Environ Sci Pollut Res DOI 10.1007/s11356-016-7473-8
RESEARCH ARTICLE
Determination of 210Po and 210Pb in red-capped scaber (Leccinum aurantiacum): bioconcentration and possible related dose assessment Dagmara I. Strumińska-Parulska 1 & Karolina Szymańska 1 & Grażyna Krasińska 1 & Bogdan Skwarzec 1 & Jerzy Falandysz 1
Received: 15 June 2016 / Accepted: 15 August 2016 # Springer-Verlag Berlin Heidelberg 2016
Abstract The paper presents the studies on 210Po and 210Pb activity determination in red-capped scaber (Leccinum aurantiacum (Bulliard) Gray) collected in northern Poland. The aims of the studies were to determine 210Po and 210Pb content in analyzed mushrooms, evaluate the bioconcentration levels, and estimate possible related annual effective radiation dose to mushrooms consumers. The activities of 210Po and 210 Pb in red-capped scaber were un-uniform and depended on sampling sites. But 210Po and 210Pb activity concentrations did not reflect their concentrations in topsoil. The results showed that the consumption of analyzed mushrooms should not increase significantly the total effective radiation dose from 210Po and 210Pb decay. Keywords Polonium 210Po . Radiolead 210Pb . Mushrooms . Soil . Effective radiation dose
Introduction Natural radioactive elements are present in very low concentrations in earth’s crust. Human activities, such as oil and gas exploration, mining, or coal burning in power plants, can enhance their content. Technologically enhanced naturally occurring radioactive materials (TENORM) consist of materials, usually industrial wastes or by-products enriched with radioactive elements found in the environment, such as uranium Responsible editor: Philippe Garrigues * Dagmara I. Strumińska-Parulska
[email protected]
1
Environmental Chemistry and Radiochemistry Department, Gdańsk University, Wita Stwosza 63, 80-308 Gdańsk, Poland
(U), thorium (Th), and potassium (K) and any of their decay products, such as radium (Ra) and radon (Rn), polonium (Po), and radiolead (Pb) (Bem 2005). Also, the accident at the Chernobyl nuclear power plant (April 1986), and the following radioactive contamination of most European territory, initiated extensive research on the environment, including mushrooms (Heinrich 1992). There were many papers written about cesium 137Cs accumulation in the environment, wild plants, berries, and mushrooms as well (Gruter 1964; Gruter 1971; Gwynn et al. 2013). But the studies on 210Po and 210Pb, much harder to conduct, were not carried out on such large scale (Guillen and Baeza 2014). Polonium 210Po (T1/2 = 138.4 days) and radiolead 210Pb (T1/2 = 22.2 years) appear at the end of the decay-chain of uranium 238U and are radio-ecologically interesting natural elements to investigate due to their significant radiotoxic characteristics (Heiserman 1997; Persson and Holm 2011). These radionuclides are introduced into the biosphere through various routes of terrestrial and marine pathways and continuously deposited from the atmosphere in association with aerosols (Persson and Holm 2011). 210Po and 210Pb are, together with radon and potassium, the natural radioactive material delivering the highest natural dose to living organisms: radon in air gives 0.5–1.36 mSv per year while 40K and 210Po + 210Pb + 226 Ra in diet give 165 and 140 μSv per year, respectively (Bem 2005). Mushrooms typically grow in forests and fields, but almost all ecosystems will favor their growth in the correct substrate medium (Kalač 2001; Kalač 2012). The fruiting bodies of mushrooms are generally considered as absorbing mineral constituents, including heavy metals and radionuclides. They could be used as environmental biomonitoring indicators to evaluate the level of the environment contamination as well as the quality of the ecosystem (Skwarzec and Jakusik 2003). The activity concentrations of 210Po and 210Pb in mushrooms
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were higher comparing to other groundcover plants (Kostiainen 2007). Mushroom species have different retain capacities of 210Po and 210Pb (Skwarzec and Jakusik 2003; Malinowska et al. 2006; Guillen et al. 2009). Previous studies on King Bolete (Boleus edulis Bull) showed that the values of 210 Po concentration in caps were higher in comparison to its levels in stems (from 1.02 to 2.05; mean value 1.44) (Skwarzec and Jakusik 2003). The highest activity concentration of 210Pb in samples of Finnish mushrooms was detected in red-banded Cortinarius (Cortinarius armillatus (Fr) Fr), (16.2 Bq kg−1 dry biomass; db) while the lowest in Foxy Bolete (Leccinum vulpinum Watling) (1.38 Bq kg−1 db) (Vaaramaa et al. 2009). Mushrooms also influence natural radionuclides migration in soil and food chains (Ibrahim and Whicker 1987; Calmon et al. 2009). Many species of wild edible mushrooms adsorb and bioaccumulate mercury (Hg), chromium (Cr), silver (Ag), cadmium (Cd), as well as radionuclides, i.e., cesium (Cs), strontium (Sr), polonium (Po), radiolead (Pb), uranium (U), and plutonium (Pu) (Gentili et al. 1991; Falandysz et al. 1994; Falandysz et al. 2002; Falandysz et al. 2003; Falandysz et al. 2012; Zhang et al. 2013; Guillen and Baeza 2014). The studies about determination of 210Po and 210Pb were carried out in red-capped scaber (Leccinum aurantiacum (Bulliard) Gray); known also as Boletus aurantiacus Bull., Boletus aurantiacus var. rufus (Schaeff.) Mérat 1821; Boletus scaber var. aurantiacus (Bull.) Opat. 1836. Its cap can be orange, brown, or red with 3–25 cm diameter. In favorable conditions, they can grow very fast—in 1 day can grow to 5–8 cm diameter, 6 days—23 cm (Perz 2004). Its flesh is white, bruising at first burgundy, then grayish or purple-black; has nice smell and good taste. The underside of the cap has very small whitish pores that bruise olivebrown. The stipe is rough, 10–25 cm tall, and 2–5 cm thick; can bruise blue-green. Red-capped scaber can be collected during summer and autumn (from June to October) in enlightened mixed forests, scrublands, or parks throughout whole Europe and North America. The association between fungus and the host tree is mycorrhizal (Škubla 2007; Gminder 2008). In Europe, red-capped scaber has been traditionally known to be associated with poplar trees; these mushrooms have been recorded with various deciduous trees including beech, birch, chestnut, willow, and lime. There were no L. aurantiacum in Europe associating with conifers (Škubla 2007). Red-capped scaber is not an endangered species in Poland, and this is one of a favorite among edible mushrooms, prepared similarly to other edible boletes (Škubla 2007; Gminder 2008). The aims of this study were to determine 210Po and 210Pb content in fruiting bodies (caps and stems, and further whole mushrooms) of edible red-capped scaber (L. aurantiacum) and topsoil; recognize radionuclides distribution; calculate the levels of 210Po and 210Pb bioconcentration as well as their translocation; estimate possible annual effective radiation
doses to mushrooms’ consumers from digested 210Po and 210 Pb decay; and evaluate the level of their radiotoxicity.
Material and methods Fruiting bodies of wild edible mushrooms red-capped scaber (L. aurantiacum) and topsoil samples (0–10 cm layer) underneath the fruiting bodies were collected from distantly distributed forested places across Pomerania (northern Poland) near villages: Trzechowo (53° 52′ 12″ N 18° 13′ 48″ E) (2006), Orzechowo (54° 35′ 54″ N 16° 55′ 20″ E) (2008) and Parchowo (54° 12′ N 17° 40′ E) (2010) (Fig. 1). Among all sampling sites (Fig. 1), Orzechowo lies the closest to the Baltic Sea and the soil is poor in organic matter. Opposite, Parchowo has very good soil conditions, and this part of Pomerania is rich in fertile dystrophic brown earth. Trzechowo lies on podsols, pseudopodsolic, and rusty soils—poor for agriculture due to the sandy portion, resulting in a low level of moisture and nutrients (Kubiak 2008). Soil types in Pomerania (Fig. 2) strictly depended on its geological past and were highly differentiated. All mushroom samples, after the removal of plant and soil using plastic knife, were separated into caps and stipes, sliced and oven dried at 65 °C to constant weight, and further ground in porcelain mortar to fine powder. The soil samples, free of any visible organisms, small stones, sticks, and leaves, were dried at 65 °C to constant mass. Next, the soil samples were ground in a porcelain mortar and sieved through a pore size of 2-mm plastic sieve. About 2 g of soil and 5 g of mushrooms were digested using 65 % nitric acid (HNO3) and 36 % hydrochloric acid (HCl) with a 209Po (9 mBq) spike added as a yield tracer. The cold mineralization took 7 days. Furthermore, the samples were mineralized in hot aqua regia about 5 days to receive clear color of the solution, and then evaporated. The dry residue was dissolved in 25 mL of 0.5 M HCl and 0.5 g of ascorbic acid (C6H8O6) was added to reduce iron Fe3+ to Fe2+, then the solution was transferred to PTFE vessels equipped with silver sheet bottom disc. Polonium was autodeposited at 90 °C for 4 h. 210Po activity was measured using an alpha spectrometer equipped with semiconductor silicon detectors and a 450 mm 2 active surface barrier (Alpha Analyst S470, Canberra-Packard, USA). Polonium samples were measured for 1–3 days (Skwarzec 1995, 1997, 2010). Activity concentration of 210Pb in analyzed samples was calculated indirectly via its daughter 210Po activity measurement. All samples after the first 210Po deposition were stored for 6 months to allow for 210Po increment from 210Pb. The deposition of 210Po on silver disc was repeated, and the activities of ingrowing 210Po were measured in alpha spectrometer (Alpha Analyst S470, Canberra-Packard). The measurement
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Fig. 1 Localization of the sampling sites
of a single sample took 1–4 days, and 210Po activity in analyzed samples was corrected for decay to the day of polonium deposition (time of separation 210Po from 210Pb). 210Pb activity at the time of sample collection was calculated using the simplified form of the Bateman equation (Skwarzec 1997, 2010). The 210Po and 210Pb yield in the analyzed mushroom and soil samples ranged from 95 to 100 %. The results of 210Po and 210Pb concentrations were given with standard deviation (SD) calculated for 95 % confidence intervals. The accuracy and precision of the radiochemical method were positively evaluated using IAEA reference materials (IAEA-414; IAEA-384), and both estimated at less than 5 %. Statistic tests showed there was positively skewed non-normal distribution Fig. 2 A rough overview of soil conditions in the eastern region of the Pomerania land (DRRiP 2000)
of the results which showed statistically significant differences (Mazerski 2009). Information about radionuclides bioaccumulation and transfer could give the values of bioconcentration and translocation factors. The simplified evaluation of soilto-mushroom (via mycelium) radionuclides accumulation level gave the bioconcentration factor (BCF) (Eq. 1). The mushroom translocation factor (TF) described the transfer between mushroom parts (eq. 2) and could show the influence of atmospheric fallout on radionuclides presence or their selective transfer. Equations for BCFs and TFs were modified to our study’s needs, and the BCF and the TF were calculated on the basis of formulas (Olszewski et al. 2015):
1.2 ± 0.4 0.87 ± 0.25 0.76 ± 0.26 1.7 ± 0.4 4.9 ± 0.9 4.7 ± 1.1 3.8 ± 1.0 3.9 ± 1.1 3.8 ± 1.1 2.1 ± 0.5 2.2 ± 0.7 2.8 ± 0.5 0.93 ± 0.05 0.50 ± 0.04 0.40 ± 0.03 1.1 ± 0.1 1.1 ± 0.1 2.6 ± 0.1 1.1 ± 0.1 1.1 ± 0.1 1.6 ± 0.1 1.3 ± 0.1 1.7 ± 0.0 2.4 ± 0.2 1.6 ± 0.1 0.81 ± 0.07 0.91 ± 0.07 2.1 ± 0.1 4.1 ± 0.2 5.2 ± 0.2 2.7 ± 0.2 2.5 ± 0.1 3.6 ± 0.2 2.3 ± 0.1 3.8 ± 0.2 5.1 ± 0.4
a
Trzechowo
Parchowo
Number of individuals in composite sample
0.56 ± 0.04 0.39 ± 0.02 0.35 ± 0.03 0.60 ± 0.05 1.12 ± 0.08 0.94 ± 0.07 0.78 ± 0.07 1.79 ± 0.12 1.31 ± 0.10 0.78 ± 0.05 0.66 ± 0.05 1.19 ± 0.07 1 (4) 1 (8) 1 (4) 1 (3) 1 (3) 1 (3) 1 (3) 1 (3) 1 (3) 1 (4) 1 (2) 1 (2) O1 O2 O3 O4 P1 P2 P3 P4 P5 T1 T2 T3 Orzechowo
0.92 ± 0.08 0.92 ± 0.03 0.65 ± 0.03 1.3 ± 0.1 5.8 ± 0.1 4.1 ± 0.1 5.0 ± 0.2 5.4 ± 0.2 4.1 ± 0.2 1.9 ± 0.1 0.87 ± 0.09 2.0 ± 0.1
Pb
210
Po
210
Pb
210
Po
210
Pb
Po
210 210
0.72 ± 0.24 0.44 ± 0.15 0.37 ± 0.18 0.84 ± 0.29 1.1 ± 0.5 1.8 ± 0.6 0.93 ± 0.40 1.4 ± 0.6 1.4 ± 0.6 1.0 ± 0.3 1.2 ± 0.2 1.5 ± 0.3
1.72 ± 0.84 2.00 ± 0.89 2.04 ± 1.22 2.05 ± 0.89 4.37 ± 2.22 2.61 ± 1.11 4.05 ± 2.05 2.69 ± 1.44 2.65 ± 1.39 2.03 ± 0.74 1.91 ± 0.72 1.86 ± 0.46
25 ± 1 486 ± 1 32 ± 1 35 ± 1 36 ± 1 100 ± 1 100 ± 1 41 ± 1 20 ± 1 7.3 ± 1.5 8.1 ± 1.3 5.7 ± 1.4
Pb
210
Po
210
16 ± 1 30 ± 1 23 ± 1 22 ± 1 22 ± 1 65 ± 1 64 ± 1 28 ± 1 14 ± 1 5.8 ± 1.5 6.3 ± 1.3 4.6 ± .1.4
1.55 ± 0.13 1.59 ± 0.08 1.42 ± 0.10 1.54 ± 0.11 1.61 ± 0.12 1.52 ± 0.04 1.56 ± 0.04 1.45 ± 0.09 1.42 ± 0.19 1.26 ± 0.41 1.28 ± 0.34 1.25 ± 0.50
Po/210Pb activity ratio in topsoil 210
Whole mushrooms
The results of average 210Po and 210Pb activity concentrations in analyzed red-capped scaber (L. aurantiacum) samples from Pomerania (northern Poland) were presented in Table 1. The highest 210Po activity concentrations were in fruiting bodies of L. aurantiacum collected in Parchowo (from 3.8 ± 1.0 to 4.9 ± 0.9 Bq kg−1 db), while the lowest were measured in mushrooms collected in Orzechowo (from 0.76 ± 0.26 to 1.24 ± 0.45 Bq kg−1 db). In the case of 210Pb results, the observations were similar; the highest 210Pb activity concentrations were determined in red-capped scaber collected in Parchowo (from 0.93 ± 0.40 to 1.8 ± 0.6 Bq kg−1 db), while the lowest were measured in mushrooms collected in Orzechowo (from 0.37 ± 0.18 to 0.72 ± 0.24 Bq kg−1 db). All mushrooms contained more 210Po than 210Pb, confirmed by the values of 210Po/210Pb activity ratio higher than 1 (Table 1), and those results were similar to previously obtained by Skwarzec and Jakusik (2003). Observed differences could be a result of disparities in topsoil, dry atmospheric fallout (mineral particles from dusty soils covering the surface of plants and ground, gravitationally deposited), and bioaccumulation levels. Almost all mushrooms have been collected in forests, which were seminatural ecosystems and differed from agricultural cultivated lands; its soils were multilayer, hemi-organic, and mineral. Mushrooms and microbes biological activities effect on long-term radionuclides retention in organic layers of forest soil, and the soil represents the major reservoir of radionuclides—thus they can be easily available for mushrooms and mycelium located in organic layers. Among the soil samples, the highest activity concentrations of 210Po and 210Pb were noticed in Parchowo (respectively at 100 ± 1 Bq kg−1 dry matter and 65 ± 1 Bq kg−1 dm), while the lowest in Trzechowo (8.1 ± 1.3 Bq kg−1 dry matter and 6.3 ± 1.3 Bq kg−1 dm respectively) (Table 1). The highest values of 210Po and 210Pb activities found in Parchowo could depend on soil fertility— high moisture and radionuclides bonding by organic matter (Fig. 2). 210Po and 210Pb activity concentrations in analyzed topsoil were highly differentiated, in some cases an order of
Stipes
Po and 210Pb activity concentrations in red-capped scaber
Caps
210
Activity concentration in topsoil (Bq kg−1 dry matter)
Results and discussion
Po/210Pb activity ratio in whole mushrooms
ð2Þ
210
cap T F stem
Activity concentration (Bq kg−1 dry biomass)
ð1Þ Radionuclide activity concentrationcap Bq⋅kg‐1 ¼ Radionuclide activity concentrationstem Bq⋅kg‐1
na
Radionuclide activity concentrationwhole mushroom Bq⋅kg‐1 Radionuclide activity concentrationsoil Bq⋅kg‐1
Sampling site
BC F whole soil mushroom ¼
Table 1 Average values of 210Po and 210Pb activity concentrations in red-capped scaber (L. aurantiacum) mushrooms and average values of 210Po and 210Pb activity concentration in topsoil as well as the values of 210Po/210Pb activity ratio
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magnitude higher than those in mushrooms (Table 1). But the activities of 210Po and 210Pb in mushrooms were not correlated with their activities in topsoil (r = 0.48 for 210Po and r = 0.13 for 210Pb). The obtained results of 210Po and 210Pb activity concentrations in mushrooms (also caps and stems) as well as topsoil allowed for calculating the bioconcentration factors (BCF) and translocation factors (TF) (Table 2). The simplified equation of soil-to-mushroom (omitting mycelium) BCF (eq. 1) gave slight information about the radionuclides accumulation level. In the case of plants or mushrooms, the value of BCF describes its capability to chemical elements accumulation according to its original concentration in topsoil. Among all analyzed mushroom samples, 210Po and 210Pb concentrations were lower than their activities in soil, and BCF values ranged 0.02–0.50 for 210Po and 0.01–0.34 for 210Pb (Table 2), but lead (Pb) weak bioconcentration capabilities were previously observed (Kalač and Svoboda 2000; Ociepa et al. 2014). The highest values of BCF were observed in Trzechowo area (0.27–0.50 for 210Po and 0.18–0.34 for 210Pb)—the sampling site rich in podsols characterized by high permeability of ions transfer, high acidity, and low humus content. Transfer of radionuclides from soil to mushrooms depends on soil properties. The amount of organic matter in soil as well as its pH strongly influence on metals content in mushrooms (Calmon et al. 2009; Melgar et al. 2009; Mleczek et al. 2013). However, these conditions have small impact on Pb bioconcentration (Babich and Stotzky 2005; Kalač and Svoboda 2000). The results showed that the transfer and bioconcentration of reactive 210Po was a little more effective than 210Pb, but both processes (transfer and bioconcentration from soil via mycelium) were at small scale, and Po was not selectively Table 2 Values of bioconcentration factor (BCF) and translocation factor (TF) for analyzed mushroom fruits of red-capped scaber (L. aurantiacum) mushrooms and topsoil Sampling site Bioconcentration factor (BCF) Translocation factor (TF) 210
210
210
210
0.05 0.02 0.02 0.05 0.14 0.05 0.04 0.09 0.19 0.29 0.27 0.50
0.04 0.01 0.02 0.04 0.05 0.03 0.01 0.05 0.10 0.18 0.18 0.34
0.56 1.14 0.71 0.63 1.42 0.80 1.88 2.20 1.12 0.85 0.23 0.40
0.60 0.78 0.87 0.56 0.99 0.36 0.72 1.59 0.83 0.60 0.38 0.49
Po
Orzechowo
Parchowo
Trzechowo
Pb
Po
Pb
bioaccumulated, similarly to Pb (Ociepa et al. 2014). Very low bioconcentration factors of 210Po and 210Pb in analyzed red-capped scaber indicated that this species is not a hyperaccumulator. The calculated values of mushroom translocation factor (TF) (Eq. 2) could show the influence of atmospheric fallout on radionuclides presence. Atmospheric fallout of these radon decay products results in the contamination of organisms and the top layer of soil. But in favorable conditions, red-capped scaber can grow very fast—in 1 day, it can grow to 5–8 cm diameter (Perz 2004). The highest values of TFs were calculated for fertile soils of Parchowo area ranging 2.20 for 210Po and 1.59 for 210Pb (Table 2), but in majority of the samples the TFs were lower than 1; analyzed mushroom cap contained less 210Po and 210Pb than its stem. It means 210 Po and 210Pb could come from internal processes during mushroom growth. Furthermore, the obtained results for 210 Po/210Pb activity ratios in the caps (generally lower than 1) indicate that this route of 210Po and 210Pb radionuclides incorporation plays minor role. However, in the nearest future, it could be interesting to evaluate such contribution of the gravitational deposition level. Principal component analysis (PCA) was conducted to examine the differences in activity concentrations of 210Po and 210 Pb in whole mushrooms as well as caps and stipes of L. aurantiacum mushrooms and topsoil, also to investigate the intercorrelations between elements and sampling sites. PCA data revealed that 77.1 % of information regarding the radionuclides compositional variability for three sites could be described by two varifactors (Fig. 3). PCA analysis confirmed that the excess of 210Po in the surface soil is probably due to atmospheric deposition and the topsoil properties, but high correlation between 210Po and 210Pb concentrations in soil could indicate that the overcapacity of 210Po content in soil was simply the subtraction of the activity of 210Pb (Fig. 3). It did not look similar in the case of whole mushrooms—excess of 210Po in mushrooms samples could be an effect of two processes: selective or increased transfer, and further bioaccumulation, of more reactive 210Po or its surface adsorption. But the samples were collected at different years, and we could not compare sampling sites because of differentiated atmospheric fallout. However, we observed that 210Po BCFs were highly correlated to 210Pb BCFs (Pearson’s correlation value calculated at 0.995), and the correlation between 210Po TFs and 210 Pb TFs was lower (0.791) (Fig. 3). The values of BCFs and TFs showed the slight inverse proportion—the higher the bioconcentration factor values are, the lower the translocation factor values were observed (Pearson’s correlation coefficients for 210Po and 210Pb were −0.397 and −0.318, respectively) (Fig. 3). The other studies showed, in the case of metal bioconcentration, that its level depended on metal chemical properties and less on its concentration in soil and soil fertility. As opposed to bioconcentration, the translocation process depended on soil fertility, amount of organic matter, and soil
Environ Sci Pollut Res Fig. 3 PCA biplot (no rotation) based on the activity concentrations as well as BCF and TF values and score plots of the sampling sites in space of first and second varifactors
pH that changed the metal mobility and bioavailability (Ociepa et al. 2014). These processes could be observed also in the case of analyzed radionuclides—210Po and 210Pb—in red-capped scaber.
Table 3 Assessed average values of the annual effective radiation dose from 210Po and 210Pb decay while ingested with red-capped scaber (L. aurantiacum) mushrooms for adult members of the public
Sampling site
Effective radiation doses In order to identify the potential radiotoxicity, on the basis of previously calculated 210Po and 210Pb content in dried and
Annual effective radiation dose (μSv year−1) Caps
Parchowo
Trzechowo
Whole mushrooms
210
210
210
210
210
210
0.55 ± 0.05 0.55 ± 0.02 0.39 ± 0.02 0.79 ± 0.03 3.5 ± 0.1 2.5 ± 0.1 3.0 ± 0.1 3.2 ± 0.1 2.4 ± 0.1 1.2 ± 0.1 0.5 ± 0.0 1.2 ± 0.1
0.19 ± 0.02 0.13 ± 0.01 0.12 ± 0.01 0.21 ± 0.02 0.39 ± 0.03 0.32 ± 0.03 0.27 ± 0.02 0.62 ± 0.04 0.45 ± 0.03 0.27 ± 0.02 0.23 ± 0.02 0.41 ± 0.03
0.98 ± 0.06 0.49 ± 0.04 0.55 ± 0.04 1.3 ± 0.1 2.4 ± 0.1 3.1 ± 0.1 1.6 ± 0.1 1.5 ± 0.1 2.2 ± 0.1 1.4 ± 0.1 2.3 ± 0.2 3.0 ± 0.2
0.32 ± 0.02 0.17 ± 0.01 0.14 ± 0.01 0.37 ± 0.02 0.39 ± 0.03 0.90 ± 0.04 0.37 ± 0.02 0.39 ± 0.03 0.55 ± 0.04 0.45 ± 0.03 0.60 ± 0.02 0.84 ± 0.07
0.74 ± 0.27 0.52 ± 0.15 0.45 ± 0.16 1.0 ± 0.3 2.9 ± 0.6 2.8 ± 0.7 2.3 ± 0.6 2.3 ± 0.7 2.3 ± 0.6 1.2 ± 0.3 1.3 ± 0.4 1.7 ± 0.3
0.25 ± 0.08 0.15 ± 0.05 0.13 ± 0.06 0.29 ± 0.10 0.39 ± 0.18 0.62 ± 0.22 0.32 ± 0.14 0.50 ± 0.22 0.50 ± 0.22 0.35 ± 0.10 0.40 ± 0.07 0.53 ± 0.10
Po
Orzechowo
Stipes Pb
Po
Pb
Po
Pb
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unprocessed culinary fruiting bodies of L. aurantiacum, the annual effective radiation doses were calculated (Table 3). The effective dose conversion coefficient from 210Po and 210Pb ingestion for adult members of the public recommended by ICRP is 1.2 and 0.69 μSv Bq−1, respectively (ICRP 2012). The average mushrooms consumption in Poland was calculated at 0.5 kg dry biomass, but in some cases consumption exceeds 1–1.5 kg dry biomass. The results showed that the consumption of 0.5 kg of whole dried mushrooms, in the case of 210Po decay, could lead the annual effective dose from 0.45 ± 0.16 to 2.9 ± 0.6 μSv, while in the case of 210Pb decay from 0.13 ± 0.06 to 0.62 ± 0.22 μSv per year (Table 3). The total annual effective dose from natural radiation in Poland was estimated at 2.1–2.6 mSv (including 222Rn) while the annual effective dose from 210Po and 210Pb intake with different foodstuffs and water was estimated at 54 μSv per year for both (Jagielak et al. 1997; Pietrzak-Flis et al. 1997; Dobrzyński et al. 2005). It means if consumers would eat the analyzed mushrooms, they should not increase significantly the total effective radiation dose from 210Po and 210Pb from typical dietary intake. For comparison, eating B. edulis collected in Białogard could result in an annual effective dose from 210Po decay at 37 μSv (Skwarzec and Jakusik 2003).
Conclusions The studies showed that edible wild mushrooms, namely redcapped scaber (L. aurantiacum), accumulate 210Po and 210Pb at different level, and this process depends on soil type and atmospheric fallout. The highest 210Po and 210Pb activity concentrations were found in mushrooms collected in Parchowo which fertile soil contained the highest activity concentrations of 210Po and 210Pb also. But we found that 210Po and 210Pb activity concentrations in mushrooms did not reflect their concentrations in topsoil, thus Po and Pb were not selectively bioaccumulated by. It means that, also supported by very low values of 210Po and 210Pb BCFs and TFs calculated, analyzed red-capped scaber is not a hyperaccumulator. Consumption of analyzed mushrooms (0.5 kg of dry mushrooms per year) in the case of 210Po could lead the annual effective dose at 0.45–2.9 μSv, while in the case of 210 Pb at 0.13–0.62 μSv per year. This indicated that analyzed red-capped scaber was safe from a radiological point of view.
Acknowledgments The authors would like to thank the Ministry of Sciences and Higher Education for the financial support under grant DS/530-8635-D646-16. Many thanks to Dorota Chojnacka, Anna Jedrzejczyk, and Dorota Stenka for their technical help. This study was partly supported (samples collection) by the National Science Centre of Poland under grant code PRELUDIUM 2011/03/N/NZ9/04136 for Grażyna Krasińska.
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