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Fig 2 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 2 Mean values (min-max and ±SE) of main parameters of orthopteran assemblages under different grazing pressure. Significant (p<0.05) differences detected by Mann-Whitney U test are indicated by different letters.

Fig 1 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 1 Location and land use-changes of the studied sites (G: grazed; G–A: grazing-abandoned; M–G: moderately grazed; U–G: ungrazed). Letters to the left of the arrow indicate land use in 2012 and 2013; letters to the right of the arrow indicate land use in 2014, 2015 and 2016.

Fig 1 from: Joubert-Van der Merwe L, Pryke JS (2018) Is cattle grazing more important than landscape heterogeneity for grasshoppers in Afromontane grassland? Journal of Orthoptera Research 27(1): 13-21. https://doi.org/10.3897/jor.27.15027

Fig 1 Map of study sites in the KwaZulu-Natal Midlands. Abbreviations for grazing intensity: light in iMpendle Nature Reserve (square symbols), and moderate (circular symbols) or heavy (triangular symbols) in the ecological network. Abbreviations for fire regime: annual burning (AB, solid black symbols), grasslands with longer fire rotation that were recently-burned (RB, solid grey symbols) i.e. burned < 12 months prior to sampling and unburned (UB, open symbols) i.e. burned >12 months prior to sampling.

Fig 2 from: Joubert-Van der Merwe L, Pryke JS (2018) Is cattle grazing more important than landscape heterogeneity for grasshoppers in Afromontane grassland? Journal of Orthoptera Research 27(1): 13-21. https://doi.org/10.3897/jor.27.15027

Fig 2 Grasshopper species richness responds to grazing intensity under different fire regimes. Pairwise comparisons among grazing intensity classes (light, moderate and heavy) for annually-burned firebreaks and grasslands with longer fire rotations that were recently-burned i.e. <12 months prior to sampling and unburned i.e. burned >12 months prior to sampling. Bars with the same letters are not significantly different from one another.

Figure 2 from: Aguirre MP, Ortego J, Cordero PJ (2018) Influence of grazing on populations of the specialist grasshopper Mioscirtus wagneri inhabiting hypersaline habitats in La Mancha Region, Central Spain. Journal of Orthoptera Research 27(1): 75-81. https://doi.org/10.3897/jor.27.21064

Figure 2 Alkali seepweed prairie (Suaeda vera) without grazing, typical habitat of Mioscirtus wagneri in the study area (Peña Hueca lagoon, Villacañas, Toledo province, Spain). Photo by P.J. Cordero.

Fig 5 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 5 Mean values (min-max and ±SE) of relative frequency of geophilic and vegetation structure-dependent species under different grazing pressure. Significant (p<0.05) differences detected by Mann-Whitney U test are indicated by different letters.

Fig 3 from: Selman RG, Cherrill AJ (2018) The lesser mottled grasshopper, Stenobothrus stigmaticus: lessons from habitat management at its only site in the British Isles. Journal of Orthoptera Research 27(1): 83-89. https://doi.org/10.3897/jor.27.15123

Fig 3 The impact of targeted grazing in January 2017 after clearance of gorse two years earlier, A. vegetation either side of fencing; B. hardy Welsh Mountain-Texel cross sheep grazing on-site.

Fig 4 from: Lightfoot DC (2018) The effects of livestock grazing and climate variation on vegetation and grasshopper communities in the northern Chihuahuan Desert. Journal of Orthoptera Research 27(1): 35-51. https://doi.org/10.3897/jor.27.19945

Fig 4 Examples of each grasshopper life-form type; A. Arbusticole; Bootettix argentatus on Larrea tridentata; B. Graminicole; Paropomala pallida on Bouteloua eriopoda; C. Terri-graminicole; Phlibostroma quadrimaculatum; D. Herbicole; Tropidolophus formosus on Spharalcea hastulata; E. Terricole; Trimerotropis pallidipennis.

Figure 5 from: Aguirre MP, Ortego J, Cordero PJ (2018) Influence of grazing on populations of the specialist grasshopper Mioscirtus wagneri inhabiting hypersaline habitats in La Mancha Region, Central Spain. Journal of Orthoptera Research 27(1): 75-81. https://doi.org/10.3897/jor.27.21064

Figure 5 Relationship between number of Mioscirtus wagneri per square meter (ABUNDANCE) and A. Cover (%) of Suaeda vera (SEEPWEED), and B. Livestock droppings per square meter (DROPPINGS). Open circles may correspond to one or more overlapping data points.

Fig 3 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 3 PCoA ordination (sum of all eigenvalues: 20.008, similarity index: correlation) based on Orthoptera data. The different years are marked by A, B, C, D and E (A: 2012, B: 2013, C: 2014, D: 2015 and E: 2016; e.g. 1-A: site 1 in 2012, 2-B: site 2 in 2013, C-C: control site in 2014).

Figure 6 from: Piry S, Berthier K, Streiff R, Cros-Arteil S, Foucart A, Tatin L, Bröder L, Hochkirch A, Chapuis M-P (2018) Fine-scale interactions between habitat quality and genetic variation suggest an impact of grazing on the critically endangered Crau Plain grasshopper (Pamphagidae: Prionotropis rhodanica). Journal of Orthoptera Research 27(1): 61-73. https://doi.org/10.3897/jor.27.15036

Figure 6 Maps of A. density of grasshopper in number of individuals per hectare, B. rescale NDVI values and C. mean genetic differentiation between individuals resulting from the MAPI analysis.

Fig 2 from: Selman RG, Cherrill AJ (2018) The lesser mottled grasshopper, Stenobothrus stigmaticus: lessons from habitat management at its only site in the British Isles. Journal of Orthoptera Research 27(1): 83-89. https://doi.org/10.3897/jor.27.15123

Fig 2 Aerial photograph of Langness, showing the area covered by the golf course (light green), the distribution of S. stigmaticus in August 1964 (vertical hatching), 1990 (horizontal hatching), and sites occupied from 2002 in the absence of grazing (dark green) and sites occupied from 2002 where grazing had been reintroduced (red) (based on mapping by Mr. J. F. Burton reported in RPS Clouston (1990), Cherrill (1990, 1994) and subsequent observations by the authors).

Figure 3 from: Piry S, Berthier K, Streiff R, Cros-Arteil S, Foucart A, Tatin L, Bröder L, Hochkirch A, Chapuis M-P (2018) Fine-scale interactions between habitat quality and genetic variation suggest an impact of grazing on the critically endangered Crau Plain grasshopper (Pamphagidae: Prionotropis rhodanica). Journal of Orthoptera Research 27(1): 61-73. https://doi.org/10.3897/jor.27.15036

Figure 3 Illustrations of the Coussoul habitat of Prionotropis rhodanica with A. sheep accompanied by cattle egrets and B. researchers surveying the species using a circle-based method.

Figure 1 from: Aguirre MP, Ortego J, Cordero PJ (2018) Influence of grazing on populations of the specialist grasshopper Mioscirtus wagneri inhabiting hypersaline habitats in La Mancha Region, Central Spain. Journal of Orthoptera Research 27(1): 75-81. https://doi.org/10.3897/jor.27.21064

Figure 1 Map of the study area (Villacañas, Toledo Province, Central Spain) showing the location of the hypersaline lagoons Tirez and Peña Hueca.

Figure 5 from: Piry S, Berthier K, Streiff R, Cros-Arteil S, Foucart A, Tatin L, Bröder L, Hochkirch A, Chapuis M-P (2018) Fine-scale interactions between habitat quality and genetic variation suggest an impact of grazing on the critically endangered Crau Plain grasshopper (Pamphagidae: Prionotropis rhodanica). Journal of Orthoptera Research 27(1): 61-73. https://doi.org/10.3897/jor.27.15036

Figure 5 Linear regression between genetic distance â and geographical distances computed between pairs of individuals. Variation in point density is represented by colors, from blue (low density) to red (high density).

Fig 3 from: Lightfoot DC (2018) The effects of livestock grazing and climate variation on vegetation and grasshopper communities in the northern Chihuahuan Desert. Journal of Orthoptera Research 27(1): 35-51. https://doi.org/10.3897/jor.27.19945

Fig 3 Cluster analysis dendrogram showing the similarities of plant species compositions at sites and grazed and not grazed transects within sites, from annual canopy cover/m2 averaged over all years and seasons; A. Spring; B. Fall.

Fig 7 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 7 CCA ordination based on Orthoptera data and environmental parameters (VCOV: total vegetation cover; BSOIL: percentage of bare soil; VH: height of the vegetation). Abbreviations of species names: Acr ins: Acrotylus insubricus; Acr ung: Acrida ungarica; Ail tha: Aiolopus thalassinus; Cal bar: Calliptamus barbarus; Cal ita: Calliptamus italicus; Cel var: Celes variabilis; Cho apr: Chorthippus apricarius; Cho big: Chorthippus biguttulus; Cho bru: Chorthippus brunneus; Cho mol: Chorthippus mollis; Doc bre: Dociostaurus brevicollis; Euc dec: Euchorthippus declivus; Euc pul: Euchorthippus pulvinatus; Gam gla: Gampsocleis glabra; Mon mon: Montana montana; Myr mac: Myrmeleotettix maculatus; Oed cae: Oedipoda caerulescens; Oed dec: Oedaleus decorus; Omo hae: Omocestus haemorrhoidalis; Omo min: Omocestus minutus; Omo pet: Omocestus petraeus; Omo ruf: Omocestus rufipes; Pla alb: Platycleis albopunctata; Sph cae: Sphingonotus caerulans; Ste fis: Stenobothrus fischeri; Ste lin: Stenobothrus lineatus; Ste nig: Stenobothrus nigromaculatus.

Figure 4 from: Aguirre MP, Ortego J, Cordero PJ (2018) Influence of grazing on populations of the specialist grasshopper Mioscirtus wagneri inhabiting hypersaline habitats in La Mancha Region, Central Spain. Journal of Orthoptera Research 27(1): 75-81. https://doi.org/10.3897/jor.27.21064

Figure 4 Relationship between probability of presence of Mioscirtus wagneri in the transects (PRESENCE) and A. Cover (%) of Suaeda vera (SEEPWEED) for extreme values of livestock droppings per square meter (DROPPINGS), and B. Livestock droppings per square meter (DROPPINGS) for extreme values of cover (%) of S. vera (SEEPWEED).

Fig 3 from: Joubert-Van der Merwe L, Pryke JS (2018) Is cattle grazing more important than landscape heterogeneity for grasshoppers in Afromontane grassland? Journal of Orthoptera Research 27(1): 13-21. https://doi.org/10.3897/jor.27.15027

Fig 3 Canonical analysis of principal coordinates ordination (CAP) of grasshopper assemblage composition to display patterns in the data. Abbreviations for grazing intensity: light in the protected area (square symbols), and moderate (circular symbols) or heavy (triangular symbols) in the ecological network. Abbreviations for fire regime: annual burning (AB, solid black symbols), grasslands with longer fire rotation that were recently-burned (RB, solid grey symbols) i.e. burned < 12 months prior to sampling and unburned (UB, open symbols) i.e. burned >12 months prior to sampling. Significance values for pairwise comparisons are in Table 4.

Fig 6 from: Kenyeres Z (2018) Effects of grazing on orthopteran assemblages of Central-European sand grasslands. Journal of Orthoptera Research 27(1): 23-33. https://doi.org/10.3897/jor.27.15033

Fig 6 Mean values (min-max and ±SE) of vegetation cover and vegetation height on the studied sites. Significant (p<0.05) differences detected by Mann-Whitney U test are indicated by different letters.