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The megabiota are disproportionately important for biosphere functioning

Abstract

A prominent signal of the Anthropocene is the extinction and population reduction of the megabiota—the largest animals and plants on the planet. However, we lack a predictive framework for the sensitivity of megabiota during times of rapid global change and how they impact the functioning of ecosystems and the biosphere. Here, we extend metabolic scaling theory and use global simulation models to demonstrate that (i) megabiota are more prone to extinction due to human land use, hunting, and climate change; (ii) loss of megabiota has a negative impact on ecosystem metabolism and functioning; and (iii) their reduction has and will continue to significantly decrease biosphere functioning. Global simulations show that continued loss of large animals alone could lead to a 44%, 18% and 92% reduction in terrestrial heterotrophic biomass, metabolism, and fertility respectively. Our findings suggest that policies that emphasize the promotion of large trees and animals will have disproportionate impact on biodiversity, ecosystem processes, and climate mitigation.

Introduction

Perhaps the most conspicuous aspect of the diversity of life on the planet is the enormous range of the diversity of sizes of organisms. Indeed, large animals and trees (such as elephants, rhinos, whales, and large trees such as redwoods, sequoias, and mountain ash) are also often seen as charismatic and are often used as flagship species for conservation decisions. Large animals and trees are often highlighted as they have inspired much conservation effort and policy and effectively convey conservation principles to the public1,2. However, there is debate on if the charismatic nature of a species is a good indicator of conservation value or even a good predictor of conservation efficiency1,3,4.

One of the primary signatures of the Anthropocene has been a progressive elimination of the largest organisms5,6,7,8, especially if one of the first antecedents of the Anthropocene is argued to be the decimation of the Pleistocene megafauna9. Throughout most of the Phanerozoic, large animals and trees have been ubiquitous across the globe, except immediately following major extinction events in Earth history. Human activities are now disproportionately impacting the largest animals and trees2,8. This downsizing of the biosphere started in the Late Pleistocene with the extinction of much of the megafauna and continued through the rise of human societies marked by the exploitation of forests, ongoing hunting of large animals and clearing of land for agriculture and industry10. Here we coin the term megabiota to refer collectively to the largest plants and animals in the biosphere (i.e. the megafauna and megaflora). The megabiota are disproportionately impacted by land clearing, landscape fragmentation, hunting, overfishing, selective logging, human conflict, and climate change. As a result, populations of free ranging biodiverse megabiota on the planet have continued to be whittled down.

Since the rise of humanity it is primarily the largest and oldest trees that have become disproportionately rarer and more threatened. For example, since the start of civilization, the global number of trees on the planet has fallen by ~46%11 and now ~15 billion trees are cut down per year11. However, it is the largest trees that have experienced the largest reductions. Primary and intact forests hold the largest trees, and these forest types are the most threatened (representing only one-third of all remaining forested land). Further, only 12–22% of primary and intact forests are largely safeguarded in protected areas, the remainder is vulnerable to exploitation12. Climate change and shifts in localized climate due to deforestation is now disproportionately impacting big and old trees. Large trees are declining in forests at all latitudes2. For example, in increasingly more fragmented rainforests half of the large trees (≥60 cm diameter) are at risk of loss just in the first three decades after isolation13. The density of the largest trees in Yosemite National Park have declined by 24% between the 1930s and 1990s2,14. Among the largest trees on earth, the mountain ash Eucalyptus trees (E. regnans) in Australia are predicted to decline from 5.1 in 1997 to 0.6 trees per hectare by 20702.

The average body mass of mammals on the continents has dropped precipitously with the spread of humans around the world15. Across the Earth today, it is the larger animals that are increasingly in peril, particularly predators10,15,16,17. With almost a quarter of large species at risk. Starting in the Pleistocene, due largely to hunting, large-bodied mammals have been systematically extirpated17,18. Importantly, the accelerated loss of large mammals also occurred during intervals that experienced combinations of regional environmental change including aridification and increased biome heterogeneity within continents19 (Fig. 1). Today, of the world’s largest carnivores (greater than or equal to 15 kg) and the world’s largest herbivores (≥100 kg) 59% and 60% respectively are classified as threatened with extinction20. The major threats to the remaining megafauna include hunting, land-use change, and resource depression by livestock. Further, human conflict frequency (warfare etc.) predicts variation in population declines among wild large herbivores in protected areas in Africa, the last significant megafaunal continent, from 1946 to 201021.

Marine mammals have also seen broad population reductions due to widespread hunting over the past few hundred years22. Global fisheries have also been characterized by a reduction in the mean and maximum size of fish in the ocean. Since the 1950s there has been a persistent and gradual transition from large long-lived, high trophic level, piscivorous fish toward smaller, short-lived, low trophic level invertebrates and planktivorous pelagic fish23,24. With climate change, the oceans will become warmer, more acidic, and contain less oxygen. Due to physiological requirements of fish, these changes are predicted to shrink the assemblage-averaged maximum body weight by 14–24% globally from 2000 to 2050 under a high greenhouse gas emissions scenario25.

The reduction of the largest body sizes across of the diversity of life will increasingly have a major impact on the functioning of the biosphere26. However, given the scale of the problem, it is unclear if ecological theory can begin to predict the magnitude and extent of this perturbation on the biosphere27. We lack a general predictive framework to quantify how reductions in the size range of animals and plants will influence ecosystem and biosphere processes28,29. The rate of decline in the megabiota suggests that ever-larger regions of the world will soon lack many of the vital ecological services large organisms provide30. Therefore, there is an urgent need to understand how ecosystems change and may unravel with the decline of the megabiota18,28,31.

Here we provide a theoretical underpinning to: (i) understanding why large animals and trees deserve conservation attention; (ii) the first set of comprehensive predictions for how the loss of the megabiota (the largest plants and animals) will impact (and has impacted) the biosphere; and (iii) policies that emphasize the promotion of large trees and animals on biodiversity, ecosystem processes, and climate mitigation. We first use analytical theory (Metabolic Scaling Theory or MST) to provide a foundation to generate a baseline set of predictions. We show that, in times of global change, the megabiota are more prone to extinction and decreases in their abundances disproportionately influence ecosystem and Earth system processes. We predict that compared to ecosystems where body size ranges are reduced ecosystems with megabiota will disproportionately house more biomass, carbon, and nutrients and will be more fertile. As a result, the loss of large organisms will decrease the metabolism and fertility of the biosphere. These findings also indicate that efforts to conserve both the megabiota and increase the area devoted to conserving the megabiota will have a multiplicative impact on ecosystem functioning. We assessed these predictions within a set global General Ecosystem Model (GEM) set of global simulations. We also test if potential variation in size scaling within complex ecological systems impact variation in ecosystem and biosphere metabolism. Our results underscore the importance of the megabiota to the functioning of the biosphere and to conservation priorities.

Results

Applying metabolic scaling theory to the megabiota

Ultimately, cellular metabolism sets the pace of life and controls the flux of matter and energy in the biosphere32. The scaling of organismal metabolism powerfully constrains the functioning and life history of organisms across organisms from small to large sizes33,34,35. The scaling of metabolism sets the demand for resources, the space organisms require to forage, and the rate at which they interact with other organisms. Metabolism also influences the flux of energy and nutrients through organisms, populations, and ecosystems33,36. It constrains the rate of disease progression37, the magnitude of how organisms interact with each other and their environment and influences their risk of extinction18.

MST provides an analytical foundation to begin to understand the role of organismal size in ecology and evolution32. Building on previous work, we derive a baseline set of predictions that show that the largest body sized plants and animals have a disproportionate impact on ecological systems. Our extensions of MST to the ecology and evolution of the megabiota (See Supplementary Information) makes five general sets of predictions:

The megabiota have a higher risk of mortality and extinction

The megabiota are more prone to population reductions and extinction than smaller body sized species due to the compounding effects of habitat loss, human hunting and harvesting, and climate change (Fig. 1). Future climate projections show that terrestrial regions will be characterized by hotter and more pronounced droughts, and oceans and freshwater habitats will be characterized by warmer temperatures, decreased pH, and reduced oxygen concentrations25,38. These factors will place additional physical limits on plant and animal size, and reduce available habitat. As a result, rapid sudden climate change will negatively impact the growth and survivorship of larger trees (Fig. 1c), fish, and aquatic invertebrates leading to reductions in body sizes and potentially exacerbating feedbacks to climate change39 (Supplementary Information).

As we show in Supplementary Eqs. 45, Fig. 1a, b the probability of extinction, Eλ, in times of rapid climate change and/or exploitation and habitat loss, will scale positively with body size19. This is due to three key characteristics of the megabiota. First, they often operate closer to biophysical, physiological, and abiotic limits. So, the risk of mortality due to extreme events, R, is more pronounced in times of rapid climate change40. Second, as they have lower per capita fecundity rates, F41, their populations cannot rapidly rebound to change. Third, as a result, to maintain viable global population sizes, they require a larger minimum area, Am of habitat to avoid stochastic extinction42. Together, each of these characteristics scale with organism size, m, and combine to give a general allometric scaling expression for the probability of extinction, Eλ

$$E_\lambda \propto f\left[ {R\left( {m^b} \right) \cdot 1/F(m^{ - c}) \cdot A_m(m^d)} \right]\; \propto \;m^{b + c + d}$$
(1)

We predict that during times of rapid habitat loss and climate change Eλ will scale positively with body size (see also ref. 43). Values of the scaling exponents are expected to approximate b ~ 1, d ~ 1, and c ≈ 0.25 so that $$E_\lambda \propto m^{2.5}$$ (see Supplementary Information). Thus, as a rule of thumb, an organism that is 10 times larger in size will be about 316 times more susceptible to extinction during times of rapid change. Depending on the organism and environmental driver the values of b, d, and c will likely vary indicating that we expect this rule of thumb to vary. Nevertheless,  compared to smaller body sized flora and fauna, in times of rapid climate change and reductions of geographic range, larger body-sized species face disproportionally increased risk of extinction19,44.

The findings of numerous recent studies are generally consistent with the above predictions. In times of rapid human land use and climate change, when compared to smaller flora and fauna, larger plants and animals face increased risk of mortality events8,19,38,43,44. Indeed, large trees are most susceptible to changing climate via warming temperatures and drought39. Compared to smaller trees, the biggest trees exhibit the greatest increases in mortality rate in hotter droughts relative to non-drought conditions39. An Amazon forest drought experiment has been simulating the impact of a moderate drought by reducing rainfall by a third in a 1-hectare forest plot45. In that experiment, tree mortality rates doubled for smaller trees but increased 4.5 times for the bigger canopy trees (Fig. 1). Similarly, the fossil record indicates that increasing drought and habitat fragmentation are associated with elevated extinction rates of larger mammals relative to those of smaller mammals19 (Fig. 1).

The megabiota disproportionately impact ecosystem stocks and total biomass

The megabiota disproportionately impact ecosystem functioning via influencing the scaling of total ecosystem standing stocks (e.g. the total amount of ecosystem carbon, nitrogen etc.; Fig. 2) and biomass (Supplementary Eqs. 69). This impact is the result of two important ecological factors—the size spectra (the distribution of the sizes of all plant or animal individuals found in a given location, Fig. 2a), and f, the allometric relationships that characterize how structural attributes and physiological/metabolic rates of an individual change or scale with differences in body size. Depending on the environment, plants and animals can fill and occupy space differently (three-dimensional packing of roots and canopies vs. more two-dimensional packing of animal home ranges and territories). As a result, the impacts of the megabiota can differ depending on their ecology.

In the case of terrestrial plants (autotrophs), the total biomass of the forest, MTot can be related by a primary size measure—the radius of the plant stem, r, and the size distribution of the stems in that forest, f(r) where $$f(r) = cr^{ - \eta }$$ (see Supplementary Eq. 7). The value of the exponent, η, may vary but is hypothesized to approximate $$\eta \approx - 2$$ in undisturbed forests, a value supported by empirical studies46. Using idealized allometries, the total phytomass of an individual, m, can be related to the primary size measure—stem radius of a tree, r, where $$m\left( r \right) = c_m^{8/3}r^{8/3}$$, where cm is an allometric constant that may vary within or across taxa. We can then derive a general scaling law relating MTot and the size of the largest plant’s stem radius, rmax,

$$M_{\mathrm{Tot}} = \, {\int} m\left( r \right)f\left( r \right){\mathrm{dr}}\, = {\int} \left( {\frac{r}{{c_m}}} \right)^{\frac{8}{3}}\left( {c_nr^{ - 2}} \right)\mathrm{d}r\\ \approx \, \left( {\frac{3}{5}\frac{{c_n}}{{c_m^{8/3}}}} \right)r_{\mathrm{max}}^{5/3}$$
(2)

As the trunk radius of the largest tree in the forest increases, the total forest biomass, Mtot, increases disproportionately faster. Specifically, total biomass increases as the size of the largest individual tree raised to the 5/3 or 1.67 power of its trunk radius, rmax. Expressed as a function of the mass of the largest tree in the forest, mmax (kg), the total forest biomass increases as the $$M_{\mathrm{Tot}} \propto m_{\mathrm{max}}^{5/8}$$ (Supplementary Information). So, the total amount of biomass contained within the forest increases as the 5/8 or 0.625 power of the mass of the largest tree in the forest.

Similarly, in the case of animals (applied to all individuals within a trophic level), the total biomass of a trophic group, MTot can be related by its primary size measure—organism biomass, m. The size frequency distribution of all animals is measured in terms of animal mass, f(m) where $$f(m) = cm^{ - {\it{\epsilon }}}$$. The value of $${\it{\epsilon }}$$ may vary but is hypothesized to approximate $${\it{\epsilon }}$$ =−3/447. The total biomass of all animals in that trophic level, MTot is predicted to scale with the size of the largest animal, mmax (see Supplementary Information) as

$$M_{\mathrm{Tot}} = \, \int m\left( m \right)f\left( m \right){\mathrm{dm}} = \int m \cdot c_am^{ - 3/4}{\mathrm{dm}}\\ \approx \, \frac{4}{5}c_nm_{\mathrm{max}}^{5/4}$$
(3)

This predicted relationship, indicates that, in a given trophic level, as the mass of the largest animal increases, the total trophic biomass of all animals increases disproportionately faster. When expressed in terms of organismal biomass, this predicted superlinear scaling of total trophic biomass, shows that changes in maximum size of an animal mmax will have a larger and disproportionate impact on the total trophic biomass MTot (see Supplementary Fig. 1)

We tested these predictions via several different approaches. Observations of forests across the globe, in both temperate and tropical forest communities (Fig. 3) show that the size of the largest individual, mmax is a strong predictor of total forest biomass, MTot. The fitted scaling exponent for total forest biomass, 0.62 (95% CI = 0.58–0.66), is indistinguishable from the MST prediction of 5/8 = 0.625 (see ref. 48; Fig. 3). As we discuss below, global simulation models that incorporate metabolic and allometric scaling also show the predicted positive scaling relationship between body mass and total heterotrophic biomass (see below), but the relationship is modified by local climate.

The megabiota disproportionately impact ecosystem flows

MST predicts that the megabiota impact ecosystem functioning via their disproportionate impact on total trophic biomass which then drives the total metabolic and resource fluxes and ecosystem net primary productivity33. For autotrophs, the total energy flux through all plants, BTot and the total net biomass productivity or net primary productivity or NPP (or the total resource flux JTot) scales with the size of the largest individual and the total autotrophic biomass. In Supplementary Eqs. 1013 we derive a general scaling law for how total trophic biomass, MTot, influences variation in ecosystem fluxes including total energy, BTot, biomass productivity, NPP, and carbon, and nutrients. The total resource utilization rate JTot (kg yr−1) of a given resource i, such as nitrogen, water, carbon etc, can be written as

$$J_{\mathrm{Tot}} \propto NPP \propto B_{\mathrm{Tot}} \approx \left( {\tau \kappa _i^{ - 1}B_0c_n} \right)r_{\mathrm{max}}$$
(4)

As the size of the largest tree within a forest increases, the total system flux will scale in direct proportion to the largest individual. The total amount of resources (carbon, water, nutrients) that pass through the ecosystem or through a food web will increase as maximum tree height increases. In terms of the total autotrophic biomass, as the size of the largest tree influences total forest biomass, MTot, (Eq. 2) and NPP, we can relate NPP to MTot as $${\mathrm{NPP}} \propto B_{\mathrm{Tot}} \approx b_0c_m^{8/5}c_n^{2/5}\left[ {5/3M_{\mathrm{Tot}}} \right]^{3/5}$$. Thus, forests with trees 10 times larger in trunk diameter will store ~47 times more carbon (see above, Eq. 3) and will assimilate 10 times more carbon and produce 10 times more biomass. As a result, vegetation that contains larger individuals will disproportionately absorb and store more carbon and cycle more water and nutrients and in turn produce more biomass.

Similarly, for animals, because of the allometry of resource use and packing of ecological space, we have a similar but slightly different scaling relationship indicating that increases in the maximum body mass of an animal would also disproportionately increase the total amount of flux through the heterotrophic food web. With substitution, we then have

$$J_{\mathrm{Tot}} \approx \left( {\tau \kappa _i^{ - 1}B_0c_n\frac{4}{5}c} \right)m_{\mathrm{max}}^{5/4}$$
(5)

Importantly, for animals, the flux of energy and matter through the heterotrophic food web is predicted to scale to the 5/4th or 1.25 power of the total heterotrophic biomass. Ecosystems with the largest animals 10 times larger in mass flux ~18 times more energy and nutrients (see above, Eq. 3). Thus, as the size of the largest individual (as measured by the primary size) within a given trophic group increases, the total ecosystem trophic flux will scale superlinearly.

Support for the above MST predictions are shown in Fig. 3, Supplementary Information, and by recent studies assessing the dynamical predictions for ecosystems46,49,50. Variation in forest biomass has a larger effect on variation in ecosystem productivity (NPP) than precipitation, temperature, and forest age51. Similarly, the best predictor of forest biomass is the size of the largest individual (Fig. 3a), together these results show that forests with large megaflora are more productive and contain more stored carbon (Fig. 3). For animals, tentative support for this prediction is given by earlier macroecological analyses where species of large body sized birds flux more energy than small body sized birds52.

The megabiota disproportionately impact ecosystem fertility

Larger herbivorous animals are disproportionately more important in the lateral movement of nutrients and energy in the biosphere via dung, urine and flesh. This movement takes two main forms: diffusion and directional transport. Recent work has utilized aspects of metabolic scaling theory to quantify the movement of nutrients across space by herbivores53. We show that MST makes specific predictions for the scaling of nutrient diffusivity in ecosystems as a function of the largest sized animal (“Methods”; Supplementary Information). Specifically, the diffusion of nutrients across the landscape by herbivores via defecation and urination, ϕ, scales positively with the size of the largest herbivore, mHerbivore.

$${\phi} \propto m_{\mathrm{Herbivore}}^{1.17}$$
(6)

We assessed these predictions, by (i) simulating how a reduction in body size of herbivores in Amazonian forests affects the distribution of soil phosphorus across the Amazon basin (see the “Methods” section); and (ii) implementing the allometric scaling of metabolism and animal movement in a global simulation model (see below). Consistent with predictions, the Amazonian simulations show that the observed reduction in  the size range of the megafauna in the Amazon from the Pleistocene baseline leads to reduction in ecosystem fertility as measured by steady state soil phosphorus concentrations (Fig. 4). Under a series of size thresholds for the extinct megafauna, we expect a 20–40% reduction in soil steady state P concentrations. Recent empirical studies are consistent with these predictions and point to the importance of megafauna on nutrient redistribution and fertilization of ecosystems54,55.

Conservation implications of the multiplicative importance of the megabiota and total area protected

The megabiota are also disproportionately more impactful for conservation efforts prioritizing ecosystem functioning. For example, because the total biomass of a given trophic level, Mtot, will be directly proportional to the amount of area A (Mtot ~ A) protected56, doubling the area available for the megabiota will further have a disproportionate effect on ecosystem functioning (see Supplementary Eq. 16; Supplementary Fig. 1B). For example, efforts to maximize ecosystem services can be amplified by effort to maintain and increase large body sized plants and animals (Supplementary Fig. 1) and also conserve larger areas. Allowing for increases in maximum organism size and allowing more area to be restored to forest or to rewild large animals57 will together have a multiplicative and nonlinear effect on ecosystem services (Supplementary Fig. 2).

Global simulations of the biosphere with and without megaherbivores

One of the limitations of the above derivations from MST is that the analytical theory does not yet tackle the complexity of species interactions in differing landscapes. In particular, including how ecological interactions and dynamics within and across differing landscapes and trophic levels have yet to be detailed by MST. Removing the megabiota does more than just reduce the body size range of plants and animals—it changes how individuals and species interact with each other58. These networks of ecological interactions are also fundamentally altered by shifting the relative importance of competitive and mutualistic interactions and the presence of trophic cascades10. For example, loss of the megabiota could influence the growth and abundance of smaller plants and animals. Their response could then compensate for ecosystem functions and possibly negate the above predictions. To more fully assess how downsizing of the planet’s fauna will influence ecosystem processes within the context of complex species interaction networks we utilized a General Ecosystem Model (GEM).

We used the Madingley Model as it explicitly incorporates the importance of organismal body size (metabolic demands, foraging area, and population dynamics59; see Supplementary Fig. 2). This formulation of a GEM represents complex ecological interaction networks and whole-ecosystem dynamics at a global scale60. It is capable of modelling emergent ecosystem and biosphere structure and function by simulating a core set of biological and ecological processes for all terrestrial and marine organisms between 10 μg and 150,000 kg. Details of the simulation model are described in the methods section, Supplementary Information, supplementary Figs. 29).

We generated a set of forecasts for how, since the Pleistocene, the downsizing of the terrestrial megafauna has altered or will alter the functioning of ecosystems and biosphere. We ran three sets of simulations, or three different worlds (see “Methods” and Supplementary Information). In each world, we simulated the loss of the endotherm herbivore megafauna by experimentally changing the maximum attainable body mass. Each world differed in maximum size by an order of magnitude, from 10,000 kg (the largest terrestrial Pleistocene herbivore, Mammuthus columbi), to 1000 kg (typical modern day maximum size of terrestrial  mammalian taxa) and finally 100 kg (a future world lacking wild megaherbivores). The body mass ranges for all other terrestrial animal cohorts were held constant and approximating those found in the Pleistocene fossil record (see ref. 60; Table 1; see Supplementary Fig. 2). We hereafter refer to these three worlds as (i) Pleistocene world, (ii) Modern world; and (iii) Future world.

Multiple lines of evidence from the GEM simulations (Fig. 5a–c) are consistent with predictions from MST (Eqs. 26; see also Supplementary Eqs. 9, 11, 1315). We observed a disproportionate impact of the megabiota with a positive, but increasing, relationship with maximum body size and ecosystem function (Fig. 5d–f),. Reductions in the size of the largest animal—megaherbivores—leads to a decrease in biosphere functioning (Table 1; Fig. 5d–f). Compared to the Pleistocene baseline, the total biosphere biomass is predicted to decrease 44.1% from 23.60 Pg to 13.20 Pg (Fig. 5d, Table 1). The impacts of megaherbivore loss vary spatially indicating that local climate and species composition may further modify MST predictions. Large impacts of megaherbivore loss are observed in sub-tropical regions of the world (see Supplementary Figs. 4,8–9) because these regions are characterized by the largest animals (see Supplementary Fig. 4c, e). Reductions in maximum herbivore body size have the greatest impact on ecosystem nutrient diffusivity, with global measures of future nutrient diffusivity decreasing by 92.4% between the Pleistocene and Future worlds (Fig. 5f, Table 1). The loss of megaherbivores in a future world has a smaller impact on global heterotrophic metabolism (decreasing 18%; see Table 1).

We also tested an important alternative hypothesis—with the loss of the megabiota, the response of smaller organisms could compensate for the loss of the megabiota. Specifically, with the loss of ecological interactions from the megabiota, ecological and evolutionary responses from smaller organisms could lead to changes in their abundance and range61 and compensate for the loss of large herbivores and carnivores. We used the GEM to test if smaller animals experience an ecological release with the loss of the larger body plants and animals, and if they can they provide the ecosystem functions of the megabiota. Our results indicate that while there is some compensation from the smaller organisms in terms of heterotrophic metabolism (Fig. 5e), we see little to no compensation in global heterotrophic biomass and nutrient diffusivity (Fig. 5d, f).

Discussion

There has been considerable debate, on whether conservation goals are best achieved by promoting management of a single charismatic species or focusing on whole-ecosystem functioning1. Charismatic species in conservation are most often large mammals and vertebrates1,62, although large old growth trees and old growth forests can also be charismatic63. Conservationists have argued that actions intended to preserve an iconic charismatic species can have an umbrella effect and save less-glamorous species and whole ecosystems that thrive in its shadow. However, can large organisms act as a proxy for the diversity and functioning of whole ecosystems31? Such proxies are difficult to measure. The natural charisma of large animals and trees is often cited as the best justification to protect habitat and entire ecosystems64. Nonetheless, considerable debate remains. Daniel Simberloff, noted that “whether many other species will really fall under the umbrella is a matter of faith rather than research”4. A worry is that while only charismatic species seem able to appeal enough interest to raise sufficient funds and interest a focus on the large charismatic fauna and flora is not based on science65.

Our simulation results are consistent with the arguments of Estes et al.10 who underscored that ecological theory based on species trophic interactions implies that downsizing of the biosphere will result in major shifts in ecosystem and biosphere functioning (Supplementary Information). Ecological theory based on species interactions further points to the importance of the megabiota in also influencing other aspects of ecosystem functioning tied to human health and well-being. For example, there are strong lines of evidence to suggest that loss of the megabiota negatively impacts ecosystem resilience to climate change, human health via disease dynamics (influencing emerging diseases and pathogenesis), biological diversity, and buffering ecosystem functioning66. We are only starting to understand the connections between human health and the megabiota but preliminary data and extensions of MST to pathogenesis and ecosystem resilience points to important linkages37.

Together, our theory and simulations indicate that many conservation and climate change mitigation policies can be assisted by emphasizing the conservation reestablishment and promotion of the largest organisms. The widespread extinction of megafauna and decline in abundance of many remaining megafauna have progressively eliminated an interlinked biosphere system for the recycling of nutrients and reducing the metabolism of the biosphere. In a world with megabiota more carbon and nutrients are stored in vegetation and through animal movements, they flow against entropy from the ocean depths to continental interiors and from fertile soils to relatively poorer soils67. Our results support past speculations that a reduction in the largest animals will result in a drop in nutrient diffusion capacity67. A decrease in nutrient concentrations in regions that are distant from their abiotic sources result in broad global regions being less fertile27,67. Simply put, landscapes and ecosystems that contains larger and more abundant organisms are more productive, more resilient to climate change, and will provide disproportionately more ecosystem services to humanity.

Our growing understanding of the role of the megabiota raises numerous questions that future research will need to address. In Supplementary Box 1 we detail a set of questions that stem from our findings (see Supplementary Box 1; Supplementary Information). Key questions remain in terms of how reductions of the largest sized individuals influence complex ecological networks, human health, and biosphere functioning. For example, in a world with fewer megabiota, how will the dynamics of ecosystems and biodiversity change7,18? Because large organisms are long lived and their population cycles are longer, the presence of large-bodied organisms can buffer ecological systems from environmental variation. Will ecological systems and human interactions with ecological systems (fisheries, forestry) become less buffered with time with loss of the megabiota? How long will it take reforestation and restoration efforts to revive ecosystem processes promoted by large body sized species68?

It is also important to emphasize that while the wild megabiota has greatly decreased, that nature of the megabiota has profoundly changed and become domesticated18. Our results do not incorporate increases in the population of large domestic animals (domesticates such as cattle, pigs etc.) and forest plantations and management that have greatly increased. Further, an important question is to what extent the anthropocentric megabiota functionally compensate for or exacerbates the impacts of lost wild animal biomass. Some forms of megabiota domestication and management may replicate the functioning of wild megabiota e.g. nomadic pastoralism, forest and woodland management. Many other forms, such as industrialized animal farming and forest management with restricted animal movement and limits on tree size from fencing and human land use, do not.

Our results do not argue or indicate that smaller organisms are less important or that they should be ignored. Indeed the role of the smaller organisms (e.g. microbes69, insects70, etc.) are crucial to ecosystem and biosphere functioning. Our point is that the functioning of the biosphere and the well-being of increasingly smaller organisms disproportionately relies on the largest organisms. Further, the smaller organisms cannot provide most of the distinctive ecological roles and services played by large old trees and animals. Nonetheless, more research is needed to help understand uncertainties and clarify limits of our theoretical predictions numerous lines of evidence point to the disproportionate impact of the megabiota to the functioning of the biosphere.

In conclusion, we have presented a theoretical framework and a global simulation model that provides a set of baseline predictions for how the loss of the megabiota will influence several aspects of ecosystem structure and function and tested several predictions of metabolic scaling theory. Our analytical theory predicts that forests and animal communities with larger body sizes will disproportionately contain more biomass, carbon, and nutrients and disperse nutrients further than ecosystems where body size ranges are reduced. Further, as the land area devoted to conservation of megabiota increases, the megabiota have a multiplicative impact on total biomass and ecosystem functioning.

There is an urgent need for interdisciplinary research to forecast the effects of trophic downsizing on process, function, and resilience within ecosystems and the biosphere10 (see Supplementary Box 2). In this paper, we introduced the term megabiota to refer to the biosphere consisting of the largest plants and animals. We provided an overview and extended metabolic scaling theory to show how MST can be used to provide a set of strong predictions for the importance of the largest plants and animals for ecosystem structure and functioning. We utilized a global simulation model to more fully assess and explore several predictions from metabolic scaling theory. Both theory and our simulation results show the disproportionate importance of the megabiota on the impact on ecosystems and the functioning of the biosphere.

Our results show that a biosphere with larger plants and animals is more productive, contains more biomass, and is more fertile than a biosphere lacking in the largest animals. Further, it is also increasingly clear that a biosphere with megabiota is more buffered, resilient, and positively influences biological diversity. There is mounting evidence that the megabiota, via how they influence ecological interactions, encapsulate the checks and balances that minimize boom-and-bust cycles of species outbreaks, disease dynamics, and ecosystem imbalances (Supplementary Information). The result is a benefit to human health and economies by minimizing biological ecosystem stochastic variation and increasing the fertility and productivity of the biosphere. Ecological systems that are missing these key regulatory players, such as large predators, herbivores, and trees, provide fewer ecosystems services, are less predictable, and can collapse10. While there are important caveats and uncertainties (Supplementary Box 2) promoting the conservation and management of the largest organisms enhances numerous linkages to whole-ecosystem diversity, functioning, and services. The continued reduction of the megabiota will have long lasting and profound impacts on the Earth System that are not included in our current earth system models18. We are only starting to realize and quantify these impacts. Conservation and climate mitigation policies that emphasize the conservation, reestablishment, and promotion of the largest trees and animals will have more impact on biodiversity and ecosystem processes than polices that do not prioritize the megabiota.

Methods

Analytical derivations

Detailed analytical derivations are given in the Supplementary Information in Supplementary Eqs. 116.

Amazon fertility simulation

Following Doughty et al.27, we modelled how reductions in the maximum size of herbivores would then impact the fertility of the soils of the Amazon Basin27. We calculated the steady state estimate of soil P concentrations in the Amazon basin prior to the megafaunal extinctions. The extinctions of the megafauna in South America has led to drastic changes in animal size distributions with 70% of mammal species greater than 10 kg going extinct (62 species) since the Pleistocene including such large iconic species as gomphotheres, giant sloths and glyptodonts. This simulation is characterized by lateral diffusivity of nutrients (Φ) by mammals away from the Amazon river floodplain source. In the simulation, animal nutrient transport are modelled via diffusivity of nutrients via ingestion, transport, and eventual defecation.

GEM simulations

The conceptual basis for GEMs is described by Purves et al.60 and a comprehensive explanation of the GEM are provided by Harfoot et al.59 The Madingley model GEM explicitly simulates the dynamics of plants and all heterotroph organisms between 10 μg and 150,000 kg. The model is mechanistic, generating emergent ecosystem structure and function by simulating a core set of biological and ecological processes at the level of an individual. The GEM is global in scope, but is spatially and temporally flexible, allowing for application at regional and local scales and can be applied in both the terrestrial and marine realms.

On land, plants are represented by stocks of biomass simulated using the climate-driven model of Smith et al.71. Plant biomass is added to the autotroph stock each time step in each grid cell through environmentally-driven primary production, the seasonality of which is calculated using remotely-sensed Net Primary Productivity or NPP. This production is allocated to above-ground/below-ground, structural-non-structural and evergreen/deciduous components as a function of the environment. Biomass is lost from plant stocks through mortality from fire, senescence and herbivory.

Our simulations do not directly change the available plant biomass or abundance of animal cohorts modelled within each grid cell, which is instead a function of environmental suitability and ecological pressures. Nor do these simulations include future land use, historic land use, the rise of domesticated animals (cattle, pigs etc.) or differing climate change scenarios. Instead, to start, we assess the effects of reducing the maximum size of just warm-blooded herbivorous animals. Due to stochasticity generated within the GEM, we performed an ensemble of five 100-year global simulations for each world using a monthly time step and a resolution of 2° × 2° grid cells. To understand the importance of the loss of megabiota in one trophic level (megaherbivores) in shaping ecosystems, we considered three ecosystem-level measures; total heterotrophic biomass, total heterotrophic metabolism and nutrient diffusivity (for further details on the calculation of these metrics please refer to Supplementary Information).

GEM experimental constraints

The complex network of dynamic ecological interactions modelled within the Madingley GEM model can lead to unpredictable behaviour. Consequently, to constrain our analysis to a single cause we circumscribed our experiments to manipulating the body size of endothermic herbivores only. For this, we exclusively modelled the terrestrial realm because the megafauna extinctions have been less severe in the oceans than on land72.

The constraining characteristics of cohorts used in the three experiments are summarized in Supplementary Table 1. For all cohorts except endothermic herbivores, these properties were kept as those used by Harfoot et al.59, which are broadly realistic of the late Pleistocene prior to the megafauna extinctions73. We use the same annual time-series of monthly climatological input data for each year of the 100-year simulation, and importantly do not include the effects of anthropogenic habitat conversion or the harvesting of plants and animals. As a result, except for climatic conditions which are based on averaged data between 1961 and 2000, our simulations represent a late-Pleistocene ecological world.

We experimentally changed the maximum attainable body size of endothermic herbivores across two orders of magnitude from 10,000 kg to 100 kg. This upper value is representative of the largest known herbivorous mammal, Mammuthus columbi, as estimated from the fossil record by Faurby and Svenning73. Importantly, these upper and lower body masses determine the possible range over which cohorts can theoretically be realised in each grid cell. Once the model is running, however, environmental and ecological pressures may not allow these limits to be reached.

Heterotroph biomass

The GEM is not deterministic, so we performed an ensemble of five 100-year global simulations for each world using a monthly time step and a resolution of 2° × 2° grid cells. After 100 model years simulations reached a dynamic steady state. Heterotrophic organisms were assigned to one of 25 mass bins based upon the natural logarithm of their individual body mass. To capture the seasonal variations in grid cell heterotroph biomass, we calculated the mean heterotrophic biomass in each grid cell using the last 12 monthly time steps, or one whole year. This was performed for the five simulations run for each world, from which an ensemble mean value was derived for each terrestrial grid cell. Heterotroph biomass within each grid cell and globally was then summarised by trophic group, thermoregulatory strategy and mass bin for use in our experimental analysis.

Heterotroph metabolism

The metabolic rate, in kJ/day, for each organism was calculated assuming a power-law relationship with body mass and an exponential relationship with temperature following74. Whilst an organism is active, metabolism is described by field metabolic rates, whilst when inactive metabolism is described by basal metabolic rates (see Supplementary Eq. 2 and ref. 59). Endothermic functional groups were considered to be metabolically active for the entirety of a time step with a body temperature of 310 K. For ectothermic functional groups, the proportion of time active and body temperature was derived from the ambient temperature TK.

Nutrient diffusivity

Nutrient diffusivity was calculated from a modified version of Eq. 3 in Wolf et al.53: Next, because our GEM can calculate animal density, we then calculated Φexcreta by inputting animal density predicted by our GEM into Supplementary Eq. 3.

Reporting summary

Further information on research design is available in the Nature Research Reporting Summary linked to this article.

Data availability

The datasets generated during and/or analyzed during the current study are available in the via our github repository https://github.com/andrewjabraham/Megabiota.

Code availability

The source code underlying the Amazon phosphorus simulation (Fig. 4) in Matlab is available via GitHub https://github.com/andrewjabraham/Megabiota. The C# code to run the GEM Madingley simulation is available via GitHub (https://github.com/Madingley/C-sharp-version-of-Madingley). There are good instructions here on how to run the model here should any readers wish to do so. The R codes to analyse the GEM simulations and recreate all associated figures and tables (and Fig. 5, Supplementary Figs. 2-8 as well as Table 1 and Supplementary Table 2) are available via GitHub https://github.com/andrewjabraham/Megabiota.

References

1. 1.

Ducarme, F., Luque, G. M. & Courchamp, F. What are ‘charismatic species’ for conservation biologists? Biosci. Master Rev. 1, 1–8 (2013).

2. 2.

Lindenmayer, D. B., Laurance, W. F. & Franklin, J. F. Global decline in large old trees. Science 338, 1305–1306 (2012).

3. 3.

Sergio, F. et al. Top predators as conservation tools: ecological rationale, assumptions, and efficacy. Annu. Rev. Ecol., Evolution, Syst. 39, 1–19 (2008).

4. 4.

Simberloff, D. Flagships, umbrellas, and keystones: Is single-species management passe in the landscape era? in. Biol. Conserv. 83, 247–257 (1998).

5. 5.

Williams, M. et al. The anthropocene biosphere. Anthropocene Rev. 2, 196–219 (2015).

6. 6.

Burney, D. A. & Flannery, T. F. Fifty millennia of catastrophic extinctions after human contact. Trends Ecol. Evolution 20, 395–401 (2005).

7. 7.

Dirzo, R. et al. Defaunation in the Anthropocene. Science 345, 401–406 (2014).

8. 8.

Smith, F., Smith, R. E. E., Lyons, S. K. & Payne, J. L. Body size downgrading of mammals over the late Quaternary. Science 360, 310–313 (2018).

9. 9.

Malhi, Y. The Concept of the Anthropocene. Annu. Rev. Environ. Resour. 42, 77–104 (2017).

10. 10.

Estes, J. A. et al. Trophic downgrading of planet earth. Science 333, 301–306 (2011).

11. 11.

Crowther, T. W. et al. Mapping tree density at a global scale. Nature 525, 201–205 (2015).

12. 12.

IUCN. Raising the profile of primary and intact forests. https://www.iucn.org/theme/forests/our-work/slowing-global-deforestation-rate-and-primary-forests/raising-profile-primary-and-intact-forests. (2018).

13. 13.

Laurance, W. F., Delamônica, P., Laurance, S. G., Vasconcelos, H. L. & Lovejoy, T. E. Rainforest fragmentation kills big trees. Nature 404, 2000–2000 (2000).

14. 14.

Lutz, J. A., van Wagtendonk, J. W. & Franklin, J. F. Twentieth-century decline of large-diameter trees in Yosemite National Park, California, USA. For. Ecol. Manag. 257, 2296–2307 (2009).

15. 15.

Barnosky, A. D. et al. Variable impact of late-Quaternary megafaunal extinction in causing ecological state shifts in North and South America. Proc. Natl Acad. Sci. USA 113, 856–861 (2016).

16. 16.

Hoffmann, M. et al. The changing fates of the world’s mammals. Philos. Trans. R. Soc. B: Biol. Sci. 366, 2598–2610 (2011).

17. 17.

Courchamp, F., Jaric, I., Albert, C., Meinard, Y. & Ripple WJ, C. G. The paradoxical extinction of the most charismatic animals. PLoS Biol. 6, e2003997 (2018).

18. 18.

Smith, F. A., Doughty, C. E., Malhi, Y., Svenning, J. C. & Terborgh, J. Megafauna in the Earth system. Ecography 39, 99–108 (2016).

19. 19.

Tomiya, S. Body size and extinction risk in terrestrial mammals above the species level. Am. Naturalist 182, E196–E214 (2013).

20. 20.

Ripple, W. J. et al. Saving the World’s Terrestrial Megafauna. BioScience 66, 807–812 (2016).

21. 21.

Daskin, J. H. & Pringle, R. M. Warfare and wildlife declines in Africa’s protected areas. Nature 553, 328–332 (2018).

22. 22.

Branch, T. A. et al. Past and present distribution, densities and movements of blue whales Balaenoptera musculus in the Southern Hemisphere and northern Indian Ocean. Mammal. Rev. 37, 116–175 (2007).

23. 23.

Pauly, D., Christensen, V., Dalsgaard, J., Froese, R. & Torres, F. Fishing down marine food webs. Science 279, 860–863 (1998).

24. 24.

Jennings, S., Greenstreet, S. P. R. & Reynolds, J. D. Structural change in an exploited fish community: a consequence of differential fishing effects on species with contrasting life histories. J. Anim. Ecol. 68, 617–627 (1999).

25. 25.

Cheung, W. W. L. et al. Shrinking of fishes exacerbates impacts of global ocean changes on marine ecosystems. Nat. Clim. Change 3, 254–258 (2013).

26. 26.

Chown, S. L. & Gaston, K. J. Macrophysiology for a changing world. Proc. R. Soc. B: Biol. Sci. 275, 1469–1478 (2008).

27. 27.

Doughty, C. E., Wolf, A. & Malhi, Y. The legacy of the Pleistocene megafauna extinctions on nutrient availability in Amazonia. Nat. Geosci. 6, 761–764 (2013).

28. 28.

Sheridan, J. A. & Bickford, D. Shrinking body size as an ecological response to climate change. Nat. Clim. Change 1, 401–406 (2011).

29. 29.

Barneche, D. R., Ross Robertson, D., White, C. R. & Marshall, D. J. Fish reproductive-energy output increases disproportionately with body size. Science 360, 642–645 (2018).

30. 30.

Ripple, W. J. et al. Collapse of the world’s largest herbivores. Sci. Adv. 1, e1400103–e1400103 (2015).

31. 31.

Owen-Smith, R. N. Megaherbivores: The influence of very large body size on ecology. (Cambridge University Press, 1988).

32. 32.

West, G., Brown, J. H. & Enquist, B. J. A general model for the origin of allometric scaling laws in biology. Science 276, 122–126 (1997).

33. 33.

Enquist, B. J., Michaletz, S. T. & Kerkhoff, A. J. in A Biogeoscience Approach to Ecosystems (eds. Johnson, E. A. & Martin, Y. E.) 9–46 (Cambridge University Press, 2016).

34. 34.

Peters, R. H. The ecological implications of body size. Cambridge studies in ecology (Cambridge, 1983).

35. 35.

Calder, W. A. Diversity and Convergence: Scaling for Conservation. in Scaling in Biology (eds. Brown, J. H. & West, G. B.) 297–323 (Oxford University Press, 2000).

36. 36.

Michaletz, S. T. S. T., Cheng, D., Kerkhoff, A. J. A. J. & Enquist, B. J. B. J. Convergence of terrestrial plant production across global climate gradients. Nature 512, 39–43 (2014).

37. 37.

Doughty, C.E. et al. Megafauna decline have reduced pathogen dispersal which may have increased emergent infectious diseases. Preprint at https://www.biorxiv.org/content/10.1101/2020.01.21.914531v1 (2020)

38. 38.

McDowell, N. G. et al. Predicting chronic climate-driven disturbances and their mitigation. Trends Ecol. Evolution 33, 15–27 (2018).

39. 39.

Bennett, A. C., Mcdowell, N. G., Allen, C. D. & Anderson-Teixeira, K. J. Larger trees suffer most during drought in forests worldwide. Nat. Plants 1, 5139 (2015).

40. 40.

Anderson-Teixeira, K. J. et al. Size-related scaling of tree form and function in a mixed-age forest. Funct. Ecol. 29, 1587–1602 (2015).

41. 41.

Calder, W. A. & Calderiii, W. An allometric approach to population cycles in mammals. J. Theor. Biol. 100, 275–282 (1983).

42. 42.

Marquet, P. A. & Taper, M. L. On size and area: patterns of mammalian body size extremes across landmasses. Evol. Ecol. 12, 127–139 (1998).

43. 43.

Ripple, W. J. et al. Extinction risk is most acute for the world’s largest and smallest vertebrates. Proc. Natl Acad. Sci. USA 114, 10678–10683 (2017).

44. 44.

Cardillo, M. et al. Evolution: multiple causes of high extinction risk in large mammal species. Science 309, 1239–1241 (2005).

45. 45.

Nepstad, D. C., Tohver, I. M., David, R., Moutinho, P. & Cardinot, G. Mortality of large trees and lianas following experimental drought in an amazon forest. Ecology 88, 2259–2269 (2007).

46. 46.

Duncanson, L. I. L. I., Dubayah, R. O. R. O. & Enquist, B. J. B. J. Assessing the general patterns of forest structure: quantifying tree and forest allometric scaling relationships in the United States. Glob. Ecol. Biogeogr. 24, 1465–1475 (2015).

47. 47.

White, E. P., Ernest, S. K. K. M. K. M., Kerkhoff, A. J. & Enquist, B. J. Relationships between body size and abundance in ecology. Trends Ecol. Evol. 22, 323–330 (2007).

48. 48.

Stegen, J. C. J. C. et al. Variation in above-ground forest biomass across broad climatic gradients. Glob. Ecol. Biogeogr. 20, 744–754 (2011).

49. 49.

Fyllas, N. M. et al. Solar radiation and functional traits explain the decline of forest primary productivity along a tropical elevation gradient. Ecol. Lett. 20, 730–740 (2017).

50. 50.

Enquist, B. J. et al. Assessing trait-based scaling theory in tropical forests spanning a broad temperature gradient. Glob. Ecol. Biogeogr. 26, 1357–1373 (2017).

51. 51.

Michaletz, S. T., Kerkhoff, A. J. & Enquist, B. J. Drivers of terrestrial plant production across broad geographical gradients. Glob. Ecol. Biogeogr. 27, 166–174 (2018).

52. 52.

Brown, J. H. & Maurer, Ba Macroecology: the division of food and space among species on continents. Science 243, 1145–1150 (1989).

53. 53.

Wolf, A., Doughty, C. E. & Malhi, Y. Lateral diffusion of nutrients by mammalian herbivores in terrestrial ecosystems. PLoS ONE 8, e71352 (2013).

54. 54.

Doughty, C. E. Herbivores increase the global availability of nutrients over millions of years. Nat. Ecol. Evolution 1, 1820–1827 (2017).

55. 55.

Bump, J. K. Fertilizing riparian forests: nutrient repletion across ecotones with trophic rewilding. Philos. Transact. R. Soc. B: Biol. Sci. 373, 20170439 (2018).

56. 56.

Hubbell, S.P. The Unified Neutral Theory of Biodiversity and Biogeography (Princeton University Press, 2001)

57. 57.

Sandom, C., Donlan, C. J., Svenning, J. C. & Hansen, D. Rewilding. Key Top. Conserv. Biol. 2, 430–451, https://doi.org/10.1002/9781118520178.ch23 (2013).

58. 58.

Peres, C.A. Effects of subsistence hunting on vertebrate community structure in Amazonian forests. Conservation biology 14, 240–253. (2000).

59. 59.

Harfoot, M. B. J. et al. Emergent global patterns of ecosystem structure and function from a mechanistic general ecosystem model. PLoS Biol. 12, e1001841 (2014).

60. 60.

Purves, D. et al. Time to model all life on Earth. Nature 493, 295–297 (2013).

61. 61.

Tóth, A. B. et al. Reorganization of surviving mammal communities after the end-Pleistocene megafaunal extinction. Science 365, 1305–1308 (2019).

62. 62.

Macdonald, E. A. et al. Identifying ambassador species for conservation marketing. Glob. Ecol. Conserv. 12, 204–214 (2017).

63. 63.

Blicharska, M. & Mikusiński, G. Incorporating social and cultural significance of large old trees in conservation policy. Conserv. Biol. 28, 1558–1567 (2014).

64. 64.

Sergio, F., Newton, I., Marchesi, L. & Pedrini, P. Ecologically justified charisma: Preservation of top predators delivers biodiversity conservation. J. Appl. Ecol. 43, 1049–1055 (2006).

65. 65.

Barua, M. Mobilizing metaphors: the popular use of keystone, flagship and umbrella species concepts. Biodivers. Conserv. 20, 1427–1440 (2011).

66. 66.

Dobson, A. Population dynamics of pathogens with multiple host species. Am. Nat. 164, S64–S78 (2004).

67. 67.

Doughty, C. E. et al. Global nutrient transport in a world of giants. Proc. Natl. Acad. Sci. 113, 868–873 (2016).

68. 68.

Svenning, J. C. et al. Science for a wilder Anthropocene: synthesis and future directions for trophic rewilding research. Proc. Natl. Acad. Sci. USA 113, 898–906 (2016).

69. 69.

Cavicchioli, R. et al. Scientists’ warning to humanity: microorganisms and climate change. Nat. Rev. Microbiol. 17, 569–586 (2019).

70. 70.

Weisser, W. W. & Siemann, E. in Insects and Ecosystem Function. Ecological Studies (Analysis and Synthesis) (eds. Weisser, W. W. & Siemann, E.) 3–24 (Springer, 2008).

71. 71.

Smith, M. J. et al. The climate dependence of the terrestrial carbon cycle, including parameter and structural uncertainties. Biogeosciences Discuss. 9, 13439–13496 (2013).

72. 72.

McCauley, D. J. et al. Marine defaunation: animal loss in the global ocean. Science 347, 1255641 (2015).

73. 73.

Faurby, S. & Svenning, J. C. Historic and prehistoric human-driven extinctions have reshaped global mammal diversity patterns. Diversity Distrib. 21, 1155–1166 (2015).

74. 74.

Gillooly, J. F., Brown, J. H., West, G. B., Savage, V. M. & Charnov, E. L. Effects of size and temperature on metabolic rate. Science 293, 2248–2251 (2001).

Acknowledgements

B.J.E., Y.M., M.B.J.H. and C.E.D. thank the Gordon Research Conference on Metabolic Ecology for providing the atmosphere to help generate the early seeds of the ideas that spurred this work. We thank members of the Enquist Lab for feedback on early discussion of these ideas. C.E.D. and A.J.A. acknowledge funding by NASA award 16-HW16_2-0025 and a Google Earth Engine research award, Y.M. by the Jackson Foundation. M.B.J.H. by a KR Foundation grant FP-1503-01714, and B.J.E. by NSF award DEB 1457812. B.J.E. was also supported by a Visiting Professorship Grant from the Leverhulme Trust, UK and an Oxford Martin School Fellowship.

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B.J.E, A.J.A, Y.M., M.B.J.H. and C.E.D. designed the research; B.J.E. and A.J.A. gathered data; A.J.A., M.B.J.H., and C.E.D. carried out simulations; A.J.A. and B.J.E. analyzed the data; B.J.E. and Y.M. carried out the analytical derivations; B.J.E. wrote the first draft of the manuscript; B.J.E., A.J.A., Y.M., M.B.J.H. and C.E.D. contributed to the revisions.

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Correspondence to Brian J. Enquist.

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Enquist, B.J., Abraham, A.J., Harfoot, M.B.J. et al. The megabiota are disproportionately important for biosphere functioning. Nat Commun 11, 699 (2020). https://doi.org/10.1038/s41467-020-14369-y

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• Elephant rewilding indirectly affects the abundance of an arboreal but not generalist savanna lizard

• Christopher E. Gordon
• , Rion E. Lerm
• , Paul Allin
• , Michelle Greve
•  & Jens-Christian Svenning

Biodiversity and Conservation (2021)