PBDEs: Sjodin's response.
Pentabromodiphenyl ether (pentaBDE), along with the lower brominated congeners, was the topic of our investigation (Sjodin et al. (2004). Cleet's statement emphasizing that the current production of PBDEs is solely in the form of decabromodiphenyl ether belittles the fact that, in 2001, 95% of the 7,500 metric tons of pentaBDE was produced and consumed in the United States [Bromine Science and Environmental Forum (BSEF) 2003]. The industry's withdrawal of pentaBDE and octabromodiphenyl ether (octaBDE) from the market by the end of 2004 will decrease environmental output. However, continued monitoring of environmental and human levels is needed to measure exposures originating from pentaBDE and octaBDE manufactured before 2005 and to study potential exposure to decaBDE, which will continue to be manufactured.
Cleet's second remark proposes the possibility that current human PBDE levels have reached a plateau. Because of the variability in our data (Sjodin et al. (2004) and the regionalized sampling, we believe such a conclusion may be premature. As Cleet mentions later in his letter, these studies may not be representative of U.S. and European populations. We did not claim that the sampled pools are representative. To further confirm and track our preliminary observations of human exposure to PBDEs, broader representative studies have been proposed.
Cleet's third issue concerns comparability of our data on BDE-47 with earlier studies. We referenced several publications regarding the similarity of our measured levels to earlier findings. In a 1988 Illinois study, human levels of BDE-47 were reported to be 0.63 ng/g lipid, with a range of < 0.4-24 ng/g lipid (Sjodin et al. 2001). These Illinois levels can be contrasted to the data from serum pools collected in the southeastern United States, where we found a range of < 1-6 ng/g lipid for the same year [see Figure 1 in our paper (Sjodin et al. 2004)]. We also compared our BDE-47 levels to those in other studies: for example, 33 ng/g lipid in breast adipose tissue (range 7-200 ng/g) collected in the late 1990s (She et al. 2002); 83 ng/g lipid in a milk pool (n = 19) collected in 1997 in New York (Betts 2002); 130 ng/g lipid in a milk pool collected in 2000 in Austin, Texas, and Denver, Colorado (Papke et al. 2001); and 41 ng/g lipid in milk collected in 2001 in Texas (Schecter et al. 2003). These authors reported concentrations in the same range as our study [e.g., Figure 1 in our paper (Sjodin et al. 2004)].
I appreciate Cleet's clarification concerning production stoppage of hexabromobiphenyl (hexaBB) in Europe. Also, Cleet's speculation about the differences in outcomes in animal studies is potentially useful. Although we did not study toxic effects of PBDEs, we asserted the cited studies to be examples of potential concern. We selected the work of Eriksson and colleagues in this regard, demonstrating observed effects in four publications: Eriksson et al. (2001, 2002), Viberg et al. (2002), and Sand et al. (2004).
The author declares he has no competing financial interests.
Betts K S. 2002. Rapidly rising PBDE levels in North America. Environ Sci Technol 36: 50A-52A.
BSEF. 2003. Major Brorninated Flame Retardants Volume Estimates: Total Market Demand By Region in 2001. Brussels:Bromine Science and Environmental Forum. Available: http://www.bsef-site.com/docs/R FR_vols_2001.doc [accessed 20 October 2004].
Eriksson P, Jakobsson E, Fredriksson A. 2001. Brominated flame retardants: a novel class of developmental neurotoxicants in our environment? Environ Health Perspect 109: 903-908.
Eriksson P, Viberg H, Jakobsson E, Orn U, Fredriksson A. 2002. A brominated flame retardant, 2,2',4,4',5-pentabromodiphenyl ether: uptake, retention, and induction of neurobehavioral alterations in mice during a critical phase of neonatal brain development. Toxicol Sci 67:98-103.
Papke O, Bathe L, Bergman [Angstrom], Furst P, Meironyte Guvenius D, Herrmann T, et al. 2001. Determination of PBDEs in human milk from the United States--comparison of results from three laboratories. Organohalogen Compounds 52:197-200.
Sand S, von Rosen D, Eriksson P, Fredriksson A, Viberg H, Victorin K, et al. 2004. Dose-response modeling and benchmark calculations from spontaneous behavior data on mice neonatally exposed to 2,2',4,4',5-pentabromodiphenyl ether. Toxicol Sci 81: 491-501.
Schecter A, Pavuk M, Papke O, Ryan JJ, Birnbaum L, Rosen R. 2003. Polybrominated diphenyl ethers in U.S. mothers milk. Environ Health Perspect 111:1723-1729.
She J, Petreas M, Winkler J, Visita P, McKinney M, Kopec D. 2002. PBDEin the San Francisco Bay area: measurement in harbor seal blubber and human breast adipose tissue. Chemosphere 46:697-707.
Sjodin A, Jones R, Focant JF, Lapeza C, Wang R, McGahee E, et al. 2004. Retrospective time-trend study of polybrominated diphenyl ether and polybrominated and polychlorinated biphenyl levels in human serum from the United States. Environ Health Perspect 112:654-658.
Sjodin A, Patterson DG Jr, Bergman [Angstrom]. 2001. Brominated flame retardants in serum from U.S. blood donors. Environ Sci Technol 35:3830-3833.
Viberg H, Fredriksson A, Eriksson P. 2002. Neonatal exposure to the brominated flame retardant 2,2',4,4',5-pentabromodiphenyl ether causes altered susceptibility in the cholinergic transmitter system in the adult mouse. Toxicol Sci 67:104-107.
Center for Disease Control and Prevention
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|Title Annotation:||Perspectives / Correspondence|
|Publication:||Environmental Health Perspectives|
|Date:||Dec 1, 2004|
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