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Levels and congeners distribution of dioxins, furans and dioxin-like PCBs in buffaloes adipose tissues sampled in vivo and milk

ABSTRACT The levels of PCDDs, PCDFs and DL-PCBs were analyzed both in milk and adipose tissues sampled “in vivo” from lactating, drying off and heifer buffaloes from a Campania farm which had been impounded by the competent authority owing to the high dioxin levels found in bulk milk. The chemical determination was carried out by HRGC-HRMS using US EPA Method 1613b. The range of WHO-TEQ values for the PCDDs/PCDFs in adipose tissues was 1.79 to 68.64 pg g−1 fat and in milk was 8.33 to 13.95 pg g−1 fat. The contamination profile for dioxins and furans was given by 1,2,3,7,8-PeCDD; 2,3,4,7,8-PeCDF; 1,2,3,6,7,8-HxCDD and 2,3,7,8-TCDD. The levels of DL-PCBs in adipose tissue varied from 1.38 to 20.13 pg g−1 fat while ranged from 8.33 to 13.95 pg g−1 fat in milk. The pattern of DL-PCBs in both matrices was dominated by congeners PCB 126 and PCB 169. Graphical Abstract


Introduction
Dioxins belong to a group of 75 polychlorinated dibenzop-dioxin congeners (PCDDs) and 135 polychlorinated dibenzofuran congeners (PCDFs), among which 17 are of toxicological concern. Polychlorinated biphenyls (PCBs) are a group of 209 different congeners which can be divided into two groups according to their toxicological properties (non-ortho and mono-ortho PCBs). Only 12 congeners of this group exhibit toxicological properties similar to dioxins and are therefore often referred to as "dioxin-like PCBs" (DL-PCBs) (Schecter, Birnbaum, Ryan, & Constable, 2006).
PCDDs, PCDFs and DL-PCBs are recognized as Persistent Organic Pollutants (POPs) of mainly anthropogenic origin and are characterized by semi-volatility and resistance to degradation (EPA 2004). Because of the large number of compounds and depending on the chlorination level, relevant individual congeners are assigned with a toxic equivalency factor (TEF) that relate their toxicity to 2,3,7,8-tetrachlorodibenzo-p-dioxin, the most toxic compound (TEF 1). Each concentration of an individual congener in a mixture is multiplied with its TEF, and the resulting TCDD equivalents are added up and expressed as toxic equivalents endorsed by WHO (Van Den Berg et al., 2006).
The recognized main exposure to dioxins, furans and dioxin-like PCBs for the general population in Europe occurs via food, especially fish, meat and dairy products (EFSA 2012 of dioxins, furans, DL-PCBs and non-dioxin-like PCBs in food items, mainly of animal origin (Regulation EU No 1259/2011. Adipose tissues are the pool of POPs in animals. In the context of food safety, many authors carried out studies on the exposure and elimination of these contaminants. Hoogenboom et al. (2004) reported accumulation of residues of dioxins and polychlorinated biphenyls in the fat of the growing pigs and broilers fed with contaminated feed. Several other studies (Covaci et al. 2002;Guruge, Seike, Yamanaka, & Miyazaki, 2005;Simm et al., 2006;Spitaler, Iben, & Tausch, 2005;Thorpe, Kelly, Sartin, Harrison, & Rose, 2001) reported the occurrence of POPs in animal fat-based foods.
The presence of occasional and diffuse sources of emission, generally represented by accidental fires, burnings and open air disposal of ashes from combustion processes has been reported in some rural areas of Italy, as in the case of the buffalo milk dioxin crises in Campania Region (Borrello et al., 2008). The concern about dioxins contamination in Campania Region began in 2001, during the implementation of the National Residue Plan (PNR), when two sheep milk samples resulted non-compliant with contamination levels above the limits set by Commission Regulation 466/2001. The well-known "buffalo milk crisis" re-emerged in 2008 and extensive monitoring plans were set up in order to keep the situation under control. Milk from several buffalo farms of a restricted area of the Caserta province continued to result contaminated for long times, notwithstanding the application of suitable restrictive measures, change of pasture and/ or forage in particular, since PCDDs/PCDFs and DL-PCBs, owing to their resistance to degradation and high lipophilicity, may be accumulated into fat tissues and then transferred to milk during lactation period, as reported also by Fürst, Krause, Hein, Delschen, and Wilmers (1993).
In literature there are no in vivo studies on adipose tissues contamination levels in buffaloes from a dairy farm naturally exposed to these chemicals. Marchand et al. (2010) and Shen et al. (2012) reported the possibility of predicting levels of PCDDs/PCDFs and DL-PCBs by an "in vivo" sampling of bovine edible tissues and pig fat tissues, respectively. Aim of the present study was to investigate the levels of the PCCDs, PCDFs and DL-PCBs and evaluate the contamination profile in subcutaneous adipose tissues sampled in vivo from heifers, drying off and lactating buffaloes of an impounded herd of the Campania region during the "dioxin crisis" and to research correlations, if any, with the concentrations in the milk of the lactating animals.

Animal study
Nine dairy buffaloes (Bubalus bubalis), from a farm (Caserta province, Campania region, southern Italy) which had been impounded for a long time since the bulk milk was noncompliant to the PCDDs, PCDFs and DL-PCBs levels set by Regulation EU No 1259/2011, were selected for the study and divided into three groups. The first group included No 3 lactating buffaloes (L 1 , L 2 , L 3 ), the second group No 3 drying off buffaloes (D 1 , D 2 , D 3 ) and the last group No 3 heifers (H 1 , H 2 , H 3 ). Animals of each group were selected for similar age and weight. The lactating buffaloes were randomly chosen among animals of the most abundant class (parity 4-5) and the same lactating period, specifically not beyond the six month of lactation. Moreover they were not pregnant and had been fed in the same way.
Subcutaneous fat biopsies were performed in the milking parlor by a veterinarian of the National Sanitary Service after local anesthesia, following the animal welfare rules. After the sanitization procedures, a 3 cm incision was realized near the ischial tuberosity of each animal and a subcutaneous fat sample (about 1 g) was taken. The incision was sutured and each buffalo remained under observation for a couple of hours. The whole sampling procedure was realized within not more than 15 minutes.
The total morning milking was collected from the three lactating buffaloes prior to the in vivo fat sampling. Adipose tissues and milk samples were immediately stored at −25°C and sent under the same temperature conditions to Eurofins GfA GmbH laboratory Hamburg (Germany) for the analysis.

GC-HRMS analyses
Analysis of the 17 PCDDs/PCDFs congeners and 12 DL-PCBs congeners were carried out by high-resolution gas chromatography coupled to high resolution mass spectrometry (HRGC-HRMS) in agreement with EPA method 1613-b (1997). Samples were analyzed at Eurofins GfA GmbH laboratory Hamburg (Germany) according to accepted European directives and certified standard operating procedures (Decision 2002/657/EC and subsequent amendments and additions). The 6 non-dioxin-like PCBs (NDL-PCBs) set by Regulation EU No 1259/2011 were not considered to be consistent with previous survey programs performed in Campania region.
The fat percentage and the cumulative PCDDs, PCDFs and DL-PCBs in milk and adipose tissues from individual buffaloes are expressed on WHO 2005 TEQ scale on a fat basis (pg g −1 ) (Table 1) following the upper bound (ub) approach. Data are reported for the current World Health Organization Toxicity Equivalent factors (TEF-WHO 2005 ) as required by the Regulation (EU) No. 1259/2011. The total PCDDs/PCDFs concentration is expressed as the sum of TEQs of ten furans and seven dioxins congeners having chlorine atoms in 2,3,7,8-positions, the total DL-PCBs concentration is expressed as the sum of TEQs of twelve nonortho and mono-ortho PCB congeners (PCB 77,81,105,114,118,123,126,156,157,167,169 and 189).

Levels of PCDDs/PCDFs and DL-PCBs
In adipose tissues the total levels of PCDDs and PCDFs varied from 1.79 to 68.64 pg TEQ g −1 fat in lactating animals, from 18.25 to 43.2 pg TEQ g −1 fat in drying off buffaloes and from 6.88 to 18.52 pg TEQ g −1 fat in heifers. DL-PCBs ranged from 1.38 to 20.13 pg TEQ g −1 fat, 9.63 to 17.59 pg TEQ g −1 fat and 5.11 to 11.6 pg TEQ g −1 fat in lactating animals, drying off and heifers, respectively.
In milk the sum of PCDDs and PCDFs congeners ranged from 8.33 to 13.95 pg TEQ g −1 fat and those of DL-PCBs from 3.89 to 5.95 pg TEQ g −1 fat. Therefore, on the whole, only in adipose tissue of the buffalo L 2 the sums of PCDDs/PCDFs and that of PCDDs/PCDFs and DL-PCBs resulted lower than the limits of 2.5 and 4.0 pg/g fat set by EU Regulation 1259/ 2011 (Table 1).
(68-83%) followed by PCB 169 (15-29%) (Figure 2). Cumulated contributions of the remaining DL-PCBs congeners were no higher than 3% in all examined samples and the occurrence of DL-PCBs to total PCDDs/PCDFs and DL-PCBs (WHO 2005 TEQ) ranged from 18 to 30% in lactating animals, 22 to 26% in drying off subjects and from 24 to 30% in heifers. In the three milk samples DL-PBCs contributed to the total TEQ for 21, 24 and 26%, respectively.
Among the DL-PCBs, the toxicological contribution of PCB 126 is particularly relevant in relation to both the high toxicity value (TEF = 0.1) and concentration. This result might be due to PCB 126 high resistance to metabolic degradation. Corsolini, Focardi, Kannan, Tanabe, and Tatsukawa (1995) relate this resistance to the enzymes involved in the detoxification pathways and report that in their studies DL-PCB 118, 156 and 126 were the main contributors to toxicity in humans and foxes, suggesting that the significant contribution of mono-ortho congeners in humans and non-ortho congeners in foxes might be due to differences in metabolic potential affecting the PCB toxicity pattern. Storelli et al. (2012) found only PCB 118 in 51% of 80 sheep milk samples from an industrialized area of Sardinia (Italy). PCB 118, PCB 126 and PCB 169 were the most represented DL-PCB in buffaloes milk samples from Campania herds exposed to these chemicals (De Filippis et al., 2013).
The fat content in milk of the lactating buffaloes L 1 , L 2 and L 3 were in the order 6.2, 6.0 and 8.1% (Table 1b). According to Zicarelli (2004), only the animal L 3 showed fat percentage close to the physiologic buffalo milk composition. This buffalo also showed the highest contaminants concentration in adipose tissue (88 pg/g fat sum of PCDDs/PCDFs/DL-PCBs TEQ), at a level more than seven times higher than the corresponding in milk (12.22 pg/g fat sum of PCDDs/PCDFs/DL-PCBs TEQ). Contamination levels in milk and adipose tissues of L 1 resulted rather close, whereas PCDD/F and DL-PCB concentrations in milk resulted higher than those found in fat only for L 2 , that resulted lower than the limits of 2.5 (WHO-PCDD/F TEQ) and 4.0 pg/g fat (WHO-PCDDs/PCDFs/DL-PCBs TEQ) set by EU Regulation 1259/2011. This result might be related to the unsatisfactory state of nutrition of the subject, also demonstrated by a degenerated fat, characterized by a macroscopic gelatinous consistence, possibly caused by trials of starvation carried out in some instance by the farmers in an effort to decontaminate the animals since milk represents the main route of excretion of the lipophilic contaminants in dairy animals (Schulz et al., 2005).
Analyses of edible matrices for the determination of PCDDs, PCDFs and DL-PCBs levels is not always realizable on living animals. For milk and dairy products sampling at the farm or in the dairy plants is practicable, but sampling in the live animal appears inappropriate because of reasons of animal welfare. However, the assessment of the contamination profile in fat, using a weakly invasive biopsy of subcutaneous adipose tissue in living buffaloes from impounded farms (fast recovery, no major side effects), could be used to evaluate dioxins, furans and DL-PCBs congeners pattern transferred in milk and mozzarella cheese intended to human consumption. This approach could be considered a useful tool after acute or chronic exposure events. Figura 2. Perfiles de los congéneres de PCB no ortos y mono ortos en los tejidos adiposos de búfalos lactantes L 1 -L 2 -L 3 (a), en el periodo de secado D 1 , D 2 , D 3 (b), en vaquillas H 1 , H 2 , H 3 (c) y en la leche (d). Los valores se presentan como porcentajes de los totales de WHO2005-TEQ (DL-PCBs).

Disclosure statement
No author had a financial or personal relationship with people or organizations that could inappropriately influence or bias the content of this paper. The authors confirm that the data supporting the findings of this study are available within the article and/or its supplementary materials