The term flame retardants defines a diverse group of chemicals added to manufactured materials, such as plastics and textiles, as well as coatings and surface coatings. Flame retardants are activated by the presence of an ignition source and are intended to prevent or slow the further development of ignition by different physical and chemical methods. They may be added as copolymers during polymerization of polymers, mixed with polymers on the molding or extrusion process or, particularly for textiles, applied as topical finishes. Mineral flame retardants are usually additive while organohalogen and organophosphorus compounds can be reactive or additive.
Video Flame retardant
Class
Both types of Reactive and Additive Flame retardants, can be further separated into different classes:
- Minerals such as aluminum hydroxide (ATH), magnesium hydroxide (MDH), hunters and hydromagnesites, various hydrates, red phosphorus, and boron compounds, mostly borate.
- Organohalogen compounds. This class includes organochlorines such as chlorendic acid derivatives and chlorinated paraffins; organobromins such as decabromodiphenyl ether (decaBDE), decabromodiphenyl ethane, polymeric brominated compounds such as brominated polystyrene, brominated bromine oligomers (BCOs), brominated epoxy oligomers (BEO), tetrabromophthalic anyhydride, tetrabromobisphenol A (TBBPA) and hexabromocyclododecane (HBCD). Most but not all halogenated flame retardants are used together with synergists to improve their efficiency. Antimony trioxide is widely used but other forms of antimony such as pentoxide and sodium antimonate are also used.
- Organophosphorus compounds. This class includes organophosphates such as triphenyl phosphate (TPP), resorcinol bis (diphenylphosphate) (RDP), bisphenol A diphenyl phosphate (BADP), and tricresyl phosphate (TCP); phosphonates such as dimethyl methylphosphonate (DMMP); and phosphinates such as aluminum diethyl phosphinate. In an important class of flame retardants, the compounds contain phosphorus and halogens. Such compounds include tris (2,3-dibromopropyl) phosphate (brominated tris) and chlorinated organophosphates such as tris (1,3-dichloro-2-propyl) phosphate (chlorine tris or TDCPP) and tetrakis (2-chlorethyl) dichloroisopentyldiphosphate ( V6). ).
The flame retardants of minerals primarily act as additive flame retardants and do not become chemically attached to the surrounding system. Most organohalogen compounds and organophosphates also do not react permanently to attach themselves to their environment but further work is now done to graft further chemical groups into these materials to enable them to become integrated without losing their inhibiting efficiency. It will also make these materials not radiate to the environment. Some of the new non-halogen products, with these reactive and impartial characteristics, have been on the market since 2010, due to the public debate about refractory emissions. Some of these new Reactive materials have even received US-EPA approval for their low environmental impact.
Maps Flame retardant
Retardation mechanism
The basic mechanism of flame retardance varies depending on the specific flame retardant and the substrate. Refractory and reactive chemicals may function either in the vapor (gas) or solid (solid) phases.
Endothermic degradation
Some compounds break down endothermic when experiencing high temperatures. Magnesium and aluminum hydroxide are examples, together with various carbonates and hydrates such as mixtures of huntite and hydromagnesite. The reaction removes heat from the substrate, thus cooling the material. The use of hydroxide and hydrate is limited by a relatively low decomposition temperature, which limits the maximum processing temperature of the polymer (usually used in polyolefins for wire and cable applications).
Thermal shielding
The way to stop the spread of fire on the material is to create a thermal insulation barrier between burned and non-burning parts. Intumescent additives are often used; its role is to change the surface of the polymer into charcoal, which separates the flame from the material and slows the heat transfer to unburned fuel. Inhaled phosphorus inorganic and organic phosphorus inhibitors typically act through this mechanism by producing a polymeric layer of charred phosphoric acid.
Gas phase dilution
Inert gases (most often carbon dioxide and water) produced by thermal degradation of some materials act as diluents of flammable gases, lowering their partial pressure and oxygen partial pressures, and slowing down the reaction rate.
Gas phase radical shutdown
Chlorinated and brominated materials undergo thermal degradation and release hydrogen chloride and hydrogen bromide or, when used in the presence of synergists such as antimony trioxide, antimony halides. It reacts with a very high H Ã, Â · and OH Ã, Â · in a flame, producing inactive molecules and Cl Ã, Â · or Br Ã, Â · radical. Halogen radicals are less reactive compared to H Ã, Â · or OH Ã, Â · , and therefore have much lower potency to propagate radical oxidation reactions from combustion.
Use and effectiveness
Fire safety standard
Flame retardants are usually added to industrial and consumer products to meet flammability standards for furniture, textiles, electronics, and building products such as insulation.
In 1975, California began implementing the 117th Technical Bulletin (TB 117), which requires materials such as polyurethane foam used to fill furniture can withstand small open flames, equivalent to candles, for at least 12 seconds. In polyurethane foams, furniture manufacturers usually meet 117 TB with halogenated organic retardant additives. Although no other US state has the same standards, since California has a very large market, many manufacturers are meeting TB 117 in products distributed throughout the United States. Proliferation of flame retardants, and in particular halogenated organic flame retardants, in furniture throughout the United States is strongly associated with TB 117.
Responding to concerns about the health effects of flame retardants in upholstered furniture, in February 2013 California proposed modifying TB 117 to require that fabric covering upholstered furniture meet the coal test and to eliminate flammable foam standards. Governor Jerry Brown signed TB117-2013 which was modified in November and became effective by 2014. The modified rule does not require the reduction of flame retardants.
However, these questions to remove emissions into the environment from flame retardants can be solved by using a new classification of highly efficient flame retardants, which contain no halogen compounds, and which can also be typed permanently into the chemical structure of the foams used in the furniture industry and bed. The resulting foam has been certified to produce no fire retardant emissions. The new technology is based on a completely newly developed "Green Chemistry" with a final foam containing about one-third the weight of natural oil. The use of this technology in the production of 117 TB of California foam, will enable ongoing protection for consumers against open flame lighting while providing newly recognized and newly needed protection against chemical emissions into the home and office environment. More recent work in 2014 with "Green Chemistry" shows that a foam containing about fifty percent of natural oils can be made that produces far less smoke when involved in a fire situation. This low-emission foam capability to reduce smoke emissions by up to 80% is an attractive property that will help escape from a fire situation and also reduce the risk for first responders ie emergency services in general and fire department personnel in particular.
In Europe, fireproof standards for furniture vary, and most tightly in the UK and Ireland. Generally the ratings of various general worldwide refractory tests for furniture and soft furnishings will show that the California Cal TB117 test - the 2013 test is the easiest to skip, there is an increasing difficulty in passing Cal TB117 -1975 followed by the UK BS 5852 test and followed by Cal TB133. One of the most demanding fire tests in the world is probably a US Federal Aviation Aviation test for aircraft seating involving the use of a kerosene burner that blows fire on a specimen. Greenstreet Berman's 2009 study, conducted by the British government, shows that in the period between 2002 and 2007, the UK Furniture Safety Safety Regulations contributed 54 fewer deaths per year, 780 fewer non-fatal casualties per year and 1065 fewer fires every year after the introduction of British furniture safety regulations in 1988.
Effectiveness
The effectiveness of refractory chemicals to reduce flammable consumer products in home fires is debatable. Advocates for the flame-retardant industry, such as the American Chemistry Council's American Flame Retardant Alliance, cite a study from the National Bureau of Standards which shows that a room full of spark-ignitioned products (polyurethane foam seats and some other objects, including cabinets and electronics ) offers a 15-fold window of time for occupants to escape from the room rather than similar spaces free from flame retardants. However, critics of this position, including the lead author, argue that the flame retardant rate used in the 1988 study, when found commercially, is much higher than the level required by TB 117 and is widely used in the United States on upholstered furniture.
Another study concluded flame retardants are an effective tool to reduce the risk of fire without creating toxic emissions.
Several studies in the 1980s tested ignition in all parts of furniture with different types of coatings and filling, including different refractory formulations. In particular, they see maximum heat release and time for maximum heat release, two main indicators of fire hazard. These studies found that this type of covering fabric had a major influence on the ease of ignition, that the cotton patch is much more flammable than the polyurethane foam filler, and that the interliner material substantially reduces the ignitionability. They also found that although some flame retardant formulations decrease the ease of ignition, the most basic formulations that meet TB 117 have very little effect. In one study, a foam filler that complied with TB 117 had an equivalent ignition time as the same foam filler without flame retardant. A report from the Proceedings of the Polyurethane Foam Association also shows no benefit in flame and cigarette testing with foam pads treated with flame retardants to meet 117 TB. However, other scientists support this open flame test.
Environmental and health issues
The environmental behavior of flame retardants has been studied since the 1990s. Especially brominated flame retardants are found in many environmental compartments and organisms including humans, and some individual substances are found to have toxic properties. Therefore, alternatives have been requested by the authorities, NGOs and equipment manufacturers. The EU-funded collaborative research project, ENFIRO (European Union research project FP7: 226563, concluded in 2012) starts from the assumption that not enough environmental and health data are known about alternatives to existing brominated fire retardants. To make the evaluation completely comprehensive, it was decided to compare also the performance of materials and APIs and to try lifecycle assessment of reference products containing halogen-free compared to brominated flame retardants. About a dozen halogen-free fire retardants are studied that represent a wide range of applications, from engineering plastics, printed circuit boards, encapsulation to textiles and intumescent layers. A large group of flame retardants studied were found to have good environmental and health profiles: ammonium polyphosphate (APP), Aluminum diethyl phosphinate (Alpi), aluminum hydroxide (ATH), magnesium hydroxide (MDH), melamine polyphosphate (MPP), dihydrooxaphosphaphenanthrene (DOPO) , zinc stannate (ZS) and zinc hydroxstannate (ZHS). Overall, they were found to have a much lower tendency to accumulate in fat tissue than the studied brominated flame retardants.
Tests on the flame retardant behavior of materials with different flame retardants revealed that halogen-free flame retardants produce less smoke and toxic fire emissions, with the exception of arth fosfat RDP and BDP in styrenic polymers. The washing experiment shows that the polymer properties are the dominating factor and that the halogen and brominated halogen-free fire retardant behavior is comparable. More porous or "hydrophilic" porous or more fire retardant polymers. However, plates representing real-world plastic products show a much lower leaching rate than extruded polymer granules. The impact assessment study reaffirms that improper waste and the treatment of recycling of electronic products with brominated flame retardants can produce dioxins that do not occur with halogen-free alternatives. Furthermore, the US Environmental Protection Agency (US-EPA) has implemented a series of projects related to environmental assessments of alternative fire retardants, environmental "design for environmental" projects on flame retardants for printed cable boards and alternatives to decabromo diphenylethers and hexabromocyclododecane (HBCD).
In 2009, the US National Oceanic and Atmospheric Administration (NOAA) released a report on diphenyl ether sheeting (PBDEs) and found that, in contrast to previous reports, they were found throughout the US coastal zone. The national survey found that the Hudson Raritan Estuary in New York had the highest overall PBDE concentrations, both in sediment and shellfish. Individual sites with the highest PBDE measurements were found on shells taken from Anaheim Bay, California, and four sites in Muara Raritan Hudson. Watersheds include Southern California Bight, Puget Sound, Gulf of Mexico central and east off the coast of Tampa and St. Louis. Petersburg, in Florida, and the waters of Lake Michigan near Chicago and Gary, Indiana, were also found to have high PBDE Concentrations.
Health issues
The earliest fire retardants, polychlorinated biphenyls (PCBs), were banned in the US in 1977 when it was discovered that they were toxic. The industry uses brominated flame retardants instead, but these are now receiving closer scrutiny. In 2004 and 2008 the EU prohibited some types of ethyl diphenyl ether (PBDEs). Negotiations between the EPA and two US manufacturers DecaBDE (flame retardant that has been used in electronics, wire and cable insulation, textiles, automobiles and aircraft, and other applications), Albemarle Corporation and Chemtura Corporation, and the largest US importer, ICL Industrial Products, Inc. , resulted in commitments by these companies to exit decaBDE for the majority of use in the United States on December 31, 2012, and to terminate all use by the end of 2013. The state of California has registered Tris chlorinated tris flame retardant (1 , 3-dichloro-2-propyl) phosphate or TDCPP) as a chemical known to cause cancer. In December 2012, the nonprofit California Environmental Health Center filed a notice of intent to sue several leading retailers and manufacturers of baby products for violating California laws for failing to label products containing this cancer-causing fire barrier. While the demand for brominated and chlorinated flame retardants in North America and Western Europe is decreasing, it is increasing in all other regions.
There is a potential relationship between exposure to Phosphorus Flame Retardants (PFR) in household dust and the development of allergies, asthma and dermatitis. A study was conducted in 2014 by Araki, A. et al. in Japan to assess this relationship. They found a significant relationship between Tris (2-chloro-iso-propyl) phosphate (TCIPP) and atopic dermatitis with an odds ratio of 2.43. They also found that Tributyl phosphate was associated with the development of allergic rhinitis and asthma with an odds ratio of 2.55 & amp; 2.85 each.
Almost all Americans tested have trace levels of flame retardant on their bodies. Recent research links some of the dust exposure to television sets, which may result from warming flame retardants on TV. Uncut TV removal and other equipment such as microwaves or old computers can greatly increase the amount of environmental pollution. A recent study conducted by Harley et al. 2010 in pregnant women, living in low-income communities, dominated by Mexican-immigrants in California showed a significant decrease in fecundity associated with PBDE exposure in women.
Another study conducted by Chevrier et al. 2010 measures the concentrations of 10 PBDE congeners, free thyroxine (T4), total T4, and thyroid-stimulating hormone (TSH) in 270 pregnant women around the 27th week of pregnancy. The associations between free and total PBDE and T4 were found to be statistically insignificant. However, the authors found a significant association between PBDEs exposure and decreased TSH during pregnancy, which may have implications for maternal health and fetal development.
A prospective longitudinal cohort study that began after September 11, 2001, included 329 mothers who gave birth at one of three hospitals in Manhattan, New York, conducted by Herbstman et al. 2010. The authors of this study analyzed 210 umbilical cord blood specimens for selected PBDE equations and neurodevelopmental effects assessed in children aged 12-48 and 72 months. The results showed that children who had higher cord blood concentrations than diphenyl ether terpolymers (PBDEs) scored lower on mental and motor development tests at 1-4 and 6 years. This is the first study to report such relationships in humans.
A similar study was conducted by Roze et al. 2009 in the Netherlands in 62 mothers and children to estimate the association between 12 Organohalogen (OHC) compounds, including polychlorinated biphenyls (PCBs) and retudant brudinated diphenyl ether (PBDE), measured in maternal serum during the 35th week of pregnancy and motor performance ( coordination, fine motor skills), cognition (intelligence, visual perception, visuomotor integration, inhibition control, verbal memory, and attention), and behavioral scores at 5-6 years. The author demonstrates for the first time that transplacental displacement of retardant polygromas is related to the development of children at school age.
Another study was conducted by Rose et al. in 2010 to measure PBDE levels circulating in 100 children between 2 and 5 years from California. The rate of PBDE according to this study, in children aged 2 to 5 years in California is 10 to 1,000 times higher than that of European children, 5 times higher than other US children and 2 to 10 times higher than for people adult US. They also found that diet, indoor environments, and social factors influence the body's burden levels. Eating poultry and pork contribute to an increased body burden for almost all types of flame retardants. The study also found that lower independent education was significantly and significantly associated with higher rates of most fire retardant entertainers in children.
San Antonio Statement on Brominated and Chlorinated Flame Retardants 2010 : A group of 145 leading scientists from 22 countries signed the first consensus statement documenting the health hazards of refractory chemicals found at high levels in home furnishings, electronics, insulation, and other products. This statement documents that, with limited fire safety benefits, this fire barrier may cause serious health problems, and, since this type of fire retarder is prohibited, alternatives must be proven safe before use. The group also wants to change the widespread policies that require the use of flame retardants.
A number of recent studies have shown that food intake is one of the main routes for human exposure to PBDEs. In recent years, PBDEs have become enormous environmental pollutants, while body burdens in the general population have increased. The results show a real coincidence between China, Europe, Japan and the United States such as dairy products, fish, and seafood being the cause of human exposure to PBDE due to environmental pollutants.
A study in February 2012, genetically engineered female rats have mutations in the MECP2 x-chromosome gene, associated with Rett syndrome, a human-like disorder similar to autism. After exposure to BDE-47 (a PDBE), their children, who are also exposed, have lower birth weight and survival, and demonstrate social skills and learning.
A study in January 2013 showed brain damage from BDP-49, through inhibition of mitochondrial ATP production processes necessary for brain cells to gain energy. Toxicity is at a very low level. This study offers a possible pathway where PDBE leads to autism.
Mechanism of toxicity
Live lighting
Many flame retardants are halogenated with aromatic rings, including most brominated flame retardants, possibly thyroid hormone disorders. Thyroid hormones triiodothyronine (T3) and thyroxine (T4) carry iodine atoms, other halogens, and are structurally similar to many halogenated flame retardants, including PCB, TBBPA, and PBDEs. Therefore the flame retardant appears to compete to bind the site in the thyroid system, disrupting the normal function of thyroid transport proteins (such as transthyretin) in vitro and thyroid hormone receptors. An 2009 in vivo animal study conducted in 2009 by the US Environmental Protection Agency (EPA) showed that deiodination, active transport, sulfation, and glucuronidation may be involved in thyroid homeostatic disorders after perinatal exposure to PBDE during critical development. the point of time in the womb and immediately after birth. The deiodinase disorders as reported in the Szabo et al., 2009 study in vivo were supported in advanced studies in vitro. The adverse effects on the liver mechanism of thyroid hormone disorders during development have been shown to persist into adulthood. The EPA notes that PBDE is highly toxic to animal brain development. Studies reviewed have shown that even a single dose administered to mice during brain development can lead to permanent changes in behavior, including hyperactivity.
Based on in vitro laboratory studies, some flame retardants, including PBDE, TBBPA, and BADP, may also mimic other hormones, including estrogen, progesterone, and androgens. Bisphenol A compounds with lower brominated degrees seem to show greater estrogenism. Some halogenated flame retardants, including non-brominated PBDE, may be directly in-vitro neurotoxic in cell culture studies: By altering calcium homeostasis and signaling neurons, as well as the release of neurotransmitters and uptake in the synapses, they interfere with neurotransmission normal. Mitochondria may be highly susceptible to PBDE toxicity because of their effects on oxidative stress and calcium activity in the mitochondria. Exposure to PBDE may also alter the differentiation of nerve cells and migration during development.
Product degradation
Many flame retardants decrease to compounds that are also toxic, and in some cases degradation products can be a major toxic agent:
- Halogenated compounds with aromatic rings can be degraded into dioxin and dioxin compounds, especially when heated, such as during production, fire, recycling, or sun exposure. Chlorinated dioxin is one of the most toxic compounds listed in the Stockholm Convention on Persistent Organic Pollutants.
- Polybrominated diphenyl ether with higher number of bromine atoms, such as decaBDE, is less toxic than PBDE with lower bromine atoms, such as pentaBDE. However, since higher-level PBDEs decrease biotically or abiotically, bromine atoms are removed, resulting in a more toxic PBDE congener.
- When some halogenated flame retardants such as PBDE are metabolized, they form a hydroxylation metabolite that can be more toxic than the parent compound. This hydroxylated metabolism, for example, can compete more strongly to bind with transthyretin or other components of the thyroid system, it can more strongly mimic estrogen than the parent compounds, and may strongly influence the activity of neurotransmitter receptors.
- Bisphenol-A diphenyl phosphate (BADP) and tetrabromobisphenol A (TBBPA) may be degraded into bisphenol A (BPA), an endocrine intruder of concern.
Exposure route
One can be exposed to flame retardants through several routes, including diet; consumer products at home, vehicle, or workplace; occupation; or contamination of the environment near their home or workplace. Populations in North America tend to have higher levels of flame retardants than people living in many other developed regions, and worldwide the rate of inhibition of human body fire has increased over the last 30 years.
Exposure to PBDEs has been studied extensively. Because PBDE is not used due to health problems, flame retardants of organophospores, including flame retardants of halogenated organophosphates, are often used to replace them. In some studies, indoor airborne concentrations of phosphorus flame retardants have been found to be larger than in-room PBDE air concentrations. The European Food Safety Authority (EFSA) issued its 2011 scientific opinion on the exposure of HBCD and TBBPA and its derivatives in food and concluded that current dietary exposure in the EU poses no health problems
Exposure in the general population
The PBDE body burden in the United States correlates well with the level of PBDEs measured in their hand swabs, possibly taken from dust. <55> [56] Exposure to dust may occur in your home, car, or workplace. The rate of PBDEs can be as much as 20 times higher in vehicle dust like household dust, and interior heating of vehicles on summer days can break up flame retardants into more toxic degradation products. [57] However, blood serum levels from PBDEs seem to be most correlated with levels found in dust at home. [56] 60-80% of the exposure is caused by inhalation of dust or consumption. [50] [51] . In addition, 20% to 40% of adult US exposure to PBDE is through food intake as bioaccumulation of PBDE in the food chain. High concentrations can be found in meat, milk and fish with the remaining exposure largely due to inhalation of dust or swallowing [50] [51] . Individuals can also be exposed via electronic and electrical devices. Young people in the United States tend to carry higher flame retardants per unit of body weight than adults. [59] [60] Infants and toddlers are highly exposed to halogenated flame retardants found in breast milk and dust. Because many fat-soluble halogenated flame retardants, they accumulate in fatty areas such as breast tissue and are mobilized into breast milk, providing a high level of flame retardant to breastfed babies. [51] PBDEs also cross the placenta, which means the baby is exposed to the uterus. Mother hormone thyroid (T4) levels can be impaired and exposure in the uterus in rat studies has been demonstrated to alter motor control, delaying sensory development and puberty.
Another reason for high levels of exposure in children is because of the age of aging consumer products, small particles of material into dust particles in the air and land on the surface around the house, including the floor. Small children crawling and playing on the floor often bring their hands to their mouths, engulfing about twice as much house dust as adults per day in the United States. [58] Children also have higher food intake per kilogram of body weight than adults. Young children are also exposed to flame retardants through their clothes, car seats and toys. The introduction of these chemicals occurred after the tragic death of children wearing rayon cloth that would be flammable. The US applied the "Flammable Fabric Fabric" passed in 1953 (will direct to the wiki page for 'U.S Flammable Fabrics Act') after that, flame retardants are mandated to be added to many children items, including pajamas. While flame retardants are shown to reduce the risk of burns in children, the risk of thyroid disorders as well as delayed physical and cognitive development, is not comparable.
A study was conducted by Carignan in 2013, C. et al. found that gymnasts were exposed to some fireproof products such as PentaBDE and TBB over the general population in the United States. After testing hand-washing samples before and after the exercise, they found that BDE-153 concentrations were four to six times greater among gymnasts than for the US population. Also, the PentaBDE concentration is higher up to three times after exercise compared to the previous level; show a higher level of flame-retardants on training equipment. In addition, they also found several refractory products with different concentrations in the air and higher dust at the gym than residency. However, this study was conducted on a small sample size; and further studies are recommended to assess associations.
Work exposure
Some work exposes workers to higher levels of halogenated flame retardants and their degradation products. A small study of foam recoverers and US carpet installers, which handle the often-made padding of recycled polyurethane foams, shows elevated flame retardants in their tissues. Workers in electronic recycling plants worldwide also have higher body rates than fire retardants relative to the general population. Environmental control can reduce this exposure substantially, while workers in the area with little supervision can take a very high level of fire retardant. The electronic recycler in Guiyu, China, has the highest level of human body PBDEs in the world. A study conducted in Finland determines workers' exposure to brominated flame retardants and chlorinated flame retardants (TBBPA, PBDEs, DBDPE, HBCD, Hexabromobenzene and Dechlorane plus). In 4 locations of electrical and electronic equipment waste recycling (WEEE), the study concluded that the control measures implemented on the site significantly reduced exposure. Workers who make products containing flame retardants (such as vehicles, electronics, and baby products) may be equally exposed. US firefighters can have high PBDE levels and high levels of brominated fans, toxic degradation products from brominated flame retardants.
Environmental exposure
Flame retardants manufactured for use in consumer products have been released into the environment around the world. The flame retardant industry has developed a voluntary initiative to reduce emissions to the environment (VECAP) by promoting best practices during the manufacturing process. Communities near electronics factories and disposal facilities, especially areas with little supervision or environmental control, develop high levels of fire retardants in the air, soil, water, vegetation, and humans.
Organophosphere flame retardants have been detected in wastewater in Spain and Sweden, and some compounds do not seem to be completely removed during water treatment. Fire resistant organophosphorus is also found in tap and bottled water in China. Likewise on the river Elbe in Germany.
Disposal
When products with flame retarders reach the end of their usable lives, they are usually recycled, burned, or stockpiled.
Recycling may contaminate workers and communities near recycling plants, as well as new materials, with halogenated flame retardants and their breakdown products. Electronic waste, vehicles, and other products often melt to recycle their metal components, and such heating can produce toxic and furan dioxins. When wearing Personal Protective Equipment (APD) and when the ventilation system is installed, workers' exposure to dust can be significantly reduced, as demonstrated in the work performed by the Stena-Technoworld AB recycling plant in Sweden. Brominated flame retardants can also alter the physical properties of plastics, resulting in lower performance in recycled products and in "downcycling" of the material. It appears that plastic with brominated flame retardant mixes with flame-retardant plastic in the recycle stream and downcycling as it happens.
Low quality incineration also produces and releases large quantities of toxic degradation products. Controlled incineration of materials with halogenated flame retardants, while costly, substantially reduces the release of toxic byproducts.
Many products containing halogenated flame retardants are delivered to landfill. Additives, as opposed to reactive, flame retardants are not chemically bonded with the base material and leach out more easily. Brominated flame retardants, including PBDEs, have been observed laundering from landfills in industrialized countries, including Canada and South Africa. Some landfill designs allow for the capture of leachate, which needs to be treated. This design also decreases the time.
Regulatory Opposition
Shortly after California changed TB117 in 2013 to require only fire-proof furniture cover (no restrictions on interior components), furniture manufacturers across the US heard of increasing demands for flame-free furniture. Of note, the refractory fabrics used in flame retardants do not contain PBDE, organophosphates, or other chemicals that have historically been associated with adverse effects on human health. A number of decision makers in the health sector - who account for nearly 18% of US GDP - are committed to buying the materials and furniture. Early adopters of this policy included Kaiser Permanente, Advocate Health Care, Hackensack University Hospital, and University Hospital. Overall, furniture purchasing power from these hospitals totaled $ 50 million. All hospitals and hospital systems refer to the Healthy Hospital Initiative, which has more than 1300 member hospitals, and promotes environmental sustainability and public health in the health care industry.
Further legislation in California has served to educate the public about flame retardants in their homes, which essentially reduces consumer demand for products containing these chemicals. According to the bill (Senate Bill, 1019) signed by Governor Jerry Brown in 2014, all furniture produced after January 1, 2015 must contain a consumer warning label stating whether or not to contain refractory chemicals
In September 2017, the topic reached the attention of federal regulators at the Consumer Product Safety Commission, who chose to draw up a Chronic Hazard Advisory Panel that focused on explaining certain risks from various consumer products, particularly baby and child products (including beds and toys), furniture layered houses, mattresses and mattresses and mattress pads, and plastic casing that surrounds the electronics. This advisory panel is specially charged to overcome additive risk, a non-polymer organohalogen flame retardant (OFRs). Although these chemicals have not been banned, this decision is fueling a deep consumer safety inquiry that can ultimately lead to the complete elimination of these substances from consumer manufacturing.
Under the Toxic Substances Control Act of 1976, the Environmental Protection Agency also actively evaluates the safety of flame retardants, including chlorinated phosphate ester, tetrabromobisphenol A, cyclic aliphatic bromide, and brominated phthalates. Further regulation depends on the EPA findings from this analysis, although the regulatory process may take several years.
National Bureau of Standards Test
In the 1988 pilot program, conducted by the former National Bureau of Standards (NBS), it is now the National Institute of Standards and Technology (NIST), to measure the effects of refractory chemicals against total fire hazards. Five different types of products, each made of different types of plastic are used. This product is manufactured in fire resistant (FR) and non-retarded (NFR) analogue variants.
The impact of FR (fireproof) materials on the survivability of building occupants is assessed in two ways:
First, comparing time to domestic space is unsuitable for occupation in the combustion chamber, known as "disability"; this applies to the occupants of the combustion chamber. Second, comparing the total production of heat, toxic gas, and smoke from fire; this applies to residents of buildings away from the fire origin room.
Time for helplessness is determined by the time available to the inhabitants before (a) a flashover of space occurs, or (b) impartiality due to toxic gas production occurring. For the FR test, the average available spare time is more than 15 times greater than for the occupants of the room without fire retarder.
Therefore, with regard to the production of combustion products,
- The amount of material consumed in a fire for fire retardant test (FR) is less than half the amount lost in a non-fire retardant (NFR) test.
- The FR test shows the amount of heat released from the 1/4 fire released by the NFR test.
- The total amount of toxic gas produced in the indoor fire test, expressed in "CO equivalent," is 1/3 for the FR product, compared with the NFR.
- Smoke production did not differ significantly between indoor fire tests using NFR products and FR products.
Thus, in this test, the fire retardant additive lowers the overall fire hazard.
Global query
In 2013, world flame retardants consumption is more than 2 million tons. The most commercial import application area is the construction sector. Flame retardants are needed for example for pipes and cables made of plastic. In 2008 the United States, Europe, and Asia consumed 1.8 million tons, valued at US $ 4.20-4.25 billion. According to Ceresana, the market for flame retardants is increasing due to rising safety standards worldwide and increasing use of flame retardants. It is expected that the global flame retardant market will generate US $ 5.8 billion. In 2010, Asia-Pacific was the largest market for flame retardants, accounting for about 41% of global demand, followed by North America, and Western Europe.
See also
- Flammable
- Brominated flame retardant
- Flame retard
External links
- Hazards of Brominated Flame Retardants , by Nick Gromicko, International Association of Certified Home Inspectors, Inc., viewed Jan 2018.
- Resistant and Fireproof Cable , by Steven McFadyen, myElectrical Engineering, July 4, 2013.
References
External links
- FlameRetardants-Online from Clariant Produkte (Deutschland) GmbH
- Phosphorus, Inorganic and Nitrogen Flame Retardants Association
- The European Flame Retardants Association (EFRA)
Source of the article : Wikipedia
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