Bulk atmospheric deposition samples were regularly collected at four high mountain European areas (Table 1) over the same period: monthly between 2004 and 2006 in Gossenköllesee (Tyrolean Alps), Redon (Central Pyrenees) and Skalnate Pleso (Tatra Mountains) and biweekly between 2004 and 2007 in Lochnagar (Grampian Mountains) (Fig. 1). All lakes are located in remote areas under special protection. Lake Redon is situated within the Aigüestortes area belonging to the Natura 2000 European network. Lochnagar is located within the Deeside and Lochnagar National Scenic Area, which define protected landscapes in Scotland in the same category as national parks. Gossenköllesee and its catchment area constituted one of the UNESCO Biosphere Reserve from 1977 to 2014, while Skalnate Pleso is situated in the area of the Tatra National Park. Meteorological parameters, i.e. air temperature and precipitation, were provided by automatic weather stations (AWSs) located at each site except in Skalnate Pleso where data were provided by the meteorological observatory of the Earth Science Institute of the Slovak Academy of Science. In summer, precipitation was collected with a polyethylene funnel (different diameter depending on the sampling site) and connected to stainless steel or Teflon-coated reservoirs by a tube. In winter, precipitation occurs as snow and sampling was performed either with a wider tube assembled to the top of a tank or with cylindrical collectors. These devices were equipped with windscreens around the collector's mouth to prevent wind disturbance. The samplers were placed 1.5 m above ground level. Samples were filtered on site using pre-weighed Whatman glass fibre filters (GF/B, 45 mm diameter, 1 µm pore size) at each field station and the filtrates were solid-phase-extracted with C18 Empore disks (47 mm diameter, 0.5 mm thickness) as described elsewhere (Carrera et al., 1998). After sample removal, the bulk collectors were rinsed with Milli-Q water, which was filtered and solid-phase-extracted with the same disk used for the corresponding deposition sample. Glass fibre filters and disks were wrapped in aluminium foil and transported frozen to the laboratory. More details on sampling procedures are reported elsewhere (Arellano et al., 2015).

Glass-fibre filters were freeze-dried and weighed for measuring total particle content in bulk atmospheric deposition. PAHs were extracted from the filters by sonication with dichloromethane:methanol (2:1) (3×10 mL, 20 min each). The pollutants adsorbed in the C18 disks were eluted sequentially with methanol, cyclohexane and dichloromethane (Carrera et al., 1998). Both phases were combined and purified by column adsorption chromatography with aluminium oxide after adding a recovery standard mixture of perdeuterated anthracene-d10, benz[a]anthracene-d10, benzo[b]fluoranthene-d12 and benzo[ghi]perylene-d12 (Dr. Ehrenstorfer GmbH; Augsburg, Germany). Prior to instrumental analysis, samples were spiked with an internal standard mixture of pyrene-d10 and perylene-d12 dissolved in isooctane.

PAHs were analysed by gas chromatography–mass spectrometry (GC–MS; Trace DSQ II Instrument Thermo, Austin, USA.) using a 60 m HP-5MS column (0.25 mm i.d. ×0.25 µm film thickness). The oven temperature programme started at 90 ∘C (held for 1 min) and increased to 120 ∘C at 10 ∘C min-1, and then to 310 ∘C at 6 ∘C min-1 (final holding time 25 min). Injector, transfer line and ion source temperatures were 280, 270 and 250 ∘C. Helium was used as the carrier gas (1.2 mL min-1). The injector operated in splitless mode. Data were acquired in electron impact and selective ion monitoring modes. Further details on the ions selected for quantification and mass spectrometric conditions are reported elsewhere (Fernández et al., 1999).

Quantification was performed by the internal standard method. Recoveries of the analytical procedure were evaluated using surrogate standards. The reported values were corrected by these recoveries, which varied between 76 % for benz[a]anthracene-d10 and 53 % for benzo[ghi]perylene-d12.

Field and procedural blanks were collected at each sampling site and processed together with the samples. For field blanks, Milli-Q water was filtered and solid-phase adsorbed, transported and stored for subsequent analysis. In general, blank values represented less than 10 % of bulk deposition sample concentrations. These values were used to determine method detection limits (MDLs) that were established as average blank values plus 3 times the standard deviation. These limits ranged between 0.45 and 28 pg depending on the compound.

Three-day back trajectories were calculated using the Hybrid Single-Particle Lagrangian Integrated Trajectory (HYSPLIT data available at http://ready.arl.noaa.gov/HYSPLIT.php) modelling system developed by the National Oceanic and Atmospheric Administration (NOAA) Air Resources Laboratory (ARL) (Draxler and Hess, 1998; Draxler and Rolph, 2013).

The meteorological data used to compute the 6-hourly back trajectories were obtained from the National Centre for Environmental Prediction (NECP) Global Data Assimilation System (GDAS) and from Eta Data Assimilation System (EDAS). The trajectories were calculated for those days with precipitation (rain or snow) and every 2 days when no precipitation was recorded by the AWS.

Different altitudes were used to calculate the trajectories. Usually, they did not show differences; thus altitudes representing the air mass above the sampling point were selected at 3000 m above sea level (a.s.l.) in Redon and Skalnate Pleso, 3500 m a.s.l. for Gossenköllesee and 2000 m a.s.l. for Lochnagar. The total number of backward trajectories was 1968, being 335, 475, 598 and 560 for Redon, Gossenköllesee, Lochnagar and Skalnate Pleso. More details on air mass trajectory determination can be found in Arellano et al. (2014).

Mean, minimum and maximum atmospheric deposition fluxes of the PAHs at the four sampling sites during the studied period are summarised in Table 1. A strong contrast is found between the total PAH mean fluxes found in Lochnagar, Gossenköllesse and Redon of 0.80–2.1 µg m-2 month-1, and in Skalnate Pleso of 9.7 µg m-2 month-1, the latter showing PAH deposition fluxes between 5 and 10 times higher than the others. In Table 2, these deposition fluxes are compared with those observed in different environments, e.g. remote, rural, coastal, industrial, suburban and urban areas. In addition, the deposition fluxes of benzo[a]pyrene are also included in this Table for comparison. This hydrocarbon is a known carcinogen taken for reference in regulatory pollution values of PAH concentrations. As observed for total PAHs, the benzo[a]pyrene mean deposition fluxes in Skalnate Pleso, 280 ng m-2 month-1, are much higher than those observed in Lochnagar, Gossenköllesee and Redon, 20–61 ng m-2 month-1 (Table 2).

The observed PAH deposition fluxes in these high mountain European areas, 0.02–0.28 µg m-2 d-1, range among the lowest values reported in the literature (Table 2). Thus, PAH deposition fluxes of 0.40–0.55 µg m-2 d-1 have been recorded at remote sites from the USA (Su et al., 2007; McVeety and Hites, 1988; Leister and Baker, 1994; Dickhut and Gustafsson, 1995), whereas Foan et al. (2012) reported mean deposition fluxes of PAHs of 0.18 µg m-2 d-1 in remote areas of northern Spain. The reported PAH depositions in background areas are again higher than those observed in the high mountain European sites, 0.19–0.82 µg m-2 d-1 (Brorstrom-Lunden et al., 1998; Horstmann and McLachlan, 1998; Garban et al., 2002). Higher PAH deposition has also been measured in rural areas, 0.09–3.9 µg m-2 d-1 (Kiss et al., 2001; Garban et al., 2002; Menichini et al., 2006; Gocht et al., 2007; Wang et al., 2011b) or in coastal sites, 0.4–6.8 µg m-2 d-1 (Lipiatou et al., 1997; Golomb et al., 2001; Park et al., 2001; Brun et al., 2004; Poor et al., 2004; Gigliotti et al., 2005; Tsapakis et al., 2006). As expected, the PAH deposition fluxes measured in industrial areas, 0.3–19.5 µg m-2 d-1 (Esen et al., 2008), in suburban areas, 0.13–39 µg m-2 d-1 (Bae et al., 2002; Motelay-Massei et al., 2003; Fang et al., 2004; Gigliotti et al., 2005), and in urban areas 0.63–49 µg m-2 d-1 (Halsall et al., 1997; Bae et al., 2002; Garban et al., 2002; Ollivon et al., 2002; Fang et al., 2004; Gigliotti et al., 2005; Pekey et al., 2007; Wang et al., 2011b), are higher than those in the remote European mountains.

Concerning the benzo[a]pyrene deposition fluxes, again those observed in the European high mountains, 20–280 ng m-2 month-1, range among the lowest described (Table 2). However, the values reported for different types of sites do not show uniform trends such as those observed when considering total PAH deposition. Thus, benzo[a]pyrene deposition fluxes ranged between 225 and 500 ng m-2 month-1 in remote sites (Su et al., 2007; McVeety and Hites, 1988; Leister and Baker, 1994; Foan et al., 2012). In forested and rural areas, the benzo[a]pyrene deposition has been measured to account between 140 and 15 000 ng m-2 month-1 (Horstmann and McLachan, 1998; Garban et al., 2002; Kiss et al., 2001; Menichini et al., 2006). Finally, benzo[a]pyrene fluxes between 42 and 9000 ng m-2 month-1 have been reported in urban sites (Halsall et al., 1997; Gigliotti et al., 2005; Pekey et al., 2007).

The differences between Lochnagar, Gossenköllesee, and Redon, and separately at Skalnate Pleso cannot be explained by differences in precipitation (e.g. 120 mm month-1 in Skalnate Pleso and 66–129 mm month-1 in the other sites) (Table 1) or particle flux (330 mg m-2 month-1 in Skalnate Pleso and 145–320 mg m-2 month-1 in the other lakes) (Table 1). The higher PAH deposition in Skalnate Pleso compared to the other sites is in agreement with atmospheric PAH concentrations and probably reflects regional contributions from industrial emissions by factories located in southern Poland and other areas such as the Black Triangle (Fig. 1) (van Drooge et al., 2010). This geographical difference is consistent with PAH concentrations reported in air on a European scale, which identified high PAH emissions in eastern Europe (Jaward et al., 2004).

Comparison of the PAH deposition measured in Gossenköllesee and Redon in 2004–2006 with those found in 1996–1998 (Fernandez et al., 2003) shows nearly the same values at Gossenköllesee (Table 2) but statistically significant differences in Redon (p>0.05), involving lower fluxes in the 2004–2006 period. In both cases, the deposition fluxes range among the lowest measured in remote sites (Table 2), which suggest that they correspond to background concentrations of long-range-transported PAHs and not to direct pollution inputs. A very similar deposition of total particles has been measured in Gossenköllesee in the two sampling periods, 145 mg m-2 month-1 in 4 June–6 August (Table 1) and 130 mg m-2 month-1 in October 1996–October 1998 (Fernandez et al., 2003), whereas total precipitation shows a strong difference, with lower values in 2004–2006 of 66 mm month-1 (Table 1) vs. 110 mm month-1 (Fernandez et al., 2003) in the 1996–1998 period. Precipitation in the recent period is quite low, suggesting that the PAH fallout fluxes at Gossenköllesee were mainly determined by particle deposition. By contrast, in Redon both decreases in particle deposition of 320 mg m-2 month-1 (Table 1) from 420 mg m-2 month-1 (Fernandez et al., 2003) and atmospheric precipitation of 79 mm month-1 (Table 1) from 110 mm month-1 (Fernandez et al., 2003) are observed when comparing the recent (4 May–6 September) and previous sampling periods (March 1997–October 1998). The differences in the deposition of particles and wet precipitation are consistent with the lower PAH fallout from the atmosphere observed at this site in 2004–2006.

Overall, the PAH composition in the atmospheric deposition samples was dominated by parent compounds and, among these, the low molecular weight fraction (LMW-PAHs, from acenaphthene to pyrene). Phenanthrene, fluoranthene and pyrene were the most abundant, representing between 32 % and 60 % of the total PAH mixture (Fig. 2). These compounds are also the most abundant in the atmosphere, namely in the gas phase (Fernández et al., 2002). Dominance of LMW-PAHs in atmospheric deposition and, particularly, phenanthrene, fluoranthene and pyrene, is a common feature of studies in Europe (Halsall et al., 1997; Holoubek et al., 2007; Fernández et al., 2003; Cetin et al., 2016), America (Gigliotti et al., 2005; Brun et al., 2004) and Asia (Li et al., 2009; Wang et al., 2011b; Sharma et al., 2018).

In the present study, no significant differences in qualitative composition between sites were observed, except for the relative proportion of phenanthrene, the most volatile and abundant compound. The PAH distributions from the sites with lower annual mean temperature, Gossenköllesee and Skalnate Pleso at -1.4 and 2.2 ∘C respectively (Table 1), were those with highest proportion of this compound (31 %–32 %), whereas the lowest was observed in Redon (12 %, 5.3 ∘C). Lochnagar (4.9 ∘C) also showed a low but intermediate proportion of phenanthrene (18 %). Higher local temperatures likely involve lower condensation of the most volatile PAHs and therefore lower deposition fluxes.

Consistently with these differences in phenanthrene content, the coldest sites, Gossenköllesee and Skalnate Pleso, were those with the highest deposition of low and high molecular weight PAHs, of 0.89 and 0.40 µg m-2 month-1 and 5.6 and 3.9 µg m-2 month-1 (Table 1), whereas this proportion was inverse in Redon, with 0.30 and 0.49 µg m-2 month-1, and about the same in Lochnagar, with 1.1 and 0.97 µg m-2 month-1 (Table 1).

Further assessment on the qualitative changes in PAH composition between samples can be obtained from the study of diagnostic ratios (Table 3; Sicre et al., 1987). The pyrene / (fluoranthene + pyrene) ratios showed a uniform composition between samples and therefore no environmental dependence. In contrast, the sites located at lower altitude, e.g. Lochnagar (790 m) and Skalnate (1787 m) were those with a higher relative proportion of benz[a]anthracene to its less labile to photooxidation isomer, chrysene (Ding et al., 2007; Xing et al., 2016). The lower-altitude sites receive less insolation than those located at higher altitude. Accordingly, the average benz[a]anthracene / (chrysene + benz[a]anthracene) ratios were higher in Skalnate (1787 m a.s.l.) and Lochnagar (790 m a.s.l.), between 0.28 and 0.31, than in Gossenköllesee (2413 m a.s.l.) and Redon (2230 m a.s.l.), 0.17–0.18 (Table 3). Furthermore, the average benz[a]anthracene / (chrysene + benz[a]anthracene) ratio in Skalnate Pleso (0.28; 1787 m) was even lower than the one in Lochnagar (0.31; 790 m). Thus, insolation and not local temperature was the main driver of the relative changes between benz[a]anthracene and chrysene in all sites. Differentiation between the cold (November–May) and the warm (June–October) sampling periods, involving higher insolation in the latter, did not show significant differences in this ratio in Gossenköllesee, Redon and Lochnagar (Table 3). However, in Skalnate Pleso higher benz[a]anthracene / (chrysene + benz[a]anthracene) ratio was observed in the cold season (Table 3), which confirmed a predominant insolation effect in the relative concentrations of these two PAHs.

The average benzo[a]pyrene / (benzo[e]pyrene + benzo[a]pyrene) ratios found in Gossenköllesee, Redon and Skalnate Pleso were also consistent with insolation differences, since the proportion of benzo[a]pyrene, the compound more labile to photooxidation, was higher at the lower-altitude sampling sites, at 0.38, 0.42 and 0.45 (Table 3). However, this trend was not observed in Lochnagar, the lowest-altitude site, which showed the lowest average benzo[a]pyrene / (benzo[e]pyrene + benzo[a]pyrene) ratio. In general, the benzo[a]pyrene / (benzo[e]pyrene + benzo[a]pyrene) ratio is less sensitive to photooxidation than the benz[a]anthracene / (chrysene + benz[a]anthracene) ratio (Behymer and Hites, 1988).

The influence of particle deposition, precipitation and temperature on PAH fallout fluxes at these remote sites was investigated. Pearson correlation coefficients between the log-transformed PAH monthly deposition fluxes and these variables were calculated at each site. The statistically significant correlations found at 95 % (p<0.05) and 99 % (p<0.01) confidence levels are shown in Table 4.

In Redon and Lochnagar, the two sites receiving highest precipitation, the fallout fluxes of most of these hydrocarbons were directly correlated to wet deposition, e.g. higher precipitation involving higher PAH fallout. At these two sites, no significant correlations were observed between PAH fluxes and particle deposition or temperature. Normalisation of PAH fallout to particle deposition also showed significant positive correlations with precipitation (p<0.01), which corroborated the dominant role of rain and snow in the transfer of PAHs from the atmosphere to the soil. These results are also consistent with reports indicating that particle scavenging processes are significant mechanisms of PAH removal from the atmosphere (Gocht et al., 2007; Li et al., 2016).

In Gossenköllesee, the site receiving lowest precipitation, 66 mm month-1 (Table 1), PAH fallout was significantly correlated to particle deposition for the higher molecular weight PAHs (p<0.05; Table 4) and no correlation was observed between PAH fluxes and precipitation. Normalisation of the PAH fluxes to particle deposition showed significant negative correlations with precipitation for some compounds in the low molecular weight range, e.g. fluoranthene, pyrene and chrysene (p<0.05; Table 4). The particle-normalised deposition flows of these compounds were also negatively correlated to temperature. Lower temperatures enhance the PAH transfer from gas phase to particles and this effect is stronger among the PAHs of higher volatility, such as fluoranthene, pyrene and chrysene. This association with the particulate matter increases the deposition of these compounds.

Previous studies considering the gas-particle partitioning of these compounds in Gossenköllesee, Redon and Skalnate Pleso showed that the observed distributions in Gossenköllesee and Skalnate more closely followed the theoretical slope constants of the correlations between gas-phase partition coefficients and octanol–air constants (Fernandez et al., 2002; van Drooge et al., 2010), which was consistent with a temperature-dependent reversible transfer between gas phase and particle adsorption. Moreover, the significant negative correlations of the particle-normalised deposition fluxes of these compounds in Gossenköllesee with precipitation may be explained by the significant positive correlation between precipitation and temperature at this site. Accordingly, in the cold period lower precipitation and higher particle-normalised PAH deposition were observed.

Skalnate Pleso has some specific features since this location receives enhanced PAH inputs from regional emissions. These emissions involve the release of large amounts of particulate matter containing PAHs (van Drooge et al., 2010). This site received the highest particle deposition flux, 330 µg m-2 month-1 (Table 1), and PAH fallout was significantly correlated with particle deposition (p<0.05; Table 4). Some PAHs, e.g. benzo[a]pyrene (R2=0.585), benzo[ghi]perylene (R2=0.516 at p<0.001) and coronene (R2=0.561), also showed significant negative correlations with temperature (p<0.05; Table 4), which may reflect the effects of higher winter production of electric power or other combustion processes in the region. These results are consistent with previous studies in urban and rural areas (Schifman and Boving, 2015; Birgul et al., 2011; Gaga et al., 2009; Gocht et al., 2007; Brun et al., 2004; Shahpoury et al., 2015), which also found higher PAH fluxes in winter. The observed seasonal trend in Skalnate Pleso could reflect direct impacts of regional sources, while Redon, Lochnagar and Gossenköllesee received PAH mixtures from more distant areas and no significant seasonal influences were recorded.

Normalisation of the PAH fallout to particle deposition showed that precipitation is not a main driver of the transfer of these hydrocarbons from atmosphere to soil in Skalnate Pleso. However, temperature appeared as a significant parameter that was negatively correlated with PAH deposition fluxes (p<0.05; Table 4). As in the case of Gossenköllesee, these negative correlations may reflect the higher adsorption of PAHs to particles at lower temperatures, involving higher particle PAH content and therefore higher deposition fluxes of these hydrocarbons. Lower temperatures enhance the capacity of settling particles for the transfer of PAHs from atmosphere to soil.

Determination of the PAH source regions for each site was performed by 72 h backward trajectory analyses using the HYSPLIT model for the entire sampling periods (Table 1). A detailed description of the back trajectory analyses performed in each study site is reported elsewhere (Arellano et al., 2014). Air mass back trajectories and their contributions to the total trajectories measured in each sampling period were assigned to each monthly deposition sample. The number of trajectories calculated in each sampling site is indicated in Table 5.

The relationship between air mass trajectories and PAH deposition was investigated for each sample. No trend was observed at Lochnagar, indicating diffuse PAH inputs from unspecific sources in this site.

In Skalnate Pleso, a negative dependence between particle-normalised PAH fluxes and air masses from the south was observed, which may indicate that particles from this origin were depleted in PAH content (Table 5).

In Gossenköllesee, total particle mass was negatively correlated with air masses from the North Atlantic (Table 5). These air masses were also negatively correlated with total PAHs, including LMW-PAHs and HMW-PAHs (from benzo[a]anthracene to coronene) (Table 5), which is consistent with the predominant role of particle deposition at this site (Table 4). Normalisation of PAH fallout to particle deposition showed a positive correlation with air masses from central and eastern Europe (Table 5).

The two main air mass trajectories arriving at Redon are clearly different in terms of meteorological characteristics and PAH deposition fluxes. As reported elsewhere, backwards air mass trajectories in Redon showed a well-defined seasonal pattern (Arellano et al., 2014). Southern trajectories were dominant during the warm season (June–October; 59 %; see Fig. 3 as an example), while North Atlantic trajectories prevailed during cold periods (November–May; 48 %). The central and eastern European trajectories identified in this site were less frequent and did not show any seasonal trend.

Southern air masses in this site are characterised by high temperature and particle content (positive correlation with T and particle deposition flows, Table 5), which is consistent with Saharan dust inputs and the well-known geographical characteristics of the northern African regions. In this case, a significant negative association was observed between particle-normalised PAH flows and air masses from this origin, mainly for the LMW-PAHs (Table 5), which may respond to both a gas-phase–aerosol displacement towards the former and a low PAH content of the Saharan dust in comparison to the PAH concentrations in particles from other areas. Despite this, the overall result is an increase in PAH loads to Redon during the warm periods due to the high amount of particles arriving at this site in spring–summer (Table 1). Air masses originating from the North Atlantic involved higher precipitation and lower particle content (significant positive and negative correlation with these variables respectively). Particle-normalised PAH fallout was positively correlated with air masses of this origin (Table 5), which was consistent with the dependence of PAH deposition on precipitation at this site (Table 4), likely enhanced by gas phase-aerosol partitioning of PAHs at low temperatures and increased scavenging efficiency of snow compared to rain (Fernandez et al., 2002; Arellano et al., 2011). Finally, air masses from central and eastern Europe are negatively correlated with PAH deposition fluxes, mainly for HMW-PAHs (Table 5). Air masses from this origin were therefore not significant for PAH fallout.

The atmospheric deposition samplers are located close to high mountain lakes. Previous studies of sediment cores in these lakes allowed the average PAH sediment fluxes to be determined in the top cores from Redon and Gossenköllesee, 120 and 125 µg m-2 yr-1 respectively (Fernandez et al., 1999). The sedimentation flux in Lochnagar was calculated from the PAH concentrations (4000 ng g-1 dw; data not published) using a sedimentation rate of 0.012 g cm-2 yr-1 (Rose, 2001), which resulted in a PAH flux of 480 µg m-2 yr-1. No lake sediment was available for Skalnate Pleso. Therefore, PAH fluxes from two nearby lakes in the Tatra Mountains were considered, e.g. Starolesnianske Pleso with 3000 µg m-2 yr-1 (Fernandez et al., 1999) and Ladove Pleso with 1400 µg m-2 yr-1 (Drooge et al., 2011).

Comparison of the PAH atmospheric deposition and lacustrine sedimentary fluxes showed much higher values in sediments, i.e. 24–100 and 120–3000 µg m-2 yr-1 respectively (Table 6). All lakes considered in this comparison are located in high mountain areas and their hydrological regime is determined by atmospheric precipitation into the watershed. The strong difference in flux values of the direct PAH atmospheric and sedimentary measurements may respond to processes such as the sediment focusing (Rowan et al., 1995) or lake sediment concentration of these hydrocarbons falling into the surface of the lake catchment. Studies at low altitude (seawater) have reported that air–water exchange is the most important process for low molecular weight PAH inputs into aquatic systems, exceeding the wet and dry deposition (Tsapakis et al., 2006; Ruge et al., 2015). In these high mountain lakes, the average concentrations of volatile PAHs are lower than in low-altitude aquatic systems, e.g. air and water concentrations of phenanthrene 0.99 ng m-3 (Fernandez et al., 2003; van Drooge et al., 2010) and 180 ng m-3 (Vilanova et al., 2001) respectively vs. 3.3–16 and 450–5600 ng m-3 in marine systems (Gigliotti et al., 2002; Tsapakis et al., 2006). The smaller concentrations in high mountains should involve lower gas–water transfer gradients (Nelson et al., 1998). Irrespective of these values, flux calculations in some of these high mountain lakes for compounds with properties similar to those of PAH showed that the main transfer essentially occurs from water to air (Meijer et al., 2009). The overall mass balance involved pollutant incorporation into the lake waters due to atmospheric precipitation and a substantial degassing to the atmosphere. Thus, in these lakes the air–water transfer processes cannot explain the higher sedimentation fluxes in comparison to atmospheric precipitation.

Regarding the contributions of PAH inputs from the watershed, an estimated sediment flux was calculated considering that the total amount of atmospheric PAHs deposited in the lake and its catchment area were accumulated in the lake sediments (Table 6). Interestingly, in the case of Lochnagar, Redon and Ladove, the ratio between calculated and measured sediment fluxes varied between 0.5 and 0.7. This consistency between atmospheric and sedimentary PAHs in high-altitude areas situated in different areas of Europe is remarkable, taking into account that it has been considered that sediment area equals lake area, and confirms the predominant atmospheric PAH origin in all studied sites. In Gossenköllesee, calculated sediment fluxes are 6-fold higher than measured values, which indicates that a small fraction of the PAHs deposited in the lake watershed accumulate in the surface sediments. On the contrary, calculated sediment fluxes in Starolesnianske Pleso are 1 order of magnitude lower than measured fluxes. The difference between Ladove and Starolesnianske Pleso, both situated in the same region could be related to orographic and hydrological characteristics of the latter that enhanced the PAH inputs and accumulation in Staroleniasnke Pleso sediments. This would explain the high concentration of PAHs found in this site in comparison with other lakes from the same area (Fernández et al., 1999, 2000). Another possibility for these differences could be related to a decrease in PAH atmospheric concentrations in this region during the last decades. Atmospheric deposition fluxes were measured between 2004 and 2006, whereas sedimentary fluxes correspond to 2001 in Ladove, but 10 years before in the case of Starolesnianske Pleso (1991).

Representation of the PAH sedimentary settling fluxes and average atmospheric deposition from each high mountain site showed a strong significant correlation (R2=0.99; p<0.01; Fig. 4). The standardised residual of this correlation fulfilled the normality conditions according to the Shapiro–Wilk test. Representation of the same data set excluding the area of highest PAH deposition, High Tatras, also showed a strong correlation (R2=0.86; p<0.20) but in this case there was no statistical significance given the small statistical freedom resulting from the number of cases considered. In any case, the values of both data sets (Table 6) followed parallel distributions.