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    Unveiling the unknown phylogenetic position of the scallop Austrochlamys natans and its implications for marine stewardship in the Magallanes Province

    This is the first comparative study of commercial scallop species in the Pacific coast of the MP combining morphological and molecular characters. Our phylogenetic analyses highlight the association between A. natans and Ad. colbecki; two members of monospecific tribes and last extant representatives of their Southern Ocean-restricted genera.These results confirm the presence of both Magallanes scallops in the MP, as well as the so-far unsuspected presence of mixed “banks” where both species occur in sympatry. The BND/VH ratio helps discriminate between two distinct entities that belong to the genetic lineage of Z. patagonica and to a different lineage, highly divergent from the former, which corresponds to A. natans. A. natans is the only species of a whole lineage with a particular phylogenetic value, therefore having developed and tested an accurate identification criterion for both scallops will allow efficient fishery management in the future.Here we discuss the phylogenetic position and the taxonomic status of both Magallanes scallops, as well as the implications of these results for the future management and conservation of Z. patagonica and A. natans in the Magallanes Region. Despite the numerous classifications built on morphological, ecological or molecular data, the relationships among pectinids are still under constant modification depending on the number of taxa, loci, length of the sequence and the selected outgroups1,4. The work of Alejandrino et al.7 is the most inclusive so far in terms of taxon sampling, with 81 species. Although Scherrat et al.25 included 143 species, the node supports of the phylogenetic trees are not provided, making it difficult to assess the robustness of this large phylogeny. In order to define the phylogenetic position of Zygochlamys patagonica and Austrochlamys natans, we included 93 pectinid taxa (43 genera) representative of tribes Chlamydini, Crassadomini, Fortipectini, Palliolini, Aequipectinini, Pectinini and Amussini. Comparing to Waller’s5 and Dijkstra’s15 classifications, only the subfamily Camptonectinae and the tribe Mesoplepini are missing. We used three ribosomal regions (one nuclear and two mitochondrial). Compared to Alejandrino et al.7, histone H3 is missing here, however this locus is among the least informative4. The family Pectinidae appears to be monophyletic with high support values (Fig. 5, S2), as previously demonstrated4,7,26,27,28. According to Dijkstra15 there are currently five subfamilies of Pectinidae, two of which are absent from our analysis: Camptonectinae and Pedinae. This topology supports the classifications of Waller5 and Dijkstra15, except for the position of the tribe Austrochlamydini.Our Magallanes scallops separated into two very divergent clades: Z. patagonica is associated with its conspecifics and congenerics in a single lineage (Fig. 5), which also contains species of Veprichlamys and Talochlamys. This lineage already appeared well supported as the sister clade to Palliolinae and Pectininae in Alejandrino7. For the first time, Talochlamys dichroa and T. gemmulata are nested with high support values into the Zygochlamys clade, making this latter genus paraphyletic (Fig. 5). These taxa are all restricted to high latitudes of the Southern Ocean. Due to phylogenetic and geographic affinities, we suggest that these three genera may constitute a tribe separate from Chlamydini. Since Dijkstra15 moved the two Atlantic ‘Crassadoma’ into the genus Talochlamys, the affinities among Talochlamys spp. had not been explored until now. Talochlamys species rather associate according to geographic affinities, splitting the genus into two highly divergent entities corresponding to European and New Zealand Talochlamys. A systematic revision of these four species would be useful.Austrochlamys natans associated with the Palliolinae, which was elevated to a subfamily rank by Waller5. Of the three extant tribes that compose this group, Mesopleplini are missing from our phylogenetic analyses. We included 4 genera (8 species) of the remaining two tribes: Adamussium (Adamussini) and Palliolum, Pseudamussium, Placopecten (Palliolini). The present sampling of Palliolini is the most inclusive to date and led to the monophyly and full support of the tribe Palliolini. Our phylogenetic results do not support any of the previous classifications of the tribe Austrochlamydini1,5,9,13,15, and introduce this monospecific tribe as a new member of the subfamily Palliolinae. Indeed, Austrochlamys natans clusters together with Adamussium colbecki, both in a sister clade to Palliolini. The first molecular characterization of Ad. colbecki did not lead to a clear classification due to the low polymorphism of the 18S26. Later, Ad. colbecki appears either as sister species to Chlamydinae or to Palliolini, depending on tribe sampling and the choice of outgroup and loci4,10,11. However, in the most recent and inclusive studies of taxon sampling7 (present study) or genomic cover29, Ad. colbecki is the sister group of the tribe Palliolini, as in the present phylogeny.The subfamily Palliolinae originated from a Chlamydinine ancestor in the Cretaceous and subsequently underwent diversification in the Northern Hemisphere1 and in the Southern Hemisphere, where the extinct genus Lentipecten spread in the Paleocene–Eocene Thermal Maximum30. The genus Adamussium derived from Lentipecten and appeared in the early Oligocene; it comprises 5 endemic Antarctic species; Ad. colbecki is the only one extant13,31,32. The genus Austrochlamys also appeared in the Oligocene and was first restricted to King George Island (South Shetlands), then spread around the north of the Antarctic Peninsula and achieved a circum-Antarctic distribution until the Pliocene13,33,34. Austrochlamys persisted during the progressive cooling of the Antarctic Continent from the Paleocene to the Pliocene, dominating the coastal areas, while Adamussium occupied the deep seas and continental platform33. The opening and deepening of the Drake Passage and the intensification of the Antarctic Circumpolar Current during the Pliocene provoked a drastic cooling and the extension of sea ice over the coastal habitat, which caused the northward movement of Austrochlamys and its subsequent disappearance from Antarctica, along with the circumpolar expansion of Ad. colbecki in Antarctic shallow waters33. The colonization of the coastal habitat has been related to the sea ice extent that provided a more stable environment and low-energy fine-grained sediment with which Adamussium was associated in the deep waters. Austrochlamys fossils appear in the Subantarctic Heard Island in late Pliocene layers (3.62–2.5 Ma35). Today Ad. colbecki is a circum-Antarctic and eurybathic species that reaches high local density in protected locations13,36, while all Austrochlamys became extinct except for A. natans, which is restricted to southern South America33. The phylogenetic affinity highlighted here between A. natans and Ad. colbecki has its origins in the Southern Ocean; the deep divergence between the lineages of these monospecific tribes attests to the long time since their common origin in the Paleogene. These results point out both species as relevant biogeographic models to address longstanding questions regarding the origin of marine biota from Southern Ocean.The nomenclature, taxonomy and ecology of both A. natans and Z. patagonica have been problematic for almost 200 years. Since its original description37, Z. patagonica, a.k.a. the “Ostión Patagónico” has been named with more than 10 synonyms, probably due to the great intra-specific morphological variability throughout its distribution19,38 (see the nomenclatural history in Supplementary Table S1). In contrast, there are very few records in the scientific literature and no genetic data on A. natans, a.k.a. the “Ostión del Sur”13,14,17,19, and some problems of nomenclature and establishing diagnostic characters persist since its description13,39. Many of the current junior synonyms of both species were described from small and juvenile specimens (under 52 mm VH39,40,41). Indeed, all deposited type material of A. natans ranges from 23.5 to 52 mm VH; the latter is half of the maximum size39. The criteria most commonly used for the identification of both scallops were number of radial primary ribs, maximum size, shell colour and presence of laminated concentric lines (Supplementary Table S1). Specimens with marked primary and secondary radial ribs alternated regularly and more whitish colouring of the right shell were attributed to Z. patagonica, while those with weaker and less markedly coloured radial ribs and the maximum size were considered as A. natans42. However, the number of radial ribs overlaps between Z. patagonica (26–4212,43) and A. natans (22–5017,19). These characters also have high variability across different environments and during ontogeny13,17. Thus the use of a taxonomy based on environment-sensitive and allometric characters has led to confusion in the morphological identification of these species13,38. The criterion used in the present study, the BND/VH ratio established by Jonkers13, discriminates the species efficiently. As attested by the narrow dispersal cluster in Fig. 3, this character has low intra-population variability13. In some cases a level of intraspecific variation can be detected, and this is mainly due to the environments where the scallop populations inhabit19 (e.g. exposed, protected, substrate type, fjord, oceanic). However, although there may be some intraspecific variability between populations, this variability does not generate problems for the identification of the two species. Individuals of A. natans generally presented a significantly greater BND/VH ratio than those of Z. patagonica. However, it is important to consider that, given that this character varies during ontogeny, it is more accurate in individuals over 25 mm VH13. Only the molecular identification was able to discriminate juvenile scallops of both species accurately.According to the literature, A. natans is restricted to interior waters of channels and is associated with kelp forests of M. pyrifera (Supplementary Table S1). Z. patagonica inhabits a wider range of environments such as bottoms of shells, sand, mud and gravel in protected and exposed areas, between 2 and 300 m depth (Supplementary Table S1), but is also associated with kelp forests in fjords with different degrees of glacial retreat12,16,44. The juveniles of both scallops recruit in kelp forests44,45. According to the local artisanal fishermen, adults of “Ostión del Sur” (A. natans) occur in fjords with glaciers (orange circles in Fig. 123). We included two sampling locations near glaciers (in Pia and Montañas fjords), where large individuals (between 46 and 86 mm) of A. natans and Z. patagonica occur in sympatry. This sympatry was previously reported in Silva Palma Fjord between 5 and 25 m depth16. In conclusion, scallop banks are not monospecific but rather mixed and Z. patagonica occurs in the interior waters of the channels and fjords. Consequently, these two species have overlapping ecology (recruiting zone and glacial affinity) in the channels and fjords, overturning a long-held view that these scallops have marked habitat segregation.The fishery for both species was established in the 1990s in the political-administrative Region of Magallanes16, despite the complexity of the morphological recognition of scallops. The distinction between species was based on shell colour and radial ribs42, two characters that, given the results of this study, do not have this diagnostic capacity. Consequently, the scallop fisheries in the Magallanes Region are currently based on inaccurately discriminative characters. Scallop banks in MP have always been considered as monospecific16,47. A great part of scallop landing has always been attributed to A. natans47, about which the scientific literature is scarce (Supplementary Table S1). Conversely, Z. patagonica, which was erroneously considered as the commercial species of southern Chile, has more scientific research (Supplementary Table S1).The difficulty to discriminate A. natans and Z. patagonica morphologically may lead to incorrect fishery statistics and uncertain conservation status of A. natans. Incorrect fishery statistics could overestimate the abundance of banks of A. natans compared to Z. patagonica. If the minimum catch size is reduced23 in the context of the fishing overuse of the last decade, A. natans may suffer a reduction of its maximum size48. Therefore, an identification criterion between species is a need to improve fishery management. We showcased a quantified criterion that is useful to identify both species. In the short-term, this method can be used, but it is difficult to enforce in practical ways. We suggest to train fishing inspectors, following three guidelines. First, the identification should consider only the right valve (RV) for species identification, since the left valve is not taxonomically informative. Second, for visual classification, check the outline of the BN, mainly because the individuals of Z. patagonica have a more arcute BN. Third, a reliable identification has to measure the depth of the byssal notch (BND) and shell height (VH) ratio. Lastly, future research and fishery monitoring should follow these criteria to carry out a correct identification and subsequently better landings statistics.Molecular tools allowed evaluating the phylogenetic relationships of scallops globally or regionally and incorporating parameters that can be used for the management and conservation of species of commercial interest49. For example, in the last few decades metrics have been developed to address conservation problems that give us a measure of the current state of particular taxa. These conservation priorities are often seen as measures for threatened species categorized by the IUCN Red List (World Conservation Union, 1980), one of the most widely and recognized systems. Although this prioritization metric incorporates phylogenetic distinctiveness (PD), this factor has been updated due to the importance of quantifying the loss of evolutionary diversity that would be implied by the extinction of a species50. The magnitude of the PD loss from any species will depend (but not exclusively) on the fate of its close relatives51. The “Ostión del Sur”, Austrochlamys natans is the last representative of its tribe (Austrochlamydini) in the Southern Ocean. Its phylogenetic position and the long branch length (i.e. the length of the branch from the tip to where it joins the tree), which represents an important amount of evolutionary change, highlights the degree of isolation of A. natans and calls attention to the possible loss of a unique genetic lineage. There is currently no conservation value for this relict species; we sought to alert the current fishery management that the “Ostión del Sur” is a distinct taxon and provide integrative evidence for further conservation studies.Finally, regarding the overlapping niche of these scallops and the conservation importance of the clade of A. natans, we propose three key recommendations for the future scallop fishery policies in the sub-Antarctic channels. First, it is necessary to assess the proportion of both species per bank and landing to generate a distribution map through the sub-Antarctic channels. For this assessment, the byssal notch depth is the most appropriate morphological character. Second, we recommend reassessments of biological and ecological parameters (e.g. size at first maturity) for A. natans across the glacial fjords, which are the most relevant fishing sites. As a final point, today there is a complete lack of knowledge of the genetic connectivity along the Subantarctic Channels. Thus we should generate more research about spatial population genetics at different temporal scales. The integration of genomic approaches (e.g. SNPs) with macro- and micro-environmental modelling approaches provide enormous opportunity to establish a new regional zoning for fishery management and conservation scallop strategy. More

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    Assessing multiple threats to seabird populations using flesh-footed shearwaters Ardenna carneipes on Lord Howe Island, Australia as case study

    1.Dias, M. P. et al. Threats to seabirds: A global assessment. Biol. Cons. 237, 525–537 (2019).Article 

    Google Scholar 
    2.Crain, C. M., Kroeker, K. & Halpern, B. S. Interactive and cumulative effects of multiple human stressors in marine systems. Ecol. Lett. 11, 1304–1315 (2008).PubMed 
    Article 

    Google Scholar 
    3.Michael, P. E. et al. Illegal fishing bycatch overshadows climate as a driver of albatross population decline. Mar. Ecol. Prog. Ser. 579, 185–199 (2017).ADS 
    Article 

    Google Scholar 
    4.Melo-Merino, S. M., Reyes-Bonilla, H. & Lira-Noriega, A. Ecological niche models and species distribution models in marine environments: A literature review and spatial analysis of evidence. Ecol. Model. 415, 108837 (2020).Article 

    Google Scholar 
    5.Rayner, M. J. et al. Predictive habitat modelling for the population census of a burrowing seabird: A study of the endangered Cook’s petrel. Biol. Cons. 138, 235–247 (2007).Article 

    Google Scholar 
    6.Habeeb, R. L., Trebilco, J., Wotherspoon, S. & Johnson, C. R. Determining natural scales of ecological systems. Ecol. Monogr. 75, 467–487 (2005).Article 

    Google Scholar 
    7.Li, G. D., Sun, S. A. & Fang, C. L. The varying driving forces of urban expansion in China: Insights from a spatial-temporal analysis. Landscape Urban Plan. 174, 63–77 (2018).Article 

    Google Scholar 
    8.Ranjeva, S. L. et al. Untangling the dynamics of persistence and colonization in microbial communities. ISME J. 13, 2998–3010 (2019).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    9.Thurman, L. L., Barner, A. K., Garcia, T. S. & Chestnut, T. Testing the link between species interactions and species co-occurrence in a trophic network. Ecography 42, 1658–1670 (2019).Article 

    Google Scholar 
    10.Murcia, C. Edge effects in fragmented forests: implications for conservation. Trends Ecol. Evol. 10, 58–62 (1995).CAS 
    PubMed 
    Article 

    Google Scholar 
    11.Jonzen, N., Wilcox, C. & Possingham, H. P. Habitat selection and population regulation in temporally fluctuating environments. Am. Nat. 164, 103–114 (2004).Article 

    Google Scholar 
    12.Coulson, J. C. Difference in the quality of birds nesting in the centre and on the edges of a colony. Nature 217, 478–479 (1968).ADS 
    Article 

    Google Scholar 
    13.Reid, T., Hindell, M., Lavers, J. L. & Wilcox, C. Re-examining mortality sources and population trends in a declining seabird: using Bayesian methods to incorporate existing information and new data. PLoS ONE 8(4), e58230 (2013).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    14.Lavers, J. L., Hutton, I. & Bond, A. L. Changes in technology and imperfect detection of nest contents impedes reliable estimates of population trends in burrowing seabirds. Global Ecol. Conserv. 17, e00579 (2019).Article 

    Google Scholar 
    15.Priddel, D., Carlile, N., Fullagar, P., Hutton, I. & O’Neill, L. Decline in the distribution and abundance of flesh-footed shearwaters (Puffinus carneipes) on Lord Howe Island, Australia. Biol. Cons. 128, 412–424 (2006).Article 

    Google Scholar 
    16.Baker, G. B. & Wise, G. S. The impact of pelagic longline fishing on the flesh-footed shearwater Puffinus carneipes in Eastern Australia. Biol. Cons. 126, 306–136 (2005).Article 

    Google Scholar 
    17.Tuck, G. N. & Wilcox, C. Assessing the potential impacts of fishing on the Lord Howe Island population of flesh-footed shearwaters 86 (Australian Fisheries Management Authority and CSIRO Marine and Atmospheric Research, 2010).
    Google Scholar 
    18.Carlile, N., Priddel, D., Reid, T. & Fullager, P. Flesh-footed shearwater decline on Lord Howe Island: rebuttal to Lavers et al 2019. Global Ecol. Conserv. 20, 1–3 (2019).
    Google Scholar 
    19.Lavers, J. L. Population status and threats to flesh-footed shearwater (Puffinus carneipes) in Western and South Australia. ICES J. Mar. Sci. 72, 316–327 (2014).Article 

    Google Scholar 
    20.Carey, M. J. The effects of investigator disturbance on procellariiform seabirds: a review. N. Z. J. Zool. 36, 367–377 (2009).Article 

    Google Scholar 
    21.Carey, M. J. Investigator disturbance reduces reproductive success in Short-tailed Shearwaters Puffinus tenuirostris. Ibis 153, 363–372 (2011).Article 

    Google Scholar 
    22.Orr, J. A. et al. Towards a unified study of multiple stressors: divisions and common goals across research disciplines. Proc. R. Soc. B Biol. Sci. 287, 20200421. https://doi.org/10.1098/rspb.2020.0421 (2020).Article 

    Google Scholar 
    23.Piggott, J. J., Townsend, C. R. & Matthael, C. D. Reconceptualizing synergism and antagonism among multiple stressors. Ecol. Evol. 5(7), 1538–1547 (2015).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    24.Ormerod, S. J., Dobson, M., Hildrew, A. G. & Townsend, C. R. Multiple stressors in freshwater ecosystems. Freshw. Biol. 55(Suppl. 1), 1–4. https://doi.org/10.1111/j.1365-2427.2009.02395.x (2010).Article 

    Google Scholar 
    25.Powell, C. D. L. Foraging movements and the migration trajectory of Flesh-footed Shearwaters Puffinus carneipes from the south coast of Western Australia. Mar. Ornithol. 37, 115–120 (2009).
    Google Scholar 
    26.Rexer-Huber, K., Parker, G. C., Ryan, P. G. & Cuthbert, R. J. Burrow occupancy and population size in the Atlantic Petrel Pterodroma incerta: a comparison of methods. Mar. Ornithol. 42, 137–141 (2014).
    Google Scholar 
    27.Rebstock, G. A., Boersma, P. D. & Garcia-Barbaroglu, P. Changes in habitat use and nesting density in a declining seabird Colony. Popul. Ecol. 58, 105–119 (2016).Article 

    Google Scholar 
    28.Ponchon, A. et al. When things go wrong: intra-season dynamics of breeding failure in a seabird. Ecosphere 5(1), 4. https://doi.org/10.1890/ES13-00233.1 (2014).Article 

    Google Scholar 
    29.Jackson, A. L., Bearhop, S. & Thompson, D. R. Shape can influence the rate of colony fragmentation in ground nesting seabirds. Oikos 111, 473–478 (2005).Article 

    Google Scholar 
    30.Martinez-Abrain, A. Why do ecologists aim to get positive results? Once again, negative results are necessary for better knowledge accumulation. Anim. Biodivers. Conserv. 36, 33–36 (2013).Article 

    Google Scholar 
    31.Gales, R., Brothers, N. & Reid, T. Seabird mortality in the Japanese longline tuna fishery around Australia, 1988–1995. Biol. Cons. 86, 37–56 (1997).Article 

    Google Scholar 
    32.Trebilco, R. et al. Characterizing seabird bycatch in the eastern Australian tuna and billfish pelagic longline fishery in relation to temporal, spatial and biological influences. Aquat. Conserv. Mar. Freshwat. Ecosyst. 20, 531–542 (2010).Article 

    Google Scholar 
    33.Chan, K. M. A. Value and advocacy in conservation biology: crisis discipline or discipline in crisis. Conserv. Biol. 22, 1–3 (2008).PubMed 
    Article 

    Google Scholar 
    34.Hindwood, K. A. The birds of Lord Howe Island. Emu 40, 1–86 (1940).Article 

    Google Scholar 
    35.McDougall, I., Embleton, B. J. J. & Stone, D. B. Origin and evolution of Lord Howe Island, Southwest Pacific Ocean. J. Geol. Soc. Aust. 28, 155–176 (1981).CAS 
    Article 

    Google Scholar 
    36.Pickard, J. Vegetation of Lord Howe Island. Cunninghamia 1, 133–265 (1983).
    Google Scholar 
    37.Marchant, S. & Higgins, P. J. (eds) Handbook of Australian, New Zealand and Antarctic Birds. Ratites to Ducks Vol. 1 (Oxford University Press, 1990).
    Google Scholar 
    38.Serventy, D. L. & Whittell, H. M. A Handbook of the Birds of Western Australia 2nd edn. (Paterson Brokensha Pty., Ltd, 1951).
    Google Scholar 
    39.Powell, C. D. L., Wooller, R. D. & Bradley, J. S. Breeding biology of the flesh-footed shearwater (Puffinus carneipes) on Woody Island, Western Australia. Emu 107, 275–283 (2007).Article 

    Google Scholar 
    40.Reid, T. A. et al. Nonbreeding distribution of flesh-footed shearwaters and the potential for overlap with north Pacific fisheries. Biol. Cons. 166, 3–10 (2013).Article 

    Google Scholar 
    41.Lombal, A. J. et al. Genetic divergence between colonies of flesh-footed shearwaters Ardenna carneipes exhibiting different foraging strategies. Conserv. Genet. 9, 27–41 (2018).Article 

    Google Scholar 
    42.Carlile, N. & Priddel, D. Seabird islands No. 261: Mutton Bird Island, Lord Howe Group, New South Wales. Corella 37(4), 94–96 (2013).
    Google Scholar 
    43.Carlile, N., Priddel, D. & Bower, H. Seabird islands No. 256: Roach Island, Lord Howe Group, New South Wales. Corella 37(4), 82–85 (2013).
    Google Scholar 
    44.R Core Team. R: A language and environment for statistical computing. R Foundation for Statistical Computing. https://www.R-project.org/. (2015)45.Wood, S. N. Generalised Additive Models: An Introduction with R (Chapman and Hall/CRC, 2006).
    Google Scholar 
    46.Burnham, K. R. & Anderson, D. R. Model Selection and Multimodal Inference: A Practical Information Theoretic Approach (Springer, 2002).
    Google Scholar 
    47.Barton, K. MuMIn: Multi-Model Inference. R package version 1.15.1. http://CRAN.R-project.org/package=MuMIn (2015).48.Pebesma, E. J. & Bivand, R. S. Classes and methods for spatial data in R. R News 5 (2), https://cran.r-project.org/doc/Rnews/.(2005).49.Bivand, R. S., Pebesma, E. & Gomez-Rubio, V. Applied Spatial Data Analysis with R 2nd edn. (Springer, 2013).
    Google Scholar  More

  • in

    Geographical distribution of the dispersal ability of alien plant species in China and its socio-climatic control factors

    1.Bartz, R. & Kowarik, I. Assessing the environmental impacts of invasive alien plants: a review of assessment approaches. Neobiota https://doi.org/10.3897/neobiota.43.30122 (2019).Article 

    Google Scholar 
    2.Chen, C. et al. Historical introduction, geographical distribution, and biological characteristics of alien plants in China. Biodivers. Conserv. 26, 353–381. https://doi.org/10.1007/s10531-016-1246-z (2017).Article 

    Google Scholar 
    3.Feng, J. & Zhu, Y. Alien invasive plants in China: risk assessment and spatial patterns. Biodivers. Conserv. 19, 3489–3497. https://doi.org/10.1007/s10531-010-9909-7 (2010).Article 

    Google Scholar 
    4.Thapa, S., Chitale, V., Rijal, S. J., Bisht, N. & Shrestha, B. B. Understanding the dynamics in distribution of invasive alien plant species under predicted climate change in Western Himalaya. Plos One https://doi.org/10.1371/journal.pone.0195752 (2018).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    5.Majewska, M. L. et al. Do the impacts of alien invasive plants differ from expansive native ones? An experimental study on arbuscular mycorrhizal fungi communities. Biol. Fertil. Soils 54, 631–643. https://doi.org/10.1007/s00374-018-1283-8 (2018).Article 

    Google Scholar 
    6.Shi, J., Luo, Y.-Q., Zhou, F. & He, P. The relationship between invasive alien species and main climatic zones. Biodivers. Conserv. 19, 2485–2500. https://doi.org/10.1007/s10531-010-9855-4 (2010).Article 

    Google Scholar 
    7.Hulme, P. E. Trade, transport and trouble: managing invasive species pathways in an era of globalization. J. Appl. Ecol. 46, 10–18. https://doi.org/10.1111/j.1365-2664.2008.01600.x (2009).Article 

    Google Scholar 
    8.Hulme, P. E. et al. Grasping at the routes of biological invasions: a framework for integrating pathways into policy. J. Appl. Ecol. 45, 403–414. https://doi.org/10.1111/j.1365-2664.2007.01442.x (2008).Article 

    Google Scholar 
    9.Jara-Guerrero, A., De la Cruz, M. & Mendez, M. Seed dispersal spectrum of woody species in south ecuadorian dry forests: environmental correlates and the effect of considering species abundance. Biotropica 43, 722–730. https://doi.org/10.1111/j.1744-7429.2011.00754.x (2011).Article 

    Google Scholar 
    10.van Oudtshoorn, K. v. R. & van Rooyen, M. W. Dispersal biology of desert plants. (Springer 1999).11.Liu, J., Liang, S. C., Liu, F. H., Wang, R. Q. & Dong, M. Invasive alien plant species in China: regional distribution patterns. Divers. Distrib. 11, 341–347. https://doi.org/10.1111/j.1366-9516.2005.00162.x (2005).Article 

    Google Scholar 
    12.Caughlin, T. T., Ferguson, J. M., Lichstein, J. W., Bunyavejchewin, S. & Levey, D. J. The importance of long-distance seed dispersal for the demography and distribution of a canopy tree species. Ecology 95, 952–962. https://doi.org/10.1890/13-0580.1 (2014).Article 
    PubMed 

    Google Scholar 
    13.Nathan, R. et al. Mechanisms of long-distance seed dispersal. Trends Ecol. Evol. 23, 638–647. https://doi.org/10.1016/j.tree.2008.08.003 (2008).Article 
    PubMed 

    Google Scholar 
    14.Wang, R. et al. Multiple mechanisms underlie rapid expansion of an invasive alien plant. New Phytol. 191, 828–839. https://doi.org/10.1111/j.1469-8137.2011.03720.x (2011).Article 
    PubMed 

    Google Scholar 
    15.Vittoz, P. & Engler, R. Seed dispersal distances: a typology based on dispersal modes and plant traits. Bot. Helv. 117, 109–124. https://doi.org/10.1007/s00035-007-0797-8 (2007).Article 

    Google Scholar 
    16.Willson, M. F., Rice, B. L. & Westoby, M. Seed dispersal spectra – a comparison of temperate plant-communities. J. Veg. Sci. 1, 547–562. https://doi.org/10.2307/3235789 (1990).Article 

    Google Scholar 
    17.Nilsson, C., Brown, R. L., Jansson, R. & Merritt, D. M. The role of hydrochory in structuring riparian and wetland vegetation. Biol. Rev. 85, 837–858. https://doi.org/10.1111/j.1469-185X.2010.00129.x (2010).Article 
    PubMed 

    Google Scholar 
    18.Eminniyaz, A. et al. Dispersal Mechanisms of the Invasive Alien Plant Species Buffalobur (Solanum rostratum) in Cold Desert Sites of Northwest China. Weed Sci. 61, 557–563. https://doi.org/10.1614/ws-d-13-00011.1 (2013).CAS 
    Article 

    Google Scholar 
    19.Soons, M. B., Heil, G. W., Nathan, R. & Katul, G. G. Determinants of long-distance seed dispersal by wind in grasslands. Ecology 85, 3056–3068. https://doi.org/10.1890/03-0522 (2004).Article 

    Google Scholar 
    20.Tackenberg, O. Modeling long-distance dispersal of plant diaspores by wind. Ecol. Monogr. 73, 173–189. https://doi.org/10.1890/0012-9615(2003)073[0173:mldopd]2.0.co;2 (2003).Article 

    Google Scholar 
    21.Wallace, H. M., Howell, M. G. & Lee, D. J. Standard yet unusual mechanisms of long-distance dispersal: seed dispersal of Corymbia torelliana by bees. Divers. Distrib. 14, 87–94. https://doi.org/10.1111/j.1472-4642.2007.00427.x (2008).Article 

    Google Scholar 
    22.Soons, M. B., Nathan, R. & Katul, G. G. Human effects on long-distance wind dispersal and colonization by grassland plants. Ecology 85, 3069–3079. https://doi.org/10.1890/03-0398 (2004).Article 

    Google Scholar 
    23.Taylor, K., Brummer, T., Taper, M. L., Wing, A. & Rew, L. J. Human-mediated long-distance dispersal: an empirical evaluation of seed dispersal by vehicles. Divers. Distrib. 18, 942–951. https://doi.org/10.1111/j.1472-4642.2012.00926.x (2012).Article 

    Google Scholar 
    24.Cain, M. L., Milligan, B. G. & Strand, A. E. Long-distance seed dispersal in plant populations. Am. J. Bot. 87, 1217–1227. https://doi.org/10.2307/2656714 (2000).CAS 
    Article 
    PubMed 

    Google Scholar 
    25.Thomson, F. J., Moles, A. T., Auld, T. D. & Kingsford, R. T. Seed dispersal distance is more strongly correlated with plant height than with seed mass. J. Ecol. 99, 1299–1307. https://doi.org/10.1111/j.1365-2745.2011.01867.x (2011).Article 

    Google Scholar 
    26.Zhu, J., Liu, M., Xin, Z., Zhao, Y. & Liu, Z. Which factors have stronger explanatory power for primary wind dispersal distance of winged diaspores: the case of Zygophyllum xanthoxylon (Zygophyllaceae)?. J Plant Ecol 9, 346–356. https://doi.org/10.1093/jpe/rtv051 (2016).Article 

    Google Scholar 
    27.Jones, F. A. & Muller-Landau, H. C. Measuring long-distance seed dispersal in complex natural environments: an evaluation and integration of classical and genetic methods. J. Ecol. 96, 642–652. https://doi.org/10.1111/j.1365-2745.2008.01400.x (2008).Article 

    Google Scholar 
    28.Snell, R. S. Simulating long-distance seed dispersal in a dynamic vegetation model. Glob. Ecol. Biogeogr. 23, 89–98. https://doi.org/10.1111/geb.12106 (2014).Article 

    Google Scholar 
    29.Jongejans, E. & Telenius, A. Field experiments on seed dispersal by wind in ten umbelliferous species (Apiaceae). Plant Ecol. 152, 67–78. https://doi.org/10.1023/a:1011467604469 (2001).Article 

    Google Scholar 
    30.Guitian, J. & Sanchez, J. M. Seed dispersal spectra of plant-communities in the Iberian Peninsula. Vegetatio 98, 157–164. https://doi.org/10.1007/bf00045553 (1992).Article 

    Google Scholar 
    31.Ou, H., Lu, C. & O’Toole, D. K. A risk assessment system for alien plant bio-invasion in Xiamen China. J. Environ. Sci. 20, 989–997. https://doi.org/10.1016/s1001-0742(08)62198-1 (2008).Article 

    Google Scholar 
    32.Huang, Q. Q., Wu, J. M., Bai, Y. Y., Zhou, L. & Wang, G. X. Identifying the most noxious invasive plants in China: role of geographical origin, life form and means of introduction. Biodivers. Conserv. 18, 305–316. https://doi.org/10.1007/s10531-008-9485-2 (2009).Article 

    Google Scholar 
    33.Liu, J. et al. Invasive alien plants in China: role of clonality and geographical origin. Biol. Invasions 8, 1461–1470. https://doi.org/10.1007/s10530-005-5838-x (2006).Article 

    Google Scholar 
    34.Xu, H., Wang, J., Qiang, S. & Wang, C. Study of key issues under the convention on biological diversity: alien species invasion, biosafety, genetic resources. (Science Press, 2004).35.Ma, J. & Li, H. The checklist of the alien invasive plants in China. (Higher Education Press, 2018).36.Wang, C., Liu, J., Xiao, H., Zhou, J. & Du, D. Floristic characteristics of alien invasive seed plant species in China. Anais Da Academia Brasileira De Ciencias 88, 1791–1797. https://doi.org/10.1590/0001-3765201620150687 (2016).Article 
    PubMed 

    Google Scholar 
    37.Xie, Y., Li, Z. Y., Gregg, W. P. & Dianmo, L. Invasive species in China – an overview. Biodivers. Conserv. 10, 1317–1341 (2001).Article 

    Google Scholar 
    38.Qi, W., Liu, S. H., Zhao, M. F. & Liu, Z. China’s different spatial patterns of population growth based on the “Hu Line”. J. Geog. Sci. 26, 1611–1625. https://doi.org/10.1007/s11442-016-1347-3 (2016).Article 

    Google Scholar 
    39.Chen, M. X., Gong, Y. H., Li, Y., Lu, D. D. & Zhang, H. Population distribution and urbanization on both sides of the Hu Huanyong Line: answering the Premier’s question. J. Geog. Sci. 26, 1593–1610. https://doi.org/10.1007/s11442-016-1346-4 (2016).Article 

    Google Scholar 
    40.Pan, X. B. et al. Spatial similarity in the distribution of invasive alien plants and animals in China. Nat. Hazards 77, 1751–1764. https://doi.org/10.1007/s11069-015-1672-3 (2015).Article 

    Google Scholar 
    41.Yan, X. et al. The categorization and analysis on the geographic distribution patterns of Chinese alien invasive plants. Biodiv. Sci. 22, 667–676 (2014).Article 

    Google Scholar 
    42.Wang, G., Bai, F. & Sang, W. Spatial distribution of invasive alien animal and plant species and its influencing factors in China. Plant Sci. J. 35, 513–524 (2017).
    Google Scholar 
    43.Weber, E., Sun, S. G. & Li, B. Invasive alien plants in China: diversity and ecological insights. Biol. Invasions 10, 1411–1429. https://doi.org/10.1007/s10530-008-9216-3 (2008).Article 

    Google Scholar 
    44.Zhou, Q. et al. Geographical distribution and determining factors of different invasive ranks of alien species across China. Sci. Total Environ. 722, 137929. https://doi.org/10.1016/j.scitotenv.2020.137929 (2020).ADS 
    CAS 
    Article 
    PubMed 

    Google Scholar 
    45.Ding, J., Mack, R. N., Lu, P., Ren, M. & Huang, H. China’s booming economy is sparking and accelerating biological invasions. Bioscience 58, 317–324. https://doi.org/10.1641/b580407 (2008).Article 

    Google Scholar 
    46.Pysek, P. et al. Alien plants in checklists and floras: towards better communication between taxonomists and ecologists. Taxon 53, 131–143. https://doi.org/10.2307/4135498 (2004).Article 

    Google Scholar 
    47.Zeng, C. & Chen, W. A forecasting model of urban underground space development intensity. Chin. J. Undergr. Space Eng. 14, 1154–1160 (2018).
    Google Scholar 
    48.Shao, M. N. et al. Outbreak of a new alien invasive plant Salvia reflexa in north-east China. Weed Res. 59, 201–208. https://doi.org/10.1111/wre.12357 (2019).Article 

    Google Scholar 
    49.Wan, F. H. et al. Invasive mechanism and control strategy of Ageratina adenophora (Sprengel). Sci. China-Life Sci. 53, 1291–1298. https://doi.org/10.1007/s11427-010-4080-7 (2010).Article 
    PubMed 

    Google Scholar 
    50.Poudel, A. S., Jha, P. K., Shrestha, B. B. & Muniappan, R. Biology and management of the invasive weed Ageratina adenophora (Asteraceae): current state of knowledge and future research needs. Weed Res. 59, 79–92. https://doi.org/10.1111/wre.12351 (2019).Article 

    Google Scholar 
    51.Datta, A., Schweiger, O. & Kuehn, I. Niche expansion of the invasive plant species Ageratina adenophora despite evolutionary constraints. J. Biogeogr. 46, 1306–1315. https://doi.org/10.1111/jbi.13579 (2019).Article 

    Google Scholar 
    52.Guo, X., Ren, M. & Ding, J. Do the introductions by botanical gardens facilitate the invasion of Solidago canadensis (Asterceae) in China?. Weed Res. 56, 442–451. https://doi.org/10.1111/wre.12227 (2016).Article 

    Google Scholar 
    53.Ganneru, S., Shaik, H., Peddi, K. & Mudiam, M. K. R. Evaluating the metabolic perturbations in Mangifera indica (mango) ripened with various ripening agents/practices through gas chromatography – mass spectrometry based metabolomics. J. Sep. Sci. 42, 3086–3094. https://doi.org/10.1002/jssc.201900291 (2019).CAS 
    Article 
    PubMed 

    Google Scholar 
    54.Mahandran, V., Murugan, C. M., Marimuthu, G. & Nathan, P. T. Seed dispersal of a tropical deciduous Mahua tree, Madhuca latifolia (Sapotaceae) exhibiting bat-fruit syndrome by pteropodid bats. Glob. Ecol. Conserv. 14, e00396. https://doi.org/10.1016/j.gecco.2018.e00396 (2018).Article 

    Google Scholar 
    55.Weber, E. & Li, B. Plant invasions in China: What is to be expected in the wake of economic development?. Bioscience 58, 437–444. https://doi.org/10.1641/b580511 (2008).Article 

    Google Scholar 
    56.Jian, L., Hua, C., Kowarik, I., Zhang, Y. & Wang, R. Plant invasions in China: an emerging hot topic in invasion science. Neobiota 15, 27–41 (2012).Article 

    Google Scholar  More

  • in

    Contracting eastern African C4 grasslands during the extinction of Paranthropus boisei

    1.Leakey, L. S. B., Tobias, P. V. & Napier, J. R. A new species of the genus Homo from Olduvai Gorge. Nature 202, 7–9 (1964).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    2.Bromage, T. G. & Schrenk, F. Biogeographic and climatic basis for a narrative of early hominid evolution. J. Hum. Evol. 28, 109–114 (1995).Article 

    Google Scholar 
    3.Klein, R. The causes of “robust” australopithecine extinction in Evolutionary history of the “robust” australopithecines (ed. Grine, F.E.) 499–505 (Aldine de Gruyter, 1988).4.McPherron, S.P. et al. Evidence for stone-tool-assisted consumption of animal tissues before 3.39 million years ago at Dikika, Ethiopia. Nature 466, 857–860 (2010).5.Harmand, S. et al. Before the Oldowan: 3.3 Ma Stone Tools from Lomekwi 3, West Turkana, Kenya. Nature 521, 310–315 (2015).6.Cerling, T. E. et al. Diet of Panthropus boisei in the early Pleistocene of East Africa. Proc. Natl. Acad. Sci. USA 108, 9337–9341 (2011).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    7.Ungar, P. S. & Sponheiner, M. The diets of early hominins. Science 334, 190–193 (2011).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    8.Cerling, T. E. et al. Stable isotope-based diet reconstructions of Turkana Basin hominins. Proc. Natl. Acad. Sci. USA 110, 10501–10506 (2013).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    9.Cerling, T. E. et al. Diet of Theropithecus from 4 to 1 Ma in Kenya. Proc. Natl. Acad. Sci. 110, 10507–10512 (2013).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    10.Ungar, P. S., Grine, F. E. & Teaford, M. F. Dental microwear and diet of the Plio-Pleistocene hominin Paranthropus boisei. PLoS ONE 3, e2044 (2008).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    11.Ludecke, T. et al. Dietary versatility of early Pleistocene hominins. Proc. Natl. Acad. Sci. USA 115, 13330–13335 (2018).PubMed 
    Article 
    CAS 
    PubMed Central 

    Google Scholar 
    12.Wynn, J. G. et al. Isotopic evidence for the timing of the dietary shift toward C4 foods in eastern African Paranthropus. Proc. Natl. Acad. Sci. USA https://doi.org/10.1073/pnas.2006221117 (2020).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    13.Martin, J. E., Tacail, T., Braga, J., Cerling, T. E. & Balter, V. Calcium isotopic ecology of Turkana Basin hominins. Nat. Commun. 11, 3587 (2020).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    14.Dominguez-Rodrigo, M. et al. First partial skeleton of a 1.34-million-year-old Paranthropus boisei from Bed II, Oluvai Gorge, Tanzania. PLoS ONE 8, e80347 (2013).15.Wood, B., Wood, C. & Konigsberg, L. Paranthropus boisei: An example of evolutionary stasis?. Am. J. Phys. Anthropol. 95, 117–136 (1994).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    16.Wood, B. A. & Patterson, B. A. Paranthropus through the looking glass. Proc. Natl. Acad. Sci. USA https://doi.org/10.1073/pnas.2016445117 (2020).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    17.Antón, S. C., Potts, R. & Aiello, L. C. Evolution of early Homo: an integrated biological perspective. Science 345, 1236828 (2014).PubMed 
    Article 
    CAS 
    PubMed Central 

    Google Scholar 
    18.Wood, B. & Constantino, P. Paranthropus boisei: Fifty years of evidence and analysis. Yrbk. Phys. Anthropol. 50, 106–132 (2007).Article 

    Google Scholar 
    19.Muttoni, G., Scardia, G. & Kent, D. V. Early hominins in Europe: The Galerian migration hypothesis. Quat. Sci. Rev. 180, 1–29 (2018).ADS 
    Article 

    Google Scholar 
    20.Shultz, S., Nelson, E. & Dunbar, R. I. M. Hominin cognitive evolution: identifying patterns and processes in the fossil and archaeological record. Phil. Trans. R. Soc. B 367, 2130–2140 (2012).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    21.Clark, P. U. et al. The middle Pleistocene transition: characteristics, mechanisms, and implications for long-term changes in atmospheric pCO2. Quat. Sci. Rev. 25, 3150–3184 (2006).ADS 
    Article 

    Google Scholar 
    22.Raymo, M. E., Oppo, D. W. & Curry, W. The mid-Pleistocene climate transition: a deep sea carbon isotopic perspective. Paleoceanogr. 12, 546–559 (1997).ADS 
    Article 

    Google Scholar 
    23.Levin, N. E. Environment and climate of early human evolution. Ann. Rev. Earth Planet. Sci. 43, 405–429 (2015).ADS 
    CAS 
    Article 

    Google Scholar 
    24.Cerling, T. E. et al. Woody cover and hominin environments in the past 6 million years. Nature 476, 51–56 (2011).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    25.Potts, R. & Faith, J. T. Alternating high and low climate variability: the context of natural selection and speciation in Plio-Pleistocene hominin evolution. J. Hum. Evol. 87, 5–20 (2015).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    26.Cerling, T. E. et al. Dietary changes of large herbivores in the Turkana Basin, Kenya from 4 to 1 Ma. Proc. Natl. Acad. Sci. USA 112, 11467–11472 (2015).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    27.Negash, E. W. et al. Dietary trends in herbivores from the Shungura Formation, southwestern Ethiopia. Proc. Natl. Acad. Sci. USA https://doi.org/10.1073/pnas.2006982117 (2020).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    28.Pasquette, J. & Drapeau, M. S. M. Environmental comparisons of the Awash Valley, Turkana Basin and lower Omo Valley from upper Miocene to Holocene as assessed from stable carbon and oxygen isotopes of mammalian enamel. Palaeogeogr. Palaeoclimatol. Palaeoecol. 562, 110099 (2021).Article 

    Google Scholar 
    29.Bobe, R. & Behrensmeyer, A. K. The expansion of grassland ecosystems in Africa in relation to mammalian evolution and the origins of the genus Homo. Palaeogeogr. Palaeoclimatol. Palaeoecol. 207, 399–420 (2004).Article 

    Google Scholar 
    30.Nutz, A. et al. Plio-Pleistocene sedimentation in West Turkana (Turkana Depression, Kenya, East African Rift System): paleolake fluctuations, paleolandscapes and controlling factors. Earth-Sci. Rev. 211, 103415 (2020).CAS 
    Article 

    Google Scholar 
    31.Sankaran, M. et al. Determinants of woody cover in African savannas. Nature 438, 846–849 (2005).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    32.Saji, N. H., Goswami, B. N., Vinayachandran, P. N. & Yamagata, T. A dipole in the tropical Indian Ocean. Nature 401, 360–363 (1999).ADS 
    CAS 
    PubMed 
    PubMed Central 

    Google Scholar 
    33.Peterson, L. C., Haug, G. H., Hughen, K. A. & Rohl, U. Rapid changes in the hydrologic cycle of the tropical Atlantic during the Last Glacial. Science 290, 1947–1951 (2000).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    34.Schefuß, E., Schouten, S., Jansen, J.H.F., Sinninghe Damste, J.S. African vegetation controlled sea surface temperatures in the mid-Pleistocene period. Nature 422, 418–421 (2003).35.deMenocal, P.B. African climate change and faunal evolution during the Pliocene-Pleistocene. Earth Planet. Sci. Lett. 220, 3–24 (2004).36.Trauth, M. H., Maslin, M. A., Deino, A. & Strecker, M. R. Late Cenozoic moisture history of East Africa. Science 309, 2051–2053 (2005).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    37.Donges, J. F. et al. Nonlinear detection of paleoclimate-variability transitions possibly related to human evolution. Proc. Natl. Acad. Sci. USA 108, 20422–20427 (2011).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    38.Polissar, P. J., Rose, C., Uno, K. T., Phelps, S. R. & deMenocal, P. Synchronous rise of African C4 ecosystems 10 million years ago in the absence of aridification. Nat. Geosci. 12, 657–660 (2019).ADS 
    CAS 
    Article 

    Google Scholar 
    39.Gathogo, P. N. & Brown, F. H. Stratigraphy of the Koobi Fora Formation (Pliocene and Pleistocene) in the Ileret region of northern Kenya. J. Afr. Earth Sci. 45, 369–390 (2006).ADS 
    Article 

    Google Scholar 
    40.Feibel, C. S. A geological history of the Turkana Basin. Evol. Anthropol. 20, 206–216 (2011).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    41.Faith, T. J., Rowan, J., Du, A. & Koch, P. L. Plio-Pleistocene decline of African megaherbivores: No evidence for ancient hominin impacts. Science 362, 938–941 (2018).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    42.Blumenthal, S. A. et al. Aridity and hominin environments. Proc. Natl. Acad. Sci. USA 114, 7331–7336 (2017).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    43.Lepre, C. J. Constraints on Fe-oxide formation in monsoonal Vertisols of Pliocene Kenya using rock magnetism and spectroscopy. Geochem. Geophys. Geosyst. 20, 4998–5013 (2019).ADS 
    CAS 
    Article 

    Google Scholar 
    44.Faurby, S., Silvestro, D., Werdelin, L. & Antonelli, A. Brain expansion in early hominins predicts carnivore extinctions in East Africa. Ecol. Lett. 23, 537–544 (2020).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    45.Faith, T. J., Rowan, J. & Du, A. Early hominins evolved within non-analog ecosystems. Proc. Natl. Acad. Sci. USA 116, 21478–21483 (2019).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    46.Bond, W. J., Midgley, G. F. & Woodward, F. I. The importance of low atmospheric CO2 and fire in promoting the spread of grasslands and savannas. Glob. Change Biol. 9, 973–982 (2003).ADS 
    Article 

    Google Scholar 
    47.Bragg, F. J. et al. Stable isotope and modeling evidence for CO2 as a driver of glacial-interglacial vegetation shifts in southern Africa. Biogeosci. 10, 2001–2010 (2013).ADS 
    CAS 
    Article 

    Google Scholar 
    48.Ehleringer, J. R., Cerling, T. E. & Helliker, B. R. C4 photosynthesis, atmospheric CO2, and climate. Oecologia 112, 285–299 (1997).ADS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    49.Da, J., Zhang, Y., Li, G., Meng, X. & Ji, J. Low CO2 levels of the entire Pleistocene epoch. Nat. Commun. 10, 4342 (2019).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    50.Stap, L. B. et al. CO2 over the past 5 million years: continuous simulation and new δ11B-based proxy data. Earth Planet. Sci. Lett. 439, 1–10 (2016).ADS 
    CAS 
    Article 

    Google Scholar 
    51.van de Wal, R.S.W., de Boer, B., Lourens, LJ.., Kohler, P., Bintanja, R. Reconstruction of a continuous high-resolution CO2 record over the past 20 million years. Clim. Past 7, 1459–69 (2011).52.Passey, B. H., Levin, N. E., Cerling, T. E., Brown, F. H. & Eiler, J. M. High-temperature environments of human evolution in East Africa based on bond ordering in paleosol carbonates. Proc. Nat. Acad. Sci. USA 107, 11245–11249 (2010).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    53.Petit, J.R. et al. Climate and atmospheric history of the past 420,000 years from the Vostok ice core, Antarctica: Nature 399, 429–436 (1999).54.Schefuß, E. & Dupont, L. M. Multiple drivers of Miocene C4 ecosystem expansions. Nat. Geosci. 13, 463–464 (2020).ADS 
    Article 
    CAS 

    Google Scholar 
    55.Johnson, T.C. et al. A progressively wetter climate in southern East Africa over the past 1.3 million years. Nature 537, 220–224 (2016).56.Skonieczny, C. et al. Monsoon-driven Saharan dust variability over the past 240,000 years. Sci. Adv. 5, eaav1887 (2019).57.Caley, T. et al. A two-million-year-long hydroclimatic context for hominin evolution in southeastern Africa. Nature 560, 76–79.58.Kim, S.-J. et al. High-resolution climate simulation of the last glacial maximum. Clim Dyn 31, 1–16 (2008).Article 

    Google Scholar 
    59.Tierney, J. E., Russell, J. M., Sinninghe Damsté, J. S., Huang, Y. & Verschuren, D. Late quaternary behavior of the East African monsoon and the importance of the Congo Air Boundary. Quatern. Sci. Rev. 30, 798–807 (2011).ADS 
    Article 

    Google Scholar 
    60.Kingston, J. D. & Harrison, T. Isotopic dietary reconstructions of Pliocene herbivores at Laetoli: implications for early hominin paleoecology. Palaeogeogr. Palaeoclimatol. Palaeoecol. 243, 272–306 (2007).Article 

    Google Scholar 
    61.Quinn, R. L. Isotopic equifinality and rethinking the diet of Australopithecus anamensis. Am. J. Phys. Anthropol. 169, 403–421 (2019).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    62.Wood, D. Strait, Patterns of resource use in early Homo and Paranthropus. J. Hum. Evol. 46, 119–162 (2004).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    63.Patterson, D. B. et al. Comparative isotopic evidence from East Turkana supports a dietary shift within the genus Homo. Nat. Ecol. Evol. https://doi.org/10.1038/s41559-019-0916-0 (2019).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    64.Lepre, C. J. et al. An earlier origin for the Acheulian. Nature 477, 82–85 (2011).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    65.Braun, D.R. et al. Earliest known Oldowan artifacts at >2.58 Ma from Ledi-Geraru, Ethiopia, highlight technological diversity. Proc. Natl. Acad. Sci. USA 116, 11712–11717 (2019).66.Mana, S., Hemming, S., Kent, D. V. & Lepre, C. J. Temporal and stratigraphic framework for paleoanthropology site within East-Central Area 130, Koobi Fora Kenya. Front. Earth Sci. 7, 230 (2019).ADS 
    Article 

    Google Scholar 
    67.Shea, J. J. Occasional, obligatory, and habitual stone tool use in hominin evolution. Evol. Anthropol. 26, 200–217 (2017).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    68.de la Torre, I. The origins of the Acheulean: past and present perspectives on a major transition in human evolution. Philos. Trans. R. Soc. B 371, 20150245 (2016).Article 

    Google Scholar 
    69.Harris, J. M., Brown, F. H. & Leakey, M. G. Geology and paleontology of Plio-Pleistocene localities west of Lake Turkana Kenya. Contrib. Sci. 399, 1–128 (1988).
    Google Scholar 
    70.McDougall, I. et al. New single crystal 40Ar/39Ar ages improve time scale for deposition of the Omo Group, Omo-Turkana Basin East Africa. J. Geol. Soc. Lond. 169, 213–226 (2012).CAS 
    Article 

    Google Scholar 
    71.Quinn, R. L. et al. Pedogenic carbonate stable isotopic evidence for wooded habitat preference of early Pleistocene tool makers in the Turkana Basin. J. Hum. Evol. 65, 65–78 (2013).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    72.Potts, R. et al. Environmental dynamics during the onset of the Middle Stone Age in eastern Africa. Science 360, 86–90 (2018).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    73.Levin, N. E., Zipser, E. J. & Cerling, T. E. isotopic compositions of waters from Ethiopia and Kenya: insights into moisture sources for eastern Africa. J. Geophys. Res. 114, D23306 (2009).ADS 
    Article 
    CAS 

    Google Scholar  More

  • in

    First insights into the impacts of benthic cyanobacterial mats on fish herbivory functions on a nearshore coral reef

    1.Ford, A. K. et al. Reefs under siege: the rise, putative drivers, and consequences of benthic cyanobacterial mats. Front. Mar. Sci. 5, 18 (2018).Article 

    Google Scholar 
    2.Brocke, H. J. et al. Organic matter degradation drives benthic cyanobacterial mat abundance on Caribbean coral reefs. PLoS ONE 10, e0125445 (2015).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    3.Charpy, L., Casareto, B. E., Langlade, M. J. & Suzuki, Y. Cyanobacteria in coral reef ecosystems: a review. J. Mar. Biol. 2012, e259571 (2012).Article 

    Google Scholar 
    4.Mangubhai, S. & Obura, D. O. Silent killer: black reefs in the Phoenix Islands Protected Area. Pac. Conserv. Biol. 25, 213 (2019).Article 

    Google Scholar 
    5.de Bakker, D. M. et al. 40 years of benthic community change on the Caribbean reefs of Curaçao and Bonaire: the rise of slimy cyanobacterial mats. Coral Reefs 36, 355–367 (2017).ADS 
    Article 

    Google Scholar 
    6.Albert, S., Dunbabin, M., Skinner, M., Moore, B. & Grinham, A. Benthic shift in a Solomon Islands’ lagoon: corals to cyanobacteria. In Proceedings of the 12th International Coral Reef Symposium, Cairns, Australia, 9–13 July 2012 1–5 (2012).7.Puyana, M., Acosta, A., Bernal-Sotelo, K., Velásquez-Rodríguez, T. & Ramos, F. Spatial scale of cyanobacterial blooms in Old Providence Island Colombian Caribbean. Universitas Scientiarum 20, 83–105 (2015).Article 

    Google Scholar 
    8.Ford, A. K. et al. High sedimentary oxygen consumption indicates that sewage input from small islands drives benthic community shifts on overfished reefs. Environ. Conserv. 44, 405–411 (2017).Article 

    Google Scholar 
    9.Chapra, S. C. et al. Climate change impacts on harmful algal blooms in US freshwaters: a screening-level assessment. Environ. Sci. Technol. 51, 8933–8943 (2017).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    10.Huisman, J. et al. Cyanobacterial blooms. Nat. Rev. Microbiol. 16, 471–483 (2018).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    11.Gobler, C. J. Climate change and harmful algal blooms: insights and perspective. Harmful Algae 91, 101731 (2020).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    12.Wood, S. A. et al. Toxic benthic freshwater cyanobacterial proliferations: challenges and solutions for enhancing knowledge and improving monitoring and mitigation. Freshw. Biol. 65, 1824–1842 (2020).Article 

    Google Scholar 
    13.Brown, K. T., Bender-Champ, D., Bryant, D. E. P., Dove, S. & Hoegh-Guldberg, O. Human activities influence benthic community structure and the composition of the coral-algal interactions in the central Maldives. J. Exp. Mar. Biol. Ecol. 497, 33–40 (2017).Article 

    Google Scholar 
    14.Titlyanov, E. A., Yakovleva, I. M. & Titlyanova, T. V. Interaction between benthic algae (Lyngbya bouillonii, Dictyota dichotoma) and scleractinian coral Porites lutea in direct contact. J. Exp. Mar. Biol. Ecol. 342, 282–291 (2007).Article 

    Google Scholar 
    15.Carmichael, W. W. Cyanobacteria secondary metabolites—the cyanotoxins. J. Appl. Bacteriol. 72, 445–459 (1992).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    16.Ritson-Williams, R., Paul, V. J. & Bonito, V. Marine benthic cyanobacteria overgrow coral reef organisms. Coral Reefs 24, 629–629 (2005).ADS 
    Article 

    Google Scholar 
    17.Kuffner, I. et al. Inhibition of coral recruitment by macroalgae and cyanobacteria. Mar. Ecol. Prog. Ser. 323, 107–117 (2006).ADS 
    Article 

    Google Scholar 
    18.Kuffner, I. B. & Paul, V. J. Effects of the benthic cyanobacterium Lyngbya majuscula on larval recruitment of the reef corals Acropora surculosa and Pocillopora damicornis. Coral Reefs 23, 455–458 (2004).Article 

    Google Scholar 
    19.Ritson-Williams, R., Arnold, S. N. & Paul, V. J. The impact of macroalgae and cyanobacteria on larval survival and settlement of the scleractinian corals Acropora palmata, A cervicornis and Pseudodiploria strigosa. Mar. Biol. 167, 31 (2020).Article 

    Google Scholar 
    20.McClanahan, T. R. et al. Prioritizing key resilience indicators to support coral reef management in a changing climate. PLoS ONE 7, e42884 (2012).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    21.Cardini, U., Bednarz, V. N., Foster, R. A. & Wild, C. Benthic N2 fixation in coral reefs and the potential effects of human-induced environmental change. Ecol. Evol. 4, 1706–1727 (2014).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    22.Brocke, H. J. et al. Nitrogen fixation and diversity of benthic cyanobacterial mats on coral reefs in Curaçao. Coral Reefs 37, 861–874 (2018).ADS 
    Article 

    Google Scholar 
    23.Brocke, H. J. et al. High dissolved organic carbon release by benthic cyanobacterial mats in a Caribbean reef ecosystem. Sci. Rep. 5, 8852 (2015).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    24.Haas, A. F. et al. Global microbialization of coral reefs. Nat. Microbiol. 1, 1–7 (2016).Article 
    CAS 

    Google Scholar 
    25.Box, S. J. & Mumby, P. J. Effect of macroalgal competition on growth and survival of juvenile Caribbean corals. Mar. Ecol. Prog. Ser. 342, 139–149 (2007).ADS 
    Article 

    Google Scholar 
    26.Webster, F. J., Babcock, R. C., Keulen, M. V. & Loneragan, N. R. Macroalgae inhibits larval settlement and increases recruit mortality at Ningaloo Reef, Western Australia. PLoS ONE 10, e0124162 (2015).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    27.Barott, K. et al. Natural history of coral−algae competition across a gradient of human activity in the Line Islands. Mar. Ecol. Prog. Ser. 460, 1–12 (2012).ADS 
    Article 

    Google Scholar 
    28.Bonaldo, R. M. & Hay, M. E. Seaweed-coral interactions: variance in seaweed allelopathy, coral susceptibility, and potential effects on coral resilience. PLoS ONE 9, e85786 (2014).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    29.Rasher, D. B., Hoey, A. S. & Hay, M. E. Consumer diversity interacts with prey defenses to drive ecosystem function. Ecology 94, 1347–1358 (2013).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    30.Capper, A., Cruz-Rivera, E., Paul, V. J. & Tibbetts, I. R. Chemical deterrence of a marine cyanobacterium against sympatric and non-sympatric consumers. Hydrobiologia 553, 319 (2006).CAS 
    Article 

    Google Scholar 
    31.Clements, K. D., German, D. P., Piché, J., Tribollet, A. & Choat, J. H. Integrating ecological roles and trophic diversification on coral reefs: multiple lines of evidence identify parrotfishes as microphages. Biol. J. Linn. Soc. https://doi.org/10.1111/bij.12914 (2016).Article 

    Google Scholar 
    32.Cissell, E. C., Manning, J. C. & McCoy, S. J. Consumption of benthic cyanobacterial mats on a Caribbean coral reef. Sci. Rep. 9, 12693 (2019).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    33.Edwards, C. B. et al. Global assessment of the status of coral reef herbivorous fishes: evidence for fishing effects. Proc. Biol. Sci. 281, 20131835 (2014).CAS 
    PubMed 
    PubMed Central 

    Google Scholar 
    34.Goatley, C., Bonaldo, R., Fox, R. & Bellwood, D. Sediments and herbivory as sensitive indicators of coral reef degradation. Ecol. Soc. 21, 29 (2016).35.Robinson, J. P. W. et al. Habitat and fishing control grazing potential on coral reefs. Funct. Ecol. 34, 240–251 (2020).Article 

    Google Scholar 
    36.Mouillot, D. et al. Functional over-redundancy and high functional vulnerability in global fish faunas on tropical reefs. PNAS 111, 13757–13762 (2014).ADS 
    CAS 
    PubMed 
    Article 

    Google Scholar 
    37.Elmqvist, T. et al. Response diversity, ecosystem change, and resilience. Front. Ecol. Environ. 1, 488–494 (2003).Article 

    Google Scholar 
    38.Duperron, S. et al. New benthic cyanobacteria from Guadeloupe mangroves as producers of antimicrobials. Mar. Drugs https://doi.org/10.3390/md18010016 (2020).Article 

    Google Scholar 
    39.Bonaldo, R. M., Pires, M. M., Junior, P. R. G., Hoey, A. S. & Hay, M. E. Small marine protected areas in Fiji provide refuge for reef fish assemblages, feeding groups, and corals. PLoS ONE 12, e0170638 (2017).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    40.Ford, A. K. et al. Evaluation of coral reef management effectiveness using conventional versus resilience-based metrics. Ecol. Ind. 85, 308–317 (2018).Article 

    Google Scholar 
    41.Robinson, J. P. W. et al. Environmental conditions and herbivore biomass determine coral reef benthic community composition: implications for quantitative baselines. Coral Reefs 37, 1157–1168 (2018).ADS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    42.Capper, A. et al. Palatability and chemical defences of benthic cyanobacteria to a suite of herbivores. J. Exp. Mar. Biol. Ecol. 474, 100–108 (2016).CAS 
    Article 

    Google Scholar 
    43.Cruz-Rivera, E. & Paul, V. J. Chemical deterrence of a cyanobacterial metabolite against generalized and specialized grazers. J. Chem. Ecol. 33, 213–217 (2007).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    44.Bejarano, S. et al. The shape of success in a turbulent world: wave exposure filtering of coral reef herbivory. Funct. Ecol. 31, 1312–1324 (2017).Article 

    Google Scholar 
    45.Lefcheck, J. S. et al. Tropical fish diversity enhances coral reef functioning across multiple scales. Sci. Adv. 5, eaav6420 (2019).ADS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    46.Nagle, D. G. & Paul, V. J. Chemical defense of a marine cyanobacterial bloom. J. Exp. Mar. Biol. Ecol. 225, 29–38 (1998).CAS 
    Article 

    Google Scholar 
    47.Wilson, S. K., Graham, N. J., Pratchett, M. S., Jones, G. P. & Polunin, N. V. C. Multiple disturbances and the global degradation of coral reefs: are reef fishes at risk or resilient? Glob. Change Biol. 12, 2220–2234 (2006).ADS 
    Article 

    Google Scholar 
    48.Pratchett, M. S. et al. Effects of climate-induced coral bleaching on coral-reef fishes: ecological and economic consequences. Oceanogr. Mar. Biol. Ann. Rev. 46, 251–296 (2006).
    Google Scholar 
    49.Pratchett, M. S., Hoey, A. S., Wilson, S. K., Messmer, V. & Graham, N. A. J. Changes in biodiversity and functioning of reef fish assemblages following coral bleaching and coral loss. Diversity 3, 424–452 (2011).Article 

    Google Scholar 
    50.Potts, D. C. Suppression of coral populations by filamentous algae within damselfish territories. J. Exp. Mar. Biol. Ecol. 28, 207–216 (1977).Article 

    Google Scholar 
    51.Mumby, P. J. et al. Empirical relationships among resilience indicators on Micronesian reefs. Coral Reefs https://doi.org/10.1007/s00338-012-0966-0 (2012).Article 

    Google Scholar 
    52.Birrell, C. L., McCook, L. J. & Willis, B. L. Effects of algal turfs and sediment on coral settlement. Mar. Pollut. Bull. 51, 408–414 (2005).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    53.Wismer, S., Tebbett, S. B., Streit, R. P. & Bellwood, D. R. Spatial mismatch in fish and coral loss following 2016 mass coral bleaching. Sci. Total Environ. 650, 1487–1498 (2019).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    54.de la Morinière, E. C. et al. Ontogenetic dietary changes of coral reef fishes in the mangrove-seagrass-reef continuum: stable isotopes and gut-content analysis. Mar. Ecol. Prog. Ser. 246, 279–289 (2003).ADS 
    Article 

    Google Scholar 
    55.Komárek, J. A polyphasic approach for the taxonomy of cyanobacteria: principles and applications. Eur. J. Phycol. 51, 346–353 (2016).Article 
    CAS 

    Google Scholar 
    56.Xiao, X. et al. Use of high throughput sequencing and light microscopy show contrasting results in a study of phytoplankton occurrence in a freshwater environment. PLoS ONE 9, e106510 (2014).ADS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    57.Palinska, K. A. & Surosz, W. Taxonomy of cyanobacteria: a contribution to consensus approach. Hydrobiologia 740, 1–11 (2014).Article 

    Google Scholar 
    58.Li, X. et al. Factors related to aggravated Cylindrospermopsis (cyanobacteria) bloom following sediment dredging in an eutrophic shallow lake. Environ. Sci. Ecotechnol. 2, 100014 (2020).Article 

    Google Scholar 
    59.Taton, A., Grubisic, S., Brambilla, E., De Wit, R. & Wilmotte, A. Cyanobacterial diversity in natural and artificial microbial mats of Lake Fryxell (McMurdo Dry Valleys, Antarctica): a morphological and molecular approach. Appl. Environ. Microbiol. 69, 5157–5169 (2003).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    60.Knight, R. et al. Best practices for analysing microbiomes. Nat. Rev. Microbiol. 16, 410–422 (2018).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    61.Kim, M., Oh, H.-S., Park, S.-C. & Chun, J. Towards a taxonomic coherence between average nucleotide identity and 16S rRNA gene sequence similarity for species demarcation of prokaryotes. Int. J. Syst. Evol. Microbiol. 64, 346–351 (2014).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    62.Hoffmann, L. & Demoulin, V. Marine Cyanophyceae of Papua New Guinea. III. The genera Borzia and Oscillatoria. Bot. Mar. 36, 451–459 (1993).Article 

    Google Scholar 
    63.Engene, N. et al. Moorea producens gen. nov., sp. Nov. and Moorea bouillonii comb. nov., tropical marine cyanobacteria rich in bioactive secondary metabolites. Int. J. Syst. Evol. Microbiol. 62, 1171–1178 (2012).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    64.Engene, N. et al. Five chemically rich species of tropical marine cyanobacteria of the genus Okeania gen. nov. (Oscillatoriales, Cyanoprokaryota). J. Phycol. 49, 1095–1106 (2013).PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    65.Komarek, J., Kaštovský, J., Mares, J. & Johansen, J. R. Taxonomic classification of cyanoprokaryotes (cyanobacterial genera) 2014, using a polyphasic approach. Preslia 86, 295–335 (2014).
    Google Scholar 
    66.Wilmotte, A., Laughinghouse, H. D. I., Capelli, C., Rippka, R. & Salmaso, N. Taxonomic Identification of Cyanobacteria by a Polyphasic Approach. Molecular Tools for the Detection and Quantification of Toxigenic Cyanobacteria (Wiley, 2017).
    Google Scholar 
    67.Salmaso, N. et al. Diversity and cyclical seasonal transitions in the bacterial community in a large and deep perialpine lake. Microb. Ecol. 76, 125–143 (2018).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    68.Zubia, M. et al. Benthic cyanobacteria on coral reefs of Moorea Island (French Polynesia): diversity response to habitat quality. Hydrobiologia 843, 61–78 (2019).Article 

    Google Scholar 
    69.Bernard, C. et al. Appendix 2: Cyanobacteria Associated with the Production of Cyanotoxins. Handbook of Cyanobacterial Monitoring and Cyanotoxin Analysis 501–525 (Wiley, 2017). https://doi.org/10.1002/9781119068761.app2.
    Google Scholar 
    70.Moritz, C. et al. Status and Trends of Coral Reefs in the Pacific (Global Coral Reef Monitoring Network, 2018).
    Google Scholar 
    71.Smith, J. E. et al. Re-evaluating the health of coral reef communities: baselines and evidence for human impacts across the central Pacific. Proc. R. Soc. B Biol. Sci. 283, 20151985 (2016).Article 
    CAS 

    Google Scholar 
    72.Kelly, L. W. et al. Black reefs: iron-induced phase shifts on coral reefs. ISME J. 6, 638–649 (2012).CAS 
    PubMed 
    Article 

    Google Scholar 
    73.Bohnsack, J. A. & Bannerot, S. P. A stationary visual census technique for quantitatively assessing community structure of coral reef fishes. NOAA Technical Report NMFS 41, 21 (1986).74.Froese, R. & Pauly, D. FishBase. World Wide Web electronic publication. www.fishbase.orghttps://www.fishbase.org/.75.Heenan, A., Hoey, A. S., Williams, G. J. & Williams, I. D. Natural bounds on herbivorous coral reef fishes. Proc. R. Soc. B Biol. Sci. 283, 20161716 (2016).Article 

    Google Scholar 
    76.R Development Core Team. R: A Language and Environment for Statistical Computing. (R Foundation for Statistical Computing, 2019).77.Brooks, M. E. et al. glmmTMB balances speed and flexibility among packages for zero-inflated generalized linear mixed modeling. R J. 9, 378–400 (2017).Article 

    Google Scholar 
    78.Hartig, F. DHARMa: Residual Diagnostics for Hierarchical (Multi-Level/Mixed) Regression Models. R package version 0.3.3.0. (2020). http://florianhartig.github.io/DHARMa/79.Wickham, H. ggplot2: Elegant Graphics for Data Analysis (Springer, 2016).
    Google Scholar 
    80.Komárek, J. & Anagnostidis, K. Cyanoprokaryota 2.Teil: Oscillatoriales (Elsevier, 2005).
    Google Scholar 
    81.Quince, C., Lanzen, A., Davenport, R. J. & Turnbaugh, P. J. Removing noise from pyrosequenced amplicons. BMC Bioinform. 12, 38 (2011).Article 

    Google Scholar 
    82.Bolyen, E. et al. Reproducible, interactive, scalable and extensible microbiome data science using QIIME 2. Nat. Biotechnol. 37, 852–857 (2019).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    83.Ramos, V., Morais, J. & Vasconcelos, V. M. A curated database of cyanobacterial strains relevant for modern taxonomy and phylogenetic studies. Sci. Data 4, 170054 (2017).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    84.Katoh, K., Rozewicki, J. & Yamada, K. D. MAFFT online service: multiple sequence alignment, interactive sequence choice and visualization. Brief. Bioinform. 20, 1160–1166 (2019).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    85.Price, M. N., Dehal, P. S. & Arkin, A. P. FastTree 2: approximately maximum-likelihood trees for large alignments. PLoS ONE 5, e9490 (2010).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    86.Letunic, I. & Bork, P. Interactive tree of life (iTOL) v4: recent updates and new developments. Nucl. Acids Res. 47, W256–W259 (2019).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar  More

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    In situ recordings of large gelatinous spheres from NE Atlantic, and the first genetic confirmation of egg mass of Illex coindetii (Vérany, 1839) (Cephalopoda, Mollusca)

    Confirmation of species, using DNA analysisBecause the DNA of our sphere samples matches that of adult squid identified as I. coindetii from Norwegian waters we infer that the spheres are from I. coindetii. Much has been written about taxonomic difficulties in Illex. The COI tree comprises four clades of Illex, one of which clearly pertains to Illex argentinus (Castellanos, 1960). There are three other described species: Illex coindetii, Illex illecebrosus (Lesueur, 1821), and I. oxygonius Roper, Lu & Mangold, 1969. We labelled our clades A, B, and C, to indicate their correspondence with the findings of Carlini et al.32, and assume that each pertains to one of the described species of Illex. Carlini was unable to match species to clades, but Clade A not only contains the adults identified in this project as I. coindetii, but also contains specimens from the Mediterranean (DQ373941). Since I. coindetii is the only species of Illex known from the Mediterranean, this is further confirmation of the identity of Clade A, and thus our spheres, as Illex coindetii.Using citizen science from roughly 200 divers secured observations of 90 spheres, including rare tissue samples of four of them, thus enabling a molecular approach towards the first confirmation of egg masses in situ as those of the broadtail shortfin squid, Illex coindetii. Illex coindetii was named in honour of Dr. Coindet from Geneva in 185137. It took 180 years from the description of the adult to identification of its egg mass in the wild. To our knowledge no whole egg mass of Illex spp. has previously been reported from the wild, except by Adolf Naef, who reported on live ommastrephid embryos and paralarvae from Naples, Italy2. The embryos were pulled out of a floating spawn or floating egg mass, or as he describes «Fig. 1 und 2 sind aus einem flottierenden Laich gezogene Larven von Ommatostrephiden». These illustrations were later identified as Illex coindetii by Boletzky et al.26, studying egg development of I. coindetii in the laboratory, claiming «The general characteristics of the embryonic developement observed by us match the figures given by Naef (1923 : plts 9–12) of an unidentified egg mass of a member of the Ommastrephidae (Naef 1921)». However, no drawing of the «laich» was provided.Challenges collecting in situ materialHuge gelatinous spheres from squid are difficult to study in situ. They are rarely reported, and hard to sample. We have collected 90 sphere observations from ~ 35 years back (~ 1985 to 2019), from an area stretching from the Mediterranean Sea north to the Norwegian Sea, which gives a good illustration on sphere findings of ~ 2.6 sphere observations per year. In addition, the spheres most likely have a short-life span. Life span of spheres spawned and reared in aquaria (between 40 and 120 cm in diameter) of Todarodes pacificus (Steenstrup, 1880) is 5–7 days, with the smallest disintegrating first38.Sphere shape and sizeGelatinous egg masses of cephalopods vary in size and form among species. Some egg masses are spherical, but there are also examples of oblong structures39,40,41. Sphere size may be up to 4 m in diameter1,5,42. Ringvold and Taite (op. cit.) collected information on a total of 27 spheres recorded in European waters varying from 0.3 to 2 m in diameter, as also for the additional spheres from this study. The four spheres in our study, confirmed to belong to I. coindetii, measured between 0.5 and 1 m in diameter.Egg mass of another ommastrephid squid, Todarodes sagittatus, has yet to be found in situ. The species is known to be larger than Illex species, and egg mass is also most probably larger. The largest spheres recorded in our study measured up to 2 m in diameter, but none of these were sampled for molecular analysis, nor were pictures taken. It is uncertain whether they could belong to other species e.g., Todaropsis eblanae (Ball, 1841), Todarodes sagittatus or Ommastrephes sp..Dark streak through coreAlmost 60% of the spheres had a dark streak through the center. This feature might be ink, one important characteristic of cephalopods, produced by most cephalopod orders. The ink sac with its ink glands produces black ink containing melanin43. During fertilization, sperm are released—as well as possibly some ink. Spheres with or without ink may be a result of spheres beeing at different maturity stages1, where spheres with ink are freshly spawned. After a while, when embryos starts developing, the whole sphere, including the streak, will start to disintegrate.Some of us speculate that one function of the streak through the center might serve as visual mimics e.g. of a large fish in order to scare off predators. Other possible functions discussed are also if the streak/structure can be caused by a sphere strengthening structure which is denser or having a higher optical density than the sourrounding structure. A disadvantage with the streak is that it might reveal the whole transparent sphere in the water, visible to e.g. scuba divers.Function of the gelatinous matrixObservations in captivity3,44 showed that species within the genus Illex produce gelatinous egg masses while swimming in open water. Gel functions as a buoyancy mechanism that prevents eggs from sinking, and complete density equilibration requires many days under most conditions44. Such a buoyancy mechanism keeps pelagically spawned eggs of Illex in areas where temperatures are most optimal for embryonic development. Optimal environmental conditions will likely have a positive effect on survival of both hatchlings and paralarvae. Despite consistency in where spawning areas are found, interannual variability has been recorded in the main recruitment areas, which could be related to e.g. mesoscale eddies and/or affecting post-hatching dispersal45.Huge spheres are formed of mucus produced by the nidamental glands, situated inside the mantle cavity of the female46,47. When fully developed, hatchlings emit an enzyme which starts to dissolve the mucus. Eggs and embryos from our four spheres were covered in sticky gelatinous mass, except for a few specimens (from Arendal, collected 7 August, and Søgne) laying in the petri dish outside the sticky gel, in the surrounding sea water following the tissue sample, and might have been old enough to start producing such enzymes.When at hatching, Illex coindetii eggs are about 2 mm long26,48, in line with other ommastrephids12. The longest of our embryos (from Arendal, collected 7 August) measured ~ 2 mm, a developed embryo with long proboscis, mantle about ½ of total body length, as well as chromatophores, large eyes and funnel visible (Fig. 3). It could possibly be a hatchling.Abiotic factors and locationsThe success and duration of embryonic development is related to water temperature. All observations available to date indicate that successful embryonic development for I. coindetii takes ca. 10–14 days at 15 °C; this temperature corresponds to the median temperature value reported for Mediterranean Sea midwater48. Boletzky et al.26 reports on a temperature minimum above 10 °C. Spheres in the Mediterranean were observed in temperatures ranging between 14 and 24 °C. Watermass temperature for one sphere with recently fertilized eggs (Ålesund sample, embryos stage ~ 3) from Norway was 8 °C. It was also observed north of the existing known distribution range for I. coindetii, in the Norwegian Sea, at 43 m depth. Most spheres from Norway were observed from July and August, in water mass 10–14 °C, with maximum temperature at 18 °C.It is unknown whether some of the observed spheres had drifted to water layers unsuitable for the development of the eggs, and, eventually, would have died due to unfavourable abiotic conditions (e.g. transport outside the optimal temperature- or depth range for that particular species), but most likely they were in an area where they would survive. Higher occurrence of sphere sightings from 2017 to 2019, could be a combination of higher abundance of these squid in the area as well as increased knowledge regarding our Citizen Science Sphere Project, and thereby increased reports of observations.Illex coindetii may be considered as an intermittent spawner with a spawning season extending throughout the year, reaching a peak in July–August18.Our sphere observations from all areas were made from March to October: The earliest sphere which can be documented (to month) in the North Sea to date was observed 27 May (2001), and the last sphere was reported on 20 October (2019), coinciding with a study on adult Illex condetii from the North Sea where the spawning season has been suggested to be between spring and autumn49. However, our data show a peak of sphere observations from July to September (all areas combined), from July to August in Norway and from August to September in the Mediterranean Sea. The two recordings from Galicia in Spain, and Seiano in Italy, were the earliest recordings of the year, observed 24 March (in 2017 and 2019, respectively). For all areas combined, no observations during wintertime (November to February) have been recorded.Embryonic development and consistencies of spheresWe collected tissue mass of four different spheres of I. coindetii, and embryos in each sphere were at different developmental stages, ~ 3 to 30, according to Sakai et al.36 based on I. argentinus. The sphere walls of the four spheres were also of different consistencies (Table 2); from Ålesund sphere with recently fertilized eggs and firm, transparent sphere wall to Søgne and Arendal spheres (the latter collected 7 August) with developed embryos and disintegrating sphere walls. The remains of the Arendal sphere was hanging as a long «scarf» in the water. Experienced divers, who previously had seen a few spherical spheres, recognized this disintegrating sphere.Function of spheresOmmastrephidae fecundity is extremely high, and a single sphere may contain thousands to several hundred thousands of eggs41,50,51,52. The function of the spheres is protection and transport of the offspring by sea currents for paralarval dispersal. Inside these gelatinous structures, the eggs and newly hatched paralarvae are protected from predation by e.g. fish, parasite infection and infestation by crustaceans and protozoans during a first relative short period of their lives5,51. Bottom trawlers operate in spawning areas of squids, exposing them to a risk of egg loss, as also for our fisherman at Askøy, Norway, who caught a sphere in his trawl1,5.Scientific cruises and fisheryThe Institute for Marine Research in Norway started identification of cephalopods on their regular scientific cruises in 2013, but no Illex coindetii was recorded that year. However, data show increasing catches from 2014 to 2019 (unpublished). No spheres are reported from Norway in 2013, but between 1995 to 2010, and from 2015 to 2019, observations were made. Most observations are between 2017 and 2019, indicating more frequent squid visits/spawnings. This coincides with more frequent sphere observations from 2017 to 2019.The broadtail shortfin squid, Illex coindetii, is probably the most widespread species found on both sides of the Atlantic and throughout the Mediterranean Sea12. In the NE Atlantic, it has been reported from Oslofjorden, Norway (59°N);53 and the Firth of Forth, east Scotland54, southwards along the European and African coasts to Namibia, including Hollam’s Bird Island (24°S) and Cape Frio (18°S)55. For example, I. coindetii is periodically very abundant in coastal waters of the eastern North Atlantic off Scotland, Ireland and Spain, where it supports opportunistic fisheries. However, the oceanographic and biological factors that drive this phenomenon, are still unknown12.Illex coindetii is widely distributed throughout the Mediterranean Sea11, where it is caught commercially mostly by Italian trawlers, usually as a by-catch, but also by recreational fishing, by means of squid jigging. Annual Italian landings during the last five years have varied between two and three thousand tonnes, but with historical landings reaching numbers of more than eight thousand tonnes during the 1980s and 1990s (FAO 2019)15.In the North Sea, studies show that inshore squids (Alloteuthis subulata (Lamarck, 1798) and Loligo forbesii Steenstrup, 1856) are more abundant than short-finned squid (Illex coindetii, Todaropsis eblanae and Todarodes sagittatus), and I. coindetii is among the rarest ommastrephid species caught49,56. However, two recent studies (1) on summer spawning stock of Illex coindetii in the North Sea57 and (2) I. coindetii recorded from the brackish Baltic Sea58 suggest more frequent visits to this area. Reports on Illex coindetii from Norwegian waters are scarce, but it has been reported from Oslofjorden53, and recently as by-catch from Stavanger area, and by divers from Oslofjorden and Bergen. More

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    Highest risk abandoned, lost and discarded fishing gear

    Most problematic fishing methods based on ALDFG relative risksThis study presents the first quantitative assessment of gear-specific relative risks from ALDFG. Findings accounted for the: (a) derelict gear leakage rate; (b) fishing gear quantity indicators of catch and area of fishing grounds; and (c) adverse consequences from ALDFG. Maximum global conservation gains can be achieved through focusing ALDFG mitigation efforts on the fishing gears with the highest overall relative risk. Set and fixed gillnets and trammel nets, drift gillnets, gears using drifting and anchored FADs (tuna purse seines and pole-and-lines), and bottom trawls were the five most problematic gears on a global scale. This was followed by traps (fyke nets, pots, barriers, fences, weirs, corrals and pound nets).The overall RR score indicates a fishing gear’s relative degree of total adverse effects from ALDFG, accounting for the quantity of ALDFG produced by that gear (estimated from the ALDFG leakage rate and indices of fishing gear quantity of catch and area of fishing grounds), and the adverse consequences that result from ALDFG from that gear type relative to other gears. Globally, gillnets have the highest risks from ALDFG, while hand dredges and harpoons were least problematic.The focus of local management interventions to address problematic derelict fishing gear will be dictated by the specific context. Locally, adopting ALDFG controls following a sequential mitigation hierarchy and implementing effective monitoring, surveillance and enforcement systems are needed to curb derelict gear from these most problematic fisheries. This includes accounting for which fishing gears are predominant and the existing fisheries management framework. For example, a site may have pot and tuna purse seine anchored FAD fisheries. The purse seine fishery has a higher relative risk globally. However, a fisheries management system may have effective ALDFG preventive methods in place for this fishery, such as a high rate of detection and recovery of anchored FADs when they break from moorings, and minimization methods, such as prescribing the use of only non-entangling and biodegradable FAD designs to minimize adverse effects from derelict FADs35, 36. But there may be minimal measures in place to monitor and manage ALDFG from pots. In this hypothetical example, it would be a higher priority locally to improve ALDFG management for the pot fishery.Priority data quality improvementsThere are several priorities for data quality improvement to increase the certainty of future assessments. Given substantial deficits both in estimates of gear-specific quantity/effort and ALDFG rates, it is not yet possible to produce a robust contemporary estimate to replace the ca. five decades-old crude estimate of the magnitude of the annual quantity of leaked ALDFG4, 30. More robust estimates of ALDFG rates are needed for all gear types. Gear-specific estimates have low certainty due to small numbers of studies and sample sizes. Many compiled records estimate only one ALDFG component, typically only loss rates, and therefore may substantially underestimate total ALDFG rates. Most records are dated and may not accurately characterize contemporary rates. There is geographical sampling bias with estimates being primarily derived from the northern hemisphere. Furthermore, many estimates were derived from expert surveys (Supplementary Material Table S1), which have a higher risk of error and bias than approaches higher on the evidence hierarchy37. Substantially more primary studies with robust designs are needed.An expanded meta-analysis on gear-specific ALDFG rates is an additional priority, once sufficient sample sizes of robust studies accumulate. The statistical modeling approach used by Richardson et al.34 could be readily improved by using (1) a random-effects instead of a fixed effects structure to account for study-specific heterogeneity, and (2) a more appropriate model likelihood, such as zero-inflated Beta likelihood, to account for the zero values in the dataset38. Due to larger sample sizes and the number of independent studies, meta-analyses can produce estimates with increased accuracy, with increased statistical power to detect real effects. By synthesizing estimates from an assortment of independent, small and context-specific studies, pooled estimates from random-effects meta-analyses are generalizable and therefore relevant over diverse settings39. The strength of conclusions of hypotheses based on a single study can vary. This is because a single study can be context-specific, where true results may be affected by conditions specific to that single study, such as the species involved and environmental conditions, that cause the results from the single study to not be applicable under different conditions. A single study may also fail to find a meaningful result due to small sample sizes and low power. However, robust synthesis research, including meta-analysis, is more precise and powerful once a sufficient number of similar studies have accumulated, and therefore investing in more primary ALDFG studies is a high priority.For some gear types and fisheries, estimated ALDFG rates may overestimate adverse effects when gear that is abandoned, lost or even discarded does not become derelict because another fishing vessel continues to use the gear. For example, gear that is lost by theft remains in use. Macfadyen et al.4 explained that theft was likely a minor contribution to ALDFG, occurring, for instance, in inshore fishing grounds where static commercial fishing gear and recreational marine activities conflict. However, fishing gear theft may be prevalent in some developing country fisheries (e.g., Cambodian crab traps40). And, there is one gear type where theft has become a globally prevalent, routine and largely accepted practice: Tuna purse seine vessels routinely exchange satellite buoys attached to drifting FADs that they encounter at sea. The stolen FAD, lost by the previous vessel that had been tracking its position, remains in-use and not derelict, although it may eventually become derelict41, 42. Furthermore, because ALDFG leakage rates may be highest in illegal and unregulated fisheries4, if only legal fisheries are sampled, then this may produce underestimates. Thus, accounting for theft and illegal and unregulated fishing would increase the certainty of estimates of ALDFG leakage rates for some fishing gear types.The 20% ALDFG global production rate value used for anchored FADs by pole-and-line fisheries was likely an underestimate. We relied on a single value from the contemporary Maldives pole-and-line fishery’s government-owned and -managed network of anchored FADs. This fishery underwent a substantial reduction in anchored FAD loss rate, from 82 to 20%, by improving designs and a government incentive program that pays fishers to retrieve FADs when they break from their moorings35, 43. For comparison, describing Indonesia’s pole-and-line fishery’s anchored FADs, Widodo et al.44 stated: “Inaccuracy of number and position of FADs in the fishing ground are the outstanding issue facing by fisheries manager…This was largely the result of the current lack of effective systems of FAD registration and monitoring, and also because of the desire of fishing companies and vessel skippers to keep FADs position information confidential. [sic]”.Proctor et al.45, who estimated that between 5000 and 10,000 anchored FADs are used in Indonesian tuna fisheries, also reported a lack of accurate estimates of the numbers and locations of anchored FADs due to ineffective implementation of the government registration system and to high loss rates, including from storms, strong currents, vandalism, vessel collisions and wear and degradation of the FADs. Using the estimated rates of (1) Shainee and Leira43 that 82% of anchored FADs were lost per year prior to the Maldivian government’s incentives program, which might accurately characterize the Indonesian and other anchored FAD networks used by pole-and-line fisheries, and (2) the 20% loss rate value from Adam et al.35, the posterior mean = 0.506 (95% HDI: 0.15–0.84). Thus, 51% might have been a more appropriate estimate for a global ALDFG production rate for pole-and-line anchored FADs. The Maldivian and Indonesian pole-and-line fisheries, which combined supply over half of global pole-and-line catch, rely heavily on anchored FADs, as do several other smaller pole-and-line fisheries (e.g., Solomon Islands, segments of the Japanese pole-and-line fleet)35, 45,46,47,48.Units for ALDFG rates are highly variable. Records using different rates cannot be pooled for synthesis research29, 34. For example, some records reported rates of the percent of number of panels (sheets) or fleets (strings) of gillnets that were lost, while others reported the percent of the length or area of gillnets that were lost29. Similarly, for longline gear, some studies reported the percent of the length of the mainline, while others reported the percent of the number of branchlines/snoods that were lost34. Employment of agreed harmonized units for ALDFG rates are needed.Future assessments could use a ratio of ALDFG risk-to-seafood production to assess gear-specific relative risks locally and globally, similar to assessments of vulnerable fisheries bycatch by using bycatch-to-target catch ratios49. This would enable the assessment of risk from ALDFG to be balanced against meeting objectives of food security and nutritional health.Relationship between alternative indices with the quantity of fishing gearWe used gear-specific annual catch and area of fishing grounds as indicators of the relative global amount of each gear that is used annually as two terms in the model to assess gear-specific relative risks from ALDFG. However, the assumption of a linear relationship between these indices and gear quantity is questionable for similar reasons that have been raised with the relationship between various indices of effort (number of fishing hours, number of vessels, engine power, vessel length, gross tonnage, gear size, hold capacity, as well as kWh) and catch. For example, the ratio of catch from one set by an anchoveta purse seiner to the volume or weight of the gear is likely substantially different than for pots or driftnets. Not only is the relationship between catch and amount of gear variable by gear type and target species, there is also high variability within gear types—by fishery and within fisheries—due to the broad range of factors that significantly explain fishing efficiency per unit of nominal effort50, 51. Similarly, the relationship between catch weight and number of fishing operations varies substantially across gear types. For example, an industrial tropical tuna purse seine vessel might have a total catch of about 37 t per set on a drifting FAD27 while a tuna pole-and-line vessel catches about 1 t per fishing day52.Similarly, the relationship between the area of fishing grounds and amount of gear may vary substantially between gear types. A small number of vessels using a relatively small magnitude of active, mobile gear may have a much larger area of fishing grounds than a large number of vessels and shore-based fishers using a large amount of passive and static gears. For example, about 686 large-scale tuna purse seine vessels fish across the tropics53, while gillnets, which may be the most globally prevalent gear type, are used predominantly within 20 nm (37 km) of shore, most intensively in southeast Asia and the northwest Pacific54.Fishing effort has also been estimated using engine power as well as by using energy expended, such as in kilowatt-hours (kWh), the product of the fishing time and engine power of a fishing vessel, including non-motorized vessels55,56,57. We did not use these metrics for effort because the correlation between rate of production of ALDFG and vessel engine power or kWh, including of non-motorized vessels (1.70 million of the estimated global 4.56 million fishing vessels21), has not been explored. In general, vessel power and power per unit of fishing period largely distinguishes between mobile and passive gears, where the former (e.g., trawls, dredges), use substantially more vessel power per weight of catch than passive gears (traps, gillnets). Also, estimates using these fishing effort metrics used a small number of aggregated gear categories and extrapolated estimates primarily from sampled developed world fisheries (however, see56). These effort indices would also prevent inclusion of shore-based fishing methods.There have been recent gear specific estimates of effort, in units of time spent fishing and the estimated energy expended (fishing power * fishing time), using Automated Identification Systems (AIS) data, which are available for industrial fishing vessels, primarily using longlines, trawls and pelagic purse seines6, 58. AIS data provide coverage of the majority of large fishing vessels ≥ 24 m in overall length58. However, this accounts for only about 2% of the number of global fishing vessels (of an estimated 4.56 million global fishing vessels, about 67,800 are ≥ 24 m in length21).ALDFG monitoring, management and performance assessmentsA sequential mitigation hierarchy of avoidance, minimization, remediation and offsets can be applied to manage ALDFG29, 59. Referring to the three components of relative risk assessed by this study, avoidance and minimization of risks from ALDFG is achieved by reducing the ALDFG leakage rate, fishing effort, and/or adverse consequences from derelict gear. Remedial methods reduce adverse effects, such as reducing ghost fishing by reducing the duration that ALDFG remains in the marine environment1, 29, 60. In general, preventative methods are more cost effective than remedial methods—it is less expensive to prevent gear abandonment, loss and discarding than it is, for example, to detect and then disable or remove derelict gear61. Methods to prevent ALDFG include, for instance, spatially and temporally separating passive and mobile fishing gears, having bottom trawlers avoid features that could snag the net such as by using high-resolution seabed maps, tracking the real-time position of unattended fishing gears using various electronic technologies, and using gear marking to identify the owner and increase the visibility of passive gears. Furthermore, because some remedial methods, such as using less durable materials for fishing gear components, can reduce economic viability and practicality, preventative methods and remediation through quick recovery of ALDFG may be more effective as well as elicit broader stakeholder support29, 62.To assess the performance of global ALDFG management interventions against this study’s quantitative benchmark, substantial deficits in monitoring and surveillance of fisheries’ waste management practices must first be addressed1. Of 68 fisheries that catch marine resources managed by regional fisheries management organizations, 47 lack any observer coverage, half do not collect monitoring data on ALDFG, and surveillance and enforcement systems are rudimentary or nonexistent in many fisheries1, 63.Findings from this quantitative, global assessment of ALDFG risks guide the allocation of resources to achieve the largest improvements from preventing and remediating derelict gear from the world’s 4.6 million fishing vessels. With improved data quality and governance frameworks for fishing vessel waste management, including ALDFG, we can expect reductions in ecological and socioeconomic risks from derelict gear. More