Wiley

Frontiers in Ecology and The Environment

Published by Wiley and Ecological Society Of America

Online ISSN: 1540-9309

·

Print ISSN: 1540-9295

Journal websiteAuthor guidelines

Top-read articles

151 reads in the past 30 days

Sustainability of large language models—user perspective

June 2025

·

156 Reads

·

Shane Canavan

·

·

[...]

·

Download

81 reads in the past 30 days

(a) Number of studies using drones on birds per year of publication. The year 2023 (indicated by the dashed rectangle) is incomplete because extraction was performed on March 27 of that year. (b) Distribution of field sites across the 149 studies in which drones were used to monitor birds.
Steps of inclusion and exclusion of references in our meta‐analysis based on a PRISMA flow diagram.
Distribution of (a) bird species and (b) drone type in the 149 studies that used drones to monitor birds. Icons by Christina Petalas.
Recommendations for how to approach birds using drones. The given distances are estimated to result in an absence of flushing response 95% of the time, according to our meta‐analysis of 149 bird monitoring studies that employed drones. Artwork by Lauren Jackson.
Summary of the best-fitted binomial model predicting bird reactions to drones
A meta‐analysis of the impact of drones on birds

October 2024

·

861 Reads

·

1 Citation

Aims and scope


Known for clearly articulated, novel research, Frontiers in Ecology and the Environment publishes interdisciplinary, problem-oriented articles. Our applied, integrated science addresses current and emerging ecological and environmental issues. Our authors’ experience matters to us, and we provide personalized attention to every article.

Recent articles


Cultivating curiosity
  • Article
  • Publisher preview available

June 2025

Paul J CaraDonna

·

Nicholas N Dorian

·

Dylan T Simpson

·

Mark EK Dorf


We identified three main stakes corresponding to each stakeholder (in pink, blue, and green) concerning the interconnection between sport and wildlife. This schematic representation in a tripartite framework illustrates the assets that each of the three stakeholders (conservationists, fans, and sport organizations) can bring to one another. Their interests could align around the central figure of a wildlife species (here, a lion Panthera leo) used as an emblem of many sport organizations. Each stake unpacks into hypothetical links that are developed in the respective sections of the main text. Disclosure statement: the image of the lion was created with the assistance of Artificial Intelligence.
Professional sport organizations as potential champions of biodiversity conservation

June 2025

·

61 Reads

Biodiversity loss is a global crisis, human-driven species extinction rates are higher than ever before, and these rates are expected to worsen. This calls for new socioeconomic business models that could inspire societal transformations benefitting biodiversity conservation and restoration. The emblems of sport organizations are often articulated around the central figure of a wildlife species. Such species occupy an important part of the cultural space and can therefore serve as important flagship species for conservation through sport, particularly those most threatened with extinction. At the intersection of two hitherto unrelated realms (ie sport and conservation), there are potentially important synergies that are unique to the sport sector among three groups of stakeholders: professional team-sport organizations, fan communities, and biodiversity conservationists.


The conceptual and mathematical definitions of resistance consider the direction and magnitude of initial change in ecosystem process or function following disturbance. By this definition, resistance is the log‐normalized ratio of the peak initial negative or positive response to disturbance relative to pre‐disturbance or control values (Mathes et al. 2021).
Insect pest functional groups with ecological and economic consequences to temperate forests. Meristem feeders stunt or arrest tree growth and prompt deformities by causing shoot mortality (Asaro et al. 2003). Seed, cone, and/or fruit feeders diminish reproductive success (Bell and Clark 2016). Sap‐suckers or phloem‐feeders, such as the hemlock woolly adelgid, can cause tree mortality within 3–5 years following infestation, highlighting the gradual progression of many insect disturbances. Foliage feeders are limited to larvae of Lepidopterans and Hymenopterans and are typically generalists, feeding on a variety of host tree species (Elkinton et al. 2017). Defoliated trees may replace lost leaves during the same growing season, but consecutive outbreaks can lead to tree mortality (Campbell and Sloan 1977). Wood borers and bark beetles can devastate forest stands within a single year and are vectors for fungal diseases (Hicke et al. 2012). Illustration by Catherine McGuigan.
Wood production and carbon sequestration in (a) forests subjected to field‐simulated wood‐boring insect disturbance (b) or stand‐replacing clear‐cut harvesting followed by fire (c). Wood production increased following wood‐boring because residual vegetation grew more rapidly after disturbance, fully offsetting production losses. Despite increases in stand‐scale wood production, carbon sequestration declined as an influx of dead wood elevated decomposition and associated carbon emissions. In (a), means and 95% confidence intervals (CIs) appear as symbols and error bars, respectively. Sources: Gough et al. (2007); Haber et al. (2023). Illustrations by Catherine McGuigan.
Sequential years of compounding defoliation by spongy moth (Lymantria dispar) reduced stem growth resistance of impacted individuals in southern New England oak–hickory (Quercus–Carya spp) forests as leaf biomass and carbon fixation declined at the tree scale (Plotkin et al. 2021). Whether such tree‐level responses scale to affect stand‐scale wood production and carbon sequestration depends on a combination of factors, including disturbance severity, frequency of disturbance recurrence, and the quantity and growth of unaffected vegetation. Illustration by Catherine McGuigan.
Wood production resistance and structural diversity resistance track each other following simulated wood‐boring insect disturbance, demonstrating the coupled nature of structural and functional responses. The solid red line is 1:1, with the sign of individual values indicating the direction and magnitude of change in wood production or structural diversity following disturbance. Reproduced using data from Niedermaier et al. (2022). Illustrations by Catherine McGuigan.
Resist!: Sustaining forest carbon sequestration and wood production after insect disturbance

June 2025

·

7 Reads

Disturbances from insect pests threaten ecologically and economically important goods and services supplied by forests, including wood production and carbon sequestration. We highlight the factors that influence these services’ resistance, a term quantifying the initial response to disturbance. Insects inflict damage through a range of mechanisms, prompting distinct plant physiological responses that scale to influence ecosystem processes and, with time, goods and services. The degree and timing of tree mortality and defoliation affect the amount of residual vegetation available to support compensatory wood production and influence carbon sequestration by changing rates of detritus‐fueled decomposition. Compounding, or sequential, insect attacks may prime a forest for additional disturbance, further eroding wood production and carbon sequestration. Forest management practices that promote biological and structural diversity, and augment or retain limiting biological and nutrient resources, may buffer against the effects of insect pests on wood production and carbon sequestration.


Map of the 332 National Park Service (NPS) units (black circles) included in these analyses across the seven National Climate Assessment regions (groups of adjacent states with assigned colors) in the contiguous US, with associated illustrative national parks and preserves (photographs). Image credits: Acadia (Victoria Stauffenberg/NPS), Channel Islands (Christina Kennedy), Crater Lake (NPS), Everglades (Federico Acevedo/NPS), Grand Canyon (NPS), Great Smoky Mountains (NPS), Indiana Dunes (Jeff Manuszak/NPS), Tallgrass Prairie (Billy Robb/NPS), Yellowstone (Jacob W Frank/NPS).
Top panel (a): Mean projected change in climatic water deficit (CWD) and the uncertainty in that change for each park unit across seven National Climate Assessment regions. Each circle represents a single park unit, and shading represents the density of the data. The projected change (mean of the delta) and uncertainty (range of the deltas across climate models) are calculated as z‐scores, with the axes representing standard deviations away from the historical mean. Dashed lines at one standard deviation are included on both axes to aid in comparison across regions. Bottom panels (b and c): Modeled regional means (black circles), confidence intervals (gray shading), and comparison arrows for the (b) projected change in CWD and (c) uncertainty in future CWD. The comparison arrows are based on pairwise comparisons between all park units within a single region (alpha = 0.05). Non‐overlapping arrows indicate significant differences between regions.
Drought and deluge—opportunities for climate‐change adaptation in US national parks

In a changing climate, resource management depends on anticipating changes and considering uncertainties. To facilitate effective decision making on public lands, we regionally summarized the magnitude and uncertainty of projected change in management‐relevant climate variables for 332 national park units across the contiguous US. Temperature, frequency of extreme precipitation events, and drought exposure are all projected to increase within seven regions delineated in the US National Climate Assessment. In particular, the anticipated collective impacts of droughts and flooding events will lead to unique management challenges, including combinations of management actions that may seem inconsistent. Furthermore, uncertainty in the magnitude of change varied by region and climate variable considered, pointing to specific opportunities for prioritization, transferability, and innovation of climate adaptation regionally and at the park‐unit scale.


Conceptual framework for integrating rewilding into agricultural landscapes. By adopting a whole‐landscape perspective, the framework moves beyond the simplified view of having at the local scale either a mix of intensive farming and natural ecosystems (land sparing) or only extensive farming (land sharing). The space for nature recovery is defined by two axes: ecological integrity (y axis) and intensity of local land use (x axis). The rewilded agricultural landscape represents intermediate values along these axes, in contrast to the extremes of intensive farming and natural ecosystems. A combination of farming practices (precision, ecologically intensified, or extensive), on one side, and nearby separate rewilded land, on the other side, contribute to forming wilder, multifunctional agricultural landscapes. The dashed arrow from extensive farming denotes that moderate ecological integrity comes at the expense of crop production. The framework differentiates local‐scale management (in blue) from landscape‐scale management (in green). Ultimately, the multi‐scale management results in a rewilded agricultural landscape. The photographs illustrate representative examples (clockwise from top‐left): extensive cropland in central Spain; cropland restored by planting a mixture of native trees in central Spain; a nature reserve in the Páramos of Chingaza, in Colombia; an ecologically intensified coffee plantation shaded by Erythrina trees, a leguminous, natural fertilizer species, in Costa Rica; intensive vineyard in central Spain; and precision agriculture in Germany. All photographs by JM Rey Benayas except the example of intensified farming (Pixabay/clarrycola [CC0]).
A multi‐scale approach to integrating rewilding into agricultural landscapes

June 2025

·

19 Reads

Finding ways to improve the sustainability of modern agriculture by recovering nature in agricultural landscapes is critical for conserving biodiversity and enhancing human well‐being. Rewilding principles could be applied to any type of landscape, which raises the possibility of employing rewilding approaches in agricultural areas while maintaining some degree of food production therein. Moving beyond the simple dichotomy of land sparing versus land sharing, here we propose a multi‐scale approach that integrates rewilding principles into agricultural landscapes by combining the creation of wilder ecosystems in separate set‐aside recovered areas with the implementation of farming approaches that are more sustainable, such as precision farming, ecologically intensified farming, and extensive farming, in adjacent areas. Adoption of such approaches would allow for more biodiversity elements to persist within the agricultural matrix. We explain how this approach could support the three critical components of rewilded land—dispersal, trophic complexity, and stochastic disturbances—and create agroecological landscapes that are biodiverse, resilient, and functionally connected at multiple scales.


(a) Invasive plants suppress native competitors in their introduced environment. (b) Over time, some native plant, herbivore, and soil microbial populations may adapt to become stronger consumers of or competitors with the invasive. (c) When introduced in other areas, these adapted species have the potential to induce biological resistance to the invasive plant. Created in BioRender by S Clark in 2025: https://biorender.com/r38o889.
Inducing biological resistance to invasive plants using adapted native species as a potential management option is illustrated here with native herbivores. Panel (a) depicts the spatial extent of an invasive plant, with darker areas indicating older populations. Surveys of invasive plant populations (a) across their spatial and temporal range could help (b) identify native species that are stronger competitors with or consumers of the invasive. (c) The key then is to determine if the adapted native species has a greater suppressive effect on the invasive plant than other co‐occurring natives. If that is the case, then closely monitored distribution of adapted species (d) may facilitate coexistence between the invasive plant and the native community. Created in BioRender by S Clark in 2025: https://biorender.com/s75z232.
Inducing biological resistance to invasive plants with adapted native species

Invasive plants often benefit from a change in eco‐evolutionary context, escaping the herbivores, pathogens, and competing plants from their native range. Introduced into naïve native communities, invasive plants can spread rapidly, threatening native plant diversity and ecosystem functioning. Increasingly, studies have shown that native species sometimes adapt in response to the selection pressures imposed by an invasive plant. While researchers have periodically suggested using adapted native species in the management of invasive plants, the idea generally has not found its way to the field. Here, we (1) compare the concept to the more established practices of assisted migration, classic biological control, and microbiome engineering; (2) discuss some of the hurdles to practical implementation; and (3) outline directions for further research that would help expose the role of native adaptations in shaping the trajectory of plant invasions.




Number of papers on ecological integrity published in the journals Biological Conservation, Conservation Biology, Ecological Applications, Ecological Indicators, and Forest Ecology and Management. In (a), colors represent the cumulative number of papers that (1) are about ecological integrity (light), (2) are about ecological integrity and calculate one or more metrics (medium), and (3) include animal communities in these metrics (dark). (b) Breakdown by environment for papers that included animal communities in integrity metrics. “Multiple*” environments were the interface between an aquatic and riparian or marine and estuarine environment. Icons are from Microsoft PowerPoint (CC‐0 license).
Examples of using the functional ecology of animal communities to track the ecological integrity of ecosystems across the globe. We highlight examples from four common integrity components: structure, composition, function, and connectivity. For these and other studies monitoring integrity with functional traits, field‐measured traits and trait databases (eg AVONET, FishTraits) were used in conjunction with other standard monitoring protocols. Images are from Wikimedia Commons (CC‐0 license).
A worked example of monitoring animal communities for ecological integrity using bird community data from Colorado. (1) The combination of expanding data sources and statistical approaches leads to (2) an improved understanding of the functional composition of seed‐dispersing birds across a range of habitat conditions, which in turn can lead to (3) predictions of the integrity of seed‐dispersing bird communities given a range of land management decisions. Figure was created by Ana Miller‐ter Kuile and Jamie S Sanderlin. Bar graph icon is from streamlinehq.com (CC‐0 license). Vector images of birds and trees were created by Jamie S Sanderlin. In (2), horizontal lines within boxes depict median values, boxes represent the interquartile range (25th–75th percentiles), whiskers (vertical lines) represent 1.5×interquartile range, and solid circles depict outliers.
Functionalizing ecological integrity: using functional ecology to monitor animal communities

May 2025

·

64 Reads

·

1 Citation

Ecological integrity—the degree to which an ecosystem supports ecological structure, composition, diversity, function, and connectivity typical of natural conditions—has been a guiding principle in ecosystem monitoring around the world. However, in terrestrial ecosystems, integrity‐based monitoring often excludes animal communities, even though they are critical drivers of integrity. Methodological advances in monitoring and data science have made it easier to document animal communities. We highlight examples of these advances and how they remove barriers to adopting animal‐specific integrity metrics. We then illustrate how describing animal communities in terms of functional ecology, which has also undergone substantial development over the past several decades, can provide a generalizable approach to incorporating animal communities into integrity‐based monitoring across taxa and ecosystems. Incorporating animal communities into ecological integrity monitoring is a vital step toward understanding how human‐driven change, restoration, and conservation shape terrestrial ecosystems worldwide.


The number/taxon (a), region of origin (b), introduction pathway (c), time since introduction (d), and provincial distribution (e) of invasive alien species (IAS) in China. In (b), colors indicate the continental origins (native ranges) of species introduced into China. The greatest width of a given chord within the upper semicircle represents the number of species originating per continent (including unknown), and the number outside the perimeter of the lower semicircle displays the cumulative value of the frequency of species introduced from all continents (note that some species have multiple origins). In (c), intentional introduction includes pathways of release in nature and escape from confinement, unintentional introduction involves transport of contaminants or stowaways, and natural spread refers to species dispersal through interconnected corridors or other unaided pathways (Scalera et al. 2016). The map in panel (e) includes mainland China and nearby islands. Animal and plant silhouettes in (a) courtesy of PhyloPic (www.phylopic.org/images, CC0 1.0 Universal).
Examples of projects on the control and eradication of invasive alien species in China. Site locations denoted by red circles in inset maps. (a) Removal of common water hyacinth Eichhornia crassipes in Shanghai (image credit: Yucheng Lyu). (b) Precise chemical control of fire ant Solenopsis invicta in Sichuan (image credit: Zhendong Song). (c) Biocontrol of ragweed Ambrosia artemisiifolia with leaf beetles in Guangxi (image credit: Zhongshi Zhou). (d) Removal of cordgrass Spartina alterniflora along the eastern coast (image credit: Hanzhong Liu).
Proposed priorities for the improved management of invasive alien species in China. Priorities of each issue are assigned based on their universality, urgency, and novelty. These priorities are not presented in hierarchical order because they must be conducted simultaneously and may be subject to further scrutiny, debate, and enhancement.
How can China curb biological invasions to meet Kunming‐Montreal Target 6?

To meet Kunming‐Montreal Target 6 of the Convention on Biological Diversity (CBD), we argue that more comprehensive measures are needed to manage invasive alien species (IAS), which is especially true for China, given that it is undergoing an unprecedented wave of invasions due to its rapid development. Here, we consider the status of IAS in China, evaluate China's ongoing countermeasures against IAS, and provide recommendations for improving management. In total, 802 IAS have been identified in China. Facing the growing threats of IAS, China has made progress in IAS management, but more stringent and thorough measures are still required. In addition to improving legislation and governance, China should strengthen transdisciplinary and proactive research, implement more comprehensive prevention and control actions against IAS, and enhance international cooperation and translational education. By creating a model for IAS management that other countries can follow, China's efforts can contribute substantially to the CBD's Kunming‐Montreal 2030 Global Targets.


Key components of solutions‐oriented environmental research that are supported by activities and reflexive processes, such as those listed in Table 1.
Teams can represent socio‐environmental systems visually in various ways, which help them develop a shared understanding of system components and important relationships. Shown are examples from the literature: (a) causal diagram of human–forest interactions generated by scientists and community members in the Philippines (diagram modified from Olabisi [2010], CC BY‐SA 3.0; background image: Adobe Stock/Glebstock); (b) network diagram to depict a social–environmental system of forest patches, clans, and their different interrelationships in an agricultural landscape in southern Madagascar (reproduced with permission from Bodin and Tengö [2012]); (c) diagram depicting the cascading effects of climate change on a socio‐environmental system involving fisheries and people in the North Pacific (reproduced from Bograd et al. [2019], CC BY 4.0). Acronyms in panel (c): KE (Kuroshio Extension), MLD (mixed layer depth).
A study of the Baltic Cod fishery collapse by Lade et al. (2015) illustrates research to understand the interacting environmental and social factors causing an environmental problem (reproduced with permission from Lade et al. [2015]). Arrows indicate direction of factor influences; smaller text indicates external drivers. The authors combined quantitative fisheries data with qualitative data on the social drivers and used generalized quantitative modeling (Lade and Niiranen 2017) to identify factors influencing fisher decisions to keep fishing even when catches were low. Hertz et al. (2024) used the same example to illustrate how different research approaches (eg methods, theories, causal reasonings) common to different disciplines can affect conclusions on the types of interventions. Acronym: CPUE (catch per unit effort).
A stepwise process for actionable environmental science research

May 2025

·

33 Reads

Scholars have long recognized the social dimensions of environmental problems. Environmental scientists have responded by increasingly focusing on the interactions between nature and social dynamics. This helps reveal problematic interactions that cause environmental challenges, many of which impact human well‐being. Research teams that include environmental and social scientists engaging with diverse stakeholders can use many available tools to ask how changing a factor pivotal to problematic interactions influences environmental and social outcomes. When the research also includes identifying actions targeting those interactions and identifying those who can implement the actions, the research is most likely to lead to positive outcomes in the long term. This is especially true when researchers link changes to improving a given ecosystem service. Changes can not only involve adapting natural resource policies but also involve altering attitudes and beliefs. We describe a stepwise process that eases the path toward such actionable environmental science by researchers.




Juvenile salmonids traverse saltwater environments to inhabit non‐natal drainages among Deep Creek, West Twin River, and East Twin River freshwater systems along the Olympic Peninsula, in western Washington State. This schematic highlights empirically observed paths of two juvenile coho (Oncorhynchus kisutch, orange and purple) and one juvenile Oncorhynchus mykiss (yellow) that made complex movements among drainages over periods of 203 days, 305 days, and 241 days, respectively. Numbers track individuals’ chronological detection sequences. Arrows indicate movement paths among drainages, with dashed line arrows showing additional details of individuals that moved back and forth between the East Twin and West Twin Rivers. For presentation purposes, points and arrows are staggered vertically, distances between streams are compressed, and the bottom of the figure points north. Image credit: Su Kim.
Juvenile movements among drainages of the Klamath River, Redwood Creek, and Humboldt Bay systems, in northern California. Circles indicate detections and lines connect detections of the same individuals. Note that lines are “as the crow flies” rather than “as the fish swims” and are randomly colored to improve discernment among individuals. Thick pink and purple lines highlight the greatest distance between two detections and an instance of a juvenile that moved back and forth between drainages, respectively.
of juvenile salmonid movements among drainages (D#) in Washington State. (a) Sankey diagram showing the paths and prevalence of juvenile movements. Node colors indicate the drainage where individuals were detected and arcs flow to the next drainage where individuals were detected. Thicker lines indicate more individuals. n indicates the total number of individuals represented. x axes indicate sequential order of movements over time. y axes arbitrarily spread lines to improve their visibility. (b) Proportion of juveniles that moved from one drainage to another. x axes indicate where juveniles departed and colors indicate where juveniles arrived. Note that (a) shows values in absolute terms whereas (b) shows proportional movements that account for differences among drainages in the number of juveniles that were redetected after tagging.
Juvenile salmonids traverse coastal meta‐nurseries that connect rivers via the sea

April 2025

·

112 Reads

Conventionally, juvenile salmonids are thought to migrate unidirectionally from freshwater systems to marine systems and therefore only inhabit natal drainages. Although scattered evidence suggests juveniles can move bidirectionally between freshwater rivers and the ocean, including into non‐natal drainages, such movements have never been documented with high replication. Here, we detected hundreds of movements of juvenile salmonids between drainages that involved 0–22% of cohort emigrants in Washington State and California. Individuals moved up to nine times and between drainages up to 70 km apart. These findings reveal a life‐history type of salmonids whose remarkably complex migrations have gone unnoticed. Implicitly, juveniles may use any coastal freshwater habitat accessible from the sea and may not descend from spawning populations of drainages they inhabit. Consequently, typical conservation focused on natal drainages may overlook freshwater habitat elsewhere. A concept of coastal areas as meta‐nurseries formed by multiple watersheds connected by the sea may accurately describe anadromous species’ habitat options and better inform management.



The approximate proportions of time spent by workshop participants discussing certain topics within each of the three themes—Engage, Heal, and Reconcile—during the two‐day Elevating Indigenous Knowledges in Ecology workshop at the Ecological Society of America's 2022 Annual Meeting. Image created by J Gazing Wolf in Microsoft Word.
A path to reconciliation between Indigenous and settler–colonial epistemologies

April 2025

·

41 Reads

There is a movement across settler–colonial institutions of education and research to engage with Indigenous Peoples and Knowledges. Many settler and Indigenous governments are pursuing pathways to move forward together to address global problems such as climate change. However, given the pervasive history of exploitation and displacement of Indigenous communities, this development has caused some concern among Indigenous leaders and scholars. At the 2022 Annual Meeting of the Ecological Society of America (ESA) in Montreal, Canada, the Traditional Ecological Knowledge Section of the ESA hosted a 2‐day workshop. This gathering of 21 Indigenous environmental scientists included scholars from across the career and professional spectrum. By consensus, workshop participants identified three emergent themes—Engage, Heal, and Reconcile—that provide a pathway toward reconciliation between Indigenous and settler–colonial ways of knowing. This path allows for an ever‐greater sharing of institutional resources and power toward a co‐equal interfacing of Indigenous Knowledges and settler science.


Integration of research on climate change, biological invasions, and diseases (left) can help not only to identify the likely effects of climate change on invasion‐related wildlife diseases, as captured in the classic epidemiological triad (middle), but also to develop appropriate policy and management actions (right), which currently are siloed and focus only on single aspects: for instance, climate‐specific policies by the UN Framework Convention on Climate Change (UNFCCC), invasion‐specific regulations by the European Union (EU) and the US, and disease‐specific policies by the World Health Organization (WHO) and the World Organisation for Animal Health (WOAH).
Climate‐change phenomena, such as rising temperatures and extreme weather events, can affect wildlife diseases by altering various infection‐related traits of parasites (solid circles) and hosts/vectors (ovals and triangle), as well as mediating the impact of facilitator and inhibitor species (crosses) on parasite transmission. Thermometer and cloud icons designed by OpenMoji.org (CC BY‐SA 4.0).
The four stages of the invasion process—transport, introduction & establishment, spread, and impact—for parasites, hosts, and vectors, with examples of the mechanisms through which climate change can affect invasion‐related wildlife diseases at each stage. See main text for details. Thermometer and cloud icons designed by OpenMoji.org (CC BY‐SA 4.0).
Potential implications of climate‐change effects on invasion‐related diseases for research gaps and management options, sorted by the different stages of the invasion process for parasites, hosts, and vectors. Thermometer and cloud icons designed by OpenMoji.org (CC BY‐SA 4.0).
Integrating climate change, biological invasions, and infectious wildlife diseases

April 2025

·

181 Reads

Climate change is likely to affect infectious diseases that are facilitated by biological invasions, with repercussions for wildlife conservation and zoonotic risks. Current invasion management and policy are underprepared for the future risks associated with such invasion‐related wildlife diseases. By considering evidence from bioclimatology, invasion biology, and disease research, we illustrate how climate change is anticipated to affect disease agents (parasites and pathogens), hosts, and vectors across the different stages of invasions. We highlight the opportunity to integrate these disciplines to identify the effects of climate change on invasion‐related wildlife diseases. In addition, shifting to a proactive stance in implementing management and policy, such as by incorporating climate‐change effects either into preventative and mitigation measures for biosecurity or with rapid response protocols to limit disease spread and impacts, could help to combat future ecological, economic, and human health risks stemming from invasion‐related wildlife diseases.




Conceptual model of hypotheses. This research determines whether disturbance history (i) predicts current forest composition and structure and (ii) quantifies patterns of forest inequity across racial groups. Image credit: Galen Pejeau.
Species composition and structure was different across three patch histories—novel, regrowth, and remnant—in core plots (left) but not in edge plots (right). (a) Species composition across patch histories was defined using non‐metric multidimensional scaling (NMDS) ordination. (b and c) Structural differences were identified using analysis of variance (ANOVA) on two plot‐based and four aerial lidar (light detection and ranging)‐based metrics. Statistical significance is indicated as follows: *P < 0.05, **P < 0.01, and ***P < 0.001. Horizontal lines within boxes depict median values, boxes represent the interquartile range (25th–75th percentiles), whiskers (vertical lines) represent 1.5×interquartile range, and solid circles depict outliers.
Distribution of racial groups and forest patches with different histories was not uniform across the Chicago region. Areas with higher percentages of White residents had greater extents of forest cover, dominated by remnant forests (top); however, the ratio of edges and cores was relatively even across the racial gradient (bottom). Shading denotes 95% confidence intervals.
Ecological and developmental history impacts the equitable distribution of services

March 2025

·

53 Reads

·

1 Citation

The ecological and developmental history of the Chicago, Illinois, region has affected the current distribution of forests therein. These same factors, along with systemic and long‐lasting racial segregation, have shaped the distribution of the urban populations that benefit from the ecosystem services provided by urban forests. This study demonstrates that forest patch history is related to forest attributes like tree species composition, tree density, canopy height, and structural heterogeneity—all of which are important predictors of a forest's ability to provide ecosystem services. However, this effect of forest history was only seen in forest cores, as forest edges were similar regardless of patch history. We also found that forests in minoritized communities tended to be less able to support high levels of ecosystem services. This research indicates that, when improving green equity, it is important to consider the variable capacity of forests to provide ecosystem services.


Nine recommendations that can be adopted to help ensure built marine infrastructure reduces impacts to and potentially supports natural habitats. These recommendations integrate understanding from ecology, economics, sociology, engineering, and other fields to develop a new paradigm of ocean management. Illustration by Alex Boersma.
Recommendations for built marine infrastructure that supports natural habitats

March 2025

·

180 Reads

The extent of built marine infrastructure—from energy infrastructure and ports to artificial reefs and aquaculture—is increasing globally. The rise in built structure coverage is concurrent with losses and degradation of many natural habitats. Although historically associated with net negative impacts on natural systems, built infrastructure—with proper design and innovation—could offer a largely unrealized opportunity to reduce those impacts and support natural habitats. We present nine recommendations that could catalyze momentum toward using built structures to both serve their original function and benefit natural habitats (relative to the status quo, for example). These recommendations integrate functional, economic, and social considerations with marine spatial planning and holistic ecosystem management. As the footprint of the Anthropocene expands into ocean spaces, adopting these nine recommendations at global scales can help to ensure that ecological harm is minimized and that, where feasible, ecological benefits from marine built structures are accrued.


Influence of introduced, naturalized, rewilding, recently (re)colonized, and extirpated species on native bird diversity. Bar height indicates the increase in native (a) functional diversity and (b) phylogenetic diversity when adding an individual introduced, naturalized, rewilding, recently (re)colonized, or extirpated species to native assemblages of species, standardized to vary from 0 to 1. Colors represent different species groups (see key). (c) Two‐dimensional representation of the overlap in five‐dimensional trait space. Different colors represent different species groups: native (gray, full volume ~92 SD⁵), introduced (yellow, full volume ~10 SD⁵), naturalized (turquoise, full volume ~5 SD⁵), rewilding (purple, full volume ~6 SD⁵), recent (re)colonists (blue, full volume ~6 SD⁵), and extirpated (red, full volume ~0.4 SD⁵). Hypervolumes for each group of species were constructed from five z‐transformed traits: log10 (body mass), log10 (clutch size), log10 (generation length), diet, and foraging strata. Units for the unique and overlapping fractions are expressed as SD⁵ (see main text). Bird silhouettes (www.phylopic.org, CC0 1.0 Public Domain) depict examples of different species groups.
Influence of introduced, naturalized, rewilding, and extirpated species on native mammal diversity. Bar height indicates the increase in native (a) functional diversity and (b) phylogenetic diversity when adding an individual introduced, naturalized, rewilding, or extirpated species to native assemblages of species, standardized to vary from 0 to 1. Colors represent different species groups (see key). (c) Two‐dimensional representation of the overlap in five‐dimensional trait space. Different colors represent different species groups: native (gray, full volume ~20 SD⁵), introduced (yellow, full volume not available as the number of species is less than the number of traits), naturalized (turquoise, full volume ~9 SD⁵), rewilding (purple, full volume ~ 0.3 SD⁵), and extirpated (red, full volume ~3 SD⁵). Hypervolumes for each group of species were constructed from five z‐transformed traits: log10 (body mass), log10 (litter size), log10 (generation length), square root (habitat breadth), and diet. Units for the unique and overlapping fractions are expressed as SD⁵ (see main text). Mammal silhouettes (www.phylopic.org, CC0 1.0 Public Domain) depict examples of different species groups.
Intentional and unintentional changes to avian and mammalian diversities in the UK

March 2025

·

81 Reads

Rewilding is emerging as a promising restoration strategy to tackle the challenges posed by global change and maintain natural ecosystems and their biodiversity. However, rewilding has also been criticized for the absence of a consistent definition and insufficient knowledge about its possible outcomes. Here, we explored the effects of rewilding on filling functional gaps created by the extirpation of native species. We contrasted rewilding with three other mechanisms for change in community composition—species extirpation, species introduction, and unassisted colonization—in terms of their impacts on changes in avian and mammalian diversity in the UK. We found that (i) while rewilding increases functional diversity most on average, introduced/naturalized birds contribute more functional uniqueness to native functional space than other groups of birds; and (ii) changes in functional diversity associated with “rewilded” organisms were species‐dependent and idiosyncratic. Our results suggest that although rewilding can expand or infill native functional trait space to some extent, such effects require careful assessment.


Local giant panda populations and five prospective scenarios for habitat restoration. (a) Satellite imagery showing the location of the Sichuan portion of the Giant Panda National Park (GPNP) in China (imagery from Google Earth; data: SIO, NOAA, US Navy, NGA, GEBCO, Landsat/Copernicus, IBCAO; © 2024 Google). (b) Geographic range of 13 discrete local giant panda populations within the Sichuan portion of the GPNP. Abbreviations for the local giant panda populations: QL_F: Qinling_F; MS_J: Minshan_J; MS_G: Minshan_G; MS_K: Minshan_K; MS_L: Minshan_L; QLS_A: Qionglaishan_A; QLS_B: Qionglaishan_B; QLS_C: Qionglaishan_C; QLS_D: Qionglaishan_D; DXL_A: Daxiangling_A; DXL_B: Daxiangling_B; XXL_A: Xiaoxiangling_A; XXL_B: Xiaoxiangling_B. (c) Illustrations depicting the five scenarios, labeled (i) through (v).
Habitat suitability under the five prospective scenarios for habitat restoration. (a) Differences in habitat suitability index (HSI) under the five scenarios (i) through (v) (Figure 1c) as compared to the baseline (o) for giant pandas. Abbreviations for the local giant panda populations are the same as in Figure 1. (b) Comparison of suitable habitat area of giant pandas within their local population ranges under the five scenarios (i) through (v) relative to the baseline (o). Violin plot width corresponds to the frequency of data points. Horizontal lines within boxes depict median values, boxes represent the interquartile range (25th–75th percentiles), and whiskers (vertical lines) represent 1.5×interquartile range. Significant differences: *P < 0.05; non‐significant (ns) differences: P ≥ 0.05. (c) Change in suitable habitat area of the 31 sympatric species within local giant panda population ranges under the five scenarios (i) through (v) as compared to the baseline (abbreviated species names appear along the circumference; for more details, see Yang et al. [2024]). The colored bars and error bars denote means and standard errors, respectively.
Species diversity indices among the five prospective scenarios for habitat restoration. (a–c) Differences in species richness (SR), phylogenetic diversity (ses.MPD), and functional diversity (ses.MFD) within local giant panda population ranges under the five scenarios (i) through (v) (Figure 1c) as compared to the baseline state (o). Abbreviations for local giant panda populations are the same as in Figure 1. (d–f) Comparison of these three indices under the five scenarios (i) through (v) relative to the baseline state (o). Violin plot width corresponds to the frequency of data points. Horizontal lines within boxes depict median values, boxes represent the interquartile range (25th–75th percentiles), whiskers (vertical lines) represent 1.5×interquartile range, and solid circles depict outliers. Significant differences: *P < 0.05, **P < 0.01, and ***P < 0.001; non‐significant (ns) differences: P ≥ 0.05.
Restoration of giant panda habitat requires balancing single‐ and multi‐species benefits

March 2025

·

160 Reads

·

1 Citation

Efforts to restore habitat for wildlife often target single species, with limited consideration of the potential benefits provided to sympatric species. On the basis of range‐wide data from the Fourth National Giant Panda Survey and infrared camera trapping, we used species distribution models to project the outcomes of five habitat restoration scenarios—designed to benefit giant pandas (Ailuropoda melanoleuca)—for giant pandas as well as for sympatric birds and mammals. Scenario outcomes, particularly those involving the conversion of plantation forests and shrublands into suitable forests, demonstrated a significant enhancement in giant panda habitat suitability, but with contrasting effects for sympatric species. Moreover, while restoration of giant panda habitat may enhance species richness and functional diversity, especially when shrublands are converted into forests, such action could also reduce phylogenetic diversity. Our findings suggest that single‐species habitat restoration may have negative outcomes for sympatric species, highlighting the need to consider trade‐offs between focal and non‐focal taxa.


(a) Map of the study area with elevation and the survey locations for the Sierra Nevada bioregion. (b–k) The indicator species included in this study (with image credit and Macaulay Library unique identifier): (b) fox sparrow (Passerella megarhyncha) (Connor Cochrane, ML417831361); (c) yellow warbler (Setophaga petechia) (Bradley Hacker, ML102888141); (d) black‐backed woodpecker (Picoides arcticus) (Vladimir Pravosudov, ML474401111); (e) hairy woodpecker (Leuconotopicus villosus) (Aidan Brubaker, ML450485851); (f) mountain quail (Oreortyx pictus) (Shailesh Pinto, ML586116811); (g) California spotted owl (Strix occidentalis occidentalis) (Danny Hofstadter); (h) hermit warbler (Setophaga occidentalis) (Marky Mutchler, ML438636841); (i) olive‐sided flycatcher (Contopus cooperi) (Michael Stubblefield, ML465414131); (j) acorn woodpecker (Melanerpes formicivorus) (Steve Tucker, ML167275911); and (k) American goshawk (Astur atricapillus) (Eric Tipton, ML384343761). Species photos with solid borders are designated USDA Forest Service indicator species; species photos with dashed borders were selected for this study.
Full results for California spotted owl and black‐backed woodpecker across the Sierra Nevada bioregion. (a and b) Comparison of posterior distributions of scaled covariate estimates and widely applicable information criterion (WAIC) for the forest model (top distributions) and the forest+fire model (bottom distributions) for (a) California spotted owl and (b) black‐backed woodpecker; 95% credible intervals (CIs) are denoted by the light‐colored sections and 50% CIs by the dark‐colored sections. (c and d) Maps of predicted occupancy (left) and standard deviation (right) for both species across the bioregion. (f) Examples of large fires in the Sierra Nevada bioregion over the past 10 years and estimated occupancy of (e) California spotted owl and (g) black‐backed woodpecker in relation to fire footprints. Image credits are the same as in Figure 1.
Interpolated occupancy estimates across the Sierra Nevada bioregion for (a) acorn woodpecker, (b) fox sparrow, (c) hairy woodpecker, (d) hermit warbler, (e) mountain quail, (f) American goshawk, (g) olive‐sided flycatcher, and (h) yellow warbler. Posterior distributions of occupancy parameter estimates and maps of error for interpolated occupancy can be found in Appendix S1: Figure S1. Image credits are the same as in Figure 1.
Bioregional‐scale acoustic monitoring can support fire‐prone forest restoration planning

March 2025

·

246 Reads

In many forests globally, resilience‐focused restoration is necessary to prevent fire‐driven regime shifts. However, restoration planning is challenged by limited resources for monitoring biodiversity responses to management intervention and to natural disturbances. Bioregional‐scale passive acoustic monitoring, when combined with automated species identification tools and management‐relevant habitat data, can be a tractable method to simultaneously monitor suites of complementary indicator species and rapidly generate species‐specific information for resource managers. We demonstrate these methods by mapping the occurrence of ten avian indicator species while examining the impact of fire history on patterns of occurrence across 25,000 km² of California's Sierra Nevada mountains. Monitoring complementary indicator species with rapidly developing bioacoustics technology and relating their occurrence to policy‐ready habitat metrics have the potential to transform restoration planning by providing managers with high‐resolution, ecosystem‐scale information that facilitates adaptive management in an era of rapid environmental change.



Journal metrics


10.0 (2023)

Journal Impact Factor™


15%

Acceptance rate


18.3 (2023)

CiteScore™


5 days

Submission to first decision


2.727 (2023)

SNIP


$3,970.00 / £2,650.00 / €3,310.00

Article processing charge

Editors