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© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
455
INVESTIGATION ON METALLIC ELEMENTS IN FUNGUS
AMANITA MUSCARIA (FLY AGARIC) AND THE FOREST
SOILS FROM THE MAZURIAN LAKES DISTRICT OF POLAND
Małgorzata Drewnowska*, Krzysztof Lipka,
Grażyna Jarzyńska, Dorota Danisiewicz-Czupryńska and Jerzy Falandysz
Research Group of Environmental Chemistry, Ecotoxicology & Food Toxicology, Institute of
Environmental Sciences & Public Health, University of Gdańsk, 19 Sobieskiego Str., 80-952 Gdańsk, Poland
ABSTRACT
In the current study, we determined concentrations
and bioconcentration potential of Ag, Al, Ba, Ca, Cd, Co,
Cu, Cr, Fe, Hg, K, Mg, Mn, Na, Ni, Rb, Sr and Zn by Fly
Agaric fungus (Amanita muscaria). Caps and stipes of Fly
Agaric and the upper 0-10 cm layer of the soils collected
from the outskirts of Kętrzyn town in the Mazurian Lake
District of Poland have been examined. The elements
were determined using validated methods - inductively
coupled plasma atomic emission spectroscopy (ICP-AES)
and cold vapor atomic absorption spectrometry (CV-AAS).
K, Mg, Ca and Zn were the most abundant among the ele-
ments determined in the fungus. Cd, K, Rb, Hg, Cu and Zn
were effectively absorbed by the fungus underlining its
biogeochemical role in their turnover in the forest ecosys-
tems. Contrary, Ag, Al, Ba, Ca, Co, Cr, Fe, Mn, Mg, Na
and Sr showed BCF <1, what implies on their exclusion
by the fungus. In spite of low potential for bioconcentra-
tion of Ca, Fe, Mn and Mg, Fly Agaric can be also con-
sidered to be a species involved in their biogeochemical
turnover in the forests ecosystems.
KEYWORDS:
forest, Fly Agaric, fungi, metals, soil
1 INTRODUCTION
Macrofungi play a vital role in metallic elements and
metalloids turnover in the forest ecosystems [1-15]. Mush-
rooms are an important piece in the forest food chains,
because they are eaten by numerous animals and are rich in
mineral substances [7, 16-20]. An ability of fungi to dis-
solve, up-take and accumulate in their flesh metals that are
contained in mineral and humified fraction of soils, is of
primarily role in introducing them into the biosphere [2,
15]. The uptake process and sequestration of heavy metals
* Corresponding author
in fruiting bodies depend on environmental factors, and on
the particular genetic characteristics of each species [19,
21-31].
Edible wild mushrooms are considered to be delicacy
and they are source of many essential elements [32-39].
However, fungi can contain both the essential mineral
nutrients and hazardous metals at elevated concentrations
[40-43]. Mercury, cadmium and lead are considered as the
most hazardous ones [44, 45]. Compared to edible mush-
rooms, a much less attention is devoted to inedible spe-
cies. One of the most recognizable inedible mushrooms is
Amanita muscaria (Fly Agaric). This species occurs com-
monly in the forests of Europe and is easily recognizable as
having a beautiful red cap with white patches. Because of
the hallucinogenic properties of A. muscaria was used
during religious rites and rituals by shamans/sorcerers, e.g.
Tribal peoples of Siberia [46-48]. A. muscaria belongs to
the ectomycorrizal fungi, which have specific morphologi-
cal and physiological properties. The mineral compound
composition of the Basidiomycetes was a subject of wide
interest in the recent decade of years. Potassium and
phosphorous are major mineral compounds in flesh of
mushrooms but many others can be accumulated to ele-
vated concentrations also e.g. cadmium, mercury, lead
vanadium and selenium [15, 40, 49-51].
The aim of this study was to characterize a profile of
17 metals and their bioconcentration potential by Fly Aga-
ric collected from Mazury Lake District in the Kętrzyn
region in north-eastern part of Poland.
2 MATERIALS AND METHODS
Fifteen mature specimens of Fly Agaric (Amanita mus-
caria) and, beneath to them, surface layer of soils (0-10 cm;
100 g) were collected from forested areas localised at east
(Kwiedzina site) and south-east (Zalesie Kętrzyński site) to
town of Kętrzyn in Masuria land of Poland, in 1999. The
sampling site was situated far away from any pollution
sources, like plants or high-density traffic roads. The sam-
© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
456
ples were divided into caps and stalks, carefully hand-
cleaned using a plastic knife to remove the attached soil
particles and other debris (e.g. leaves), dried to constant
weight, crushed and pulverized in an agate mortar, and kept
in dry condition in sealed polyethylene bags until chemical
analysis. Next, the pulverized sub-samples (~0.5 g) of caps
and stipes were weighted into polytetrafluoroethylene
(PTFE) vessels, pre-digested for 24 h with 7 ml concen-
trated nitric acid (65%, Suprapure, Merck) at room tem-
perature, and further digested under pressure in an auto-
matic microwave digestion system type MARS 5 of CEM
corp., Matthews, NC, USA. The digest was diluted to 25
ml using deionized water and stored until instrumental
analysis.
The soil substrate samples were air-dried at room
temperature in clean conditions for a few weeks, and then
sieved (pore size 2 mm) and further dried in an electronic
oven at 40 ºC for 48 h. Metals from the soil samples (1.5 g)
were leached using 10 ml of 20% nitric acid solution (Su-
prapure, Merck) in open PTFE vessels, that were gently
heated up to 105 ºC for 2 h. After cooling, the leachates
obtained were filtered through Whatman No. 42 filter paper
- directly into a volumetric flask, and volume was brought
to 25 ml with deionised water [52, 53].
Contents of 16 metals in fungus and soil were deter-
mined by inductively coupled plasma - optical emission
spectroscopy (ICP-OES; Optima 2000 DV, Perkin Elmer,
USA) and yttrium was used as an internal standard. Mer-
cury was determined by cold-vapour atomic absorption
spectroscopy (CV-ASA) using fully automated mercury
monitor (Mercury monitor 3200, Thermo Separation Pro-
ducts, USA). Each spectroscopic measurement for each
individual sample was repeated in triplicate. Detection limits
were as follows: K, Mg, Na 5 µg/g; Rb 1 µg/g; Al, Ag, Ca,
Cd, Co, Cr, Fe, Zn 0.1 µg/g; Ba, Cu, Mn, Sr 0.05 µg/g, and
Hg 0.005 µg/g dry weight. Both methods were well validated
on several occasions by participation in intercalibration
trials and by periodic analysis of certified reference mate-
rials and detailed results were given to the public [52-55].
Duplicates and blanks followed with every examined set
of 10 mushroom or soil samples.
3 RESULTS AND DISCUSSION
3.1 Fruiting bodies
Data obtained on metallic elements of Fly Agaric and
the soils are given in Table 1. Concentrations were char-
acterised by arithmetical mean values, the corresponding
standard deviations (SD), median values and ranges, and
expressed in µg/g on a dry weight basis (dw). Potassium,
followed by Mg, Al, Rb, Fe, Ca and Zn, occurred in the
greatest concentrations in Fly Agaric. In caps, K concentra-
tions ranged from 32000 to 45000, and in stipes from
26000 to 53000 µg/g dw. These are the values like shown
by Vetter [51] for some Amanitaceae mushrooms. For Bay
Bolete (Xerocomus badius) in a study by Malinowska et
al. [42] and for Poison Pax (Paxillus involutus) in studies
by Brzostowski et al. [52, 53], concentrations of K were
roughly similar or smaller than determined in Fly Agaric,
respectively (Table 1).
Magnesium concentration in caps varied from 600 to
870 and in stipes from 330 to 820 µg/g dw. Metals,
such as Rb, Al and Ca, were noted in caps of Fly Agaric
in comparable concentrations (Table 1), and Ca in stipes
(210±420 µg/g dw) was twice more abundant compared
to caps (113±58 µg/g dw). In the reports by Müller et al.
[56] and Rudawska and Leski [57], Al concentrations in
mushrooms were in the range of the median values de-
termined in caps and stipes of Fly Agaric in this study, i.e.
170 and 130 µg/g dw, respectively. Also for Fe, the me-
dian concentration values of 120 µg/g dw in caps and 100
µg/g dw in stipes of Fly Agaric agree with observations
for this species by Vetter [51] and Rudawska and Leski
[57], on the average.
Zinc was next in its abundance amongst the metals
determined in Fly Agaric (its caps 97±46 and stipes
61±24 µg Zn/g dw; Table 1). This species, in studies from
Czech Republic, Hungary and Poland, contained Zn in
caps at 130, 120 and 200 µg/g dw (data rounded), respec-
tively [32, 51, 57]. The median concentration values of
essential trace elements, such as Na, Cu and Na, in caps
were 34, 30 and 18 µg/g dw but in stipes 21, 15 and 17
µg/g dw, respectively (Table 1). Vetter [51] stated that
essential Cu concentration in several species of Amanita-
ceae mushrooms is in a relatively narrow range from 23
to 73 µg/g dw, and variability was low.
Ag, Ba, Co, Cr and Sr evidenced concentrations close
to 1 µg/g dw in Fly Agaric but many other mushrooms
were richer in Ag [6, 7]. Borovička et al. [3], in a recent
study, found the Warted Amanita (Amanita strobiliformis)
and the European Solitary Lepidella (A. solitaria) to be
species hyperaccumulating Ag.
Cd and Hg are highly toxic metals that can be effi-
ciently accumulated by many fungi in their fruiting bodies
[27-29, 39, 43]. Fly Agaric contained Cd in caps in 2-fold
greater concentration compared to stipes, and the medians
were 11 and 5.3 µg/g dw, respectively. In a study on King
Bolete (Boletus edulis), Cd was the only metal for which,
at the unpolluted forested areas of Poland, a positive ten-
dency was noted between concentrations determined in
flesh and in the soil substrates [58]. Fly Agaric, in this
study, contained Hg in ca. 2-fold concentrations in caps
(median: 0.68 µg/g dw) and stipes (0.46 µg/g dw), when
compared to the specimens from Umeå in Sweden, having
0.39±0.54 (caps) and 0.22±0.30 µg/g dw (stipes) [8]. In a
study of Fly Agaric from the Mierzeja Wiślana sand-bar,
the median values of Hg in caps and stipes were 0.15 and
0.096 µg/g dw, respectively [55], and for several other
regions of Poland, the median values were between 0.19
and 1.4 µg/g dw in caps and between 0.18 and 0.67 µg/g
dw in stipes [50].
Caps of Fly Agaric, on the average, contained Al, Cd,
Co, Cr, Cu, Fe, Hg, Mg and Rb in more or less greater
© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
457
TABLE 1 - Metallic elements content (µg/g dry weight; mean±SD, range and median values) of A. muscaria samples (n=15) and their cap to
stipe concentration quotient (QC/S) and bioconcentration (BCF) values
Metal Cap Stipe QC/S Soil BCFC BCFS
Ag 0.84±0.12
0.79
0.71-1.0
1.2±0.4
1.0
0.66-1.9
0.79±0.32
0.71
0.40-1.4
2.4±0.9
2.4
1.3-3.5
0.75±0.63
0.79
0.30-1.2
0.74±0.79
0.62
0.18-1.3
Al 200±97
170
88-460
160±72
130
79-330
1.3±0.4
1.2
0.67-2.4
17000±2000
16000
13000-21000
0.019±0.003
0.018
0.017-0.02
0.008±0.002
0.008
0.007-0.009
Ba 1.3±0.6
1.2
0.64-2.5
1.2±0.4
1.1
0.82-2.2
1.0±0.4
1.0
0.48-1.7
170±44
160
120-250
0.005±0.003
0.005
0.003-0.008
0.006±0.001
0.006
0.005-0.006
Ca 110±58
120
41-240
210±420
100
42-1800
1.1±0.5
0.92
0.07-2.0
510±140
550
240-630
0.17±0.09
0.15
0.11-0.24
0.15±0.04
0.15
0.12-0.18
Cd 11±3
11
4-14
5.5±1.8
5.3
1.5-7.7
2.0±0.4
1.9
1.4-2.5
0.045±0.020
0.040
0.027-0.076
260±140
290
16-350
160±99
180
89-230
Co 0.81±0.43
0.62
0.45-1.7
0.64±0.30
0.55
0.36-1.3
1.2±0.1
1.2
1.0-1.4
1.0±0.3
1.1
0.60-1.5
0.22±0.10
0.20
0.15-0.29
0.13±0.02
0.13
0.12-0.15
Cr 0.78±0.20
0.77
0.56-1.2
0.55±0.13
0.51
0.40-0.83
1.4±0.2
1.4
1.1-1.7
7.1±1.5
6.7
5.4-9.0
0.031±0.035
0.046
0.007-0.056
0.017±0.009
0.014
0.011-0.023
Cu 30±9
30
20-55
17±7
15
6.0-35
2.0±1.0
1.8
0.58-5.4
1.5±0.5
1.4
0.94-2.1
18±10
14
11-25
11±8
12
6-17
Fe 150±80
120
66-380
130±67
100
65-290
1.3±0.4
1.31
0,52-2,15
3400±790
3200
2620-4520
0.049±0.043
0.028
0.019-0.079
0.030±0.010
0.030
0.023-0.037
Hg 0.79±0.33
0.68
0.33-1.4
0.51±0.28
0.46
0.16-1.3
1.8±1.0
1.6
0.32-4.3
0.027±0.008
0.028
0.021-0.037
38±23
29
15-47
32±18
21
16-42
K 38000±3100
37000
32000-45000
36000±7300
36000
26000-53000
1.1±0.1
1.0
0.75-1.3
710±200
690
460-1020
45±19
49
32-58
44±26
41
25-62
Mn 17±7
18
8-29
20±17
17
8-81
1.1±0.3
1.1
0.14-1.7
130±55
140
56-190
0.062±0.045
0.060
0.030-0.094
0.078±0.061
0.053
0.035-0.12
Mg 710±74
710
600-870
510±110
500
330-820
1.4±0.2
1.4
0.90-1.9
1260±360
1200
870-1820
0.60±0.37
0.49
0.34-0.86
0.46±0.35
0.27
0.21-0.71
Na 36±25
34
12-119
20±9
21
12-36
0.71±0.38
0.64
0.28-1.9
24±6
23
16-34
0.76±0.51
0.73
0.40-1.1
0.82±0.32
0.81
0.60-1.0
Rb 180±180
110
38-620
110±110
65
28-350
1.6±0.2
1.7
1.3-2.0
5.8±1.9
5.5
3.5-8.7
20±20
25
6.0-35
14±15
17
3.0-24
Sr 0.41±0.17
0.40
0.23-0.73
0.40±0.23
0.34
0.22-1.2
1.1±0.4
1.1
0.38-2.0
27±5
26
22-35
0.011±0.005
0.011
0.007-0.014
0.010±0.001
0.010
0.009-0.011
Zn 97±46
65
37-210
61±24
77
26-110
0.97±0.56
0.93
0.16-2.1
12±1
12
9-13
8.6±4.0
7.5
5.7-11
5.8±3.1
5.1
3.6-8.0
concentrations compared to stipes whereas stipes were
enriched in Ag and Na compared to caps for Ag, Ba, Ca,
K, Mn, Sr and Zn, distribution was similar between these
two morphological parts (Table 1).
3.2 Soil
Al, Fe, Mg and K in upper soil layer at the unpolluted
sites are mainly supplied from the bed rock or the original
material of the soil [31]. In this study, the upper layer of
soils sampled at the stands of Fly Agaric collection con-
tained Al, Fe, Mg and K in median concentrations of 6000,
3200, 1200 and 690 µg/g dw, respectively (Table 1).
Toxic Cd and Hg in the soil examined were trace con-
taminants (median concentration of 0.040 and 0.028 µg/g
dw) (Table 1). Mercury, found in the soils of various
types, ranged between 0.050.2 µg/g dw, usually consid-
ered to be a “natural” level [44]. A surface of the forest
floor (humifying and mineral layers) is a known site of
airborne Hg accumulation while in the soil profile, Hg is
decreasing with increasing depth [59]. Several hundreds of
forest soils sampled across Poland contained Hg in theup-
per layer (0-10 cm) in concentrations between 0.011-
0.057 µg/g dw (range of median values) while at some
sites, median were noted, e.g. 0.098 (Rogalin), 0.14 (Sta-
© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
458
rachowice forest), 0.15 (Kłodzka Dale), 0.35 (Złotoryja),
or 0.45 µg/g dw (Karpacz) implying that there are con-
tamination problems ([16, 17, 38], unpublished data).
3.3 Bioconcentration
A potential of fungi, plants or animals to accumulate
chemical substances in their body is estimated by biocon-
centration factor (BCF). This parameter is calculated as
quotient of substance concentrations in the whole fruiting
body (carpophore, mushroom) or its parts such as cap or
stalk, compared to substratum colonized by mycelium,
and is expressed on dry weight basis. BCF >1 means the
ability to accumulate a substance but BCF <1 refers to
bio-exclusion. In this study, Cd, found at ultra-trace
amongst the metals determined in the soil, exhibited the
highest values of BCF (averaged 290 (caps) and 180 (sti-
pes)) (Table 1). A significance of Fly Agaric as a species
involved in the biogeochemical turnover of Cd and V in
the forest ecosystem was high-lined by Lepp et al. [15].
Fly Agaric is a spectacular example of ability to accumu-
late vanadium, identified as the metalorganic compound
amavadine.
Also K, Rb, Hg, Cu and Zn exhibited BCF >1 in caps
and stipes of Fly Agaric. For K and Rb, the median BCFs
for caps were 49 and 25, and for Cu and Zn 14 and 7.5,
respectively. The median BCF values for Hg were 29
(caps) and 21 (stipes) showing good availability of this
element to Fly Agaric in the soils surveyed. In earlier
studies of Fly Agaric and the soils from Mierzeja Wiślana
(1993-94) and Zaborski Landscape Park (1997-98), the
BCF values of Hg in caps were between 9.033, and in
stipes between 4.719 [26, 55]. The median BCF values for
Ag, Al, Ba, Ca, Co, Cr, Fe, Mn, Mg, Na and Sr were <1,
implying a limited up-take/availability and bio-exclusion
(Table 1).
In conclusion, Fly Agaric, apart from Cd and V, due
to high BCF values noted, plays also a biogeochemical
role in turnover of K, Rb, Hg, Cu and Zn in unpolluted
forests. Ca, Fe, Mn and Mg, inspite of low BCF values,
are also substances relatively abundant in fruiting bodies of
Fly Agaric, signifying its involvement in biogeochemical
turnover of forests ecosystems.
REFERENCES
[1] Alonso, J., Garciá, M.Á., Pérez-López, M. and Melgar, M.J.
(2003) The concentrations and bioconcentration factors of
copper and zinc in edible mushrooms. Arch. Environ. Con-
tam. Toxicol., 44, 180-188.
[2] Borovička, J., Kotrba, P., Gryndler, M., Mihaljevič, M.,
Řanda, Z., Rohovec, J., Cajthaml, T., Stijve, T. and Dunn
C.E. (2010) Bioaccumulation of silver in ectomycorrhizal
and saprobic macrofungi from pristine and polluted areas.
Sci. Total. Environ., 408, 2733-2744.
[3] Drewnowska, M., Jarzyńska, G., Kojta, A.K., Falandysz, J.
(2012) Mercury in European Blusher, Amanita rubescens,
mushroom and soil. Bioconcentration potential and intake as-
sessment. Journal of Environmental Sciences and Heath, Part
B, 47 (5), 466-474.
[4] Falandysz, J. (2002) Mercury in mushrooms and soil of the
Tarnobrzeska Plain, southeastern Poland. J. Environ. Sci.
Health Pt A, 37, 343-352.
[5] Falandysz, J. (2008) Selenium in edible mushrooms. J. Envi-
ron. Sci. Health Pt C, 26, 256-299.
[6] Falandysz, J. and Danisiewicz, D. (1995) Bioconcentration
factors (BCF) of silver in wild Agaricus campestris. Bull.
Environ. Contam. Toxicol., 55, 122-129.
[7] Falandysz, J., Bona, H. and Danisiewicz, D. (1994) Silver
content of wild-grown mushrooms from northern Poland.
Zeitschr. Lebensm. Unters. Forsch., 199, 223-224.
[8] Falandysz, J., Gucia, M., Frankowska, A., Kawano M. and
Skwarzec, B. (2001) Total mercury in wild mushrooms and
underlying soil substrate from the city of Umeå and its sur-
roundings. Bull. Environm. Contam. Toxicol., 67, 763-770.
[9] Falandysz, J., Szymczyk, K., Ichihashi, H., Bielawski, L.,
Gucia, M., Frankowska, A. and Yamasaki, S. (2001)
ICP/MS and ICP/AES elemental analysis (38 elements) of
edible wild mushrooms growing in Poland. Food Addit. Con-
tam., 18, 503-513.
[10] Falandysz, J., Jędrusiak, A., Lipka, K., Kannan, K., Ka-
wano, M., Gucia, M., Brzostowski, A. and Dadej, M. (2004)
Mercury in wild mushrooms and underlying soil substrate
from Koszalin, North-central Poland. Chemosphere, 54, 461-
466.
[11] Jarzyńska, G. and Falandysz, J. (2011) The determination of
mercury in mushrooms by CV-AAS and ICP-AES tech-
niques. J. Environ. Sci. Health Pt. A., 46(6), 569–573.
[12] Garciá, M.Á., Alonso, J. and Melgar, M.J. (2005) Agaricus
macrosporus as a potential bioremediation agent for sub-
strates contaminated with heavy metals. J. Chem, Technol.
Biotechnol., 80, 325-330.
[13] Kojta, A.K., Gucia, M., Jarzyńska, G., Lewandowska, M.,
Zakrzewska, A., Falandysz, J., Zhang, D. (2011) Phospho-
rous and metallic elements in Parasol Mushroom (Macrole-
piota procera) and soil from the Augustowska Forest and Ełk
regions in north-eastern Poland. Fresenius Environ Bull 20
(11a) 3044-3052.
[14] Konuk, M., Afyon,A., Yağız, D. (2007) Minor element and
heavy metal contents of wild growing and edible mushrooms
from western Black sea region of Turkey. Fresenius Environ
Bull 16 (11a), 1359-1362.
[15] Lepp, N.W., Harrison, S.C.S. and Morrell, B.G. (1987) A
role for Amanita muscaria L. in the circulation of cadmium
and vanadium in non-polluted woodland. Envion. Geo.
Health., 9, 61-64.
[16] Chudzyński, K., Bielawski, L. and Falandysz, J. (2009) Mer-
cury bio-concentration potential of Larch Bolete, Suillus gre-
villei, mushroom. Bull. Environ. Contam. Toxicol. 83, 275-
279.
[17] Chudzyński, K., Jarzyńska, G., Stefańska, A. and Falandysz,
J. (2011) Mercury content and bio-concentration potential of
Slippery Jack, Suillus luteus, mushroom. Food Chem, 125,
986-990.
[18] Falandysz, J. and Gucia, M. (2008) Bioconcentration factors
of mercury by Parasol Mushroom (Macrolepiota procera).
Environ. Geochem. Health, 30, 121-125.
[19] Falandysz, J., Bona, H. and Danisiewicz, D. (1994) Silver up
take by Agaricus bisporus from an artificially enriched sub-
strate. Zeitschr. Lebensm. Unters. Forsch., 199, 225-227.
© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
459
[20] Zhang, D., Frankowska, A., Jarzyńska, G., Kojta, A.K.,
Drewnowska, M., Wydmańska, D., Bielawski, L., Wang, J.
and Falandysz, J. (2010) Metals of King Bolete (Boletus
edulis) Bull.: Fr. collected at the same site over two years.
Afr. J. Agric. Res., 5, 3050-3055.
[21] Brzostowski, A., Falandysz, J., Jarzyńska, G. and Zhang, D.
(2011) Bioconcentration potential of metallic elements by
Poison Pax (Paxillus involutus) mushroom. J. Environ. Sci.
Health Part A, 46 (4), 378-393.
[22] Brzostowski, A., Falandysz, J., Jarzyńska, G. and Zhang D.
(2011) Bioconcentration potential of metallic elements by
Poison Pax (Paxillus involutus) mushroom. J. Environ. Sci.
Health Part A, 46 (4), 378-393.
[23] Falandysz, J., Bielawski, L., Kannan, K., Gucia, M., Lipka,
K. and Brzostowski, A. (2002) Mercury in wild mushrooms
and underlying soil substrate from the great lakes land in Po-
land. J. Environ. Monit., 4, 473-476.
[24] Falandysz, J., Bielawski, L., Kawano, M., Brzostowski, A.
and Chudzyński, K. (2002) Mercury in mushrooms and soil
from the Wieluńska Upland in south-central Poland. J. Envi-
ron. Sci. Health Pt A., 37, 1409-1420.
[25] Falandysz, J., Gucia, M., Skwarzec, B., Frankowska, A.,
Klawikowska, K. (2002) Total mercury in mushrooms and
underlying soil from the Borecka Forest, Northeastern Po-
land. Arch. Environ. Contam. Toxicol., 42, 145-154.
[26] Falandysz, J., Lipka, K., Gucia, M., Kawano, M., Strumnik,
K., Kannan, K. (2002). Accumulation factors of mercury in
mushrooms from Zaborski Lndscape Park, Poland. Environ.
Int., 28, 421-427.
[27] Falandysz, J., Kawano, K., Świeczkowski, A., Brzostowski,
A. and Dadej, M. (2003) Total mercury in wild-grown higher
mushrooms and underlying soil from Wdzydze Landscape
Park, Northern Poland. Food Chem., 81, 21-26.
[28] Falandysz, J., Gucia, M., Brzostowski, A., Kawano, M., Bie-
lawski, L., Frankowska, A. and. Wyrzykowska, B (2003)
Content and bioconcentration of mercury in mushrooms from
northern Poland. Food Addit. Contam., 20, 247-253.
[29] Falandysz, J., Kubota, R., Kunito, T., Bielawski, L., Brzos-
towski, A., Gucia, M., Jędrusiak, A., Lipka, K., Tanabe, S.
(2003) Relationships between selenium and mercury in the
fruiting bodies of some mushrooms growing in Poland. J.
Physique IV. 107, 443-446.
[30] Ohtonen, R. (1982) Mineral concentrations in some edible
fungi and their relation to fruit-body size and mineral status
of substrate. Ann. Bot. Fenn., 19, 203-209.
[31] Yoshida, S., and Muramatsu, Y. (1997) Determination of ma-
jor and trace elements in mushroom, plant and soil samples
collected from Japanese forest. In. J. Environ. Anal. Chem.,
67, 49-58.
[32] Borovička, J., and Řanda Z. (2007). Distribution of iron, cobalt,
zinc and selenium in macrofungi. Mycol Progr, 6: 249-259.
[33] Falandysz, J., Frankowska, A., Mazur, A. (2007) Mercury and
its bioconcentration factors in King Bolete (Boletus edulis)
Bull. Fr. J. Environ. Sci. Health Pt. A., 42, 2089-2095.
[34] Falandysz, J., Gucia, M. and Mazur, A. (2007) Content and
bioconcentration factors of mercury by Parasol Mushroom
Macrolepiota procera. J. Environ. Sci. Health Pt B., 42, 735-
740.
[35] Falandysz, J., Kunito, T., Kubota, R., Bielawski, L., Mazur,
A., Falandysz, J.J. and Tanabe, S. (2007) Selected elements
in Brown Birch Scaber Stalk Leccinum scabrum. J. Environ.
Sci. Health Pt A., 42, 2081-2088.
[36] Falandysz, J., Kunito, T., Kubota, R., Bielawski, L.,
Frankowska, A., Falandysz, J.J. and Tanabe S. (2008) Multi-
variate characterization of elements accumulated in King Bo-
lete Boletus edulis mushroom at lowland and high mountain
regions. J. Environ. Sci. Health Pt A., 43,1692-1699.
[37] Falandysz, J., Kunito, T., Kubota, R., Gucia, M., Mazur, A.,
Falandysz, J.J. and Tanabe, S. (2008) Some mineral constitu-
ents of Parasol Mushroom Macrolepiota procera. J. Environ.
Sci. Health Pt B., 43, 187-192.
[38] Frankowska, A., Ziółkowska, J., Bielawski, L. and Fa-
landysz, J. (2010) Profile and bioconcentration of minerals
by King Bolete (Boletes edulis) from the Płocka Dale in Po-
land. Food Addit. Contam. Pt B., 3, 1-6.
[39] Gucia, M., Jarzyńska, G., Kojta, A.K. and Falandysz, J.
(2011) Temporal variability in twenty chemical elements
content of Parasol Mushroom (Macrolepiota procera) col-
lected from two sites over a few years. J. Environ. Sci.
Health, Pt B., 47, 81–88.
[40] Cenci, R.M., Cocchi, L., Petrini, O., Sena, F., Siniscalco, C.
and Vescovi, L. (2010) Elementi chimici nei funghi superiori.
I funghi di riferimento come strumento di lavoro per la bio-
indicazione e la biodiversità. JRC Scientific and Technical
Reports. EUR 24415 IT.
[41] Chudzyński, K. and Falandysz, J. (2008) Multivariate analy-
sis of elements content of Larch Bolete (Suillus grevillei)
mushroom. Chemosphere, 78, 1230-1239.
[42] Malinowska, E., Szefer, P. and Falandysz, J. (2004) Metals
bioaccumulation by bay bolete, Xerocomus badius, from se-
lected sites in Poland. Food Chem. 84, 405-416.
[43] Melgar, M.J., Alonso, J., Pérez-López, M. and Garcia, M.A.
(1998) Influence of some factors in toxicity and accumula-
tion of cadmium from edible wild macrofungi in NW Spain.
J. Environ. Sci. Health Pt B., 33, 439-455.
[44] Kabata-Pendias, A. and Pendias, H. (1999) Biogeochemia
pierwiastków śladowych. Warszawa. Wydawnictwo Nukowe
PWN. Warszawa.
[45] Falandysz, J. and Bielawski, L. (2001) Mercury content of
wild edible mushrooms collected near the town of Augustów.
Pol. J. Environ. Stud., 10, 67-71.
[46] Li, Ch., and Oberlies, N.H. (2005) The most widely recog-
nized mushrooms: Chemistry of the genus Amanita. Life Sci.,
78, 532-538.
[47] Michelot, D., and Melendez-Howell, M. (2003) Amanita
muscaria: chemistry, biology, toxicology and ethnomycol-
ogy. Mycol. Res., 107, 131-146.
[48] Saar, M. (1991) Ethnomycological data from Siberia and
north-east Asia on the effect of Amanita muscaria. J. Ethno-
pharmacol. 31, 157-173.
[49] Falandysz, J., Kunito, T., Kubota, R., Lipka, K., Mazur, A.,
Falandysz, J.J. and Tanabe, S. (2007) Selected elements in
Fly Agaric Amanita muscaria. J. Environ. Sci. Health Pt. A.,
42, 1615-1623.
[50] Falandysz, J., Lipka, K., Mazur, A. (2007) Mercury and its
bioconcentration factors in Fly Agaric (Amanita muscaria)
from spatially distant sites in Poland. J. Environ. Sci. Health
Pt. A., 42, 1625-1630.
[51] Vetter, J. (2005) Mineral composition of basidiomes of Ama-
nit species. Mycol. Res., 109, 746-750.
[52] Brzostowski, A., Bielawski, L., Orlikowska, A., Plichta, S.
and Falandysz, J. (2009) Instrumental analysis of metals pro-
file in Poison Pax (Paxillus involutus) collected at two sites
in Bory Tucholskie. Anal. Chem. (Warsaw), 54, 907-920.
© by PSP Volume 22 – No 2. 2013 Fresenius Environmental Bulletin
460
[53] Brzostowski, A., Jarzyńska, G., Kojta, A.K., Wydmańska, D.
and Falandysz, J. (2011) Variations in metal levels accumu-
lated in Poison Pax (Paxillus involutus) mushroom collected
at one site over four years. J. Environ. Sci. Health Pt A,
46(6), 581–588.
[54] Falandysz, J. (1990) Mercury content of squid Loligo opales-
cens. Food Chem, 38, 171-177.
[55] Falandysz, J. and Chwir, A. (1997) The concentrations and
bioconcentration factors of mercury in mushrooms from the
Mierzeja Wiślana sand-bar, Northern Poland. Sci. Total. En-
viron., 20, 221-228.
[56] Müller, M., Anke, M. and Illing-Günther, H. (1997) Alumin-
ium in wild mushrooms and cultivated Agaricus bisporus. Z.
Lebensm. Unters. Forsch., 205, 242-247.
[57] Rudawska, M., and Leski, T. (2005) Trace elements in fruit-
ing bodies of ectomycoriizal fungi growing in Scots pine (Pi-
nus silvestris L.) stands in Poland. Sci. Total. Environ., 339,
103-115.
[58] Falandysz, J., Frankowska, A., Jarzyńska, G., Dryżałowska,
A., Kojta, A.K. and Zhang, D. (2011) Survey on composition
and bioconcentration potential of 12 metallic elements in
King Bolete (Boletus edulis) mushroom that emerged at 11
spatially distant sites. J. Environ. Sci. Health Part B, 46(3),
231-246.
[59] Falandysz, J., Kawano, M., Danisiewicz, D., Chwir, A.,
Boszke, L., Gołębiowski, M. and Boryło, A. (1996) Badania
nad występowaniem rtęci w glebach w Polsce. Bromatol.
Chem. Toksykol. 29, 177- 181.
Received: June 26, 2012
Revised: August 23, 2012
Accepted: August 27, 2012
CORRESPONDING AUTHOR
Małgorzata Drewnowska
University of Gdańsk
Institute of Environmental Sciences & Public Health
19 Sobieskiego Str.
80-952 Gdańsk
POLAND
Phone: +48 58 523 54 72, +48 58 34 504 45
Fax: +48 58 523 54 72
E-mail: malgorzata.drewnowska@gmail.com
FEB/ Vol 22/ No 2/ 2013 – pages 455 - 460
