Svalbardrype     Some more pictures from the field work


Uptake, metabolism and effects of Deca-BDE, HCBD and TBBPA in terrestrial bird
s

 

Professor Bjørn Munro Jenssen and post doc fellow Tomasz Ciesielski

Department of Biology, Norwegian University of Science and Technology, NO-7491 Trondheim, Norway

 

<>Partners

Professor Janneche Utne Skaare, Norwegian Veterinary Institute and School of Veterinary Science, Oslo, Norway. Analyses of BFRs in tissues of the birds; exposure characterization. E-mail: janneche.skaare@vetinst.no

Professor Jan Boon, Netherlands Institute for Sea Research, Texel, The Netherlands. Analysis of BFR metabolites and cytochrome P450 enzymes. E-mail: boon@nioz.nl

Professor Bernt Erik Sæther, Department of Biology, Norwegian University of Science and Technology, Trondheim, Norway. http://www.bio.ntnu.no/users/berntes/indexeng.htm , email: bernt.erik.sather@bio.ntnu.no

Professor Hans Christian Pedersen, Norwegian Institute of Nature Research, Trondheim, Norway. Field studies on willow and rock ptarmigan. E-mail: Hans.pedersen@nina.no

Professor Claus Bech, Department of Biology, Norwegian University of Science and Technology, Trondheim, Norway. Laboratory studies on zebra finches. http://www.nt.ntnu.no/users/clabec/  E-mail: claus.bech@bio.ntnu.no

Associate professor Augustine Arukwe, Department of Biology, Norwegian University of Science and Technology, Trondheim, Norway. Analysis of TH gene expression and cyp26. http://www.bio.ntnu.no/users/arukwe/  E-mail: arukwe@bio.ntnu.no

Professor Rolf A. Andersen, Department of Biology, Norwegian University of Science and Technology, Trondheim, Norway. Analysis of ROS, CAT, SOD and metallothioneins. http://www.bio.ntnu.no/users/raa/index.htm  E-mail: rolf.arvid.andersen@bio.ntnu.no

 

 

Bakground

Brominated flame retardants (BFRs) are used in a wide range of products to reduce flammability, and thus to decrease human and economical loss due to fire (Birnbaum and Staskal, 2004) In 2002 the usage of BFRs was approximately 200.000 metric tonnes, of which 56% was used in Asia, 29% in the Americas, and ca. 15% in Europe (BSEF, 2001) Currently, the three main groups of chemicals used as BFRs are polybrominated diphenylethers (PBDEs), hexachlorocyclododecane (HBCD) and tetrabromobisphenol A (TBBPA).

 

In the late 1990ies a number of the BFRs were found in human breast milk (Meironyte et al., 1999) and in the biota (De Wit, 2002)and this lead to concern about their persistent and bioaccumulative properties. Documentation of the ability of penta- to octa-brominated BDEs to bioaccumulate and to undergo long-range transport, together with documentation of their potential toxic effects have resulted in the ban of the Penta- and Octa-technical BDE-mixtures in the EU from August 2004 (Cox and Efthymiou, 2003) Following the ban of the Penta- and Octa-technical BDE-mixtures in California (from 2008), the sole American manufacturer (Great Lake Chemical) have introduced a voluntary moratorium on the production of these technical mixtures from 2005 [www.epa.gov]. Thus, the only PBDE-product currently in use is the Deca-mixture, which has been believed not to be bioavailable due to its large molecular weight, and to be non-toxic. In 2002, the use of the Deca-technical mixture, which consists of 97% BDE-209, was 56.000 tonnes.

 

However, recently the deca-BDE (BDE-209) has been detected in biota in different ecosystems. As part of the EU-financed FIRE-project (Risk Assessment of Brominated Flame Retardants as Suspected Endocrine Disrupters for Human and Wildlife Health, QLK4-CT-2002-00596, www.rivm.nl/fire), we have found deca-BDE in invertebrates, birds and mammals from the marine ecosystems in Norway and Svalbard (Gaustad, 2005; Jenssen et al., 2004a; Salmer et al., 2005; Sørmo et al., 2003). Although it is especially noteworthy that deca-BDE was detected in the blubber of polar bears (Ursus maritimus) (Jenssen et al., 2004a; Salmer et al., 2005), the deca-BDE seem to bioaccumulate particularly in birds, from both terrestrial and marine food chains (Gaustad, 2005; Jaspers et al., 2005; Jenssen et al., 2004b; Lindberg et al., 2004; Salmer et al., 2005; Sørmo et al., 2003) and even in humans. (Thuresson et al., 2005).

 

In the FIRE-project, and in a project financed by the Norwegian Research Council (ProFo project no.: 141369/720), we have also shown the presence of HBCD in species from most trophic levels (including birds) of marine food chains along the coast of Norway and Svalbard (Gaustad, 2005; Jenssen et al., 2004a; Murvoll et al., 2005a; Murvoll et al., 2005b; Salmer et al., 2005; Sørmo et al., 2003). HBCD has also been found in birds in the terrestrial food chains in Scandinavia and in central Europe (Jaspers et al., 2005; Lindberg et al., 2004). With respect to TBBPA, there are few reports about levels in both marine and terrestrial biota, including birds (Birnbaum and Staskal, 2004). It is believed that TBBPA is relatively easily metabolised in the organism and that a continuous exposure is necessary to uphold high levels(Sjodin et al., 2003). However, it should be noted that TBBPA has been detected in eggs from Norwegian birds of prey (Berger et al., 2004).

 

With respect to effects of BFRs, several studies have documented in-vitro and in-vivo effects of penta- to octa-BDEs that are similar to those reported for PCBs (Darnerud et al., 2001). In a recent study, deca-BDE was demonstrated to affect behaviour in mice in a way that suggests that deca-BDE may have thyroid disruptive effects (Viberg et al., 2003). Also several in vitro studies indicate that HBCD has the potential to cause neurobehavioral alterations (Eriksson et al., 2002; Mariussen and Fonnum, 2003; Murai et al., 1985). Results from the FIRE project also indicate that HBCD have thyroid disruptive effects (Hamers et al., 2004). In-vitro studies strongly indicate that TBBPA is a very potent TH-disrupter (Hamers et al., 2004; Legler and Brouwer, 2003), having an affinity to the plasma transport protein for thyroxin (transthyretine) up to 10 times that of T4. In addition, one of the metabolic break-down products of TBBPA is BPA (bisphenol A), which have been documented to have estrogenic properties. Even though one study has shown that there is a low maternal transfer of TBBPA in Japanese quail (Coturnix japonica) (Halldin et al., 2001), adult birds may be exposed to this compound via their food. Thus, there is considerable concern about the effects of the main groups of BFRs still in use on humans and wildlife.

 

Most of the studies related to BFRs and other halogenated organic compounds have been conducted on species from aquatic or marine ecosystems. However, recent information strongly indicate that BFRs, and in particular the higher brominated compounds such as BDE-209 behave very differently from organochlorines (OCs) with respect to disposition and exposure and uptake in organisms (results presented at meetings of the FIRE-project, the Third International Workshop on Brominated Flame Retardants in Toronto in June 2004, and on the Dioxin 2004 meeting in Berlin). Relatively high concentrations in both humans and in terrestrial ecosystems (Lindberg et al., 2004; Mariussen et al., 2004) indicate that BFRs are more readily taken up in terrestrial animals than are OCs. This may be because some of them are large and easily associate with particles. Their high Kow partitioning coefficients may also cause them to adhere to leaf surfaces and thus be available uptake and biomagnification in the terrestrial food web. It has for instance been documented that BFRs readily adhere to organic film that covers windows (Butt et al., 2004).

 

It has been documented that that the deposition and organismal uptake of organohalogenated persistent compounds tend to be higher at high altitudes than at low altitudes (Ohyama et al., 2004). This may have impact for the uptake and effects of BRFs in Norwegian terrestrial food webs. Thus, we wish to compare exposure and uptake of BFRs in two closely related species which inhabits two compartments of the Norwegian mountain ecosystem: the willow ptarmigan and the rock ptarmigan (Lagopus mutus). Furthermore, due to biomagnification levels of OCs have been reported to reach levels that cause adverse effects in birds of prey, and these birds may therefore also be vulnerable to exposure to BFRs (Lindberg et al., 2004).

 

Aims

1.      Determine between-species differences in levels, uptake and metabolism of deca-BDE (BDE-209), HBCD and TBBPA in altricial and precocial birds from terrestrial ecosystems. Levels will be examined in house sparrows, willow ptarmigan and rock ptarmigan, and if possible in birds of prey.

2.      Examine uptake and metabolism and effects of deca-BDE, HBCD and TBBPA on development of the thyroid hormone system, the vitamin A and E and on formation of ROS and antioxidant defence (CAT and SOD) in precocial and altricial birds. Japanese quail and/or hens will be applied as model species for precocial birds, and the zebra finch (Taeniopygia guttata castanotis) as a model for altricial species.

 

The results from the study will generate results important for risk assessment of exposure to BFRs in terrestrial birds in Norwegian ecosystems.

 

 

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