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Faecal samples analysed per bat species for each location, season and habitat type in northern Madagascar
<p>This table is part of the PhD thesis of Carme Tuneu-Corral, entitled '<strong>Bats and rice: promoting Integrated Pest Management to enhance biodiversity conservation</strong>'. It is the <strong><em>Table A4.1 </em></strong>of the supplementary material of the Chapter 5 '<em>Beyond borders: evaluating the role of protected areas in promoting bat-mediated pest suppression in rural areas of northern Madagascar</em>', and compiles the information on the number of samples analysed per bat species for each location, season and habitat type. Buildings were all located in rural villages outside protected areas, and caves and forest were all located inside protected areas.</p> <p>Methodology: </p> <p>Due to the subtropical climate of this country, we sampled bats in two periods representing the two main seasons for both Amber Mountain and Ankarana. Dry and wet season vary slightly in timing and extent, and we adjusted the field periods to cover the end of the dry season (October – November 2022), and the end of the wet season (May 2023, as in April one of the protected areas was inaccessible due to the poor state of the road caused by heavy rains). French Mountain was visited only in the dry season (October – November 2022) due to logistic limitations. We used mist-nets and harp traps to sample insectivorous bats in protected areas and rural villages. Bat captures were conducted for 7-10 consecutive nights in each protected area, changing sampling points daily to cover a wider area. We sampled bats in a total of six caves and four forest points in Ankarana; six caves and two forest points in French Mountain; and 10 forest points in Amber Mountain (there are no known caves in this protected area). Three school buildings were visited at 16 km from Ankarana borders, two public buildings at 3 km from Amber Mountain borders, and two school buildings at 1 km from French Mountain borders. When sampling forest habitats, mist-nets and harp traps were installed 30 minutes before sunset and remained open for at least four hours. When sampling bats at roost entrances (caves inside protected areas and buildings in rural villages), bats were captured before sunrise when returning to the colony after feeding. In these cases, we used mist-nets and harp traps set up four hours before dawn, which remained in place until 30 minutes after sunrise.</p> <p>All insectivorous bats captured were measured, weighed and identified using different bibliographic references. Bat captures and handling were conducted following guidelines approved by the American Society of Mammalogists (Sikes and Gannon, 2011). Bats were kept in clean cloth bags until they defecated, generally for a maximum of one hour. In case the bat individuals had not defecated within that time interval, they were released after being measured, weighted and identified. Faecal pellets of each individual were immediately collected and stored in 2 ml tubes with 95% ethanol and labelled accordingly. All bats were released at the same site where they were captured. We gathered a total of 500 samples to assess bat diet: 250 samples collected in the dry season and 250 samples in the wet season. The number of samples collected per species varied according to their rate of capture at the different sampling points.</p> <p>We were able to trap 15 different insectivorous bat species, 11 Madagascar endemics, and four regional endemics also occurring on nearby islands. Twelve bat species were captured exclusively inside the protected areas and those considered largely forest dependent are highlighted in bold (C<em>haerephon jobimena, Laephotis matroka, Macronycteris commersoni, Miniopterus aelleni, M. ambohitrensis, M. gleni, M. griveaudi, Myotis goudoti, Otomops madagascariensis, <strong>Paratriaenops auritus, Paremballonura tiavato</strong>, Triaenops menamena</em>), and two were captured exclusively outside the protected areas (<em>Chaerephon leucogaster, Mops leucostigma</em>). <em>Mormopterus jugularis</em> was the only species found roosting both in caves and buildings, although it was primarily captured in natural roosts in this study. We collected faecal samples for all these species, obtaining operational genetic material (i.e. OTUs representing more than 1% of the total dietary reads of each sample) from 454 of the 500 faecal samples analysed (Table A4.1). </p>
FIGURE 1 in A new crayfish of the genus Cambarus Erichson, 1846 (Decapoda: Cambaridae) from an under-sampled habitat type in central Ten- nessee, USA
FIGURE 1. Typical habitat for Cambarus clivosus, new species—a high gradient, seepfed creek in Cannon Co., TN.
FIGURE 4 in A new crayfish of the genus Cambarus Erichson, 1846 (Decapoda: Cambaridae) from an under-sampled habitat type in central Ten- nessee, USA
FIGURE 4. Known range of Cambarus clivosus, new species, in central Tennessee, USA. Closed circles indicate sites at which C. clivosus was found; open circles indicate sites at which C. clivosus was absent.
Water body type Fig. 7 in Ecomorphology of a generalist freshwater gastropod: complex relations of shell morphology, habitat, and fecundity
Water body type Fig. 7 Variation in shell shape (a) and size (b) between water body types. notches extend to ± 1.58 times the IQR divided by the root squared The boxplots show the median (middle line), quartiles (boxes), 1.5 times number of observations, overlapping notches being strong evidence that the interquartile range (IQR) (whiskers), extreme values (dots). The the two medians do not differ (Chambers et al. 1983)
Data from: Modelling the area of occupancy of habitat types with remote sensing
1. A current challenge of biodiversity and conservation is the estimation of the spatial extent of habitat types across broad territories. In the absence of fine-resolution maps, predictive modelling helps in assessing the spatial distribution of vegetation cover. However, such approaches are still uncommon in regional planning and management. Here, we present a framework for mapping the area of occupancy (AOO) of habitat types that allows highly suitable estimates at different scales. 2. We model the potential AOO with abiotic variables related to topography and climate, resulting in broad AOO estimates that are subsequently downscaled to the local AOO with remote sensing. The combination of individual local AOO estimates allows the defining of the realized AOO, comprising locations with a high likelihood of occurrence and low uncertainty for each habitat. We applied this framework to mapping 24 protected habitat types of Natura 2000 sites in northern Spain. 3. Local and realized AOO were highly accurate, with a 70% overall accuracy for the realized AOO. Remote sensing data, and especially LiDAR, were the most important predictors in habitat types related to forests and shrubs, followed by rock outcrops and pastures. Environmental variables were also relevant for specific habitats subject to abiotic constraints. 4. The combination of ecological modelling with remote sensing offers multiple advantages over traditional field surveys and image interpretation, allowing the harmonization of habitat maps across large regions and through time. This is particularly useful for implementing conservation actions under Natura 2000 principles or assessing IUCN criteria for ecosystems.
Supplementary Table S1 for manuscript Two new species of Russula subsection Amoeninae described from dry dipterocarp forest in Thailand suggest niche speciali-zation to this habitat type
<p>Specimens and GenBank accession number of DNA sequences used in the phylogenetic analyses. The newly generated sequences in this study are presented in boldface. The A is indicated for angiocarpic specimens.</p>
Fig. 4. 1938 in Determining Type Locality Habitat and Historic Land Use at Current Sites of the Miami Tiger Beetle, Cicindelidia floridana (Cartwright) (Coleoptera: Carabidae: Cicindelinae)
Fig. 4. 1938 aerial photograph of Richmond pine rocklands and vicinity. White rectangle indicates location of Fig. 5A–D. Pine rockland forests are visible on elevated terrain (diagonally from upper right to lower left), largely adjacent to riverbeds and interspersed with agricultural development (in the lower left quarter).
Fig. 3. Terrestrial photographs from 1940 in Determining Type Locality Habitat and Historic Land Use at Current Sites of the Miami Tiger Beetle, Cicindelidia floridana (Cartwright) (Coleoptera: Carabidae: Cicindelinae)
Fig. 3. Terrestrial photographs from 1940 at the site of Barry University. Photographs provided by Barry University Archives and Special Collections.
Fig. 2 in Determining Type Locality Habitat and Historic Land Use at Current Sites of the Miami Tiger Beetle, Cicindelidia floridana (Cartwright) (Coleoptera: Carabidae: Cicindelinae)
Fig. 2. Peter's (1981) "island" (outlined area), type locality of Cicidelidia floridana (circle), and approximate location of Fig. 3 (star). A) 1940 aerial photograph, B) 1950 aerial photograph. Satellite image underlay courtesy of Google Earth.
Fig. 5 in Determining Type Locality Habitat and Historic Land Use at Current Sites of the Miami Tiger Beetle, Cicindelidia floridana (Cartwright) (Coleoptera: Carabidae: Cicindelinae)
Fig. 5. Cicindelidia floridana occurrences projected on Richmond pine rocklands. A) 1938 aerial photograph, B) 1952 aerial photograph (arrows indicate areas of modified substrate without canopy), C) 1963 aerial photograph (stars approximately indicate areas with little or no canopy), D) 2017 satellite imagery, courtesy of Google Earth.
FIGURE. Thalictrum tsawarungense in the wild (Zayu in Xizang, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruits. N. Achenes (immature). Photographed by Y.P. Zeng. in Thalictrum hengduanshanense and T. longistipitatum (Ranunculaceae), two new species from southeastern Xizang and northwestern Yunnan, China
FIGURE. Thalictrum tsawarungense in the wild (Zayu in Xizang, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruits. N. Achenes (immature). Photographed by Y.P. Zeng.
FIGURE. Thalictrum hengduanshanense in the wild (Dêqên in northwestern Yunnan, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruits. N. Achenes (immature). Photographed by Y.P. Zeng. in Thalictrum hengduanshanense and T. longistipitatum (Ranunculaceae), two new species from southeastern Xizang and northwestern Yunnan, China
FIGURE. Thalictrum hengduanshanense in the wild (Dêqên in northwestern Yunnan, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruits. N. Achenes (immature). Photographed by Y.P. Zeng.
FIGURE. Thalictrum wangii in the wild (Lijiang in northwestern Yunnan, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruit. N. Achenes (immature). Photographed by Y.P. Zeng. in Thalictrum hengduanshanense and T. longistipitatum (Ranunculaceae), two new species from southeastern Xizang and northwestern Yunnan, China
FIGURE. Thalictrum wangii in the wild (Lijiang in northwestern Yunnan, China, the type locality). A. Habitat. B. Habit. C. Roots. D. Portion of stem. E. Leaf (left: adaxial side; right: abaxial side). F. Leaflet (adaxial side). G. Portion of adaxial side of leaflet. H. Portion of abaxial side of leaflet. I. Flower. J. Sepal (left: adaxial side; right: abaxial side). K. Stamens. L. Carpels. M. Aggregate fruit. N. Achenes (immature). Photographed by Y.P. Zeng.
Species of Acantholichen occurring only in the Neotropics show a high degree of endemism (Dal Forno et al. 2016). Of the seven species now recognized in this genus (Table 2), 71.4% (5) are known only from South America. As with Dictyonema, Acantholichen seem to be specific to substrate type and appears in the Andean small forest occurring on mosses in tree bark inhabiting mostly exposed habitats. Cyphellostereum is also represented by a high number of species restricted to the Neotropics [6 (66.6%)], while one is known only from North America, one from Southeastern United States and Puerto Rico, and another species is known only from Borneo and Fiji (Table 2). It is probably due to their unusual appearance that these lichens are getting confused with free-living cyanobacteria colonies, and that there are still undescribed species in the Neotropics. in Eight new species of lichenized Basidiomycota in the genera Acantholichen, Cyphellostereum and Dictyonema s.str. (Agaricales, Hygrophoraceae) from northern South America
Species of Acantholichen occurring only in the Neotropics show a high degree of endemism (Dal Forno et al. 2016). Of the seven species now recognized in this genus (Table 2), 71.4% (5) are known only from South America. As with Dictyonema, Acantholichen seem to be specific to substrate type and appears in the Andean small forest occurring on mosses in tree bark inhabiting mostly exposed habitats. Cyphellostereum is also represented by a high number of species restricted to the Neotropics [6 (66.6%)], while one is known only from North America, one from Southeastern United States and Puerto Rico, and another species is known only from Borneo and Fiji (Table 2). It is probably due to their unusual appearance that these lichens are getting confused with free-living cyanobacteria colonies, and that there are still undescribed species in the Neotropics.
Effects of habitat types on the dynamic changes of allocation in carbon and nitrogen storage of vegetation-soil system in sandy grasslands
<p>The progressive restoration of degraded vegetation in semiarid and arid desertified areas undoubtedly formed different habitat types. The most plants regulate their growth by fixing carbon with their energy deriving from photosynthesis, carbon (C) and nitrogen (N) play the crucial role in regulating plant growth, community structure and function in the vegetation restoration progress. However, it is still unclear how habitat types affect the dynamic changes of allocation in C and N storage of vegetation-soil system in sandy grasslands. Here, we investigated plant community characteristics and soil properties across three successional stages of habitat types: semi-fixed dunes (SFD), fixed dunes (FD) and grasslands (G) in 2011, 2013 and 2015. We also examined the C and N concentrations of vegetation-soil system, and estimated their C and N storage. The C and N storage of vegetation system, soil and vegetation-soil system remarkably increased from SFD to G. The litter C and N storage in SFD, N storage of vegetation system in SFD and N storage of soil and vegetation-soil system in FD increased from 2011 to 2015, while aboveground plant C and N storage of FD were higher in 2011 than in 2013 and 2015. Most of C and N were sequestered in soil in the vegetation restoration progress. These results suggest that the dynamic changes of allocation in C and N storage in vegetation-soil systems varied with habitat types. Our study highlights that SFD has higher N sequestration rate in vegetation, while FD has the considerably N sequestration rate in the soil.</p>
The type of leg lost affects habitat use but not survival in a non-regenerating arthropod
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Data from: Indirect effects of a large mammalian herbivore on small mammal populations: context-dependent variation across habitat types, mammal species and seasons
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Data from: Butterfly community ecology: the influences of habitat type, weather patterns, and dominant species in a temperate ecosystem
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Data from: Matrix type and landscape attributes modulate avian taxonomic and functional spillover across habitat boundaries in the Brazilian Atlantic Forest
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Effects of habitat types on the dynamic changes of allocation in carbon and nitrogen storage of vegetation-soil system in sandy grasslands
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Allen Brain Atlas
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