Environ Sci Pollut Res
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Fig. 5 The median concentration of selected compounds for winter (W, full-colored column) and summer (S, stripped column) cruises. Data: see Tab. S8
period as well (Fig. 5). The high summer concentrations for
PFOA, PFOS-1, and ATR at PB1-3, shown in Tab. S8, should
be interpreted with precaution as they are statistically of low
relevance (only one cruise). Flowever, for most herbicides, on
average, high spatial variations are observed in summer.
Especially, DIU and Irgarol (IRG) exhibit high hot spots at
the western coastal stations (KB2, MB1, Tab. S8). Even
though DIU is prohibited as a pesticide, in Germany since
2009, it is still used as a biocide and was detectable in the
marine environment during the winter cruises (2009-2014)
(European Commission 2007). Other herbicides (ISO,
MCPA, TERB) show elevated concentrations at the western
stations as well, but to a much smaller extent (Tab. S8). For
TERB, it was reported that its occurrence is of high spatial and
temporal variability (Orlikowska et al. 2015). Thus, for most
herbicides, more or less pronounced concentration gradients
can be observed during summer from west to east.
In contrast, 2,4-D shows high summer concentrations at the
eastern stations, starting at DZ1 and TF030 (north of the
Darss) and peaking at the Arkona Basin (TF113 and
TF109). 2,4-D shows high concentrations at the Odra near
station PB1-3. Another compound with large input from the
Odra is CARB (PB1-3, 7.2-12.2 ng/L), despite that it does not
show elevated concentrations at the Arkona Basin (TF109,
1.6-2.3 ng/L, Fig. 5, Tab. S7). In 2013, Bjorlenius et al.
(2018) conducted widespread pharmaceutical screening in
Baltic Sea coastal waters. The detected CARB concentrations
during this study are in similar range (2.5-9.1 ng/L, 2.1-3.3
ng/L, respectively) as station PB1-3 and TF109. Furthermore,
the study presented a similar decrease from the near coastal
water in the Odra Bay towards the Arkona Basin. ISO and
TERB show elevated concentrations at PB1-3 to a medium
extent (Tab. S8). For most other compounds, the Odra input
seems to be less pronounced.
Spatial distribution in the central and eastern Baltic
Sea
The station net, sampled during the MM0803 cruise, allowed
the investigation of the occurrence of the determined com
pounds in the central and eastern part of the Baltic Sea (parts
of the PFAS data has been published by Kirchgeorg et al.
(2010)). The median results are displayed in Fig. 6a, b (data;
Tab. S9). Most of the prominent compoimds were detected in
the east, at concentrations similar to the western and central
part of the Baltic Sea (median east 10.7 ng/L (n = 15), median
west 10.0 ng/L (;? = 25), Tab. S9, east-west split at N 16° 30'
0"). Thus, there is a fairly homogenous distribution of
micropollutants in the Baltic Sea, although the concentration
range in the west is higher than in the east (west 5.9-27.4 ng/
L, east 5.9-12.9 ng/L, Tab. S9). At the eastern edge of the
survey area, the concentrations split into lower concentrations
at the northern stations of the Bothnian Sea (GB2 and GB3),
and higher concentrations at the southern stations of the outer
GulfofFinland (GF4 and NG3-4) (Fig. 6a). The degree ofthis
“splitting” is different for the various micropollutants. In the
western part of the Baltic Sea, the three most dominating
compoimds are DIU, 2,4-D, and ATR, whereas, in the eastern
part, ATR, MCPA, and 2,4-D are the more dominating com
pounds, but at a marginally lower level.
A homogenous distribution, with gradually declining con
centrations from west to north-east, is observed for PFOA. No
significant variability, for the Gulf of Finland and only a small
decrease for the Bothnian Sea, was identified (Fig. 6a). The
detected concentrations of PFASs, during the MM0308, are in
a similar range as published PFAS concentrations by
Kirchgeorg et al. (2010) for the same year (Tab. S15).
Similar distributions are encountered for PFOS and ISO
(Fig. 6a, b. Tab. S9). ISO was increased up to 4.0 ng/L only