Effects of Benzene (A Water-Soluble Component of Crude Oil) on Eggs and Larvae of Pacific Herring and Northern Anchovy

Struhsaker, Jeannette W.; Eldridge, Maxwell B.; Echeverria, Tina

doi:10.1016/b978-0-12-718250-6.50019-5

Cited by 34 publications

(5 citation statements)

References 6 publications

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“…In the same study, oil-contaminated prey (6 mg/L) caused larval mortality but did not affect feeding or growth of survivors. Thirdly, embryonic exposure to 45 mg/L benzene (an aromatic component of crude oil) resulted in delayed development, irregular heartbeat, and fin and jaw lesions, and larval exposure to 12 mg/L decreased feeding and growth (Struhsaker et al 1974). Note that Carls (1987) found that the water-soluble fraction he used contained 95% monoaromatic and only 5% diaromatic hydrocarbons, so direct comparisons of total aromatic hydrocarbons in these laboratory studies with PAHs in the water column of PWS in 1989 are not possible.…”

Section: Level Of Significancementioning

confidence: 99%

Histopathology and cytogenetic evaluation of Pacific herring larvae exposed to petroleum hydrocarbons in the laboratory or in Prince William Sound, Alaska, after the Exxon Valdez oil spill

Marty¹,

Hose²,

McGurk³

et al. 1997

Can. J. Fish. Aquat. Sci.

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Following the 1989 Exxon Valdez oil spill in Prince William Sound, Alaska, USA, Pacific herring (Clupea pallasi) larvae sampled from oiled sites had ascites, pericardial edema, and genotoxic damage. Laboratory study confirmed that these lesions were consistent with oil exposure. Pacific herring larvae were trawled from two oiled and two unoiled sites in Prince William Sound in May 1989. Larvae from oiled sites were shorter, had ingested less food, had slower growth (oiled, 0.07-0.10 mm/day; unoiled, 0.15-0.18 mm/day), and had higher prevalence of cytogenetic damage (oiled, 56-84%; unoiled, 32-40%) and ascites (oiled, 16%; unoiled, 1%) than from unoiled sites. In the laboratory experiment, Pacific herring eggs were exposed to an oil-water dispersion of Prudhoe Bay crude oil (initial concentrations of 0.0, 0.10, 0.24, 0.48, and 2.41 mg/L) and sampled for histopathology <24 h after hatching. Effects were significant at the 0.48 mg/L dose (Dunnett's procedure, P < 0.05). Lesions included ascites; hepatocellular vacuolar change; and degeneration or necrosis of skeletal myocytes, retinal cells, and developing brain cells. Lesions in field-sampled larvae were consistent with higher mortality rates documented in larvae from oiled sites.Résumé : Après le déversement pétrolier de l'Exxon Valdez qui a eu lieu en 1989 dans le golfe du Prince-William, Alaska, É.-U., des larves de hareng du Pacifique (Clupea pallasi), prélevées dans des sites exposés au pétrole présentaient des ascites, de l'oedème péricardique et des lésions génotoxiques. Une étude en laboratoire a confirmé qu'il y avait compatibilité entre ces lésions et l'exposition au pétrole. Des larves de hareng du Pacifique ont été récoltées par chalutage dans deux sites exposés au pétrole et dans deux sites non exposés dans le golf du Prince-William en mai 1989. Les larves provenant des sites exposés étaient plus courtes, avaient ingéré moins d'aliments, avaient une croissance plus lente (site exposé, 0,07-0,10 mm/jour; site non exposé, 0,15-0,18 mm/jour) et présentaient une fréquence plus élevée de lésions cytogénétiques (site exposé, 56-84 %; site non exposé, 32-40 %) et d'ascites (site exposé, 16 %; site non exposé, 1 %) que les larves provenant des sites non exposés au pétrole. Au cours d'une expérience de laboratoire, des oeufs de hareng du Pacifique ont été exposés à une dispersion pétrole-eau de pétrole brut de Prudhoe Bay (concentrations initiales de 0,0, 0,10, 0,24, 0,48 et 2,41 mg/L) et ont été examinés pour déceler des manifestations histopathologiques moins de 24 h après leur éclosion. Les effets étaient statistiquement significatifs à la dose d'exposition de 0,48 mg/L (méthode de Dunnett, P < 0,05). Parmi les lésions figuraient des ascites, des modifications vacuolaires hépatocellulaires et une dégénérescence ou une nécrose des myocytes squelettiques, des cellules rétiniennes et des cellules cérébrales en développement. Les lésions chez les larves échantillonnées sur le terrain correspondaient avec les taux de mortalité élevés documentés chez les larves pr...

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Section: Level Of Significancementioning

confidence: 99%

Histopathology and cytogenetic evaluation of Pacific herring larvae exposed to petroleum hydrocarbons in the laboratory or in Prince William Sound, Alaska, after the Exxon Valdez oil spill

Marty¹,

Hose²,

McGurk³

et al. 1997

Can. J. Fish. Aquat. Sci.

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“…In most experiments a nominal C w,c was reported, except for Pimephales promelas and Hyalella azteca exposed to pyrene and fluorene . In 5 out of the 6 survival experiments the test solutions were changed daily or every other day to achieve the initial concentration specified . If weight or lipid content was not reported, we used a value obtained from other experimental studies on the same species of a similar developmental stage (Supplemental Data, Table S1).…”

Section: Methodsmentioning

confidence: 99%

“…We compared our model estimates on survival with experimental data on the survival of 4 arthropod species (Branchiopoda and Malacostraca) and 3 fish species (Actinopterygii) exposed to various oil constituents: pyrene, fluoranthene, fluorene, phenanthrene, retene (i.e., PAHs), naphthalene, and 2 benzenes (Table 2; Supplemental Data, Table S4) [7][8][9]14,27,38]. The experimental survival data were relative to the survival representative of the control situation.…”

Section: Comparison With Experimental Datamentioning

confidence: 99%

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Time‐varying effects of aromatic oil constituents on the survival of aquatic species: Deviations between model estimates and observations

Hoop

Viaene

Schipper

et al. 2016

Enviro Toxic and Chemistry

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There is a need to study the time course of toxic chemical effects on organisms because there might be a time lag between the onset of chemical exposure and the corresponding adverse effects. For aquatic organisms, crude oil and oil constituents originating from either natural seeps or human activities can be relevant case studies. In the present study the authors tested a generic toxicokinetic model to quantify the time-varying effects of various oil constituents on the survival of aquatic organisms. The model is based on key parameters applicable to an array of species and compounds with baseline toxicity reflected by a generic, internal toxicity threshold or critical body burden (CBB). They compared model estimates with experimental data on the effects of 8 aromatic oil constituents on the survival of aquatic species including crustaceans and fish. The average model uncertainty, expressed as the root mean square error, was 0.25 (minimum-maximum, 0.04-0.67) on a scale between 0 and 1. The estimated survival was generally lower than the measured survival right after the onset of oil constituent exposure. In contrast, the model underestimated the maximum mortality for crustaceans and fish observed in the laboratory. Thus, the model based on the CBB concept failed to adequately predict the lethal effects of the oil constituents on crustaceans and fish. Possible explanations for the deviations between model estimates and observations may include incorrect assumptions regarding a constant lethal body burden, the absence of biotransformation products, and the steady state of aromatic hydrocarbon concentrations in organisms. Clearly, a more complex model approach than the generic model used in the present study is needed to predict toxicity dynamics of narcotic chemicals. Environ Toxicol Chem 2017;36:128-136. © 2016 SETAC.

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“…Petroleum aromatic hydrocarbons (AH) are one of the more toxic components of crude oil, particularly because they are relatively soluble in water. Thus, many studies of the effects of oil contamination on fish and other aquatic life have focused on either the water-soluble portions of whole crude oil or separate AH (Andelman & Snodgrass, 1974;Levitan & Taylor, 1979;Meyerhoff, 1975;Morrow et al, 1975;Struhsaker et al, 1974;Hedtke & Puglisi, 1982;Dalich et al, 1982;Woodward et al, 1981;Moles et al, 1981). Aromatic hydrocarbons have served as markers of fish exposed to oil pollution (Ogata & Miyake, 1979) and some AH are known carcinogens (Andelman & Snodgrass, 1974).…”

Section: Introductionmentioning

confidence: 99%

The effect of water‐soluble aromatic hydrocarbons on some haematological parameters of rainbow trout, Salmo gairdneri Richardson, during acute exposure

Zbanyszek¹,

Smith²

1984

Journal of Fish Biology

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Rainbow trout were exposed to a model mixture of water-soluble aromatic hydrocarbons (AH) at concentrations of0.3-15.2 ppm for periods of 1-72 h. None of the parameters monitored except RBC changed at 0.3 ppm AH, while all constituents, except blood glucose, changed at 7.2 ppm AH. At 15.2 ppm, all fish died within I h. Haematological changes included increased haematocrit, haemoglobin concentration, erythrocyte counts, and blood clotting (prothrombin) times. Plasma CI-concentration decreased significantly. Changes resembled a stress response except for the increased clotting times, which typically decrease, and lack of increase in blood glucose.

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Effects of Benzene (A Water-Soluble Component of Crude Oil) on Eggs and Larvae of Pacific Herring and Northern Anchovy

Cited by 34 publications

References 6 publications

Histopathology and cytogenetic evaluation of Pacific herring larvae exposed to petroleum hydrocarbons in the laboratory or in Prince William Sound, Alaska, after the Exxon Valdez oil spill

Histopathology and cytogenetic evaluation of Pacific herring larvae exposed to petroleum hydrocarbons in the laboratory or in Prince William Sound, Alaska, after the Exxon Valdez oil spill

Time‐varying effects of aromatic oil constituents on the survival of aquatic species: Deviations between model estimates and observations

The effect of water‐soluble aromatic hydrocarbons on some haematological parameters of rainbow trout, Salmo gairdneri Richardson, during acute exposure

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