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Dietary exposure to methyl mercury and PCB and the associations with semen parameters among Swedish fishermen


Dietary POP exposure have shown negative effects on sperm motility and sperm chromatin integrity, as well as an increased proportion of Y-chromosome bearing sperms. However, it has been suggested that in epidemiological studies investigating persistent organochlorine pollutant (POP)-toxicity, other pollutants occurring simultaneously may carry an increased risk of effects, which may obscure a clear interpretation of the role of POP toxicity. One such pollutant is methyl mercury (MeHg), which has been found in fatty fish from the Baltic Sea and as a consequence men with a high consumption of such fish has been found to have twice the MeHg levels compared to men with a low fish consumption.

The aim of the present study was to assess if exposure to MeHg affects male reproductive function, assessed by measuring human sperm motility, sperm concentration, total sperm count, sperm chromatin integrity and the proportion of Y-chromosome bearing sperms. Secondly we also investigated a possible interaction between MeHg and 2, 2', 4, 4', 5, 5'-hexachlorobiphenyl (CB-153), a biomarker for POP exposure, with respect to sperm outcome measures.

Blood and semen samples were collected from 195 Swedish fishermen with a mean age of 47 (range 24–67 years). Blood levels of MeHg ranged from 0.11 to 16.59 μg/L (median 2.25 μg/L) and serum levels of CB-153 from 37 to 1460 ng/g lipid (median 190 ng/g lipid).

The analyses revealed no association between MeHg and any of the outcomes investigated. Although men with low MeHg and high CB-153 had slightly higher DNA Fragmentation Index and fraction of Y-chromosome bearing sperms than men with low levels of both compounds, the effects were not statistically significant. In conclusion, we did not find any associations between MeHg exposure and semen quality or quantity in the dose range observed neither was any synergistic effects between MeHg and CB-153 noted.

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The Baltic Sea, off the east coast of Sweden, has for several decades, been polluted by persistent organochlorine pollutants (POPs), such as polychlorinated biphenyls (PCBs), polychlorinated dibenzo-p-dioxins (PCDDs), polychlorinated dibenzofurans (PCDFs), and dichloro diphenyl trichloroethane (DDT), with its major metabolite dichloro diphenyl dichloroethene (DDE). As a consequence, consumption of fatty fish from the Baltic Sea, such as herring and salmon, constitutes an important exposure source for POPs in the Swedish population [13]. Studies on the effects of dietary POP exposure on male reproductive function have shown negative effects on sperm motility [47] and sperm chromatin integrity [8]. An increased proportion of Y-chromosome bearing sperm has also been reported [9]. In a majority of these studies 2, 2', 4, 4', 5, 5'-hexachlorobiphenyl (CB-153) has been used as a biomarker for POP, since it correlates very well with total PCB concentration in serum [10] and plasma [11], as well as with the PCB derived dioxin-like effect [11] and the total POP derived dioxin-like effect [12]. Another relevant exposure biomarker is p, p'-DDE, which is present in relatively high serum concentrations in subjects consuming fatty fish from the Baltic Sea [13]. Fatty fish from the Baltic Sea is also a source of exposure to other pollutants, such as methyl mercury (MeHg) [14], and as a consequence men with a high consumption of such fish have been found to have twice the MeHg levels of men with a low consumption [3].

Animal studies suggest an effect on male reproduction of MeHg: from laboratory studies on rats there is evidence that exposure to MeHg impairs spermatogenesis by germ cell deletion via cell-and stage-specific apoptosis [15]. Furthermore, mice exposed to mercury showed a decreased testicular weight [16], and serum testosterone levels were lower than normal in rats treated with MeHg [17]. Monsees et al. [18] studied the in vitro effect of mercury on Sertoli cells from rat, and observed that concentrations at non-toxic or slightly cytotoxic concentrations sharply reduced inhibin B production.

Studies in humans have also reported a negative influence of MeHg on human male reproduction. Infertile [19] and subfertile [20, 21] men have been found to have higher MeHg levels than fertile men, and Sertoli cell only syndrome and tubular atrophy has been observed among infertile patients with MeHg exposure [22]. Moreover, mercury seminal fluid levels have been found to correlate with abnormal sperm morphology and abnormal sperm motility [23].

Thus, consumption of fatty fish from the Baltic Sea may be a shared exposure route for POPs and MeHg, both found to be hazardous to male reproduction. Indeed, it has been suggested that, in epidemiological studies investigating POP-toxicity, other pollutants occurring simultaneously, such as MeHg, may obscure a clear interpretation of the role of POP toxicity [24]. The difficulty in interpreting results from these studies may occur if the less hazardous compound is acting as a biomarker for the other, but also if there is a synergistic effect of the two chemicals. Results from a recent laboratory experiment suggested that some combinations of concentrations of MeHg and CB-153 have an antagonistic effect on PC12 cells [25]. Moreover, some experimental studies on rats have found synergistic effects on cerebellar functions [26] and brain dopamine [27], although others failed to find impairments on spatial alternation tasks from exposure to both MeHg and PCBs [28]. In humans, studies have suggested that an interaction between PCBs and MeHg may be present with respect to neonatal brain development [29], and cognitive development in preschool children [30]. To the best of our knowledge, no studies have been performed on interacting effects on outcomes related to male reproductive function.

The aim of the present study was to assess if exposure to MeHg affects male reproductive function, assessed by measuring human sperm motility, sperm concentration, total sperm count, sperm chromatin integrity and the proportion of Y-chromosome bearing sperms. Secondly, if there may be an interaction between MeHg and CB-153 with respect to sperm outcome measures.


Study population

Cohorts of fishermen from the Swedish east and west coasts were established in 1988 [3]. In 2000, a postal questionnaire, mainly focused on fracture incidence, was sent to 3,505 west and 1,678 east coast fishermen, born in 1935 or later. The questionnaire included a question about whether the subjects were interested in more information on a study of male semen function. Among the 2,614 subjects (east n = 848 and west n = 1,766) who responded to this specific question, 479 (east n = 171 and west n = 308) wanted more information. These subjects, as well as another 169 east coast fishermen who had become members of the east coast fishermen's organization after the closure of the original cohorts, were contacted and given written detailed information. From the east coast, 130 (38%) men wanted to participate and gave their written informed consent. The corresponding number on the west coast was 136 (44%). During the field study period, another 37 subjects from the west coast and 34 from the east coast were excluded due to logistical reasons, change of mind, sickness or recent vasectomy. Thus, the final number of men included in the present study was 189 (Table 1). Additional details of subject recruitment are given elsewhere [7].

Table 1 Distribution of basic semen variables, SCSA results, fraction of Y-chromosome bearing sperms and potential confounders among 189 Swedish fishermen.


The non-participants from the original fishermen's cohort had similar age distribution (median 51.8 years, range 29–67) as the participants (median 47.5 years, range 24–67). This was also the case with the fishermen who had become members since 1988 (median 47 years, range 20–67 vs. median 46 years, range 24–59). The fraction of smoking men was 23% among both participants and non-participants.

The men who wanted more information about the semen study had similar body mass index (BMI) values as those who did not want such information (median BMI 27, range 20–37 and 26, 18–44, respectively). However, the median age differed slightly (median 51 years, range 29–67 and 54 years, range 29–67, respectively).


Information on lifestyle, and medical and reproductive history was collected through telephone interviews performed by the same person during the whole study. The questionnaire was sent out to the participants a couple of weeks before telephone contact. In this way the subjects had time to get acquainted with the questions. During the telephone contact, an agreement was reached on time and date for collection of semen and blood samples at the subject's home. The participants received information on the procedures for collecting the semen samples both in verbal and written form.

All participants gave their written informed consent and the study was approved by The Ethical Committee at Lund University.

Mobile laboratory unit

A mobile laboratory unit was established for this study. A mini-van was equipped with all necessary instruments to perform the immediate semen analyses. Phase contrast microscope, 37°C microscope stage heater, centrifuge, incubator, 4-channel cell counter, vortex mixer, Sartorius® scale, PC for CASA (computer assisted sperm analysis) and a freezer/dry ice device was installed.

Semen sampling and analyses

Semen samples were obtained from 188 men by masturbation into a plastic container. The subjects were requested to have 3–4 days of abstinence before the collection. The median abstinence time was 3.0 days. Only two men had an abstinence time less than one day and five men had an abstinence time of more than 10 days. When a semen sample was collected, the participant completed a form regarding time, date, and the duration of abstinence, spillage, fever and medical treatment during the past 3 months. The sampling was performed between March 2001 and November 2001, and March 2002 and September 2002.

The semen samples were analyzed immediately with respect to semen volume, sperm motility and sperm concentration in the mobile laboratory. All analyses were performed by one person (ARH) and according to guidelines of the World Health Organisation [31]. A detailed description of the procedure has been given elsewhere [7].

The investigator had no knowledge about the exposure biomarker levels of the subjects when she analyzed the semen samples. The Fertility Center is accredited by the European Academy of Andrology and participates in the Nordic Association of Andrology and European Society of Human Reproduction and Embryology (ESHRE) quality control program. The intra-laboratory coefficient of variation (CV) for assessment of sperm concentration was found to be less than 8.5 percent. The average discrepancies for sperm concentration and motility (sum of A + B grade) between the principal investigator (ARH) and the laboratory staff at the Fertility Centre in Malmö were 7 percent and 11 percent, respectively. Previous studies have demonstrated a coefficient of variation among trained technicians within one laboratory, performing analysis of sperm concentration to be 11 percent [32].

Sperm Chromatin Structure Assay (SCSA)

The samples were quickly thawed in a 37°C water bath and analysed immediately. The SCSA was applied following the procedure described elsewhere [8, 33] In short, cells were stained with acridine orange (AO; Molecular Probes, Eugene, OR, USA), and analyzed by a FACScan (Becton Dickinson, San Jose, California, USA) equipped with an air cooled argon ion laser and standard optical filters to collect green and red fluorescence. A total of 10,000 events were accumulated for each measurement. AO, when intercalated with double-stranded DNA, emits green fluorescence, while AO associated with single-stranded DNA emits red fluorescence. Thus, sperm chromatin damage can be quantified by the flow cytometric measurements of the metachromatic shift from green to red (denatured, single-stranded DNA) fluorescence. In the present study, the extent of DNA denaturation was expressed in terms of DNA Fragmentation Index (DFI), which is the ratio of red to total (red plus green) fluorescence intensity [33].

Additionally, the fraction of high DNA stainable (HDS) cells, which represents immature spermatozoa with incomplete chromatin condensation, was also considered. The percentage of HDS cells was calculated by setting an appropriate gate on the bivariate cytogram and considering those events which exhibit green fluorescence intensity higher than the upper border of the main cluster of the sperm population with a non-detectable % DFI, as immature spermatozoa.

For the flow cytometer set-up and calibrations, a reference semen sample retrieved from the laboratory repository was used. Samples were measured twice during independent flow cytometry sessions and the average value was used. Results from the two measurements were highly correlated (DFI, r = 0.96; HDS, r = 0.96).

Y:X sperm chromosome ratio

After thawing and mixing, 10 μl of semen was smeared on to cleaned microscope slides (Superfrost Plus slides, Menzel Gläser, Germany) as described in detail elsewhere [9]. To determine the proportion of X- and Y-chromosomes two-colour fluorescence in situ hybridization (FISH) was performed using PNA (protein-nucleic acid) probes (provided by DakoCytomation, Glostrup, Denmark) targeted against the centromeric region of the X chromosome (Rhodamine-labelled) and the q-arm of the Y chromosome (FITC-labelled).

Slides were examined blindly with an Olympus AX 70 epifluorescence microscope (magnification: 400×) equipped with a single and double band pass filter to detect DAPI, FITC and Rhodamine. The examination was performed blindly, i. e. without knowledge of the exposure levels or other subject characteristics. An X or Y chromosome in a sperm nucleus was recognized by a red or a green fluorescent spot, respectively. Sperm nuclei were only scored when morphologically preserved, and sperms showing two signals (disomic or diploidic) were not counted. In every sample the proportion of sperms presenting with a clear red or green signal was ≥ 95%. The median number of sperm nuclei scored per slide in each specimen was 981 (range 276–1917), in 96% being 500 or more. As quality control of the method, in the first part of the study, 500 spermatozoa in 26 slides were assessed by two investigators and in 10 slides twice by the first author. Based on these analyses intra- and inter-observer CVs, as considers the proportion of Y bearing sperms, was estimated to 3.3% and 2.3%, respectively.

Blood sampling and analysis

Blood samples from 189 men were collected by venepuncture in connection to the collection of the semen samples. The time during the day when the samples were collected varied between 6 AM and 10 PM. Whole blood samples (Venoject, VT-100SH, Leuven, Belgium) were stored at -80° for Hg analysis. Serum from blood samples (BD Vacutainer, SST II Advance; Plymouth, UK) was transferred with ethanol rinsed pasteur pipettes to ethanol rinsed brown glass bottles and special tube and stored at -80°C for POP analysis.

Mercury analysis

The determination of total (T)-Hg and inorganic (I)-Hg in whole blood was made in acid-digested samples by cold vapour atomic fluorescence spectrometry [34]. The concentration of MeHg was calculated by subtraction of the concentration of I-Hg from that of T-Hg, assuming that the major part of the organic mercury fraction is in the form MeHg. The limit of detection calculated as three times the standard deviation (SD) for the blanks were for T-Hg and I-Hg in blood, 0.20 and 0.37 μg/L, respectively. The analytical accuracy was checked against reference material. Seronorm trace elements in whole blood (Nycomed Pharma., Oslo, Norway) with recommended values and certified blood samples from Centre de Toxicologie du Quebec, International Comparison Program; Canada (QTC) were used. The obtained result for T-Hg in the Seronorm samples were 1.6 ± 0.19 μg/L (mean ± SD) vs. recommended 1.7 – 2.4 μg/L (N = 20) and for the QTC samples 4.8 ± 0.19 μg/L vs. certified 5.0 μg/L (N = 10). However, there are no reference samples for I-Hg available, but the obtained values for I-Hg in the Seronorm samples (0.72 ± 0.19 μg/L; N = 24) were well in agreement with the results from previous analytical runs of the same batch.

CB-153 analysis

The levels of CB-153 were determined as previously described by Richthoff et al. (2003). Briefly, the CB-153 was extracted from the serum by solid phase extraction (Isolute ENV+; IST, Hengoed, UK) using on-column degradation of the lipids and analysis by gas chromatography mass spectrometry. 13C12-labeled CB-153 was used as an internal standard. The relative standard deviations, calculated from samples analyzed in duplicate at different days, was 7 percent at 0.6 ng/mL (n = 76) and 5 percent at 1.5 ng/mL (n = 37) for CB-153 and the detection limits were 0.05 ng/mL for CB-153. The analyses of CB-153 is part of the Round Robin inter-comparison program (Professor Dr. med. Hans Drexler, Institute and Out-Patient Clinic for Occupational, Social and Environmental Medicine, University of Erlangen-Nuremberg) with analysis results within the tolerance limits.

Determination of lipids by enzymatic methods

Plasma concentrations of triglycerides, cholesterol and phospholipids were determined by enzymatic methods using reagents from Boehringer-Mannheim (triglycerides and cholesterol; Mannheim, Germany) and Waco Chemicals (phospholipids; Neuss, Germany). The total lipid concentration in plasma was calculated by summation of the amounts of triglycerides, cholesterol and phospholipids. In these calculations, the average molecular weights of triglycerides and phospholipids were assumed to be 807 and 714. For cholesterol we used an average molecular weight of 571, assuming that the proportion of free and esterified cholesterol in plasma was 1:2.

Statistical analysis

MeHg was split into quintiles at 1.08, 1.86, 2.79, and 4.40 μg/L (n = 36–37 in each group) and data was analyzed using non-parametric methods. The rationale for this was that the model fit, assessed by checking the distribution of the residuals, was not satisfactory for the original values, for log-transformed values or for the categorized exposure variable. Thus, Kruskal-Wallis' test was used to evaluate differences between exposure groups with respect to the different outcomes. Furthermore, Mann-Whitney's U-test was used to examine differences between the lowest and highest quintile.

CB-153 and MeHg were dichotomized at their respective median (193 ng/g lipid for CB-153 and 2.25 μg/L for MeHg), and the dichotomized variables were then combined so that four groups were established: low MeHg/low CB-153 (n = 56), high MeHg/low CB-153 (n = 34), low MeHg/high CB-153 (n = 35), and high MeHg/high CB-153 (n = 55). A possible interaction between the two exposures was investigated as follows. The relative excess risk due to interaction (RERI), a measure of departure from additivity [35], was calculated for each outcome. Since calculations of RERI depends on risk estimates for each exposure, something that is not available when using non-parametric methods, the outcomes were dichotomized at their respective means in order to produce odds ratios (ORs) for being above the median by using logistic regression. RERI was then estimated using the formula RERI = OR(AB) - OR(AB') - OR(A'B) + 1, where A indicates high CB-153 and A' low CB-153, with the corresponding definition for B and MeHg, and each OR is calculated using the A'B' (i.e. low CB-153 and low MeHg) group as reference. 95% confidence intervals (CIs) for RERI were estimated using the bootstrap percentile 1 method on 500 data sets resampled with replacement from the original data [36].

Correlations were estimated using the Spearman correlation coefficient (rS).

Age and abstinence time [33, 3742], BMI [43], season of sampling [4448], and previous reproductive malformations and diseases [49, 50] have all previously been found to be associated with different measures of male reproduction and where thus considered as potential confounders. However, only if a factor was found to correlate (rS > 0.20) with both exposure and outcome, the variable was adjusted for. Only age fulfilled this criterion (irrespective of which exposure measure was used).

Analyses were performed using StatXact-6 (Cytel Studio) and SPSS 12.0. The term statistically significant is used to denote a two-sided p-value less than 5%.


MeHg and CB-153

Blood levels of MeHg ranged from 0.11 to 16.59 μg/L (median 2.25 μg/L) and serum levels of CB-153 from 37 to 1460 ng/g lipid (median 190 ng/g lipid). There was a high correlation between MeHg and CB-153 (rS = 0.51, p = 0.001, fig. 1).

Figure 1
figure 1

Correlation between serum levels of MeHg and CB-153 among Swedish fishermen (r = 0.51; p < 0.001).

MeHg vs. outcomes

The analyses using Kruskal-Wallis' test revealed no association between MeHg and DFI (p = 0.3), HDS (p = 0.7), fraction of Y-chromosome bearing sperms (p = 0.2), sperm motility (p = 0.9), sperm concentration (p = 0.9), total sperm count (p = 1.0), or semen volume (p = 0.6) (Table 2). The lowest and highest exposure groups differed with respect to the fraction of Y-chromosome bearing sperms (p = 0.03; Figure 2), but after adjustment for age this difference was no longer statistically significant (p = 0.4). No differences between lowest and highest exposure was found for the other outcomes (data not shown).

Table 2 Outcome variables (median and 5–95% range) among 189 Swedish fishermen depending on exposure to methyl mercury (MeHg).
Figure 2
figure 2

Fraction of Y chromosome bearing sperms (%) for different levels of MeHg. Circles denotes outliers (1.5–3 quartile intervals from the box) and stars denotes extremes (>3 quartile intervals from the box). Please note that the y-axes do not start at zero.

Interaction between CB-153 and MeHg

Although men with low MeHg/high CB-153 had slightly higher DFI and fraction of Y-chromosome bearing sperms, none of the age adjusted RERIs were statistically significant (Table 3).

Table 3 Outcome variables (median and 5–95% range) among 189 Swedish fishermen, depending on exposure to MeHg and CB-153.


The present study gave no support to the hypothesis that exposure to MeHg is hazardous to any of the outcome variables, neither did it provide any support for a synergistic effect between POPs and MeHg.

The low participation rate is a weakness of the study. Although the men had no knowledge of their MeHg and CB-153 levels, they knew that they had been chosen for the study since they were suspected to have a high consumption of fish. Furthermore, even though it is unlikely that the majority of the men have any knowledge of their sperm quality, individuals may know, or suspect, themselves of having low sperm quality if they and their partners have experienced difficulties in conceiving. If, among the 2,614 responders to the original questionnaire, those men with the highest consumption of fatty fish and those with a history of reproductive problems decided not to participate in the study, we run the risk of underestimating a possible association between MeHg and low sperm quality. On the other hand, if men with high fish consumption and reproductive problems are overrepresented in the present study, the risk would be to overestimate a possible association.

Although the studied population was relatively large, the categorization of exposure resulted in groups of only some 30 men. Thus, some of the comparisons may have had insufficient statistical power to detect any differences. However, this categorization method was preferred to be able to detect possible trends with increasing exposure. Moreover, analyses were performed comparing the lowest to highest exposure category, thereby maximising differences in exposure levels.

Due to the relatively strong correlation between CB-153 and MeHg, the joint categorization of the two variables were not optimal, in that the median CB-153 were consistently increasing for the groups low/low – high/low – low/high – high/high, with the corresponding phenomenon for MeHg. Thus, a strong effect of either compound could appear as a synergistic effect between the two. However, since we failed to find such a synergistic effect, the skewed distribution of CB-153 and MeHg in the four exposure groups should not pose a major problem in the present study.

However, the present study has several important strengths. Firstly, the analyst who made the initial semen analyses, sperm motility, sperm concentration and measuring volume was not aware of the participants CB-153 or MeHg levels. Moreover, all analyses were performed by one of the authors (ARH), which is expected to reduce the variation in the assessment of sperm characteristics. As for the other outcome variables, SCSA and FISH were carried out in complete blindness towards exposure. Finally, all the interviews were made by one person.

In the present study, the correlation between MeHg and CB-153 was reasonably high (rS = 0.51). This is in agreement with previous studies were the coefficient of correlation between mercury and CB-153 in blood varied between 0.35 and 0.47 [24, 51]. When interpreting these correlation coefficients, one must bear in mind that the two compounds behave differently in the human body: Whereas MeHg in general is present as water-soluble complexes and does not distribute to fatty or lipid regions in the body but accumulates to a higher degree in the muscles, lipid rich tissue is the most important storage site for POPs [52].

The blood levels of MeHg in the present study ranged from 0.1 to 17 μg/L, with a median at 2.25 μg/L, and represented on average 86% of total Hg level (data not shown). Thus, the levels are in the same order of magnitude as those found by Chia et al [53], who failed to find any difference in blood mercury between men with <40% motile sperm compared to those with ≥ 40% (1.8 μg/L vs 1.91 μg/L). In studies of men with higher levels of blood mercury, infertile men were found to have higher levels than the control group (8.1 μg/L vs 6.2 μ/L [assuming that the unit "mmol/L" was a misprint in the paper and should really be "nmol/L"]) [19], and men with blood mercury higher than 10 μg/L had reduced sperm concentration, percentage of morphologically normal sperm, and percentage of motile sperm, although the differences were not statistically significant [54] Furthermore, in a population of men with mean blood mercury concentration of 8.3 μg/L, seminal fluid concentrations of mercury were found to correlate with abnormal sperm morphology and abnormal sperm motion, although not with the overall percentage of motile sperm or sperm concentration [23]. Other studies have measured mercury in urine or hair rather than blood. The levels of mercury are therefore not easily compared to those in the present study. However, the results from the studies on hair mercury suggest subfertile men to have higher concentrations of mercury than fertile men [20, 21], whereas a study on mercury in urine failed to find a correlation between mercury concentrations and semen quality [55].

In some studies, interacting effects of MeHg and PCBs have been found with respect to neurobehavioral endpoints in children [29, 30]. However, the literature on this topic is scarce, and we have not been able to find any studies investigating an interacting effect with respect to male reproductive parameters.

In a previous study concerning POPs and male reproduction, a threshold-like effect was noted when categorizing CB-153 serum levels into equally sized quintiles [8]. A significantly lower DFI was found in the lowest CB-153 quintile compared to the other quintiles. The lowest quintile was then defined as having less than 113 ng/g lipid, which is lower than the cut-off used to define low and high CB-153 in the present study (193 ng/g lipid). Using this cut-off in the present analysis, the results were however similar to those presented (data not shown). Thus, the differences in the findings should not be the result of the low exposure group being diluted in the present study.


In conclusion, we did not find any associations between MeHg exposure and semen quality or quantity, at least in the dose range observed, neither was any synergistic effects between MeHg and CB-153 noted.


  1. Ahlborg UG, Lipworth L, Titus-Ernstoff L, Hsieh CC, Hanberg A, Baron J, Trichopoulos D, Adami HO: Organochlorine compounds in relation to breast cancer, endometrial cancer, and endometriosis: an assessment of the biological and epidemiological evidence. Crit Rev Toxicol. 1995, 25 (6): 463-531.

    Article  CAS  Google Scholar 

  2. Asplund L, Svensson BG, Nilsson A, Eriksson U, Jansson B, Jensen S, Wideqvist U, Skerfving S: Polychlorinated biphenyls, 1, 1, 1-trichloro-2, 2-bis(p-chlorophenyl)ethane (p, p'-DDT) and 1, 1-dichloro-2, 2-bis(p-chlorophenyl)-ethylene (p, p'-DDE) in human plasma related to fish consumption. Arch Environ Health. 1994, 49 (6): 477-486.

    Article  CAS  Google Scholar 

  3. Svensson BG, Nilsson A, Jonsson E, Schutz A, Akesson B, Hagmar L: Fish consumption and exposure to persistent organochlorine compounds, mercury, selenium and methylamines among Swedish fishermen. Scand J Work Environ Health. 1995, 21 (2): 96-105.

    Article  CAS  Google Scholar 

  4. Guo YL, Hsu PC, Hsu CC, Lambert GH: Semen quality after prenatal exposure to polychlorinated biphenyls and dibenzofurans. Lancet. 2000, 356 (9237): 1240-1241. 10.1016/S0140-6736(00)02792-6.

    Article  CAS  Google Scholar 

  5. Hauser R, Chen Z, Pothier L, Ryan L, Altshul L: The relationship between human semen parameters and environmental exposure to polychlorinated biphenyls and p, p'-DDE. Environ Health Perspect. 2003, 111 (12): 1505-1511.

    Article  CAS  Google Scholar 

  6. Richthoff J, Rylander L, Jonsson BA, Akesson H, Hagmar L, Nilsson-Ehle P, Stridsberg M, Giwercman A: Serum levels of 2, 2', 4, 4', 5, 5'-hexachlorobiphenyl (CB-153) in relation to markers of reproductive function in young males from the general Swedish population. Environ Health Perspect. 2003, 111 (4): 409-413.

    Article  CAS  Google Scholar 

  7. Rignell-Hydbom A, Rylander L, Giwercman A, Jonsson BA, Nilsson-Ehle P, Hagmar L: Exposure to CB-153 and p, p'-DDE and male reproductive function. Hum Reprod. 2004, 19 (9): 2066-2075. 10.1093/humrep/deh362.

    Article  CAS  Google Scholar 

  8. Rignell-Hydbom A, Rylander L, Giwercman A, Jonsson BA, Lindh C, Eleuteri P, Rescia M, Leter G, Cordelli E, Spano M, et al: Exposure to PCBs and p, p'-DDE and human sperm chromatin integrity. Environ Health Perspect. 2005, 113 (2): 175-179.

    Article  CAS  Google Scholar 

  9. Tiido T, Rignell-Hydbom A, Jonsson B, Giwercman YL, Rylander L, Hagmar L, Giwercman A: Exposure to persistent organochlorine pollutants associates with human sperm Y:X chromosome ratio. Hum Reprod. 2005, 20 (7): 1903-1909. 10.1093/humrep/deh855.

    Article  CAS  Google Scholar 

  10. Glynn AW, Wolk A, Aune M, Atuma S, Zettermark S, Maehle-Schmid M, Darnerud PO, Becker W, Vessby B, Adami HO: Serum concentrations of organochlorines in men: a search for markers of exposure. Sci Total Environ. 2000, 263 (1–3): 197-208. 10.1016/S0048-9697(00)00703-8.

    Article  CAS  Google Scholar 

  11. Grimvall E, Rylander L, Nilsson-Ehle P, Nilsson U, Stromberg U, Hagmar L, Ostman C: Monitoring of polychlorinated biphenyls in human blood plasma: methodological developments and influence of age, lactation, and fish consumption. Arch Environ Contam Toxicol. 1997, 32 (3): 329-336. 10.1007/s002449900193.

    Article  CAS  Google Scholar 

  12. Brouwer A, Ahlborg UG, Van den Berg M, Birnbaum LS, Boersma ER, Bosveld B, Denison MS, Gray LE, Hagmar L, Holene E, et al: Functional aspects of developmental toxicity of polyhalogenated aromatic hydrocarbons in experimental animals and human infants. Eur J Pharmacol. 1995, 293 (1): 1-40. 10.1016/0014-2999(95)90111-6.

    Article  CAS  Google Scholar 

  13. Sjodin A, Hagmar L, Klasson-Wehler E, Bjork J, Bergman A: Influence of the consumption of fatty Baltic Sea fish on plasma levels of halogenated environmental contaminants in Latvian and Swedish men. Environ Health Perspect. 2000, 108 (11): 1035-1041. 10.2307/3434955.

    Article  CAS  Google Scholar 

  14. Skerfving S, Bencko V, Vahter M, Schutz A, Gerhardsson L: Environmental health in the Baltic region – toxic metals. Scand J Work Environ Health. 1999, 25 (Suppl 3): 40-64.

    CAS  Google Scholar 

  15. Homma-Takeda S, Kugenuma Y, Iwamuro T, Kumagai Y, Shimojo N: Impairment of spermatogenesis in rats by methylmercury: involvement of stage- and cell-specific germ cell apoptosis. Toxicology. 2001, 169 (1): 25-35. 10.1016/S0300-483X(01)00487-5.

    Article  CAS  Google Scholar 

  16. Orisakwe OE, Afonne OJ, Nwobodo E, Asomugha L, Dioka CE: Low-dose mercury induces testicular damage protected by zinc in mice. Eur J Obstet Gynecol Reprod Biol. 2001, 95 (1): 92-96. 10.1016/S0301-2115(00)00374-2.

    Article  CAS  Google Scholar 

  17. Burton GV, Meikle AW: Acute and chronic methyl mercury poisoning impairs rat adrenal and testicular function. J Toxicol Environ Health. 1980, 6 (3): 597-606.

    Article  CAS  Google Scholar 

  18. Monsees TK, Franz M, Gebhardt S, Winterstein U, Schill WB, Hayatpour J: Sertoli cells as a target for reproductive hazards. Andrologia. 2000, 32 (4–5): 239-246. 10.1046/j.1439-0272.2000.00391.x.

    Article  CAS  Google Scholar 

  19. Choy CM, Lam CW, Cheung LT, Briton-Jones CM, Cheung LP, Haines CJ: Infertility, blood mercury concentrations and dietary seafood consumption: a case-control study. Bjog. 2002, 109 (10): 1121-1125.

    CAS  Google Scholar 

  20. Dickman MD, Leung CK, Leong MK: Hong Kong male subfertility links to mercury in human hair and fish. Sci Total Environ. 1998, 214: 165-174. 10.1016/S0048-9697(98)00062-X.

    Article  CAS  Google Scholar 

  21. Dickman MD, Leung KM: Mercury and organochlorine exposure from fish consumption in Hong Kong. Chemosphere. 1998, 37 (5): 991-1015. 10.1016/S0045-6535(98)00006-X.

    Article  CAS  Google Scholar 

  22. Keck C, Bergmann M, Ernst E, Muller C, Kliesch S, Nieschlag E: Autometallographic detection of mercury in testicular tissue of an infertile man exposed to mercury vapor. Reprod Toxicol. 1993, 7 (5): 469-475. 10.1016/0890-6238(93)90092-L.

    Article  CAS  Google Scholar 

  23. Choy CM, Yeung QS, Briton-Jones CM, Cheung CK, Lam CW, Haines CJ: Relationship between semen parameters and mercury concentrations in blood and in seminal fluid from subfertile males in Hong Kong. Fertil Steril. 2002, 78 (2): 426-428. 10.1016/S0015-0282(02)03232-6.

    Article  Google Scholar 

  24. Grandjean P, Weihe P, Burse VW, Needham LL, Storr-Hansen E, Heinzow B, Debes F, Murata K, Simonsen H, Ellefsen P, et al: Neurobehavioral deficits associated with PCB in 7-year-old children prenatally exposed to seafood neurotoxicants. Neurotoxicol Teratol. 2001, 23 (4): 305-317. 10.1016/S0892-0362(01)00155-6.

    Article  CAS  Google Scholar 

  25. Vettori MV, Goldoni M, Caglieri A, Poli D, Folesani G, Ceccatelli S, Mutti A: Antagonistic effects of methyl-mercury and PCB153 on PC12 cells after a combined and simultaneous exposure. Food Chem Toxicol. 2006, 44 (9): 1505-1512. 10.1016/j.fct.2006.04.009.

    Article  CAS  Google Scholar 

  26. Roegge CS, Wang VC, Powers BE, Klintsova AY, Villareal S, Greenough WT, Schantz SL: Motor impairment in rats exposed to PCBs and methylmercury during early development. Toxicol Sci. 2004, 77 (2): 315-324. 10.1093/toxsci/kfg252.

    Article  CAS  Google Scholar 

  27. Bemis JC, Seegal RF: Polychlorinated biphenyls and methylmercury act synergistically to reduce rat brain dopamine content in vitro. Environ Health Perspect. 1999, 107 (11): 879-885. 10.2307/3454475.

    Article  CAS  Google Scholar 

  28. Widholm JJ, Villareal S, Seegal RF, Schantz SL: Spatial alternation deficits following developmental exposure to Aroclor 1254 and/or methylmercury in rats. Toxicol Sci. 2004, 82 (2): 577-589. 10.1093/toxsci/kfh290.

    Article  CAS  Google Scholar 

  29. Fischer C, Fredriksson A, Ericsson P: Co-exposure to an ortho-substituted PCB (PCB 153) and methylmercury enhances developmental neurotoxic effects. Dioxin -04: 2004. 2004, 3160-3162.

    Google Scholar 

  30. Stewart PW, Reihman J, Lonky EI, Darvill TJ, Pagano J: Cognitive development in preschool children prenatally exposed to PCBs and MeHg. Neurotoxicol Teratol. 2003, 25 (1): 11-22. 10.1016/S0892-0362(02)00320-3.

    Article  CAS  Google Scholar 

  31. WHO: WHO laboratory manual for examination of human semen and sper-cervial mucus interaction. 1999, Cambridge University Press

    Google Scholar 

  32. Cooper TG, Bjorndahl L, Vreeburg J, Nieschlag E: Semen analysis and external quality control schemes for semen analysis need global standardization. Int J Androl. 2002, 25 (5): 306-311. 10.1046/j.1365-2605.2002.00370.x.

    Article  CAS  Google Scholar 

  33. Evenson DP, Larson KL, Jost LK: Sperm chromatin structure assay: its clinical use for detecting sperm DNA fragmentation in male infertility and comparisons with other techniques. J Androl. 2002, 23 (1): 25-43.

    Google Scholar 

  34. Sandborgh-Englund G, Elinder CG, Langworth S, Schutz A, Ekstrand J: Mercury in biological fluids after amalgam removal. J Dent Res. 1998, 77 (4): 615-624.

    Article  CAS  Google Scholar 

  35. Rothman K: Modern Epidemiology. 1986, Boston: Little, Brown & Co

    Google Scholar 

  36. Assmann SF, Hosmer DW, Lemeshow S, Mundt KA: Confidence intervals for measures of interaction. Epidemiology. 1996, 7 (3): 286-290. 10.1097/00001648-199605000-00012.

    Article  CAS  Google Scholar 

  37. Bonde JP, Storgaard L: How work-place conditions, environmental toxicants and lifestyle affect male reproductive function. Int J Androl. 2002, 25 (5): 262-268. 10.1046/j.1365-2605.2002.00373.x.

    Article  CAS  Google Scholar 

  38. Eskenazi B, Wyrobek AJ, Sloter E, Kidd SA, Moore L, Young S, Moore D: The association of age and semen quality in healthy men. Hum Reprod. 2003, 18 (2): 447-454. 10.1093/humrep/deg107.

    Article  CAS  Google Scholar 

  39. Magnus O, Tollefsrud A, Abyholm T, Purvis K: Effects of varying the abstinence period in the same individuals on sperm quality. Arch Androl. 1991, 26 (3): 199-203.

    Article  CAS  Google Scholar 

  40. Schwartz D, Laplanche A, Jouannet P, David G: Within-subject variability of human semen in regard to sperm count, volume, total number of spermatozoa and length of abstinence. J Reprod Fertil. 1979, 57 (2): 391-395.

    Article  CAS  Google Scholar 

  41. Giwercman A, Richthoff J, Hjollund H, Bonde JP, Jepson K, Frohm B, Spano M: Correlation between sperm motility and sperm chromatin structure assay parameters. Fertil Steril. 2003, 80 (6): 1404-1412. 10.1016/S0015-0282(03)02212-X.

    Article  Google Scholar 

  42. Spano M, Kolstad AH, Larsen SB, Cordelli E, Leter G, Giwercman A, Bonde JP: The applicability of the flow cytometric sperm chromatin structure assay in epidemiological studies. Asclepios. Hum Reprod. 1998, 13 (9): 2495-2505. 10.1093/humrep/13.9.2495.

    Article  CAS  Google Scholar 

  43. Jensen TK, Andersson AM, Jorgensen N, Andersen AG, Carlsen E, Petersen JH, Skakkebaek NE: Body mass index in relation to semen quality and reproductive hormones among 1,558 Danish men. Fertil Steril. 2004, 82 (4): 863-870. 10.1016/j.fertnstert.2004.03.056.

    Article  CAS  Google Scholar 

  44. Andolz P, Bielsa MA, Andolz A: Circannual variation in human semen parameters. Int J Androl. 2001, 24 (5): 266-271. 10.1046/j.1365-2605.2001.00297.x.

    Article  CAS  Google Scholar 

  45. Chen Z, Godfrey-Bailey L, Schiff I, Hauser R: Impact of seasonal variation, age and smoking status on human semen parameters: The Massachusetts General Hospital experience. J Exp Clin Assist Reprod. 2004, 1 (1): 2-10.1186/1743-1050-1-2.

    Article  Google Scholar 

  46. Gyllenborg J, Skakkebaek NE, Nielsen NC, Keiding N, Giwercman A: Secular and seasonal changes in semen quality among young Danish men: a statistical analysis of semen samples from 1927 donor candidates during 1977–1995. Int J Androl. 1999, 22 (1): 28-36. 10.1046/j.1365-2605.1999.00137.x.

    Article  CAS  Google Scholar 

  47. Levine RJ: Male factors contributing to the seasonality of human reproduction. Ann N Y Acad Sci. 1994, 709: 29-45. 10.1111/j.1749-6632.1994.tb30386.x.

    Article  CAS  Google Scholar 

  48. Politoff L, Birkhauser M, Almendral A, Zorn A: New data confirming a circannual rhythm in spermatogenesis. Fertil Steril. 1989, 52 (3): 486-489.

    Article  CAS  Google Scholar 

  49. Kamal KM, Jarvi K, Zini A: Microsurgical varicocelectomy in the era of assisted reproductive technology: influence of initial semen quality on pregnancy rates. Fertil Steril. 2001, 75 (5): 1013-1016. 10.1016/S0015-0282(01)01698-3.

    Article  CAS  Google Scholar 

  50. Veznik Z, Pospisil L, Svecova D, Zajicova A, Unzeitig V: Chlamydiae in the ejaculate: their influence on the quality and morphology of sperm. Acta Obstet Gynecol Scand. 2004, 83 (7): 656-660. 10.1111/j.0001-6349.2004.00542.x.

    Article  Google Scholar 

  51. Saint-Amour D, Roy MS, Bastien C, Ayotte P, Dewailly E, Despres C, Gingras S, Muckle G: Alterations of visual evoked potentials in preschool Inuit children exposed to methylmercury and polychlorinated biphenyls from a marine diet. Neurotoxicology. 2006, 27 (4): 567-578. 10.1016/j.neuro.2006.02.008.

    Article  CAS  Google Scholar 

  52. Clarkson TW: The toxicology of mercury. Crit Rev Clin Lab Sci. 1997, 34 (4): 369-403.

    Article  CAS  Google Scholar 

  53. Chia SE, Ong CN, Lee ST, Tsakok FH: Blood concentrations of lead, cadmium, mercury, zinc, and copper and human semen parameters. Arch Androl. 1992, 29 (2): 177-183.

    Article  CAS  Google Scholar 

  54. Leung TY, Choy CM, Yim SF, Lam CW, Haines CJ: Whole blood mercury concentrations in sub-fertile men in Hong Kong. Aust N Z J Obstet Gynaecol. 2001, 41 (1): 75-77.

    Article  CAS  Google Scholar 

  55. Hanf V, Forstmann A, Costea JE, Schieferstein G, Fischer I, Schweinsberg F: Mercury in urine and ejaculate in husbands of barren couples. Toxicol Lett. 1996, 88 (1–3): 227-231. 10.1016/0378-4274(96)03742-3.

    Article  CAS  Google Scholar 

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Final support was given by the Swedish Research Council for Medicine and the Swedish Research Council for Environment, Agriculture Sciences and Spatial Planning, and the Medical Faculty of Lund University, Sweden. We thank Ms Helene Åkesson, Ms Berit Holmskov and Mr Giovanni Ferrari for skilful technical assistance.

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Correspondence to Anna Rignell-Hydbom.

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Authors' contributions

A R-H collected all samples and carried out some of the semen analysis. Drafted the manuscript and performed some of the statistical analysis. A.A performed the statistical analysis and helped to draft the manuscript. T.L carried out the mercury analysis. B.AG. J was responsible for the organochlorine analysis. T.T performed the FISH analysis. M.S performed the SCSA analysis and helped to draft the manuscript. All authors have read and commented on the manuscript.

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Rignell-Hydbom, A., Axmon, A., Lundh, T. et al. Dietary exposure to methyl mercury and PCB and the associations with semen parameters among Swedish fishermen. Environ Health 6, 14 (2007).

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