Species composition and forest structure explain the temperature sensitivity patterns of productivity in temperate forests
- 1Helmholtz Centre for Environmental Research – UFZ, Permoserstr. 15, 04318 Leipzig, Germany
- 2German Centre for Integrative Biodiversity Research (iDiv) Halle-Jena-Leipzig, Deutscher Platz 5e, 04103 Leipzig, Germany
- 3University of Osnabrück, Barbarastr. 12, 49076 Osnabrück, Germany
Correspondence: Friedrich J. Bohn (firstname.lastname@example.org)
Rising temperatures due to climate change influence the wood production of forests. Observations show that some temperate forests increase their productivity, whereas others reduce their productivity. This study focuses on how species composition and forest structure properties influence the temperature sensitivity of aboveground wood production (AWP). It further investigates which forests will increase their productivity the most with rising temperatures. We described forest structure by leaf area index, forest height and tree height heterogeneity. Species composition was described by a functional diversity index (Rao's Q) and a species distribution index (ΩAWP). ΩAWP quantified how well species are distributed over the different forest layers with regard to AWP. We analysed 370 170 forest stands generated with a forest gap model. These forest stands covered a wide range of possible forest types. For each stand, we estimated annual aboveground wood production and performed a climate sensitivity analysis based on 320 different climate time series (of 1-year length). The scenarios differed in mean annual temperature and annual temperature amplitude. Temperature sensitivity of wood production was quantified as the relative change in productivity resulting from a 1 ∘C rise in mean annual temperature or annual temperature amplitude. Increasing ΩAWP positively influenced both temperature sensitivity indices of forest, whereas forest height showed a bell-shaped relationship with both indices. Further, we found forests in each successional stage that are positively affected by temperature rise. For such forests, large ΩAWP values were important. In the case of young forests, low functional diversity and small tree height heterogeneity were associated with a positive effect of temperature on wood production. During later successional stages, higher species diversity and larger tree height heterogeneity were an advantage. To achieve such a development, one could plant below the closed canopy of even-aged, pioneer trees a climax-species-rich understorey that will build the canopy of the mature forest. This study highlights that forest structure and species composition are both relevant for understanding the temperature sensitivity of wood production.
Climate change alters wood production by modifying the rates of photosynthesis and respiration rates of trees (Barber et al., 2000; Luo, 2007; Peñuelas and Filella, 2009; Reyer et al., 2014). Changes in forest productivity have been observed in past decades all over the world (Nemani et al., 2003; Boisvenue and Running, 2006; Seddon et al., 2016). The carbon stock of forests and their role as carbon sinks are therefore changing. These findings have stimulated discussions about whether forest management strategies can be adapted to reduce forest vulnerability to climate change, support recovery after extreme events and foster the carbon sink function of forests (Spittlehouse and Stewart, 2004; Spittlehouse, 2005; Bonan, 2008).
Wood production is influenced by several factors, such as CO2 fertilization, nitrogen deposition, precipitation and temperature (Barford et al., 2001). For instance, rising CO2 increases water use efficiency of forests (Keenan et al., 2013), which could compensate negative effects of climate change on European forest growth (Reyer et al., 2014). Another important process is fertilization (De Vries et al., 2006, 2009). Due to depositions of nitrogen in the second half of the last century, wood production had increased in European forests (Solberg et al., 2009). However, temperature modifies photosynthesis, respiration and growth rates of trees (Dillon et al., 2010; Piao et al., 2010; Wang et al., 2011; Jeong et al., 2011; Heskel et al., 2016). In the temperate biome, positive effects on wood production (e.g. Bontemps et al., 2010; Delpierre et al., 2009; Pan et al., 2013; McMahon et al., 2010) as well as negative ones have been found (e.g. Barber et al., 2000; Jump et al., 2006; Charru et al., 2010). However, it remains unclear why forests react differently to temperature change.
In addition to the influence of climate variables, wood production is also affected by internal forest properties. These properties can be grouped into two types: properties which describe forest structure and those which describe species composition (Fig. 1). For instance, changes in productivity can result from changes in basal area (Vilà et al., 2013), in leaf area index (Asner et al., 2003) or in the heterogeneity of tree heights within a forest (Bohn and Huth, 2017). Furthermore, wood production often increases with the increasing number of species (Zhang et al., 2012; Vilà et al., 2007).
Forest stands, which differ in their forest properties, might respond differently to the same climate change (Huete, 2016). For instance, the positive effect of increasing temperature on wood production fades with forest age in temperate deciduous forest (e.g. McMahon et al., 2010; Bontemps et al., 2010), and Morin et al. (2014) showed that higher diversity buffers the effect of inter-annual variability on wood production. However, these studies include only a few forest properties and rarely include properties related to both species composition and forest structure. Hence, it is unclear how these forest properties influence wood production change due to temperature rise and which forests will benefit from rising temperatures.
As far as we know, there is no data set available that covers forests, differing in structure and diversity, under almost identical climatic conditions. Even if a larger number of forest stands were available, it would be difficult to manipulate, for instance, temperature while keeping all other climate variables constant. Forest simulation models offer an alternative to the analysis of field experiments. Such models are able to estimate wood production under different climate conditions (e.g. Lasch et al., 2005; Bohn et al., 2014). For instance, Reyer et al. (2014) investigated the effect of climatic change on forests by simulating 30-year time slices of a range of different future climates for 135 inventoried forest stands. There are also model-based studies, which systematically analysed the effect of species diversity on productivity and stability over long periods (Morin et al., 2011, 2014). However, disturbed or managed forest stands and the influence of climate change have not been included in these analyses.
In this study, we therefore propose a new simulation-based approach. First, we generate a large number of forest stands covering various forest structures and species compositions (for up to eight temperate tree species). Annual aboveground wood production (AWP) is then calculated for all forest stands based on climate time series. These time series differ in the mean annual temperature and the intra-annual temperature amplitude. We aim to analyse how productivity of forest stands (AWP) is influenced by (i) increasing mean annual temperature and (ii) increasing intra-annual temperature amplitude. Furthermore, we address the question of which forest stands will benefit most from rising temperatures.
To analyse the effect of temperature on the productivity of forest stands, we applied the “forest factory” model approach (Bohn and Huth, 2017). The forest factory generated 370 170 different forest stands (see Sect. 2.1) and allowed the estimation of AWP under various climate time series (see Sect. 2.2). The 320 scenarios differed in mean annual temperature and annual temperature amplitude. Finally, we calculated the forest-stand-specific sensitivity of productivity to temperature change as the relative change of wood production per temperature change of 1 ∘C (see Sect. 2.2). To relate these sensitivities to forest structure and species composition, we characterized every forest stand with five properties (see Sect. 2.4). We analysed the influence of the five forest properties on temperature sensitivity using boosted regression trees (see Sect. 2.5). Finally, we analysed which combination of forest properties resulted in the highest sensitivity values for different successional stages (see Sect. 2.6). All analysed data are available in the Supplement to this manuscript.
2.1 The forest factory approach
The forest factory creates forest patches based on different stem size distributions and species mixtures. We used 15 stem size distributions covering a gradient from young to old and disturbed to undisturbed forests. Species mixtures included all 256 possible combinations of Pinus sylvestris, Picea abies, Fagus sylvatica, Quercus robur, Fraxinus excelsior, Populus x canadensis, Betula pendula and Robinia pseudotsuga. We used the species parameter set and algorithms of the FORMIND model version for temperate forests within the forest factory (Bohn et al., 2014; Fischer et al., 2016). A total of 100 forest patches of each combination were built.
To generate forest patches, the forest factory randomly chose trees from the stem size distribution, assigned a species identity and planted them within a patch of 400 m2 size. To place a tree within a patch, the following rules must be met: (i) there must be enough space available for crowns of every tree, and (ii) every tree in the forest must have a positive productivity under its environmental conditions (light, temperature, water).
We used climate time series from the year 2007, measured at Hainich National Park, central Germany. We assumed this time series to be a typical example for a temperate year (in principle, it is possible to use climate data from any other location). In contrast to an artificially generated climate, this climate is perfectly physically consistent (with regard to light, air temperature and precipitation).
In a few cases, not all species of the mixture could be placed within a patch by the algorithm, so we rejected such forests. We ended up with 370 100 forest stands. For more details regarding the forest factory, see Bohn and Huth (2017).
2.2 Wood production
The calculation of AWP of trees was based on algorithms of the model FORMIND (Bohn et al., 2014; Fischer et al., 2016). In this model, the wood production of a single tree is calculated as the difference between climate variables driven respiration rates and photosynthesis. The photosynthesis rate (Ptree) results from the crown size, self-shading within the crown and available light at the top of the tree. The available light depends on the radiation above the canopy, reduced by the shading of larger trees within the forest stand. Furthermore, productivity can be limited due to air temperature and available soil water, which is expressed by the photosynthesis-limiting factor ϕ for each tree (Gutiérrez, 2010; Fischer, 2013; Bohn et al., 2014). Available soil water within the stand results from precipitation, interception and evapotranspiration of trees and runoff.
One part of the photosynthesis production of a tree (Ptree) is allocated to its maintenance respiration (and to non-wood tissues; Rm). Maintenance respiration depends on tree biomass and temperature ψ (Piao et al., 2010). The remaining organic carbon is transformed into newly grown aboveground wood (AWPtree) and a proportional growth respiration (rg).
2.3 Climate sensitivity
To generate a set of 320 annual climate time series, we selected daily climate measurements of the Hainich station in central Germany between the years 2000 and 2004. This time series includes mean daily radiation, precipitation and air temperature (see Appendix A1, Fig. A1). We separated these time series into five distinct time series of 1-year length. First, we increased or decreased the mean annual temperature of each year by adding or subtracting 0.5 ∘C steps between −1.5 and +2 ∘C. Second, we changed the amplitude of the annual temperature cycle for these time series variation of each year. To do so, we modified the standard deviation of each year by 4 % steps between −12 and +16 %. We ended up with five sets of climate time series (of 1-year length) that differ in temperature, precipitation and radiation. Each of these five sets includes 64 time series, which differ only in temperature (see Appendix A1, Fig. A2). Temperature change was quantified using two indices: (i) mean annual temperature and (ii) annual temperature amplitude, which described the 95 % interquartile range of all daily temperature values of a given year. We did not model the effects of nitrogen and CO2 fertilization (as both do not vary strongly within 1 year) or extreme anomalies (e.g. pathogen attacks) on wood production. Figure 2a–c show the AWP for different annual temperatures for three different forest stands.
We analysed the sensitivity of every forest stand to temperature change following the approach of Piao et al. (2010). For every forest stand, a general linear model was fitted relating wood production mean annual temperature (MAT) and intra-annual temperature amplitude (Q95), as well as the nuisance parameter year.
For every forest, we calculated the relative change of productivity resulting from an increase of 1 ∘C:
In our analysis, we excluded all forests stands for which AWP turns negative if the temperature rises by 1 ∘C (this occurs in 2 % of all stands).
We also determined the sensitivity of forests to temperature change using the German forest inventory to validate our results. However, the inventory does not include leaf area index (LAI) measurements. We therefore assumed the basal area as a proxy for LAI, and we selected subsamples of forests stands with similar structure (basal area, tree height heterogeneity, forest height and same species mixtures). In addition, we used elevation as a proxy for mean annual temperature, assuming temperature changes of 0.65 ∘C per 100 m on average (Foken and Nappo, 2008). Only in the case of spruce and beech monocultures did we find enough data to calculate SIMAT values for several forest structures (for more details, see Appendix A3, Fig. A3).
The comparison between the SIMAT estimation based on the German forest inventory with SIMAT values of corresponding forests from the forest factory showed quite good agreement (R2=0.65). However, the simulated SIMAT values of the forest factory slightly overestimated the sensitivity compared to the inventory-based values (Fig. 3). This might be explained by the difference in the methods used because, in the case of the inventory, we used basal area instead of LAI and altitude instead of temperature. Another explanation could be that in our approach the climate time series showed relatively high and regular precipitation. In the German forest inventory, warmer sites might be more frequently exposed to water stress, which then reduced the SIMAT values.
2.4 Five forest properties to describe forest stands
We used three indices to describe the forest structure: LAI, maximum forest height (Hforest), which corresponds to the height of the largest tree in a forest stand, and tree height heterogeneity (θ), which was quantified by the standard deviation of the tree heights. To describe species composition, we used Rao's Q and species distribution index (ΩAWP). Rao's Q quantified functional diversity based on species abundances and differences in species traits (Botta, 2005, for details, see Appendix A2). ΩAWP analysed the optimal location of species within the forest structure. ΩAWP is defined as the ratio of the forest's productivity to the maximum possible productivity of the forest without changing tree sizes or number (Bohn and Huth, 2017). Hence, the maximum productivity can be obtained by varying only the species identities of trees in the forest stand. We changed the assigned species of each tree until we found the optimal species for each individual tree and its specific environmental condition. All five indices were nearly uncorrelated for the investigated forest stands (Appendix A2, Table A1).
2.5 Boosted regression trees
We applied boosted regression trees to quantify the influence of the five forest properties on SIMAT and SIQ95. Boosted regression trees are a machine learning algorithm using multiple decision (or regression) trees. It is able to address unidentified distributions (De'Ath, 2007; Elith et al., 2008). Each model was fitted in a forward stage-wise procedure to predict the response of the dependent variable on (SIMAT or SIQ95) to multiple predictors (tree height heterogeneity, forest height, LAI, Rao's Q and ΩAWP). To omit an overfitting with regard to maximal forest height, we classified forest stands into 18 classes. Each class had a width of 2 m, starting with 4 to 6 m and finishing with 36 to 38 m. The boosted regression trees tried an iterative process to minimize the squared error between predicted SI values and those of the data set. Hereby, part of the data were used for a fitting procedure and the rest was used for computing out-of-sample estimates of the loss function (Ridgeway, 2015). This boosted regression tree analysis was performed in the R package gbm 2.1.1 (Ridgeway, 2015).
We used a quarter of the data (randomly sampled) for the machine learning procedure. To get the best model, we varied the following four parameters of the boosted regression tree algorithm: learning rates (0.1, 0.05 and 0.01), the bag fractions (0.33, 0.5 and 0.66), the interaction depths (1, 3 and 5) and the cross validation (3-, 6- and 9-fold) assuming a Gaussian error structure (the default setting). The best-fitted boosted regression tree for both SIMAT and SIQ95 showed a learning rate of 0.1, a bag fraction of 0.66, an interaction depth of 5 and a 3-fold cross validation. These two models were used for all further analyses. The remaining 75 % of the data were used to validate the fitted boosted regression tree algorithm.
2.6 Finding the forest stands for different successional stages that benefit the most increasing temperatures
Here, we assumed forest height as a proxy for the successional stage of a forest. In every height class, we selected those 5 % of forests that showed the highest sensitivity values (SIMAT and SIQ95). We removed the forest height classes between 10 and 14 m, as they only contained only 15 forests. For all other classes, we analysed the relationship between height class and the forest properties (ΩAWP, Rao's Q, LAI and tree height heterogeneity).
We analysed the sensitivity of productivity (AWP) to temperature for forest stands that differ in forest properties (species distribution index (ΩAWP), functional diversity (Rao's Q), tree height heterogeneity (θ), forest height class and LAI). The annual AWP was estimated for each forest stand using 320 different climate time series. We then quantified the changes in productivity resulting from changes in mean annual temperature (SIMAT) and intra-annual amplitude (SIQ95). For the analysed forest stands, the average SIMAT is 1.5 % ∘C−1 and the average SIQ95 is −5.4 % ∘C−1 (see also the frequency distribution in Appendix B1, Fig. B1).
With a boosted regression tree algorithm, we analysed how the five forest properties influence the temperature sensitivity of forests. To validate the fitted boosted regression tree algorithm, we compared SI values, which are not used for the fitting, with the SI value predicted by the boosted regression tree algorithm (Fig. 4). The sensitivities to mean annual temperature change (SIMAT) correlated very well (R2 of 0.84) and showed a low root mean squared error (RMSE) of ±2.9 % ∘C−1 (see Appendix B2, Fig. B3). The RMSE even decreased to ±1.5 % ∘C−1 if a subset of the forest stands was analysed that showed SIMAT values larger than −5 % ∘C−1 (90 % of the data). The accuracy of the sensitivities to temperature amplitude change (SIQ95) was even slightly better. In addition, a subset that included SIQ95 values larger than −15 % ∘C−1 (93 % of the data) showed a RMSE of only ±1.1 % ∘C−1 (see Appendix B2, Fig. B4).
According to boosted regression tree analysis, ΩAWP was the most relevant forest property to explain temperature sensitivities (relative influence of 87 % for SIMAT and 89 % for SIQ95; see also Appendix B2, Fig. B2). However, the influence of ΩAWP on temperature sensitivity flattened out for high ΩAWP levels (Fig. 5). The second relevant forest property was forest height (Hforest). Forests with heights between 25 and 30 m benefited the most from increasing mean annual temperatures. The other three properties (LAI, Rao's Q and tree height heterogeneity) had a low influence on SIMAT.
Both sensitivity indices showed similar relationships to the five forest properties. However, an increase in annual temperature amplitude always reduced productivity, whereas increasing mean annual temperature could result in a positive effect on wood production. To detect those stands that benefit the most from increasing temperature, we selected the 5 % of forest stands that showed the highest SIMAT values in each forest height class (Fig. 5). In all forests classes, we found forest stands that would benefit from increasing temperatures. Analyses of their forest properties revealed that the ΩAWP levels were always high. Young forests (low forest height), which had a positive temperature sensitivity, showed low functional diversity and low tree height heterogeneity (θ). For older forests (of intermediate and high forest height) with positive temperature sensitivity, we found an intermediate level of functional diversity. Interestingly, for three variables (Rao's Q, tree height heterogeneity and LAI), the relationships changed their character between young and intermediate forest heights. We obtained similar simulation patterns for SIQ95 (Appendix B3, Fig. B5).
3.1 Understanding the patterns
3.1.1 The influence of forest structure on temperature sensitivity
Forest structure affects the wood production of single trees in two ways. First, it determines the amount of light available to each individual tree, and second, the size of trees influences their photosynthesis and respiration rates (Fig. B6). Hence, based on the height of a tree and the amount of light available to it, it was possible to calculate its SI values (for a detailed discussion of these calculations, see Appendix B4).
In even-aged forests, all trees have the same height and receive full light (e.g. Fig. 6; forest C). In our study, such forests showed a bell-shaped relationship between forest height and temperature sensitivity (Fig. 6; SI values for 100 % available light depending on tree height).
In the case of a forest consisting of trees of different heights, smaller trees receive less light due to shading. Note that, even if trees received less light, the bell-shaped relationship between tree height and productivity persisted (Fig. 6). Two cases will be discussed (assuming identical LAI as forest C; Fig. 6). In the first case, all trees have not yet reached their maximal SI values (Fig. 6; forest A); in the second case, all trees have already passed their maximal SI values (Fig. 6; forest B). In the case of forest A, trees in the shade of larger trees always had lower SI values if they belonged to the same species (see Appendix B4). Hence, the temperature sensitivity level of this forest was lower than the sensitivity of an even-aged forest, whose trees have the same size as the largest tree in forest A (Fig. 6; tree 1). Hence, if maximal SI values were not reached, increasing height heterogeneity decreased SI values of a forest.
In forest B (Fig. 6), SI values of the shaded trees can be similar (or even higher) than the SI value of the largest trees in the forest (SI values of tree 1 show similar levels to trees 2, 3 and 4 in forest B; Fig. 6). Hence, if maximal SI values were passed, increasing tree height heterogeneity resulted in similar (or even more positive) temperature sensitivity levels compared to even-aged forest trees (an even-aged forest consisting only of trees similar to tree 1 of forest B in Fig. 6). These general considerations explain the change from low levels of height heterogeneity in young forests to a more heterogeneous structure in the analysis of those forests, which will benefit from increasing temperature (see Fig. 5d).
3.1.2 The effect of species composition on temperature sensitivity
In this study, we use the new ΩAWP index called the species distribution index (Bohn and Huth, 2017). ΩAWP is the ratio between current AWP and the highest possible AWP of the forest which can be reached due to shuffling of species identities. Its huge importance for forest temperature sensitivity might be illustrated by the following considerations. If species are unfavourably distributed within the forest (low ΩAWP), the AWP of the forest is low.
Increasing functional diversity (Rao's Q) stabilized the forests' sensitivity to temperature. This corresponds to results of Morin et al. (2014) and the theoretical consideration of Yachi and Loreau (1999). The analysis of the single species can give additional insight into the mechanisms behind those species that benefited the most from temperature increase, which were deciduous trees under most conditions. This is reasonable as warmer regions host more deciduous species than needleleaf species. The highest functional diversity (Rao's Q), on the other hand, occurred in mixtures of deciduous and needleleaf trees (Appendix B5, Fig. B7). As only two needleleaf species were considered here in the species pool, low Rao's Q values were dominated by mixtures of deciduous trees. Such deciduous tree mixtures mostly benefited from temperature increases. In contrast, mixtures with high Rao's Q values, which mostly included both functional types, reacted more poorly (Fig. 4; Appendix B5, Fig. B7).
We developed two diagrams that show the species with the highest temperature sensitivity and with the highest productivity for different conditions (available light and height of a tree) (Fig. 7). Interestingly, the species with the highest productivity differed from the species that benefit most from rising temperatures in many cases. This has important implications. The highest benefit due to increasing temperatures was obtained by forests with high but not maximal ΩAWP (Fig. 5). Additionally, deciduous trees benefited more than coniferous trees from rising temperatures (Fig. 7, Appendix B5, Fig. B7). Hence, young forests should consist of deciduous trees (compare Figs. 6 and 7; forest A), although the highest productivity values are found for coniferous trees (Fig. 7; forest A). Forests including large trees obtained the highest sensitivity values if intermediate-sized trees differed in their species identity from the largest trees (Fig. 7).
4.1 The study design
In this theoretical study, we present a new climate sensitivity analysis (with regard to temperature) of AWP. This approach extends field observations and long-term model simulations, as it allows the analysis of existing forests but also of those that might exist in the future due to management changes and/or disturbances. Our approach includes only forest stands in which every tree has positive productivity and enough space for its crown. Hence, it is impossible, for instance, that light-demanding species grow below a closed canopy or forests are overcrowded. However, the data set also includes a few very unusual stand structures or species combinations, which cannot emerge in a natural system, but may result from disturbances or management. In the case of field observations, it is difficult to explore the influence of a single climate variable (e.g. temperature) on one target variable (e.g. AWP), as in most cases, several variables are altered at the same time (see also Appendix A3). Process-based models are one option to analyse such relationships and separate these effects. The simulation of AWP with the FORMIND model in temperate forests has been successfully compared to eddy flux sites (Rödig et al., 2017b), the national German forest inventory (Bohn and Huth, 2017) and European yield tables (Bohn et al., 2014).
An advantage of the forest factory approach is the huge set of various forests stands that can be analysed. The data set includes forest stands that often occur in temperate forests (even-aged spruce, pine and beech stands). However, it also includes hypothetical ones that could occur through alternative forest management or disturbances (fire, bark beetles, etc.). Hence, our data set of forest stands covers a much larger variety of forest property combinations compared to long-term forest simulations with the focus on natural forests in their equilibrium state (e.g. Morin et al., 2011) or on monocultures (e.g. Reyer et al., 2014). Long-term simulations with ecosystem models, which process modelled climate projections, face a trade-off between cascade uncertainty and path dependency (Wilby and Dessai, 2010; Reyer et al., 2014). The accumulations of model uncertainties over such a process chain result in increasing uncertainty. Our study design tries to minimize this uncertainty and omit path dependencies by including only those processes that might be relevant for the research question. In this study, for instance, we omit the effect of climate change on regeneration and mortality. Furthermore, using several climate variables as model inputs but only analysing the effect of one variable might lead to incorrect interpretations of its effect. For example, temperature and radiation often correlate, and both might increase productivity. Therefore, in this study, we only vary one variable in all five sets of time series. This guarantees that there are no relationships between the target climate variable and the remaining climate variables.
As an increase in global mean temperature of 1.5 to 2 ∘C can hardly be avoided, even under the Representative Concentration Pathway (RCP) 2.6 climate scenario (IPCC, 2013), this study focuses on temperature change. This RCP scenario predicts only small changes in annual precipitation levels for temperate regions. Hence, our approach focuses only on the effect of temperature change on wood production. However, this might be critical for the analysis of strong temperature changes (e.g. RCP8.5) which will result in an increased incidence of drought and changes in the annual temperature cycles and a strong change in CO2. Such more complex scenarios should be analysed in future studies. Further, we neglect the effect of time lags (e.g. bud building in the previous year). However, it is possible to extend the used time series to analyse the behaviour of the forest over longer time periods and study not only productivity but also effects on regeneration or mortality.
To characterize the annual temperature cycles, we used two variables: mean annual temperature and intra-annual temperature amplitude. Both variables can be varied independently. In the case of higher mean annual temperature, we observe an elongation of the vegetation period. This leads to higher forest productivity (if other resources are not limiting (Luo, 2007) and explains why SIMAT is often positive. However, warmer summer temperatures can also lead to a decline in wood production due to an increase in respiration. In the case of increasing intra-annual temperature amplitude, more days with extreme temperatures will occur in a year. Thus, an increase of 1 ∘C−1 of intra-annual temperature amplitude will increase respiration more strongly compared to an increase of 1 ∘C−1 of mean annual temperature. Hence, the increase of intra-annual temperature amplitude normally has negative effects on the productivity (negative SI values).
The temperature sensitivity values obtained here are in the same range as those found for temperate ecosystems in heating experiments (Lu et al., 2013, 4.4 ± 2.2 % ∘C−1). Within the 16 analysed studies reviewed by Lu et al. (2013), the experimental plots show almost identical environmental conditions (soil, radiation and precipitation) and species composition. To heat the plots, greenhouses or infrared heaters were used. Another study, based on natural forest stands in New Zealand, found an AWP increase of between 5 and 20 ∘C−1 for forests, assuming no change in forest structure and species composition (Coomes et al., 2014). The analysed plots were spread throughout New Zealand, and warmer temperatures coincided with higher radiation (Mackintosh, 2016). Hence, the analysed temperature effect also includes the influence of radiation. In our setting, however, the influence of temperature is independent of radiation (Lu et al., 2013, as in). We also found a good correlation between SI values derived from growth measurements of the German forest inventory and simulated SI values based on the forest factory (Fig. 3, Appendix A3, Fig. A3).
4.2 Implications for forest management
Our findings might be relevant for future management strategies for temperate forests. Specifically, our new understanding of which species benefit most from rising temperatures (Fig. 6) suggests possible strategies, e.g. replacing spruce monocultures with mixtures of deciduous trees. Further, based on the analysis of which forest structure benefits most from rising temperatures (Figs. 4, 5, 6), early-stage even-aged forests should include mainly pioneer species. In the mature stage, we predict a positive effect of temperatures on wood production for a mixture of climax species including different tree sizes. These climax species could be planted below the canopy of the pioneer species in young forests. In our approach, we do not simulate the establishment of very young trees. However, during the conversion between these two forest types, one big challenge might be the removal of the pioneer trees without damaging the young trees that will build the mature forest.
4.3 Implications for global vegetation modelling
Most global vegetation models represent vegetation as fractional cover of different plant functional types within a grid cell (e.g. Lund–Potsdam–Jena (LPJ); Sitch et al., 2003). Only a few global vegetation models include a more detailed representation of vegetation structure and functional diversity (Sato et al., 2007; Scheiter et al., 2013; Sakschewski et al., 2016). It would be interesting to perform the analysis presented here with global vegetation models which include structure to better understand the mechanisms driving forest systems' sensitivity to climate change.
Besides the global vegetation models, forest gap models, which have been restricted to local stands, are now able to simulate forest dynamics in regions or even entire continents (Seidl and Lexer, 2013; Rödig et al., 2017a). Studies using global vegetation models or large-scale forest gap models simulate natural succession. Our analysis indicates that natural and managed (or disturbed) forest systems, which differ in forest structure, might react differently to climate change. Hence, we suggest considering forest structure in future analyses of global vegetation. Such information on forest structure might be derived from remote sensing.
The temperature sensitivity of wood production in temperate forests is influenced by forest structure and species diversity as our study showed. The species distribution index (ΩAWP) and forest height seem to be the most important forest properties influencing temperature sensitivity.
Temperate forests that benefit most from temperature rise are those which consist of even-aged deciduous pioneer species in the case of young forests; mature forests benefit most if tree height heterogeneity is large and the forest includes different deciduous climax species.
This study also attempts to explain why certain forest types will decrease their productivity and others will not. Our findings highlight the importance of forest structure for future studies investigating wood production under climate change.
The R workspace which includes the data set of the analysed forests (“foreststands”) and the calculated SI values (“SIValues”) can be found in the Supplement to this paper.
A1 Climate data
The construction of the 320 climate time series is based on measured climate time series of the eddy flux Hainich station in central Germany (Knohl et al., 2003) for the years 2000–2004 (Fig. A1). Mean annual temperature of these 5 years does not correlate with the annual precipitation sum, nor with the mean annual radiation (Fig. A2). Radiation and precipitation within these years correlate quite well (Pearson's r=0.73).
A2 Forest properties
We use three forest properties to describe forest structure (tree height heterogeneity (θ), forest height class and LAI) and two properties to describe species diversity (Rao's Q describes functional diversity and ΩAWP describes suitability). The calculation of Rao's Q is based on 12 species-specific parameters which are relevant for productivity (AWP) and species abundance (based on crown area). None of the properties correlate (Table A1).
A3 Validation with the German forest inventory
We analysed the influence of forest structure on temperature sensitivity within the German forest inventory (beech monocultures and spruce monocultures. Tree height was used to calculate forest height (Hforest) and tree height heterogeneity (θ). We replaced LAI, which is not measured, by basal area (both properties correlate quite well in the forest factory data set; R2=0.74). The forest stands of each species were classified into six structure classes: three classes which are based on the height of the largest tree in the forest stand (10–15, 20–25 and 30–35 m) and two classes representing different tree height heterogeneities (0–1 and >1.6 m). Only plots that are located on flat terrain (slope of less than 15 %) and have a maximum stem diameter of 0.5 m) were analysed. A linear model was fitted to the data of every class using basal area and elevation as input variables to predict AWP.
B1 Frequency distribution of sensitivity values
The analysed forest stands show a large range of temperature sensitivity levels, which reach up to 8.5 % ∘C−1 in the case of SIMAT (Fig. B1a). This means that one forest increases its productivity by 8.5 % due to an increase in the mean annual temperature of 1 ∘C. In the case of the annual temperature amplitude, the best forest reduces its productivity by −0.5 % ∘C−1 (Fig. B1b). The mean SIMAT is 1.5 % ∘C−1 and the interquartile range (iqr) ranges from 1.6 to 5.2 % ∘C−1. The mean SIQ95 is −5.4 % ∘C−1 and the iqr ranges from −5.2 to −2.2 % ∘C−1.
B2 Analysis with boosted regression trees
Boosted regression trees provide information about the underlying relationship between input variables (here forest properties) and output variables (here SI values). Several techniques were developed to visualize and interpret the high-dimensional relationship of input and target variables (Friedman, 2001). The comparisons between SI values of the forest factory and predicted SI values (based on the five properties as input), show a very high agreement (Figs. B2 and B3). The obtained vertical patterns for SIMat (0) and SIQ95 (−6 % ∘C−1) are probably artefacts of the boosted regression tree algorithm.
Other commonly used visualizations of the relationship of input and target variables are partial dependency plots (Fig. 4). These plots show the influence of an input variable on the target variable considering the influence of all input variables which have higher relative importance. In our study, the most important variable is ΩAWP; hence, the first plot shows the relationship between suitability and SI values. The second relationship (forest height and SI values) is based on the residuals of the first relationship (here between SI values and ΩAWP; Becker et al., 1996). Although a collection of such plots can seldom provide a comprehensive analysis of the boosted regression trees, it can often produce helpful hints, especially if variables show very low correlations, as in this study.
Forest stand properties with highest SIQ95 values over a forest height gradient
The analysis of those forests, which lie above the 95th percentile of SIQ95, depending on forest height, shows almost the same pattern as the identical analysis of SIMAT (compare Fig. B4 with Fig. 5).
B4 SI values of single trees
To understand the origin of the SI values, we make the following assumptions. An increase of 1 % ∘C−1 always results in an increase of 8.6 % of the respiration rate in the model (Fig. B5b; Piao et al., 2010). The positive effect of a temperature increase of 1 % ∘C−1 on the photosynthesis rate varies between the years due to the assumed species-specific bell-shaped relationship (Fig. B5a). In the case of deciduous trees, the length of the vegetation period (leaf onset to fall) additionally affects the annual photoproduction (e.g. Haxeltine and Prentice, 1996; Luo, 2007; Horn and Schulz, 2011; Gutiérrez and Huth, 2012; Sato et al., 2007). If the photosynthesis rate is much larger than the respiration rate (high AWP; for instance, low ratio of maintenance respiration to photosynthesis under full light in Fig. B6b), the positive effect of temperature on photosynthesis causes an increase of AWP in some simulated years. If both rates show the same magnitude (ratio of maintenance respiration to photosynthesis under full light is close to 1 in Fig. B6b), higher temperatures increase respiration more than photoproduction (in most years), which results in a decrease of AWP.
B5 Functional diversity and temperature sensitivity
To analyse the effect of functional diversity on temperature sensitivity, we first calculated SIMAT for every species depending on tree height and light availability (as done for pine trees in Fig. 6). Then, we calculated a mean SIMAT value for each species mixture for all light–height combinations. Finally, we averaged those SI values which were larger than −7.5 % ∘C−1 () and calculated the Rao's Q of the mixtures (based on equal abundances). The highest values were found for deciduous forests (Fig. B7). Mixed forests with deciduous and needleleaf trees showed lower values than the deciduous forests but higher Rao's Q values.
The supplement related to this article is available online at: https://doi.org/10.5194/bg-15-1795-2018-supplement.
FJB, FM and AH conceived of the study. FJB implemented and analysed the simulation model and wrote the first draft of the manuscript. AH and FM contributed to the text. All authors gave their final approval for publication.
The authors declare that they have no conflict of interest.
We thank Edna Rödig, Franziska Taubert, Nikolaj Knapp, Rico Fischer and Kristin Bohn for providing many helpful suggestions and comments.
We also thank the Department of Bioclimatology of the University of Göttingen
and the Max Planck Institute of Biogeochemistry for providing climate data
and the administration of Hainich National Park for permission to conduct
The article processing charges for this open-access
publication were covered by a Research
Centre of the Helmholtz Association.
Edited by: Sebastiaan Luyssaert
Reviewed by: Christopher Reyer and one anonymous referee
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