Bioaccumulation, biotransformation, and biochemical effects of brominated diphenyl ethers in juvenile lake trout (Salvelinus namaycush).

Juvenile lake trout (Salvelinus namaycush) were exposed to three dietary concentrations (0, approximately 2.5, and approximately 25 ng/g per BDE congener) of 13 BDE congeners (3-10 Br atoms) in the laboratory for 56 days, followed by 112 days of clean food, to examine bioaccumulation parameters and potential biochemical effects. The bioaccumulation of BDEs by the trout was highly influenced by biotransformation, via debromination, which resulted in bioaccumulation parameters that were much different than would be expected based on studies of chlorinated organic compounds (e.g., PCBs). Half-lives (t1/2's) for some BDE congeners (e.g., BDE-85 and -190) were much lower than expected based on their Kow, which was likely due to biotransformation, whereas t1/2's of other BDE congeners (e.g., BDE-66, -77, -153, and -154) were much longer than anticipated based on Kow. This was likely because the metabolites of BDE formed via debromination had the same chemical structure of these BDE congeners, which supplemented measured concentrations. The detection of three BDE congeners (an unknown penta, BDE-140, and an unknown hexa) in the fish that were not present in the food or in the control fish provide further evidence forthe debromination of BDEs. Half-lives of BDEs ranged from 38 +/- 9 to 346 +/- 173 days and biomagnification factors ranged from 1.6 (BDE-190) to 45.9 (BDE-100), but these bioaccumulation parameters need to be viewed with caution because they were highly influenced by debromination and relative abundance of individual BDEs that the fish were exposed to. CYP1A enzyme activity, measured as EROD, and free tri-iodothyronine (T3) concentrations in the plasma of lake trout varied significantly throughout the experiment but were not related to BDE exposure. In contrast, plasma levels of thyroxine levels (T4) were lower in both groups of PBDE-exposed fish compared with control fish after 56 days of exposure, and after 168 days in the high dose, suggesting that PBDEs may influence thyroid homeostasis at levels that are higher than what is normally found in the environment.

Biotransformation of N-ethyl perfluorooctanesulfonamide by rainbow trout (Onchorhynchus mykiss) liver microsomes.

Rainbow trout (Onchorhynchus mykiss) liver microsomes were incubated with N-ethyl perfluorooctanesulfonamide [N-EtPFOSA, C8F17SO2NH(C2H5)], to examine the possibility of in vitro biotransformation to perfluorooctane sulfonate (PFOS, C8F17SO3-) and perfluorooctanoate (PFOA, C7F15COO-). Incubations were performed by exposing trout liver microsomes to N-EtPFOSA at 8 degrees C in the dark. Reaction mixtures were analyzed after incubation periods of 0, 2, 4, 8, 16, and 30 h for N-EtPFOSA, PFOS, PFOA, and perfluorooctanesulfonamide (PFOSA, C8F17SO2NH2), a suspected intermediate. Amounts of PFOS and PFOSA were found to increase with incubation time, but only background levels of PFOA were detected. Three possible reaction pathways are proposed for the conversion of N-EtPFOSA to PFOS: (i) direct conversion of N-EtPFOSA to PFOS by deethylamination accompanied by conversion of the sulfone group to sulfonate, (ii) deethylation of N-EtPFOSA to PFOSA, followed by deamination to form PFOS, and (iii) direct hydrolysis of N-EtPFOSA. These findings represent the first report indicating a possible biotransformation of a perfluorosulfonamide to PFOS in fish and may help to explain the detection of PFOS, which is relatively involatile, and thus not likely to undergo atmospheric transport, in biota from remote regions.

CYP1A induction and blue sac disease in early developmental stages of rainbow trout (Oncorhynchus Mykiss) exposed to retene.

Early life stages of rainbow trout were exposed to different regimes of water-borne retene (7-isopropyl-1-methylphenanthrene) to determine if there is an ontogenic stage particularly sensitive to retene toxicity, and if cytochrome P-4501A (CYP1A) induction is a forerunner to blue sac disease (BSD), the syndrome of toxicity. CYP1A protein concentrations, measured by immunohistochemistry, were first detected during organogenesis, when organ and enzyme systems are first being developed, and steadily increased until swim-up. The prevalence of signs of BSD rose 1 wk following a marked increase in CYP1A activity after hatch, suggesting that CYP1A induction is related to BSD. The larval stage was the most sensitive to retene toxicity, based on CYP1A induction and a high prevalence of BSD. The most common signs of BSD were hemorrhaging, yolk-sac edema, and mortality, but hemorrhaging was the first and most frequently observed response. Tissue concentrations of retene were elevated just after fertilization, but decreased steadily as fish developed to the swim-up stage, most likely due to the establishment of more efficient metabolic and excretory systems in later stages of development.

CYP1A Induction and Blue SAC Disease in Early Developmental Stages of Rainbow Trout (Oncorhynchus Mykiss) Exposed to Retene.

Early life stages of rainbow trout were exposed to different regimes of water-borne retene (7-isopropyl-1-methylphenanthrene) to determine if there is an ontogenic stage particularly sensitive to retene toxicity, and if cytochrome P-4501A (CYP1A) induction is a forerunner to blue sac disease (BSD), the syndrome of toxicity. CYP1A protein concentrations, measured by immunohistochemistry, were first detected during organogenesis, when organ and enzyme systems are first being developed, and steadily increased until swim-up. The prevalence of signs of BSD rose 1 wk following a marked increase in CYP1A activity after hatch, suggesting that CYP1A induction is related to BSD. The larval stage was the most sensitive to retene toxicity, based on CYP1A induction and a high prevalence of BSD. The most common signs of BSD were hemorrhaging, yolk-sac edema, and mortality, but hemorrhaging was the first and most frequently observed response. Tissue concentrations of retene were elevated just after fertilization, but decreased steadily as fish developed to the swim-up stage, most likely due to the establishment of more efficient metabolic and excretory systems in later stages of development.