Polybrominated diphenyl ethers. Polybrominated diphenyl ethers or PBDEs, are a class of organobromine compounds that are used as flame retardants. Like other brominated flame retardants, PBDEs have been used in a wide array of products, including building materials, electronics, furnishings, motor vehicles, airplanes, plastics, polyurethane foams, and textiles.  They are structurally akin to polychlorinated diphenyl ethers (PCDEs), polychlorinated biphenyls (PCBs) and other polyhalogenated compounds, consisting of two halogenated aromatic rings. PBDEs are classified according to the average number of bromine atoms in the molecule.  The life-saving benefits of fire retardants led to their popularization.  Standards for mass transit vehicles continues to increase as of 2021.

Because of their toxicity and persistence, all commercially relevant PBDEs have been marked for elimination under the Stockholm Convention, a treaty to control and phase out major persistent organic pollutants (POPs).

Classes of PBDEs
The family of PBDEs consists of 209 possible substances, which are called congeners (PBDE = C12H(10−x)BrxO (x = 1, 2, ..., 10 = m + n)).  The number of isomers for mono-, di-, tri-, tetra-, penta-, hexa-, hepta-, octa-, nona-, and decabromodiphenyl ethers are 3, 12, 24, 42, 46, 42, 24, 12, 3 and 1, respectively.

Lower-brominated PBDEs with 1–4 bromine atoms per molecule are regarded as more dangerous because they more efficiently bioaccumulate. They have been known to affect thyroid hormone levels, and studies have linked them to reproductive and neurological risks at certain concentrations or higher. Higher-brominated PBDEs are less acutely dangerous but biotically and photochemically debrominate to lower-brominated congeners.

Production
PBDEs were produced commercially via the bromination of diphenyl ether, with three technical-grade mixtures being sold, varying by degree of bromination.

In the United States, PBDEs were marketed with the trade names DE-60F, DE-61, DE-62, and DE-71 applied to pentaBDE mixtures, DE-79 applied to octaBDE mixtures, and DE 83R and Saytex 102E applied to decaBDE mixtures. The available commercial PBDE products were not single compounds or even single congeners but rather mixtures of congeners.

Technical pentaBDE predominantly contained pentabromo derivatives (50–62%); however, the mixture also contained tetrabromides (24–38%) and hexabromides (4–8%), as well as traces of the tribromides (0–1%). Technical octaBDE was a mixture of homologs: hexa-, hepta-, octa-, nona-, and decabromides. Technical decaBDE was 97% decabromide, with small amounts of octa- and nonabromides.

Commercial production of PBDEs began in the 1970s, and continued until the early 2010s. Cumulative global production is estimated to have been 175kt for pentaBDE, 130kt for octaBDE, and 1600kt for decaBDE.

Health and environmental concerns

Exposure

Polybrominated diphenyl ethers (PBDEs) can be released into the environment where they are used or produced, possibly entering air, water, soil or the human digestive system when consumed, inhaled or via the skin. Despite the banning and phase out of several forms of PBDEs, many consumer products still contain them in the 21st century, and represent potential exposure sources, including furniture and other consumer products containing polyurethane foam, appliances, pipes, plastics, and old electronic equipment.

Generally, governments have determined that PBDEs are not harmful to human health in the exposure amounts assessed. Ingestion of house dust accounts for 80-90% of total PBDE exposure, while the remaining exposure occurs from food ingestion. PBDE-contaminated foods, particularly those high in fat content, such as fatty meats or fish, are possible sources of exposure. In breastfeeding infants, breast milk may be an exposure source because PBDEs can be present in the mother and her milk. Various other food items may contain PBDEs, including meat, meat products, dairy products,  and seafood. 

PBDEs have not been detected beyond trace levels in water. In the environment, soils and sediments are the major deposits for PBDEs. PBDEs can enter soil from discarded products, such as in landfills. As biosolids (sewage) may contain PBDEs, exposure from soils or farmlands that have been fertilized with biosolids may occur. Wildlife may have exposure by consuming foods containing PBDEs, whereas organisms that live in sediments may be contaminated by PBDEs.

Excretion
PBDEs and their metabolites are excreted mainly in the feces and some in the urine. Owing to their deposition in body fat stores, some PBDEs remain in the body for many years, and may enter the bodies of unborn babies via the placenta.

Research on health effects
Nothing certain has been established about the effects of PBDEs on human health. Most information regarding toxicity of PBDEs and their metabolites is from early-stage animal studies. Evidence for PBDE-mediated effects from human studies in systems other than the developing nervous system, such as in cancer development, is inconclusive or non-existent. Particularly for the potential effects of PBDEs on the developing fetus, research has focused on the health status of mothers and gestational age of the infant.

Sediment contamination
Increasing environmental concentrations and changing distributions of PBDEs in sediments of the Clyde River Estuary in Scotland, UK have been assessed. Analysis of six sediment cores each of 1 m depth from Glasgow city to Greenock revealed that total concentrations increased toward the river bed surface (0–10 cm). Amounts of PBDE ranged from 1 to 2,645 µg/kg (dry wt. sediment) with a mean of 287 µg/kg (dry wt. sediment). Down-core PBDE congener profiles showed that higher concentrations were due to elevated levels of BDE-209. The majority of the sediment records clearly showed a change from mainly lower molecular weight BDEs 47,99, 183, 153 at lower depths to BDE-209 near the surface, a change in congener and homologue group patterns that corresponds to the restrictions of penta- and octaBDE commercial mixtures under EU law in 2004–2006.

While biodegradation is not considered the main pathway for PBDEs, photolysis and pyrolysis can be of interest in studies of transformation of PBDEs.

Regulations of PBDEs

United States
In August, 2003, the State of California outlawed the sale of penta- and octaBDE and products containing them, effective January 1, 2008. PBDEs are ubiquitous in the environment, and, according to the EPA, exposure may pose health risks. According to U.S. EPA's Integrated Risk Information System, evidence indicates that PBDEs may possess liver toxicity, thyroid toxicity, and neurodevelopmental toxicity. In June 2008, the U.S. EPA set a safe daily exposure level ranging from 0.1 to 7 μg/kg body weight per day for the four most common PBDE congeners. In April 2007, the legislature of the state of Washington passed a bill banning the use of PBDEs. The State of Maine Department of Environmental Protection has restrictions on PBDEs, and in 2008, the legislature passed a bill phasing out the use of decaBDE.

The U.S. importers and manufacturers of PBDEs withdrew pentaBDE and octaBDE from sale in 2004, and decaBDE from sale by the end of 2013. In November 2024, the EPA added decaBDE to the Toxic Substances Control Act to prohibit release into water during manufacturing, processing or distribution in commerce of decaBDE and decaBDE-containing products, and a phase-out of processing and distribution of wire and cable insulation containing decaDBE for nuclear power facilities.

Canada
Since 2012, PBDEs are among chemicals prohibited from manufacture, use, sale, offer for sale or import, as regulated in the Prohibition of Certain Toxic Substances Regulations of the 1999 Canadian Environmental Protection Act. PBDEs are regarded in the regulation as  "toxic to the environment and/or human health, are generally persistent, bioaccumulative, and/or inherently toxic."

European Union
The European Union decided to ban the use of two classes of flame retardants, in particular, PBDEs and polybrominated biphenyls (PBBs) in electric and electronic devices. This ban was formalised in the RoHS Directive, and an upper limit of 1 g/kg for the sum of PBBs and PBDEs was set. In February 2009, the Institute for Reference Materials and Measurements released two certified reference materials to help analytical laboratories better detect these two classes of flame retardants. The reference materials were custom-made to contain all relevant PBDEs and PBBs at levels close to the legal limit.

International
At an international level, in May 2009 the Parties of the Stockholm Convention on Persistent Organic Pollutants (POPs) decided to list commercial pentaBDE and commercial octaBDE as POP substances. This listing is due to the properties of hexaBDE and heptaBDE, which are components of commercial octaBDE, and to the properties of tetraBDE and pentaBDE, which are the main components of commercial pentaBDE. In 2017, it was decided to also list decaBDE.

Alternatives
Major decaBDE producers have switched to manufacturing decabromodiphenyl ethane, a structurally related compound that has also come under suspicion as an environmental pollutant. Non-halogenated alternatives also exist.

References

External links 
 U.S. EPA. An Exposure Assessment of Polybrominated Diphenyl Ethers. U.S. Environmental Protection Agency, Washington, DC, EPA/600/R-08/086F, 2010
 Sandy, Martha. Polybrominated Diphenyl Ethers: Recommendations to Reduce Exposure in California. Office of Environmental Health Hazard Assessment. 25 Apr. 2008
 Polybrominated diphenylethers (PBDEs) | U.S. Environmental Protection Agency

Flame retardants
Endocrine disruptors
Persistent organic pollutants under the Stockholm Convention
Bromoarenes
Diphenyl ethers