Contributions of a global network of tree diversity experiments to sustainable forest plantations.

The area of forest plantations is increasing worldwide helping to meet timber demand and protect natural forests. However, with global change, monospecific plantations are increasingly vulnerable to abiotic and biotic disturbances. As an adaption measure we need to move to plantations that are more diverse in genotypes, species, and structure, with a design underpinned by science. TreeDivNet, a global network of tree diversity experiments, responds to this need by assessing the advantages and disadvantages of mixed species plantations. The network currently consists of 18 experiments, distributed over 36 sites and five ecoregions. With plantations 1-15 years old, TreeDivNet can already provide relevant data for forest policy and management. In this paper, we highlight some early results on the carbon sequestration and pest resistance potential of more diverse plantations. Finally, suggestions are made for new, innovative experiments in understudied regions to complement the existing network.

A global call for sustainable forest plantations

Although the global forest area declined by ca. 13 million ha per year between 2000 and 2010, the forest plantation area actually increased annually by ca. 5 million ha in the same time period, representing ca. 7 %, i.e., 264 million ha, of the global forest area in 2010 (FAO 2010). Afforestation rates may increase further due to incentives for carbon sequestration and the global pledge to protect the remaining natural forests of the world against degradation, e.g., as part of REDD+. Forest plantations already provide up to 33 % of the total industrial roundwood volume harvested annually in the world, and are projected to make up as much as 50 % of the global industrial roundwood production by 2040 (Kanninen 2010). Beyond wood production, plantations also provide a range of other ecosystem services, including carbon sequestration and water retention (Pawson et al. 2013). Moreover, when incorporated into integrated landscape management, plantations can play a large role in achieving biodiversity conservation objectives by offsetting the need to extract resources from natural forests (Paquette and Messier 2010).

Currently, plantation forests are almost exclusively planted as monocultures (Nichols et al. 2006, Box 1). Yet, several reviews published recently provide evidence, from both natural forests and plantations that biomass production and the delivery of other ecosystem services can improve with tree diversity (Nadrowski et al. 2010; Scherer-Lorenzen 2014). Furthermore, global change may increase disturbance frequencies and intensities in both natural forest (Woods et al. 2005) and plantations (Pawson et al. 2013), significantly affecting wood supply chains with severe economic consequences (Hanewinkel et al. 2012). Forest plantations that are diverse in genotypes, species, structure, and function, should be better able to adapt to changing environmental conditions than monocultures (van Hensbergen 2006; Bauhus et al. 2010). This calls for the development of novel, more diversified forest plantations that can improve plantations’ stability, productivity, and delivery of ecosystem services. Since plantations are often established near human settlements, they are the primary window through which society looks at forest management. Changing the way we manage plantations and setting objectives for them can therefore have profound and rapid impacts on the social acceptance of forestry (Paquette and Messier 2013). It has been noted, however, that foresters currently resist establishing mixed plantations, in large parts because of the perception that mixing genotypes and species reduces yield and complicates forest management operations (Carnol et al. 2014).

TreeDivNet, a new global network of tree diversity experiments, responds to the need for a solid, science-based framework for documenting and understanding the benefits and drawbacks of mixed plantations. In this paper, we explain the need for new afforestation trials and present the TreeDivNet network of experimental plantations. We show some early results from the network and formulate suggestions for additional experimental plantations that may cover existing research gaps.

Box 1

Multi-species tree plantations are still relatively rare worldwide, but is this topic important within the forest research communities and is there an increasing interest in the last 10 years? We investigated these questions using the software WORDSTAT 6.0 (Péladeau 2003) by comparing the percentage of abstracts containing the word “plantation” that also contained the words “species mixture, mixed system, mixed plantation, mixed-species plantation or multi-species plantation” between the proceedings of the IUFRO World Congresses1 of 2005 and 2014. In the proceedings of 2014, we found 2426 abstracts of which 267 used the term “plantation”. Of these 267 abstracts, 20 (or 7.5 %) also used at least one of the terms referring to mixed plantation mentioned above. In the proceedings of 2005, we found 1454 abstracts of which 238 used the term “plantation”. Of these 238 abstracts, only 1 (or 0.4 %) used at least one of the terms referring to mixed plantation. This clearly shows that the interest in multi-species tree plantations is increasing, which bodes well for the future of such plantations worldwide.

The need for a twenty-first century generation of forest plantation trials

In the eighteenth and nineteenth century, foresters such as von Carlowitz, Hartig and Cotta developed the concepts of sustainable forest management as a response to the increasing overexploitation of European forests (Morgenstern 2007). To base these concepts upon science, the first long-term silvicultural trials were established to identify the most productive species and provenances to plant in novel forests. The trials were definitely a success for the development of production-oriented management; large-scale forest plantations were established with fast-growing tree species. The trials were often designed as common garden experiments comparing the growth and performance of different species and provenances at one site, i.e., under similar environmental conditions. Despite the lively debate about the advantages and disadvantages of pure versus mixed forests (even in that early era), most of the trials consisted of monocultures or, less frequently, two-species mixtures (Scherer-Lorenzen 2014). Presently, 300 years after von Carlowitz´s proposition of sustainability and given recent advances in biodiversity science (e.g., Cardinale et al. 2012), we need to know which mixtures provide higher levels of biomass production and of other ecosystem services and how environmental conditions affect the relationship between tree diversity and forest functioning, both in space and time.

To address these issues, several scientific approaches are available. Given the long lifespan and size of trees, simulation models that predict ecosystem service output along a range of tree diversities and environmental conditions are an obvious approach. However, such models need parameterization, which is an enormous challenge given how poorly we understand biotic interactions among species. Parameters can be estimated based on experiments or observational studies, but both the types and ranges of tree diversities we seek to study are not always present. Still, highly interesting and relevant work has been accomplished with simulation tools (e.g., Morin et al. 2011). Observational studies are invaluable for providing real-world reference data (Baeten et al. 2013), but also have many drawbacks because tree species composition strongly depends on environmental factors or management. Experiments avoid these issues, but there are still relatively few experiments with replicated stands of mixed species (Scherer-Lorenzen 2014), and many of these use only a small number of (nevertheless commercially important) tree species.

TreeDivNet and examples of its potential to contribute to sustainable forest plantations

In response to the need for in-depth knowledge of the functioning of mixed plantations and the services they provide, tree diversity experiments have been planted worldwide over the past 15 years. These experiments have now been integrated within the global network TreeDivNet (www.treedivnet.ugent.be). The unifying characteristic of TreeDivNet experiments is that tree species are grown in both monoculture and mixtures, and that tree diversity levels are replicated in a randomized design, allowing for the effects of diversity to be tested. Tree diversity experiments can yield reliable estimates of ecosystem functioning as the experimental design controls the levels and range of tree diversity and allows accounting for potentially confounding factors due to site conditions and local environmental gradients. In addition, long-term monitoring of the performance of individual trees and multiple ecosystem processes in experiments will provide a rich record of the development of the forest ecosystem and its overall functioning (see for example Potvin and Gotelli 2008). This will lead to a deeper understanding of the influence of the diversity, composition and structure of a forest on its functioning, and a more complete picture of the relationships between productivity and other ecosystem functions and services. Long-term monitoring will also allow us to better understand how forest diversity, structure, and composition influence forest stability. We will then be able to plant and manage forests in a way that increases their resistance and resilience to, e.g., predicted changes in climate. Different aspects of tree diversity, i.e., species richness, genetic diversity, structural, and functional diversity, will be used as tools to face the key challenges of modern sustainable afforestation.

At present, TreeDivNet consists of 18 experiments, located at 36 sites and in five ecoregions (Fig. 1; Table 1). More than 1 000 000 trees have been planted in the experiments on a total surface area of ca. 800 ha, which makes TreeDivNet one of the largest research infrastructures in ecology worldwide. The oldest experiment (Satakunta, Finland) was planted in 1999. The experiments included in TreeDivNet manipulate woody plant diversity—in terms of species richness (taxonomic diversity), evenness, composition, genetic, and functional diversity—over wide diversity gradients and are designed to allow separation of diversity and identity effects (see Fig. 2 for an example, and Bruelheide et al. 2014). The tree species in the TreeDivNet experiments are both widely planted commercial species, but also many less frequently used species. One important additional component is the inclusion of tree provenances from different regions (e.g., BiodiversiTREE, US; FORBIO, Belgium; and Climate Match, UK), providing a valuable opportunity to test whether assisted migration enhances the services provided by diverse plantations in the face of climate change (Pedlar et al. 2012).

Fig. 1

The 18 experiments of TreeDivNet in the boreal (bo), temperate (te), Mediterranean (me), subtropical (st), and tropical (tr) regions of the world. The dark gray dots represent the IDENT experiment; the light gray dotted ones are the ECOLINK-Salix experiment; the other experiments are in black. See Table 1 for the characteristics of the experiments. Map based on Olson et al. (2001), data from http://www.worldwildlife.org/publications/terrestrial-ecoregions-of-the-world

Table 1

The 18 experiments of TreeDivNet are established around the globe (see Fig. 1) to investigate the relations between different aspects of forest ecosystem functioning and tree diversity: species richness (SR), functional diversity (FD), genetic diversity (GD), phylogenetic diversity (PD), and evenness (EV). See www.treedivnet.ugent.be for more information on the experiments

ID	Ecoregion	Name	Plant year	No sites	No plots	Species pool	Plot size (m2)	Tree diversitya	SR gradient	FD variables	GD gradient
bo1	Boreal	Satakunta	1999	4	163	5	400	SR, GD, PD	1, 2, 3, 5	–	1, 2, 4, 8 clones (Betula)
te1	Temperate	BiodiversiTREE	2013	1	75	16	1225	SR, FD, GD	1, 4, 12	AM, EM fungi	1, 2 provenances
te2	Temperate	BangorDIVERSE	2004	1	92	7	45–196	SR, FD	1, 2, 3	Shade tolerance	–
te3	Temperate	Climate Match	2011	2	177	4	144, 1152	SR, GD	1, 4	–	1, 2, 3, 4 provenances
te4	Temperate	FORBIOb	2010, 2012	3	127	10	1296, 1575, 1764	SR, GD	1, 2, 3, 4	–	1, 3 provenances (Quercus, Fagus)
te5	Temperate	ORPHEE	2008	1	256	5	400	SR, FD	1, 2, 3, 4, 5	Deciduous/evergreen	–
te6	Temperate	Communitree	2009	1	90	1	0.24	GD	–	–	1, 2, 3, 4 half-sib families
te7	Temperate	ECOLINK-Salix	2014	3	99	1	92	GD	–	–	1, 2, 3, 4 clones (Salix)
te8	Temperate	Kreinitz	2005	1	98	6	25	SR, FD	0, 1, 2, 3, 5, 6	Litter decomposition rate	–
te9	Temperate	B-Tree	2013	1	44	4	170–300	SR, FD	1, 2, 4	AM, EM fungi	–
te10	Temperate	BIOTREEb	2003, 2004	4	117	19	300–12 000	SR, FD, EV	1, 2, 3, 4, 6, 10	9 traits	–
te11	Temperate	IDENTb	2009, 2010, 2012, 2013	5	1192	1919	8–16	SR, FD, PD	1, 2, 4, 6, 12	Native/exotic ca. 20 traits	–
me1	Mediterranean	IDENTb	2014	1	308	12	10	SR, FD, PD	1, 2, 4, 6	Evergreen/deciduous drought resistance	–
me2	Mediterranean	Ridgefieldb	2010	1	124	8	447	SR, FD	0, 1, 2, 4, 8	Nutrient acquisition growth form	–
st1	Subtropical	BEF-Chinab	2009/2010	2	566	60	667	SR, GD	0, 1, 2, 4, 8, 16, 24 tree sp. crossed with 0, 2, 4, 8 shrub sp.	Random extinction scenarios and directed scenarios based onSLA and rarity	3–38 half-sib families (for 13 tree species)1 or 4 seed families per species
tr1	Tropical	Agua Salud	2008	1	267	10	1755	SR	1, 2, 5, 6	–	–
tr2	Tropical	Sardinilla	2001/2003	2	32	26	675–2025	SR, FD	1, 3, 6, 9, 18	Shade tolerance	–
tr3	Tropical	Gazi Bay	2004	1	32	3	36	SR	1, 2, 3	–	–
tr4	Tropical	Sabahb	2010	1	124	16	40 000	SR, FD, GD	1, 4, 16	Tree height	2, 4 genera

aExtra treatments investigated: water availability (ORPHEE, IDENT), fertilization with N, P, N + P (IDENT), N deposition and non-native weed cover (Ridgefield), liana removal (Sabah)

bExtensive info on the design of these experiments can also be found in Bruelheide et al. (2014; BEF-China), Hector et al. (2011; Sabah), Perring et al. (2012; Ridgefield), Scherer-Lorenzen et al. (2007; BIOTREE), Tobner et al. (2014; IDENT), and Verheyen et al. (2013; FORBIO)

Fig. 2

Example of the design of one of the TreeDivNet experiments. The FORBIO experiment was established at three sites in Belgium. The tree species diversity per plot ranges from one to four species. The within-plot design is shown for a two-species and a four-species plot. The trees were planted on a 1.5 m × 1.5 m grid, in small monospecific patches of 3 × 3 trees. These patches are arranged in a checkerboard pattern in the two-species mixtures and randomly attributed to the species in the three- and four-species mixtures (see Verheyen et al. 2013 for more details)

TreeDivNet functions according to the guidelines for globally distributed experiments (cf. Borer et al. 2014). At present, the network has no central funding. Participation is entirely voluntary, but has clear benefits for the participants. TreeDivNet offers unique opportunities for multidisciplinary and multifunctional research on the relationship between tree diversity and ecosystem functioning in major forest types around the world and enables synthesis studies across the globe. Thus, TreeDivNet contributes to the lively field of functional biodiversity research, which has delivered a wealth of knowledge about the biotic control of ecosystem functioning over the last two decades. However, most of this knowledge was gained in smaller-stature, shorter-lived vegetation such as grasslands; forests came into the focus of this research field only recently. Despite the young age of most experiments, TreeDivNet can already provide results relevant for policy and management, as illustrated in the following two examples.

Species identity, plot diversity, and mixture composition as determinants of aboveground carbon sequestration

The possibility of using afforestation to create carbon sinks while taking biodiversity concerns into account provides a good example of the potential contributions of experimental tree plantations within TreeDivNet. Sequestering both above and belowground carbon has been recognized in the context of the Clean Development Mechanism of the Kyoto protocol (Thomas et al. 2010), and has gained momentum with the development of an International mechanism for reducing emissions from deforestation and forest degradation known as REDD+ (Cerbu et al. 2011). However, the choice of provenance/genotype and species, each with different carbon sequestration time profiles, and the positive or negative effects of mixtures for maximizing carbon sequestration rates in forest plantations at different sites across the globe are still open to debate.

According to FAO’s Global Planted Forest Assessment database (FAO 2006), the total number of species used in plantations ranges from four in Finland to twenty in China, France, India, and Ukraine. Yet, studies in TreeDivNet experimental plantations suggest that the carbon sequestration rates of tree species that are rarely planted in forestry may be higher than for species that are traditionally planted for wood production. In Sardinilla, Panama, for instance, only one of the four species with the highest carbon stocks after 10 years of growth, Dalbergia retusa, is currently used as a timber-producing species (Fig. 3a). In BEF-China, Choerospondias axillaris, Nyssa sinensis, Triadica cochinchinensis, Melia azedarach, and Schima superba, which are not currently used for commercial timber, were found to sequester more carbon 2 years after planting than the commercially planted timber species Cunninghamia lanceolata or Pinus massioniana. Early observations thus support the presence of species identity effects, which highlights the importance of increasing the number of species used in plantation projects. Nevertheless, widespread application of these new species is probably contingent on their potential use as timber species.

Fig. 3

Aboveground biomass (Mg C ha−1) after 10 years of growth in the Sardinilla experiment (Panama). The common timber species are indicated in green in the figure and underlined here. Species abbreviations are the first letter of the genus and species name: Albizia adinocephala, , Astronium graveolens, , Calycophyllum candidissimum, Colubrina glandulosa, , , Diphysa robinioides (DRO), Enterolobium cyclocarpum, Erythrina fusca, Gliricidia sepium, Guazuma ulmifolia, Hura crepitans, Inga punctata, Luehea seemannii, Ormosia macrocalyx, , Pseudosamanea guachapele, Spondias mombin, . The biomass was calculated using the equation of Chave et al. (2005) equation for tropical moist forest, and mean tree biomass per species was scaled up to 1 ha assuming 1000 trees per plot. Estimations were done for the species represented in the Sardinilla planted forest by at least five individuals

TreeDivNet experiments also allow comparing the provisioning of ecosystem services from mixed as opposed to monoculture plantations. A recent meta-analysis, using data from a TreeDivNet experiment and elsewhere, indicates that woody mixtures sequester at least as much aboveground carbon as the most productive monocultures in any given location (Hulvey et al. 2013). This suggests that plantations could use mixtures of multiple species selected outside of traditional forestry practice to maximize aboveground carbon storage, if the latter would be the primary interest. Furthermore, early TreeDivNet results indicate that the performance of high carbon sequestering species might be contingent upon the diversity level of the plot in which they are growing. In BangorDIVERSE, UK, Alnus glutinosa and Betula pendula were more efficient at storing carbon after 9 years than some traditional timber-producing species, with A. glutinosa performing better in mixture than in monoculture (Fig. 4). In Sardinilla, mixtures established with three and six species overyielded compared with monocultures and this effect of diversity increased with time over 10 years (Sapijanskas et al. 2013). However, variability among plots with the same species richness level also suggests that certain combinations of species are apparently able to sequester more carbon than others.

Fig. 4

Aboveground carbon (Mg C ha−1) after 9 years of growth at the BangorDIVERSE experiment (UK). Species abbreviations are the first letter of the genus and species name: Alnus glutinosa, Acer pseudoplatanus, Betula pendula, Castanea sativa, Fraxinus excelsior, Fagus sylvatica. The biomass was calculated using general European temperate forest equations from Ziania et al. (2005) and site-specific equations from Smith et al. (2013). Mean tree biomass per species was scaled up to one hectare assuming 1000 trees per plot. Biomass estimations were based on the average species diameter of each replicate plot (n = 3)

We propose that, in order to more easily identify species and mixtures that sequester high levels of carbon, relationships between carbon sequestration rates and common life history traits could be useful. Early data collected at TreeDivNet experiments suggest that these relationships may be site specific, as has been found in natural forests (Stegen et al. 2009).

Which mixtures optimize insect pest control in young tree plantations?

Although often less spectacular than abiotic disturbances such as storms or fires, biotic damage can dramatically alter the functioning of forest ecosystems and reduce their productivity. For instance, every year, on average 15–20 % of the trees in European forests are affected by pest and pathogen damage, resulting in increased tree mortality or reduced tree growth. Climate change with increasing temperatures and more frequent drought events is expected to aggravate forest pest damage through increased pest proliferation or reduced plant defense (Jactel et al. 2012). It is therefore critical to better understand the significance of forest diversity for the forest’s resistance to pest insects and its resilience to their outbreaks.

Meta-analyses have shown that, overall, mixed forests are less prone to pest insect damage than monocultures (Jactel and Brockerhoff 2007), supporting the associational resistance hypothesis. This hypothesis states that focal trees surrounded by heterospecific neighbors are less likely to be found and affected by insect herbivores. However, these reviews have several limitations: (1) they focused on the effects of single pest species, whereas the entire community of insect herbivores interacts with the trees; (2) the long-term effects of insect herbivory have not been studied; and (3) the ecological mechanisms underlying associational resistance could not be investigated in detail.

By contrast, the design of the TreeDivNet experiments makes it possible to address these issues. Indeed, early results on diversity–herbivore resistance relationships from BIOTREE (Germany), FORBIO (Belgium), Satakunta (Finland), and ORPHEE (France) indicate that the identity of the focal (Fig. 5) and associated tree species appeared to be more important than plot species richness per se in explaining the effects of tree diversity on insect herbivory damage. Interestingly, there were more cases found for associational susceptibility, which might be due to the young age of the experiments and/or the assessment of all insect damage rather than focus on few pests, as done in other studies. Insect damage is now a staple protocol in most TreeDivNet experiments and so more results over a greater span of conditions will be available soon.

Fig. 5

Species-specific responses of defoliation (chewing + skeletonizing damage) to tree diversity in four TreeDivNet experiments. Green and red arrows indicate reduced and increased herbivory in mixed plots as compared to monocultures, i.e., associational resistance and associational susceptibility, respectively. It was estimated based on the site-specific difference in mean damage on a given species grown in mixtures and mean damage on corresponding monocultures. Data were taken from Setiawan et al. (2014) for the FORBIO experiment and from Haase et al. (2015) for the BIOTREE, ORPHEE, and Satakunta experiment

A recent meta-analysis, which included data from several TreeDivNet experiments, has shown that both phylogenetic relatedness of tree species in mixtures and insect herbivore feeding specialization are important predictors of forest diversity effects on insect pests (Castagneyrol et al. 2014). The degree of dilution of a focal tree species among non-host trees was also important in associational resistance (Castagneyrol et al. 2013). Moreover, reduced host-tree apparency recently emerged as a main driver of resistance in mixed stands as neighboring heterospecific trees can disrupt host-finding behavior in insect herbivores (Castagneyrol et al. 2013). Finally, mixed forests can provide natural enemies with more feeding resources or microhabitats and thus enhance the biological control of pest insects (Riihimaki et al. 2005).

These preliminary findings provide a basis for several recommendations for the design of mixed species plantations that can be more resistant to insect pests: (1) mixing more functionally and phylogenetically dissimilar tree species, such as conifers and broadleaves, can result in a more effective reduction in herbivore damage (Castagneyrol et al. 2014), but (2) a significant reduction in the proportion of host trees in mixtures is required to reduce damage by specialist herbivores (Jactel and Brockerhoff 2007).

Ideas for additional experimental tree diversity plantations

We are now entering the second decade of experimental manipulations of tree diversity. The TreeDivNet experiments have been designed to understand mechanisms and to quantify a large suite of ecosystem functions and services relevant to twenty-first century forest plantations. Gaps remain, however, in both the scale and scope of the existing experiments. We outline some important aspects here to guide future tree diversity experiments (see also Bruelheide et al. 2014).

First, while biodiversity research has made considerable advances on theoretical grounds, there is still a lack of linkages to applied sciences and industrial practices, even though it has been shown that different management types and intensities affect diversity–function relationships (e.g., Weigelt et al. 2009). In addition, the provision of wood is always listed among the ecosystem services a forest, planted or not, can provide. The outreach of next-generation experiments would be tremendously increased if practical issues were added already during the design phase, for example treatment testing and costing different planting patterns, maintenance methods, and harvesting techniques in a multi-species context, both in plantations and in naturally regenerated forests (see also Nichols et al. 2006). There is hence an important need for mixed species demonstration experiments, set-up in collaboration with forest managers and industries, and established at operational scales using available equipment and techniques. This could apply to both forestry and agroforestry systems, including short-rotation coppices and all variations of selection and multi-cohort stands. Moreover, to be practically relevant, future experiments may need to focus more strongly on testing or finding well-functioning genotypic and species compositions.

A second big issue in the design of tree diversity experiments is the scale, both temporal and spatial. Because of the high costs of large plots and the long-term time commitments, most plots in TreeDivNet experiments are, with a few exceptions, ¼ hectare or smaller (Table 1). Many processes affecting forest dynamics, e.g., competition and mortality, are scale dependent, and many of the forest ecosystem services, including the provision of timber, biodiversity, water purification, carbon storage, and recreational opportunities, are supplied at different spatial and temporal scales. Hence, there is an urgent need for tree diversity experiments that capture these larger-scale processes, similar to seminal watershed-level studies such as Hubbard Brook (www.hubbardbrook.org). Studies spanning multiple scales could provide pivotal information regarding the spatial and temporal scales at which forest biodiversity influences ecosystem functions and services. Comparing watersheds with different manipulated tree diversities would be a truly important step forward. Such large-scale experiments could be inspired by a land-sharing vs. land-sparing approach, such as the functional zoning in forestry (e.g., Messier et al. 2009). Furthermore, as effects of biodiversity on ecosystem functioning appear to be time dependent and to grow larger with time (Reich et al. 2012), longer-term studies are also required. While some of our experiments are planned with such long-term temporal perspective, others focus on early phases of establishment. Still missing are experiments where species are planted at different points in time, with pioneer and mid- to late-successional species, which without doubt would enhance our predictive capabilities of diversity effects along successional trajectories.

Third, theory and empirical evidence suggests that biodiversity is particularly important to buffer ecosystems against stressors and to increase their stability (Loreau and de Mazancourt 2013), but to date few TreeDivNet experiments explicitly incorporate stress as an experimental factor. The ORPHEE (France) and IDENT (Canada, Italy) experiments have incorporated a water availability treatment, and the IDENT site in Germany and Ridgefield (Australia) incorporate nutrient addition treatments, but the inclusion of other stressors would clearly broaden the inferences of TreeDivNet experiments. For example, results from smaller-scale experiments have shown that including factors such as mammalian herbivory (Cook-Patton et al. 2014) and fire (Adair et al. 2009) can influence the direction and magnitude of diversity effects.

Fourth and finally, although TreeDivNet includes experiments in tropical, temperate, and boreal systems, the distribution of experiments is skewed as relatively few are located in other important biomes/climate regions. For example, only two experiments lie in Central/South America and one in Africa, but these are not located in the largest forested areas and biodiversity hotspots on either continents (i.e., in the Amazon or Congo Basin). In addition, despite covering large areas on the globe, shrublands are also underrepresented.

The foresters of the nineteenth century demonstrated an impressive long-term perspective when they established the first forestry trials to find answers to the pressing questions of that time. Globally distributed experiments, such as TreeDivNet, could become new important research pillars to face the great challenges that global changes will put on forest ecosystems and to deliver highly relevant guidelines for forest policy and management worldwide. This is particularly important since plantations are likely to increase tremendously in area worldwide in the next decades.