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41 results for “soil arthropods”
Soil Arthropods in Hemlock Removal Experiment at Harvard Forest 2008
In eastern North American forests, eastern hemlock (Tsuga canadensis) is a foundation species. As hemlock is lost from forests due to the invasive hemlock woolly adelgid (Adelges tsugae) and pre-emptive salvage logging, the structure of assemblages of species associated with hemlock is expected to change. We manipulated hemlock canopy structure at hectare scales to investigate the effects of hemlock death on assemblages of ants, beetles, and spiders in a New England forest. Relative to reference hemlock stands, both in situ death of hemlock and logging and removal of hemlock altered composition and diversity of beetles and spiders, and logging increased the species richness and evenness of ant assemblages. Species composition of ant assemblages in disturbed habitats was non-random relative to the regional species pool, but we found no evidence that interspecific competition shaped the structure of ant, beetle or spider assemblages, in either manipulated or intact forest stands. Environmental filtering by hemlock appears to maintain low levels of species richness and evenness in forest stands, suggesting that the loss of hemlock due to the hemlock woolly adelgid or human activities will not likely lead to extirpations of ant, beetle, or spider species at local scales.
Soil microarthropods, ground-dwelling arthropods and soil properties in mown and grazed grasslands in the Veluwe region
<p>In order to find out which factors limit the restoration of soil life and their ecosystem services under grasslands on sandy soils, we studied 40 grasslands of which 20 had agricultural and 20 nature land use, all after an agricultural history.</p> <p> </p> <p><strong>Site selection</strong></p> <p>Within the Veluwe region (The Netherlands), we selected 40 grasslands: 20 agricultural grasslands and 20 nature grasslands which were managed as new nature reserves since last tillage. Within each of these two land-use types, two types of grassland management were selected: mowing and grazing. Within each of the four combinations of land use and management we selected ten grasslands over a broad age range since last tillage. All grasslands were located on sandy soils (Typic Haploquod and Plaggeptic Haploquod; Soil Survey Staff 1999) with a deep water table to rule out dispersal of soil fauna during waterlogging (Siepel 1996; Jabbour & Barbercheck 2008).</p> <p> </p> <p><strong>Vegetation and insect surveys</strong></p> <p>Within each grassland a 5×5 meter monitoring plot was laid-out for plant cover surveys, insect and soil-microarthropod sampling and soil analyses. The vegetation surveys were carried out in 2019 at the end of May and in early June, using the Braun-Blanquet method (Braun-Blanquet 1932). In June 2019 soil-surface dwelling insects were sampled with a pitfall trap (Wiggers et al. 2015). Three pitfall traps (8 cm diameter, ca. 20 cm deep) were placed in each plot. Traps were half filled with a solution of water and glycol (3:1) and 3 % Extran soap. A plexiglass cover 20 cm above the trap prevented rainfall diluting the liquid. Traps were removed and emptied after seven days. Insects were identified and grouped at the order level, however, predator groups (carabid and staphylinid beetles, ants and spiders) were identified to the species level in order to group those by their feeding guild.</p> <p> Before analyzing the pitfall trap catches we first removed certain groups from the counts because pitfall traps are not well-suited to catch them systematically: Acari, Collembola, Psocoptera, Thysanoptera, Trichoptera, Lepidoptera, Siphonaptera, Diptera, Symphyta, Apocrita, and Parasitica. The remaining 62.0% of the caught individuals were surface-dwelling animals, and their totals (of three pitfall traps per site) were analyzed with negative-binomial generalized linear models. We also analyzed the subset of predators (73.6% of the surface dwellers).</p> <p> </p> <p><strong>Soil chemical and pesticide sampling and analysis</strong></p> <p>On 8, 9 and 16 October 2019, a bulk soil sample of 50 soil cores (0 - 10 cm) was collected from each 5×5 meter monitoring plot. After homogenization a sub-sample was analyzed for soil chemical analysis. Prior to chemical analysis, samples were oven-dried at 40 °C. Soil acidity of the oven-dried samples was measured in 1 M KCl (pH-KCl). Soil Organic Matter (SOM) was determined by loss-on-ignition (Ball 1964). Ammonium-lactate-extractable P (PAL) was determined according to the standard method (Bronswijk et al. 2003). Total potassium (K) in solution was determined using flame photometry after extraction of soil with HCl (0.1 M) and oxalic acid (0.5 M) in a 1:10 M:V ratio and filtration (Bronswijk et al. 2003). Clay (<2 μm diameter) content was determined through density fractionation (NEN 5753, 2018). Another soil sub-sample was sent to Eurofins Zeeuws-Vlaanderen for pesticide/residue analysis. Samples were freeze-dried and homogenized prior to analysis. Homogenized samples were extracted with acetone, petroleum ether and dichloro-methane using an optimized mini-Luke method. In total 664 pesticides and pesticide residues were analyzed with gas chromatography (Agilent) and liquid chromatography (LC-chromatograph (Agilent) and MSMS (Sciex)). Glyphosate, its residue AMPA and gluphosinate were analyzed using single residue analysis. The detection limit (LOD) was 0,1 mg per kg sample.</p> <p> </p> <p><strong>Soil microarthropods sampling and determination</strong></p> <p>Grasslands were sampled for microarthropods on 8, 9 and 16 October 2019, taking three cores per monitoring plot of 5×5 m. Cores were 5 cm Ø and 5 cm deep mineral soil plus upper litter. Cores were taken in the middle of the monitoring plots, 1 m apart from each other. Cores were extracted on a Tullgren funnel for 7 days. During that period temperature was increased from 35 to 45 <sup>0</sup>C. Ethanol 70% was used as conservation fluid and microarthropods obtained were put into lactic acid 30% for clarification and identification (Siepel & van de Bund 1988). Identification for the main groups is according to Weigmann (2006) for Oribatida, Karg (1993) for Gamasina and Karg (1989) for Uropodina. Nomenclature is according to Siepel et al. (2009) (Oribatida), Siepel et al. (2016) (Astigmatina) and Siepel et al. (2018) (Mesostigmata).</p> <p> </p> <p><strong>Litter decomposition</strong></p> <p>To determine the potential decomposition of soil organic matter on each grassland the Tea Bag Index (TBI) was used (Keuskamp et al. 2013). In each grassland four green tea and four rooibos tea bags were buried at 8 cm deep in May 2019 in the 5×5 meter monitoring plots. After 90 days tea bags were collected and stored at 4 ⁰C prior to drying at 70 ⁰C for 48 hours. After drying, remaining sand and (fine) plant roots were carefully removed and the teabags were weighted to determine weight loss. The decomposition rate (<em>k</em>) and the litter stabilization factor (<em>S</em>) of the tea was calculated using the Tea Bag Index (Keuskamp et al. 2013).</p> <p> </p> <p><strong>Data files</strong></p> <p><em><strong>siteData.csv</strong></em></p> <p>site: grassland ID</p> <p>landuse: agricultural or nature land use</p> <p>treat: mowing or grazing management</p> <p>yearsManaged: number of years since last tillage</p> <p>fertilization: kg available nitrogen applied per hectare</p> <p>nGrazingDaysPerHa: livestock days per hectare per year</p> <p>N: mg nitrogen per 100 g </p> <p>PAl: mg P<sub>2</sub>0<sub>5</sub> per 100 g</p> <p>organicMatter: soil organic matter percentage</p> <p>clay: soil clay percentage</p> <p>nPlantSpecies: number of plant species</p> <p>nForbSpecies: number of forb species</p> <p>nMitesSpringtails: total number of individuals of mites and springtails in three core samples</p> <p>nMitesSpringtailsSpecies: number of mite and springtail species in three core samples</p> <p>shannonMitesSpringtails: Shannon diversity index for microarthropods (mites and springtails)</p> <p>nHerboFungivorousGrazerMitesSpringtails: total number of individuals of mites and springtails that are (herbo-)fungivorous grazers, in three core samples</p> <p>nInsectsSpidersPitfall: number of ground-dwelling insect and spider individuals in pitfall traps</p> <p>nPredatorInsectsSpidersPitfall: number of ground-dwelling insect and spider individuals that are predators, in pitfall traps</p> <p>decompositionRate: decomposition rate based on the Tea Bag Index</p> <p>litterStabilisationFactor: litter stabilization factor based on the Tea Bag Index</p> <p>nPesticides: number of detected pesticides</p> <p>avicidesTotalConcentration: microgram antraquinon per kg dry soil</p> <p>fungicidesTotalConcentration: total microgram of fungicides per kg dry soil</p> <p>insecticidesTotalConcentration: total microgram of insecticides per kg dry soil</p> <p>herbicidesTotalConcentration: total microgram of herbicides per kg dry soil</p> <p>pesticidesTotalConcentration: total microgram of pesticides (avicides+fungicides+herbicides+insecticides) per kg dry soil</p> <p>nPredatorCarabids: number of predator carabid beetles in pitfall traps</p> <p>nPredatorStaphylinids: number of predator staphylinid beetles in pitfall traps</p> <p>distanceToNearestHighway: shortest distance (in meters) to the nearest highway (A-road)</p> <p>distanceToNearestNroad: shortest distance (in meters) to the nearest national road (N-road)</p> <p> </p> <p><em><strong>mitesSpringtails.csv</strong></em></p> <p>core: core ID, consisting of the site ID (number) and core-within-site ID (letter)</p> <p>species: soil mite or springtail taxon encountered in a soil core</p> <p>guild: feeding guild of the soil mite or springtail taxon:</p> <p> b: bacterivorous</p> <p> fb: fungivorous browser</p> <p> fg: fungivorous grazer</p> <p> gp: general predator</p> <p> hb: herbivorous browser</p> <p> hfg: (herbo-)fungivorous grazer</p> <p> hg: herbivorous grazer</p> <p> o: omnivore</p> <p> ohf: opportunistic herbo-fungivore</p> <p>droughtSens: drought strategy of soil mite and springtail taxa</p> <p> 1: drought avoiders</p> <p> 2: drought sensitive</p> <p> 3: drought mesotolerant</p> <p> 4: drought tolerant</p> <p>microart: number of individuals of a taxon found in a soil core</p> <p> </p> <p><em><strong>insecticideData.csv</strong></em></p> <p><em><strong>fungicideData.csv</strong></em></p> <p><em><strong>herbicideData.csv</strong></em></p> <p>site: grassland ID</p> <p>other variables: microgram of a certain pesticide per kg dry soil</p> <p> </p>
Vegetation influences desert soil arthropods and their response to altered precipitation
Altered size and frequency of precipitation pulses will influence both plant and soil communities in water-limited systems such as the Sonoran Desert. Little is known about the response of desert soil fauna communities, particularly the mesofauna that are important components of the detrital food web. Further, while there is a well-documented impact of vegetation on soil fauna communities, the role of vegetation in buffering the soil community against such environmental changes is unclear. We conducted a short-term field study to (1) assess how the amount and frequency of monsoon season precipitation pulses influence soil arthropod communities and (2) explore the role of plant-soil linkages in the response of soil arthropod communities to altered precipitation. We experimentally altered the size (ambient and 50% increase) and frequency (ambient and 2X reduced frequency) of monsoon season precipitation for two dominant shrubs representing distinctly different functional types, as well as interplant spaces. We measured the resulting soil arthropod abundance, diversity, and composition, as well as key soil properties to characterize the soil habitat beneath each vegetation type.
FIGURE 3. Quantitative burrow properties. A in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 3. Quantitative burrow properties. A) Measurements were taken for number of surface openings (SO), burrow slope (S), maximum depth (D), total length (L), tunnel, shaft, and chamber width (w), height (h), and circumference (c), and branching angles (BA). B) Complexity includes the number of segments (s), chambers (h), and surface openings (e) within a single burrow system. C) Tortuosity of a single burrow segment is found by dividing the total length (u) by the straight-line distance (v) from end to end. Modified from Hembree (2019).
FIGURE 7 in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 7. Burrow morphology: architecture and bioglyphs. A) Simple subhorizontal burrow of Hadrurus arizonensis with a single entrance. B) Helical subhorizontal burrow of H. arizonensis with a single entrance. C) Simple subhorizontal burrow of Pandinus imperator with a single entrance. D) Branching subhorizontal burrow of P. imperator with a single entrance. E) Branching, helical burrow of P. imperator with a large terminal chamber (at arrow). F) Mazework of H. arizonensis with multiple branches and two entrances (at arrows). G) Multiple, fine striations (at arrows) along, and parallel to, the shaft of a Gorgyrella inermis burrow. H) Pair of protrusions (at arrows) on the roof of a terminal chamber of Mastigoproctus giganteus. I) Large striations (at arrows) along the side of a subhorizontal burrow of Aphonopelma chalcodes. J) Burrow opening of Hogna lenta showing silk and sediment lining (at arrow). K) Compression lining (at arrow) visible in a cross section of a tunnel of Scolopendra polymorpha.
FIGURE 6 in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 6. Burrow morphology: openings and architecture. A) Elliptical burrow opening of Scolopendra polymorpha. B) Circular burrow opening of Hysterocrates gigas surrounded by a mound of excavated sediment. C) Paired triangular burrow openings of Pandinus imperator. D) Simple vertical burrow of Gorgyrella inermis with a single entrance. E) Vertical branching burrow of Pelinobus muticus with a single entrance. F) Vertical burrow Hysterocrates gigas with large terminal chamber and a single entrance. G) Subvertical helical burrow of Aphopelma chalcodes with a single entrance. H) J-shaped burrow of Mastigoproctus giganteus with a single entrance. I) U-shaped burrow of M. giganteus with two entrances. J) Y-shaped burrow of M. giganteus with two entrances. K) Mazework of M. giganteus with five entrances (at numbers). L) U-shaped burrow of S. polymorpha with two entrances. M) Mazework of S. polymorpha with four entrances (at numbers).
FIGURE 4. Burrowing techniques observed among the studied arthropod predators. A in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 4. Burrowing techniques observed among the studied arthropod predators. A) Initial burrowing by intrusion by Scolopendra polymorpha (burrow opening at arrow). B) Burrowing by intrusion by Hogna lenta. C) Continued construction of a vertical shaft by compression by Gorgyrella inermis, compressing sediment along burrow boundary (at arrow) to increase the width. D) Subsurface tunnel construction by intrusion by Hemiscolopendra marginata. No sediment is removed as the tunnel is extended but is pressed against the tunnel boundary (at arrow). E) Burrowing by excavation by Mastigoproctus giganteus. Sediment is removed and carried with the pedipalps (at arrow). F) Burrowing by excavation by Pelinobus muticus. Sediment is removed and carried with the pedipalps (at arrow). G) Burrowing by excavation by Hadrurus arizonensis. Sediment is scraped and kicked back out (at arrow) of the developing burrow with the first two pairs of legs. H) Backfilling of a tunnel by S. polymorpha. The centipede removes sediment from the developing tunnel and uses it to fill the old tunnel (at arrow). I) Light silk lining around the opening, shaft, and chamber (at arrows) of Hysterocrates gigas. J) Thick silk lining around the shaft (at arrow) of G. inermis producing a smooth interior surface. K) Six silk runners (example at arrow) connected to the burrow entrance of G. inermis with a closed trap door.
FIGURE 2 in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 2. Examples of experimental enclosures used in this study. A) Surface view of a 212 L enclosure before the introduction of the study animal. Objects were placed on the surface to encourage burrowing. B) Side view of a 246 L enclosure filled with 60 cm of an organic rich clay loam. C) A 212 L enclosure filled with 55 cm of an organic-rich clay loam. Five specimens of Pandinus imperator produced a branching burrow complex in the subsurface (at arrow). D) Plaster-filled, connected U-shaped burrows produced by Mastigoproctus giganteus in a 38 L enclosure filled with an organic-rick clay loam.
FIGURE 1 in Linking burrow morphology to the behaviors of predatory soil arthropods: Applications to continental ichnofossils
FIGURE 1. Burrowing arthropod predators investigated in this study. A) Scolopendra viridis, B) Scolopendra polymorpha, C) Hemiscolopendra marginata, D) Hadrurus arizonensis, E) Smeringurus mesaensis, F) Uroctonus mordax, G) Heterometrus spinifer, H) Pandinus imperator, I) Mastigoproctus giganteus, J) Hogna lenta, K) Gorgyrella inermis, L) Myrmekiaphilia sp., M) Aphonopelma chalcodes, N) Hysterocrates gigas, and O) Pelinobus muticus.
Figure 2 in The influence of distance from crushed stone mining on surface-active arthropods and soil chemical properties
Figure 2. Principal coordinates analyses (PCO) of the composition of soil chemical properties across sampling points from A, Blue Rock and B, Ikwezi mining sites. Grey triangles = 5 m, circles = 30 m, squares = 50 m, and open triangles = 70 m from the mining activities.
Figure 1 in The influence of distance from crushed stone mining on surface-active arthropods and soil chemical properties
Figure 1. Study sites showing sampling points (5 m, 30 m, 50 m and 70 m) from the mining activities at Blue Rock and Ikwezi mining sites.
Figure 3 in The influence of distance from crushed stone mining on surface-active arthropods and soil chemical properties
Figure 3. Effect of distance from the mining sites on the mean values of zinc. A, Blue Rock and B, Ikwezi mining site.
Channelling of basal resources and use of allochthonous marine carbon by soil arthropods of the Wadden Sea salt marsh
<p>Salt marshes are located between the marine and terrestrial systems. Because they form as sediment accumulates, they comprise a gradient of shore height with differing inundation frequencies and associated abiotic soil conditions. Along this gradient, both autochthonous vascular plant resources and allochthonous marine algal or detrital resources are available, with the availability of both varying with season and salt marsh zone. However, little is known about the importance of either resource for the soil animal food web. We investigated both spatial and temporal resource use of the soil macro- and mesofauna of the salt marsh using neutral lipid fatty acids (NLFAs). Generally, irrespective of season and zone the soil animal food web relied on carbon originating from autochthonous vascular plants and associated bacteria and fungi, with the role of bacteria generally exceeding that of fungi. However, the channelling of fungal resources consistently peaked in October, whereas seasonal changes in the channelling of plant and bacterial resources varied among salt marsh zones. Further, variations in the channelling of resources with season and zone varied among salt marsh animal species. Although being only minor, allochthonous resources of marine origin contributed to soil food web nutrition across salt marsh zones and seasons. The contribution of algae to soil food web nutrition depended on inundation frequency and season, i.e. algal productivity. Overall, the results demonstrate that the salt marsh soil fauna predominantly relies on autochthonous vascular plant resources, with the contribution of allochthonous marine resources being minor and restricted to few taxa.</p>
Genetic diversity varies with species traits and latitude in predatory soil arthropods (Myriapoda: Chilopoda)
<p><strong>Aim</strong></p> <p>To investigate the drivers of intra-specific genetic diversity in centipedes, a group of ancient predatory soil arthropods.</p> <p><strong>Location</strong></p> <p>Asia, Australasia and Europe</p> <p><strong>Time period</strong></p> <p>Present</p> <p><strong>Major taxa studied</strong></p> <p>Centipedes (Class: Chilopoda)</p> <p><strong>Methods</strong></p> <p>We assembled a database of 1245 mitochondrial cytochrome c oxidase subunit I sequences representing 128 centipede species from all five orders of Chilopoda. This sequence dataset was used to estimate genetic diversity for centipede species and compare its distribution with estimates from other arthropod groups. We studied the variation in centipede genetic diversity with species traits and biogeography using a beta regression framework, controlling for the effect of shared evolutionary history within a family.</p> <p><strong>Results</strong></p> <p>A wide variation in genetic diversity across centipede species (0 to 0.1713) falls towards the higher end of values among arthropods. Overall, 27.57% of the variation in mitochondrial COI genetic diversity in centipedes was explained by a combination of predictors related to life history and biogeography. Genetic diversity decreased with body size and latitudinal position of sampled localities, was greater in species showing maternal care and increased with geographic distance among conspecifics.</p> <p><strong>Main conclusions</strong></p> <p>Centipedes fall towards the higher end of genetic diversity among arthropods, which may be related to their long evolutionary history and low dispersal ability. In centipedes, the negative association of body size with genetic diversity may be mediated by its influence on local abundance or the influence of ecological strategy on long-term population history. Species with maternal care had higher genetic diversity, which goes against expectations and needs further scrutiny. Hemispheric differences in genetic diversity can be due to historic climatic stability and lower seasonality in the southern hemisphere. Overall, we find that despite the differences in mean genetic diversity among animals, similar processes related to life history strategy and biogeography are associated with the variation within them.</p>
Data supplementing Lichtenberg et al. (2023) Differential effects of soil conservation practices on arthropods and crop yields. Journal of Applied Entomology
<p>This dataset contains data and scripts that supplement the publication</p> <p>Lichtenberg et al. Differential effects of soil conservation practices on arthropods and crop yields. J. Appl. Entomol. 147: 931-940. <a href="https://doi.org/10.1111/jen.13188">https://doi.org/10.1111/jen.13188</a></p> <p>Please cite the above article if you use any of the included data or code.</p> <p>Files are described in README.md.</p>
Data from: Soil and ground-dwelling arthropod diversity on green roofs: Functional groups are strongly influenced by substrate depth and plant community
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Channelling of basal resources and use of allochthonous marine carbon by soil arthropods of the Wadden Sea salt marsh
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Grasshoppers, other arthropods, plant, and soil data from Konza Prairie bison grazing lawns
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Genetic diversity varies with species traits and latitude in predatory soil arthropods (Myriapoda: Chilopoda)
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Biodiversity - Fauna - Soil Fauna - Relative frequency of soil arthropod groups at Cub Hill
Relative frequency of soil arthropod groups at Cub Hill Introduction The Baltimore Ecosystem Study (BES) has established a network of long-term permanent forest plots. These plots will provide long-term data on vegetation, soil and hydrologic processes in the key ecosystem types within the urban ecosystem. The current network of study plots includes eight forest plots, chosen to represent the range of forest conditions in the area. The goal of the soil invertebrate survey was to compare community composition and abundance of soil macrofauna, primarily earthworms (Oligochatea), terrestrial isopods (Isopoda: Oniscidea), and millipedes (Diplopoda). Plot Locations and Characterizations In November of 1998 four rural, forested plots were established at Oregon Ridge Park in Baltimore County northeast of the Gwynns Falls Watershed. Oregon Ridge Park contains Pond Branch, the forested reference watershed for BES. Two of these four plots are located on the top of a slope; the other two are located midway up the slope. Four urban, forested plots were established in November 1998, two at Leakin Park and two adjacent to Hillsdale Park in west Baltimore City in the Gwynns Falls. One of the plots in Hillsdale Park was abandoned in 2004 due to continued vandalism. Plot locations: Hillsdale 1: 39deg19'28.14degN, 76deg42'16.49"W Hillsdale 2: 39deg19'31.24degN, 76deg42'28.62"W Leakin 1: 39deg18'1.32"N, 76deg41'37.08"W Leakin 2: 39deg18'5.42"N, 76deg41'34.15"W Oregon top-slope - 1: 39deg28'51.11"N, 76deg41'22.50"W Oregon mid-slope - 1: 39deg28'51.32"N, 76deg41'18.24"W Oregon top-slope - 2: 39deg29'12.74"N, 76deg41'22.88"W Oregon mid-slope - 2: 39deg29'12.68"N, 76deg41'18.62"W Soil arthropods were sampled between November 1999 and 2000 using pitfall traps. At each plot a total of ten traps were placed which were emptied monthly. Earthworms were sampled using a combination of formalin solution (Raw 1954) and mustard suspension. 50cm x 50cm quadrats were used. Earthworms samples were tak
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