spiders (araneae) of the fishpond eulittoral zone - European Society ...

Ekológia (Bratislava) Vol. 19, Supplement 4, 51-54, 2000
SPIDERS (ARANEAE) OF THE FISHPOND
EULITTORAL ZONE
MICHAL HOLEC
University of South Bohemia, Faculty of Biological Sciences, Na sádkách 7, 37005 České Budějovice, Czech
Republic; Institute of Soil Biology, Academy of Sciences of the Czech Republic, Na sádkách 7, 37005 České
Budějovice, Czech Republic. E-mail: mh@tix.bf.jcu.cz
Introduction
Abstract
HOLEC M.: Spiders (Araneae) of the fishpond eulittoral zone. In GAJDOŠ P., PEKÁR S. (eds): Proceedings
of the 18th European Colloquium of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava),
Vol. 19, Supplement 4/2000, p. 51-54.
A study was made of spiders living in vegetation (Phragmites australis, Typha angustifolia and
Carex) of the eulittoral zone of ponds in the Czech Republic. Specimens were collected from
floating pitfall traps, by beating vegetation and by hand collection. In total, 38 spider species
were recorded, and ten of these are considered to be specialised inhabitants of the eulittoral zone.
The spider assemblage of tall sedge vegetation exhibited the highest abundance and species diversity.
Various types of wetlands have been studied in the Czech Republic. Bogs were studied
intensively by KŮRKA (e.g. 1990, 1995) and (MILLER, 1951), wet meadows by RŮŽIČKA (1987).
MILLER, OBRTEL (1975) investigated the terrestrial zone of fishpond reed marshes. The
arachnofauna of the eulittoral zone of fishpond vegetation has not been studied previously
in the Czech Republic.
SZINETÁR (1993) summarised the literature on spiders of moorlands in Hungary. SZINETÁR
(1995) published interesting faunistic data for the reed beds of Lake Balaton. RENNER,
BELLMAN (1995) investigated the spider fauna of the lake ,,Schmiechener See“. Spider communities
of the Danube Delta were investigated by WEISS et al. (1998). The distribution
pattern of hygrophilous species of the genus Pirata was described by RENNER (1986) and
that of Tetragnatha species in the Danube Delta by UHL et al. (1992). Data on the ecology
and distribution of species of the genus Dolomedes were summarised by HELSDINGEN (1993)
and DUFFEY (1995).
51

T a b l e 1. List of spider species recorded in vegetation
stands of Cx -Carex, Ta- Typha angustifolia, Pa-
Phragmites australis. – A: in small numbers and locally
distributed, B: in small numbers and widespread, C:
abundant and locally distributed, D: abundant and
widespread. * eulitoral specialists.
Cx Ta Pa
Araeoncus crassiceps (WEST.) A
Antistea elegans (BL.) B B B
Aphileta misera (O. P.-C.) A
Bathyphantes approximatus (O. P.-C.) D B B
Bathyphantes gracilis (BL.) D B B
*Clubiona juvenis SIMON A A
Clubiona phragmitis C. L. K. B D D
Dismodicus bifrons (BL.) A
Dolomedes fimbriatus (CL.) A
*Dolomedes plantarius (CL.) D
*Donacochara speciosa (TH.) B D D
Enoplognatha caricis (FICK.) A
Gnathonarium dentatum (WIDER) B B B
Gongylidiellum murcidum SIMON A A A
Hypomma bituberculatum (WIDER) D B B
Kaestneria pullata (O. P.-C.) A A A
Larinioides folium (SCH.) B B B
Lophomma punctatum (BL.) A A
*Marpissa radiata (GRUBE) B A A
*Microlinyphia impigra (O. P.-C.) B B B
Neriene clathrata (SUND.) D B B
Pachygnatha clercki SUND. D B B
Pardosa prativaga (L. K.) B B B
Pardosa sphagnicola (F. D.) A
Pirata piraticus (CL.) D D D
Pirata piscatorius (CL.) B B
Pirata tenuitarsis SIMON C C C
Porrhomma pygmaeum (BL.) A A A
*Rugathodes instabilis (O. P.-C.) C C A
Silometopus elegans (O. P.-C.) A A
Sitticus floricola (C. L. K.) B A A
Taranucnus setosus (O. P.-C.) A
Tetragnatha extensa (L.) D B B
*Tetragnatha shoshone LEVI A C C
*Tetragnatha striata L. K. C C C
*Theridion hemerobius SIMON A D A
*Theridiosoma gemmosum (L. K.) B B B
Tibellus maritimus (MENGE) A A A
52
total number of species 37 28 29
I studied spiders in three different
types of littoral vegetation. Selected
faunistic data were published
by RŮŽIČKA, HOLEC (1998).
Material and methods
Spiders were collected from the
vegetation by hand, and by beating the
vegetation. Floating pitfall traps (RŮŽIČKA,
1982; RENNER, 1986) were used in order to
collect spiders walking on the water
surface. Spiders were collected from the
end of April to July in 1996 and 1997. 702
determinable individuals representing 38
species were collected. Thirteen stands of
vegetation in eight ponds in different parts
of the Czech Republic were investigated.
Spiders were collected from three types of
littoral vegetation - Phragmites australis
(five plots), Typha angustifolia (three plots)
and stands with Carex (three plots
vegetated by Carex acutiformis and two by
Carex elata).
Abundance data were treated semiquantitatively,
and coded as follows; - A:
species in small numbers and locally
distributed, B: in small numbers and
widespread, C: abundant and locally
distributed, D: abundant and widespread.
This classification is based on our own data
and on the literature (BUCHAR, 1989).
Results and discussion
38 species were recorded (Table
1). 10 of these have not been recorded
before in terrestrial habitats
or in wetlands in the Czech Republic.
These species are considered
to be specialists of the eulittoral
zone (these species are marked by
an asterisk in Table 1).
Tetragnatha shoshone LEVI and
Tetragnatha striata L. KOCH were

collected predominantly at the water’s edge near reed and cattail stands. Donacochara
speciosa (THORELL), Clubiona juvenis SIMON were associated mainly with reed and dense
cattail stands. Theridion hemerobius SIMON was collected in highest numbers in the canopy
layers of cattail. Marpissa radiata (GRUBE) prefers sedge, although it seems to be more
terrestrial than the other species. HOLEC (unpubl.) observed several females with cocoons in
a pea field surrounding large reed marshes. BÍLEK (in BUCHAR, 1989) collected this species
from oak seedlings near a pond. Records of M. radiata from the Czech Republic are rare,
its occurrence in sedge is relatively common, and I consider this species to be a specialist
of the eulittoral zone. Theridiosoma gemmosum (L. KOCH) is a widespread species, but
usually very time-consuming to find. Although I searched intensively in reed, sedge and
cattail stands, I never found large numbers of specimens. T. gemmosum was recorded in
higher numbers (about 50 subadult males in five minutes) in grass overhanging the banks of
channels (HOLEC, RŮŽIČKA,1998). Similarly, BOGGILD (BOGGILD, CROCKER, 1971) collected it
in higher numbers (40 specimens in half an hour), although none were found in the first half
hour. Dolomedes plantarius (CLERCK) was recorded only among sedges along eutrophic
fishponds or among water lilies, surrounded by sedge stands. Our results correspond with
DUFFEY (1995), who showed that D. plantarius is a species of mesotrophic/eutrophic wetlands.
There is no firm evidence for D. plantarius coexisting with D. fimbriatus (CLERCK)
anywhere in Europe (DUFFEY, 1995). Three localities were recorded where both species
were caught together at the same site and in the same habitat (flooded sedge) in the Czech
Republic. Two records were from South Bohemia (1 ex. D. plantarius and 1 ex. D. fimbriatus,
Potěšil pond, lgt. Růžička; 1 ex. D. plantarius and 1 ex D. fimbriatus, Velký Tisý pond, lgt.
Holec) and two were from North Bohemia (1 ex. D. plantarius and 1 ex. D. fimbratus,
Břehyně ponds, lgt. Holec; 4 ex. D. plantarius and 2 ex. D. fimbriatus, Hradčanské rybníky
ponds, lgt. Holec). KŮRKA (1997) investigated pine bogs surrounding both North Bohemian
ponds mentioned and recorded only D. fimbriatus.
Coexistence of both species at ponds can probably be common at localities where the
bog habitat of D. fimbriatus shows a gradual transition to the pond habitat of D. plantarius.
RENNER, BELLMAN (1995) described two main factors influencing the spider fauna at
Schmiechener See in Southern Germany. The first factor is the presence of extensive stands
of Carex elata and the second is an extreme fluctuation of water level. Despite methodological
problems with data collection, it seems that permanently flooded sedge tussock
stands are unique habitats for retaining species diversity. Thirty seven species were recorded
here and the abundance of most species also seemed to be higher.
Similarly, LUFF (1966), BOSSENBROEK et al. (1977), KESSLER et al. (1988) and DENIS et al.
(1998) found that grass or sedge tussock can harbour rather large numbers of invertebrates
under adverse weather conditions. Tussocks of Carex elata and C. acutiformes are typical
of permanently high water and sedges provide relative stable biotopes. The high degree of
spatial variability of sedge tussocks is evident. Most spiders are associated with the zone of
overhanging old leaves.
The eulittoral zone of reed vegetation is a relatively homogeneous habitat without much
spatial variability. High water level can be much more important here than in the case of
sedge tussocks. The water level determines the spatial variability of the ground zone where
53

there is reed litter. Narrow-leaved cattail grows in permanently deeper water. Its lowest
layer is thin and only rarely emerges from the deep water. Most of its diversity is associated
with higher leaf canopy layers.
I can confirm the importance of both factors. More detailed studies on the structure of
pond vegetation and faunistics studies are needed to understand its diversity.
References
BOSENBROEK, P., KESSLER, A., LIEM, A.S.N., VLIJM, L., 1977: The significance of plant growth –forms as shelter
for terrestrial animals. J. Zool. Lond., 182, p. 1-6.
BØGGILD, O., CROCKER, J., 1971: Notes on the habitat of Theridiosoma gemmosum (L. Koch). Newsl. Br. Arachnol.
Soc., 2, p. 6.
BUCHAR, J., 1989: The knowledge of the present Bohemian arachnofauna and its improvement to evaluation of
natural conditions. Thesis, Charles University, Praha. (In Czech)
DENIS, P.Y., GORDON, I.J., 1998: Distribution and abundance of small Insects and Arachnids in Relation to Structural
Heterogenity of grazed, indigenous Grasslands. Ecol. Entomol., 23, 3, p. 253-264.
DUFFEY, E., 1995: The distribution, status and habitat of Dolomedes fimbriatus (Clerck) and D. plantarius in
Europe. In RŮŽIČKA, V. (ed.): Proceedings of the 15 th European Colloquium of Arachnology, České Budějovice,
1994, p. 54-65.
VAN HELSDINGEN, P.J., 1993: Ecology and distribution of Dolomedes in Europe (Araneida: Dolomedidae). Boll.
Acc. Gioenia Sci. Nat., 26, 345, p. 181-187.
KESSLER, A., VERMEULEN, J.W.C., WAPENAAR, P., 1984: Partitioning of the space in tussock of the sedge, Carex
distans, during winter, by spider community. J. Zool. Lond., 204, p. 259-269.
KŮRKA, A., 1990: The arachnofauna Bohemian peat bogs. Spiders of the State Nature Reserve Mrtvý Luh.
Šumava Mts. Acta Mus. Nat. Pragae. Ser. B, 46, p. 37-77.
KŮRKA, A., 1995: Some rare and remarkable spiders species from peat bogs of the Czech Republic. Čes. Nár.
Muz., Řada přírodověd., 164, p. 77-86.
KŮRKA, A., 1997: The spider fauna (Araneida) of the military area Ralsko. Bezděz, 5, p. 237-268. (In Czech)
LUFF, M.L., 1966: The abundance and diversity of the beetle fauna of grass tussock. J. Anim. Ecol., 35, p. 189-208.
MILLER, F., 1951: Araneous-Fauna of the Peat-Bogs near Rejvíz (High Jeseník). Přírodovědecký sborník ostravského
kraje, 12, p. 202-247. (In Czech)
MILLER, F., OBRTEL, R., 1975: Soil surface spiders (Araneida) in terrestrial reed swamp in southern Moravia
(Czechoslovakia). Acta Entomol. Bohemoslov., 72, p. 272-285.
RENNER, F., 1986: Zur Nischendiffer enzierung bei Pirata-Arten (Araneida, Lycosidae). Verh. naturwiss. Ver.
Hamburg (NF), 28, p. 75-90.
RENNER, F., BELLMANN, H., 1995: Zur Spinnenfauna des Naturschutzgebietes ,,Schmiechener See“. Beih. Veröff.
Naturschutz Landschaftspflege Bad.- Württ., 78, p. 403-410.
RŮŽIČKA, V., 1982: Modification to improve the efficiency of pitfall traps. Newsl. Br. Arachnol. Soc., 34, p. 2-4.
RŮŽIČKA, V., 1987: An analysis of spider communities in the meadows of the Třeboň basin. Acta Sc. Nat., Brno,
21, 5, p. 1-39.
RŮŽIČKA, V., HOLEC, M., 1998: New records of spiders from pond littoral in the Czech Republic. Arachnol. Mitt.,
16, p. 1-7.
SZINETÁR, C., 1993: The spider of reed marshlands in Hungary. Folia ent. hungarica, 54, p. 155-162. (In Hungarian)
SZINETÁR, C., 1995: Some data on the spider fauna of reeds in Hungaria. I. Interesting faunistic data from the
reeds of Lake Balaton. Folia ent. hung, 56, p. 205-209.
UHL, G., SACHER P., WEISS I., KRAUS, O., 1992: Europaische Vorkomen von Tetragnatha shoshone (Arachnida,
Araneae, Tetragnathidae). Verh. naturwiss. Ver. Hamburg (NF), 33, p. 247-261.
WEISS, I., SCHNEIDER, E., ANDRIESCU, I., 1998: Die Spinnen des Biosphärenreservats Donau-Delta, Rumanien
(Arachnida, Araneae). Linzer biol.Beitr., 30, 1, p. 263-275.
54

Ekológia (Bratislava) Vol. 19, Supplement 4, 55-64, 2000
LONG TERM CHANGES IN SPIDER (ARANEAE)
COMMUNITIES IN NATURAL AND DRAINED FENS
IN THE BIEBRZA RIVER VALLEY
ANNA KAJAK 1 , JANUSZ KUPRYJANOWICZ 2 , PETER PETROV 1
1 Institute of Ecology PAS, 05-092 Łomianki, Poland. E-mail: ekolog@warman.com.pl
2 University in Bialystok, Institute of Biology, Swierkowa 20B, 15-950 Bialystok, Poland. E-mail:
kuprzool@cksr.ac.bialystok.pl
Introduction
Abstract
Kajak A., Kupryjanowicz J., Petrov P.: Long term changes in spider (Araneae) communities in
natural and drained fens in the Biebrza River Valley. In Gajdoš P., Pekár S. (eds): Proceedings of
the 18th European Colloquium of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava), Vol.
19, Supplement 4/2000, p. 55-64.
The density and diversity of spiders were compared in three periods: I – 1955, II – 1978-1983, III-
1996-1998. The quadrat method was applied to estimate the density of spiders, and the Shannon-
Wiener index was used to calculate species diversity. A decrease in spider species diversity, through
time, was detected in managed grasslands. It was accompanied by a decrease in the number of
families. This tendency was not found in natural fens. Spider density was similar in the compared
periods. In period III, spider diversity and total density were positively correlated with soil moisture,
abundance of microhabitats in an area and landscape heterogeneity, measured by the distance to
shrubs. A negative correlation was found between the density of spiders and the intensity of management
practice (mowing by heavy machines and grazing by cattle), and the bulk density of the soil.
Plant diversity (H‘ based on the proportion of the area covered by each plant species) did not
influence the diversity of spiders. The proportion of species connected exclusively with the field
layer decreased with time. The effect of management on spider mobility was positive.
The objective of our study was to analyse changes in spider species diversity and density in
fens, over time and over environmental gradients. Impoverishment of a community is considered
an indicator of the deterioration of habitat quality. Spider communities are a reliable
source of information concerning the condition of habitats, because of their sensitivity to
environmental conditions, their high number of species, and their tendency to occur abundantly
in various ecosystems (DUFFEY, 1978; MAELFAIT et al., 1997; HÄNGGI et al., 1995). This
problem is especially relevant to peatlands, which are endangered habitats, due to their dimin-
55

T a b l e 1. Number of study sites in natural and
managed grasslands, on soil formed from sedge
moss (A), tall sedge (B), or alder (C) type of peat,
analysed for three periods.
Period Sites
(Years) Natural Managed
A B A B C
I 1955 – 2 2 – –
IIa 1978-1979 1 2 1 3 1
IIb 1982-1983 1 2 1 3 2
III 1996-1998 1 2 2 2 2
T a b l e 2. Characteristics of study sites in natural (N) grasslands in
period III. Data after SZUNIEWICZ, CHRZANOWSKI (in press),
KAMIŃSKI (in press).
Parameter A B
Peat origin sedge-moss Sedge
Mean soil moisture (% by volume) 85.0 83.9-87.6
Soil bulk density (g.cm -3 ) 0.154 0.151-0.160
Thickness of peat deposit (cm) 150 70-170
Yield (g.dwt.m -3 ) 350 200-250
T a b l e 3. Characteristics of study sites in managed grasslands, analysed in period III. Data after
PASTERNAK-KUŚMIERSKA et al.1997, SZUNIEWICZ, CHRZANOWSKI (in press), KAMIŃSKI (in press).
Parameter A B C
Peat origin sedge-moss sedge alder
Mean soil moisture (% by volume) 78-82 68-79 59-71
Soil bulk density (g cm -3 ) 0.198-0.209 0.229-0.371 0.256-0.332
Thickness of peat deposit (cm) 400 140-400 80-265
Yield (g d.wt m -2 ) 460 350 - 395 264 - 900
T a b l e 4. Spider species diversity and mean density (ind.m -2 ) in natural and managed peat grasslands.
Period Natural grasslands Managed grasslands P
Density H’ Density H’
1 3 2 4 1-2 3-4
I 19.0 ±1.0 4.42 - 4.54 12.6 ± 0.7 3.90 – 4.45

for use as hay meadows and pastures. Other parts were included in the Biebrza National
Park and left without human interference. We tried to analyse how spider communities
changed in both natural (N) and managed (M) grasslands by comparing (1) species diversity,
(2) total density, and (3) community structure, from three sampling periods (Table 1).
Material and methods
All study sites were located on peat soils originating from the three plant communities, which are most
common in the valley. These were: A. sedge-moss communities (Caricetum limoso-diandrae) in the emersion
zone of the valley, B. tall sedge communities (Caricetum elatae and Peucedano-Caricetum paradoxae), in
immersion, flooded zone, or C. alder carr (Carici elongatae –Alnetum), which border the valley (Table 1).
The soil properties, such as soil moisture content, decomposition rate of peat deposits, and soil texture, depend
considerably on the origin of peat (Table 2 and 3). Soils formed from the sedge-moss community were
characterised by a well-developed moss layer, the highest water-holding capacity of the soil and relatively
stable moisture level throughout the year, in natural and drained grasslands (Table 2 and 3). The lowest moisture
content was found in soils originating from alder peat (C). They were mineralised at the highest rate after
drainage. Soils formed from tall sedge peat were intermediate in respect to water content and decomposition
rate of peat deposits (Table 2 and 3).
In most cases managed grasslands (M) were mown 2-3 times a year by heavy machines, and the hay was
immediately removed. The drainage system was extended for hundreds of hectares between period I and II.
Presently drained grasslands accounted for 62% of the area of organic soils in the valleys (OKRUSZKO, 1990).
In period I small patches of cultivated grasslands were surrounded by extensive areas of natural fens (N). In
Period II management was intensified. The drainage induced rapid mineralization of organic matter accumulated
in peat, and the thickness of peat deposits declined gradually. A characteristic feature of drained fens is high
variability of soil properties and of plant and animal communities. The system is subjected to secondary
succession. More information about the grasslands studied is given in KAJAK (1962), KACZMAREK (1991),
STEPA,PAŁCZYŃSKI (1991).
In all periods compared, the quadrat method was applied to assess spider density. The effectiveness of
collecting spiders improved with time. In period I, spiders were hand-collected from large frames (0.25 m 2 in
area). 16 samples were taken per site on each sampling date. In the next two periods (II and III) spiders were
collected from smaller frames (0.0625 m 2 ), 10 samples per site were taken. Starting in 1982 (Period II b),
samples were cut out of grassland turf and shaken several times over a plastic sheet until no more spiders
could be seen. In each period samples were taken from May until October (190 –250 per site in period I, 40 –
190 in period II, 60 in period III).
Species diversity was calculated by using the Shannon-Wiener diversity index H‘, the t-test was applied to
estimate significance of differences between the values obtained. The number of specimens used in calculations
ranged from 150 to 850 from particular sites and periods. In calculating the diversity index (H‘) for plants, the
per cent of area covered by each plant species was used. The data after KOTOWSKA et al.(1998) and KAMIŃSKI (in
press) were used in calculations.
The Wilcoxon signed rank test was applied to compare differences in diversity between periods in pooled
spider data, and the Mann-Whitney U test to compare differences between natural and managed grasslands. The
Kendall rank correlation coefficient was used to analyse the correlation between spider diversity and habitat
properties (soil moisture, plant species diversity, plant complexity and distance to the nearest shrubs) in period
III. An analysis of covariance was applied to estimate density response to the same environmental factors. In the
ranking of the grasslands studied with respect to plant complexity (number of microsites per area), the highest
rank was given to grassland with a thick layer of mosses and litter and a multi-layered sward, formed by sedges
and grasses with an admixture of forbes. The lowest rank was assigned to a grassland with low vegetation and
patches of bare ground. The distance to the nearest shrubs was treated as a measure of landscape heterogeneity.
This distance ranged from several meters to hundreds of meters in particular sites.
57

T a b l e 5. Correlation coefficients (Kendall tau) between
spider species diversity index (H`) and environmental factors
(Period III).
Variable tau N P
Soil moisture 0.64 12 0.002
Plant species diversity 0.11 16 0.27
Number of microhabitats 0.68 16 0.0003
Intensity of management –0.71 8 0.007
Landscape heterogeneity 0.78 8 0.0012
T a b l e 6. Number of spiders belonging to various families as a percentage of the total number of spiders
during three periods in natural peat grasslands. *Symbols of sites: N – natural fen, A- grassland located on
sedge-moss peat, B- grassland located on tall sedge peat.
Family
I
Periods
II
Study sites*
III
NB1 NB2 NA NB3 NA NB3
Araneidae 11.5 22.1 0.3 0.1 0.1 0.8
Linyphiidae 10.1 11.6 68.0 70.6 69.3 57.8
Lycosidae 37.1 29.1 13.5 2.0 19.6 23.4
Tetragnathidae 10.1 4.4 0.6 0.2 1.4 0.4
Thomisidae 0.85 3.8 4.0 4.5 2.1 5.3
Philodromidae 7.5 11.0 0.4 0.4 0.2 1.4
Salticidae 4.2 3.8 10.7 18.4 0 1.3
Clubionidae 4.7 5.1 2.1 3.6 1.1 3.3
Gnaphosidae 4.5 2.0 0 0 0 0.2
Theridiidae 1.8 0.4 0.2 0.2 1.3 1.5
Hahnidae 9.8 2.15 0 0 3.6 1.8
Dictynidae 2.4 1.2 0.2 0 0.7 1.3
Zoridae 0.2 1.7 0 0 0.2 1.0
Liocranidae 0 0.1 0 0 0.4 0.3
Pisauridae 0 2.0 0 0 0 0
Mimetidae 0 0 0 0 0 0.2
No. of families 13 15 10 9 12 15
Results and discussion
Species diversity and composition
Species diversity ranged from 2.95 to 4.72 for the periods and sites compared (Table 4).
Species diversity was significantly higher in natural fens than in managed grasslands (P

T a b l e 7. Number of spiders belonging to various families as a percentage of the total number of spiders in
three periods in managed grasslands. *Site symbols: M – managed grassland site, A- soil formed from sedgemoss
peat, B –soil formed from tall sedge peat.
Family
I
Periods
II a
Study sites*
III
MA1 MA2 MB1 MA1 MB1 MA1
Araneidae 25.9 15.0 0 0 0.6 0.7
Linyphiidae 16.5 24.5 59.1 71.4 36.3 73.1
Lycosidae 6.4 9.3 21.3 2.8 35.6 5.2
Tetragnathidae 39.8 32.4 13.6 25.8 13.0 3.2
Thomisidae 6.4 7.0 3.3 0 13.2 12.4
Philodromidae 1.9 1.9 0 0 0 0
Salticidae 0.4 0.4 1.3 0 0 0
Clubionidae 0.4 5.1 0 0 0 0
Gnaphosidae 0.4 5.7 0 0 0 0
Theridiidae 1.9 3.2 0.7 0 0.6 5.4
Hahnidae 0 0.2 0.7 0 0.4 0
Dictynidae 0 0.2 0 0 0.3 0
Zoridae 0 0.2 0 0 0 0
No. of families 10 13 7 3 8 6
Mann-Whitney U test). The trend of decreasing diversity with respect to time was found for
managed grasslands only. In managed sites compared in successive periods, lower index values
were found in the later period (P80% of all specimens collected on both natural and managed grasslands. According to the
estimations for period I, these families accounted for 50% of the spider community in natural
grasslands and for about 60% in managed grasslands (Table 6 and 7). The changes in
methods of spider collecting may have influenced and exaggerated these differences between
periods, but similar values were noted also in period II a, when the method of spider
collecting was similar to that used during period I. A decrease in the proportion of spiders
59

T a b l e 8. Correlation coefficients (r) (analysis of covariance)
between total spider density and environmental factors (Period
III).
Variable r F P
Soil moisture 0.337 67.292

which can determine spider abundance and community composition (DE KEER et al., 1989;
RUSHTON, EYRE, 1992; MAELFAIT et al., 1997; MERKENS, 1997). The other important factors
influencing spider density are management practice (DUFFEY, 1978; DE KEER et al., 1989;
DECLEER, 1990; RUSHTON, EYRE, 1992; MAELFAIT et al., 1997; MERKENS, 1997) and plant
complexity (DUFFEY, 1978). Authors have shown that certain species prefer managed or
unmanaged patches. In our data, the negative effect of mowing and grazing, on total spider
density and species richness is very clear. According to the results of this paper, plant species
diversity is less important for the diversity of spiders, than is plant complexity (abundance
of microhabitats in an area). This result is in an agreement with UETZ (1979), who
showed, experimentally, the relationship between spider density and litter thickness. He
considered litter complexity to be the primary factor influencing the structure of spider
communities. We observed a similar importance of the moss and litter layer in the range of
grasslands analysed in this paper.
Properties of dominant species
In all the grasslands compared, the family Linyphiidae was of greatest significance. Different
members of this family dominated in natural and managed grasslands, and there were
only a few common species (Appendix 1). Those dominating in managed grasslands can be
characterised according to HÄNGGI et al.(1995), as an eurytopic species. They are abundant
in arable fields, urban areas, fens, shrubs, permanent meadows and leys. The species dominant
in natural grasslands were categorised by HÄNGGI et al. (1995) as occurring in raised
bogs, fens, wet meadows and the shores of inland waters. Among them some endangered
species were found.
Mobility index
6
5
4
3
2
1
0
0,2
NB3
1
0,3
NA
2
0,52
NB1
3
0,92
MB1
4
1,09
MA1
5
Intensity of management
4,28
MC3
6
3,32
MB2
7
5,29
MC1
8
Fig. 1. Relationship between
mobility index (ratio of number
of ind. captured per pitfall trap
per 10 days to number of ind. per
m 2 ) and intensity of grassland
management. 1-8 – study sites;
symbols A,B,C denote peat origin
(explained in table 1), N –
natural grasslands, M – managed
grasslands.
61

A p p e n d i x 1. Species composition. Dd – dominant species in drained fens; Dn – dominant species in
natural fens; R – rare species
MIMETIDAE Meioneta affinis (KULC.)
Ero cambridgei KULC. R Meioneta rurestris (C.L. K.) Dd
THERIDIIDAE Meioneta tenera (MENGE)
Crustulina guttata (WIDER) Metopobactrus prominulus (O. P.-C.)
Enoplognatha ovata (CL.) Micrargus subaequalis (WEST.)
Euryopis flavomaculata (C. L. K.) Microlinyphia pusilla (SUND.)
Robertus arundineti (O. P.-C.) Microneta viaria (BL.)
Robertus insignis O. P.-C. R Notioscopus sarcinatus (O. P.-C.)
Robertus neglectus (O. P.-C.) Oedothorax apicatus (BL.)
Theridion bimaculatum (L.) Oedothorax fuscus (BL.)
Theridion sisyphium (CL.) Oedothorax gibbosus (BL.) Dn
LINYPHIIDAE Oedothorax retusus (WEST.)
Agyneta decora (O. P.-C.) R Pelecopsis parallela (WIDER)
Allomengea vidua (L. K.) Pocadicnemis juncea LOCK. ET MILL.
Aphileta misera (O. P.-C.) Pocadicnemis pumila (BL.)
Araeoncus crassiceps (WEST.) R Porrhomma pygmaeum (BL.) Dn
Araeoncus humilis (BL.) Savignya frontata BL. Dn
Baryphyma gowerense (LOCK.) R Silometopus elegans (O. P.-C.)
Baryphyma trifrons (O. P.-C.) R Silometopus reussi (TH.)
Bathyphantes approximatus (O. P.-C.) Tallusia experta (O. P.-C.)
Bathyphantes gracilis (BL.) Dn Taranucnus setosus (O. P.-C.)
Bathyphantes parvulus (WEST.) Tiso vagans (BL.) Dd
Bathyphantes setiger O. P.-C. Walckenaeria kochi (O. P.-C.)
Bolyphantes luteolus (BL.) Walckenaeria nodosa O. P.-C.
Carorita limnaea (CROS. ET BISH.) R Walckenaeria nudipalpis (WEST.)
Centromerita bicolor (BL.) Walckenaeria unicornis O. P.-C.
Centromerus incilium (L. K.) Walckenaeria vigilax (BL.)
Centromerus semiater (L. K.) TETRAGNATHIDAE
Centromerus sylvaticus (BL.) Pachygnatha clercki SUND.
Ceraticelus sibiricus ESKOV R Pachygnatha degeeri SUND. Dd
Ceratinella brevipes (WEST.) Tetragnatha extensa (L.)
Ceratinopsis stativa (SIMON) ARANEIDAE
Dicymbium nigrum (BL.) Dd Araneus quadratus CL.
Entelecara omissa O. P.-C. R Hypsosinga heri (HAHN)
Erigone atra BL. Dd Hypsosinga pygmaea (SUND.)
Erigone dentipalpis (WIDER) Dd Larinioides cornutus (CL.)
Erigone longipalpis (SUND.) Mangora acalypha (WALC.)
Glyphesis cottonae (LA TOUCHE) R Neoscona adianta (WALC.)
Gnathonarium dentatum (WIDER) Singa hamata (CL.)
Gongylidiellum murcidum SIMON Dn LYCOSIDAE
Hypomma bituberculatum (WIDER) Dn Alopecosa cuneata (CL.)
Kaestneria pullata (O. P.-C.) Alopecosa pulverulenta (CL.)
Lophomma punctatum (BL.) Arctosa leopardus (SUND.)
Maso gallicus SIMON R Hygrolycosa rubrofasciata (OHLE.)
62

A p p e n d i x 1.
Pardosa amentata (CL.) CLUBIONIDAE
Pardosa lugubris (WALC.) Clubiona diversa O. P.-C.
Pardosa maisa HIPPA ET MANN. R Clubiona rosserae LOCK. R
Pardosa paludicola (CL.) Clubiona stagnatilis KULC.
Pardosa palustris (L.) Dd Clubiona subtilis L. K.
Pardosa prativaga (L. K.) GNAPHOSIDAE
Pardosa pullata (CL.) Drassodes lapidosus (WALC.)
Pardosa sphagnicola DAHL Zelotes electus (C. L. K.)
Pirata latitans (BL.) Dn Zelotes latreillei (SIMON)
Pirata piraticus (CL.) Dn ZORIDAE
Pirata piscatorius (CL.) Zora armillata SIMON R
Pirata tenuitarsis SIMON Zora spinimana (SUND.)
Pirata uliginosus (TH.) Dn PHILODROMIDAE
Trochosa ruricola (DE GEER) Thanatus striatus C. L. K.
Trochosa spinipalpis (F. O. P.-C.) Tibellus maritimus (MENGE)
Xerolycosa miniata (C.L. K.) THOMISIDAE
PISAURIDAE Ozyptila gertschi KURA. R
Dolomedes fimbriatus (CL.) Ozyptila trux (BL.)
HAHNIIDAE Xysticus cristatus (CL.)
Antistea elegans (BL.) Dn Xysticus erraticus (BL.)
Hahnia pusilla C.L. K. Xysticus kochi TH.
DICTYNIDAE Xysticus ulmi (HAHN)
Argenna albopunctata (MENGE) R SALTICIDAE
Argenna subnigra (O. P.-C.) Evarcha falcata (CL.)
Dictyna arundinacea (L.) Heliophanus flavipes (HAHN)
Dictyna uncinata TH. Neon reticulatus (BL.)
LIOCRANIDAE Neon valentulus FALC. R
Agraecina striata (KULC.) Phlegra fasciata (HAHN)
Agroeca dentigera KULC. R Sitticus caricis (WEST.)
Sitticus floricola (C.L. K.)
Spiders occurring in natural fens are less mobile than those from managed grasslands.
Mobility index values are

The diversity and density of spiders increase with soil moisture, and abundance of microhabitats
in the ecosystem. They decrease with intensity of management, soil compactness, and
increasing distance to shrubs. The diversity of spiders is hardly affected by plant species diversity.
Diversity and density of spider communities can be improved by leaving grassland margins
uncut and by increasing the heterogeneity of the landscape.
References
ANDRZEJEWSKA, L., 1991: Formation of Auchenorrhyncha communities in diversified structures of agricultural
landscape? Pol. Ecol. Stud., 17, p. 267-287.
DECLEER, K., 1990: Experimental cutting of remarsh vegetation and its influence on the spider (Araneae) fauna
in the Blankaart Nature Reserve, Belgium. Biol. Conserv., 52., p. 161-185.
De KEER, R., ALDERWEIRELDT, M., DECLEER, K., SEGERS, H., DESENDER, K., MAELFAIT, J.-P., 1989: Horizontal
distrbution of the spider fauna of intensively grazed pastures under the influence of diurnal activity and grass
height. J. Appl. Ent., 107, p. 455-473.
DUFFEY, E. 1978: Ecological strategies in spiders including some characteristics of spiders in pioneer and mature
habitats. Symp.zool. Soc. Lond., 42, p. 109-123.
HÄNGGI, A., STÖCKLI, E., NENTWIG, W., 1995: Lebensräume mitteleuropäischer Spinnen – Habitats of Central
European spiders. Misc. Faun. Helvet., 4, p. 1-459.
KACZMAREK, M., 1991: Characteristics of the studied habitats in the Biebrza and Narew Old River Valleys. Pol.
ecol Stud., 17, p.7-18.
KAJAK, A., 1960: Changes in the abundance of spiders in several meadows. Ekol. pol., Ser.A, 9, p. 1-30.
KAJAK, A., 1962: Comparison of spider fauna in artificial and natural meadows. Ekol. pol., Ser.A, 1, p. 1-20.
KAJAK, A., 1987: Long term changes in the composition of grassland spiders and attempt to estimate role of
epigeic species. Zpravodaj ochrany prirody mesta Ostravy, p. 45-59. (In Polish)
KAJAK, A.,1993: Long-term changes in spider communities of drained fens. In FŰRST, P.-A., MULHAUSER, G. (eds):
XIIe Colloque Européen d’Arachnologie (116), Fascicule 1, p.125-131.
KAJAK, A., KACZMAREK, M., 1994: Could wetland soil fauna be restored after restoration of fen habitats? In JANKOW-
SKA-HUFLEJT, H., GOLUBIEWSKA, E. (eds): Proc. Int. Symposium Conservation and management of fens, p. 428-436.
KAMIŃSKI, J.: Assessment of long tern changes in plant communities in natural and cultivated peat grasslands in
the Biebrza Valley. Pol. J. Ecol. (in press)
KOTOWSKA, J., PASTERNAK-KUŚMIERSKA, D., WILPISZEWSKA, I., 1998: Comparative analysis of hay-growing meadows
on peat muck soils. Pol. ecol. Stud., 22, p. 141-159.
MALEFAIT, J.-P., BAERT, L., DESENDER, K., 1997: Effects of groundwater catchment and grassland management on
the spider fauna of the dune Nature Reserve ’De Westhoek’ (Belgium). In ŻABKA, M. (ed.): Proc.16 th Europ.
Coll. Arachnol., Siedlce, 1996, p. 221-236
MERKENS, S., 1997: Influence of environmental factors on the community structure of spiders in a humidity
gradient of extensively managed, moist pastures. In ŻABKA, M. (ed.): Proc.16 th Europ. Coll. Arachnol., Siedlce,
1996, p. 237-248.
OKRUSZKO, H., 1990: Wetlands of the Biebrza Valley their value and future management. PAS, Warszawa, 107 pp.
PASTERNAK-KUŚMIERSKA, D., WILPISZEWSKA, I., CIEŚLEWICZ, M., 1997: Structure and dynamics of plant biomass on
drained peatlands of different peat origin (Inc. marginal valley of Biebrza River – Poland). Ekol. pol., 45, p.
395-422.
RUSHTON, S.P., EYRE, M.D., 1992: Grassland spider habitats in north-east England. Journal of Biogeography, 19,
p. 99-108.
STEPA, T., PAŁCZYŃSKI, A.1991: Effect of ecological zonation on diversification of soil conditions at various plant
associations in the Biebrza Valley. Pol. ecol. Stud., 17, p.19-33.
SZUNIEWICZ, J., CHRZANOWSKI, S.: Assessment of changes in moisture content in peat soils of natural and drained
grasslands in the Biebrza Valley. Pol. J. Ecol. (in press)
UETZ, G.W., 1979: The influence of variation in litter habitats on spider communities. Oecologia (Berlin), 40, p.
29-42.
64

Ekológia (Bratislava) Vol. 19, Supplement 4, 65-77, 2000
HARVESTMEN AND SPIDERS IN THE AUSTRIAN
WETLAND “HÖRFELD-MOOR”
(ARACHNIDA: OPILIONES, ARANEAE)
CHRISTIAN KOMPOSCH
Ökoteam - Institute of Faunistics and Animal Ecology, Bergmanngasse 22, 8010 Graz, Austria.
Introduction
Abstract
Komposch C.: Harvestmen and spiders in the Austrian wetland “Hörfeld-Moor” (Arachnida:
Opiliones, Araneae). In GAJDOŠ P., PEKÁR S. (eds): Proceedings of the 18th European Colloquium
of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava), Vol. 19, Supplement 4/2000, p. 65-77.
Aspects of the fauna of the montane wetland „Hörfeld-Moor“ were investigated with regard to
taking an inventory of the nature reserve and determining its conservation value. The harvestmen
and spider fauna was studied by means of pitfall traps, light-traps, soil-sifter and hand-collecting
in nine sample areas representing typical biotope types within the wetland: alder forest, willow
shrub, hay meadow, moist meadow, sedge swamp, reed bed, meadowsweet fen, floating mat and
raised bog. The following noteworthy arachnids were found: Nemastoma schuelleri, Opilio dinaricus,
Platybunus pinetorum, Enoplognatha caricis, Diplocephalus helleri, Drepanotylus uncatus,
Maro lepidus, Pardosa fulvipes, Pirata tenuitarsis, Clubiona germanica and Gnaphosa nigerrima.
19 of the spider species found are new to Carinthia. An interesting result is the
attractiveness of light-traps for particular harvestmen and spider species.
The percentage of endangered arachnid species was not related to either the diversity and evenness
indices of the investigated biotope types or with the percentage of endangered plant species.
Furthermore, the present analysis is a useful approach for applying zoological results obtained in
particular places to an entire area.
Fens belong to the most endangered biotope types of Central Europe. The Hörfeld-Moor
is one of the largest near-natural fens of Austria. It has carried the status of a nature reserve
since 1984 (Carinthia) and 1987 (Styria) respectively. In 1996 it became a Ramsar-area and
it has been suggested as a Natura 2000-area.
The arachnid fauna from Austrian wetlands is still poorly known; moreover only few
data are available from wetlands above 900 metres altitude. The results are part of an integrated
monitoring programme of the development of the ecosystem, including fauna and
vegetation. Faunistical investigations have been carried out on Opiliones, Araneae, Odonata,
65

T a b l e 1. Floral characterisation of the investigated biotope-types.
no abbr. biotope type characterisation
Auchenorrhyncha, Heteroptera (FRIESS, 1998), Coleoptera (Carabidae, Staphylinoidea) and
Lepidoptera (HUEMER, WIESER, 1997) and vertebrates. The aim of the project is to prepare
an inventory and evaluation of the nature reserve to derive recommendations for biotope
management.
Study area
The area of investigation is the wetland „Hörfeld-Moor“ which extends over 133 hectares
at a height of 930 metres in the Gurktaler Alps, a southern part of the Central Alps (S
Mühlen, N Hüttenberg, Carinthian and Styrian border, Austria; 47°00‘N, 14°30-31‘E).
Material and methods
The arachnid fauna was studied by means of pitfall traps, light-traps, soil-sifter and hand-collecting in the
vegetation period of 1996. Four pitfall traps in each biotope type were exposed from May until October: Data for
harvestmen come from the whole period, but spider material was determined only from May/June (1.05.-
13.06.1996)., because of the large amount of effort needed to process the samples. Faunistical investigations
were carried out in nine representative biotope types (Table 1).
66
1 Alnus Alder forest
Alnus incana dominates the tree layer, Scirpus sylvaticus, Caltha
palustris, Filipendula ulmaria
A late stage of succession of a former hay meadow: Salix cinerea, S.
2 Salix Willow shrub repens, Betula pendula, B. pubescens beside a species spectrum similar
to the moist meadow (4)
3
smead
Hay meadow
Typical species of fresh meadows: Holcus lanatus, Scirpus sylvaticus,
Ranunculus acris, Juncus effusus, Leucanthemum vulgare, Cirsium
palustre
4 m-
The cultivation of this oligotrophic meadow with a high species richness
mead
Moist meadow
ended a few years ago: Carex acutiformis, C. paniculata, C. rostrata,
Molinia coerulea, Menyanthes trifoliata, Persicaria bistorta, Briza
media, Potentilla erecta, Succisa pratensis
5 Carex Sedge swamp
Formed as a floating mat on an acidic and oligotrophic substrate: Carex
rostrata in high dominance, partly with hillocks of Carex elata
6 Phrag Reed bed
Large reed beds (Phragmites australis) with Carex elata-hillocks in
between
7 fen Meadowsweet fen Dominated by Filipendula ulmaria
8 float Floating mat
Dominated by Menyanthes trifoliata, Potentilla palustris, Carex
paniculata, Carex rostrata, Caltha palustris
A very small hummock area with mire spruces (Picea abies),
9 bog Raised bog Eriophorum vaginatum, Vaccinium oxycoccos, Drosera rotundifolia,
Andromeda polifolia, Vaccinium vitis-idaea

Beside biotopes and vegetation, parameters like soil type, water budget, distance from the ground water,
cover of the herb-, shrub- and tree layer, thickness of the litter etc. were mapped in the whole area. The present
analysis includes, in total, 13 harvestmen (209 specimens) and 111 spider species (2150 specimens).
Results
Method comparison
It is a well-known fact, that the use of pitfall traps, soil-sifter and hand-collecting leads to
a distinct species-spectrum; consequently every zoological inventory of a richly-structured area
requires the application of different sampling-methods. The attractiveness of light-traps for
particular harvestmen and spider species results in an interesting and characteristic coenosis of
phalangiids, theridiids, linyphiids, tetragnathids, araneids, pisaurids, gnaphosids and clubionids.
10 to 25% of the harvestmen and spider species of the Hörfeld-area were caught exclusively by
light-traps (the low intensity of hand collecting must be mentioned). In the present case lighttraps
caught rarely-collected arachnids such as Opilio dinaricus ŠILHAVÝ, Enoplognatha caricis
(FICKERT), Cheiracanthium punctorium (VILLERS) and Clubiona germanica THORELL.
Species assemblages
Regarding the harvestmen-coenosis the dominance of Nemastoma schuelleri GRUBER ET M.
in the litter of the alder forests and of Mitopus morio (FABRICIUS) in the raised bog is noteworthy;
this phalangiid is a very common species in montane and alpine zones above 1 500 metres but
rather sporadic in lower regions of the Eastern Alps. The phenotype of M. morio (with its white
stripe on the opisthosoma) from the cold bog – the temperature figure sensu ELLENBERG (1979)
T = 3, – is similar to those of specimens of altitudes above 1 500/2 000 metres.
The spider assemblages are characterised by the occurrence of hygro- and hydrophilous
lycosids and linyphiids. The most frequent species in this area is Pirata hygrophilus THORELL,
and the floating mat seems to be the optimal habitat for Pirata piscatorius (CLERCK). The
sympatric occurrence of Trochosa terricola THORELL and Trochosa spinipalpis (F. O. P.-
CAMBRIDGE) forms the spider-coenosis of the raised bog.
Cluster analysis
The hierarchical cluster analysis of harvestmen-coenoses based on species and dominance
identity show both the isolated position of the raised bog (9) and a similarity between
alder forests (1) and meadowsweet fens (7). Analysis of spider-coenoses led to a similar
picture regarding the status of the raised bog. Concerning species identity a cluster of all
wet biotope types is noticeable (Fig. 2); the dendrogram based on the dominance identity
accentuates the high- and low vegetation associations willow shrub (2) - meadowsweet fen
(7) and sedge swamp (5) - floating mat (8) respectively.
67

40 40% -20% 20 0% 0 %
20% 20
40% 40 60% 60 80% 80 100 100%
68
pitfall traps
light traps
soil-sift. &
hand-coll.
similarity
0
10
20
30
40
50
60
70
80
90
100
5
8
9
3
2
1
1/ 31
3/ 12
1/ 28
O piliones Araneae
% 7
fen
8
float
5
Carex
6
Phrag
19
35
2
Salix
39
3
s-mead
exclusiv.
rest
Fig. 1. Comparison of sampling methods: percentage of species recorded exclusively by pitfall traps, light-traps,
soil-sifter and hand-collecting.
4
m-mead
1
Alnus
Fig. 2. Hierarchical cluster analysis of spider-coenoses based on species identity. Dendrogram using Average
Linkage (between groups) and Sörensen´s quotient of similarity.
9
bog

The majority of harvestmen recorded are eurytopic species; the single record of the
forest-inhabiting phalangiid Platybunus pinetorum (C. L. KOCH) in the hay meadow (3) can
be regarded as an artefact. A richness of spider species in combination with a high percentage
(58-73%) of endangered species is demonstrated for the biotope types floating mat (8),
reed bed (6), meadowsweet fen (7) and sedge swamp (5) (Fig. 3); low values are presented
for the moist meadow (4) and the small raised bog (9).
High values concerning the evenness of the spider-communities show the alder forests
(1), sedge swamps (5) and floating mats (8); the low value of the meadowsweet fen (7) is
caused by the dominance of P. hygrophilus (51%).
number of species
40
30
20
10
0
1
Alnus
2
Salix
3 4
s-mead m-mead
Aspects of nature conservation value
5
Carex
6
Phrag
The percentage of endangered arachnid species (Table 5, 6, Fig. 3) shows no relationship
with the diversity and evenness indices of the investigated biotope types (Table 5, 6) or
with the percentage of endangered plant species (Fig. 4). Fig. 4 shows high divergences in
the percentage of endangered species within one sample area between floristic and faunistic
aspects, between zoophagous and phytophagous taxa (e.g. Araneae - Auchenorrhyncha)
and even within zoophagous groups (e.g. Araneae - Carabidae). Striking differences between
zoological and botanical results are obvious if we look at reed beds (6) and the raised
bog (9). The Phragmites australis - “monoculture” contains a high diversity of carnivorous
arthropods, the floristically interesting bog presents a contrary picture. The lack of endan-
7
fen
rest (n=71)
red data-list species (n=40)
Fig. 3. Number of endangered spider species and total number of species of each sample area/biotope type.
8
float
9
bog
69

T a b l e 2. Ecological characterisation of western Central Europe with regard to distinct environmental
factors (ELLENBERG, 1979) and total number of plant species in the specific sample areas.
70
1
Alnus
2
Salix
3
s-mead
4
m-mead
5
Carex
6
Phrag
7
fen
8
float
Light value (L) 5.6 7.1 6.8 6.8 8.1 6.7 6.6 7.3 8.1
Temperature value (T) 4 3.4 5 3.8 4 4.8 5 5 3
Continentality value (K) 4.4 5.1 3.8 4 * 3.5 4.5 4.5 5.3
Moisture value (F) 7.2 8.3 6.5 7.5 9.8 8.8 7.7 8.7 6.9
Reaction value (R) 6.6 4.5 5.7 5.7 4 6.3 6 6 1.2
Nitrogen value (S) 4.9 3.7 4.7 3.8 4.1 5.4 5.5 4.1 1.1
number of plant species 20 14 24 31 4 10 14 13 11
T a b l e 3. List of collected harvestmen species. The number of specimens in each biotope type is given. The
total number of specimens and number caught by different collecting methods (pt: pitfall trap, ss: soil-sifter,
hc: hand-collecting, lt: light-trap) are also given. Systematics after MARTENS (1978).
Alnus
Salix
s-mead
m-mead
Carex
Phrag
fen
float
bog
method
family / species 1 2 3 4 5 6 7 8 9 total pt ss hc lt
NEMASTOMATIDAE
Nemastoma schuelleri GR. ET M. 29 1 30 12 16 2
Nemastoma triste (C. L. K.) 3 3 3
Paranemastoma
quadripunctatum (PANZ.)
PHALANGIIDAE
4 1 1 2 9 17 10 4 3
Amilenus aurantiacus (SIMON) 12 12 12
Lacinius ephippiatus (C. L. K.) 4 4 3 1
Lophopilio palpinalis (HERB.) 4 1 2 1 8 4 1 2 1
Mitopus morio (FABR.) 1 39 40 4 36
Nelima semproni SZAL. 1 1 1
Oligolophus tridens (C. L. K.) 28 1 1 3 5 3 41 11 11 16 3
Opilio dinaricus ŠILH. 3 3 3
Phalangium opilio L. 4 7 2 2 1 11 27 14 3 10
Platybunus pinetorum (C. L. K.) 1 1 1
Rilaena triangularis (HERB.) 7 5 2 5 2 1 22 7 5 7 3
Total 76 9 12 3 5 5 15 16 68 209 62 41 37 69
gered arachnids and insects in the raised bog could be caused by the very low size and
isolation of this area. NEET (1996) shows a significant correlation between the number of
tyrphobiont spider species influenced by habitat-size.
9
bog

percentage of endangered species
80
70
60
50
40
30
20
10
0
Opiliones
Araneae
Carabidae
Auchenorrhyncha
Spermatophyta
1
Alnus
2
Salix
3
s-mead
4
m-mead
5
Carex
Low-scale mapping versus high-scale evaluation?
6
Phrag
Fig. 4. Percentage of endangered species of Carinthia of each sample area/biotope type: Opiliones, Araneae,
Carabidae, Auchenorrhyncha, Spermatophyta.
Fig. 5. Potential map of distribution of Nemastoma schuelleri (dark areas), a litter inhabiting harvestman of
alder forests in the “Hörfeld-Moor”.
Due to the large amount of time and effort involved, faunistical data concerning
arthropods in general are derived from point sampling. A detailed zoological and botanical
analysis of representative biotope types combined with mapping of biotopes
7
fen
8
float
9
bog
71

and relevant structural parameters for the whole area can be calculated by modern software
(GIS) to map the potential distribution of selected stenotopic and sensitive
bioindicators (Fig. 5). This method should be regarded as an instrument of estimating
distribution and apparent abundance as well as evaluating divisions and biotopes of
large areas.
Further investigations would be worthwhile to check the similarities between potential
maps of distribution of the particular species with the actual one.
Notes on selected species
Nemastoma schuelleri - This endemic species of the Eastern Alps is very numerous in
alder forests.
Opilio dinaricus - This rarely collected phalangiid shows that crepuscular and not epigeic
animals seem to be under-represented in the majority of arachnological studies; there are
multiple records from Carinthia by means of light-traps.
Platybunus pinetorum - This forest inhabiting species is one of the rarest harvestmen of
southern Austria (KOMPOSCH, 1999) whereas in the Bavarian Alps it is much more common
(MUSTER, in litt.).
Enoplognatha caricis - The third record for Austria (KOMPOSCH, 1995a; ROTH, 1999: sub
E. tecta) of this endangered theridiid was made (using a light-trap ) on the 10 th June with
one male in the sedge swamp. The nomenclature follows RŮŽIČKA, HOLEC (1998).
Diplocephalus helleri (L. KOCH) - Constant occurrence in the high-alpine and nival zone
(THALER, 1992; THALER, KNOFLACH, 1997); the author knows of two further records on the
Styrian rivers Enns and Teigitsch between 520 and 635 m. In the Hörfeld-Moor one male
was found in the litter of the alder forest.
Drepanotylus uncatus (O. P.-CAMBRIDGE) and Maro lepidus CASEMIR - Tyrphobiont species
of the alder forest and reed bed (compare NEET, 1996).
Pardosa fulvipes (COLLET) - „Perhaps fulvipes has in some degree been overlooked within
its area of distribution“ (HOLM, KRONESTEDT, 1970: 423). This seems to be confirmed by
another record in Carinthia west of Spittal a.d. Drau (STEINBERGER, in litt.).
Pirata tenuitarsis SIMON - The few records from Austria (Northern Tyrol, Vorarlberg,
Styria) are probably due to confusion with the sibling species P. piraticus (BUCHAR, THALER,
1997).
Clubiona germanica - A rare (collected ?) clubionid with an Eurosiberian distribution
(MIKHAILOV, 1992).
Gnaphosa nigerrima L. KOCH - In the Hörfeld-Moor this endangered species shows a high
habitat preference for the Menyanthes - floating mat. A recent record in the Wörschacher
Moor in Styria/Austria shows it occurs on hummocks in a former peat cutting area (RUPP,
1999).
72

Discussion
The species spectrum of the Hörfeld-Moor is far from a complete inventory, but it could
be regarded as a representative survey of the arachnocoenoses of this area. In comparison
THALER (in LÖSER et al., 1982) published 158 spider species from the Bavarian nature reserve
„Murnauer Moos“, RUPP (1999) recorded 119 spider species from the Styrian bog
area “Wörschacher Moor” in Eastern Austria. 19 species are new to Carinthia (see Table 4)
- so the total number of currently known species of this southern federal country of Austria
is 610 (KOMPOSCH, STEINBERGER, 1999). This high number of first recorded species is due to
the insufficient knowledge about southern Austrian wetlands - the Hörfeld-Moor is the third
investigated wetland of Carinthia after the Sablatnigmoor (KOMPOSCH, 1995b) and the
Bleistätter Moor/Ossiacher See (KOMPOSCH, unpubl.) - as well as to the location of species
rare all over Central Europe.
Modern conservation work needs both stenotopic and sensitive bioindicators as conservation
tools and striking flagship species, which may even become symbols and leading
elements of entire conservation campaigns (compare MILASOWSZKY, ZULKA, 1998). Potential
flagship species of the Hörfeld area are the spiders Araneus alsine (WALCKENAER), Pirata
piscatorius, Dolomedes fimbriatus (CLERCK) and Gnaphosa nigerrima. Close cooperation
between botanists and zoologists seems to be a basic requirement for effective nature conservation
work. Inventories of selected arthropod groups lead to precise and detailed statements
on small-scale areas in general. Connected with results of vertebrate investigations,
geological, botanical, vegetational and structural mappings, a comprehensive picture and
conservation value for the whole area can be given. A conservation value and derived recommendations
for biotope management taking the complexity and patch connectivity of
ecosystems into consideration has to be based on adequate data of a representative spectrum
of investigated taxa - both zoophagous and phytophagous indicator groups.
Acknowledgements
I am grateful to Dr K. Thaler for help with identification, Dr W. E. Holzinger for discussion and the
“Naturschutzverein Hörfeld-Moor”, especially mayor R. Schratter and Mag K. Krainer for their interest and
financial assistance. Dr G. Egger and Mag M. Jungmeier kindly made the botanical data and maps of potential
distribution available, Dr J. Dunlop helped to improve the English of the manuscript. Thanks to Mag T. Friess,
Mag B. Komposch, Dr L. Neuhäuser-Happe, Mag W. Paill and Dr C. Wieser, who provided me with arachnid
material.
73

T a b l e 4. List of collected spider species. An asterisk (*) denotes species which are new to the fauna of Carinthia. The number of specimens in each
biotope type is given. The total number of specimens and number caught by different collecting methods (pt: pitfall trap, ss: soil-sifter, hc: handcollecting,
lt: light-trap) are also given. Systematics after KOMPOSCH, STEINBERGER (1999).
74
Alnus
Salix
s-mead
m-mead
Carex
Phrag
fen
float
bog
method
family / species 1 2 3 4 5 6 7 8 9 total pt ss hc lt
THERIDIIDAE
Crustulina guttata (WIDER) 1 1 1
Enoplognatha ovata (CL.) 1 2 3 3
Enoplognatha caricis (FICK.) 1 1 1
Episinus angulatus (BL.) 1 1 1
Euryopis flavomaculata (C. L. K.) 2 2 1 1
Robertus lividus (BL.) 1 1 1
Robertus scoticus JACK. 6 6 6
Robertus truncorum (L. K.) 1 1 1
Theridion sisyphium (CL.) 1 1 1
LINYPHIIDAE
Agyneta cauta (O. P.-C.) 2 1 1 1 5 4 1
Araeoncus crassiceps (WEST.)* 1 25 1 6 38 71 71
Bathyphantes approximatus (O. P.-C.)* 1 1 4 3 2 2 13 4 2 7
Bathyphantes nigrinus (WEST.) 11 1 1 3 16 7 7 2
Bathyphantes gracilis (BL.) 1 1 1
Bolyphantes alticeps (SUND.) 1 1 1
Centromerus arcanus (O.P.-C.)* 4 4 2 2
Centromerus levitarsis (SIMON)* 1 1 1 1 1 1 6 4 2
Centromerus pabulator (O. P.-C.) 1 1 1
Centromerus sylvaticus (BL.) 1 1 2 2
Ceratinella brevipes (WEST.) 4 1 5 5
Ceratinella brevis (WIDER) 1 1 1
Cnephalocotes obscurus (BL.)* 1 1 1
Dicymbium brevisetosum LOCK. 1 1 1
Diplocephalus helleri (L. K.) 1 1 1
Diplocephalus latifrons (O. P.-C.) 2 2 2
Diplostyla concolor (WIDER) 2 2 1 1
Dismodicus bifrons (BL.) 1 1 2 1 1
Drepanotylus uncatus (O. P.-C.)* 2 7 9 1 5 3
Entelecara congenera (O. P.-C.) 1 1 1
Erigone atra BL. 3 3 3
Erigone dentipalpis (WIDER) 5 4 9 9
Erigonella hiemalis (BL.) 1 1 1
Erigonella ignobilis (O. P.-C.)* 1 9 8 18 18
Floronia bucculenta (CL.) 1 1 2 1 1
Gnathonarium dentatum (WIDER)* 5 5 2 2 1
Helophora insignis (BL.) 16 16 4 5 7
Hypomma bituberculatum (WIDER) 1 1 9 11 8 3
Linyphia triangularis (CL.) 4 9 13 9 4
Lophomma punctatum (BL.)* 2 4 7 4 17 9 8
Maro lepidus CASE.* 2 2 2
Maso sundevalli (WEST.) 1 1 1
Neriene clathrata (SUND.) 1 1 1
Oedothorax apicatus (BL.) 1 1 1
Oedothorax fuscus (BL.) 1 1 1
Oedothorax gibbosus (BL.) 21 28 43 15 107 106 1
Oedothorax retusus (WEST.) 1 1 1
Pelecopsis elongata (WIDER) 5 5 5
Pocadicnemis pumila (BL.) 2 2 2
Porrhomma oblitum (O. P.-C.)* 1 1 1
Silometopus elegans (O. P.-C.)* 1 2 2 3 44 52 52
Tallusia experta (O. P.-C.)* 1 1 2 4 2 2
Tapinocyba insecta (L. K.) 4 4 4
Walckenaeria alticeps (DENIS) 4 4 4
Walckenaeria atrotibialis (O. P.-C.) 1 1 1
Walckenaeria kochi (O. P.-C.) 1 1 8 2 12 10 2
Walckenaeria nudipalpis (WEST.)* 1 2 3 2 1
TETRAGNATHIDAE
Metellina segmentata (CL.) 2 2 2
Pachygnatha clercki SUND. 8 2 1 44 2 2 59 17 1 5 36
Pachygnatha degeeri SUND. 37 37 37
Pachygnatha listeri SUND. 4 21 1 26 21 2 3

T a b l e 4./Cont.
Alnus
Salix
s-mead
m-mead
Carex
Phrag
fen
float
bog
method
family / species 1 2 3 4 5 6 7 8 9 total pt ss hc lt
Tetragnatha extensa (L.) 3 2 2 1 3 11 5 6
Tetragnatha montana SIMON 1 1 1 3 1 1 1
Tetragnatha pinicola L. K. 1 1 1
ARANEIDAE
Aculepeira ceropegia (WALC.) 1 1 1
Araneus alsine (WALC.) 1 1 2 1 1
Araneus diadematus CL. 1 1 1
Araneus marmoreus CL. 1 1 1
Araneus quadratus CL. 1 2 1 4 1 9 5 4
Araneus sturmi (HAHN) 1 1 1
Hypsosinga heri (HAHN) 3 1 1 5 4 1
Hypsosinga pygmaea (SUND.) 4 4 4
Larinioides patagiatus (CL.) 1 1 1
LYCOSIDAE
Alopecosa cuneata (CL.) 1 1 1
Alopecosa pulverulenta (CL.) 75 6 81 81
Alopecosa trabalis (CL.) 1 1 2 2
Pardosa amentata (CL.) 2 21 14 4 68 8 117 113 4
Pardosa fulvipes (COLL.)* 3 1 2 1 21 31 59 59
Pardosa paludicola (CL.) 1 1 1
Pardosa palustris (L.) 138 2 1 141 141
Pardosa prativaga (L. K.) 1 1 7 9 8 1
Pardosa pullata (CL.) 132 1 133 133
Pirata hygrophilus TH. 12 46 5 5 80 236 28 13 425 414 10 1
Pirata latitans (BL.) 1 1 1 3 3
Pirata piraticus (CL.) 19 1 20 20
Pirata piscatorius (CL.) 1 3 8 53 65 63 2
Pirata tenuitarsis SIMON* 4 5 47 3 22 81 79 2
Trochosa ruricola (DE GEER) 20 1 1 22 21 1
Trochosa spinipalpis (F. O. P.-C.) 13 11 12 2 8 29 75 74 1
Trochosa terricola TH. 1 1 39 41 39 1 1
PISAURIDAE
Dolomedes fimbriatus (CL.) 2 2 12 3 22 33 3 77 57 1 19
Pisaura mirabilis (CL.) 1 3 2 2 8 1 7
AGELENIDAE
Histopona torpida (C. L. K.) 1 1 1
HAHNIIDAE
Antistea elegans (BL.) 2 2 2
Cryphoeca silvicola (C. L. K.) 2 2 2
AMAUROBIIDAE
Callobius claustrarius (HAHN) 1 1 1
CLUBIONIDAE
Cheiracanthium punctorium (VILL.) 2 2 2
Clubiona germanica TH.* 1 1 1
Clubiona lutescens WEST. 8 1 4 13 2 1 1 9
Clubiona phragmitis C. L. K. 1 4 1 25 1 32 1 16 15
Clubiona reclusa O. P.- C. 1 8 1 7 1 18 3 15
Clubiona stagnatilis KULC. 5 6 11 1 7 3
GNAPHOSIDAE
Gnaphosa nigerrima L. K.* 2 8 10 10
ZORIDAE
Zora spinimana (SUND.) 2 1 2 2 7 3 4
THOMISIDAE
Ozyptila trux (BL.) 2 7 4 13 11 2
Xysticus bifasciatus C. L. K. 2 1 3 3
Xysticus cristatus (CL.) 13 1 14 13 1
Xysticus ulmi (HAHN)* 2 6 4 12 6 6
SALTICIDAE
Evarcha arcuata (CL.) 4 4 4
Evarcha falcata (CL.) 1 1 1
Neon reticulatus (BL.) 2 2 2
Sitticus floricola (C. L. K.) 1 4 3 1 8 17 2 15
Total 87 142 479 60 106 309 462 375 130 2150 1780 65 157 148
75

T a b l e 5. Number of species, diversity, evenness (Shannon index), and percentage of endangered species
and dominant harvestman species (> 5 specimens) of the specific sample areas, and total number and average
for the whole area of investigation.
76
No
sp.
div. even.
%
endang.
sp.
dominant species
1 Alnus 6 1.42 0.79 17 N. schuelleri (38%), O. tridens (37%), R. triangularis (9%)
2 Salix 2 – – 0
3 s-mead 6 1.35 0.75 17 P. opilio (58%)
4 m-mead 2 – – 0
5 Carex 3 – – 0
6 Phrag 3 – – 0
7 fen 5 1.45 0.90 20 O. tridens (33%), R. triangularis (33%)
8 float 3 0.83 0.76 0 P. opilio (69%)
9 bog 7 1.29 0.66 0 M. morio (57%), A. aurantiacus (18%), P. quadripunctatum (13%)
Total 13 – – 15
average 4 1.27 0.77 6
T a b l e 6. Number of species, diversity, evenness (Shannon index), percentage of endangered species and
dominant spider species of the specific sample areas, and total number and average for the whole area of
investigation.
No
sp.
div. even.
%
endang.
sp.
dominant species
1 Alnus 33 2.93 0.84 39 H. insignis (18%), P. hygrophilus (14%), B. nigrinus (13%)
2 Salix 29 2.52 0.75 48 P. hygrophilus (32%), O. gibbosus (15%), T. spinipalpis (9%)
3 s-mead 26 2.02 0.62 31 P. palustris (29%), P. pullata (28%), A. pulverulenta (16%)
4 m-mead 15 2.09 0.77 33 P. listeri (35%), T. spinipalpis (20%), A. pulverulenta (10%)
5 Carex 27 2.75 0.83 67 A. crassiceps (24%), P. amentata (13%), D. fimbriatus (11%)
6 Phrag 30 2.44 0.72 73 P. hygrophilus (26%), P. tenuitarsis (15%), P. clercki (14%)
7 fen 33 1.89 0.54 58 P. hygrophilus (51%), P. amentata (15%), O. gibbosus (9%)
8 float 39 2.96 0.81 59 P. piscatorius (14%), S. elegans (12%), A. crassiceps (10%)
9 bog 24 2.34 0.74 17 T. terricola (30%), T. spinipalpis (22%), P. hygrophilus (10%)
total 111 – – 36
average 28 2.44 0.74 47

References
BUCHAR, J., THALER, K., 1997: Die Wolfspinnen von Österreich 4 (Schluß): Gattung Pardosa max.p. (Arachnida,
Araneae: Lycosidae) - Faunistisch-tiergeographische Übersicht. Carinthia II, 187, 107, p. 515-539.
ELLENBERG, H., 1979: Zeigerwerte der Gefäßpflanzen Mitteleuropas. Scripta Geobotanica, 9, 122 pp.
FRIESS, T., 1998: Die Wanzen (Heteroptera) des Naturschutzgebietes Hörfeld-Moor (Kärnten/Steiermark). Carinthia
II, 188, 108, p. 589-605.
HOLM, A., KRONESTEDT, T., 1970: A taxonomic study of the wolf spiders of the Pardosa pullata-group (Araneae,
Lycosidae). Acta ent. bohemoslov., 67, p. 408-428.
HUEMER, P., Wieser, C., 1997: Bemerkenswerte Nachweise von Schmetterlingen im Hörfeldmoor (Lepidoptera).
Carinthia II, 187, 107, p. 401-408.
KOMPOSCH, C., 1995a: Enoplognatha tecta (Keyserling) und Tetragnatha shoshone Levi neu für Österreich.
(Araneae: Theridiidae, Tetragnathidae). Carinthia II, 185, 105, p. 729-734.
KOMPOSCH, C., 1995b: Spinnen (Araneae). In WIESER, C., MILDNER, P., KOFLER, A. (eds): Naturführer Sablatnigmoor.
Verl. Naturwiss. Ver. Kärnten, Klagenfurt, p. 75-89.
KOMPOSCH, C., 1999: Rote Liste der Weberknechte Kärntens. Naturschutz in Kärnten, 15, p. 547-565.
KOMPOSCH, C., STEINBERGER, K.-H., 1999: Rote Liste der Spinnen Kärntens. Naturschutz in Kärnten, 15, p. 567-618.
LÖSER, S, MEYER, E., THALER, K., 1982: Laufkäfer, Kurzflügelkäfer, Asseln, Webespinnen, Weberknechte und
Tausendfüßer des Naturschutzgebietes “Murnauer Moos” und der angrenzenden westlichen Talhänge (Coleoptera:
Carabidae, Staphylinidae; Crustacea: Isopoda; Aranei; Opiliones; Diplopoda). Entomofauna, Suppl.
1, p. 369-446.
MARTENS, J., 1978: Spinnentiere, Arachnida: Weberknechte, Opiliones. In SENGLAUB, F., HANNEMANN, H.J., SCHU-
MANN, H. (eds): Die Tierwelt Deutschlands, 64, Jena, 464 pp.
MIKHAILOV, K.G., 1992: The spider genus Clubiona Latreille, 1804 (Arachnida, Aranei, Clubionidae) in the
USSR fauna: a critical review with taxonomical remarks. Arthropoda Selecta, 1, p. 3-34.
MILASOWSZKY, N., ZULKA, K.P., 1998: Habitat requirements and conservation of the „flagship species“ Lycosa
singoriensis (Laxmann 1770) (Araneae: Lycosidae) in the National Park Neusiedler See-Seewinkel (Austria).
Z. Ökologie u. Naturschutz, 7, p. 111-119.
NEET, C.R., 1996: Spiders as indicator species: lessons from two case studies. In MAHNERT, V. (ed.): Proceedings
of the XIII th International Congress of Arachnology. Geneva, 1995. Revue suisse de Zoologie, hors serie, p.
501-510.
ROTH, A., 1999: Ökofaunistische Analyse der Spinnenzönosen (Arachnida, Araneae) zweier Enns-Inseln in Oberösterreich.
Beitr. Naturk. Oberösterreichs, 7, p. 53-78.
RUPP, B., 1999: Ökofaunistische Untersuchungen an der epigäischen Spinnenfauna (Arachnida: Araneae) des
Wörschacher Moores (Steiermark, Bez. Liezen). Mitt. naturwiss. Ver. Steiermark, 129, p. 269-279.
RŮŽIČKA, V., HOLEC, M., 1998: New records of spiders from pond littorals in the Czech Republic. Arachnol.
Mitt., 16, p. 1-7.
THALER, K., 1992: Weitere Funde nivaler Spinnen (Aranei) in Nordtirol und Beifänge. Ber. nat.-med. Verein
Innsbruck, 79, p. 153-159.
THALER, K., KNOFLACH, B., 1997: Funde hochalpiner Spinnen in Tirol 1992-1996 und Beifänge (Araneae, Opiliones,
Pseudoscorpiones, Diplopoda, Coleoptera). Ber. nat.-med. Verein Innsbruck, 84, p. 159-170.
77

Ekológia (Bratislava) Vol. 19, Supplement 4, 79-85, 2000
SPIDERS (ARANEAE) ON SANDY ISLANDS IN THE
SOUTHWESTERN ARCHIPELAGO OF FINLAND
SEPPO KOPONEN
Zoological Museum, University of Turku, FIN-20014 Turku, Finland. E-mail: sepkopo@utu.fi
Introduction
Abstract
Koponen S.: Spiders (Araneae) on sandy islands in the southwestern archipelago of Finland. In
Gajdoš P., Pekár S. (eds): Proceedings of the 18th European Colloquium of Arachnology, Stará
Lesná, 1999. Ekológia (Bratislava), Vol. 19, Supplement 4/2000, p. 79-85.
Spiders were studied on two sandy islands in the outermost part of the SW archipelago of Finland:
Korppoo Jurmo (59 0 50’N, 21 0 37’E) and Dragsfjärd Örö (59 0 50’N, 22 0 20’E). The main
collecting method was pitfall trapping. Typical, and often locally abundant, species on sandy and/
or gravel shores were e.g. Arctosa cinerea, Alopecosa fabrilis, Pardosa agricola, Xerolycosa
miniata, Zelotes longipes, Z. praeficus, Callilepis nocturna, Lasiargus hirsutus, Trichoncus hackmani,
Microlinyphia impigra, Steatoda albomaculata, Philodromus fallax, Phlegra fasciata
and Sitticus saltator. On dry heath meadows the following species, in addition to many of the
above-mentioned spiders, were typically caught: Zelotes electus, Alopecosa cuneata, Pardosa
agrestis, P. palustris, Trichopterna cito and Lepthyphantes decolor. The material included three
species listed in the Finnish Red Data Book, all in need of monitoring, i.e. Zelotes electus (abundant),
Metapanamomops kaestneri (locally abundant) and Acartauchenius scurrilis. Also many
other rare species, like Jacksonella falconeri, Argenna subnigra and Pseudicius encarpatus,
were found.
The southwestern archipelago of Finland consists of over 41 000 islands of different
size. The spider fauna of this area has been studied by e.g. HACKMAN (1953), LEHTINEN,
KLEEMOLA (1962), KLEEMOLA (1963), PALMGREN (1972), PALMGREN, LÖNNQVIST (1974),
LEHTINEN et al. (1979).
A large area (19 000 km 2 and 8 400 islands or islets) of the southern part of the archipelago
belongs nowadays to the joint working area of the Archipelago National Park, and
investigation of fauna in the Park was carried out during the 1990s. In the present paper,
data on the spider fauna on two rather large sandy islands are presented. The islands Jurmo
and Örö are situated in the outer archipelago and facing the open Baltic Sea.
79

Fig. 1. The study islands in the southwestern archipelago of Finland; 1 = Jurmo, 2 = Örö.
Study area, material and methods
The islands Jurmo (in Korppoo/Korpo; 59 0 50’N, 21 0 37’E) and Örö (in Dragsfjärd; 59 0 50’N, 22 0 20’E) are
rather isolated sandy islands (Fig. 1). The area of Jurmo is 2.7 and of Örö 2.0 km 2 . The distance between the
islands is about 35 km. In Örö there are forests of different types, with pine forests dominating naturally, whereas
in Jurmo only a planted pine woodland can be found.
Two main habitat types were studied: 1) sand/gravel sea shores 2) dry meadows and heaths. Two sea shores
and a pond shore were studied in Jurmo and five sea shores in Örö. Three dry meadows or heaths were investigated
in Jurmo and two in Örö island where, in addition, a man-made open sandy heath was studied.
The shores were characterised by sand or gravel, sometimes also by larger stones. In some places wrack (drift
of Fucus etc) was found. The sparse vegetation was formed by Leymus arenarius and several plants that are rare
in Finland, like Elymus farctus, Crambe maritima, Isatis tinctoria, Salsola kali, Atriplex littoralis, Cakile maritima,
and Honkenya peploides. In addition, some species of Carex, as well as of Poaceae, and Galium verum, Lathyrus
japonicus, Thymus serpyllum, Tanacetum vulgare and Rosa rugosa are locally typical plants.
In dry meadows and heaths e.g. Juniperus communis, Calluna vulgaris, Potentilla subarenaria, Linum
catharcticum, Arctostaphylos uva-ursi, Thymus serpyllum, Empetrum nigrum, Antennaria dioica, Cardamine
hirsuta, Artemisia campestris as well as Carex and Poaceae species are typical and at least locally common.
The main collecting method was pitfall trapping. Plastic cups (diameter 70 mm) with covers against rainfall
and litter, and with ethylene glycol and detergent as preservative, were used. The trapping period in Jurmo was
29 June - 26 August 1995, and in Örö 25 May - 13 September 1996.
The trapping sites (A-F), with characteristic plant species, were in Jurmo: 1) Shores (southern and
southwestern side), A: sand shore, Leymus, Empetrum, Galium verum; B: sand shore, Galium verum, Empetrum,
Leymus, Juniperus; C: silty shore of temporary ponds, Agrostis stolonifera; 2) Dry meadows & heaths, D:
calcareous heath, Festuca, Potentilla subarenaria, Antennaria, Linum, Juniperus, lichens; E: dry meadow,
Poaceae, Juniperus; F: thymus heath, Poaceae, Thymus, Empetrum, Calluna, Juniperus.
80

The trapping sites (A-H) in
Örö were: 1) Shores (western
side), A: sand dune, small pines,
Galium verum, Isatis, Poaceae,
Rosa rugosa, Cladonia; B:
sand-gravel-stony shore, Leymus,
Thymus, Galium verum,
Poaceae; C: sand dune, Leymus,
Galium verum, Sedum, Rosa,
Poaceae; D: sand shore, Thymus,
Galium verum, Anthriscus,
Allium, Crambe, Chamenaerium,
Tanacetum, Sedum, Rosa,
Juniperus, Poaceae; E: sand-
-gravel-stony shore, Leymus,
Galium verum, Tanacetum,
Crambe, Myosotis, Poaceae; 2)
Heaths, F: warm heath, Thymys,
Calluna, Cardamine hirsuta,
Cirsium, Poaceae; G: warm
heath, Calluna, Viola tricolor,
Artemisia campestris, Poaceae;
H: edge of man-made sand field
and dry pine forest, open sand,
Calamagrostis.
The spider material from Jurmo
and Örö consisted of about
1 600 and 3 800 identifiable
specimens, respectively. The
material is deposited in the
Zoological Museum, University of Turku.
Results and discussion
Altogether, about 190 species of spiders were found in Jurmo and Örö islands in 1995-
96. The most species-rich families were Linyphiidae (s.lat.; 67 species), Lycosidae (24),
Theridiidae (19) and Gnaphosidae (17).
Some species were frequently found both on shores and in dry meadow or heath habitats,
i.e. they were common in all open areas. These include e.g. Zelotes longipes (L. KOCH),
Pardosa palustris (LINNAEUS), P. agrestis (WESTRING) and P. agricola (THORELL) in Jurmo,
and Zelotes praeficus (L. KOCH), Z. electus (C. L. KOCH), Z. longipes, Callilepis nocturna
(LINNAEUS), Phrurolithus festivus (C. L. KOCH) and Alopecosa fabrilis (CLERCK) in Örö.
Spiders in shore habitats
T a b l e 1. The most abundant spiders caught by pitfall traps on sea
shores (sites A-B) and on a pond shore (site C) in Jurmo. Numbers are
given for each species as a percentage of the total catch at the
respective site. Numbers in brackets denote that the species was not
among the six most abundant ones, data for the dominant species are
in bold; Aver- average percentage on sea shores. For description of the
sites, see the text.
A B Aver C
Lasiargus hirsutus (MENGE) 31 4 18 –
Trichoncus hackmani MILL. (3) 27 15 –
Zelotes subterraneus (C. L. K.) 29 – 15 –
Alopecosa fabrilis (CL.) (1) 17 9 –
Pardosa agricola (TH.) (2) 13 8 2
Pardosa agrestis (WEST.) 8 – 4 (2)
Oedothorax fuscus (BL.) 7 – 3 55
Thanatus striatus C. L. K. 4 (2) 3 –
Pachygnatha degeeri SUND. – 5 3 (0)
Pirata piraticus (CL.) 3 – 2 (2)
Oedothorax retusus (WEST.) – (1) . 15
Oedothorax agrestis (BL.) (1) – . 7
Erigone longipalpis (SUND.) – – . 6
Number of species 23 20 . 14
Number of individuals 258 114 . 454
The most abundant species on sandy sea shores and on the silty pond shore in Jurmo
island are shown in Table 1. Two erigonine species, Lasiargus hirsutus (MENGE) and
81

T a b l e 2. The most abundant spiders caught by pitfall traps on shores in Örö (sites A-E). Numbers are given
for each species as a percentage of the total catch at the respective site. Numbers in brackets denote that the
species was not among the six most abundant ones, data for the dominant species are in bold; Aver- average
percentage on sea shores. For description of the sites, see the text.
A B C D E Aver
Lasiargus hirsutus (MENGE) 56 11 (1) 25 42 27
Xerolycosa miniata (C. L. K.) 12 (3) 76 13 (1) 21
Zelotes electus (C. L. K.) 5 (2) 4 11 (2) 5
Pardosa agricola (TH.) 3 (1) (0) (4) 18 5
Alopecosa fabrilis (CL.) 3 20 (0) (3) (0) 5
Callilepis nocturna (L.) (1) 16 3 (1) 3 5
Zelotes praeficus (L. K.) (2) (5) (2) 5 6 4
Arctosa cinerea (FABR.) 3 – 4 (2) (2) 2
Pardosa agrestis (WEST.) – 11 – – – 2
Micaria nivosa L. K. – 10 (0) (0) – 2
Zelotes longipes (L. K.) (0) 8 – – – 2
Phrurolithus festivus (C. L. K.) (1) (2) 2 (0) (3) 2
Trichoncus hackmani MILL. (2) (2) 2 (1) (2) 2
Pachygnatha degeeri SUND. (1) (1) (1) 6 – 2
Alopecosa pulverulenta (CL.) (0) – – 7 – 1
Thanatus striatus C. L. K. (0) (1) (1) (0) 5 1
Zelotes subterraneus (C. L. K.) (0) (2) – – 5 1
Number of species 37 34 24 46 26 .
Number of individuals 729 388 496 722 395 .
Trichoncus hackmani MILLIDGE dominated on sea shores, and Oedothorax fuscus
(BLACKWALL) and O. retusus (WESTRING) dominated the silty pond shore. Other abundant
species were e.g. Zelotes subterraneus (C. L. KOCH), A. fabrilis and P. agricola.
In Örö, L. hirsutus, Xerolycosa miniata (C. L. KOCH) and A.fabrilis were dominant species
in shore trap series (Table 2). Other abundant species were Z. electus, P. agricola, C.
nocturna, Z. praeficus and Arctosa cinerea (FABRICIUS).
The most typical and abundant sand/gravel shore species in Jurmo and Örö islands was
L. hirsutus. The species is known in Finland only from the outer part of the archipelago;
HACKMAN (1953) reported it for the first time in Finland from Fucus heaps in Jurmo and
from a few other localities.
The shore material included many rare and interesting species: species on wide sandy
shores were e.g. A. cinerea, A. fabrilis, X. miniata, Philodromus fallax SUNDEVALL, Xysticus
sabulosus (HAHN), Microlinyphia impigra (O. P.-CAMBRIDGE), Steatoda albomaculata (DE
GEER), Phlegra fasciata (HAHN) and Sitticus saltator (O. P.-CAMBRIDGE).
Typical species on shores in the SW archipelago, and many of them rare, were also Erigone
longipalpis (SUNDEVALL), T. hackmani, Linyphia tenuipalpis SIMON, Argenna subnigra (O. P.-
CAMBRIDGE), Micaria nivosa L. KOCH, Z. electus, Clubiona similis L. KOCH, Aelurillus vinsignitus
(CLERCK), Myrmarachne formicaria (DE GEER), Thanatus striatus C. L. KOCH,
Segestria senoculata (LINNAEUS), Dipoena hamata TULLGREN and D. prona (MENGE).
82

Spiders in dry meadows
and heaths
Abundant spiders
caught by pitfall traps in
dry meadows and in heaths
in Jurmo island are listed
in Table 3. Dominant in
different habitats were Z.
longipes, P. palustris and
P. agrestis, other common
species e.g. Drassodes
lapidosus (WALCKENAER),
Z. electus and locally
Trichopterna cito (O. P.-
CAMBRIDGE).
Abundant species in dry
heaths and in the manmade
sandy heath in Örö
island are given in Table 4.
Dominant species in dry
open heaths were Z.
praeficus and Alopecosa
cuneata (CLERCK), other
common species were Z.
electus, Z. longipes and
Metapanamomops
kaestneri (WIEHLE).
Lepthyphantes decolor
(WESTRING), P. festivus and
X. miniata were the most
abundant species in the
man-made heath where
also the habitat resembled
both heaths and the nearby
sandy shore.
Typical and abundant
heath species in Jurmo and
Örö islands were several
species of the genera
Zelotes (especially Z.
T a b l e 3. The most abundant spiders caught by pitfall traps in dry
meadows and heaths in Jurmo (sites D-F). Numbers for each species
are given as a percentage of the total catch at the respective site.
Numbers in brackets denote that the species was not among the six
most abundant ones, data for the dominant species are in bold; Averaverage
percentage in studied habitats. For description of the sites, see
the text.
D E F Aver
Zelotes longipes (L. K.) 31 24 23 26
Pardosa palustris (L.) 7 (4) 41 17
Pardosa agrestis (WEST.) 37 7 5 16
Drassodes lapidosus (WALC.) 7 7 5 6
Zelotes electus (C. L. K.) 2 8 4 5
Trichopterna cito (O. P.–C.) (0) 13 – 4
Pardosa agricola (TH.) (1) 11 – 4
Metopobactrus prominulus (O. P.–C.) (0) (1) 7 3
Alopecosa pulverulenta (CL.) 4 (1) (1) 2
Number of species 25 29 15 .
Number of individuals 257 174 133 .
T a b l e 4. The most abundant spiders caught by pitfall traps in dry
heaths (sites F-G) and in the man-made sandy heath in Örö (site H).
Numbers for each species are given as a percentage of the total catch
at the respective site. Numbers in brackets denote that the species was
not among the six most abundant ones, data for the dominant species
are in bold; Aver- average percentage in studied heaths. For
description of the sites, see the text.
F G Aver H
Zelotes praeficus (L. K.) 33 23 28 –
Alopecosa cuneata (CL.) 13 30 22 –
Zelotes electus (C. L. K.) 8 10 9 6
Zelotes longipes (L. K.) 6 11 9 (1)
Metapanamomops kaestneri (WIEH.) (3) 7 5 –
Callilepis nocturna (L.) 7 (2) 5 –
Alopecosa fabrilis (CL.) (2) 5 4 3
Phrurolithus festivus (C. L. K.) 6 – 3 18
Lepthyphantes decolor (WEST.) (4) – . 36
Xerolycosa miniata (C. L. K.) (1) – . 10
Pardosa lugubris (WALC.) (0) – . 6
Number of species 36 23 . 18
Number of individuals 503 246 . 67
praeficus, Z. electus, Z. longipes), Alopecosa (A. cuneata, A. fabrilis, A. pulverulenta
(CLERCK)) and Pardosa (P. agrestis, P. palustris).
83

Worth mentioning are also L. decolor (found in Jurmo and Örö), Porrhomma montanum
JACKSON (Örö), M. kaestneri (Örö), Micrargus subaequalis (WESTRING) (Jurmo), T. cito
(Jurmo and Örö), Tapinocyboides pygmaea (MENGE) (Jurmo and Örö), Typhochrestes
digitatus (O. P.-CAMBRIDGE) (Örö), Walckenaeria monoceros (WIDER) (Jurmo), Zelotes
pusillus (C. L. KOCH) (Örö), C. nocturna (Örö), Micaria silesiaca L. KOCH (Örö),
Poecilochroa variana (C. L. KOCH) (Jurmo and Örö), Phaeocedus braccatus (L. KOCH)
(Örö), Pardosa nigriceps (THORELL) (Jurmo and Örö), and Xysticus erraticus (BLACKWALL)
(Jurmo and Örö).
In addition, the following noteworthy species were found in the field/shrub layer of dry
heaths: Achaearanea riparia (BLACKWALL) (in Örö), A. saxatile (C. L. KOCH) (Jurmo and
Örö), Theridion pallens BLACKWALL (Örö), T. tinctum (WALCKENAER) (Örö).
Endangered species and faunistic rarities
Three species amongst the present material have been included in the Finnish Red Data
Book as species in need of monitoring (RASSI et al., 1992): Z. electus, M. kaestneri and
Acartauchenius scurrilis (O. P.-CAMBRIDGE). All were found in Örö, and Z. electus also in
Jurmo. Z. electus was the fourth most abundant species in Örö, and rather common also in
dry heaths in Jurmo. M. kaestneri was also locally abundant in the dry heath in Örö. Only
one specimen of A. scurrilis was found, also in dry heath in Örö. An interesting species is
Pseudicius encarpatus (WALCKENAER), listed as extinct in Sweden (EHNSTRÖM et al., 1993)
and which has also clearly declined in Finland during this century (cf. also PALMGREN, 1972);
one specimen was found in Örö.
Three species have recently been reported for the first time from Finland (KOPONEN,
1999); two of them (Jacksonella falconeri (WALCKENAER) from the gravel-sand shore in
Örö and Enoplognatha thoracica (HAHN) from dry Thymus meadow in Jurmo) are based on
the present material, and the third one (Ozyptila westringi (THORELL) from Jurmo) on previous
museum material.
Faunal comparisons
The fauna found in sandy islands of Jurmo and Örö resembled, in general, that reported
from corresponding habitats in Scania (ALMQUIST, 1973) and Öland (KRONESTEDT,
1983), South Sweden, and from the northern coast of Germany (SCHULTZ, FINCH, 1996).
However, many species common either on the North German coast or on dunes of Scania
and in heaths of Öland are absent in the present area, probably due to the rather small
size, marked isolation and northern latitude of Jurmo and Örö. On the other hand, several
common or characteristic species of the present material are absent or rare at more southern
Baltic Sea sites. Special characters of the present islands seem to be, for example, the
great number of species and individuals of Gnaphosidae and the dominance of Lasiargus
hirsutus (MENGE) on shores (cf. ALMQUIST, 1973; VILBASTE, 1974; KRONESTEDT, 1983;
SCHULTZ, FINCH, 1996).
84

Acknowledgements
The support by the Archipelago Park Area of the Finnish Forest and Park Service is greatly appreciated. The
help in the field by Veikko Rinne and Tom Clayhills is gratefully acknowledged.
References
ALMQUIST, S., 1973: Spider associations in coastal sand dunes. Oikos, 24, p. 444-457.
EHNSTRÖM, B., GARDENFORS, U., LINDELÖW, Å., 1993: Swedish red list of invertebrates 1993. Databanken för
hotade arter, Uppsala, 69 pp. (In Swedish)
HACKMAN, W., 1953: Spiders from Åland and the southwestern archipelago of Finland. Memoranda Societatis
pro Fauna et Flora Fennica, 28, p. 70-78. (In Swedish)
KLEEMOLA, A., 1963: On the zonation of spiders on stony shores of rocky islets in the southwestern archipelago
of Finland. Aquilo (Zoologica), 1, p. 26-38.
KOPONEN, S., 1999: Three species of spiders (Araneae) new to the fauna of Finland from the southwestern archipelago.
Entomologica Fennica, 10, p. 6.
KRONESTEDT, T., 1983: Spiders on the Great Alvar of the island of Öland, S Sweden. Entomologisk Tidskrift,
104, p. 183-212. (In Swedish)
LEHTINEN, P.T., KLEEMOLA, A., 1962: Studies on the spider fauna of the southwestern archipelago of Finland. I.
Archivum Societatis Zoologicae Botanicae Fennicae ‘Vanamo’, 16, 1, p. 97-114.
LEHTINEN, P.T., KOPONEN, S., SAARISTO, M., 1979: Studies on the spider fauna of the southwestern archipelago of
Finland II. The Aland mainland and the island of Eckerö. Memoranda Societatis pro Fauna et Flora Fennica,
55, p. 33-52.
PALMGREN, P., 1972: Studies on the spider populations of the surroundings of the Tvärminne Zoological Station,
Finland. Societas Scientiarum Fennica, Commentationes Biologicae, 52, p. 1-133.
PALMGREN, P., LÖNNQVIST, B., 1974: The spiders of some habitats at the Nåtö Biological Station (Åland, Finland).
Societas Scientiarum Fennica, Commentationes Biologicae, 73, p. 1-10.
RASSI, P., KAIPIAINEN, H., MANNERKOSKI, I., STÅHLS, G., 1992: Report on the monitoring of threatened animals and
plants in Finland. Ministry of the Environment, Helsinki, 328 pp. (In Finnish)
SCHULTZ, W., FINCH, O.-D., 1996: Biotoptypenbezogene Verteilung der Spinnenfauna der nordwestdeutschen
Küstenregion. Cuvillier Verlag, Göttingen, 141 pp.
VILBASTE, A., 1974: On the spider fauna of islets of Väinameri. Loodusvaatlusi, 1973, p. 132-145. (In Estonian)
85

Ekológia (Bratislava) Vol. 19, Supplement 4, 87-96, 2000
FAUNA OF SOIL-DWELLING PREDATORY
GAMASINA MITES (ACARI: MESOSTIGMATA) IN
SEASHORE HABITATS OF THE KURZEME COAST,
LATVIA
INETA SALMANE
Institute of Biology, University of Latvia, Miera iela 3, LV-2169, Salaspils, Latvia. Fax: 371-9-345 412. Email:
ineta_s@hotmail.com
Introduction
Abstract
SALMANE I.: Fauna of soil-dwelling predatory Gamasina mites (Acari: Mesostigmata) in seashore
habitats of the Kurzeme Coast, Latvia. In GAJDOŠ P., PEKÁR S. (eds): Proceedings of the 18th
European Colloquium of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava), Vol. 19, Supplement
4/2000, p. 87-96.
Because of the lack of data on the Gamasina mite fauna in coastal habitats of Latvia, sampling
was made on the seashore of the Kurzeme Coast. An unexpectedly high total number (78) of
Gamasina species was recorded. Twenty-three species were found to be new for Latvia. A previously
undescribed species (new to Science) from the genus Lasioseius was recorded from the
yellow dunes. Leioseius bicolor, Leioseius halophilus and Parasitus halophilus were recorded as
the most widely distributed Gamasina species along the Kurzeme Coast.
Driftline, primary and yellow dune Gamasina faunas were investigated separately. Fourteen Gamasina
species were found to be common to all three habitats. Driftline habitats were the most
diverse with 55 species. Twenty-two species were recorded from the primary dunes and 50 species
from the yellow dunes.
Comparison of Gamasina fauna along the coasts of the Baltic Sea and the Riga Gulf of the Kurzeme
was made. Fifty species from coastal habitats of the Riga Gulf Coast and 55 from the Baltic
Sea Coast were recorded. Twenty-seven Gamasina species were recorded as common for both
sites, but 24 species for the Riga Gulf Coast and 29 for the Baltic Sea Coast were unique for their
respective habitats.
Seashore ecosystems vary in terms of ecological conditions and biological diversity, and
can be characterised by an interaction between geomorphological and biological processes
(JUNGERIUS, 1985). Biological processes in coastal habitats are complicated and the role of
the soil fauna in them is important (MALLOW et al., 1984). Protozoa and Nematoda are
87

attracted to the active rhizosphere and may feed on bacteria, as well as on living and dead
plant material and soil algae and fungi. Collembola - bacterial and fungal grazers, and
Gamasina mites as predators of Collembola, other soil dwelling mites, Nematoda, Insecta
larvae etc. may control this system (KOEHLER et al., 1992). This complicated system is very
important for soil processes generally, but for seashore habitats in particular. Unfortunately,
little is known about the soil fauna in coastal habitats of Latvia and few data are available
concerning the soil Gamasina mites that live there.
The fauna of soil Gamasina mites of seashore ecosystems in Latvia is poorly investigated.
Some sampling was carried out by Kadite (Lithuania). She described 35 Gamasina
species from various seashore habitats (EITMINAVICHUTE, 1976). Some case studies along the
seacoast of Latvia have been made by the author of the present article (MELECIS et al., 1994;
SALMANE, 1996; PAULINA et al., 1999), the results of which stimulated the need for the sampling
reported here, with the aim of obtaining a closer insight into the Gamasina fauna of
the seashore habitats of Latvia.
Study Area
A total of 8 sampling sites were selected along the seacoast of the Kurzeme (Engure
(23°15'/57°10'), Roja (22°45'/57°30'), Kolkasrags (22°30'/57°40'), Luzna (21°55'/57°35'),
Ventspils (21°30'/57°25'), Pavilosta (21°15'/56°55'), Liepaja (21°0'/56°30') and Pape (21°5'/
56°15') in the driftline, primary and yellow dunes.
The driftline habitats were characterised mostly by fine sand and material washed ashore,
including algae and other jetsam deposited by the sea. Organic debris deposited by the sea
was the main nutrient source here. Cakile maritima, Chenopodium rubrum or Salsola calii
represented the vegetation in a few cases. The primary dunes were characterised by fine to
medium sandy soils with minimal content of organics in the soil. Single Calamophila baltica,
Ammodenia peploides, Amophila arenaria, Leymus arenarius, Festuca arenaria and Juncus
balticus represented the vegetation here.The yellow dunes were characterised by medium
sandy soils with a relatively high content of organics and more abundant vegetation represented
by Calamophila baltica, Amophila arenaria, Festuca arenaria, Hieracium
umbellatum, Carex arenarius, Ammodenia pepoloides, Anthyllis maritima, Lathyrus
japonicus and Salix sp.
Material and methods
We focused on qualitative sampling to investigate the spectrum of Gamasina species. The sampling was
performed in 8 sites along the Kurzeme Coast (Western part of Latvia), which includes the western part of the
Riga Gulf Coast and the western part of the Latvian sea coast washed by the Baltic Sea. Three sampling sites in
Riga Gulf Coast of the Kurzeme Coast and 5 at Baltic Sea Coast were chosen. At each site sampling was carried
out by hand or by using a soil corer (23cmþ x 10cm). A single sample included approximately 300-400 g of
88

substrate. Altogether 120 soil samples were taken from the organic debris of the driftline or the rhizosphere of
plants in primary and yellow dunes. The collected material was taken to the laboratory in plastic bags.
Extraction was carried out using Tullgren funnels, where samples were exposed for a period of 14 days.
Determination and nomenclature of Gamasina species are based upon the keys of BREGETOVA (1977), HIRSHMANN
(1971), KARG (1993), KOLODOCHKA (1978) and LAPINA (1976 a, b). The quantitative comparison of Gamasina
mites among sampling sites was not possible because of the unequal number of samples taken.
Results
Seventy-eight Gamasina species were recorded in the collected material, 23 of which
were found for the first time in the fauna of Latvia (Table 1). One, previously undescribed
species (new to Science) from the genus Lasioseius was found. Leioseius bicolor (BERLESE)
(8 sampling sites), L. halophilus (WILLMANN) and Parasitus halophilus (SELLNICK) (7) and
Thinoseius spinosus (WILLMANN) and Leioseius insignis HIRSCHMANN (6) were the most
widely distributed species in the seashore habitats of the Kurzeme Coast (Table 2).
Comparison of Gamasina mites’ fauna among the habitats was made and 14 species
were revealed as common for all habitats (Table 1). Species found there were mainly ubiquitous,
forest and seashore inhabitants. The driftline communities were found to be the
most diverse with 55 species, 22 of which differed from the dune fauna. At the dune habitats
22 and 50 species in primary and yellow dunes, respectively, were recorded.
Fourteen species were common for all three investigated habitat types, 3 species common
for driftline and primary dune, 15 species for driftline and yellow dune. Three Gamasina
species were common for both primary and yellow dunes. Forty-three species were recorded
only in one habitat type. Twenty-two of them were found as typical only for the
driftline, 2 species for the primary and 18 species for the yellow dune habitats.
Comparison between the fauna of Gamasina mites of the Baltic Sea Coast and Riga Gulf
Coast of Kurzeme was made. In these two sites 55 and 50 species, respectively, could be
determined. About 1/3 of them was common for both sites, but the rest of the species were
unique for one of the sites.
Discussion
Fifty-five Gamasina were recorded in the driftline habitats and the most abundant species
there found were those with demands for wet soils with a high amount of organic
material. Several species (Parasitus kempersi OUDEMANSI, Halolaelaps balticus WILLMANN,
H. incisus HYATT, Thinoseius spinosus), known as common driftline inhabitants (KARG,
1993), were found in high numbers in the material washed ashore. Also some hygrophilous
Gamasina (Gamasolaelaps excisus (C. L. KOCH), Neojordensia levis (OUDEMANS ET VOIGTS),
Cheiroseius necorniger (OUDEMANS) and Hypoaspis vacua (MICHAEL)), and species from
the genus Macrocheles, preferring habitats with high organic content, were numerous there.
89

T a b l e 1. Occurrence of Gamasina species on the seashore of the
Kurzeme Coast. (* - species recorded for the first time in Latvia).
Gamasina (Acari) Driftline Primary
dune
90
Yellow
dune
Parasitus halophilus (SELL.)* x x x
Holoparasitus excipuliger (BERL.) x x x
Pergamasus vagabundus KARG x x x
Veigaia nemorensis (C. L. K.) x x x
Leioseius bicolor (BERL.) x x x
Leioseius halophilus (WILL.) x x x
Leioseius insignis HIRS.* x x x
Amblyseius marinus (WILL.)* x x x
Amblyseius agrestis (KARG)* x x x
Dendrolaelaps nostricornutus HIRS. ET
WISN.*
x x x
Asca bicornis (CANE. ET FANZ.) x x x
Halolaelaps balticus WILL.* x x x
Thinoseius spinosus (WILL.)* x x x
Parazercon sarekensis WILL. x x x
Veigaia cervus (KRAM.) x x
Macrocheles glaber (MULL.) x x
Prozercon trägardhi (HALB.) x x
Parasitus kempersi OUDE.* x x
Pergamasus crassipes (L.) x x
Pergamasus septentrionalis (OUDE.) x x
Leioseius minutus (HALB.) x x
Pergamasus teutonicus WILL. x x
Pergamasus wasmanni (OUDE.) x x
Amblyseius bicaudus WAIN. x x
Amblyseius messor WAIN. x x
Amblyseius meridionalis (BERL.) x x
Dendrolaelaps foveolatus LEIT. x x
Macrocheles tardus (C. L. K.) x x
Hypoaspis aculeifer (CANE.) x x
Hypoaspis praesternalis WILL. x x
Hypoaspis vacua (MICH.) x x
Zercon carpathicus (SELL.) x x
Parasitus kraepelini BERL. x
Parasitus lunaris BERL. x
Parasitus fimetorum BERL. x
Pergamasus truncus SCHW.* x
Gamasodes bispinosus (HALB.)* x
Pergamasus lapponicus TRAG. x
Veigaia exigua (BERL.) x
Gamasolaelaps excisus (C. L. K.)* x
Neojordensia levis (OUDE. ET VOIG.) x
The high abundance
of these species could
be explained by the
presence of very favourable
ecological
conditions. Driftline
habitats are rich in the
organic material (nutrients)
deposited by the
sea and, thus, the most
favourable environmental
conditions for
various invertebrates,
on which Gamasina are
known to prey (COLE-
MAN, CROSSLEY, 1996;
PUGH, 1985), were
formed. Fresh organic
material attracts various
Insecta, which feed and
lay eggs there. Their
eggs, larvae and some
specialised driftline
Collembola species and
other small adult Insecta
form the main
food source for predatory
Gamasina mites.
Useful food for Gamasina
is also other soil
mite groups, Polychaeta,
Nematoda and
Enchytraeidae, dwelling
in the material
washed ashore. These
favourable ecological
conditions for Gamasina
mites enables them
to achieve a high abundance
in the driftline.
Favourable conditions
determine the ex-

istence of many Gamasina
species, which are not typical
driftline inhabitants.
Other groups recorded in
the driftline comprised species
characteristic mainly of
various inland ecosystems
(e.g. some ubiquitous species
(Pergamasus vagabundus
KARG, Holoparasitus
excipuliger (BERLESE)
and Veigaia nemorensis (C.
L. KOCH)), forest species
(Pergamasus lapponicus
TRAGARDH, Pergamasus
crassipes (LINNAEUS), P.
wasmanni (OUDEMANS),
Hypoaspis aculeifer
(CANESTRINI) and Parazercon
sarekensis WILLMANN)
and inland meadow species
(Cheiroseius borealis
(BERLESE), Leioseius minutus
(HALBERT), Asca bicornis
(CANESTRINI ET FANZAGO),
Hypoaspis praesternalis
WILLMANN, H. vacua,
Veigaia exigua (BERLESE)).
Some common dune inhabitants
(Leioseius bicolor,
Parasitus halophilus) were
also recorded in the material
from the driftline. Species
of this group were not
as numerous as the abovementioned
typical driftline
inhabitants.
Fifteen species were recorded
as common for the
driftline and yellow dunes,
T a b l e 1.
Gamasina (Acari) Driftline Primary
dune
Yellow
dune
Cheiroseius borealis (BERL.) x
Cheiroseius necorniger (OUDE.) x
Amblyseius obtusus (C. L. K.) x
Amblyseius herbarius WAIN. x
Dendrolaelaps latior (LEIT.)* x
Dendrolaelaps fallax (LEIT.) x
Halolaelaps incisus HYATT* x
Halolaelaps marinus (BRADY)* x
Macrocheles montanus (WILL.) x
Alliphis siculus (OUDE.) x
Eviphis ostrinus (C. L. K.) x
Prozercon sellnicki HALA. x
Zercon montanus WILL. x
Zercon fageticola HALA.* x
Rhodacarellus silesiacus WILL. x x
Rhodacarus reconditus ATHIAS-H. x x
Dendrolaelaps arenarius KARG* x x
Zercon zelawaiensis SELL. x
Leioseius montanulus HIRS. x
Lasioseius sp. nov. x
Hypoaspis claviger (BERL.) x
Hypoaspis sclerotarsa COSTA* x
Hypoaspis similisetae KARG* x
Hypoaspis kargi COSTA x
Laelaspis astronomicus L. K. x
Zercon spatulatus (C. L. K.) x
Leioseius minusculus (BERL.) x
Platyseius italicus (BERL.) x
Antenoseius delicatus BERL. x
Amblyseius aurescens ATHIAS-H. x
Amblyseius andersoni (CHANT) x
Amblyseius bakeri (GARM.) x
Amblyseius graminis CHANT x
Rhodacarus mandibularis BERL.* x
Rhodacarus haarlovi SHCH.* x
Minirhodacarellus minimus (KRAG)* x
Dendrolaelaspis angulosus WILL.* x
Totally 78 species 55 22 50
and this could be explained by the relatively high organic matter content in the soils of
yellow dunes. In turn, the driftline and primary dunes have only 3 common Gamasina species
because of the totally different ecological conditions for soil animals.
91

T a b l e 2. Distribution of Gamasina species in the seashore habitats of the Kurzeme Coast. Sampling sites:
1-Engure, 2- Roja, 3- Kolkasrags, 4- Lūžņa, 5- Ventspils, 6- Pāvilosta, 7- Liepāja, 8- Pape. Nr- number of
sampling sites where the respective species occur.
Riga Gulf Baltic Sea Nr
Gamasina species 1 2 3 4 5 6 7 8
Leioseius bicolor (BERL.) x x x x x x x x 8
Parasitus halophilus (SELL.) x x x x x x x 7
Leioseius halophilus (WILL.) x x x x x x x 7
Thinoseius spinosus (WILL.) x x x x x x 6
Leioseius insignis HIRS. x x x x x x 6
Hypoaspis aculeifer (CANE.) x x x x x 5
Halolaelaps balticus WILL. x x x x x 5
Dendrolaelaps nostricornutus HIRS. ET
WISN.
x x x x x 5
Cheiroseius necorniger (OUDE.) x x x x 4
Amblyseius marinus (WILL.) x x x x 4
Veigaia nemorensis (C. L. K.) x x x x 4
Pergamasus crassipes (L.) x x x 3
Pergamasus vagabundus KARG x x x 3
Amblyseius bicaudus WAIN. x x x 3
Hypoaspis vacua (MICH.) x x x 3
Parazercon sarekensis WILL. x x x 3
Halolaelaps incisus HYATT x x x 3
Pergamasus lapponicus TRAG. x x 2
Leioseius minutus (HALB.) x x 2
Rhodacarellus silesiacus WILL. x x 2
Rhodacarus mandibularis BERL. x x 2
Rhodacarus reconditus ATHIAS-H. x x 2
Macrocheles tardus (C. L. K.) x x 2
Asca bicornis (CANE. ET FANZ.) x x 2
Hypoaspis praesternalis WILL. x x 2
Hypoaspis sclerotarsa COSTA x x 2
Zercon spatulatus (C. L. K.) x x 2
Macrocheles glaber (MULL.) x x 2
Prozercon trägardhi (HALB.) x x 2
Lasioseius sp.nov. x 1
Parasitus kraepelini BERL. x 1
Parasitus lunaris BERL. x 1
Parasitus fimetorum BERL. x 1
Pergamasus truncus SCHW. x 1
Gamasodes bispinosus (HALB.) x 1
Veigaia exigua (BERL.) x 1
Gamasolaelaps excisus (C. L. K.) x 1
Neojordensia levis (OUDE. ET VOIG.) x 1
Cheiroseius borealis (BERL.) x 1
92

T a b l e 2.
Riga Gulf Baltic Sea Nr
Gamasina species 1 2 3 4 5 6 7 8
Amblyseius agrestis (KARG) x 1
Amblyseius bakeri (GARM.) x 1
Amblyseius graminis CHANT x 1
Dendrolaelaspis angulosus WILL. x 1
Dendrolaelaps latior (LEIT.) x 1
Dendrolaelaps fallax (LEIT.) x 1
Macrocheles montanus (WILL.) x 1
Alliphis siculus (OUDE.) x 1
Eviphis ostrinus (C. L. K.) x 1
Prozercon sellnicki HALA. x 1
Zercon montanus WILL. x 1
Rhodacarus haarlovi SHCH. x x x x 4
Minirhodacarellus minimus (KRAG) x x x x 4
Holoparasitus excipuliger (BERL.) x x x 3
Dendrolaelaps arenarius KARG x x x 3
Parasitus kempersi OUDE. x x 2
Pergamasus septentrionalis (OUDE.) x x 2
Pergamasus teutonicus WILL. x x 2
Pergamasus wasmanni (OUDE.) x x 2
Amblyseius messor WAIN. x x 2
Amblyseius meridionalis (BERL.) x x 2
Dendrolaelaps foveolatus LEIT. x x 2
Zercon carpathicus (SELL.) x x 2
Veigaia cervus (KRAM.) x 1
Leioseius minusculus (BERL.) x 1
Leioseius montanulus HIRS. x 1
Platyseius italicus (BERL.) x 1
Antenoseius delicatus BERL. x 1
Amblyseius obtusus (C. L. K.) x 1
Amblyseius aurescens ATHIAS-H. x 1
Amblyseius andersoni (CHANT) x 1
Amblyseius herbarius WAIN. x 1
Halolaelaps marinus (BRADY) x 1
Hypoaspis claviger (BERL.) x 1
Hypoaspis similisetae KARG x 1
Hypoaspis kargi COSTA x 1
Laelaspis astronomicus L. K. x 1
Zercon zelawaiensis SELL. x 1
Zercon fageticola HALA. x 1
In total 78 species 50 55
93

Gamasina species in dune habitats, in comparison with driftline habitats, were not so
abundant, with the exception of two species (Minirhodacarellus minimus (KRAG) and
Dendrolaelaps arenarius KARG). Gamasina species occurring in the dune habitats were
rather different from those in the driftline habitats. That is not surprising, if we take into
account the different ecological conditions there. The impact of the sea decreases roughly
in an inland direction, which leads to the absence of organic material deposited by the sea in
the dune habitats. Vegetation in the primary dunes was poorly represented, on the whole
only single plants were found and there were few places where they formed small communities.
Thus vegetation is the main factor, which determines the organic matter content in
the soil (JUNGERIUS, 1990). The production of organics in the soil is relatively slow and the
primary dunes are poor in nutrients. As known from the literature (ANDRÉ et al., 1994), the
dispersion of Gamasina in sandy habitats shows aggregation to the rhizosphere of plants,
and the density of individuals in bare sand is very low. As is clear from Table 1, the fauna of
the primary dunes was poor. The number of species recorded in the primary dunes was the
lowest among the habitats investigated. The species Rhodacarus reconditus ATHIAS-HENRIOT,
found there, is known as being characteristic for the pioneer stage of succession (CHRISTIAN,
1995). This gives evidence of the initiation of soil-forming processes there.
In the dunes occur species like Leioseius bicolor, Dendrolaelaps arenarius and plant
inhabitants from the genus Amblyseius, which are more or less adapted to the dry soil conditions
with low organic matter content. However, there are also species common for variable
habitats like the ubiquitous Gamasina species (Holoparasitus excipuliger, Rhodacarellus
silesiacus WILMANN, Veigaia nemorensis and Pergamasus vagabundus); species inhabiting
various agroecosystems (Rhodacarus mandibularis BERLESE, R. haarlovi SHCHERBAK, R.
reconditus); forest species (Pergamasus crassipes, P. wasmanni, Hypoaspis aculeifer and
Parazercon sarekensis) and meadow species (Hypoaspis vacua, H. praesternalis and
Dendrolaelaps angulosus WILMANN).
Twenty-three species were found as typical only for the primary and yellow dunes (Table
1). The difference in species composition between the primary and yellow dune fauna is
obvious. Twenty-two species were found in the primary dunes, most of them common also
to the driftline or yellow dune fauna. Two species were found to be common only to the
primary dunes. From the yellow dunes a total of 50 Gamasina species were collected, 18 of
which were recorded only there.
The great differences between the fauna of the primary and yellow dunes can be explained
by variability of the ecological conditions. At the yellow dunes more abundant
vegetation was found, which explains the formation of a larger amount of organic material
in the soil. That, in turn, creates favourable environmental conditions for Gamasina mites
and the number of species recorded was almost as high as in the driftline. The very high
abundances of microarthropods in yellow dunes were also found by KOEHLER et al. (1992).
Comparison between the fauna of Gamasina mites of the Baltic Sea Coast and Riga
Gulf Coast of Kurzeme was made. In these two sites 55 and 50 species, respectively, were
recorded (Table 2). About 1/3 of Gamasina species were found to be common to both
sites. The rest of the species were found only in one of the Kurzeme Coast sites. The
94

Baltic Sea Coast and Riga Gulf Coast of Kurzeme had 28 and 22 species, respectively.
Some species, such as Rhodacarus haarlovi and Minirhodacarellus minimus, occurred
in 4 sampling sites in the yellow dunes, Dendrolaelaps arenarius in 3 sampling sites it
the primary and yellow dunes of the Baltic Sea Coast, and they could be considered as
characteristic for the Baltic Sea Coast of Latvia. Holoparasitus excipuliger is known as
ubiquitous in the fauna of Latvia. The rest of the species do not have a wide range of
distribution (Table 2).
The species in the material from the Riga Gulf Coast of the Kurzeme were rather rare
and could be found in one sampling site only, with the exception of Macrocheles glaber
(MULLER) and Prozercon trägardhi (HALBERT), which were recorded in 2 sampling sites.
The differences between the Riga Gulf Coast and the Baltic Sea Coast of the Kurzeme
could be explained by the differing ecological conditions, which are more severe in the
Baltic Sea Coast habitats. They are swept by the prevailing West winds and are more exposed
to sea floods, which leads to more dynamic soils with a less stable organic content
and a higher salt content. The Riga Gulf Coast climate is milder. There are fewer strong
storms, the water temperature is higher, and the salt content of the water is lower, and the
West winds are not so strong there. Because of such differences, the diversity of Gamasina
mites in both sides of the Kurzeme Coast differs greatly. Species occurring only on one of
these Coasts have selected the most favourable habitats for them.
Data from the previously poorly investigated Coast of Latvia provides an explanation
for such a large number (23) of new species. Thirteen new species from the family
Rhodacaridae were recorded, because of the weak investigation of this family in Latvia so
far. The rest of the new species were common seashore inhabitants, such as Parasitus
halophilus and Parasitus kempersi, or species typical of various habitats. A new Lasioseius
sp. was found only in one sampling site of Kolkasrags in the yellow dunes and its distribution
is currently unknown.
Leioseius bicolor can be considered as the most widely distributed Gamasina mite species
in the Kurzeme Coast habitats (Tables 1, 2). It was found in all the investigated habitats
and sampling sites. Leioseius halophilus and Parasitus halophilus and Thinoseius spinosus
and Leioseius insignis were found in all habitat types and in 7 and 6 sampling sites, respectively.
The rest of the species were found in less than 6 sampling sites.
The highest numbers of Gamasina mites were found in the habitats with well-aerated and
humus-enriched soils, but dry and sandy habitats had a smaller number of species. The
most numerous species were those characteristic of specific habitats, but also a high number
of various species known to be common in inland ecosystems was recorded.
Thus this investigation gives an insight into the diverse groups of Gamasina mites inhabiting
coastal ecosystems and shows the great value of the biological diversity of soil fauna
of the seashore habitats in Latvia.
95

Acknowledgements
This study was supported by the Swedish project “Areas with high biodiversity on the Latvian Baltic Sea
Coast”, as well as by the German project “Biogeography and communities of Collembola (Insecta) and Gamasina
(Acari) in coastal dunes of the Southern Baltic”. The author is very grateful to Dr. Lars Lundquist from the
Department of Systematic Zoology, Lund University for the help given in the determination of some Gamasina
species.
References
ANDRE, H.M., NOTI, M.-I., LEBRUN, P., 1994: The soil fauna: the other last biotic frontier. Biodiversity and Conservation,
3, p. 45-56.
BREGETOVA, N.G., 1977: Identification key of soil inhabiting mites. Mesostigmata. Nauka, Leningrad, 717 pp.
(In Russian).
CHRISTIAN, A., 1995: Succession of Gamasina in coal mined areas in Eastern Germany. Acta Zoologica Fennica,
196, p. 380-381.
COLEMAN, D.C., CROSSLEY, D.A. Jr., 1996: Fundamentals of soil ecology. Academic Press, San Diego, 205 pp.
EITMINAVICHUTE, I.S. (ed.), 1976: Soil invertebrate fauna of the coastal area in the east Baltic region. Vilnius, 172
pp. (In Russian)
HIRSCHMANN, W., 1971: Gangsystematik der Parasitiformes. Acarologie, 82-88, 15, p. 10-42.
JUNGERIUS, P.D., 1990: The characteristics of dune soils. Catena, Suplement 18, (Cremlingen), p. 155-162.
KARG, W., 1993: Acari (Acarina), Milben Parasitiformes (Anactinochaeta) Cohors Gamasina Leach. Raubmilben.
2., überarbeitete Auflage. Gustav Fischer Verlag, Jena, 524 pp.
KOEHLER, H., HOFMANN, S., MUNDERLOH, E., 1992: The soil mesofauna of white-, grey- and brown-dune sites in
Jutland (Denmark) with special reference to the Gamasina (Acari, Parasitiformes). In CARTER, R.W.G., CUR-
TIS, T.G.F., SHEEHY-SKEFFINGTON, M.J. (eds.): Coastal dunes. Balkema, Roterdam, Brookfield, p. 273-281.
KOLODOCHKA, L.A., 1978: Handbook on identifying of plant inhabiting phytoseiid mites. Naukova Dumka, Kiev,
78 pp. (In Russian)
LAPINA, I., 1976a: Gamasin mites of the family Aceosejidae Baker et Wharton, 1952 in the fauna of the Latvian
SSR. Latvijas Entomologs, 19, p. 65-90. (In Russian)
LAPINA, I., 1976b: Free-living gamasin mites of the family Laelaptidae Berlese, 1892 in the fauna of the Latvian
SSR. Latvijas Entomologs, 19, p. 20-64. (In Russian)
LAPINA, I., 1988: Gamasin mites of Latvia. Zinatne, Riga, 198 pp. (In Russian)
MALLOW, D., LUDWIG, D., CROSSLEY, D.A. JR., 1984: Microarthropod community structure in a coastal dune
ecosystem on Jekyll Island, Georgia U.S.A. Pedobiologia, 27, p. 365-376.
MELECIS, V., SPOTE, I., PAULINA, E., 1994: Soil microarthropods as potential bioindicators for coastal monitoring.
In GUDELIS, V., PAVILONSKAS, R., ROEPSTORFF, A. (eds): Abstracts of the International Conference “Coastal
conservation and management in the Baltic region. Klaipedos Universitetas, Klaipeda (Lithuania), p. 111-
115.
PAULINA, E., SALMANE, I., 1999: Collembola and gamasin mites of the restricted area Lake Engure, Latvia. In
ELBERG, K., MARTIN, M., PEKKARINEN, A. (eds): Proceedings of the XXIV Nordic Congress of Entomology.
Eesti Loodusfoto, Tartu (Estonia), p. 145-150.
PUGH, P.J.A., 1985: Studies on the biology of British littoral Acari. Ph. D. thesis, University of Wales.
SALMANE, I., 1996: Gamasin mites (Acari, Gamasina) of Kurzeme coast of the Baltic Sea. Latvijas Entomologs,
35, p. 28-34.
96

Ekológia (Bratislava) Vol. 19, Supplement 4, 97-104, 2000
SPIDERS (ARANEAE) OF THE PEATBOG NATIONAL
NATURE RESERVE ŠVIHROVSKÉ RAŠELINISKO
(SLOVAKIA)
JAROSLAV SVATOŇ 1 , ROMAN PRÍDAVKA 2
1 Kernova 8, 036 01 Martin, Slovakia.
2 Novákova 5, 036 01 Martin, Slovakia.
SVATOŇ J., PRÍDAVKA R.: Spiders (Araneae) of the peatbog National Nature Reserve Švihrovské
rašelinisko (Slovakia). In GAJDOŠ P., PEKÁR S. (eds): Proceedings of the 18th European Colloquium
of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava), Vol. 19, Supplement 4/2000, p.
97-104.
Wetlands and peatbogs belong to the most rare and critically threatened ecosystems in
Slovakia. Their protection became of prime interest in land conservation recently. Some 40
to 50 years ago there were 578 peatbogs registered in Slovakia with an area of more than
4 000 ha. Most of them were located in the lowland Podunajská nížina, Záhorie, in the
valley Horehronské podolie, in the Oravská and Liptovská kotlina Basin as well as in the
High Tatras. During the last 50 years the number and the area of these habitats have dramatically
decreased as a result of intensive agriculture and pollution. All this resulted in the
patchy distribution of such habitats.
From the arachnological point of view, very little attention has been paid to wetland
habitats in Slovakia. An exception is a study of JEDLIČKOVÁ (1988) which summarised the
seasonal occurrence of 283 species of spiders collected from six biotopes of Jurský Šúr in
the lowland of Podunajská nížina, and the paper of SVATOŇ, PRÍDAVKA (1997) which deals
with the arachnofauna of the Kláštorské lúky National Nature Reserve located in the
Turčianska kotlina Basin. A number of papers have treated these habitats only superficially
(GAJDOŠ, 1988, 1994; GAJDOŠ et al., 1984a, b, 1988, 1992; MILLER, 1935, 1936, 1937, 1958,
1967; MILLER, KRATOCHVÍL, 1939, 1940; MILLER, SVATOŇ, 1974; SVATOŇ, 1981, 1983a, b, c,
1984, 1985; SVATOŇ et al., 1998; SVATOŇ, MAJKUS, 1988; SVATOŇ, MILLER, 1979; ŽITŇANSKÁ,
1977, 1981a, b).
Stimulated by the Slovak Conservation Agency, residing in Liptovský Mikuláš, we began
to investigate the spider fauna of the National Nature reserve Švihrovské rašelinisko in
1995 and continued until 1999.
97

This National Nature Reserve is situated at the border of the Liptovská kotlina Basin in
the western part of the High Tatras near the village Jamník at 600-800 m a.s.l. (grid no.
6884). The peatbog originated from the alluvium of the brook Čierny potok, in the middle
of a spruce forest. Phytocenologically it is a transitional peatbog characterised by Caricion
fuscae and Caricion lasiocarpae vegetation types. The few trees which grow on the peatbog
are Picea excelsa, Pinus silvestris and Alnus sp.
The spiders were collected at 6 sites (S1- moor biotope, S2- Alnetum incanae biotope,
S3- central peatbog, S4- border of the spruce forest, S5- spruce forest, S6- meadows surrounding
the brook) by means of pitfall traps, sweeping, beating of tree branches, sieving
and individual collecting in order to obtain as many species as possible. The study sites
were visited at one month intervals between May and October when the traps were emptied.
Species nomenclature is according to PLATNICK (1997).
During five years, 3 564 individuals of spiders belonging to 180 species (20 families)
were collected in total (Table 1). 694 individuals were juvenile, and thus could not be
identified into a species level. According to BUCHAR’S (1992) classification of
thermopreference, 59 species (32.7%) were psychrophilous (P), 43 species (23.9%) were
mesophilous (M), 67 species (37.8%) were unspecified (N), and 5 species (2.2%), namely
Entelecara congenera (O. P.-CAMBRIDGE), Metopobactrus ascitus (KULCZYŃSKI), Talavera
sp., Tegenaria domestica (CLERCK), and Xysticus sp. could not be classified. Remarkable is
the occurrence of 6 species (3.3%) which are characterised as thermophilous (T): Alopecosa
trabalis (CLERCK), Araniella opisthographa (KULCZYŃSKI), Enoplognatha thoracica (HAHN),
Meioneta fuscipalpis (C. L. KOCH), Steatoda castanea (CLERCK) and Xysticus lanio C. L.
KOCH.
Of the six study sites, the central part of the peatbog (S3) was found to be most diverse
in spider species as 138 (76.7%) species were recorded there. On the other sites only 20-70
species were found. The poorest species composition (14 species) was observed on the
Alnetum incanae biotope (S2).
From the faunistic point of view several spider species, such as Bolyphantes luteolus
(BLACKWALL), Ceratinopsis stativa (SIMON), Emblyna brevidens (KULCZYŃSKI), Entelecara
erythropus (WESTRING), Entelecara media KULCZYŃSKI, Hilaira excisa (O. P.-CAMBRIDGE),
Pirata uliginosus (THORELL), Poeciloneta variegata (BLACKWALL), Sitticus caricis (WESTRING)
and Theridion mystaceum L. KOCH are of a remarkable importance because they are known
only from few localities in Slovakia. Two species, namely Gnaphosa nigerrima L. KOCH
and Heliophanus dampfi SCHENKEL, are new to Slovakia.
The investigation of the Švihrovské rašelinisko peatbog will continue. We plan to focus
on the surrounding wet biotopes. It is important to stress that arachnological research should
be focussed on other peatbogs in Slovakia as well, particularly in the Orava region and the
western part of Slovakia.
98

T a b l e 1. List of species collected from 6 sites (S1-S6) of the peatbog. Numbers represent ♂/♀. TP stands
for thermopreference classification after BUCHAR (1992). See text for explanation of classifiation letters.
Species S-1 S-2 S-3 S-4 S-5 S-6 TP
ULOBORIDAE
Hyptiotes paradoxus (C. L. K.) –/1 P
THERIDIIDAE
Enoplognatha ovata (CL.) –/4 11/16 7/7 6/3 3/2 N
Enoplognatha thoracica (HAHN) –/2 T
Euryopis flavomaculata (C. L. K.) –/1 –/1 N
Neottiura bimaculata (L.) –/2 –/4 –/2 N
Robertus arundineti (O. P.-CBR.) 1/– N
Steatoda bipunctata (L.) 1/2 M
Steatoda castanea (CL.) –/1 T
Theridion impressum L. K. 4/6 N
Theridion mystaceum L. K. –/1 M
Theridion pinastri L. K. 1/3 M
Theridion sisyphium (CL.) –/1 6/14 1/13 1/1 –/2 N
Theridion tinctum (WALCK.) 1/9 –/6 –/2 –/2 N
Theridion varians HAHN 5/17 N
LINYPHIIDAE
Agyneta subtilis (O. P.- CBR.) 1/5 1/5 –/1 P
Bathyphantes approximatus (O. P.- CBR.) –/1 P
Bathyphantes nigrinus (WESTR.) –/3 N
Bolyphantes alticeps (SUND.) 3/4 P
Bolyphantes luteolus (BL.) –/1 P
Centromerus arcanus (O. P.- CBR.) –/1 3/5 P
Centromerus levitarsis (SIM.) 2/1 P
Centromerus sylvaticus (BL.) –/1 N
Ceratinopsis stativa (SIM.) –/2 P
Cnephalocotes obscurus (BL.) 1/– 5/– N
Dicymbium nigrum (BL.) 1/– N
Dicymbium tibiale (BL.) –/1 –/2 N
Diplocephalus latifrons (O. P.- CBR.) –/2 N
Diplocephalus permixtus (O. P.- CBR.) –/1 P
Diplostyla concolor (WID.) –/1 N
Dismodicus bifrons (BL.) 1/– P
Dismodicus elevatus (C. L. K.) 1/1 P
Drapetisca socialis (SUND.) –/1 P
Entelecara acuminata (WID.) –/1 –/2 M
Entelecara congenera (O. P.- CBR.) –/3 –/1 –/1 3/5 ?
Entelecara erythropus (WESTR.) –/2 –/3 M
Entelecara media KULCZ. –/1 P
Erigone atra BL. 1/– A
Erigone dentipalpis (WID.) 1/– A
Erigonella ignobilis (O. P.- CBR.) –/2 P
Hilaira excisa (O. P.- CBR.) 2/– P
Kaestneria dorsalis (WID.) –/1 M
Lepthyphantes alacris (BL.) 2/6 P
Lepthyphantes cristatus (MGE.) 3/2 2/8 P
Lepthyphantes crucifer (MGE.) –/3 M
Lepthyphantes mengei KULCZ. 1/– A
Lepthyphantes obscurus (BL.) –/1 P
Lepthyphantes tenebricola (WID.) 2/1 P
Lepthyphantes zimmermanni BERTH. –/1 P
99

T a b l e 1./2 Cont.
Species S-1 S-2 S-3 S-4 S-5 S-6 TP
Leptorhoptrum robustum (WESTR.) 3/– P
Linyphia hortensis SUND. –/1 M
Linyphia triangularis (CL.) 4/3 9/22 7/7 1/1 1/1 N
Lophomma punctatum (BL.) 5/3 P
Macrargus rufus (WID.) 2/1 N
Maso sundevalli (WESTR.) 2/– P
Meioneta fuscipalpis (C. L. K.) –/1 T
Meioneta rurestris (C. L. K.) –/3 N
Metopobactrus ascitus (KULCZ.) 1/– ?
Micrargus herbigradus (BL.) 1/1 1/1 P
Microlinyphia pusilla (SUND.) 1/13 N
Neriene peltata (WID.) –/1 M
Neriene radiata (WALCK.) 1/4 –/1 M
Notioscopus sarcinatus (O. P.- CBR.) –/1 15/28 –/4 P
Oedothorax agrestis (BL.) 2/– M
Oedothorax apicatus (BL.) 1/– 1/– M
Oedothorax gibbosus (BL.) 1/4 3/3 7/21 2/3 P
Oedothorax retusus (WEST.) 1/– P
Pelecopsis radicicola (L. K.) 1/– N
Pityohyphantes phrygianus (C. L. K.) 2/– 1/5 1/1 –/2 P
Pocadicnemis pumila (BL.) –/3 1/– N
Poeciloneta variegata (BL.) –/3 P
Tallusia experta (O. P.- CBR.) 5/– P
Tapinopa longidens (WID.) 1/– P
Walckenaeria acuminata BL. –/1 1/1 N
Walckenaeria antica (WID.) 1/– N
Walckenaeria atrotibialis (O. P.- CBR.) 2/2 6/13 –/2 M
Walckenaeria furcillata (MGE.) –/1 N
Walckenaeria kochi (O. P.- CBR.) 1/1 4/8 –/2 P
Walckenaeria mitrata (MGE.) –/1 N
Walckenaeria nudipalpis (WESTR.) –/1 7/2 P
TETRAGNATHIDAE
Metellina mengei (BL.) 1/4 P
Metellina segmentata (CL.) 2/2 P
Pachygnatha listeri SUND. 3/– –/2 6/9 1/4 1/– –/1 M
Tetragnatha extensa (L.) 2/5 –/2 M
Tetragnatha montana SIM. 1/1 M
Tetragnatha obtusa C. L. K. 2/1 –/3 –/2 M
Tetragnatha pinicola L. K. 4/6 –/1 –/1 N
ARANEIDAE
Aculepeira ceropegia (WALCK.) 3/27 1/1 1/4 P
Araneus alsine (WALCK.) –/1 2/6 1/7 M
Araneus diadematus CL. 1/2 8/30 –/1 –/2 N
Araneus marmoreus CL. 1/11 6/75 1/1 2/5 –/2 M
Araneus quadratus CL. –/2 15/43 –/2 –/1 –/1 N
Araneus sturmi (HAHN) P
Araniella alpica (L. K.) 4/10 1/1 –/1 P
Araniella cucurbitina (CL.) 3/4 1/3 1/1 1/– N
Araniella displicata (HENTZ) –/1 N
Araniella opisthographa (KULCZ.) –/3 T
Cyclosa conica (PALL.) 1/– 1/4 –/3 1/– P
Gibbaranea omoeda (THOR.) –/1 P
Hypsosinga sanguinea (C. L. K.) –/2 N
100

T a b l e 1./3 Cont.
Species S-1 S-2 S-3 S-4 S-5 S-6 TP
Larinioides patagiatus (CL.) –/6 M
Mangora acalypha (WALCK.) 1/4 –/1 N
LYCOSIDAE
Alopecosa aculeata (CL.) –/1 –/1 M
Alopecosa pulverulenta (CL.) –/3 1/– –/4 1/3 N
Alopecosa trabalis (CL.) –/1 1/1 T
Pardosa amentata (CL.) 1/6 P
Pardosa lugubris (WALCK.) –/1 –/1 N
Pardosa monticola (CL.) –/1 N
Pardosa palustris (L.) –/1 N
Pardosa prativaga (L. K.) –/1 P
Pardosa pullata (CL.) –/8 15/16 56/98 30/23 2/3 N
Pirata hygrophilus THOR. 3/10 1/20 40/65 13/43 P
Pirata latitans (BL.) 1/9 M
Pirata piraticus (CL.) 6/10 P
Pirata piscatorius (CL.) 2/– M
Pirata uliginosus (THOR.) 1/5 25/6 –/3 –/1 P
Trochosa spinipalpis (O. P.- CBR.) –/3 54/24 –/5 P
Trochosa terricola THOR. –/1 1/7 –/2 N
Xerolycosa nemoralis (WESTR.) 1/2 –/1 N
PISAURIDAE
Dolomedes fimbriatus (CL.) –/9 2/72 –/1 –/16 P
Pisaura mirabilis (CL.) 2/2 N
AGELENIDAE
Agelena labyrinthica (CL.) 2/– 1/– M
Tegenaria domestica (CL.) 1/– ?
Tegenaria silvestris L. K. –/1 N
CYBAEIDAE
Cybaeus angustiarum L. K. 10/3 1/– P
HAHNIIDAE
Antistea elegans (BL.) 21/7 13/8 116/99 67/54 P
Cryphoeca silvicola (C. L. K.) 1/2 P
DICTYNIDAE
Cicurina cicur (FABR.) –/2 N
Dictyna arundinacea (L.) 1/1 N
Dictyna pusilla THOR. –/5 1/1 1/2 –/2 P
Emblyna brevidens (KULCZ.) –/1 1/– M
Nigma flavescens (WALCK.) –/1 N
AMAUROBIIDAE
Callobius claustrarius (HAHN) 1/2 P
Coelotes inermis (L. K.) 12/4 P
Coelotes terrestris (WID.) 5/3 1/– 12/4 8/2 N
LIOCRANIDAE
Agroeca brunea (BL.) 2/– –/1 N
Phrurolithus festivus (C. L. K.) –/2 N
CLUBIONIDAE
Cheiracanthium erraticum (WALCK.) 2/44 1/5 2/10 M
Clubiona caerulescens L. K. –/1 N
Clubiona diversa O. P.- CBR. –/2 N
Clubiona germanica THOR. 1/1 1/1 –/1 M
Clubiona lutescens WESTR. –/1 1/32 –/3 –/2 M
Clubiona neglecta O. P.- CBR. 1/3 N
101

T a b l e 1./4 Cont.
Species S-1 S-2 S-3 S-4 S-5 S-6 TP
Clubiona pallidula (CL.) –/1 –/1 M
Clubiona reclusa O. P.- CBR. –/4 1/33 2/29 P
Clubiona stagnatilis KULCZ. –/2 M
Clubiona subsultans THOR. 3/5 P
Clubiona subtilis L. K. –/1 M
Clubiona terrestris WESTR. –/1 N
Clubiona trivialis C. L. K. 4/– 15/10 2/2 1/– –/1 N
GNAPHOSIDAE
Drassodes pubescens (THOR.) 2/– N
Gnaphosa nigerrima L. K. 1/5 M
Zelotes clivicola (L. K.) 1/– P
Zelotes latreillei (SIM.) 1/– A
ZORIDAE
Zora spinimana (SUND.) –/1 2/1 –/2 A
HETEROPODIDAE
Micrommata virescens (CL.) –/2 2/33 A
PHILODROMIDAE
Philodromus aureolus (CL.) –/1 –/1 M
Philodromus cespitum (WALCK.) –/2 M
Philodromus collinus C. L. K. 18/18 2/4 2/3 1/2 A
Philodromus margaritatus (CL.) –/1 1/25 –/2 M
Tibellus oblongus (WALCK.) –/1 9/29 –/2 –/4 M
THOMISIDAE
Diaea dorsata (FABR.) 1/4 –/1 M
Misumena vatia (CL.) –/1 2/13 –/1 –/1 –/1 A
Ozyptila trux (BL.) 1/– 4/2 P
Xysticus audax (SCHR.) 2/6 A
Xysticus bifasciatus C. L. K. –/1 A
Xysticus cristatus (CL.) –/1 1/3 –/3 1/2 A
Xysticus lanio C. L. K. 1/1 T
Xysticus sp. –/3 4/29 –/5 –/8 M
Xysticus ulmi (HAHN) 1/– M
SALTICIDAE
Bianor aurocinctus (OHL.) 1/– 1/– A
Dendryphantes rudis (SUND.) 2/– 10/21 4/9 –/6 A
Euophrys frontalis (WALCK.) –/1 A
Evarcha arcuata (CL.) 1/1 M
Evarcha falcata (CL.) 5/2 26/20 2/1 3/3 2/1 A
Heliophanus dampfi SCHENK. –/2 P
Heliophanus dubius C. L. K. –/4 M
Neon reticulatus (BL.) 1/4 M
Salticus cingulatus (PANZ.) –/2 M
Sitticus caricis (WESTR.) 1/– 8/3 P
Talavera sp. 1/– 2/– P
102

References
BUCHAR, J., 1992: Komentierte Artenliste der Spinnen Böhmens (Araneida). Acta Univ. Carol., Biol. (Praha), 36,
p. 383-428.
GAJDOŠ, P., 1988: Composition of spiders (Aranei) of the locality Úkropová in the Ponitrie Protected Landscape
Area. Rosalia (Nitra), 5, p. 117-127. (In Slovak)
GAJDOŠ, P., 1994: The epigeic spider communities of lowlands forests in the surrouding of the Morava river.
Ekológia (Bratislava), 13, Supplement 1, p. 135-144.
GAJDOŠ, P., SVATOŇ, J., KRUMPÁL, M., 1984a: New and unusual records of spiders from Slovakia I. (Araneae:
Atypidae, Dictynidae, Gnaphosidae, Clubionidae, Zoridae, Salticidae, Lycosidae). Biológia (Bratislava), 39,
2, p. 223-225.
GAJDOŠ, P., SVATOŇ, J., KRUMPÁL, M., 1984b: New and unusual records of spiders from Slovakia II. (Araneae:
Linyphiidae, Micryphantidae). Biológia (Bratislava), 39, 6, p. 633-635.
GAJDOŠ, P., SVATOŇ, J., MAJKUS, Z., 1988: Spiders (Araneae) of the surroundings of Nová Sedlica (East Carpathian).
Zborník Východoslovenského múzea v Košiciach, Prírodné vedy, (Košice), 29, p. 73-90. (In Slovak)
GAJDOŠ, P., SVATOŇ, J., ŽITŇANSKÁ, O., KRUMPÁLOVÁ, Z., 1992: Spiders (Araneae) of the Danubian plain. Entom.
Probl., (Bratislava), 23, p. 39-60.
JEDLIČKOVÁ, J., 1988: Spiders (Aranei) of the Jurský šúr Nature Reserve (Czechoslovakia). Biol. Práce (Bratislava),
34, 3, p. 1-170.
MILLER, F., 1935: Contribution to the arachnological research of south part of Bohemia. Věda přír. (Praha), 16, 1,
p. 9-21. (In Czech)
MILLER, F., 1936: Another contribution to the spider fauna of the south part of Czech. Věda přír. (Praha), 17, 4,
p. 98. (In Czech)
MILLER, F., 1937: Neue Spinnenarten (Araneae) aus der Čechoslovakischen Republik II. Festschr. Strand (Riga),
2, p. 563-570.
MILLER, F., 1958: Beitrag zur Kenntnis der tschechoslovakischen Spinnenarten aus der Gattung Centromerus
Dahl. Čas. českoslov. Společ. ent. (Praha), 55, 1, p. 71-91.
MILLER, F., 1967: Studien über die Kopulationsorgane der Spinnengattung Zelotes, Micaria, Robertus und Dipoena
nebst Beschreibung einiger neuen oder unvollkommen bekannten Spinnenarten. Přírodov. Pr. Úst. ČSAV
Brno, N. S. (Praha), 1, 7, p. 251-298.
MILLER, F., KRATOCHVÍL, J., 1939: Several new spiders for Czechoslovakia. Sbor. ent. Odd. Nár. Mus. (Praha), 17,
p. 234-244. (In Czech)
MILLER, F., KRATOCHVÍL, J., 1940: Ein Beitrag zur Revision der mitteleuropäischen Spinnenarten aus der Gattung
Porrhomma E. Sim. Zool. Anz. (Leipzig), 130, 7-8, p. 161-190.
MILLER, F., SVATOŇ, J., 1974: Contribution to the knowledge of spider fauna of Súľovské skaly. In: Štollman, A.
(ed.), Súľovské skaly – Štátna prírodná rezervácia. Monogr. Vlastiv. zbor. Považia (Martin), 1, p. 243-284.
(In Slovak, summary in German).
PLATNICK, N.I., 1997: Advances in Spider Taxonomy 1992-1995, with Redescriptions 1940-1980. New York
Entom. Society and Amer. Mus. of Nat. Hist. Publ., New York, 976 pp.
SVATOŇ, J., 1981: Einige neue oder unvollkommen bekannte Spinnenarten aus der Slowakei. Biológia (Bratislava),
36, 2, p. 167-177.
SVATOŇ, J., 1983a: Spider fauna (Arachnida, Araneae) of the State Nature Reserve Čierny kameň in Veľká Fatra.
Ochr. Prír. (Bratislava), 4, p.119-134. (In Slovak, summary in German, English and Russian.)
SVATOŇ, J., 1983b: Spiders (Araneida) of the central part of the High Tatras. Zbor. Prác o Tatran. nár. Parku
(Martin), 24, p. 95-153. (In Slovak, summary in German, English and Russian.)
SVATOŇ, J., 1983c: Weitere neue oder unvollkommen bekannte Spinnenarten aus der Slowakei. Biológia (Bratislava),
38, 6, p. 569-580.
SVATOŇ, J., 1984: Spiders (Araneida) of Turčianská kotlina Basin, 1. part (Mygalomorpha: Atypidae. Cribellatae:
Amaurobiidae, Dictynidae, Uloboridae). Kmetianum (Martin), 7, p. 217-225. (In Slovak)
SVATOŇ, J., 1985: Outline of the spider fauna (Araneida) of the proposed protected site Urpín near Banská
Bystrica. Stredné Slovensko (Martin), 4, p. 237-259. (In Slovak)
103

SVATOŇ, J., FRANC, V., KRAJČA, A., KRUMPÁLOVÁ, Z., KRÍŽOVÁ, V., PEKÁR, S., STAŇKOVÁ, E., SVATOŇOVÁ, E., 1998:
To the contribution of spiders (Araneae) of Nature Reserve Kysuce. Vlast. zborník Považia (Žilina), 19, p.
101-115. (In Slovak, summary in English.)
SVATOŇ, J., MAJKUS, Z., 1988: Contribution to the knowledge of spiders (Araneae) of Plešivská planina. Ochr.
Prír. – Výsk. Práce z ochr. prír. (Bratislava), 6B, p. 203-242. (In Slovak, summary in German, English and
Russian.)
SVATOŇ, J., MILLER, F., 1979: Spider fauna of the State Nature Reserve Rozsutec. Kmetianum (Martin), 5, p. 177-
198. (In Slovak, summary in German and Russian.)
SVATOŇ, J., PRÍDAVKA, R, 1997: Spider fauna (Araneae) of the State Nature Reserve Kláštorské lúky in the basin
Turčianska kotlina. In KADLEČÍK, J. (ed.): Zborník „Turiec 1996“, MŽP SR, Bratislava, p. 131-143. (In Slovak)
ŽITŇANSKÁ, O., 1977: Spider fauna of the surroundings of Zemplínska Šírava. Acta Fac. rer. nat. Univ. Comen.,
Zool. (Bratislava), 22, p. 69-85. (In Slovak, summary in Russian.)
ŽITŇANSKÁ, O., 1981a: Studie über die Lebensgemeinschaften der Spinnen in dem Waldtyp Querco-carpinetum
in Báb bei Nitra. Acta Fac. rer. nat. Univ. Comen., Zool. (Bratislava), 25, p. 39-59.
ŽITŇANSKÁ, O., 1981b: Zusammensetzung der Lebensgemeinschaften der Spinnen (Araneida) in dem Gebiet
Liptovská Mara. Acta Fac. rer. nat. Univ. Comen., Zool. (Bratislava), 25, p. 61-81.
104

Ekológia (Bratislava) Vol. 19, Supplement 4, 105-110, 2000
DATA ON THE BIOLOGY OF LARINIA JESKOVI
MARUSIK, 1986 (ARANEAE: ARANEIDAE) FROM
THE REED BELTS OF LAKE BALATON
CSABA SZINETÁR
Department of Zoology Berzsenyi College, H-9701 Szombathely, Károlyi Gáspár tér 4. Hungary. E-mail:
szcsaba@fs2.bdtf.hu
Introduction
Abstract
SZINETÁR C.: Data on the biology of Larinia jeskovi Marusik, 1986 (Araneae: Araneidae) from the
reed belts of Lake Balaton. In GAJDOŠ P., PEKÁR S. (eds): Proceedings of the 18th European Colloquium
of Arachnology, Stará Lesná, 1999. Ekológia (Bratislava), Vol. 19, Supplement 4/2000, p.
105-110.
Observations were made of Larinia jeskovi Marusik, 1986 in Hungary (Balatongyörök, UTM
XM87). The study describes the habitat, activity and phenological characteristics of this rare orb
web spider observed in the reed belts of Lake Balaton.
As part of a complex research project into the fauna of Hungarian reeds, the spiders of the
reed belt of Lake Balaton have been studied by the author since 1992. Some interesting observations
were previously reported on the fauna in 1995 (SZINETÁR, 1995). Several zoologists
dealt with the research of the surroundings of Lake Balaton in the nineties. The observations
of this research, together with an account of the collections made by Imre Loksa and István
Loksa in 1990-91, were summarised by SZATHMÁRY (1995). In the summer of 1996 two female
and two male Larinia jeskovi were collected during nocturnal observations and 9 further female
specimens were observed. This rare species was described from the Amur River basin
(Russia) by MARUSIK (1986). In Europe L. jeskovi has been discovered and investigated by
KUPRYJANOWICZ (1995, 1997). The European population of L. jeskovi could belong to a different
species (MARUSIK, pers. com.). One female specimen has been kept under experimental conditions
to obtain a better understanding of the process of web building. In the summer of 1997
data on the species were collected at the same habitat for a longer time. During this period
several hundred specimens were observed along the section of lakeshore under investigation.
In this study I summarise the data collected during these two years.
105

Study area
The study area is situated in the north-western region of Lake Balaton, in the vicinity of
Balatongyörök (Lat.47°10’ N, Long. 17°20’ E., UTM XM 78).
The habitat where observations were made is a typical reedy part of the northern shore.
The homogeneous reed belt has virtually disappeared from this shore section. Only some
metre-wide spots can be sporadically found. This discontinuous reedy zone is completely
washed by the waves and it creates a debris barrier beach parallel to the shore. Outwards,
a sedge-reed strip of land of variable width can be found, which turns into a marsh meadow
and fen meadow. The strip between the barrier beach and the fen meadow is a permanently
flooded area, even in the summer. In some places this zone is one hundred metres wide. Its
water is cooler than elsewhere and has a brownish colour caused by humic acids. In the
sedge-reed strip Typha angustifolia is frequent and Cladium mariscus can be found sporadically
as well. In some places T. angustifolia forms almost homogenous, reed-free stands.
Typha latifolia can also be found in limited numbers in the reedy area. On the clumps of
Carex elata, Hydrocotyle vulgaris and Pedicularis palustris are frequent. In the fragments
of the swampy meadow several orchid species (Dactylorhiza incarnata, Orchis laxiflora,
Epipactis palustris) and Eriophorum latifolium can be found. The major part of the area
marked out for data collection was covered by Caricetum elatae typhaetosum angustifoliae.
Material and methods
Since the species is exclusively nocturnal, it was only investigated at night. Probably, this is the reason
why the species has only recently been found. The research was carried out with the help of a torch, generally
between 10 and 12 p.m. The field observations were made on 21-23 August, 1996. In the summer of 1996
a total of 13 specimens were found and observed (11 female, 2 male) in the examined reed belt. Data for the
webs of eight females were collected in the surveyed habitat. From 24 August, 1996 a female specimen was
kept in an artificial habitat for 5 days to observe web-building and feeding at night. A stem of T. angustifolia
was planted in a pot filled with water. The pot had a diameter of 40 cm and height of 15 cm. The spider was
acclimatised here. In the summer of 1997, between 14 July and 28 August, the research was carried out in the
same location as in the previous year and in the surroundings along about 2-3 kilometres of a shore section. In
the area several hundreds of specimens of L. jeskovi were observed. In order to get exact data, an area was
marked out that was undisturbed by anglers and bathers. Data were collected six times here between 19 July
and 29 August. The sampling area was a 2 metre-wide and 90 metre-long strip, perpendicular to the lake. The
area was marked out with a rope at a height of 1 metre. The designated area was thoroughly examined at
night, using torches for illumination. During observation periods in the summer of 1997, data on the web sites
of 163 specimens were recorded. On the basis of this, we have factual information on the webs of 176 specimens
(1996-97). In addition, at least the same number of specimens were observed along the section of shore
examined. I recorded the exact location of the Larinia specimens, the distance between the hub of the web and
the water level, the plant species the web was fastened to, and the behaviour of the animals. In the designated
area no animals were collected. Two persons carried out the research each time, examining the sample area
with torches. Only rainless and windless nights were adequate for data collection because the animals do not
build their webs when the wind blows or it rains, and they quickly demolish their webs when the weather
changes and they withdraw to the vegetation zone. During the research period (July and August) we did not
manage to catch L. jeskovi specimens during the daytime. During nocturnal collection with sweep-netting
106

some specimens (non-quantitative sample) were caught. In the autumn of 1996 and 1997 daytime research
has been carried out for finding the egg sacs.
Results and discussion
Phenology
My observation data relate to the period between 26 June and 10 October only. Between
26 June and 24 July only juvenile specimens were found. During July these were
generally in the subadult stage (on the male spiders the swollen palpal organs were conspicuous).
On 29 July fully developed males were also found. The majority of female
spiders were still subadults. The adult male spiders were typical vagrants, but a fully
developed male was found in a small web as well, and it was in a typical position on the
hub. During August males were found in the webs of females on several occasions (for
instance from the spiders observed on 29 August, 9 were males. 5 were vagrants, 2 were
in their own web, and 2 at the edge of the web of females). The cocoon of the species
could not be found. It is presumed that the females lay their egg sacs in September. During
October 1997 daytime research was carried out in the area using sweep-netting. With
sweep-netting at a height of 50 cm I managed to catch 3 young L. jeskovi. On the basis of
their colour, shape and markings it was obvious that they were juvenile specimens from
the 1. or 2. stage of L. jeskovi.
Daily activity
According to my observations, in the testing period (subadult and adult phase) L. jeskovi
builds its web only at night. In the test area I did not manage to observe the animals during
the daytime. The female specimen reared under experimental conditions spent the day near
the water level, motionless, in a resting position. It became active during the half-hour after
sunset. Firstly only slow stretching (smaller changes of position) was observed. Web building
began 40-50 minutes after sunset and lasted for about 15-25 minutes. The building of
the main and temporary spirals took place very quickly. After building the main spiral, the
spider takes an upside-down position on the hub of the web. Like the other cross spiders, it
wraps its prey and takes it to the hub. The web is relatively weak, and is easily damaged by
the wind and by prey animals. The observed spider dismantled the web before dawn. 1.5-2
hours before sunrise the web could no longer be found. Between 17-24 July 1997 (sunset
was 8.42 p.m. on 19 July) the web was actively built between 9.15 and 9.30 p.m. Between
27-29 August (sunset was 7.38 p.m.) the webs were ready after 8.45 p.m. When it was
windy or rainy, they did not build webs. When the wind strength was increasing during the
night, they quickly dismantled their webs. This prevented us from collecting data on several
occasions.
107

108
Typha angustifolia Phragmites australis
Carex elata Typha latifolia
30%
16%
1%
53%
Fig.1. Web-site selection of Larinia jeskovi (14.07.-
29.08.1997, Balatongyörök).
Height of hub (cm)
250
200
150
100
50
0
21.07-24.07 29.07-28.08
Fig. 2. Mean height (± SD) of web hubs (of Larinia
jeskovi (21.07-24.07: only juveniles, 29.07-28.08:
adult males and subadult and adult females).
Population density
14
12
10
8
6
4
2
0
21.07. 24.07. 29.07. 28.08.
Fig.3. Mean population density (± SD) of Larinia jeskovi
at Lake Balaton (number of specimens/20m 2 ).
Website selection
The webs of female specimens found in
the summer of 1996 were all on T.
angustifolia. Some of the webs were fastened
to bulrush and reed at the same time.
In the area designated in the summer of 1997
we managed to observe the choice of plants
by 159 specimens. Between 14 July and 29
August, 52% of the observed adult and subadult
specimens fastened their webs to T.
angustifolia, 30% to reeds, 17% to C. elata,
1% to T. latifolia. From this it is clear that
this species prefers T. angustifolia (Fig. 1).
This choice can be explained by the fact that
the closing of the upper level of the vegetation
is disadvantageous for the species. The
closing of the vegetation was more significant
in the case of the reed in the examined
habitat than at places where the bulrush was
dominant at the upper level. The distance
between the hub and the water level depends,
of course, on the plant. Adults were usually
found on bulrush and reed. In 28% of cases
the height of the webs observed up to 24
July was less than 100cm, after 29 July it
was only 3.4%. In the case of the webs examined
in 1996 the average distance between
the hub and water level was 113.7
(±17.4) cm. In 1997 the height of 158 webs
was recorded in the test area between 19
July and 29 August. The distance between
the hub of the web and the water level was
139cm (138.89 ±44.54). The height of the
web found in the highest place was 225cm,
the height of the web found in the lowest
place was 40cm. The average height of the
webs observed between 29 July and 28
August (they were already adults) was
greater (159.15 ±36.65). On the basis of this
observation it can be concluded that webs
of adults were higher than those of subadults
(133.96 ±41.72) (P

Web-structure and building behaviour
L. jeskovi builds its web exclusively at night. Every night it builds its typical web, and in the
morning it recycles the web by ingesting it together with the frame threads. If it is disturbed by
wind or rain during the night, it demolishes the web. With artificial illumination the dismantling
of the web was also witnessed. This is a typical, vertical orb web. Its shape is generally
oval and extended vertically, the shape depends on the plant to which the spider has fastened
the web. Webs fastened to bulrush and reed are more stretched vertically than those fastened
to sedge. The web has relatively few radii. Webs with 18 radii (17.77 ±1.78) are the most
frequent. The maximum was 21, and the minimum was 15 radii. Usually there were some thin
threads across the centre of the web hubs. But sometimes the hub had a hole of irregular shape
in the centre. There is a relatively wide free zone between the hub and the main spirals. The
diameter of the whole capture area of the webs built by females on T. angustifolia was 38 cm
vertically (38.2 ±6.7), and 27 cm horizontally (26.7 ±4.5). The capture area was wider under
the hub. Its development also depends on the plant to which it is attached.
Population density
The density of L. jeskovi in the sample area designated in 1997 is given in Fig. 3. The
density of L. jeskovi (specimens/20 m 2 ) decreased between 29 July and 28 August. The
number of observed Larinia specimens in five zones of reed belt (from the swampy meadow
to the water) is shown in Fig. 4.
Further orb web species of the examined reed belt
Since 1992 the following orb web species have been found in the examined reed belt
(from the water to the swampy meadow): Tetragnatha striata L. KOCH, T. shoshone (LEVI),
Fig. 4. The number of observed
Larinia specimens in five zones of
reed belts at four different dates.
Number of specimens
16
14
12
10
8
6
4
2
0
21.07.1997 24.07.1997
29.07.1997 27.08.1997
1-10 m 10-20 m 20-30 m 30-40 m 40-50 m
109

T. reimoseri (ROSCA), T. extensa (LINNAEUS), T. nigrita LENDL, Larinioides ixobolus (THORELL),
Larinioides folium (SCHRANK) (=L. suspicax (O.P.-CAMBRIDGE), Larinia jeskovi MARUSIK,
Larinia bonneti SPASSKY, Singa nitidula (C. L. KOCH), Argiope bruennichi (SCOPOLI), Cyclosa
oculata (WALCKENAER), Araneus quadratus CLERCK, Cercidia prominens (WESTRING). The
species were differentiated from each other in terms of horizontal and vertical web site
locations, and in relation to daily activity. The distribution and activity of L. jeskovi overlapped
with that of only T. reimoseri, L. folium, S. nitidula and L. bonneti.
Acknowledgements
The author would like to express his thanks to Yuri Marusik and Janus Kupryjanowicz for help in connection
with Larinia jeskovi, to Samuel Zschokke in connection with web building of this species, as well as to his wife
and father for technical assistance, and to Ferenc Samu for his constructive comments on the manuscript.
The author was Bolyai Fellow of HAS.
This work was supported by Scientific Committee of Berzsenyi College.
References
KUPRYJANOWICZ, J., 1995: Larinia jeskovi Marusik, 1986, a spider species new to Europe (Araneae: Araneidea).
Bull. Br. arachnol. Soc., 10, 2, p. 78-80.
KUPRYJANOWICZ, J., 1997: Spiders of the Biebrza National Park - species new and rare to Poland. In ŻABKA, M.
(ed.): Proc. 16th Europ. Coll. Arachnol., Siedlce, 1996, p. 183-194.
MARUSIK, Yu.M., 1986: The orb-weaver genus Larinia Simon in the USSR (Aranei, Araneidea). Spixiana, 3, p.
245-254.
SZATHMÁRY, K., 1995: The spider (Araneae) fauna of the shore of Lake Balaton, Hungary. Opusc. Zool. Budapest,
27-28, p. 65-70.
SZINETÁR, Cs., 1995: Some data on the spider fauna of reeds in Hungary. I. Interesting faunistic data from the
reeds of Lake Balaton. Folia ent. Hung., 56, p. 205-209.
110