Managing coextinction of insects in a changing climate

AbstractApproximately a quarter of global terrestrial biodiversity is represented by plant dwelling insects and the potential for thousands of species to be extinguished through widespread disturbances such as a changing climate is high. From a large database of 1,019 insect species on 104 plant species, we identified that 70 species were of immediate conservation concern due to their reliance on threatened plant species. A further 15 insect species were of lesser conservation concern because they rely on several threatened plant species for survival. Of those insects that feed from non-threatened plant species, 178 host-specific species are likely to be at risk in the event that climate change or synergistic factors reduces their host plant’s range size. Insect groups that appear most prone to extinction are sessile feeders and highly host specific groups such as whiteflies, scales, mealybugs. Many weevils are also host specific and at higher risk, possibly as they are dispersal inhibited, such as through brachyptery. More surprisingly, mobile plant louse groups (Psylloidea) were also at high risk. Endophagous insects are predicted to be at high risk, but were under-studied here.Regions such as gullies and mountains provide refugia for some species. The fluctuations in temperature (less within refugia), and average humidity (higher in refugia) appear particularly important in these habitats. Particular vegetation types are associated with refugial regions, with a recognised Threatened Ecological Community (TEC) of flora species associated with the highest peaks of the Eastern Mastif, and there is evidence of insect species restricted to these peaks. For the majority of plant species that are not restricted to certain areas, their insect assemblages differ significantly between plant populations, particularly across different mountains.With the assistance of end-users, we have developed an adaptation management framework. The framework assists with conserving plant-dwelling insect species, after they are identified as in need of conservation action. Whilst the primary reason for the development of the framework was to provide adaptation actions in the face of climate change, the framework can be used when insects require conservation action to ameliorate impacts of other threatening processes. Previously published frameworks can be utilized to determine whether an insect is threatened with extinction. Despite the availability of such tools, a survey of end-users still indicted that lack of expertise is the most important factor inhibiting considering plant-dwelling insects.Land managers currently struggle to determine which insect species inhabit their lands, let alone knowing which are in need of conservation. To assist land managers with these problems, we suggest the employment of dedicated conservation entomologists by the Federal and State governments. Their role would be to bridge the interface between taxonomists, government conservation bodies, land managers and disturbance ecologists. The conservation entomologist’s principle tasks would be to identify insects most at risk of extinction, nominate them for listing, and develop management plans to ensure their survival

Native and non-native sources of carbohydrate correlate with abundance of an invasive ant

Invasive species threaten many ecological communities and predicting which communities and sites are invasible remains a key goal of invasion ecology. Although invasive ants often reach high abundances in association with plant-based carbohydrate resources, the source and provenance of these resources are rarely investigated. We characterized carbohydrate resources across ten sites with a range of yellow crazy ant abundance in Arnhem Land, Australia and New Caledonia to determine whether yellow crazy ant (Anoplolepis gracilipes) abundance and trophic position correlate with carbohydrate availability, as well as the relative importance of native and non-native sources of carbohydrates to ant diet. In both locations, measures of yellow crazy ant abundance strongly positively correlated with carbohydrate availability, particularly honeydew production, the number of tended hemipterans, and the number of plants with tended hemipterans. In Arnhem Land, 99.6% of honeydew came from native species, whereas in New Caledonia, only 0.2% of honeydew was produced by a native hemipteran. More honeydew was available in Australia due to three common large-bodied species of Auchenorrhyncha honeydew producers (treehoppers and leafhoppers). Yellow crazy ant trophic position declined with increasing yellow crazy ant abundance indicating that in greater densities the ants are obtaining more of their diet from plant-derived resources, including honeydew and extrafloral nectar. The relationships between yellow crazy ant abundance and carbohydrate availability could not be explained by any of the key environmental variables we measured at our study sites. Our results demonstrate that the positive correlation between yellow crazy ant abundance and honeydew production is not contingent upon the provenance of the hemipterans. Native sources of carbohydrate may play an underappreciated role in greatly increasing community invasibility by ants

Indigenous plants promote insect biodiversity in urban greenspaces

The contribution of urban greenspaces to support biodiversity and provide benefits for people is increasingly recognized. However, ongoing management practices favor vegetation oversimplification, often limiting greenspaces to lawns and tree canopy rather than multi-layered vegetation that includes under- and midstorey, and the use of nonnative species. These practices hinder the potential of greenspaces to sustain indigenous biodiversity, particularly for taxa like insects that rely on plants for food and habitat. Yet, little is known about which plant species may maximize positive outcomes for taxonomically and functionally diverse insect communities in greenspaces. Additionally, while cities are expected to experience high rates of introductions, quantitative assessments of the relative occupancy of indigenous vs. introduced insect species in greenspace are rare, hindering understanding of how management may promote indigenous biodiversity while limiting the establishment of introduced insects. Using a hierarchically replicated study design across 15 public parks, we recorded occurrence data from 552 insect species on 133 plant species, differing in planting design element (lawn, midstorey, and tree canopy), midstorey growth form (forbs, lilioids, graminoids, and shrubs) and origin (nonnative, native, and indigenous), to assess (1) the relative contributions of indigenous and introduced insect species and (2) which plant species sustained the highest number of indigenous insects. We found that the insect community was overwhelmingly composed of indigenous rather than introduced species. Our findings further highlight the core role of multi-layered vegetation in sustaining high insect biodiversity in urban areas, with indigenous midstorey and canopy representing key elements to maintain rich and functionally diverse indigenous insect communities. Intriguingly, graminoids supported the highest indigenous insect richness across all studied growth forms by plant origin groups. Our work highlights the opportunity presented by indigenous understory and midstorey plants, particularly indigenous graminoids, in our study area to promote indigenous insect biodiversity in urban greenspaces. Our study provides a blueprint and stimulus for architects, engineers, developers, designers, and planners to incorporate into their practice plant species palettes that foster a larger presence of indigenous over regionally native or nonnative plant species, while incorporating a broader mixture of midstorey growth forms

National tomato potato psyllid and zebra chip surveillance

Tomato potato psyllid (TPP), Bactericera cockerelli, is one of the world’s most destructive horticultural pests. This is because the psyllid acts as a vector for the bacterium Candidatus Liberibacter solanacearum (CLso) which causes Zebra chip disease and psyllid yellows in Solanaceous plants. In 2017 TPP was detected in Western Australia, after establishing in Norfolk Island in 2015, and New Zealand in 2006. The objectives of this project were to determine the status of TPP and CLso across Australia (WA, SA, Tas., Vic., NSW, Qld and NT) in a standardised manner for the horticulture industry. Surveillance occurred over a 3-year period (2019-2022), and targeted under-surveyed regions which were most likely to be the entry and establishment points for TPP; major metropolitan areas. An ‘Adopt-a-trap’ design was utilized to target metropolitan and outer metropolitan gardens throughout capital cities in most states, and regional centres in Western Australia where TPP occurrence in Perth is known. Monitoring for other exotic psyllids, in particular, the Asian citrus psyllid (Diaphorina citri) also occurred during the project. The project distributed 16,885 sticky traps nationwide, and 80.4% (13,590) were returned and assessed for exotic Psylloidea. Outside of Western Australia, no TPP, CLso or other priority exotic psyllid was positively detected. The project did find that TPP had dispersed to the regional areas of Albany, Geraldton and Carnarvon from the Perth metropolitan region in Western Australia, however, no CLso or other exotic psyllid was detected within the state. The project has resulted in a network of expert psyllid entomologists across Australia with reference material of Tomato potato psyllid and Asian citrus psyllid in all major State and Territory biosecurity collections

Revision of the lacebug tribe Ceratocaderini (Hemiptera: Tingidae)

The lacebug tribe Ceratocaderini (Tingidae: Cantacaderinae) is reviewed. The tribe comprises five genera from the Southern Hemisphere: Allocader Drake, Australocader Lis, Caledoderus Guilbert, Ceratocader Drake, and Coolacader gen. nov. The tribe is restricted to the Australian and New Caledonian regions. This revision includes the description of a new genus, Coolacader gen. nov. and six new species from three other genera: Australocader porchi sp. nov., Ceratocader piae sp. nov., Ceratocader spiculas sp. nov., Coolacader cupido sp. nov., Coolacader kardia sp. nov. and Coolacader valentine sp. nov. The nymph of Ceratocader is detailed for the first time, and the nymphs of three species of Coolacader gen. nov. are described. Allocader cordatus (Hacker, 1927) is transferred to Coolacader gen. nov., resulting in a new combination Coolacader cordatus (Hacker, 1927) comb. nov., and Allocader nesiotes Drake & Ruhoff, 1962 is transferred to the genus Caledoderus, resulting in a new combination Caledoderus nesiotes (Drake & Ruhoff, 1962) comb. nov.. This work increases the number of species in the tribe from 13 to 19. A revised key to the genera and species of the Ceratocaderini is provided

Anabunda retortinervis Emeljanov

<i>Anabunda retortinervis</i> Emeljanov <p>(Figs 2 a, 3a, 4a–e)</p> <p> <i>Anabunda retortinervis</i> Emeljanov, 2005:33, fig 13.</p> <p> <b>Material examined: Holotype:</b> 1ɗ, Coffs Harbour, NSW, 15.x.1958 (T.G. Campbell) (ANIC).</p> <p> <b>Paratypes:</b> 1Ψ, 10km SSE of Yeppoon, Qld, 21.x.1975 (I.F.B. Common) (ANIC).</p> <p> <b>Other material examined: Australia — QUEENSLAND:</b> 3ɗ, Southport, 22.ix.1929 (J.A. Bock) (UQIC); 2ɗ, E Lake Bowarrady, Fraser Island, 2–3.xii.1975 (A. Slater, G. Thompson) (QM); 2ɗ, Mt Tamborine,. xi.1918 (Froggatt collection) (ANIC); 1ɗ, Brisbane, 3.x.1936 (A.J.S.) (UQIC); 1ɗ, Murralah, Mt Emlyn, SSE Millmerran, at light, 22.xi.1992 (T.A. Lambkin) (QM); 1ɗ, Yidney rocks, Fraser Island, 4–5.xii.1975 (A. Slater, G. Thompson) (QM); 1ɗ, 0.5km SW AB Lake, Fraser Island, at light, 17.xii.1979 (K. Lambkin) (QM); 1ɗ, St Bernards, Mt Tamborine, light trap, 31.i.1961 (C.W. Frazier) (ASCU); 1ɗ, Mt Gravatt, 26.ix.1964 (A Terauds) (UQIC); 1ɗ, S Maryborough, nr Teddington Weir, 27.39S 152.43E, 5.ix.1987 (G. & A. Daniels) (UQIC); 1ɗ, Planted Creek, nr Tansey, 12.xii.1976 (G.B. & S.R. Monteith) (UQIC); 1ɗ, Redland Bay, 11.ix.1954 (G. Hooper) (UQIC); 1ɗ, Brisbane, 17.viii.1955 (F.A. Perkins) (UQIC); 3ɗ, 1Ψ, Camp Milo, Cooloola, 15–18.x.1978 (G.B. Monteith) (QM); 1ɗ, 1Ψ, Stanthorpe, 23.x.1927 (E. Sutton) (QDPI); 1Ψ, Stradbroke Island, 26.ix.1906 (Froggatt collection) (ANIC); 1Ψ, (Froggatt collection) (ANIC); 1Ψ, Brisbane, 23.x.1969 (PRB) (WINC); 1Ψ, Gatton,. iii.1954 (C. Flynn) (QM); 1Ψ, Burleigh Heads, 16.i.1973 (A. Burrows) (QM); 1Ψ, Booloumba Creek, State Forest Park, at light, 28–29.x.1988 (K.J. Lambkin) (QM); 1Ψ, Cobbs Hill, 26.02S 151.54E, pitfall & intercept traps, 19.xii.1992 –. iii.1993 (S. Hamlet) (QM); 1Ψ, vine scrub, 200m, Perry's Knob, 27.36S 152.36E, intercept trap, 15.ix.–11.xi.1998 (Monteith, Cook, Thompson) (QM); 1Ψ, Site 1, Mt Deongwar, 460m, 27.14S 152.15E, pyrethrum of trees, 14.x.1998 (P. Bouchard) (QM); 1Ψ, ex pine trees (QDPI); 1Ψ, ex banana leaf, Kandango, 22.xi.1925 (J.L.F.) (QDPI); 1Ψ, Peel Island, x.1925 (QDPI); 1Ψ, Taringa, xi.1933 (J.G. Brooks) (AM); 1Ψ, Glen Aplin, 26.x.1963 (P. Kerridge) (UQIC); 1Ψ, Noosa Heads, viii.1959 (J. Bryan) (UQIC); 1Ψ, Brisbane, 20.xi.1956 (J. Martin) (UQIC); 1Ψ, Brisbane, 18.ix.1964 (Y. Williams) (UQIC); 1Ψ, Stanthorpe, 21.ix.1930 (E. Sutton) (UQIC); 1 unknown (missing abdomen), Burleigh,. iv.1942 (Mae Smales) (ANIC) labelled as a paratype but was not included in Emeljanov (2005). <b>NEW SOUTH WALES:</b> 1ɗ, Rydalmere nr Sydney, light trap, 23.ii.1988 (G.J. Goodyer) (ASCU); 10ɗ, 1Ψ, Eastwood nr Sydney, light trap, 29.x.1991 (M.J. Fletcher) (ASCU); 1Ψ, Gilgandra, 3.xi.1973 (L.P. Kelsey) (ANIC); 1Ψ, Ulong East, Dorrigo, (W. Heron) (AM); 1Ψ, Pearl Beach, Woy Woy, 10.xii.1988 (G.R. Brown, M.A. Terras) (ASCU).</p> <p> <b>Description:</b> <i>Colour.</i> Vertex predominantly green except for three red marks on anterior margin, which may be faded in older specimens. Frons, pronotum, and mesonotum green (Fig. 2 a). Eyes black fading to brown in older specimens. Legs green with reddish colouration at posterior section of femur and anterior section of tibia. Spines on legs black. Forewings green, hindwings smoky white.</p> <p> <i>Body length.</i> ɗ 8.3–9.6 mm, Ψ 9.1–10.9 mm</p> <p> <i>Head.</i> Vertex projecting beyond eyes about two-thirds eye length. Pronotum extending to level with anterior margin of eyes, hind margin rounded. Frons widest at frontoclypeal suture, dorsal edge approximately two-thirds width of widest point. Frontoclypeal suture distinct.</p> <p> <i>Thorax.</i> Forewings with 19–20 apical cells and one to two rows of subapical cells.</p> <p>Ve i n C u A 2 strongly curved. Apical spines of hind tibia in two rows, 2nd row with 4–5 spines positioned between 7 spines of 1st row (Fig. 3 a).</p> <p> <i>Male genitalia.</i> First segment of anal tube widening along length, bearing two small flanges at posterior margin (Figs 4 d, e). Medioventral process of pygofer square (Fig. 4 b). Parameres with ventral surface smooth (Fig. 4 b), dorsal surface twisted, lined with 1 large and 4 small spines along outer margin (Fig. 4 a). Aedeagal appendages slightly broadened at midlength, each with 1 apical spine (Figs 4 a, c). Dorsal lobe of phallobase reduced to 2 small spines (Fig. 4 a). Lateral lobes greatly reduced.</p> <p> <b>Remarks:</b> Unlike other described species of the genus, <i>A. retortinervis</i> lacks dark markings on the forewings. The material examined has extended the known distribution of this species east to Fraser and Stradbroke Islands (Qld), south to Sydney (NSW), and west to Gilgandra (NSW) (Fig. 1)</p>Published as part of <i>Moir, Melinda L. & Fletcher, Murray J., 2006, Two new species of Anabunda Emeljanov (Hemiptera: Fulgoromorpha: Achilidae) from Australia, pp. 39-50 in Zootaxa 1328</i> on pages 42-45, DOI: <a href="http://zenodo.org/record/174150">10.5281/zenodo.174150</a&gt

CRYPTOBARSAC RUBRIOPS, A NEW GENUS AND SPECIES OF SELIZINE FLATIDAE (HEMIPTERA FULGOROMORPHA) FROM GRASSTREES (XANTHORRHOEA PREISSII) IN SOUTH WESTERN AUSTRALIA

Volume: 21Start Page: 221End Page: 22

Toward an optimal sampling protocol for Hemiptera on understorey plants

There are no standardised sampling protocols for inventorying Hemiptera from understorey or canopy plants. This paper proposes an optimal protocol for the understorey, after evaluating the efficiency of seven methods to maximise the richness of Hemiptera collected from plants with minimal field and laboratory time. The methods evaluated were beating, chemical knockdown, sweeping, branch clipping, hand collecting, vacuum sampling and sticky trapping. These techniques were tested at two spatial scales: 1 ha sites and individual plants. In addition, because efficiency may differ with vegetation structure, sampling of sites was conducted in three disparate understorey habitats, and sampling of individual plants was conducted across 33 plant species. No single method sampled the majority of hemipteran species in the understorey. Chemical knockdown, vacuum sampling and beating yielded speciose samples (61, 61 and 30 species, respectively, representing 53, 53 and 26% of total species collected)