Next Article in Journal
Various Energy-Saving Approaches to a TFT-LCD Panel Fab
Previous Article in Journal
Integrated Land Governance for Eco-Urbanization
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Sustainability
Volume 8
Issue 9
10.3390/su8090906
sustainability-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Assessment of Relationships between Earthworms and Soil Abiotic and Biotic Factors as a Tool in Sustainable Agricultural

by
Radoslava Kanianska
1,*,
Jana Jaďuďová
1,
Jarmila Makovníková
2 and
Miriam Kizeková
3
1
Faculty of Natural Sciences, Matej Bel University, Tajovského 40, Banská Bystrica 97401, Slovakia
2
National Agricultural and Food Centre—Soil Science and Conservation Research Institute Bratislava, Regional Station Banská Bystrica, Mládežnícka 36, Banská Bystrica 97421, Slovakia
3
National Agricultural and Food Centre—Grassland and Mountain Agriculture Research Institute, Mládežnícka 36, Banská Bystrica 97421, Slovakia
*
Author to whom correspondence should be addressed.
Sustainability 2016, 8(9), 906; https://doi.org/10.3390/su8090906
Submission received: 13 June 2016 / Revised: 1 September 2016 / Accepted: 2 September 2016 / Published: 7 September 2016
Browse Figure
Versions Notes

Abstract

:
Earthworms are a major component of soil fauna communities. They influence soil chemical, biological, and physical processes and vice versa, their abundance and diversity are influenced by natural characteristics or land management practices. There is need to establish their characteristics and relations. In this study earthworm density (ED), body biomass (EB), and diversity in relation to land use (arable land—AL, permanent grasslands—PG), management, and selected abiotic (soil chemical, physical, climate related) and biotic (arthropod density and biomass, ground beetle density, carabid density) indicators were analysed at seven different study sites in Slovakia. On average, the density of earthworms was nearly twice as high in PG compared to AL. Among five soil types used as arable land, Fluvisols created the most suitable conditions for earthworm abundance and biomass. We recorded a significant correlation between ED, EB and soil moisture in arable land. In permanent grasslands, the main climate related factor was soil temperature. Relationships between earthworms and some chemical properties (pH, available nutrients) were observed only in arable land. Our findings indicate trophic interaction between earthworms and carabids in organically managed arable land. Comprehensive assessment of observed relationships can help in earthworm management to achieve sustainable agricultural systems.

1. Introduction

Soil macro-invertebrates play a key role in soil organic matter transformations and nutrient dynamics at different spatial and temporal scales through perturbation and the production of biogenic structures for the improvement of soil fertility and land productivity [1,2]. As such, they influence soil chemical, biological, and physical processes [3] or contribute to biological control [4], food web dynamics and soil processes [5,6]. Among numerous macro-invertebrates in the soil, earthworms are the most important components of soil biota in terms of soil formation and maintenance of soil structure and fertility [7]. Due to earthworms’ activity in soil they are classified as “ecosystem engineers”, which means that they affect their environment, either biotic or abiotic. Ecosystem engineers are keystone species that modify their habitat so strongly that it in turn affects other organisms. Christensen and Mather [8] showed that earthworm number and biomass reflect both natural soil parameters, e.g., sand content, and agricultural practices. Kernecker et al. [9] confirmed the effect of soil moisture, vegetation diversity, and soil nutrient concentrations on earthworm species compositions.
There are many studies in different parts of the world which have assessed earthworm abundance and functions in the soils [10,11,12,13,14,15,16]. Focus has been given to integrate earthworms into agriculture management in order to increase the crop yield [17]. However, cultural practices are widely recognized to affect earthworms in agricultural fields [18]. Tillage, crop type and pesticide inputs have been demonstrated to affect earthworms in agroecosystems. Earthworms can serve as a tool reflecting the environmental impact of tillage operations, soil pollution, different agricultural input, trampling, industrial plant pollution, etc. [19]. Several studies have shown that earthworm abundance and diversity are reduced in agricultural fields, compared to uncropped soils [4]. Significant loss of soil faunal biodiversity or species richness has been found to accompany conventional agricultural systems based on intensive cultivation, high fertilizer inputs and crop monoculture.
In terrestrial systems the majority of ecosystem services arise from soil functions that are dependent to a greater or lesser extent on interactions between organisms, organic and mineral fractions of soil [20]. Earthworms come into interaction with other soil organisms directly or indirectly. So, to investigate the potential of the earthworms to integrate into agriculture management, knowledge on different physical, chemical, biological and management factors that affect the distribution and abundance of earthworm population is important, which will help to identify the ecological appropriateness of the earthworms in order to supplement their existing population and quantity the impact of earthworms on agricultural land [21]. Incorporating the functional roles of earthworms in agro-ecosystem management is key to sustainable agriculture. Earthworms have a potential to contribute to the management of soil fertility for plant growth, enhanced farming efficiency and agricultural sustainability. For this to be realised, it is important to understand the roles they play in driving soil based processes, their biology and ecology [22].
The linkages between earthworm activity, biotic and abiotic factors, climate change and land management practices are numerous, interrelated, and in many cases shape ecosystem service provision. Here, we present a survey of earthworm species in differently managed arable systems and permanent grasslands of Slovakia with the following objectives; (1) to record different species present in various agroecosystems; (2) to evaluate variations of earthworm density, biomass productivity, and diversity in relation to management, abiotic and biotic factors; and (3) to evaluate trophic interactions between earthworms and arthropods that can be utilised to enhance agricultural sustainability.

2. Materials and Methods

2.1. Study Area

Slovakia is a highly diversified country in respect to its natural environment. It is largely located in the mountainous territory of the western Carpathian arch, which forms the boundary between important physical and bio-geographic zones and several main European watersheds. Only a small part of Eastern Slovakia belongs to the eastern Carpathian region, and the southwestern part to the Pannonian basin. The mountain regions cover more than 55% of the total land territory. The climate is temperate but is influenced locally by elevation and type of relief. Communities vary from thermophilous in the southern parts of the country, to mountainous in the higher altitudes [23].
Seven study sites with two different land uses (arable land—AL, and permanent grasslands—PG) located in different natural conditions were selected. Only the VO study site situated at Danubian Upland with the most productive soil type (Black Chernozem) is used only as arable land (Figure 1, Table 1 and Table 2).

2.2. Methods

At each study site the biotic (earthworm density—ED, earthworm biomass—EB, earthworm diversity—EDI, earthworm species, arthropod density—AD, arthropod biomass—AB, ground beetle density—GBD, and carabid density—CD) and abiotic parameters (soil temperature—ST, soil moisture—SM, and penetration resistance—PR) were measured for two land use categories (arable land—AL and permanent grasslands—PG) with the site specific land management.
Before the earthworm collection and traps installation, measurement of the soil physical parameters was done in the same places where earthworms were collected. Soil temperature, soil moisture and penetration resistance were measured at seven points on each site at the arable land and permanent grasslands. Soil temperature (ST) was measured in °C at 0.05 (ST05) and 0.20 (ST20) m depth by insertion of a thermometer in °C. Soil moisture level (SM) was measured in soil moisture volume percentage at 0.05 (SM05) and 0.20 (SM20) m depth using a soil moisture sensor (ThetaProbe, type ML2x: Eijkelkamp Agrisearch Equipment, Giesbeek, The Netherlands, 2013) in the soil moisture volume percentage. Penetration resistance (PR) was measured with an electronic penetrometer (Penetrologger, 6987 EM: Eijkelkamp Agrisearch Equipment, Giesbeek, The Netherlands, 2013) with a cone diameter of 1 cm2 and a 60° top angle cone. Cone resistance was recorded in MPa.
On each site 1 kg of soil samples for chemical analysis were collected from four points placed at the apices of a 10-m side square. Soil samples were air dried, homogenized, sieved thoungh 2 mm sieves and analysed for soil pH in KCl, total oxidizable organic carbon (TOC) according to Tjurin’s method (a modification of Nikitin) [24], total nitrogen (Nt) according to a modified Kjeldahl method in accordance with the Slovak standardized method (STN ISO 11261), and available nutrients (P, K, Mg) according to Mehlich III [25]. The mean values were used as soil chemical status characteristics.
Earthworms were sampled in seven study sites, in seven arable land and six grasslands (at VO study site the land is not used as permanent grasslands). Sampling was done in the spring 2015 (March–April) when earthworm populations are the most active. At each site, earthworms were sampled by digging of seven pits of 35 × 35 cm2 to the depth of 20 cm placed in a line with 3 m distance between the pits. Soil from pit was replaced on plastic bag and hand sorted. The earthworms were counted and collected. Deeper-dwelling earthworms were expelled by 1.5 L of 0.2% formalin. Formalin was applied directly to the holes. After a few minutes earthworms were collected. The collected samples of earthworms were transported in glass cups with sufficient amount of soil in portable fridge to the laboratory. The next day, the collected earthworms were washed, weighed, and the sexual maturity and body colour were noted. The earthworm density and biomass from soil monoliths were recalculated per square meter. Earthworms were sacrificed, fixed in 4% formalin and mature individuals identified by the Zajonc Earthworm key [26] using a binocular microscope. Shannon-Wiener index (H′) analysis was performed to determine a measure of estimated diversity within each study site.
Soil arthropods including ground beetles and carabids were sampled in the same places where earthworms were collected. Seven plastic pitfall traps of 1.5 L volume were placed flush with the surface. The traps were filled with 200 mL 4% formalin solution. After one month the traps were collected. The captured individuals were counted, weighed, identified and preserved in formalin solution.
Correlation analysis was conducted using the Spearman’s Rank correlation coefficients to identify relationship among earthworms and selected soil abiotic and biotic factors. Differences between two different land use systems (AL, PG) were tested by a paired samples test. The statistical analysis was conducted using the PASW Statistics software version 18.0 (SPSS Inc., Chicago, IL, USA, 2016).

3. Results and Discussion

3.1. Earthworm Biomass, Density and Diversity in Differently Managed Agroecosystems

In total, 1091 earthworms were sampled representing an overall biomass of 609.8 g. Average fresh body biomass of the earthworms per 1 m2 ranged from 0 to 66.4 g·m−2 and 28.2 to 134.5 g·m−2 in arable land and permanent grasslands, respectively (Table 3).
The measured mass values indicate the fact that earthworms belong to the largest soil macrofauna species and they are a major component of soil fauna communities in most ecosystems [27,28]. In temperate zones earthworm biomass often exceeds the biomass of all other soil biota having major impacts on other soil biota and soil conditions [29].
The density of earthworms ranged from 0 to 226.2 ind·m−2 and from 74.6 to 277.6 ind·m−2 in AL and PG, respectively (Table 4).
The maximum value of 277.6 individuals per m2 was measured in permanent grasslands at the DV site in Fluvisol. The majority of individuals were juveniles (228.57 ind·m−2 of juveniles; 47.72 ind·m−2 of matures). On average, the density of earthworms per m2 was nearly twice as high in permanent grasslands (120.3 ind·m−2) compared to arable land (61.6 ind·m−2).
At the KE site we measured the second highest density of individuals per m2 (226.2 ind·m−2) in extensively managed arable land. As at the DV site juveniles dominated the samples (205.25 ind·m−2 of juveniles; 21.00 ind·m−2 of matures). The high earthworm density at the KE site is probably a consequence of ongoing erosion processes that are more intense in arable land than in permanent grasslands with permanent vegetation cover. The sampling was done on the bottom of the slope with accumulated fine materials with suitable content of organic matter, nitrogen and other nutrients that generate good living conditions for earthworms. The findings followed similar patterns as Kanianska et al. found in 2014 [30].
Mean biomass of earthworms was also more than twice as high in permanent grasslands (68.3 g·m−2) compared to arable land (33.3 g·m−2). The differences between arable land and permanent grasslands analysed by a paired samples test confirmed significant differences between the earthworm density and biomass in these two land uses. Results confirmed the opinion that the distribution and biomass of earthworms in the soil depends on land use and management practices. Several authors [31,32,33] found earthworms to be more abundant and populations to have greater biomass under long-term pasture than under long-term cropping. In addition, in permanent grasslands with managed grazing, positive effects of cattle and sheep slurry manure on earthworm populations were recorded in permanent grasslands at the NV and the TA sites similar to studies of de Goede et al. [34], Murchie et al. [35], and Pommeresche and Loes [36]. Significant loss of soil faunal abundance in arable lands is connected with intensive cultivation [37], high fertilizer inputs, crop monoculture, and machine traffic in arable land [38]. In our study the number of anecic earthworms were also reduced in intensively managed study sites.
A total of 12 species were identified of which 9 were present in arable land and 11 in permanent grasslands (Table 5 and Table 6). The percentage of juveniles within community was only slightly higher in arable land (80%) than in permanent grasslands (72.4%).
Only one species, Aporrectodea caliginosa occur in abundance at all seven study sites and was the most numerous species in both different land use sites. In permanent grasslands, A. caliginosa represented 68.8% of identified specimens in the dataset, and 32.4% in arable land. Aporrectodea rosea and Lumbricus terrestris were found at four of seven study sites. Octolasion cyaneum and Octolasion lacteum were found abundant in arable land. Other species were found irregularly. At the species level, our results are in line with the observations done of Zajonc [26,39] in agro-climatic zones of Slovakia in the 1970s and 1980s. The most abundant species in our research, Aporrectodea caliginosa, belongs to the quite common earthworm species in Europe. The assessment of earthworm field studies from six different European countries revealed that endogeic species Aporrectodea caliginosa, Aporrectodea rosea and Allolobophora chlorotica are the dominant ecological group [40]. Aporrectodea caliginosa was confirmed as the second most numerous species in a British earthworm dataset [41].
The overall effect of earthworms on soil processes varies with their ecological category and species. We identified six endogeic (Allolobophora chlorotica, Aporrectodea caliginosa, Aporrectodea rosea, Eiseniella tetraedra, Octolasion cyaneum, and Octolasion lacteum), four epigeic (Dendrobaena octaedra, Dendrodrilus rubidus, and Lumbricus castaneus, and Lumbricus rubellus), and two anecic (Aporrectodea longa, Lumbricus terrestris) species. Endogeic species dominated in both land use categories. Higher endogeic species abundance was observed in PG (85.9%) than in AL (66.2%). Epigeic species represented 4.5% and 18.9% in permanent grasslands and arable land, respectively. The anecic species represented 9.5% and 14.9% in permanent grasslands and arable land, respectively. The distribution of the different ecological categories of earthworms in arable land and permanent grasslands showed a preference of endogeic species, as soil dwellers with horizontal burrows. These worms rarely come to the surface in contrast to the epigeic species that live in the litter and humus layers or can sometimes penetrate a little deeper into loose mineral soil (particularly Lumbricus rubellus). Epigeic species are susceptible to soil cultivation, since it destroys the superficial soil layer. Epigeic species are associated with surface organic matter and may be present in agricultural settings where farming practices provide concentrations of organic materials e.g., animal faeces or crop residues. True epigeic species are often rare in natural settings. In general, they are much more abundant in non-arable habitats than in ploughed ones [42,43]. Such effect were observed in intensively managed arable land at the NV, the DV, the MJ sites where the epigeic group of earthworms was absent. In addition, the numbers of endogeic species were higher in permanent grasslands comparing to arable land. Similarly, the deep-burrowing earthworms (Lumbricus terrestris and Aporrectodea longa), which collect food from the soil surface, is adversely affected by heavy soil cultivation that destroys its burrow system and reduces food sources [44]. Overall, Aporrectodea longa was not found in arable land
The highest earthworm diversity was found at the VO site (H′ = 1.90) among arable land study sites, and at the LT (H′ = 1.85) among permanent grasslands study sites (Table 5 and Table 6). Although many authors argue that permanent grasslands have the greatest species diversity of earthworms [45,46] we confirmed the statement in only three study sites (MJ, TA, LT).

3.2. Earthworms in Relation to Soil Type and Soil Chemical Properties

Earthworm abundance and diversity is affected not only by management practices but is also influenced by abiotic and biotic factors. Soil types have an impact on soil biota. We found no earthworms at the MJ study site in Regosol used as arable land situated in a region with low precipitation and high temperature. Regosol used as arable land had unfavourable soil chemical and physical properties. Its texture is sandy, and coarse sand can be a negative factor for earthworms either because of the abrasive action of sand grains that damages earthworm skin or because this soil retains less water [47].
Generally, the abundance of species reflects their preference to site specific conditions. O. lacteum prefers soils which are rich in calcium [39]. Therefore O. lacteum was found in Rendzina, shallow soil developed on limestone rock at the LT site. E. tetraedra as semi-aquatic species [48] with affinity for moist conditions [49], was found more abundant in Fluvisol. In our research we observed the higher earthworm abundance and biomass in Fluvisols, soil types developed in alluvial zones.
Seven study sites differ in soil chemical properties (Table 7 and Table 8). In arable land, soil reaction at the VO and LT is neutral, at the DV weakly acidic, at the NV and KE acidic, and at the TA strongly acidic. In permanent grasslands, soil reaction at the NV, MJ and LT is neutral, at the KE weakly acidic, at the DV strong acidic, and at the TA extremely acidic. Content of total organic carbon is medium, high, very high, and only at the MJ is it very low. Content of available phosphorous is very low and low at all study sites. In contrast, content of available magnesium is medium, high and very high at all study sites with the exception of the MJ. Content of available potassium varies, and low content was recorded at the NV in AL, MJ, and TA in PG.
In permanent grasslands, there was no correlation between earthworm characteristics (earthworm density, biomass, and diversity) and soil chemical parameters (Table 9). In arable land, we found a positive correlation between earthworm biomass and available potassium. The available nutrients are supportive not only for plants but also for soil edaphon biomass. In contrast, nutrients and their availability are influenced by soil fauna. Zhu et al. [50] found that earthworms can activate and transform K into effective K that is more readily taken up by plants through feeding, digestion, absorption, and excretion. Earthworm diversity was positively correlated with Mg and pH in arable land (Table 9).

3.3. Earthworms in Relation to Climate Related and Physical Soil Parameters

Observation of relationships between biotic and climate related soil parameters are very important because rapid climate changes make it unlikely that earthworm communities and their ecosystem services will survive in the current form, because the environmental filters may change faster than worms can respond [51].
The development of the present ecosystems in the postglacial period (Holocene) depended on significant changes in climate, on the distance of refuges in which organisms could survive unfavourable conditions of the glacial period, and on the nature and development of soils. Glacial periods in the Carpathians caused the local extinction of many living forms. Warming in the post-glacial period, about 10,000 years ago, created conditions that facilitated migration of individual species from their refuges (dominantly in southern Europe), where they were protected during glacial periods. After the neolitic revolution, human society began to influence more noticeably the development of natural ecosystems in the lower warmer altitudes of Central Europe. During the formation period of neolitic agriculture, the Carpathians were almost completely covered by forests. Only high-montane and alpine rocky localities were without forest cover—i.e., rocky walls, avalanche slopes, and narrow belts of some river banks [52].
Anthropogenic changes relevant to earthworm communities include habitat alteration, invasive species, and climate change. Disturbance intensity and frequency are important variables for both extinction of endemics and colonization by invasive species [53]. Climate change effects on earthworm communities have not been closely explored with experimental procedures. Distributional data in temperate zones indicate a strong influence of glaciation history on modern distributions, and a very slow rebound from refugia to deglaciated land, where invasive species now dominate [54]. Under the conservative estimates of climate change, the future of earthworm ecosystem services may depend on invasive species, and topographically simple regions. Otherwise, medium-term evolutionary change may be the only response mechanism available to earthworms [55].
In relation to climate, climatic factors reflected in soil moisture and temperature are considered to be the primary factors limiting survival of earthworms [56,57]. Soil temperature and moisture varied among the study sites in different soil depths in arable land and permanent grasslands (Table 10).
In arable land, earthworm density and biomass were positively correlated with soil moisture. In permanent grasslands with significantly higher moisture content values (Table 10), temperature became a limiting factors affecting earthworm density and biomass, which is reflected in significant positive correlation (Table 11).
A negative correlation rate was measured between penetration resistance and earthworm biomass in arable land confirming the negative effect of soil compaction on earthworms. The results are in line with other studies that found a reduction in earthworm populations as a result of soil compaction in arable land [58,59].

3.4. Earthworms in Relation to Arthropods

We observed relationships between earthworms, arthropods, ground beetles and carabids (phylum Arthropoda, order Coleoptera, family Carabidae). A total of 3849 arthropod individuals were trapped representing an overall biomass of 302.3 g. The numbers of arthropods, ground beetles and carabids varied between study sites with different land management practices (Table 12).
On average, the number of arthropods was roughly twice as high in permanent grasslands compared to intensively managed arable land (NV, DV, and MJ) including extensively managed arable land at the KE. Order Coleoptera belonged to the dominant orders at all study sites.
The highest number of carabids was counted at the LT study site in organically managed arable land. Carabid recruitment is enhanced by proper organic fertilization and green manuring [60] applied at the LT study site. The second highest number was recorded again in arable land at the TA, study site with extensive land use management, located in mountain area surrounded by pastures and forests. The results suggest that land use and management determine the arthropods’ assemblages. Regarding to the effect of management on soil arthropods there are different research results. Many studies reported that extensive or organic management has positive effects on biodiversity [61], but these effects differed between species groups and spatial scales [62]. Attwood et al. [63] observed significantly higher arthropod richness in areas of less intensive land use. There are also authors who observed no effect of management on selected arthropod orders [64] or they found higher mesofauna abundance under conventional management than in under organic [65].
Our findings indicate trophic interactions between earthworms and arthropods, particularly because carabid beetles can act as predators of earthworms. Moreover, they are considered predators of crop pests, including slugs and aphids in agricultural systems. Symondson et al. [66] found out that at times when target prey (pests) is limited in ecosystem, earthworms are the most frequently detected prey in the diet of these predators. King et al. [67] found out in the field that, with little evidence of prey choice that earthworms were being predated in proportion to their densities. During the spring when our research was done target prey (pests) was limited in the agroecosystem, and earthworms could become the main prey in the diet of these predators. In the LT the lowest number of earthworms was recorded (20.99 ind·m−2, Table 3) which could be affected by the highest number of carabid beetles among all study sites. However, much is still unknown regarding the biotic interactions, and much more interdisciplinary research is needed to assess the potential role of earthworms in soil systems and the potentially beneficial or harmful effects this regulation may have on ecosystem functions in different ecosystems [68].

4. Conclusions

In spite of the fact that this paper has explored seven study sites in Slovakia, the findings have a wider relevance because of high variability in natural conditions and management practices of selected study sites. The assessment showed high relevance of dynamic but also more stable factors influencing earthworms in soil. Earthworm density and biomass were higher in permanent grasslands than in arable land. Among different abiotic soil parameters, climate related and water availability characteristics affected the distribution of earthworms. They will play an important role in the future connected with ongoing climate changes. Specifically, Fluvisols developed in alluvial zones created the most suitable conditions for earthworm abundance and biomass. These soils are influenced by sufficient water content. Relationships between earthworms and some chemical (pH, available nutrients) and physical (penetration resistance) factors were observed only in arable land. Observed biotic relations indicate trophic interactions between earthworms and arthropods, indicating that land use management may have a top-down effect on trophic interactions that shape earthworm communities. Further research is needed to link the biotic and abiotic factors, processes including land management to more complex ecosystem services.

Acknowledgments

This work was supported by the Slovak Research and Development Agency under Grant No. APVV-0098-12 Analysis, modelling and evaluation of agro-ecosystem services. The research of abiotic soil parameters was done by the equipment supported by Operational Programme Research and Development via contract No. ITMS-26210120024 Restoration and building of infrastructure for ecological and environmental research at Matej Bel University in Banská Bystrica.

Author Contributions

Radoslava Kanianska performed terrain research and literature review, analyzed the data, wrote the paper; Jana Jaďuďová performed terrain research; Jarmila Makovníková contributed to chemical analysis evaluation, Miriam Kizeková contributed to biological analysis evaluation.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Lavelle, P.; Spain, A.V. Soil Ecology; Kluwer Academic Publishers: Dordrecht, The Netherlands, 2000. [Google Scholar]
  2. Jouquet, P.; Dauber, J.; Lagerlof, J.; Lavelle, P.; Lepage, M. Soil invertebrates as ecosystem engineers: Intended and accidental effects on soil and feedback loops. Appl. Soil Ecol. 2006, 32, 153–164. [Google Scholar] [CrossRef]
  3. Suthar, S. Earthworm communities as bio-indicator of arable land management practices: A case study in semiarid region of India. Ecol. Indic. 2009, 9, 588–594. [Google Scholar] [CrossRef]
  4. Bertrand, M.; Blouin, M.; Barot, S.; Charlier, A.; Marhcnad, D.; Roger-Estrade, J. Biocontrol of eyespot disease on two winter wheat cultivars by an anecic earthworm (Lumbricus terrestris). Appl. Soil Ecol. 2015, 96, 33–41. [Google Scholar] [CrossRef]
  5. Burke, J.L.; Maerz, J.C.; Milanovich, J.R.; Melany, C.F.; Gandhi, K.J.K. Invasion by exotic earthworms alters biodiversity and communities of litter- and soil-dwelling oribatid mites. Diversity 2011, 3, 155–175. [Google Scholar] [CrossRef]
  6. Jones, C.G.; Lawton, J.H.; Shachak, M. Organisms as ecosystem engineers. Oikos 1994, 69, 373–386. [Google Scholar] [CrossRef]
  7. Curry, J.P. Factors affecting the abundance of earthworms in soil. In Earthworm Ecology; Edwards, C.A., Ed.; CRC Press LLC: Boca Raton, FL, USA, 2004; pp. 91–114. [Google Scholar]
  8. Christensen, O.; Mather, J.G. Dynamics of lumbricid earthworm cocoons in relation to habitat conditions at three different arable sites. Pedobiologia 1990, 34, 227–238. [Google Scholar]
  9. Kernecker, M.; Whalen, J.K.; Bradley, R.L. Agricultural management and flooding shape habits for non-native earthworms in southern Quebec, Canada. Appl. Soil Ecol. 2015, 96, 240–250. [Google Scholar] [CrossRef]
  10. Sheu, S. Effects of earthworms on plant growth patterns and perspecitves. Pedobiologia 2003, 47, 846–856. [Google Scholar] [CrossRef]
  11. Cortez, J. Field decomposition of leaf litters: Relationships between decomposition rates and soil moisture, soil temperature and earthworm activity. Soil Biol. Biochem. 1998, 30, 783–793. [Google Scholar] [CrossRef]
  12. Goswami, R. Determination of ecological diversity indices to assess the interrelationship between earthworm diversity and different habitats of Indian Botanic garden, Howrah, India. Biol. Forum Int. J. 2015, 7, 128–136. [Google Scholar]
  13. Jones, H.D.; Santoro, G.; Boag, B.; Neilson, R. The diversity of earthworms in 200 Scottish fields and the possible effect of New Zeland land flatworms (Arthurdendyus triangulates) on earthworm populations. Ann. Appl. Biol. 2001, 139, 75–92. [Google Scholar] [CrossRef]
  14. Ranson, T.S.; Billa, B.J. Differences in soil characteristics between field and forest may influence the distribution of an invasive earthworm. Invertebr. Biol. 2015, 134, 78–87. [Google Scholar] [CrossRef]
  15. Ravenek, J. C and N Mineralization and Earthworm Populations in a Norway Spruce Forest at Hasslov (SW Sweden), 25 Years after Liming; SLU, Department of Ecology: Uppsala, Sweden, 2009. [Google Scholar]
  16. Wever, L.A.; Timothy, J.L.; Clapperton, M.J. The influence of soil moisture and temperature on the survival, aestivation, growth and development of juvenile Aporrectodea tuberculate (eisen) (Lumbiricidae). Pedobiologia 2001, 45, 121–133. [Google Scholar] [CrossRef]
  17. Lavelle, P.; Barois, I.; Martin, A.; Zaidi, Z.; Schaefer, P. Management of earthworm populations in agro-ecosystems. A possible way to maintain soil quality? In Ecology of Arable Land—Perspectives and Challenges; Clarholm, M., Bergström, L., Eds.; Springer: Dordrecht, The Netherlands, 1989; pp. 109–122. [Google Scholar]
  18. Chan, K.Y. An overview of some tillage impacts on earthworm population abundance and diversity—Implications for functioning in soils. Soil Tillage Res. 2001, 57, 179–191. [Google Scholar] [CrossRef]
  19. Paoletti, M.G. The role of earthworms for assessment of sustainability and as bioindicators. Agric. Ecosyst. Environ. 1999, 74, 137–155. [Google Scholar] [CrossRef]
  20. Kibblewhite, M.G.; Ritz, K.; Swift, M.J. Soil health in agricultural systems. Philos. Trans. R. Soc. Lond. B 2008, 363, 685–701. [Google Scholar] [CrossRef] [PubMed]
  21. Mele, P.M.; Carter, M.R. Species abundance of earthworms in arable and pasture soils in south-eastern Australia. Appl. Soil. Ecol. 1999, 12, 129–137. [Google Scholar] [CrossRef]
  22. Manono, B. Agro-ecological role of earthworms (Oligochaetes) in sustainable agriculture and nutrient use efficiency: A review. J. Agric. Ecol. Res. Int. 2016, 8, 1–18. [Google Scholar] [CrossRef]
  23. MESR. National Biodiversity Strategy of Slovakia; MESR: Bratislava, Slovakia, 1998. [Google Scholar]
  24. Nikitin, V.; Fishman, V. On the improvement of methods for determination of soil carbon. Chem. Agric. 1969, 3, 76–77. [Google Scholar]
  25. Mehlich, A. Mehlich 3 soil test extractant: A modification of Mehlich 2 extractant. Commun. Soil Sci. Plant Anal. 1984, 15, 1409–1416. [Google Scholar] [CrossRef]
  26. Zajonc, I. Earthworms (Oligochaeta; Lumbricidae) of Slovakia. In Biological Studies; VEDA: Bratislava, Slovakia, 1981. [Google Scholar]
  27. Bhadauria, T.; Saxena, K.G. Role of earthworms in Soil fertility Maintenance through the production of Biogenic Structures. Appl. Environ. Soil Sci. 2010. [Google Scholar] [CrossRef]
  28. Edwards, C.A.; Bohlen, P.J. Biology and Ecology of Earthworms, 3rd ed.; Chapman and Hall: London, UK, 1996. [Google Scholar]
  29. Wurst, S.; De Deyn, G.B.; Orwin, K. Soil biodiversity and functions. In Soil Ecology and Ecosystem Services; Wall, D.H., Ed.; Oxford University Press: Oxford, UK, 2012; pp. 28–44. [Google Scholar]
  30. Kanianska, R.; Jaďuďuová, J.; Kizeková, M.; Makovníková, J. Earthworms as bioindicator of land use in agroecosystems. Ecol. Saf. 2015, 9, 34–41. [Google Scholar]
  31. Fromm, H.; Winter, K.; Filser, J.; Hantshcel, R.; Beese, F. The influence of soil type and cultivation system on the spatial distribution of the soil fauna and microorganisms and their interactions. Geoderma 1993, 60, 109–118. [Google Scholar] [CrossRef]
  32. Lamandé, M.; Hallaire, V.; Curmi, P.; Pérés, G.; Cluzeau, D. Changes of pore morphology, infiltration and earthworm community in a loamy soil under different agricultural managements. Catena 2003, 54, 637–649. [Google Scholar] [CrossRef]
  33. Marhan, S.; Scheu, S. The influence of mineral and organic fertilisers on the growth of the endogeic earthworm Octolasion tyrtaeum (Savigny). Pedobiologia 2005, 49, 239–249. [Google Scholar] [CrossRef]
  34. De Goede, R.G.M.; Brussaard, L.; Akkermans, A.D.L. On-farm impact of cattle slurry manure management on biological soil quality. NJAS Wagening. J. Life Sci. 2003, 51, 103–133. [Google Scholar] [CrossRef]
  35. Murchie, A.K.; Blackshaw, R.P.; Gordon, A.W.; Christie, P. Responses of earthworm species to long-term applications of slurry. Appl. Soil Ecol. 2015, 96, 60–67. [Google Scholar] [CrossRef]
  36. Pommeresche, R.; Loes, A.K. Relations between Agronomic Practice and earthworms in Norwegian Arable Soils. Dyn. Soil Dyn. Plant 2009, 3, 129–142. [Google Scholar]
  37. Crittenden, S.J.; Eswaramurthy, T.; De Goede, R.G.M.; Brussaard, L.; Pulleman, M.M. Effect of tillage on earthworms over short- and medium-term in conventional and organic farming. Appl. Soil Ecol. 2014, 83, 140–148. [Google Scholar] [CrossRef]
  38. Hansen, S.; Engelstad, F. Earthworm populations in a cool and wet district as affected by tractor traffic and fertilisation. Appl. Soil Ecol. 1999, 13, 237–250. [Google Scholar] [CrossRef]
  39. Zajonc, I. Earthworms (Lumbicidae) in Meadows of Carpathian Region in Czechoslovakia; VEDA: Bratislava, Slovakia, 1970. [Google Scholar]
  40. Dinter, A.; Oberwalder, C.H.; Kabouw, P.; Coulson, M.; Ernst, G.; Leicher, T.; Miles, M.; Weyman, G.; Klein, O. Occurrence and distribution of earthworms in agricultural landscapes across Europe with regard to testing for responses to plant protection products. J. Soils Sediments 2013, 13, 278–293. [Google Scholar] [CrossRef]
  41. Sheppard, D. Earthworms in England: Distribution, Abundance and Habitats; Natural England Commissioned Report NECR 145; Natural England: Worcester, UK, 2014.
  42. Ivask, M.; Kuu, A.; Sizov, E. Abundance of earthworm species in Estonian arable soils. Eur. J. Soil Biol. 2007, 43, 39–42. [Google Scholar] [CrossRef]
  43. Zeithaml, J.; Pižl, V.; Sklenička, P. Earthworm assemblages in an ecotone between forest and arable field and their relations with soil properties. Pesq. Agropec. Bras. Brasília 2009, 44, 922–926. [Google Scholar]
  44. Whalen, J.K. Spatial and temporal distribution of earthworm patches in corn field and forest systems of southwestern Quebec, Canada. Appl. Soil Ecol. 2004, 27, 143–151. [Google Scholar] [CrossRef]
  45. Haynes, R.J.; Dominy, C.S.; Graha, M.H. Effect of agricultural land use on soil organic matter status and the composition of earthworm communities in KwaZulu-Natal, South Africa. Agric. Ecosyst. Environ. 2002, 95, 453–464. [Google Scholar] [CrossRef]
  46. Edwards, C.A. The importance of earthworms as key representatives of the soil fauna. In Earthworm Ecology; Edwards, C.A., Ed.; CRC Press: Boca Raton, FL, USA, 2004. [Google Scholar]
  47. Laossi, K.R.; Decens, T.; Jouquet, P.; Barot, S. Can we predict how earthworm effects on plant growth vary with soil properties? Appl. Environ. Soil Sci. 2010. [Google Scholar] [CrossRef]
  48. Butt, K.R.; Lowe, C.H.N. Presence of earthworm species within and beneath Lumbricus terrestris (L.) middens. Eur. J. Soil Biol. 2007, 43, S57–S60. [Google Scholar] [CrossRef]
  49. Sims, R.; Gerard, B. Earthworms: Notes for the identification of British species. In Synopses of the British Fauna 31; Barnes, R.S.K., Crothers, J., Eds.; Field Studies Council: Shrewsbury, UK, 1999. [Google Scholar]
  50. Zhu, X.; Lian, B.; Yang, X.; Liu, C.; Zhu, L. Biotransformation of earthworm activity on potassium-bearing mineral powder. J. Earth Sci. 2013, 24, 65–74. [Google Scholar] [CrossRef]
  51. Antunes, P.M.; Franken, P.; Schwarz, D.; Rillig, M.C.; Cosme, M.; Scott, M.; Hart, M.M. Linking soil diversity and human health: Do arbuscular mycorrhizal fungi contribute to food nutrition? In Soil Ecology and Ecosystem Services; Wall, D.H., Ed.; Oxford University Press: Oxford, UK, 2012; pp. 173–232. [Google Scholar]
  52. Ložek, V. Nature in the Quaternary; Academia: Praha, Czech, 1973. [Google Scholar]
  53. Hendrix, P.F.; Callaham, M.A.; Drake, J.M.; Huang, C.; James, S.W.; Snyder, B.A.; Zhang, W. Pandor’s box contained bait: The global problem of introduced earthworms. Annu. Rev. Ecol. Evol. Syst. 2008, 39, 593–613. [Google Scholar] [CrossRef]
  54. Frelich, L.E.; Hale, C.M.; Scheu, S.; Holdsworth, A.R.; Heneghan, L.; Bohlen, P.J.; Reich, P.B. Earthworm invasion into previously earthworm-free temperate and boreal forests. Biol. Invasions 2006, 8, 1235–1245. [Google Scholar] [CrossRef]
  55. Wall, D.H.; Bardgett, R.D.; Behan-Pelletier, V.; Jeffrey, E.; Herrick, T.; Jones, H.; Ritz, K.; Six, J.; Strong, D.R.; van der Putten, W.H. Soil Ecology and Ecosystem Services; Oxford University Press: Oxford, UK, 2012. [Google Scholar]
  56. Boudiaf, N.K.M.; Metheri, M.S.; Mouas, B.S.; Derridj, A. Climate impact on the abundance of soil macroinvertebrates in Algerian olive orchards. Agric. Food 2015, 3, 320–324. [Google Scholar]
  57. Doube, B.M.; Styan, C. The response of Aporrectodea rosea and Aporrecctodea trapezoids (Oligocheta: Lumbriocidae) to moisture gradients in three soil types in the laboratory. Biol. Fertil. Soils 1996, 23, 166–172. [Google Scholar] [CrossRef]
  58. Pizl, V. Effect of soil compaction on earthworms (Lumbricidae) in apple orchard soil. Soil Biol. Biochem. 1992, 24, 1573–1575. [Google Scholar] [CrossRef]
  59. Söchtig, W.; Larink, O. Effects of soil compaction on activity and biomass of endogeic lumbricides in arable soils. Soil Biol. Biochem. 1992, 24, 1595–1599. [Google Scholar] [CrossRef]
  60. Kromp, B. Carabid beetles in sustainable ariculture: A review on pest control efficacy, cultivation impacts and enhancement. Agric. Ecosyst. Environ. 1999, 74, 187–228. [Google Scholar] [CrossRef]
  61. Bengtsson, J.; Ahnström, J.; Weibull, C. The effect of organic agriculture on biodiversity and abundance: A meta-analysis. J. Appl. Ecol. 2005, 42, 261–269. [Google Scholar] [CrossRef]
  62. Bátary, P.; Báldi, A.; Kleijn, D.; Tscharntke, T. Landscape-moderated biodiversity effects of agri-environmental management: A meta-analysis. Proc. Biol. Sci. 2011, 278, 1894–1902. [Google Scholar] [CrossRef] [PubMed]
  63. Attwood, S.J.; Maron, M.; House, A.P.N.; Zammit, C. Do arthropod assemblages display globally consistent responses to intensified agricultural land use and management? Glob. Ecol. Biogeogr. 2008, 17, 585–599. [Google Scholar] [CrossRef]
  64. Rodríguez, E.; Fernández-Anero, F.J.; Ruiz, P.; Campos, M. Soil arthropod abundance under conventional and no tillage in a Mediterranean climate. Soil Tillage Res. 2006, 85, 229–233. [Google Scholar] [CrossRef]
  65. Schon, N.L.; Mackay, A.D.; Hedley, M.J.; Minor, M.A. The soil invertebrate contribution to nitrogen mineralization differs between soils under organic and conventional dairy management. Biol. Fertil. Soils 2012, 48, 31–42. [Google Scholar] [CrossRef]
  66. Symondson, W.O.C.; Glen, D.M.; Erickson, M.L.; Liddell, J.E.; Langdon, C.J. Do earthworms help to sustain the slug predator Pterostichus melanarius (Coleoptera: Carabidae) within crops? Investigations using monoclonal antibodies. Mol. Ecol. 2000, 9, 1279–1292. [Google Scholar] [CrossRef]
  67. King, R.A.; Vaughan, I.P.; Bell, J.R.; Bohan, D.A. Prey choice by carabid beetles feeding on an earthworm community analysed using species- and lineage-specific PCR primers. Mol. Ecol. 2010, 19, 1721–1732. [Google Scholar] [CrossRef] [PubMed]
  68. Brown, G.G. How do Earthworms Affect Microfloral and Faunal Community Diversity? In The Significance and Regulation of Soil Biodiversity; Collins, H.P., Robertson, G.P., Klug, M.J., Eds.; Springer Science and Business Media: Dordrecht, The Netherlands, 1995; pp. 245–269. [Google Scholar]
Sustainability 08 00906 g001 1024
Figure 1. Map of the location of Slovakia in Europe and seven study sites.
Figure 1. Map of the location of Slovakia in Europe and seven study sites.
Sustainability 08 00906 g001
Table
Table 1. Geographic characteristics and land management of the seven study sites.
Table 1. Geographic characteristics and land management of the seven study sites.
Study SiteGeographical LocationSoil TypeSoil TextureAltitude (m)Land Management
NVEastern Slovak UplandHumic Regosol (Fluvisol)ClayeyAL-121
PG-123		AL-intensive farming
PG-cattle pasture
VODanubian UplandBlack Chernozem (Chernozem)LoamyAL-137AL-intensive farming
DVKrupina PlainHumic Regosol (Fluvisol)Sandy-loamAL-157
PG-155		AL-intensive farming
PG-alluvial meadow
MJBorská LowlandAL-Regosol (Regosol)
PG-Humic Regosol (Fluvisol)		Sandy
Sandy		AL-157
PG-160		AL-intensive farming
PG-meadow
KESlovak KarstEutric Cambisol (Cambisol)LoamyAL-360
PG-344		AL-extensive farming
PG-cattle pasture
TAKremnica MountainDystric Cambisol (Cambisol)LoamyAL-595
PG-597		AL-extensive farming
PG-sheep pasture
LTLow TatrasRegosol (Rendzina)LoamyAL-950
PG-931		AL-organic farming
PG-meadow
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; AL, arable land; PG, permanent grasslands.
Table
Table 2. Climatic characteristics from the nearest meteorological stations.
Table 2. Climatic characteristics from the nearest meteorological stations.
Study SiteMeteorological StationLong-Term Average Air Temperature (°C)Two Months Average Air Temperature before Sampling (°C)Long-Term Average Rainfall (mm)Two Months Rainfall before Sampling (mm)
NVMichalovce8.94.355928
VOKráľová pri Senci9.54.156057
DVDudince8.73.560667
MJMoravský Ján9.24.152553
KERožňava8.63.462033
TABanská Bystrica8.17.2795106
LTPoprad6.24.795041
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička.
Table
Table 3. Basic statistical characteristics of earthworm fresh biomass at seven study sites under different land use in 2015 (g·m−2).
Table 3. Basic statistical characteristics of earthworm fresh biomass at seven study sites under different land use in 2015 (g·m−2).
Study SiteALPG
MinMaxMean ± SDMedianMinMaxMean ± SDMedian
NV0.0101.640.8 ± 31.1032.664.8235.6134.5 ± 57.49132.7
VO0.093.328.2 ± 30.2623.2----
DV13.3143.566.4 ± 49.7646.884.9194.0122.0 ± 39.11129.4
MJ0.00.00.00.015.2171.084.4 ± 64.5478.0
KE42.790.463.3 ± 17.8258.37.3188.567.8 ± 63.4251.4
TA21.639.527.4 ± 6.2525.119.269.140.8 ± 19.0037.5
LT0.021.397.23 ± 8.352.128.749.828.2 ± 16.3528.8
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; AL, arable land; PG, permanent grasslands.
Table
Table 4. Basic statistical characteristics of earthworm density at 7 study sites under different land use in 2015 (ind·m−2).
Table 4. Basic statistical characteristics of earthworm density at 7 study sites under different land use in 2015 (ind·m−2).
Study SiteALPG
MinMaxMean ± SDMedianMinMaxMean ± SDMedian
NV0.057.129.2 ± 17.5424.5114.3261.2197.1 ± 53.20220.4
VO0.0122.445.5 ± 38.2540.8----
DV32.7114.353.6 ± 27.4349.0228.6383.7277.6 ± 54.15253.1
MJ0.00.00.00.016.3179.6100.3 ± 59.3798.0
KE146.9351.0226.2 ± 69.54195.932.7146.984.0 ± 48.2365.3
TA32.781.656.0 ± 21.8240.840.8179.6108.5 ± 49.3789.8
LT0.057.1420.99 ± 18.7724.4916.3163.374.6 ± 50.8665.3
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; AL, arable land; PG, permanent grasslands.
Table
Table 5. Summary of the numbers of earthworms of each species and Shannon-Wiener index at seven study sites in arable land (ind·m−2).
Table 5. Summary of the numbers of earthworms of each species and Shannon-Wiener index at seven study sites in arable land (ind·m−2).
NVVODVMJKETALTTotal
Aporrectodea caliginosa7.005.831.170.0011.700.002.3027.99
Aporrectodea rosea3.501.171.170.000.000.002.338.16
Eiseniella tetraedra0.001.170.000.001.170.000.002.33
Octolasion cyaneum0.000.000.000.000.0016.320.0016.32
Octolasion lacteum0.000.000.000.001.170.001.172.34
Sum of mature endogeic species10.508.172.340.0014.0416.325.8057.17
% of mature endogeic species64.3022.2670.010.0066.8677.7999.4966.23
Dendrobaena octaedra0.001.170.000.007.000.000.008.17
Dendrodrilus rubidus0.000.000.000.0000.004.660.004.66
Lumbricus rubellus0.002.331.170.000.000.000.003.50
Sum of mature epigeic species0.003.501.170.007.004.660.0016.33
% of mature epigeic species0.0029.9911.130.0033.3322.210.0018.92
Lumbricus terrestris5.830.007.000.000.000.000.0012.83
Sum of mature anecic species5.830.007.000.000.000.000.0012.83
% of mature anecic species35.700.0066.600.000.000.000.0014.86
Sum of mature species16.3311.6710.510.0021.0020.985.8386.30
Sum of juveniles12.8333.8243.150.00205.2534.9915.16345.20
Total sum29.1645.4953.650.00226.2555.9720.99431.50
H′1.501.901.360.001.410.791.522,72
Abbreviations: H′, Shannon-Wiener index; NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička.
Table
Table 6. Summary of the numbers of earthworms of each species and Shannon-Wiener index at six study sites in permanent grasslands (ind·m−2).
Table 6. Summary of the numbers of earthworms of each species and Shannon-Wiener index at six study sites in permanent grasslands (ind·m−2).
NVDVMJKETALTTotal
Allolobophora chlorotica3.501.170.000.000.000.004.66
Aporrectodea caliginosa39.6530.3248.9813.9923.323.50159.77
Aporectodea rosea5.837.000.000.003.508.1624.49
Eiseniella tetraedra1.170.001.170.000.000.002.34
Octolasion cyaneum0.000.000.000.001.174.665.83
Octolasion lacteum0.000.000.000.000.002.332.33
Sum of mature endogeic species50.1538.4950.1513.9927.9918.65199.42
% of mature endogeic species82.6980.4987.7470.59100.0099.9585.92
Dendrobaena octaedra1.171.171.171.170.000.004.67
Lumbricus castaneus0.000.002.330.000.000.002.33
Lumbricus rubellus0.002.331.170.000.000.003.50
Sum of mature epigeic species1.173.504.671.170.000.0010.51
% of mature epigeic species1.937.328.175.900.000.004.53
Aporrectodea longa0.000.001.170.000.000.001.17
Lumbricus terrestris9.335.831.174.660.000.0020.99
Sum of mature anecic species9.335.831.174.660.000.0020.99
% of mature anecic species15.3812.194.0923.510.000.009.55
Sum of mature species60.6547.8257.1619.8227.9918.66232.08
Sum of juveniles136.44228.5743.1564.1480.4755.98608.75
Total sum197.09276.39100.3183.96108.4574.64840.83
H′1.041.240.851.080.801.851.42
Abbreviations: H′, Shannon-Wiener index; NV, Nacina Ves; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička.
Table
Table 7. Soil chemical parameters at 7 study sites in arable land.
Table 7. Soil chemical parameters at 7 study sites in arable land.
pH KClTOC (g·kg−1)Nt (g·kg−1)P (mg·kg−1)K (mg·kg−1)Mg (mg·kg−1)
NV5.5116.672.5110.16245.59672.27
VO7.1815.891.9918.74256.53762.78
DV6.0413.541.6148.35310.84318.49
MJ4.587.430.9665.77132.1639.32
KE5.4613.091.584.84221.93184.84
TA4.8415.451.6233.56221.90127.36
LT6.7034.003.0538.23199.36949.12
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; TOC, total organic carbon; Nt, total nitrogen; P, available phosphorus; K, available potassium; Mg, available magnesium.
Table
Table 8. Soil chemical parameters at 6 study sites in permanent grasslands.
Table 8. Soil chemical parameters at 6 study sites in permanent grasslands.
pH KClTOC (g·kg−1)Nt (g·kg−1)P (mg·kg−1)K (mg·kg−1)Mg (mg·kg−1)
NV7.1823.182.7814.52293.56721.78
DV5.0813.881.913.02140.20466.68
MJ6.754.801.0231.4282.33113.11
KE5.8928.203.1322.83349.30260.85
TA4.1942.304.140.52136.22631.80
LT6.9451.305.163.82300.331233.15
Abbreviations: NV, Nacina Ves; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; TOC, total organic carbon; Nt, total nitrogen; P, available phosphorus; K, available potassium; Mg, available magnesium.
Table
Table 9. Results of a Spearman’s correlation analysis for earthworm density, biomass, diversity and selected soil, climatic and geographic parameters (n = 7 for AL, n = 6 for PG).
Table 9. Results of a Spearman’s correlation analysis for earthworm density, biomass, diversity and selected soil, climatic and geographic parameters (n = 7 for AL, n = 6 for PG).
AL PG
EDEBH′EDEBEH′
pH−0.0360.2860.893 **−0.2570.257−0.200
TOC−0.214−0.0710.750−0.543−0.771−0.029
Nt−0.214−0.0710.750−0.543−0.771−0.029
P−0.571−0.464−0.500−0.3710.2570.371
K0.4640.857 *0.393−0.429−0.200−0.429
Mg−0.1790.1430.929 **−0.086−0.257−0.486
** Correlation is significant at the 0.01 level; * Correlation is significant at the 0.05 level; Abbreviations: ED, earthworm density; EB, earthworm biomass; H′, Shannon-Wiener index; TOC, total organic carbon; Nt, total nitrogen; P, available phosphorus; K, available potassium; Mg, available magnesium; AL, arable land; PG, permanent grasslands.
Table
Table 10. Mean soil temperature and soil moisture at seven study sites under different land use in 2015 (°C, %).
Table 10. Mean soil temperature and soil moisture at seven study sites under different land use in 2015 (°C, %).
Study SiteSoil Temperature (°C)Soil Moisture (%)
ALPGALPG
5 cm20 cm5 cm20 cm5 cm20 cm5 cm20 cm
NV10.45.27.75.210.427.023.022.9
VO9.16.2--21.120.6--
DV8.97.97.97.739.031.947.629.9
MJ7.45.67.95.212.913.334.935.3
KE6.04.17.25.122.019.735.318.6
TA5.06.96.96.612.430.734.733.0
LT4.64.34.34.422.7-40.416.4
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; AL, arable land; PG, permanent grasslands.
Table
Table 11. Spearman’s Rank correlation coefficients (n = 49 for AL, n = 42 for PG) for earthworm density, biomass and selected abiotic and biotic parameters.
Table 11. Spearman’s Rank correlation coefficients (n = 49 for AL, n = 42 for PG) for earthworm density, biomass and selected abiotic and biotic parameters.
ALPG
EDEBEDEB
ST05−0.1180.1850.371 *0.457 **
ST20−0.0550.0340.481 **0.309 *
SM050.309 *0.2420.107−0.113
SM200.387 **0.528 **0.2500.225
PR80−0.137−0.307 *0.1330.072
** Correlation is significant at the 0.01 level; * Correlation is significant at the 0.05 level; Abbreviations: ED, earthworm density; EB, earthworm biomass; ST05, soil temperature in 5 cm depth; ST20, soil temperature in 20 cm depth; SM05, soil moisture in 5 cm depth; SM20, soil moisture in 20 cm depth; PR80, penetration resistance in 80 cm depth; AL, arable land; PG, permanent grasslands.
Table
Table 12. Summary of the mean numbers of arthropods, ground beetles and carabids (ind·trap−1) at seven study sites in arable land and permanent grasslands.
Table 12. Summary of the mean numbers of arthropods, ground beetles and carabids (ind·trap−1) at seven study sites in arable land and permanent grasslands.
NVVODVMJKETALT
ALArthropods15.8629.4320.2940.0045.0039.4332.71
of which Ground beetles12.4317.0012.007.1413.2923.1428.43
of which Carabids11.63.10.41.13.121.324.4
PGArthropods36.57-43.86102.5778.1431.4323.29
of which Ground beetles19.57-9.7134.5720.008.0010.14
of which Carabids13.9-0.117.78.02.04.9
Abbreviations: NV, Nacina Ves; VO, Voderady; DV, Dvorníky; MJ, Moravský Ján; KE, Kečovo; TA, Tajov; LT, Liptovská Teplička; AL, arable land; PG, permanent grasslands.

Share and Cite

MDPI and ACS Style

Kanianska, R.; Jaďuďová, J.; Makovníková, J.; Kizeková, M. Assessment of Relationships between Earthworms and Soil Abiotic and Biotic Factors as a Tool in Sustainable Agricultural. Sustainability 2016, 8, 906. https://doi.org/10.3390/su8090906

AMA Style

Kanianska R, Jaďuďová J, Makovníková J, Kizeková M. Assessment of Relationships between Earthworms and Soil Abiotic and Biotic Factors as a Tool in Sustainable Agricultural. Sustainability. 2016; 8(9):906. https://doi.org/10.3390/su8090906

Chicago/Turabian Style

Kanianska, Radoslava, Jana Jaďuďová, Jarmila Makovníková, and Miriam Kizeková. 2016. "Assessment of Relationships between Earthworms and Soil Abiotic and Biotic Factors as a Tool in Sustainable Agricultural" Sustainability 8, no. 9: 906. https://doi.org/10.3390/su8090906

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop