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process that xenobiotics are taken into the body of organisms is through consumption of food containing the chemicals. The molecules can apparently be absorbed in the intestine and lipophilic organics in food are expected to transfer (Guthrie, 1980). The bioaccumulation potential of a chemical compound is greatly affected by the rate of elimination from the organism. If an unaltered chemical can be eliminated rapidly, residues will not accumulate and tissue damage is less likely. In invertebrates, elimination can proceed by several routes, including transport across the integument or resperatory surfaces, secretion in gallbladder bile, and excretion from the kidney in urine (Spacie and Hamelink, 1985). Furthermore, passive elimination of lipid-soluble chemicals can also occur across the skin and gills (Hunn and Allen, 1974; Allen and Hunn, 1977). The choice of the model to calculate the uptake of contaminants by an organism depends on the pollution sources organisms exposed to and has to be adapted to the case encountered. If the pollution is dissolved in the water, bioconcentration factors (BCF), calculating the uptake of contaminants from the water, must be used. If the pollution is located in the sediment, biota accumulation factors (BAFs), determining the uptake of contaminants from the sediment can be used. The BCF is the ratio of the concentration of test chemical accumulated in the tissues of the test organism to the measured concentration in the water to which the organisms are exposed, while BAFs are the concentration of a chemical accumulated by an organism divided by the concentration of the same chemical in sediment (Spacie and Hamelink, 1985). In sediment toxicity studies, the design was altered to determine the biota-sediment accumulation factors (BSAFs) calculated by dividing the lipid-normalized tissue concentrations by the organic-carbon normalized sediment concentration (Lee, 1992; Kemble et al., 1998). BSAFs were compared with the theoretical values of 1.7 predicted for equilibrium partitioning of hydrophobic organic contaminants in sediment-benthos systems (McFarland and Clarke, 1986; DiToro et al., 1991). A BSAF of less than 1.7 indicates less partitioning onto lipids than predicted and a value greater than 1.7 indicates more uptake than can be explained by partitioning theory alone (Lee, 1992). For non-metabolizing chemicals, a BSAF in the 8
ange of 0.15-1.5 is thus expected providing that there is sufficient time for equilibration (Hellou et al., 1999). 1. General Characteristics 1.1 Morphology Aquatic Oligochaetes Aquatic oligochaete has the same structure as the common terrestrial earthworms classified in Phylum Annelida (Figure 1). The true aquatic oligochaetes are much more delicately constructed and small. The usual length ranges from 1 to 30 mm. The body wall is soft, muscular and covered with a thin cuticle. The prostomium is a presegmental lobe at the extreme anterior end of the body. It projects in a rooflike fashion above the mouth and is sometimes elongated into a proboscis. The body of an oligochaete is divided by a number of segments which is quite variable even in mature individuals of each family. For instance, the threadlike Haplotaxidae have the largest number of segments, sometimes up to 500. At the opposite extreme the Naididae usually have between 7 and 40 segments. The other families, Tubificidae, for example, have an intermediate number of segments, usually consist of 40 to 200 segments. The chitinoid setae are arranged in four bundles on each segment except on segment I. A bundle may consist of from 1 to as many as 20 seta. The morphology of setae and their arrangement which is important as taxonomic characters are very diverse (Figure 2). Figure 1 Aquatic oligochaete. Source: Brusca and Brusca (1990) 9
Page 1 and 2: THESIS APPROVAL GRADUATE SCHOOL, KA
Page 3 and 4: Warucha Kanchana-Aksorn 2009: Use o
Page 5 and 6: TABLE OF CONTENTS Page TABLE OF CON
Page 7 and 8: LIST OF TABLES (Continued) Table Pa
Page 9 and 10: LIST OF TABLES (Continued) Appendix
Page 11 and 12: LIST OF FIGURES Figure Page 1 Aquat
Page 13 and 14: LIST OF FIGURES (Continued) Appendi
Page 15 and 16: USE OF FRESHWATER OLIGOCHAETE (LIMN
Page 17 and 18: At this stage, laboratory study on
Page 19 and 20: LITERATURE REVIEW Methodology of To
Page 21: through development, such as hatchi
Page 25 and 26: on microcustaceans, insect larvae a
Page 27 and 28: Figure 4 Budding in oligochaete sho
Page 29 and 30: Thalassodrilus, Clitellio, Adelodri
Page 31 and 32: Figure 7 Tail protrusion and swayin
Page 33 and 34: Figure 8 Chemical structures of six
Page 35 and 36: oil and asphalt may contain several
Page 37 and 38: several PAHs in water and sediment,
Page 39 and 40: 5. Transformation by Microorganisms
Page 41 and 42: et al., 2005), while in shore crabs
Page 43 and 44: 7. Toxic Effects in Aquatic Organis
Page 45 and 46: Table 6 (Continued) PAHs Species LC
Page 47 and 48: their exposure to digestive fluids
Page 49 and 50: during the sediment aging process,
Page 51 and 52: Changes in bottom sediment in the l
Page 53 and 54: 1. Instruments MATERIALS AND METHOD
Page 55 and 56: the technique of mitochondrial 16s
Page 57 and 58: 2. Investigation on the Morphologic
Page 59 and 60: and no worms placed to the sediment
Page 61 and 62: 3.4 Data Analysis All values were r
Page 63 and 64: Table 9). Spiked sediment was subsa
Page 65 and 66: Sediment avoidance in ij = (Σ anim
Page 67 and 68: 3) Test Conditions The bioaccumulat
Page 69 and 70: uptake of naphthalene into fish, an
Page 71 and 72: 4) Exposure Study Trophic transfer
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performed with 20 ml extraction flu
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RESULTS AND DISCUSSION Results 1. B
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Figure 13 Morphological features of
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Living style of L. hoffmeisteri was
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Figure 17 Feeding behavior of L. ho
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worms in this old class whereas a l
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No. of ind No. of ind No. of ind No
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Figure 23 Adult worm (3.0-3.5 cm) i
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3.4 Relationship between Oligochaet
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Table 14 Lethal and sublethal effec
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Figure 29 Mortality of L. hoffmeist
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ioaccumulation test, respectively (
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Concentration (ug/g dwt) 2000 1500
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analysis from two-factor ANOVA show
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sediment particles and accumulated
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undulatory swimming. Also, the peri
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The existence of L. hoffmeisteri in
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Lumbriculus variegatus ceased at le
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low level of DO had thoroughly occu
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in water, and thus is available for
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(1988) who investigated subacute re
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pollutants in aquatic ecosystems (M
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et al., 1994b), in dosed sediments
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(1997) said that naphthalene is mod
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107 various studies showed that fis
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(Dobroski and Epifano, 1980; Wolfe
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111 experiment, indicated the repro
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Recommendations 1. Limnodrilus hoff
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Anderson, J. W., J. M. Neff, B. A.
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Bender, M. E. and R. J. Huggett. 19
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Broman, D., A. Colmjo and C. Naf. 1
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Collado, R. and R. M. Schmelz. 2001
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Driscoll, K. S. B. and A. E. McElro
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Fromm, P. O. and R. C. Hunter. 1969
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Harrel, R. and S. T. Smith. 2002. M
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James, M. O. 1989. Biotransformatio
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Khan, A. N., D. Kamal, M. M. Mahmud
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Lee, H. 1992. Models, muddles and m
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Lotufo, G. R. 1998. Lethal and subl
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McElroy, A. E., B. W. Tripp, J. W.
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Neff, J. M. 1979. Polycyclic Aromat
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Pearson, W. H. and B. L. Olla. 1980
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143 Reichert, W. L., B-T. LeEberhar
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Sarin, C. 1994. Distribution of Ali
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Suedel, B. C., J. A. Boraczek, R. K
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Watanabe, K. H., H. Lin, H. L. Bart
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Yoshioka, Y and Y. Ose. 1993. A qua
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Appendix A Methods of Preparation a
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Dilution of Spiked Sediment 155 The
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Naphthalene Standard Calibration Cu
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Appendix Figure A2 HPLC chromatogra
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Calculation of Naphthalene Concentr
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Appendix Table B1 Characteristics o
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Appendix Table B5 Length-class of L
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Appendix Table B7 Length-class of L
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Appendix Table B10 Acute toxicity o
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Appendix Table B12 Sublethal toxici
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Appendix Table B13 (Continued) Dura
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Appendix Table B15 Naphthalene in t
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177 Appendix Table B17 Naphthalene
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179 Appendix Table B18 Naphthalene
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Appendix C Data Analysis 181
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Appendix Table C3 Two-factor ANOVA
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Page 201 and 202:
Probit Analysis of Mortality Equati
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Probit Analysis of Autotomy Equatio
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Probit Analysis of Sediment Avoidan
Page 207 and 208:
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