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FIGURE 19 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 19. Tetranychus lintearius Dufour, female. (a) Pretarsus I; (b) Diamond-shaped pattern in dorsal striae between e and f; (c) Pregenital striae. Male. (d) Pretarsus I; (e) Pretarsus II; (f) Aedeagus.
FIGURE 22 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 22. Tetranychus macfarlanei Baker & Pritchard, female. (a) Pretarsi II, III, IV; (b) Tarsus I; (c) Diamond-shaped pattern of dorsal striae between setae e and f; (d) Pregenital striae. Male. (e) Tarsus I; (f) Aedeagus.
FIGURE 18 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 18. Tetranychus lambi Pritchard & Baker, female. (a) Pretarsus IV; (b) Tarsi I, dorsal and ventral view, dashed line indicates level of proximal duplex setae; (c) Diamond-shaped pattern of dorsal striae between setae e and f; (d) Pregenital striae, with lobes. Male. (e) Empodium I; (f) Empodium III-IV; (g) Aedeagus.
FIGURE 17 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 17. Tetranychus kanzawai Kishida, female. (a) Pretarsi; (b) Tarsus I; (c) Diamond-shaped pattern of dorsal striae
FIGURE 16 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 16. Tetranychus gloveri Banks, female. (a) Pretarsus IV; (b) Tarsus I, dorsal and ventral view, dashed line indicates level of proximal duplex setae; (c) Diamond-shaped pattern of dorsal striae between setae e and f; (d) Ventral striae with lobes (e) Pregenital striae. Male. (f) Aedeagus; (g) Pretarsus I; (h) Pretarsus II.
FIGURE 31 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 31. Tetranychus truncatus Ehara, female, paratypes. (a) Tarsus I and pretarsus II and IV; (b) Diamond-shaped pattern of dorsal striae between setae e and f; (c) Pregenital striae. Male, holotype. (d) Pretarsi I-IV; (e) Aedeagus of two specimens
FIGURE 14 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 14. Tetranychus evansi Baker & Pritchard, female. (a) Tarsus I; (b) Pretarsi II and IV; (c) Diamond-shaped pattern of dorsal striae between setae e and f; (d) Pregenital striae. Male. (e) Pretarsi I, II and III-IV; (f) Pretarsi II, III, showing empodial spurs; (g) Aedeagus of two specimens at different focal points (1,2); (h) Aedeagus.
FIGURE 15 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 15. Tetranychus fijiensis Hirst, female, paratype. (a) Pretarsus I; (b) Peritreme; (c) Pregenital striae. Male, holotype. (d) Aedeagus, in sheath. Male and Female: (e) Pretarsi.
FIGURE 10 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 10. Tetranychus bunda Flechtmann & Knihinicki, female. (a) Tarsus and pretarsus I; (b) Diamond pattern of dorsal striae between setae e and f; (c) Pregenital striae. Male: (d) Aedeagus at four different focal points; (e) Pretarsus I; (f) Pretarsus II.
FIGURE 11 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 11. Tetranychus canadensis (McGregor), female. (a) Pretarsus I; (b) Tarsi I; (c) Pregenital striae; (d) Dorsal striae between setae e and f; (e) Hourglass pattern of dorsal striae between setae e and f. Male: (f) Pretarsus I, type specimen; (g) Pretarsus II, type specimen; (h) Aedeagus, type specimen; (i) Aedeagus.
FIGURE 7 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 7. The three main forms of dorsal striae between setae e1 and f1 in Tetranychus. Scale bars = 50 µm.
FIGURE 9 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 9. Lateral view of the aedeagus of Tetranychus spp., with posterior projections to the right hand side.
FIGURE 5 in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 5. Arrangement of dorsal setae in the Tetranychidae. A. Eutetranychus sp. male. B. Oligonychus sp. female. Tetranychus has the same dorsal chaetotaxy as Oligonychus (h1 absent). Scale bar = 100 µm.
FIGURE 1. Tarsus I in Identification of exotic pest and Australian native and naturalised species of Tetranychus (Acari: Tetranychidae)
FIGURE 1. Tarsus I of a female Tetranychus sp. Setal names are given for the proximal tactile setae and both pairs of duplex setae. Scale bar = 50 µm.
Figs. 1–5 in Nothing is Perfect: Biodegradable Packing Material as Food and Transportation for a Museum Pest,Lasioderma serricorne(F.) (Coleoptera: Anobiidae)
Figs. 1–5. Lasioderma serricorne in starch-based packing peanuts. 1) Adults (2.4 mm long); 2) Two teneral adults in a whole peanut (a) and just below the peanut surface (b); 3) Eggs (0.17 mm long); 4) Pupa dissected from a peanut; 5) Teneral adult and its larval exuviae dissected from a peanut.
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest. in Suidae
Subspecies and Distribution. S. s. scrofa Linnaeus, 1758 — W Europe, from Denmark, Germany, Poland, and Czech Republic to N Italy and N Iberian Peninsula; possibly also Albania. The taxonomic status of animals in Austria, Switzerland, Slovenia, and Slovakia is unclear but presumably these populations are included in scrofa, as are the populations of Sweden, Finland, and the Baltic states. However, restocking of once depleted populations, for example in Italy, has likely involved the introduction and mixing of this subspecies with other subspecies, such as attila. S. s. affinis Gray, 1847 — S India and Sri Lanka. S. s. algirus Loche, 1867 — Tunisia, Algeria, and Morocco, on the coastal side of the mountains or in the low montane areas. S. s. attila Thomas, 1912 — Hungary, Ukraine, C & S Belarus, Romania, Moldova, and S Russia towards the N flank of the Caucasus, but not including the Transcaucasian countries of Georgia, Armenia, and Azerbaijan. The range possibly extends as far S as the Mesopotamian Delta in Iraq, in which case it would likely include W & SW Iran, and possibly E Turkey and Syria, where it borders with lybicus. Such a range could not be easily reconciled with a statement by Groves that "the difference between pigs from N and S of the Caucasus is quite striking; Transcaucasian boars are certainly not attila." This subspecies may also extend into C Asia and include Kazakhstan, Uzbekistan, and Turkmenistan, but no data exist to support this. S. s. baeticus Thomas, 1912 — originally described from Coto Donana, S Spain, and later merged with meridionalis; also S Portugal. Unless evidence is found that these Italian and Iberian populations are the relics of a much larger formerly contiguous range, this subspecies should be kept as distinct. S. s. coreanus Heude, 1897 — Korean Peninsula. S. s. eristatus Wagner, 1839 — Himalayas S to C India and E to Indochina (N of the Kra Isthmus). S. s. davidi Groves, 1981 — the arid zone from E Iran to Gujarat, including Pakistan and NW India, and perhaps N to Tajikistan. S. s. leucomystax Temminck, 1842 — main Is ofJapan (Honshu, Shikoku, Kyushu, Nakadori, Hiburijima, Tojima, Kushima, and other smaller Is). S. s. lybicus Gray, 1868 — Bulgaria, Greece, Turkey, Syria, Jordan, Israel, Palestine, in the past also in Lybia, and Egypt. The former Yugoslavia was included in its range, which would suggest that now Slovenia, Serbia, Croatia, Bosnia and Herzegovina, Montenegro, and Kosovo are within the range of this subspecies, although the exact boundaries are unclear. Pigs from Albania have been assigned to S. s. scrofa. S. s. majori De Beaux & Festa, 1927 — C & S Italian Peninsula. S. s. menidionalis Forsyth Major, 1882 — Corsica and Sardinia, with the proviso that the two populations are very likely to be introduced or feral. S. s. moupinensis Milne-Edwards, 1871 — China, S to Vietnam and W to Sichuan. S. s. nigripes Blanford, 1875 — the flanks of the Tianshan mountains in Kyrgyzstan and NW China (Xinjiang). An animal photographed in NE Iran (Golestan) looked like this subspecies. S. s. nukiuanus Kuroda, 1924 — Iriomote, Ishigaki, Okinawa, Tokunoshima, Amamioshima, and Kakerome Is in the Ryukyu chain in extreme S Japan, though some of these populations have hybridized with introduced domesticates. S. s. sibiricus Staffe, 1922 — Mongolia and Transbaikal (S & E of Lake Baikal). S. s. tawvanus Swinhoe, 1863 — Taiwan. S. s. ussuricus Heude, 1888 — far E Russia and the Manchurian region (China). Korean populations were previously included in this subspecies, but based on new evidence, the Korean taxon seems more similar to moupinensis. S. s. vittatus Boie, 1828 — Malay Peninsula, S of the Isthmus of Kra, the offshore islands of Terutai and Langkawi, Sumatra, Riau Archipelago, Java, Bali, and a range of smaller islands around these, including Babi, Bakong, Batam, Bawean, Bengkalis, Bintan, Bulan, Bunguran, Cuyo, Deli, Durian, Enggano, Galang, Jambongan, Karimon (Riau Is), Kundur, Lagong, Laut, Lingga, Lingung, Mapor, Moro Kecil, North Pagai, Nias, Panaitan, Payong, Penang, Pinie, Rupat, Siantan, Siberut, Simeulue, Singkep, Sugi, Sugi Bawa, Telibon, Tinggi, Tuangku, and the Tambelan Is. This species was originally present from the British Is in the extreme W, through Eurasia from S Scandinavia to S Siberia, extending as far E as Korea and Japan, and SE into some of the Sunda Is and Taiwan. In the S the species ranged along the Nile Valley to Khartoum, and N of the Sahara in Africa, more orless following the continental coasts of S, E, and SE Asia. Within this range it was absent only from extremely dry deserts, e.g. the driest regions of Mongolia and in China W of Sichuan; and alpine zones, such as the high altitudes of Pamir and Tien Shan. In recent centuries, the range of S. scrofa has changed dramatically because of hunting and changes in available habitat. The species disappeared from the British Is in the 17" century, from Denmark in the 19" century, and was greatly reduced in range and numbers in the 20" century from areas as distant as Tunisia, Sudan, Germany, and Russia. Following these severe declines, there were some slight population recoveries in Russia, Italy, Spain, and Germany in the mid-20™ century, and natural and assisted range expansions in Denmark and Sweden. The species has also been inadvertently reintroduced in various locations in the Great Britain via escapees of mixed origin from commercial farming enterprises. Ex-S. scrofa stocks also occur as introduced feral populations in various other parts of the world, including Australia, New Zealand, the eastern Malay Archipelago, and in North, Central, and South America. In all of these areas they are now generally recognized as a major pest.
Introduced plants induce outbreaks of a native pest and facilitate invasion in the plants' native range: Evidence from the emerald ash borer
<p>1. Biological invasions are among the most serious threats to native forest ecosystems worldwide due to ever-increasing international trade and global change. Understanding the invasion processes and ecology of invasive pests in both newly invaded and native habitats is necessary to effectively manage the risks they pose. 2. The emerald ash borer (EAB), Agrilus planipennis, is one of the most devastating invasive forest insect pests in North America and has also invaded European Russia and parts of Europe. Through synthesizing historical data spanning >100 years and contemporary field observations in China, we examined EAB's distribution, occurrence, and outbreak frequency in its native range in relation to historical introductions and plantings of non-Asian ash trees in China. 3. The frequencies and levels of EAB infestations in China gradually increased from 1900 to 2021 after a time-lag of 30-50 years following introductions and widespread plantings of non-Asian ash trees from North America. Increased frequencies of EAB outbreaks following the planting of North American ash trees in China may have increased the risk of EAB invading North America and other novel regions. 4. Synthesis. Our findings demonstrated that planting susceptible non-native host plants can induce outbreaks of a native insect pest in its native range, which in turn may enhance risks of invading novel regions via human-assisted activities (e.g., international trade). In addition, our findings suggest that lag-times of several decades between planting susceptible hosts and initial pest outbreaks may pose challenges in predicting the true risk of invading novel regions. Consequently, comprehensive risk assessment for invasive insect pests should consider the role of non-native plants introduced or planted in the pest's native range.</p>
Supplementary material 1 from: Zembrzuski D, Woller DA, Jech L, Black LR, Reuter KC, Overson R, Cease A (2021) Establishing the nutritional landscape and macronutrient preferences of a major United States rangeland pest, Melanoplus sanguinipes, in field and lab populations. Journal of Orthoptera Research 30(2): 163-172. https://doi.org/10.3897/jor.30.61605
Supplementary material 1 from: Zembrzuski D, Woller DA, Jech L, Black LR, Reuter KC, Overson R, Cease A (2021) Establishing the nutritional landscape and macronutrient preferences of a major United States rangeland pest, Melanoplus sanguinipes, in field and lab populations. Journal of Orthoptera Research 30(2): 163-172. https://doi.org/10.3897/jor.30.61605
Changes in arthropod communities mediate the effects of landscape composition and farm management on pest control ecosystem services in organically managed strawberry crops
<p>Landscape composition and local diversification practices such as polyculture, cover cropping, and hedgerows may promote natural pest control by benefiting natural enemy communities on farms. Our study employs piecewise structural equation modeling (PSEM) to test causal hypotheses regarding the effects of landscape composition and local diversification practices on arthropod communities and pest control ecosystem services.</p> <p>We sampled 27 organic strawberry fields in California's Central Coast region in 2015 and 2016 (17 repeated between years) for a total of 37 distinct sites across years. The sites were selected along orthogonal gradients of landscape composition and local diversification practices. We also investigated the effects of two common pest management practices. At each site, we sampled arthropod communities using a hand-held vacuum and performed sentinel prey experiments using the pest species <em>Lygus hesperus</em> to estimate pest control levels.</p> <p>At the landscape scale, proportion woods increased natural enemy abundance; at the local scale, diversification practices increased natural enemy diversity.</p> <p>Insecticides and tractor vacuuming, aimed at controlling pests, were indirectly detrimental to pest control services. Both practices decreased natural enemy abundance, and while insecticides also decreased pest abundance, vacuuming did not.</p> <p>Natural enemy abundance and diversity increased pest control levels, while pest abundance had the opposite effect. The PSEM results confirmed our hypotheses that landscape and local effects on pest control are mediated through changes in arthropod communities.</p> <p><em><a>Synthesis </a>and applications</em>: At the landscape scale, higher proportions of woody habitat are associated with greater natural enemy abundance, which increases pest control levels. When promoting pest control ecosystem services is a policy goal, regional planners should prioritize the conservation and restoration of woodlands in agricultural landscapes. At the local scale, decisions of individual growers can impact pest control services. For many growers, adopting practices that promote on-farm plant diversity may be a feasible solution for increasing pest control levels while avoiding the environmental and economic costs imposed by insecticide application and tractor <a>vacuuming. </a></p> <div> <div> <div class="msocomtxt"> <p class="MsoCommentText"> </p> </div> </div> </div>
Data from: Effective specialist or jack of all trades? Experimental evolution of a crop pest in fluctuating and stable environments
<p>Understanding pest evolution in agricultural systems is crucial for developing effective and innovative pest control strategies. Types of cultivation, such as crop monocultures versus polycultures or crop rotation, may act as a selective pressure on pests' capability to exploit the host's resources. In this study, we examined the herbivorous mite <em>Aceria tosichella</em> (commonly known as wheat curl mite), a widespread wheat pest, to understand how fluctuating versus stable environments influence its niche breadth and ability to utilize different host plant species. We subjected a wheat-bred mite population to replicated experimental evolution in a single-host environment (either wheat or barley), or in an alternation between these two plant species every three mite generations. Next, we tested the fitness of these evolving populations on wheat, barley, and on two other plant species not encountered during experimental evolution, namely rye and smooth brome. Our results revealed that the niche breadth of <em>A. tosichella</em> evolved in response to the level of environmental variability. The fluctuating environment expanded the niche breadth by increasing the mite's ability to utilize different plant species, including novel ones. Such an environment may thus promote flexible host-use generalist phenotypes. However, the niche expansion resulted in some costs expressed as reduced performances on both wheat and barley as compared to specialists. Stable host environments led to specialized phenotypes. The population that evolved in a constant environment consisting of barley increased its fitness on barley without the cost of utilizing wheat. However, the population evolving on wheat did not significantly increase its fitness on wheat, but decreased its performance on barley. Altogether, our results indicated that, depending on the degree of environmental heterogeneity, agricultural systems create different conditions that influence pests' niche breadth evolution, which may in turn affect the ability of pests to persist in such systems.</p>
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Allen Brain Atlas
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Annotated Behaviour and Observability Dataset (ABODe)
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