Decabromodiphenylethane

Decabromodiphenyl ethane was not detected (detection limit not reported) in 128 serum samples collected in 2006 from office cleaners, university students and policemen residing in Tianjin, China(1). Decabromodiphenyl ethane was detected at 3.5-123 and 1.7-25 ng/g lipid weight in 6 of 102 serum and 9 of 105 milk samples collected in 2008-2009 from mothers in Sherbrooke, Quebec, Canada(2).

TERRESTRIAL FATE: Based on a classification scheme(1), an estimated Koc value of 2.4X10+6(SRC), determined from a structure estimation method(2), indicates that decabromodiphenyl ethane is expected to be immobile in soil(SRC). Volatilization of decabromodiphenyl ethane from moist soil surfaces is not expected given an estimated Henry's Law constant of 2.9X10-8 atm-cu m/mole(SRC), developed using a fragment constant estimation method(2). Decabromodiphenyl ethane is not expected to volatilize from dry soil surfaces(SRC) based upon an estimated vapor pressure of 1.9X10-13 mm Hg at 25 °C(SRC), determined from a fragment constant method(2). Biodegradation data in soil were not available(SRC, 2018).

AQUATIC FATE: Based on a classification scheme(1), an estimated Koc value of 2.4X10+6(SRC), determined from a structure estimation method(2), indicates that decabromodiphenyl ethane is expected to adsorb to suspended solids and sediment(SRC). Volatilization from water surfaces is not expected(3) based upon an estimated Henry's Law constant of 2.9X10-8 atm-cu m/mole(SRC), developed using a fragment constant estimation method(2). Decabromodiphenyl ethane is not expected to undergo hydrolysis in the environment due to the lack of functional groups that hydrolyze under environmental conditions(3). According to a classification scheme(4), an estimated BCF of 7(SRC), from an estimated log Kow of 13.64(2) and a regression-derived equation(2), suggests the potential for bioconcentration in aquatic organisms is low. Biodegradation data in water were not available(SRC, 2018).

ATMOSPHERIC FATE: According to a model of gas/particle partitioning of semivolatile organic compounds in the atmosphere(1), decabromodiphenyl ethane, which has an estimated vapor pressure of 1.9X10-13 mm Hg at 25 °C(SRC), determined from a fragment constant method(2), is expected to exist solely in the particulate phase in the ambient atmosphere. Particulate-phase decabromodiphenyl ethane may be removed from the air by wet or dry deposition(SRC). Decabromodiphenyl ethane does not contain chromophores that absorb at wavelengths >290 nm(3) and, therefore, is not expected to be susceptible to direct photolysis by sunlight(SRC).

Decabromodiphenyl ethane was detected at a mean level of 9.03 ng/g lipid weight in food composite samples collected for a Chinese total diet study performed in 2011(1). Foods enriched in omega-3 contained decabromodiphenyl ethane at 0.0031-0.048, 1.5-50, not detected to 0.083, 2.7-47 and 13 pg/g fresh weight in cow's milk, chicken eggs, biscuits, fish oil dietary supplement and vegetable oil dietary supplement, respectively, samples were purchased 2010-2012 from supermarkets in Madrid, Spain(2). Decabromodiphenyl ethane was detected in 4 of 12 formula and 4 of 15 cereal baby food samples collected in 2013 in the US at 19 and 18 pg/g fresh weight, respectively(3). In China, decabromodiphenyl ethane was detected in 1 of 9 formula, 5 of 12 cereal and 3 of 6 puree baby food samples at 30, 22 and 13 pg/g fresh weight, respectively(3).

Decabromodiphenyl ethane was detected at 1.7-25 ng/g lipid weight in 9 of 105 milk samples collected in 2008-2009 from mothers in Sherbrooke, Quebec, Canada(1). Decabromodiphenyl ethane was detected at a mean level of 8.06 ng/g lipid weight in 29 human milk samples collected for a Chinese total diet study performed in 2011(2). Decabromodiphenyl ethane was detected at 0.0031-0.048 pg/g fresh weight in cow's milk purchased 2010-2012 from supermarkets in Madrid, Spain(3).

IDENTIFICATION AND USE: Decabromodiphenyl ethane (DBDPE) has been used as a substitute for decabrominated diphenyl ether (BDE-209) and therefore it is currently used in more or less the same applications as BDE-209, such as manufacture of plastics (including polyester and vinyl ester resins) and rubber products, as well as in different applications related to manufacture of textiles and leather. This compound is also found in polymers used for electronic and electrical applications. DBDPE could also be used in adhesives and sealants. HUMAN STUDIES: When tested in vitro in HepG2 cells, DBDPE was cytotoxic with anti-proliferation effect and apoptosis was accompanied with overproduction of reactive oxygen species. ANIMAL STUDIES: Male rats were orally administrated with 100 mg/kg DBDPE for 90 days. Results showed DBDPE was found in all tissues. At least seven unknown compounds were observed in the DBDPE-exposed rats, indicating that DBDPE biotransformation occurred in rats. In mice treated with DBDPE for 30 days the levels of alanine aminotransferase or ALT and aspartate aminotransferase or AST of higher dose treatment groups were markedly increased. Blood glucose levels of treatment groups were higher than those of control group. There was also an induction in TSH, T3, and fT3. Uridinediphosphoglucuronosyltransferase (UDPGT), 7-pentoxyresorufin O-depentylase (PROD), and ethoxyresorufin-O-deethylase (EROD) activities were found to have been increased significantly in the high dose group. Histopathologic liver changes were characterized by hepatocyte hypertrophy and cytoplasmic vacuolization. In rats, DBDPE induced oxidative stress, elevated blood glucose levels, increased CYP2B2 mRNA, CYP2B1/2 protein, PROD activity, and induced CYP3A2 mRNA, CYP3A2 protein, and luciferin benzylether debenzylase (LBD) activity. No evidence of maternal toxicity, developmental toxicity, or teratogenicity was observed in rats or rabbits treated with DBDPE at dosage levels up to 1,250 mg/kg-day. DBDPE was not genotoxic in bacterial assays (Ames/Salmonella typhimurium and Escherichia coli WP2 reverse mutation assays) and no chromosomal aberrations were reported in Chinese hamster lung cells. ECOTOXICITY STUDIES: In Grass carp (Ctenopharyngodon idella) 5 miRNAs were significantly down-regulated and 36 miRNAs were significantly up-regulated after DBDPE exposure indicating that miRNAs have potential for use as biomarkers. The fish hepatocyte assay, based on the synthesis and secretion of vitellogenin from isolated male liver cells produced a clear dose-response curve in the presence of DBDPE. DBDPE induced the induction of hepatic EROD activity at low test concentrations, but started to inhibit the activity at higher concentrations. Also, the induction of the hepatocyte conjugation activity, UDPGT, was induced with no signs of inhibition even at the highest test concentration. The reduced EROD activity resulted in a drop in the production of vitellogenin by the cells. In vivo tests showed that DBDPE was acutely toxic to water fleas, the 48 hr EC-50 value being 19 ug/L. Moreover, DBDPE reduced the hatching rates of exposed zebra-fish eggs and raised significantly the mortality of hatched larvae. Treatment-related effects were identified for E. fetida reproduction, C. sativa survival, and L. esculentum and A. cepa height and dry weight. The most sensitive endpoints were decreased height and dry weight for A. cepa and decreased reproduction for E. fetida.

/AQUATIC SPECIES/ Decabromodiphenyl ether (BDE-209) and its commercial alternative decabromodiphenyl ethane (DBDPE) are two structurally similar brominated flame retardants, with evidence of their ubiquitous existence in aquatic ecosystems. The present study was conducted to investigate the hepatic oxidative stress inducing potential of BDE-209, DBDPE, and their mixture in Carassius auratus after exposure to different doses (10, 50 and 100 mg/kg) for 7, 14 and 30 days. Results showed that oxidative stress was evoked evidently for the experimental groups with longer exposure duration, as indicated by significant inhibition in the antioxidant enzymes activities and decrease in the reduced glutathione level, as well as simultaneous elevation of lipid peroxidation level measured by malondialdehyde content. In addition, it was found that BDE-209 possessed a higher oxidative stress inducing ability than DBDPE. Considering the more pronounced antioxidant responses in combined exposure, the interaction of BDE-209 and DBDPE was presumed to be additive action.

/AQUATIC SPECIES/ The occurrence, partitioning and risk of eight polybrominated diphenyl ethers (PBDEs), nine new brominated (NBFRs) and ten organophosphorus flame retardants (OPFRs) were evaluated in three Spanish rivers suffering different anthropogenic pressures (Nalon, Arga and Besos). OPFRs were ubiquitous contaminants in water (sum(OPFRs) ranging from 0.0076 to 7.2 ug/L) and sediments (sum(OPFRs) ranging 3.8 to 824 ug/kg). Brominated flame retardants were not detected in waters, whereas sum(PBDEs) ranged from 88 to 812 ug/kg and decabromodiphenyl ethane (DBDPE) reached 435 ug/kg in sediments from the River Besos, the most impacted river. The occurrence of flame retardants in river water and sediment was clearly associated with human activities, since the highest levels occurred near urban and industrial zones and after wastewater treatment plants discharge. Daphnia magna toxicity was carried out for OPFRs, the most ubiquitous flame retardants, considering individual compounds and mixtures. Toxicity of nine tested OPFRs differed largely among compounds, with EC50 values ranging over three magnitude orders (0.31-381 mg/L). Results evidenced that these compounds act by non-polar narcosis, since their toxicity was proportional to their lipophilicity (Kow). Furthermore, their joint toxicity was additive, which means that single and joint toxicity can be predicted knowing their concentration levels in water using quantitative structure activity relationships (QSARs) and predictive mixture models. Based on these results, a risk assessment considering joint effect was performed calculating and summing risk quotients (RQs) for the water and sediment samples. No significant risk to D. magna (SRQs <1) was observed for any of the monitored rivers.

/AQUATIC SPECIES/ Grass carp (Ctenopharyngodon idella) is one of the most important species in China. Decabromodiphenyl ethane (DBDPE) is a brominated flame retardant that has been used widely in industry, and has been observed to accumulate in the tissues of fish from South China. Evidence has shown that DBDPE is toxic to aquatic animals, but the molecular response has been unclear. MicroRNAs (miRNAs) are small noncoding and negative regulatory RNAs that are 20-24 nucleotides in length, which are involved in a wide range of biological processes. We took advantage of deep-sequencing techniques to accurately and comprehensively profile the kidney miRNA expression of grass carp after 8weeks of oral exposure to DBDPE. After mapping sequencing data to the genome and Expressed Sequence Tags (ESTs) of grass carp, we identified 493 miRNAs in the sequenced grass carp samples, which included 51 new miRNAs. The results indicated that 5 miRNAs were significantly down-regulated and 36 miRNAs were significantly up-regulated (FDR<0.001, 1.5-fold change) after DBDPE exposure. Real-time quantitative PCR (RT-qPCR) was performed on 4 miRNAs from the two samples, and the sequencing and RT-qPCR data were consistent. This study provides the first comprehensive identification of grass carp miRNAs, and the first expression analysis of grass carp miRNAs following DBDPE exposure. The results indicated that miRNAs have potential for use as biomarkers.

Decabromodiphenyl ethane, measured in pine tree bark samples collected the autumn of 2006 from 26 US locations (Indiana, Massachusetts, Maryland, New York, Ohio, Pennsylvania, Virginia) was found at not detected to 0.73 ng/g bark(1). Decabromodiphenyl ethane was not detected in tree bark from 9 of 12 locations around the world (Birkenes, Norway; Bukit Kototabang, Indonesia; Cape Grim, Tasmania; De Aar, South Africa; Dhulikhel, Nepal; Malin Head, Ireland; Reykjavik, Iceland; Tula, American Samoa, US; Whistler, BC, Canada) but was detected at 6.63, 1.39 and 3.92 ng/g lipid in tree bark from Toronto, and Frasardale, ON, Canada, and Kosetice, Czech Republic, respectively(2). In eucalyptus (Eucalyptus spp) leaves and Masson pine (Pinus massoniana) needles of trees growing in an e-waste site in China, decabromodiphenyl ethane was detected at 9.14-35.6 and 11.2-42.3 ng/g dry weight, respectively, samples were collected Jul 2007 to Jun 2008(3).

Decabromodiphenyl ethane was not detected in serum samples collected from 17 dogs in Bloomington, IN(1). Serum samples collected 2011-2012 from green turtles (Chelonia mydas) in the Hawaiian Islands did not contain decabromodiphenyl ethane (detection limit 17 pg/g wet weight)(2). Reported concentrations of decabromodiphenyl ethane were not detected to 14.9 ng/g lipid weight in the liver of 20 franciscana dolphin (Pontoporia blainvillei), collected along the Brazilian coast between 1994 and 2008(3). Decabromodiphenyl ethane was not detected in adipose tissue from 11 circumpolar polar bear (Ursus maritimus) sub-populations in 2005-2008 spanning Alaska east to Svalbard(4). Decabromodiphenyl ethane was not detected (detection limit 1.06 ng/g lipid) in the blubber and brain of five species of stranded dolphins (Delphinus delphis, Stenella coureloalba, Globicephala melas, Grampus griseus, Tursiops truncatus) collected on the Alboran Sea coastline between 2004 and 2011(5). Decabromodiphenyl ethane was detected in adult tissues, neonates and eggs of captive Chinese alligators (Alligator sinensis) at 4.74-192, 0.24-1.94 and 0.01-0.51 ng/g lipid weight, respectively(6).

Tissue samples were collected and analyzed for decabromodiphenyl ethane from eight giant panda (Ailuropoda melanoleuca) in Dec 2006 from the Beijing Zoo and from eight red panda (Ailurus fulgens) in Nov 2006 from the Chongqing Zoo(1).[Table#8465]

Decabromodiphenyl ethane was not detected in herring gull eggs (Larus argentatus), collected fifteen years (1982-2006) from colonies at Toronto Harbor (Lake Ontario) and Channel Shelter Island (Lake Huron)(1). At other locations, decabromodiphenyl was detected at 1.3 ng/g wet weight (ww) in 1996 at a colony in Niagra River (above the falls), at 10, 11 and 104 ng/g ww in 1999, 2001 and 2004 at Gull Island (Lake Michigan), at 3.2 ng/g ww in 2003 at Fighting Island (Detroit River), at 11, 288 and 44 ng/g ww in 2004, 2005 and 2006 at Chantry Island (Lake Huron) and 4.3 and 9.3 ng/g ww in 2005 and 2006 at Agawa Rocks (Lake Superior)(1). Decabromodiphenyl ethane was not detected (detection limit 0.07 ng/g wet weight) in the plasma or liver of ring-billed gulls (Larus delawarensis) collected Apr-Jun 2010 from the St Lawrence River, downstream of Montreal, Canada(2). In light-vented bulbul (Pycnonotus sinensis), long-tailed shrike (Lanius schach) and oriental magpie-robin (Copsychus saularis) collected from 7 sampling sites in South China, decabromodiphenyl ethane levels were not detected to 130 ng/g lipid weight(3). The median concentration of decabromodiphenyl ethane in kingfishers (Alcedo atthis) collected from an e-waste recycling site in South China was reported as 12 ng/g lipid weight(4).

River Delta, Chnia collected 2010 to 2012 were reported(1).[Table#8466]

Concentrations of decabromodiphenyl ethane in bird eggs collected May 2008 from the Yellow River Delta, North China were reported(1).[Table#8467]

The following link will take the user to the National Toxicology Program (NTP) Test Status of Agents Search page, which tabulates the results and current status of tests such as "Short-Term Toxicity Studies", "Long-term Carcinogenicity Studies", "Developmental Studies", "Genetic Toxicology Studies", etc., performed with this chemical. Testing status for decabromodiphenyl ethane is available.[Available from, as of August 9, 2018: https://ntpsearch.niehs.nih.gov/?e=True&ContentType=Testing+Status]

Decabromodiphenyl ethane was detected at 6.43-1440 in 60% of 94 biosolid samples collected Feb-Mar 2001 from 32 states and the District of Columbia(1). In 42 waste water treatment plant (WWTP) sludge samples collected 1998 to 2006 from 12 different countries, decabromodiphenyl ethane was detected at 1.6-2.20 ng/g dry weight(2). Decabromodiphenyl ethane was detected in 25 of 50 sewage (8 large, 6 medium, 36 small) treatment plant sludge samples at an estimated maximum of 100 ng/g dry weight, samples were collected in 2000(3). Decabromodiphenyl ethane was detected at mean concentrations of 17 ng/L, 0.11 ng/L and 72 ng/g dry weight in influent, effluent and digested sludge samples, respectively, collected Oct-Nov 2006 from the Henriksdal WWTP in Stockholm, Sweden; in samples collected Jan 2007, respective concentrations were 26 ng/L, 0.022 ng/L and 92 ng/g dry weight(4). Decabromodiphenyl ethane was not detected in influent or effluent samples, collected in 2009 from Drammen or Tromso, Norway, WWTPs(5). It was detected in the influent of Lillehammer, Norway WWTP at 5.1 ng/L(5). In sludge samples, decabromodiphenyl ethane was detected at 6.3, 1.9 and 3.2 ng/g dry weight in samples collected from Drammen, Tromso and Lillehammer WWTPs, respectively(5). Seepage water, collected from a metal recycling site contained 80 ng/L of decabromodiphenyl ethane(5). Decabromodiphenyl ethane was detected at 5.6-31.6 ppb in 10 sewage sludge samples collected from six locations in Ontario, Canada(6). Decabromodiphenyl ethane was detected at 47.0 ng/g dry weight in sewage sludge samples collected Apr-Jun 2006 from 31 urban Spanish WWTPs(7).

... Flame retardant substance for various applications, such as plastic and rubber materials, electrical and electronic equipment, adhesives and sealants.

DBDPE was introduced more than twenty years ago and it has, at least during the last decade, been used as a substitute for decabrominated diphenyl ether (BDE-209) and therefore it is currently used in more or less the same applications as BDE-209, such as manufacture of plastics (including polyester and vinyl ester resins) and rubber products as well as in different applications related to manufacture of textiles and leather. The compound is also used in polymers used for electronic and electrical applications. DBDPE could also be used in adhesives and sealants.

Plastics -> Typical concentration range in plastic materials -> 15.0 - 35.0%

2023: 50,000,000 - <100,000,000 lb

Non-confidential 2016 Chemical Data Reporting (CDR) information on the production and use of chemicals manufactured or imported into the United States. Chemical: Benzene, 1,1'-(1,2-ethanediyl)bis[2,3,4,5,6-pentabromo-:

Plastics -> Polymer Type -> PUR; PVC (soft)

Plastics -> Flame retardants

All Other Basic Organic Chemical Manufacturing

Benzene, 1,1'-(1,2-ethanediyl)bis[2,3,4,5,6-pentabromo-: ACTIVE