Decabromodiphenylethane

971.22200

971.22

284-366-9

WZ2532TA0A

DTXSID2052732

White powder

2903999090

0

11.1

DryPowder; OtherSolid; PelletsLargeCrystals

2.816 g/cm3

334-337 °C

676.2ºC at 760 mmHg

346.6ºC

1.727

In water, 1.61X10-12 mg/L at 25 °C (est)

1.93X10-13 mm Hg at 25 °C (est)

Odorless

Henry's Law constant = 2.94X10-8 atm-cu m/mol at 25 °C (est)

Hydroxyl radical reaction rate constant = 2.39X10-12 cu cm/molec-sec at 25 °C (est)

DA0358200

P273, P501

H413

SRP: Recycle any unused portion of the material for its approved use or return it to the manufacturer or supplier. Ultimate disposal of the chemical must consider: the material's impact on air quality; potential migration in air, soil or water; effects on animal, aquatic and plant life; and conformance with environmental and public health regulations. If it is possible or reasonable use an alternative chemical product with less inherent propensity for occupational harm/injury/toxicity or environmental contamination.

Not Classified

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).

SEDIMENT: The concentration of decabromodiphenyl ethane was reported as 0.13-0.75, 0.87-8.3, 1.6-2.5, 0.19-0.44 and 2.7-3.8 ng/g dry weight in surface sediment samples collected Aug 1-25, 2007 from Lakes Superior, Michigan, Huron, Erie and Ontario, respectively(1). Decabromodiphenyl ethane was not detected in sediment samples collected Jul 2009 downstream from a textile manufacturing outfall on the Yadkin River in North Carolina(2). Decabromodiphenyl ethane was detected at 24 ng/g dry weight in a sediment sample collected in 2001 from Western Scheldt, The Netherlands(3). Sediment collected in 2007 from 11 lakes in Sweden contained decabromodiphenyl ethane at 0.23-11 ng/g dry weight; in 2008, marine sediment samples were collected at seven sites on a transect from Stockholm-Stockholm archipelago, Sweden, decabromodiphenyl ethane was detected at 0.18-11 ng/g dry weight(4). In sediment samples collected in 2009 from Loselva River, Norway, decabromodiphenyl ethane was detected at 1.2 ng/g dry weight(5). Sediment samples collected the summer of 2011 from the Lingjiang, Oujiang and Qiantang Rivers, located in the Yangtze River Delta contained 2.42-19.0 ng/g dry weight of decabromodiphenyl ethane; it was detected in 46% of samples from the East China Sea at <0.176-1.57 ng/g dry weight(6). In 28 of 45 sediment samples collected in Aug 2011 from Durban Bay and 13 rivers in the eThekwini metropolitan municipality, South Africa, decabromodiphenyl ethane was detected at 0.6-1840 ng/g dry weight(7).|SEDIMENT: Sediment samples collected in July 2009 from the deepest part of lakes at six locations in Arkansas had decabromodiphenyl ethane concentrations as follows(1):[Table#8485]|SOIL: Decabromodiphenyl ethane was detected in 38 soil samples collected May 2008 from Shouguang, China at 12.0-344 ng/g(1). In soil samples collected from 87 sites in North China, decabromodiphenyl ethane was reported at undetectable to 1612 ng/g, the highest concentration was found in Shandong(2). Decabromodiphenyl ethane was detected at <0.0059-0.24 ng/g dry weight in soil samples collected Jan 2013 from eight sites located along a transect in England (Worcester, Droitwich, Bromsgrove, Bournville, Edgbason, Digbeth, Sutton Coldfield, Tamworth)(3).

URBAN/SUBURBAN: In atmospheric samples collected in the spring, summer and autumn 2004 and the winter 2005 from Taihu Lake basin, China, the annual average concentration of decabromodiphenyl ethane was 23 pg/cu m(1). The annual deposition flux of decabromodiphenyl ethane is 41,600 ng/sq m/year, calculate from data collected Oct 2007 to Sep 2008 at an urban site (Guangzhou City) in China(2). Decabromodiphenyl ethane was detected at 5.90-216.13 pg/cu m in 3 of 17 atmospheric samples collected in 2010 from Entebbe, Lake Victoria, Uganda; it was not detected (detection limit <5.90 pg/cu m) in 9 and 30 samples collected at the same location in 2008 and 2009, respectively(3).|Concentrations (pg/cu m) of vapor and particulate decabromodiphenyl ethane measured in the air samples collected 2005 to 2009 from five locations in the Great Lakes region(1).[Table#8480]|INDOOR: Decabromodiphenyl ethane was detected in 6 of 15 home and 1 of 20 office indoor air samples at <10-97 and 54 pg/cu m, respectively, samples were collected Feb-May 2015 in Birmingham, UK(1).|RURAL/REMOTE: The annual deposition flux of decabromodiphenyl ethane is 850 ng/sq m/year, calculate from data collected Oct 2007 to Sept 2008 at a rural site in China(1). Decabromodiphenyl ethane was detected at 0.077-7.9 pg/cu m in air samples collected in a remote area in southern Sweden(2).|SOURCE DOMINATED: Decabromodiphenyl ethane was detected at 0.7 ng/cu m in the atmosphere of an electronic dismantling facility in Stockholm, Sweden(1). In samples collected Jul 2007 to Jun 2008 from an e-waste recycling site in Southern China, decabromodiphenyl ethane was detected at 75.5-635 pg/cu m in the particulate phase, it was not detected in the gaseous phase in these samples(2). The annual deposition flux of decabromodiphenyl ethane is 9780 ng/sq m/year, calculate from data collected Oct 2007 to Sep 2008 at an e-waste recycling site in China(3).

Dog food samples collected from dog owners in Bloomington, IN, contained decabromodiphenyl ethane at 0.006-0.089 ng/g wet weight; the average concentration of decabromodiphenyl ethane in dry cat food was reported as 0.022 ng/g wet weight(1). Decabromodiphenyl ethane was detected at <10-11,070, <10-3420 and <10-262 ng/g dust in samples collected in 2006 from the main living area, bedroom and home vacuum bag, respectively, of 19 homes in the Boston, MA area(2). In 95 dust samples collected May-Jun 2015 from dorm rooms and common areas of two New England colleges, decabromodiphenyl ethane was detected in 98% at 10-15,000 ng/g dust(3). In dust samples collected winter 2007-spring 2008 from 36 day-care and primary schools located in West Midlands, UK, decabromodiphenyl ethane was detected in 75% at <20-2467 ng/g dust(4). Decabromodiphenyl ethane was detected in dust samples from 39 homes and 6 offices at 55-2126 and 170-1846 ng/g dust, respectively, in samples collected Jan-Jun 2008 from Antwerp, Belgium(4). The concentration of decabromodiphenyl ethane in a TV casing was 140 mg/kg(5). Decabromodiphenyl ethane was detected in 64% of flat screen TVs sampled Aug 2012 in 35 homes located in Toronto, Canada with a mean and maximum concentration of 1.74 and 6262 ng/wipe, respectively(6). Decabromodiphenyl ethane was also detected in audio/video devices and household appliances sampled in the same study(6).|The concentration of decabromodiphenyl ethane was reported in children's toys purchased Oct 2007 to Apr 2008 from markets in Guangzhou City, South China(1). Toys were divided into four categories: hard plastic (race cars, vehicles, weapons, action figures, hand-held video game consoles), foam toys (mats, puzzles, swords), rubber/soft plastic toys (Barbie dolls, teethers) and textile and stuffed toys (animals, dolls, Christmas toys)(1).[Table#8483]

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.

LD50 Rat oral 5000 mg/kg bw[ECHA; 1,1'-(ethane-1,2-diyl)bis|LD50 Rabbit dermal 2000 mg/kg bw[ECHA; 1,1'-(ethane-1,2-diyl)bis

/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.|/AQUATIC SPECIES/ The potential toxicity of decabromodiphenyl ethane (DBDP-Ethane) was explored in 5 types of organisms residing in the water column and/or sediment, e.g. Oncorhynchus mykiss, Pseudokirchneriella subcapitata, Daphnia magna, Chironmus riparius, and Lumbriculus variegates. Fish, algae or Daphnia were unaffected by acute exposures to water accommodated fractions of 110 mg DBDP-Ethane/L. Chronic exposure to DBDP-Ethane at the highest dose tested, 5000 mg/kg dry sediment, did not affect midge mean development times, emergence or development rates or oligochaete survival, reproduction or dry weight. The chronic EC50, LOEC and NOEC were =5000 mg/kg in the two sediment species. Applying an assessment factor of 50, the unbounded predicted no effect concentration (PNEC(sediment)) was 100 mg/kg dry sediment. The calculated PNEC indicates DBDPE-Ethane presents little risk to sediment organisms. These results add to DBDP-Ethane's existing database in the terrestrial compartment and mammals.|For more Ecotoxicity Excerpts (Complete) data for Decabromodiphenyl ethane (6 total), please visit the HSDB record page.

Decabromodiphenyl ethane's production and use as an additive flame retardant(1) may result in its release to the environment through various waste streams(SRC).

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 is not expected to undergo hydrolysis in the environment due to the lack of functional groups that hydrolyze under environmental conditions(1). Decabromodiphenyl ethane does not contain chromophores that absorb at wavelengths >290 nm(1) and, therefore, is not expected to be susceptible to direct photolysis by sunlight(SRC).

An estimated BCF of 7 was calculated in fish for decabromodiphenyl ethane(SRC), using an estimated log Kow of 13.64(1) and a regression-derived equation(1). According to a classification scheme(2), this BCF suggests the potential for bioconcentration in aquatic organisms is low. The predator/prey biomagnification factor for decabromodiphenyl ethane in kingfishers/prey fish was calculated to be 0.10-0.77(3).

Using a structure estimation method based on molecular connectivity indices(1), the Koc of decabromodiphenyl ethane can be estimated to be 2.4X10+6(SRC). According to a classification scheme(2), this estimated Koc value suggests that decabromodiphenyl ethane is expected to be immobile in soil.

The Henry's Law constant for decabromodiphenyl ethane is estimated as 2.9X10-8 atm-cu m/mole(SRC) using a fragment constant estimation method(1). This Henry's Law constant indicates that decabromodiphenyl ethane is expected to be essentially nonvolatile from water and moist soil surfaces(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(SRC), determined from a fragment constant method(1).

SURFACE WATER: The mean concentration of decabromodiphenyl ethane was reported as 1.1, 0.25, 0.68, 10.8 and 6.7 pg/L in aqueous samples collected Apr-May 2011 and Apr-Jun 2012 from Lakes Erie, Huron, Michigan, Ontario and Superior, respectively(1). Decabromodiphenyl ethane was detected at geometric mean concentrations of 6.6, 100, 23, 20 and 18 pg/L in 11, 12, 12, 11 and 13 surface water samples collected in 2015 from Indiana Harbor/Ship Canal, Saint Joseph River, Kalamazoo River, Grand River and Lower Fox River, respectively; sample locations are in the states of Michigan, Indiana and Wisconsin(2).|RAIN/SNOW/FOG: Decabromodiphenyl ethane was detected in precipitation samples collected 2005-2009 from Eagle Harbor, Chicago, Sleeping Bear Dunes, Cleveland and Sturgeon Point in the Great Lakes region at 0.3; 0.8; 0.4; 0.6 and 0.5 ng/L, respectively(1).

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).

According to the 2016 TSCA Inventory Update Reporting data, 11 reporting facilities estimate the number of persons reasonably likely to be exposed in the manufacturing, processing, or use of decabromodiphenyl ethane in the United States may be as low as <10 workers up to the range of 50-99 workers per plant; the data may be greatly underestimated due to confidential business information (CBI) or unknown values(1).|Occupational exposure to decabromodiphenyl ethane may occur through dermal contact with this compound at workplaces where decabromodiphenyl ethane is produced or used. Monitoring data indicate that the general population may be exposed to decabromodiphenyl ethane via inhalation of ambient air, ingestion of food, and dermal contact with consumer products containing decabromodiphenyl ethane. (SRC)

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).

Male rats were orally administrated with corn oil containing 100 mg/kg bw/day of DBDPE or BDE-209 for 90 days, after which the levels of DBDPE and BDE-209 in the liver, kidney, and adipose were measured. Biochemical parameters, including thyroid hormone levels, 13 clinical chemistry parameters, and the mRNA expression levels of certain enzymes were also monitored. Results showed DBDPE was found in all tissues with concentrations 3-5 orders of magnitude lower than BDE-209.|/MILK/ We have examined several emerging brominated flame retardants (BFRs) including 2-ethyl-1-hexyl-2,3,4,5-tetrabromobenzoate (TBB), bis(2-ethylhexyl) tetrabromophthalate (TBPH), 1,2-bis(2,4,6-tribromophenoxy) ethane (BTBPE), 4,5,6,7-tetrabromo-1,1,3-trimethyl-3-(2,3,4,5-tetrabromophenyl)-indane (OBIND), and decabromodiphenyl ethane (DBDPE) in paired human maternal serum (n = 102) and breast milk (n = 105) collected in 2008-2009 in the Sherbrooke region in Canada. Three legacy BFRs were also included in the study for comparison: decabromobiphenyl (BB-209), 2,2',4,4',5,5'-hexabromobiphenyl (BB-153), and 2,2',4,4',5,5'-hexabromodiphenyl ethers (BDE-153). TBB, BB-153, and BDE-153 had detection frequencies greater than 55% in both serum and milk samples. Their lipid weight (lw) adjusted median concentrations (ng g(-1) lw) in serum and milk were 1.6 and 0.41 for TBB, 0.48 and 0.31 for BB-153, and 1.5 and 4.4 for BDE-153, respectively. The detection frequencies for the other BFRs measured in serum and milk were 16.7% and 32.4% for TBPH, 3.9% and 0.0% for BTBPE, 2.0% and 0.0% for BB-209, 9.8% and 1.0% for OBIND, and 5.9% and 8.6% for DBDPE. The ratio of TBB over the sum of TBB and TBPH (fTBB) in serum (0.23) was lower than that in milk (0.46), indicating TBB has a larger tendency than TBPH to be redistributed from blood to milk. Overall, these data confirm the presence of non-PBDE BFRs in humans, and the need to better understand their sources, routes of exposure, and potential human health effects|Decabromodiphenyl ethane (DBDPE), a replacement for decabromodiphenyl ether (deca-BDE), was investigated in captive Chinese alligators from China. DBDPE was detected in adult tissues, neonates and eggs of Chinese alligators with concentrations ranging from 4.74-192, 0.24-1.94, and 0.01-0.51 ng g(-1) lipid weight, respectively. Compared to PBDEs and PCBs, DBDPE contamination was limited in Chinese alligators. Additionally, DBDPE concentrations in adult muscles were one to three orders of magnitude higher than those in neonates and eggs, suggesting the limited maternal transfer potential of DBDPE in Chinese alligators. ...|Hen muscle, eggs, and newborn chick tissues (muscle and liver) were collected from an electronic waste recycling site in southern China. The authors examined the maternal transfer, potential metabolism, and tissue distribution of several halogenated flame retardants (HFRs) during egg formation and chicken embryo development. The pollutant composition changes significantly from hen muscle to eggs and from eggs to tissues of newborn chicks. Higher-halogenated chemicals, such as octa- to deca-polybrominated diphenyl ether (PBDE) congeners, deca-polybrominated biphenyl (PBB209), and dechlorane plus (DP), are less readily transferred to eggs compared with lower-halogenated chemicals. During embryo development, PBDEs are the most likely to be metabolized, whereas decabromodiphenyl ethane (DBDPE) is the least. The authors also observed selective maternal transfer of anti-DP and stereoselective metabolism of syn-DP during chicken embryo development. During tissue development, liver has greater affinity than the muscle for chemcials with a high log octanol-water partition coefficient, with the exception of DBDPE. The differences in metabolism potential of different chemicals in chicken embryos cause pollutant composition alterations. Halogenated flame retardant from maternal transfer and tissue distribution also exhibited chemical specificity, especially for DBDPE. Levels of DBDPE were elevated along with the full process from hen muscle to eggs and from eggs to chick tissues. ...|The extensive use of polybrominated diphenyl ethers (PBDEs) and decabromodiphenyl ethane (DBDPE) has made them widespread contaminants in abiotic environments, but data regarding their bioavailability to benthic organisms are sparse. The bioaccumulation potential of PBDEs and DBDPE from field-collected sediment was evaluated in the oligochaete Lumbriculus variegatus using a 49-d exposure, including a 28-d uptake and a 21-d elimination phase. All PBDEs and DBDPE were bioavailable to the worms with biota-sediment accumulation factors (BSAFs) ranging from 0.0210 g organic carbon/g lipid to 4.09 g organic carbon/g lipid. However, the bioavailability of highly brominated compounds (BDE-209 and DBDPE) was poor compared with that of other PBDEs, and this was confirmed by their relatively low freely dissolved concentrations (C(free)) measured by solid-phase microextraction. The inverse correlation between BSAFs and hydrophobicity was explained by their uptake (k(s)) and elimination (k(e)) rate constants. While ke changed little for PBDEs, ks decreased significantly when chemical hydrophobicity increased. The difference in bioaccumulation kinetics of brominated flame retardants in fish and the worms was explained by their physiological difference and the presence of multiple elimination routes. The appropriateness of 28-d bioaccumulation testing for BSAF estimation was validated for PBDEs and DBDPE. In addition, C(free) was shown to be a good indicator of bioavailability.

At least seven unknown compounds were observed in the DBDPE-exposed rats, indicating that DBDPE biotransformation occurred in rats. These compounds were identified by comparing relative retention times and full-scan mass spectra of DBDPE debrominated products from a photolytic degradation experiment using GC/EI-MS and GC/ECNI-MS analysis. The results showed that debromination of DBDPE to lower brominated BDPEs were not the primary metabolic pathway observed in rats. Two of the metabolites were proposed tentatively as MeSO(2)-nona-BDPE and EtSO(2)-nona-BDPE using GC/EI-MS, but their structures require further confirmation by other techniques and authentic standards. In addition, evidence of a biological response to DBDPE and BDE-209 and their metabolites in rats are different.|The present study assessed and compared the oxidative and reductive biotransformation of brominated flame retardants, including established polybrominated diphenyl ethers (PBDEs) and emerging decabromodiphenyl ethane (DBDPE) using an in vitro system based on liver microsomes from various arctic marine-feeding mammals: polar bear (Ursus maritimus), beluga whale (Delphinapterus leucas), and ringed seal (Pusa hispida), and in laboratory rat as a mammalian model species. Greater depletion of fully brominated BDE209 (14-25% of 30 pmol) and DBDPE (44-74% of 90 pmol) occurred in individuals from all species relative to depletion of lower brominated PBDEs (BDEs 99, 100, and 154; 0-3% of 30 pmol). No evidence of simply debrominated metabolites was observed. Investigation of phenolic metabolites in rat and polar bear revealed formation of two phenolic, likely multiply debrominated, DBDPE metabolites in polar bear and one phenolic BDE154 metabolite in polar bear and rat microsomes. For BDE209 and DBDPE, observed metabolite concentrations were low to nondetectable, despite substantial parent depletion. These findings suggested possible underestimation of the ecosystem burden of total-BDE209, as well as its transformation products, and a need for research to identify and characterize the persistence and toxicity of major BDE209 metabolites. Similar cause for concern may exist regarding DBDPE, given similarities of physicochemical and environmental behavior to BDE209, current evidence of biotransformation, and increasing use of DBDPE as a replacement for BDE209.

/SRP:/ Immediate first aid: Ensure that adequate decontamination has been carried out. If patient is not breathing, start artificial respiration, preferably with a demand valve resuscitator, bag-valve-mask device, or pocket mask, as trained. Perform CPR if necessary. Immediately flush contaminated eyes with gently flowing water. Do not induce vomiting. If vomiting occurs, lean patient forward or place on left side (head-down position, if possible) to maintain an open airway and prevent aspiration. Keep patient quiet and maintain normal body temperature. Obtain medical attention. /Poisons A and B/|/SRP:/ Basic treatment: Establish a patent airway (oropharyngeal or nasopharyngeal airway, if needed). Suction if necessary. Watch for signs of respiratory insufficiency and assist ventilations if needed. Administer oxygen by nonrebreather mask at 10 to 15 L/min. Monitor for pulmonary edema and treat if necessary ... . Monitor for shock and treat if necessary ... . Anticipate seizures and treat if necessary ... . For eye contamination, flush eyes immediately with water. Irrigate each eye continuously with 0.9% saline (NS) during transport ... . Do not use emetics. For ingestion, rinse mouth and administer 5 mL/kg up to 200 mL of water for dilution if the patient can swallow, has a strong gag reflex, and does not drool ... . Cover skin burns with dry sterile dressings after decontamination ... . /Poisons A and B/|/SRP:/ Advanced treatment: Consider orotracheal or nasotracheal intubation for airway control in the patient who is unconscious, has severe pulmonary edema, or is in severe respiratory distress. Positive-pressure ventilation techniques with a bag valve mask device may be beneficial. Consider drug therapy for pulmonary edema ... . Consider administering a beta agonist such as albuterol for severe bronchospasm ... . Monitor cardiac rhythm and treat arrhythmias as necessary ... . Start IV administration of D5W TKO /SRP: "To keep open", minimal flow rate/. Use 0.9% saline (NS) or lactated Ringer's (LR) if signs of hypovolemia are present. For hypotension with signs of hypovolemia, administer fluid cautiously. Watch for signs of fluid overload ... . Treat seizures with diazepam (Valium) or lorazepam (Ativan) ... . Use proparacaine hydrochloride to assist eye irrigation ... . /Poisons A and B/

/ALTERNATIVE and IN VITRO TESTS/ OBJECTIVE: To investigate the toxic effects of decabromodiphenyl ethane (DBDPE), used as an alternative to decabromodiphenyl ether in vitro. METHODS: HepG2 cells were cultured in the presence of DBDPE at various concentrations (3.125-100.0 mg/L) for 24, 48, and 72 hr respectively and the toxic effect of DBDPE was studied. RESULTS: As evaluated by the 3-(4,5-dimethylthiazol-2-yl)-2,5-diphenyl tetrazolium bromide and lactate dehydrogenase assays and nuclear morphological changes, DBDPE inhibited HepG2 viability in a time- and dose-dependent manner within a range of 12.5 mg/L to 100 mg/L and for 48 hr and 72 hr. Induction of apoptosis was detected at 12.5-100 mg/L at 48 h and 72 hr by propidium iodide staining, accompanied with overproduction of reactive oxygen species (ROS). Furthermore, N-acetyl-L-cysteine, a widely used ROS scavenger, significantly reduced DBDPE-induced ROS levels and increased HepG2 cells viability. CONCLUSION: DBDPE has cytotoxic and anti-proliferation effect and can induce apoptosis in which ROS plays an important role.

1,2-bis(pentabromophenyl)ethane

Custom compounding of purchased resin|Benzene, 1,1'-(1,2-ethanediyl)bis[2,3,4,5,6-pentabromo-: ACTIVE|PMN - indicates a commenced PMN (Pre-Manufacture Notices) substance.

This study presents the development and validation of a new analytical method for the simultaneous determination of fifteen analytes classified as halogenated flame retardants (HFRs) - nine brominated diphenyl ethers (BDEs) and six novel HFRs - in different kinds of mollusks using matrix solid-phase dispersion (MSPD) followed by gas chromatography coupled to negative chemical ionization-mass spectrometry (GC-NCI-MS). The proposed method is the first one developed for such a broad range of HFRs in aquatic biota, featuring several advantages, including low solvent and sample intake, simplicity of operation, reduced cost and integration of extraction and clean-up into a single step. Under optimal conditions, 0.5 g of freeze-dried sample, 0.5 g of a primary-secondary amine (PSA) as solid support, a sorbent combination of 1.75 g of florisil (deactivated with 5% Milli-Q water), 1.75 g of acidified silica (10% (w/w) H2SO4) and 0.5 g of silica, and 10 mL dichloromethane as elution solvent were used. Standard addition over the extract was required however for the correct quantification due to matrix effects in the GC system, particularly for novel HFRs, that could not be compensated with the internal standards. The method afforded LODs in the range of 0.003-0.07ng/g dry weight (0.0006-0.014ng/g on a wet weight basis, assuming an 80% sample water content), except for decabromodiphenyl ethane (DBDPE) (0.6ngg(-1) dry weight, 0.12ngg(-1) wet weight). The accuracy of the method was evaluated with three different types of spiked mollusk species using surrogate standards and standard addition over the extract for quantification and the recoveries were in the 70-120% range, except for bis(2-ethylhexyl)-3,4,5,6-tetrabromo-phthalate (DEHTBP) in clam (Ruditapes philippinarum) samples (46% recovery). Moreover, the method was successfully validated with standard reference materials (SRMs) of salmon and mussel tissues for BDEs. Finally, the method was applied to the determination of HFRs in different kind of freeze-dried mollusks: mussel (Mytilus galloprovincialis), cockle (Cerastoderma edule) and clam (R. philippinarum). Raft cultured mussels showed the highest concentrations of HFRs (up to 0.8ng/g wet weight of BDE-209).|The analysis of brominated flame retardants (BFRs) commonly relies on the use of gas chromatography coupled to mass spectrometry (GC-MS) operating in electron ionization (EI) and electron capture negative ionization (ECNI) modes using quadrupole, triple quadrupole, ion trap, and magnetic sector analyzers. However, these brominated contaminants are examples of compounds for which a soft and robust ionization technique might be favorable since they show high fragmentation in EI and low specificity in ECNI. In addition, the low limits of quantification (0.01 ng/g) required by European Commission Recommendation 2014/118/EU on the monitoring of traces of BFRs in food put stress on the use of highly sensitive techniques/methods. In this work, a new approach for the extremely sensitive determination of BFRs taking profit of the potential of atmospheric pressure chemical ionization (APCI) combined with GC and triple quadrupole (QqQ) mass analyzer is proposed. The objective was to explore the potential of this approach for the BFRs determination in samples at pg/g levels, taking marine samples and a cream sample as a model. Ionization and fragmentation behavior of 14 PBDEs (congeners 28, 47, 66, 85, 99, 100, 153, 154, 183, 184, 191, 196, 197, and 209) and two novel BFRs, decabromodiphenyl ethane (DBDPE) and 1,2-bis(2,4,6-tribromophenoxy)ethane (BTBPE), in the GC-APCI-MS system has been investigated. The formation of highly abundant (quasi) molecular ion was the main advantage observed in relation to EI. Thus, a notable improvement in sensitivity and specificity was observed when using it as precursor ion in tandem MS. The improved detectability (LODs < 10 fg) achieved when using APCI compared to EI has been demonstrated, which is especially relevant for highly brominated congeners. Analysis of samples from an intercomparison exercise and samples from the marine field showed the potential of this approach for the reliable identification and quantification at very low concentration levels.|Numerous halogenated organic compounds have been identified as pollutants of concern. Those with high persistence and hydrophobicity may concentrate in biota, sediments, and wastewater sludge. Nonetheless, the release to the environment of many remains largely unrecognized. Stabilized sewage sludge (biosolids) is increasingly being land-applied as a soil amendment. However, understanding the risks of land application has been hampered by the compositional complexity of biosolids. Compound specific analytical approaches may also underestimate environmental impact of land application by overlooking additional contaminants. However, utilizing an alternative analytical approach based on compound functional group (i.e., alkyl halides) enhanced the information content of the analysis. To illustrate, 49 organohalogens were observed by gas chromatography with electron capture negative ionization mass spectrometry in sewage sludge; 23 identified as flame-retardants: that is, PBDEs, hexabromocyclododecane, 2-ethylhexyl 2,3,4,5-tetrabromobenzoate (TBB), 2-ethylhexyl tetrabromophthalate, decabromodiphenyl ethane, 1,2-bis (2,4,6-tribromophenoxy) ethane and Dechlorane Plus. Concentrations ranged from 25 to 1,600,000 ng g(-1) total organic carbon. An additional 16 compounds were tentatively identified as triclosan, chlorinated-methoxy triclosan, chlorinated pesticides, hexachlorobiphenyl, TBB degradation products, brominated furans and nonabromochlorodiphenyl ethers. Such an analytical approach may enhance evaluations of the risks associated with biosolids land-application and assist in prioritizing specific chemicals for future environmental fate and toxicology studies.|Methods for environmental analysis of higher brominated diphenyl ethers (PBDEs), in particular decabromodiphenyl ether (BDE209), and the recently discovered environmental contaminant decabromodiphenyl ethane (deBDethane) are reviewed. The extensive literature on analysis of BDE209 has identified several critical issues, including contamination of the sample, degradation of the analyte during sample preparation and GC analysis, and the selection of appropriate detection methods and surrogate standards. The limited experience with the analysis of deBDethane suggests that there are many commonalities with BDE209. The experience garnered from the analysis of BDE209 over the last 15 years will greatly facilitate progress in the analysis of deBDethane.

Emerging flame retardants are used in a great variety of household goods and thus have the potential to pollute our indoor environment. Health concerns regarding exposure to these flame retardants demand new methods to survey their occurrence in humans. This work describes development and optimization of an analytical method comprising solid phase extraction and gas chromatography coupled to mass spectrometry for the determination of besides 15 polybrominated diphenyl ethers, 7 emerging halogenated flame retardants in human serum (1,2-bis[2,4,6-tribromophenoxy] ethane, decabromodiphenyl ethane, hexabromobenzene, Dechlorane Plus(), hexachlorocyclopentenyl-dibromocyclooctane, dechlorane 602 and 603). The method was thoroughly validated at three spiking levels obtaining averaged recoveries >80% with a RSD of 5% (n=12). Accuracies ranged from 88 to 125% except for DBDPE, which averaged 66% with overall RSD of 11% (n=12). Method limits of detection (MLD) ranged from 0.3 to 5.4 pg/mL serum, except for decabromodiphenyl ether and decabromodiphenyl ethane for which MLDs were 14 and 20 pg/mL serum, respectively. In human serum samples from Norway, we were able to detect and quantify hexabromobenzene, 1,2-bis[2,4,6-tribromophenoxy] ethane, Dechlorane Plus(), Dechlorane 602 and 603.