. Mesocosms have been defined as bounded and partially enclosed outdoor units that closely resemble the natural environment, especially the aquatic environment (Crossland 1994). Microcosms are smaller and less complex multispecies systems. They are less comparable with the real world than are mesocosms. Experimental ponds and model streams are examples of mesocosms (for examples, see Caquet et al. 2000, Giddings et al. 2001, and Solomon et al. 2001). The effects of chemicals at the levels of population and community can be tested in mesocosms, although the extent to which such effects can be related to events in the natural environment is questionable. Although mesocosms have been developed by both industrial... 

Microcosms are laboratory systems generally consisting of tanks such as fish aquaria containing natural sediment and water or soil. In those that have been most extensively evaluated for aquatic systems, continuous flow systems are used. In all of them, continuous measurement of evolved... 

Huckins JN, JD Petty, MA Heitkamp (1984) Modular containers for microcosm and process model studies on the fate and effects of aquatic contaminants. Chemosphere 13 1329-1341. 

Wilson CJ, Brian RA, Sanderson H, Johnson DJ, Bestari KT, Sibley PK, Solomon KR (2004) Structural and functional responses of plankton to a mixture of four trtracyclines in aquatic microcosms. Environ Sci Technol 38 6430-6439... 

Sugiura, K., M. Goto, and Y. Kurihara. 1982. Effect of Cu2+ stress on an aquatic microcosm a holistic study. Environ. Res. 27 307-315. 

Krantzberg, G. and P.M. Stokes. 1985. Benthic macroinvertebrates modify copper and zinc partitioning in freshwater-sediment microcosms. Canad. Jour. Fish. Aquat. Sci. 42 1465-1473. 

Brockway, D.L., P.D. Smith, and F.E. Stancil. 1984. Fate and effects of atrazine in small aquatic microcosms. Bull. Environ. Contam. Toxicol. 32 345-353. 

Stay, F.S., D.P. Larsen, A. Katko, and C.M. Rohm. 1985. Effects of atrazine on community level responses in Taub microcosms. Pages 75-90 in T.P. Boyle (ed.). Validation and Predictability of Laboratory Methods for Assessing the Fate and Effects of Contaminants in Aquatic Ecosystems. ASTM Spec. Tech. Publ. 865. American Society for Testing and Materials, 1916 Race Street, Philadelphia, PA 19103. 

Maund SJ, Williams P, Whitfield M et al (2009) The influence of simulated immigration and chemical persistence on recovery of macroinvertebrates from cypermethrin and 3,4-dichloroaniline exposure in aquatic microcosms. Pest Manag Sci 65 678-687... 

Endrin released to water will adsorb to sediments or bioaccumulate in fish and other aquatic organisms. Both bioaccumulation and biomagnification of endrin were reported to occur in an aquatic laboratory microcosm system (Metcalf et al. 1973). In terrestrial ecosystems, endrin transformation products (endrin ketone, endrin aldehyde, and endrin alcohol) have been measured in plants grown on endrin-treated soil (Beall et al. 1972 Nash and Harris 1973). 

Aquatic Microcosms for Ecological Assessment of Pesticides. Wintergreen, Virginia, 7 to 11 Oct 1991. Published by SETAC, 1992. 

K. R. and Mabury, S.A. (2004) The aquatic persistence of eight pharmaceuticals in outdoor microcosms monitored by HPLC-UV and LC-MS-MS using electrospray ionization. Environ Toxicol Chem, 23, 1431-1440. 

Paul, J. H. David, A. W. (1989). Production of extracellular nucleic acids by genetically altered bacteria in aquatic-environment microcosms. Applied and Environmental Microbiology, 55, 1865-9. 

Aquatic Pseudomonas sp. B13 (degrades 3-chlorobenzene) 28 Intact sediment cores with overlaid water column GEM survived in sediment throughout the length of study. Microcosm was healthy, and presence of GEM did not affect total numbers of bacteria present. GEM enhanced the rate of 3-chlorobenzoate and 4-methylbenzoate added to sediment. Pipke et al. (1992)... 

Pipke, R., Wagner-Dobler, I., Timmis, K. N. Dwyer, D. F. (1992). Survival and function of a genetically engineered Pseudomonad in aquatic sediment microcosms. Applied and Environmental Microbiology, 58, 1259-65. 

THE SCIENCE OF ECOLOGY emerged at the turn of the last century and brought with it the experimental approaches that were already central to the study of physiology (1-3). Manipulations of whole aquatic ecosystems— excluding aquaculture, which dates back 2500 years (4)—developed more slowly, mainly because of difficulties associated with increased biotic complexity and physical scale in larger systems. One technique initially used to overcome the problems of complexity, scale, and replicability was creation of controlled microcosms that embodied a more or less natural representation of the whole system (5, 6). 

Aside from adding defined compounds, experimental additions of natural DOM mixtures suspected to vary in lability have helped test ideas about the contribution of various DOM sources to aquatic ecosystems. In a nice example using manipulation of natural DOM sources, Battin et al. (1999) used flowthrough microcosms to measure the relative uptake rates of allochthonous and autochthonous DOM by stream sediments. They documented greater than fivefold differences or more in uptake and respiration, depending on whether the DOM was extracted from soil or periphyton. Moreover, they were able to show, via transplant experiments, several cases where prior exposure to a particular source of DOM increased the ability of that community to metabolize the DOM supplied. There appears to be some preadaptation of microbial catabolic capacity when these stream biofilms were re-exposed to a familiar type of DOM. Similarly, the response of heterotrophic bacteria to carbon or nutrient addition was greatest when the source community was particularly active (Foreman et al., 1998). Kaplan et al. (1996) showed that fixed film bioreactors, colonized on one water source, were unable to rapidly metabolize DOC in water from another source. 

Thingstad, T. F., M. Perez, S. Pelegri, J. Dolan, and F. Rassoulzadegan. 1999b. Trophic control of bacterial growth in microcosms containing a natural community from northwest Mediterranean surface waters. Aquatic Microbial Ecology 18 145-156. 

Laboratory toxicity tests have been developed and conducted over the past decades to demonstrate adverse effects that chemicals can have on biological systems. Along with other complementary tools of ecotoxicology available to measure (potential or real) effects on aquatic biota (e.g., microcosm, mesocosm and field study approaches with assessment of a variety of structural and/or functional parameters), they have been, and continue to be, useful to indicate exposure-effect relationships of toxicants under defined, controlled and reproducible conditions (Adams, 2003). 

Janati-Idrissi, M., Guerbet, M. and Jouany, J.M. (2001) Effect of cadmium on reproduction of daphnids in a small aquatic microcosm, Environmental Toxicology 16(4), 361-364. 

Traunspurger, W., Schafer, H. and Remde, A. (1996) Comparative investigation on the effect of a herbicide on aquatic organisms in single species tests and aquatic microcosms, Chemosphere 33 (6), 1129-1141. 

Aquatic plants and fish. Duckweed rapidly accumulated (r4C)-fenitrothion from the water column and maximum concentrations were observed after 5 to 10 days post-treatment in both years (Table III). The levels observed at 5 days represented concentration factors (BCFs) of 754 and 688 in shaded and unshaded exposures, respectively (Year 2), based on total radioactivity in water and plants. Concentrations in duckweed decreased to <10% of the maximum by 35 days each year. Levels of radioactivity in the plants were not significantly different in shaded and unshaded conditions. This differs from results of Weinberger et al (4) who observed 3-fold greater concentrations of ( 4C)-fenitrothion in Elodea densa in field microcosms under lighted compared to darkened conditions. Duckweed did not grow well under shaded conditions and by 17 days the density of the plant was about 10% of that in the unshaded pond. 

Sediment estimated first-order t,/2 = 23-69.3 d from biodegradation rate constant k = 0.01-0.03 d 1 at 9-21°C by river die-away test in slurry sediment of aquatic systems (Lee Ryan 1979 quoted, Scow 1982) t,/2 = 27 d for sediment-water microcosm under aerobic conditions (quoted, Muir 1991). 

Cunningham, J.J., Kemp, W.M., Stevenson, J.C., Boynton, W.R., Means, J.C. (1981) Stress effects of agricultural herbicides on submerged macrophytes in estuarine microcosms, pp. 147-182. In Submerged aquatic vegetation in Chesapeake Bay. Annual Report to USEPA, UMCEES, Horn Point Environmental Laboratories, Cambridge, Maryland. 

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