International Journal of Ecology

International Journal of Ecology / 2009 / Article

Research Article | Open Access

Volume 2009 |Article ID 683061 | 12 pages | https://doi.org/10.1155/2009/683061

Relating Plant Biodiversity in Forests with the Spatial Scale of Ecosystem Processes

Academic Editor: Mark S. Ashton
Received17 Apr 2009
Revised23 Aug 2009
Accepted03 Dec 2009
Published08 Mar 2010

Abstract

Plant species diversity of North-Central European forests is quantified by diversity profiles that give different weights to rare and dominant species. Diversity profiles saturate with increasing sample area obeying a hyperbolic saturation model. The paper addresses the question about (1) the spatial scale where this saturation is approached and (2) the nature of related processes. The study is based on about 1,700 vegetation relevés in close-to-nature beech forests and in secondary Scots pine forests which were classified in seven ecosystem types that are distinguished with respect to site factors, dominant tree species, and ecosystem processes. The relevés corresponding to a certain type are successively accumulated to composed relevés with increasing sample area in order to study saturation behaviour. The more weight is given to rare species the larger is the sample area where saturation is approached. The complexity of the processes that determine saturation increases with increasing weight of rare species. With increasing resource availability the part of the occurring plants that have immediate control on local ecosystem processes like primary production, nutrient cycling, and water balance increases. The presented approach allows an estimation of minimum area required for covering vegetation patterns that are related to these processes.

1. Introduction

Biological diversity is a complex phenomenon and it is hard to reduce this phenomenon to only one measure. Instead, various measures could be useful in order to characterize different properties of species distributions and community structure [1, 2]. Some authors use diversity profiles derived from one-parameter functions comprising species richness, Shannon and Simpson indices as special cases [36]. These diversity profiles can be used to study the effect of relative species abundance on diversity.

According to Grime’s “mass-ratio” theory [8], dominant and subordinate species have immediate control on ecosystem processes like nutrient cycling and water balance due to their overwhelming contribution to primary production. On the other hand, Grime emphasizes the importance of occasional or transient species for ecosystem function and sustainability. These low-abundant species originate from the seed dispersal and seed banks and provide the potential for developing new dominants and subordinates following temporal perturbations or systematic shifts of site conditions as can be expected, for example, in the outcome of climate change. The effects of these species become apparent on longer time scales.

Grime’s theory provides a linkage between species abundance, species function in the ecosystem, corresponding ecosystem processes and the temporal scale of these processes. In this paper I suggest a linkage between species abundance, diversity patterns, and the spatial scale of corresponding ecosystem processes.

The diversity profiles are derived from the following one parameter function with denoting relative species abundances:

This function is a generalized expression for an information entropy as described by Rényi [9]. The Rényi entropies of a given species distribution are weakly decreasing functions of the parameter q. As q approaches the limit one, it can be shown that

yields the well-known Shannon information entropy [912]. Shannon diversity mainly stresses medium abundances (relative abundances of the order 1/), whereas very small or very large provide only minor contributions to this measure.

Generalized information entropy or Rényi diversity due to (1) corresponds to a so-called “escort distribution” that weights species of different relative abundance depending on the parameter [13]. Hill [3] proposed the use of the exponential function of Rényi diversity according to (1), which he calls moments of the species distribution:

These moments characterize different properties of the species distribution. Lower moments () give greater weight to rare species. For = 0 each species makes the same contribution to diversity and (3) yields species richness represented by species number

Higher moments () give greater weight to more abundant species. Equations (1) and (3) yield with = 2

which is related to the well-known Simpson index [14]. If the probabilities are the same, then all the moments of Rényi diversities equal the species number which proves to be the upper limit of (3). The moments can be interpreted as an effective or apparent species number representing the minimum number of species of equal abundance required to produce the same diversity value [15, 16].

Equations (1) and (3) can be used to plot continuous diversity profiles, that is, to plot the diversities or the moments versus the parameter . These diversity profiles allow a comprehensive ecological interpretation [35]. Any deviation from complete evenness of species distribution yields a monotonically decreasing diversity profile with increasing . The more rapidly the profile declines, the lower the evenness of the system. Diversity profiles of different samples may be comparable; that is, they do not intersect over the entire range of . In this case one sample can be said to be more diverse than the other one. But even intersecting curves give rise to an ecological interpretation if we understand the ecological processes that determine different moments of the distributions. In this way diversity profiles might be very helpful for the investigation of relationships between diversity and ecological processes.

Diversity profiles saturate with increasing sample area. In previous work it was shown that Shannon diversity according to (2) obeys the ordinary differential equation [17]:

Equation (6) with defines a hyperbolic saturation model approaching a finite value on infinite sample area [18, 19]. The saturation diversities can be obtained easily:

Accumulating samples with similar ecological constraints yields a saturation diversity that represents the corresponding ecosystem type. This saturation diversity corresponds to a species distribution that reflects the diversity potential of a site with the given ecological constraints [17].

In the following I will demonstrate that (6) holds for the saturation of diversity profiles in a wide range of the parameter . The equation will be used for deriving characteristic spatial scales of diversity patterns for different branches of diversity profiles, that is, for dominant, subordinate, and rare species which have different meaning for ecosystem function according to Grime’s theory.

Furthermore, (6) will be used to estimate the complexity of the ecosystem processes that are related to different branches of diversity profiles. The exponent in (6) characterizes the hyperbolic asymptotic approximation to the saturation value of diversity which is forced by the ecological constraints mainly given by species pool and resource availability. Mende proposed that this exponent plays the role of a complexity measure [18]. This proposal was confirmed by the investigation of many natural and social growth and saturation processes which are highly cooperative [1821]. The more deviates from one, the larger are the number and the networking of the different processes that determine saturation. In this way I intend to relate diversity patterns with the spatial scale and complexity of ecosystem processes.

2. Material and Methods

Profiles of saturation diversity (i.e., according to (1) and (7) versus ) were calculated for a series of widespread European beech (Fagus sylvatica L.) forests within Northern Central Europe. These forests correspond to the potential natural vegetation in regions with suboceanic climates where the soils are not affected by ground- or backwater [22, 23]. The different beech forest types are distinguished by soil substrate and nutrient status (Table 1). For comparison, a series of secondary Scots pine (Pinus sylvestris L.) forests was investigated. The latter coniferous forests replace the beech forests in the overwhelming number of forest sites in the East German lowlands comprising the German Federal States of Mecklenburg-Western-Pomerania, the northern part of Brandenburg, and parts of Saxony and Saxony-Anhalt. Altogether, 905 vegetation relevés in mature close-to-nature beech forests and 767 relevés in mature secondary Scots pine forests (recorded between 1950 and 2006) were analysed for the present study.


ParameterClose-to-nature European beech forest ecosystem types
1234
Mercuriali-Fagetum sylvaticaeMelico-Fagetum sylvaticaeMilio-Fagetum sylvaticaeMajanthemo-Fagetum sylvaticae

Soil substratemarl, marly loamloamsandy loam, loamy sandsand
Soil nutrient statushypertrophic, carbonateeutrophicmeso- to eutrophicmesotrophic, meso- to oligotrophic
Humus typemullmull-like modermull-like moder to modermoder
(0–5 cm)10–1213–1516–1819–22
Site inde (m)
Ecosystem productivit (t/ha)

ParameterSecondary Scots pine forest ecosystem types
Rubo-Culto-Pinetum sylvestrisRubo-Avenello-Culto-Pin.sylv.Avenello-Culto-Pinetum sylvestris

Soil substrateloamsandy loam, loamy sandsand
Soil nutrient statuseutrophicmeso- to eutrophicmeso- to oligotrophic
Humus typemoderraw humus-like moderraw humus
(0–5 cm)20–2223–2527–29
Site inde (m)
Ecosystem productivit (t/ha)

Mean basal area height of trees at 100 years.
Maximum average net primary production of aboveground biomass (dry weight).

The individual sample plot area varied between 400 and 1600 m2. The species occurring of soil-covering vascular plants, mosses, and lichens were encountered within these sample plots. The percentage cover of plant species was estimated on the scale (very little coverage, very few individuals), + (little coverage, few individuals), 1% up to 10% in 1% increment steps, 10% up to 100% in 5% increment steps. For calculation purposes, was set equal 0.01% and + was set equal 0.2%.

The vegetation relevés were classified into four beech forest types and three Scots pine forest types due the principles developed by Hofmann [24]. According to these principles, vegetation is typified considering not only presence or absence but also percentage cover of species or species groups as well. It was shown that these vegetation types are distinguished with respect to site factors and ecosystem processes and can be considered as ecosystem types [7, 25]. Selected data on site factors, topsoil properties, and ecosystem productivity are presented in Table 1. Table 2 contains aggregated data on plant-species composition of the investigated beech forest types.


SpeciesEuropean beech forest ecosystem type
1234
Mercuriali-Fagetum sylv.Melico-Fagetum sylv.Milio-Fagetum sylv.Majanthemo-Fagetum sylvaticae

Tree layer
  Acer pseudoplatanus3
  Fraxinus excelsior2
  Tilia cordata2
  Ulmus glabra1
  Carpinus betulus31
  Fagus sylvatica67828269
  Quercus petraea1216
  Quercus robur111
  Pinus sylvestris1

Shrub layer
  Sambucus nigra2
  Acer campestre1
  Fraxinus excelsior1
  Rubus idaeus111
  Fagus sylvatica3339

Herb layer
  Mercurialis perennis25
  Aegopodium podagraria8
  Anemone ranunculoides3
  Sanicula europea2
  Impatiens parviflora2
  Glechoma hederacea1
  Impatiens noli-tangere1
  Dryopteris filix-mas1
  Corydalis cava1
  Circaea lutetiana1
  Geranium robertianum1
  Geum urbanum1
  Stachys sylvatica1
  Elymus caninus1
  Pulmonaria obscura1
  Hordelymus europaeus1
  Hepatica nobilis1
  Dentaria bulbifera1
  Polygonatum multiflorum1
  Melica uniflora821
  Lamium galeobdolon118
  Ranunculus ficaria131
  Urtica dioica21
  Deschampsia cespitosa11
  Festuca gigantea11
  Stellaria holostea21
  Carex sylvatica1
  Milium effusum3108
  Galium odoratum8155
  Brachypodium sylvaticum411
  Dactylis polygama11
  Viola reichenbachiana11
  Festuca heterophylla4
  Anemone nemorosa916101
  Oxalis acetosella61191
  Poa nemoralis141
  Carex pilulifera11
  Maianthemum bifolium12
  Convallaria maialis2
  Deschampsia flexuosa2
  Calamagrostis epigeios2

Moss layer
  Atrichum undulatum1
  Polytrichum formosum1

The were defined by the cover percentages of species in the following:

The index runs from one to total species number counted in a certain sample. Reliable diversity profiles can be obtained from measuring relative soil cover of occurring plant species on sufficiently large areas subject to the same ecological constraints.

The relevés of individual plot area corresponding to a certain ecosystem type were successively combined to composed relevés of increasing area with running from one to . For each composed relevé () the relative cover of different plant species and the Rényi diversity according to (1) were calculated with running from 0 to 2.0 in steps of 0.1. In the result there are samples: the first one consisting of the original relevés of individual plot area and the last one consisting of only one composed relevé of plot area . For each with a random sample consisting of combinations of original relevés was assembled; that is, the theoretical number of possible combinations of order was restricted to a maximum of 104. For each of the random samples, the mean Rényi diversities were plotted versus the mean sample area . Averaging may lead to a bias if individual relevés differ in plot sizes. However, this bias can be neglected in the present calculation because relevés classified into a certain ecosystem type have identical or only slightly deviating plot sizes. In order to justify this assumption, I investigated the species distributions for all forest types considered and found highly symmetrical distribution shapes that could be well approximated by Gaussian distributions (Table 3). Hence, the calculated mean Rényi diversities correspond to the most probable values that can be expected on plots of the respective sample area.


Ecosystem type 1Mercuriali-Fagetum sylvaticae
Number of relevés N244
Mean sample area of relevés0.07 ha
Mean species number of relevés ( standard deviation)
Median of species number33
Mode* of species number33
Parameter q 00.512

   6.524.092.951.86
   [ha]0.0020.0120.0190.016
   0.210.500.731.05
  RMSE0.01490.00190.00190.0003
  RMSE%0.330.050.080.02

Ecosystem type 2Melico-Fagetum sylvaticae
Number of relevés N300
Mean sample area of relevés0.06 ha
Mean species number of relevés ( standard deviation)
Median of species number20
Mode* of species number20
Parameter q 00.512

   6.333.332.111.37
   [ha]0.0020.0080.0110.012
   0.190.430.701.03
  RMSE0.00720.00250.00030.0004
  RMSE%0.170.090.010.03

Ecosystem type 3Milio-Fagetum sylvaticae
Number of relevés 203
Mean sample area of relevés0.07 ha
Mean species number of relevés ( standard deviation)
Median of species number14
Mode* of species number14
Parameter q 00.512

   5.603.341.880.98
   [ha]0.0090.0250.0250.024
   0.300.460.651.21
  RMSE0.00980.00460.00200.0020
  RMSE%0.220.220.150.15

Ecosystem type 4Majanthemo-Fagetum sylvaticae
Number of relevés N158
Mean sample area of relevés0.10 ha
Mean species number of relevés ( standard deviation)
Median of species number11
Mode* of species number10
Parameter q 00.512

   5.583.021.360.55
   [ha]0.0190.0650.0520.031
   0.290.460.571.06
  RMSE0.00200.00580.00280.0004
  RMSE%0.060.370.320.08

Calculated from a Gaussian fitting.

The following nonlinear saturation equation is solution of the ordinary differential equation (6), where and :

This equation was fitted to the calculated data curves versus the area . The three parameters were estimated by a nonlinear least squares fit using a gradient-expansion algorithm (procedure CURVEFIT implemented in IDL, versus 6.3, RSI, ITT Industries, Boulder, USA).

Finally, I investigated the reliability of the modelled saturation diversities for different values of depending on the sample area. For this purpose, the total set of original samples corresponding to a particular ecosystem type was randomly divided into each of 2, 4, 6, 8, and 16 disjunctive subsets. The saturation diversities were estimated from each of the sample subsets according to the above procedure. Mean values and standard deviations of the predicted moments of saturation diversities were plotted over the sample area (Figure 3). When the predicted saturation moments remain constant with increasing sample area, they can be considered to be reliable. In this case the sample size is sufficiently large for predicting the saturation profiles with high accuracy.

3. Results

The nonlinear saturation model (9) very closely resembles the field data (Figures 1 and 2). The root mean squared error is generally of the order of parts per thousand of the sample mean or even smaller (Tables 3 and 4). The envelopes of error curves decline with increasing sample area, that is, with the diversities coming closer to the saturation point (Figure 2). The investigated samples sizes were sufficiently large for predicting reliable values of saturation moments from the hyperbolic model for scanning parameters as is shown for one ecosystem type in Figure 3. Similar results were obtained for all the investigated ecosystem types. In these cases a high constancy of the predicted saturation values indicates that the corresponding moments are independent on sample size. For species number ( = 0), however, the predicted saturation value increases with increasing sample area. In this case the model proves to be inadequate and saturation cannot be expected within the considered data range.


Ecosystem type Rubo-Culto-Pinetum sylvestris
Number of relevés 70
Mean sample area of relevés0.08 ha
Mean species number of relevés ( standard deviation)
Median of species number26
Mode* of species number26
Parameter q 00.512

   6.754.162.922.02
   [ha]0.0040.0110.0170.023
   0.220.420.671.10
  RMSE0.00100.00170.00130.0004
  RMSE%0.030.050.050.02

Ecosystem type Rubo-Avenello-Culto-Pinetum sylvestris
Number of relevés 286
Mean sample area of relevés0.06 ha
Mean species number of relevés ( standard deviation)
Median of species number21
Mode* of species number21
Parameter q 00.512

   7.213.822.531.77
   [ha]0.0020.0070.0120.014
   0.170.370.651.04
  RMSE0.00360.00060.00080.0007
  RMSE%0.080.020.040.04

Ecosystem type Avenello-Culto-Pinetum sylvestris
Number of relevés 411
Mean sample area of relevés0.06 ha
Mean species number of relevés ( standard deviation)
Median of species number15
Mode* of species number14
Parameter q 00.512

   7.733.271.901.36
   [ha]0.0020.0060.0090.013
   0.130.320.621.07
  RMSE0.00420.00110.00060.0003
  RMSE%0.130.050.030.02

Calculated from a Gaussian fitting.

The saturation diversity and hence the effective or apparent species number decrease with increasing (Tables 3 and 4). The parameter in (9) was found to increase with increasing (Tables 3 and 4). According to (9), the curve approaches the saturation diversity more rapidly with increasing . This means that higher moments of species distributions achieve saturation on smaller sample areas A. With increasing , the complexity parameter in (6) approaches one. This means that higher moments of species distributions are related to less cooperative processes. On the other hand, saturation of lower moments is a more complex phenomenon than saturation of higher moments (e.g., Shannon or even Simpson diversity).

Determination of the spatial scale of the corresponding processes can be obtained from measures of evenness of species distribution according to

Equation (10) for = 1 corresponds to the well-known Shannon evenness. In previous work, it was shown that Shannon evenness increases up to a maximum on local scales but decreases steadily on larger areas [17]. A similar shape of evenness curves was found for all 0 in this study (Figure 4). The area , where evenness approaches its maximum, increases with decreasing (Figure 5). In beech forests on eutrophic loam soils (Melico-Fagetum) this area varies between 400 m2 for = 2 and about 4000 m2 for = 0.1. Hence a plot size of 400 m2 would be sufficient in order to record dominant species in this forest type. Otherwise, 4000 m2 would be required for sampling most of the rare species that can be expected in this forest type.

Moments with correspond to spatial scales up to the order of squared tree height which is a natural local interaction scale within forests. Diversity profiles within this parameter range reflect species abundance distributions over a wide range from less abundant up to dominant species, only excluding occasional species. On these scales the diversity is clearly related to the following ecological constraints.

(1)Plant species diversity increases with increasing soil nutrient status and water storage capacity of soils within each of the investigated ecological series of both beech and Scots-pine forests (Tables 1, 3, and 4; Figures 6 and 7). The other ecological site factors were mostly kept constant within these ecological series.(2)The investigated close-to-nature beech forests have a significantly lower plant-species diversity compared to the corresponding secondary Scots-pine forests on similar forest sites (Figures 8, 9, and 10).

The profiles of saturation diversity show a clear tendency to become more concave with decreasing soil quality (Figure 7). Moreover, diversity profiles of forests that are dominated by the strongly shading beech (Fagus sylvatica) in the tree layer are more concave than profiles of forests with the much more transparent canopies of Scots pine (Pinus sylvestris) (Figures 810). More concave diversity profiles correspond to lower evenness of plant species distributions. Summarizing the above findings, it can be confirmed that both species richness and equitability of species distribution increase with increasing availability of resources.

Both regularities are uniquely derived from the Rényi saturation diversities with the parameter continuously varying between 0.5 and 2 (a reversal of the diversity rank is observed between Melico-Fagetum and Milio-Fagetum for ). The effects are most distinct for higher moments with .

4. Discussion

Saturation profiles of diversity and the corresponding spatial scales can be well interpreted within the framework of Grime’s “mass-ratio” theory [8]. Higher moments of species distributions give more weight to dominant and subordinate species in the diversity measure. These species have immediate control on ecosystem processes such as nutrient cycling, and water balance due to their overwhelming contribution to primary production. Strongly declining diversity profiles (with increasing ) indicate that only a small part of the occurring species takes part in this immediate control. This part is decreasing with decreasing resource availability as is indicated by the increasing concavity of diversity profiles. Resource sharing between different species decreases with decreasing soil quality (Figure 7), but it increases when the dominant beech in close-to-nature forests is substituted by Scots pine in secondary forests (Figure 10). Correspondingly, natural succession in these man-made pine forests leads to a significant decrease in plant species diversity due to the growing dominance of strongly shading beech trees. Total above-ground net productivity in close-to-nature beech forests is significantly higher than in secondary pine forests due to the contribution of woody biomass (Table 1). Hence there is no simple relationship between plant species diversity and ecosystem productivity.

The more weight is given to dominant and subordinate species, the smaller is the area required to observe the corresponding diversity patterns. The minimum area to cover the vegetation patterns that determine different moments of the distribution can be estimated from the peak of the evenness curve according to (10). It turns out that area sizes about squared tree height do correspond to moments of order in North-Central European forests (Figure 5). This result is compatible with the fact that trees, in the main, control primary production, nutrient cycling and water balance in forests.

About twenty relevés of about 500 m2 plot size each are sufficient to predict reliable saturation diversities for forest ecosystem types with from a hyperbolic model. This corresponds to a total sample area of about one to few hectares. The corresponding species distributions represent the vegetation potentials of the sites that are subject to similar ecological constraints.

The more weight is given to rare species, the larger is the sample area where saturation of diversity is approached. The complexity of the processes that control the saturation of species diversity increases when greater weight is given to rare species. The lower moments (in particular species number) are more strongly influenced by species delivery from the surroundings, that is, by long-range interactions like species migration and dispersal. Grime emphasizes the importance of occasional or transient species for ecosystem function and sustainability [8]. These low-abundant species originate from the seed rain and seed banks and provide the potential for developing new dominants and subordinates following temporal perturbations or systematic shifts of site conditions as can be expected, for example, in the outcome of climate change. The effects of these species become apparent on longer time scales.

There was no reliable saturation confirmed for species number (). For close to zero, the diversity is strongly influenced by the stochastic presence of occasional species. The accumulated samples were taken from different geographic locations and may be embedded in completely different landscape surroundings with different species delivery. A saturation of species number cannot be expected under these circumstances.

Ricotta and Anand [26, 27] developed a measure of structural complexity for plant communities based on the information-theoretical framework of Juhász-Nagy [28, 29]. This measure quantifies the amount of spatial correlation between the species in plant assemblages as a function of scale. It shows a peaked behaviour with at least one maximum at intermediate scales. The approach is based on information entropies of the Shannon type. Hence it would be interesting to compare the spatial scales obtained by these authors with the corresponding values obtained for by the more simple approach presented in this paper.

In this paper I restricted myself to the discussion of the hyperbolic saturation behaviour of diversity curves. Hyperbolic saturation of diversity with increasing area can be expected for large sample areas within a particular biogeographic region (limited species pool) and with homogeneous or repeating environments. On small areas, along changing environments or changing bio-geographic regions with a changing species pool, a law with exponents can be expected not only for species richness (classical SAR) but also for Shannon and Simpson diversity [30].

5. Concluding Remarks

The hyperbolic saturation model applied in this study is not only a tool for data fitting but also a theoretical model for a certain type of saturation behaviour. This model can improve our understanding of the relationships between biodiversity, spatial scale, and ecosystem functioning when applied to the study of diversity profiles.

Shannon or Simpson diversities are well suited to describe vegetation patterns that are strongly related to ecosystem processes like primary production, nutrient cycling, and water balance. The latter processes are mainly controlled by species of high and medium abundance. Low values of these diversity indices may indicate a strong limitation of resources but also a high adaptation of few species to the site conditions. These ecosystem processes are tightly related to the local site conditions and to the dimension of dominant species, which determine the sample area required for analysing the corresponding vegetation patterns. This minimum area corresponds to the point of maximal evenness that can be obtained for a certain ecosystem type according to the method developed here.

Low moments of the diversity profiles that give more weight to rare species have a great importance for the adaptability of ecosystems. The corresponding vegetation patterns can be observed on rather large spatial scales and are the result of a complex networking of many processes as indicated by our mathematical analysis. Despite their great importance for ecosystem sustainability, these complex processes on landscape scales are poorly understood up to now.

Acknowledgments

The work was funded by the German Federal Ministry for Education and Research (BMBF) under contract no. 0330562H. The author is responsible for the content of the publication. The author is indebted to Gerhard Hofmann, Ulf Pommer, Sybille, and Michael Wehner who provided major contributions to the development of the investigated ecological database. Furthermore, the author is grateful to Carlo Ricotta and three anonymous referees who gave valuable hints on earlier versions of this paper.

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Copyright © 2009 Martin Jenssen. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.


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