- Open Access
Ingrowth, survival and height growth of small trees in uneven-aged Picea abies stands in southern Finland
© Eerikäinen et al.; licensee Springer. 2014
- Received: 25 June 2013
- Accepted: 27 September 2013
- Published: 26 February 2014
The purpose of the study was to analyse height growth, mortality, and ingrowth of individual small-sized trees in uneven-aged spruce-dominated stands. It was based on experimental data from 16 stands for a 15-year observation period including four measurements with a 5-year interval. In the data of this study, the heights of small-sized trees varied from 0.1 to about 9 m. Results showed that the growth of small trees was rather slow, particularly in the smallest size classes. With average growth rates it would take about 60 years for a freshly emerged spruce germinant to achieve 1.3 m in height. The stand density, site quality and selection cuttings affected the growth of small-sized spruces. Average five-year mortality rates for spruce, birch and pine were 17.0%, 40.9% and 33.9%, respectively. Annual ingrowth rates with the threshold height of 1.3 m for the three species were on average 30.4, 2.8 and less than 0.1 trees per hectare, respectively. Even if, a selection cutting of modest intensity (25% of basal area removed on average) seemed to have accelerated the growth of small spruces, it is recommended that more intensive harvestings be applied to enhance the survival and growth of small spruces. It is also concluded that shade intolerant species like birch and pine do not seem to be capable of developing into viable undergrowth in spruce selection stands with their current levels of stand density.
- Selection cutting
- Uneven-aged forest
One of the key dynamic components of sustainability in uneven-aged forest management is the survival and development of the small trees, which are often labelled regeneration, seedlings and sapling in practical terms with variable definitions. Their recruitment, survival and ability to withstand long suppression periods and recover after release are crucial to attaining and maintaining ecologically and economically sustainable stand structures.
The emphasis of studies on uneven-aged management has been on estimating growth and yield of larger trees and optimizing their cutting treatments. The data sets and results of the studies on regeneration and tree development have been rather limited in size, scope, and coverage of the potential sources of variation. Consequently, our knowledge on the related processes is still rather limited. It has been a weak point in studies assessing the feasibility of uneven-aged management in the Nordic countries (Kolström, 1993; Lundqvist, 1993,1995; Wikström, 2000,2008; Andreassen and Öyen, 2002; Miina et al., 2006; Lundqvist et al., 2007; Gobakken et al., 2008; Lexerød, 2008; Pukkala et al., 2009,2010; Tahvonen, 2009; Tahvonen et al., 2010). Due to the fact that the models used have been rather rudimentary and of limited reliability in simulation studies, it has been difficult to assess the reliability of the optimization results particularly on what comes to the long-term sustainability and productivity of the simulated practices.
The principal factors driving emergence, mortality and growth of new trees in Norway spruce stands with relatively high canopy closure include: seed crop, seedbed properties, climatic factors and competition from ground vegetation and larger trees (Clarke, 1992; Pukkala and Kolström, 1992; Örlander and Karlsson, 2000; Hanssen, 2002,2003; Chantal et al., 2003; Hanssen et al., 2003; Valkonen and Maguire, 2005). Regeneration surveys on experimental plots and their analyses have provided some basic knowledge on the number and distribution of germinants, seedlings, and saplings in uneven-aged spruce stands in the Nordic countries (Lundqvist, 1989,1991; Lundqvist and Fridman, 1996; Nilson and Lundqvist, 2001; Saksa, 2004; Eerikäinen et al., 2007; Lundqvist et al., 2007; Saksa and Valkonen, 2011). Compared to their emergence, less attention has been paid to the details of survival and development of established small trees in uneven-aged stands in the area. So far, datasets have been limited in terms of the number of plots and the length of observation periods.
After the emergence stage, competition by the existing larger trees is assumed to become a more and more decisive factor that affects the growth of small trees and their ingrowth into the main canopy (Lundqvist and Fridman, 1996; Nilson, 2001; Nilson and Lundqvist, 2001; Saksa, 2004; Eerikäinen et al., 2007; Lundqvist et al., 2007). However, Lundqvist (1989,1991) and Lundqvist and Fridman (1996) found that the influence of local and stand-level density had no or only a very weak effect on the growth of small trees in uneven-aged spruce stands in northern and central Sweden, whereas Chrimes and Nilson (2005) reported negative influences which occurred in the very North. In addition, small trees are often damaged and destroyed in harvesting (Fjeld, 1998; Granhus, 2001; Granhus and Fjeld, 2001; Surakka and Sirén, 2007; Surakka et al., 2011).
In many simulation models, tree emergence, survival and growth have been aggregated into lump estimation of ingrowth at a certain diameter threshold. The threshold diameter has varied from 0 to 8.5 cm in studies conducted in central and northern Sweden (Lundqvist, 1989,1993; Lundqvist et al., 2007) and to that of 5 cm used in Norway (Lexerød, 2005). For practical purposes, it could be sufficient to predict ingrowth, but the current procedures tend to be too simplistic for realistic simulation, particularly while ignoring the spatial and temporal variation of survival, growth, and distribution of regeneration which can be very large (Saksa, 2004; Saksa and Valkonen, 2011).
The Finnish Forest Research Institute has conducted detailed investigations on tree emergence, growth and mortality processes in its ongoing research on single-tree selection using a set of experimental plots entitled “ERIKA”. Saksa (2004), Valkonen and Maguire (2005) and Saksa and Valkonen (2011) utilized data collected from the ERIKA plots for examining the initial stages of the process (tree emergence, survival, and growth up to 1.3 m height) with respect to measured stand-level attributes, whereas Eerikäinen et al. (2007) modelled regeneration dynamics and tree development. The data contained just one 5-year observation period, and the models were therefore deemed preliminary. So far, a less detailed description for the response to harvesting has been obtained, for instance.
The main objective of this study was to establish an empirical basis for modelling the dynamics of the small-tree cohorts in uneven-aged Norway spruce stands in southern Finland. We explored and analysed height growth, mortality and ingrowth by expecting tree size and species, site type, and stand density (basal area) to be significant factors. These characteristics form a basis for the operational modelling, in which different tree- and stand-level models are to be synchronized in to a compatible simulation system needed for predicting the development of uneven-aged spruce stands. Another objective was to present and interpret our observations for the benefit of respective research under quite similar conditions in the Nordic area, particularly for cross-checking purposes.
The study material was acquired from a set of 16 experimental plots in southern Finland (61° 00′ N – 62° 00´, 25° 00´ – 27° 30´ E) at four locations, namely Vesijako (VES), Lapinjärvi (LAP), Evo (EVO), and Puolivälimäki in Vesijako (VEP). The plots had been explicitly established for studies on tree and stand development in managed, uneven-aged Norway spruce forests conducted under the ‘ERIKA’ research project at the Finnish Forest Research Institute (Metla). The plots had been established in 1991–1992. The study sites were subjectively selected among about 40 candidate stands available for the project on the properties of Metla, Metsähallitus (administrator of state-owned forests in Finland), Evo School Forest, and a few other forest owners. Stands that displayed a great degree of resemblance with a classic single tree selection structure in terms of diameter distribution and homogenous spatial distribution were a priori assessed to have a potential to develop towards a sustainable selection structure. The stands represented various stages of transition to some future, yet undefined sustainable single tree selection structures. Their diameter distributions ranged widely, thus representing varying forest structures. Originally 21 plots were established. One stand (LAP8) was completely destroyed by a tornado in 1998, and therefore its data were excluded from this analysis. In addition, data from four plots in Suonenjoki (SUO1, SUO2, SUO3 and SUO6) were discarded in this study due to their divergent measurement protocol: recordings for trees shorter than 1.3 metres were only available from the 64 circular regeneration plots within each of the four ERIKA plots.
Stand characteristics by the ERIKA plots at the beginning in 1991 and at the end in 2006 of the 15 years monitoring period
G rem, %
The forest stands represented the most common spruce sites on mineral soil, i.e. mesic Oxalis-Myrtillus type (OMT) and submesic Myrtillus type (MT) (Cajander, 1926; see also Table 1). At the beginning and at the end of the monitoring period, on average, 71% and 77% of the total stand volume was comprised by spruce, respectively. The remaining portions of the stand volumes comprised of Scots pine (Pinus sylvestris L.) and various broadleaf species, mainly silver birch (Betula pendula Roth), downy birch (Betula pubescens Ehrh.) and aspen (Populus tremula L.).
In each stand, all measurements took place on a 40 m × 40 m plot. All trees taller than or equal to 0.1 m were described according to species and coordinates, and measured for diameter at breast height and height in 1991, 1996, 2001 and 2006. This study was based on a subset of data containing the observations of trees that were from 0.1 to 4.0 m high at the time of plot establishment and were measured with slightly different protocols compared to trees shorter than 0.1 m and taller than 4 m. The trees were measured with identical protocols at 5-year intervals. The data from 16 stands contained 14,685 individual trees with 1-3 observation periods of 5 years each. Only spruces (14,088), birches (484), pines (107), i.e. the species of commercial value, were studied. Measurements obtained for other tree species and collected from altogether 6 trees were discarded from the analysis due to the insufficient number of species-wise observations.
In data preparation, each tree was individually traced throughout its existence during the 15-year observation period. Its presence or absence (living, dead, or missing) and height were recorded at each of the four measurements. Height increment was obtained by calculating the difference between the individual tree heights measured at the end and at the beginning of each 5-year period. Negative values where accepted when they were proved to be genuine, since breakages or abscissions and regrowths of the leader shoots of birches, especially, were rather common. A survival was recorded if a tree was present and alive both at the beginning and at the end of the 5-year period. Since the second measurement in 1996 was carried out only prior to harvesting but not repeated after harvesting, part of the mortality during 1996–2001 is due to losses and damages caused by logging.
Relationships between tree height increment and survival during the 5-year intervals and between the measurements were analysed based on tabulation and illustration frameworks. In addition, correlation coefficients between tree attributes and potential explanatory variables such as site quality and basal area were calculated and inspected. A mixed-effects modelling-based regression analysis was also applied to elucidate the relationship between height growth and size of trees and to assess the magnitude of differences in mean growth estimates obtained by forest stands and growth periods. A nonlinear mixed-effects (NLME) modelling procedure was applied, especially because of its efficiency to account for random fluctuations arising from data: both spatially hierarchical (experimental plots or forest stands and trees) and temporally cross-sectional (growth periods) correlation structures were apparent in ERIKA data and, therefore, the basic assumption about uncorrelated error terms was unlikely to hold (see Pinheiro and Bates 2002). Parameters of the NLME model were estimated using the ‘nlmer()’ function in the lme4 package under the statistical software R (R Core Team 2012).
The t-test was used to assess the significance of fixed model parameters which were treated as significant at the levels of the p-value less than 0.05, whereas the significance test for the Maximum Likelihood (ML) estimated parameters obtained for random effects was based on the Likelihood Ratio Test (LRT) (see Goldstein 1995; Pinheiro and Bates 2002). The validation of candidate models, i.e. models with different combinations of independent variables used in their fixed model parts, was based on the ML estimated parameters by employing as criteria the Akaike Information Criterion, i.e. AIC values (Pinheiro and Bates 2002). After completing the comparisons made between different parametrisations the candidate models with ML estimated parameters, the REML estimates were obtained for the final parameterisation of the nonlinear mixed-effects model (Pinheiro and Bates 2002). In order to eliminate the possible sources of prediction bias, both the standardised and pure residuals were inspected using scatterplots that were obtained for the candidate models as functions of the independent variables and with and without the estimated random coefficients.
Tree height growth was faster on the more fertile Oxalis-Myrtillus forest type (OMT) compared to that of the Myrtillus forest type (MT). Based on all increment observations in the data, the between-forest type mean ratios (OMT/MT) obtained for spruce, birch and pine were 1.67, 1.76 and 1.34, respectively. The species-specific ratios were rather consistent through the ranges of tree heights. Differences in height increments between the two site types and by the three species were also assessed using the Welch's t-test. Significant differences were obtained for spruce (t = 22.725, p-value < 0.0001) and birch (t = 6.949, p-value < 0.0001) that, however, did not hold for pine (t = 0.852, p-value = 0.4201).
where h tij is tree height, m; G ti is basal area, m2ha-1; zOMTi is a forest stand-specific dummy variable for Oxalis-Myrtillus forest type (OMT), being 1 in the case of the respective forest type and 0 otherwise; TI i is a forest stand-specific thinning intensity obtained as a ratio between the basal area removed in the thinning and the basal areabefore the thinning; zPAT1ti and zPAT2ti are dummy variables for the first and second 5-year period of growth after thinning, respectively; β0, …, β5 are parameters for fixed effects; u0,i and u1,i are random parameters for forest stand effects; and e tij is parameter for random errors of the model.
Estimates for the fixed parameters and random components of Equation 1
Random forest stand effects
4.1320 × 10-3
-9.9498 × 10-4
1.0102 × 10-3
5.0258 × 10-2
Equation (1) was applied to demonstrate the average, stand-specific height development patterns of spruce by utilising the estimates obtained for random stand-effects. A fixed time step of five years was used in simulation and measured, stand-specific values were used for basal area and thinning removal. In addition, an increment prediction was recursively added to tree height at each time step when predicting the height developments in average conditions of the 16 experimental stands, respectively.
In this study, the ingrowth denotes the number of trees that reached the breast height of 1.3 m during any of the three 5-year observation periods and survived until the last measurement. The mean annual ingrowth rates for spruce, birch and pine were 30.4, 2.8 and less than 0.1 trees per hectare, respectively. Variation between the periods and stands was remarkable, and correlations between ingrowth and basal area were very weak and nonsignificant for spruce (r = -0.009, p-value = 0.954) and birch (r = -0.162, p-value = 0.271), whereas for pine it became meaningless to estimate the correlation coefficient due to too few observations.
Due to the simultaneous growth and mortality processes, the height distribution of spruces changed only little during the entire period of 15 years. The sizeable ingrowth rate in the three lowest height classes (0.1 ≤ h ≤ 1.5 m) of spruce obviously resulted from the very abundant regeneration cohorts of 1990 and 1993 (see Saksa and Valkonen, 2011). Ingrowth and mortality seemed to have cancelled each other out in higher height classes.
It is also noteworthy that the number of trees in the smallest height class decreased only in the case of two experimental stands (LAP1 and LAP7) from the first to the last measurement on the ERIKA plots (Figure 4B). If stand No. 7 in Lapinjärvi (LAP7) is not considered, all stands (VES13, VES16, EVO2, EVO3 and VEP5) with initially high number of small-sized trees retained their rank until the end of the monitoring period of 15-years.
Lundqvist (1989) reported faster height growth with greater height of spruces (10–130 cm) in uneven-aged stands. In height class 10–40 cm, the average annual increment was about 2 cm and in the class of 100–130 cm it was about 5 cm. The annual height increment predictions obtained for the medium growth forests (LAP1 and EVO2 in Figure 2) and same size classes using Equation 1 were ca. 1 and 4 cm, respectively, which correspond to the findings of Lundqvist (1989). Nilson and Lundqvist (2001) also reported comparable results: average annual height increments of spruces (h = 50–200 cm) varied between 2–4 cm in a central Swedish location before or a few years after thinning from above. Seven years after the thinning treatment, annual height increments had increased to 5–15 cm, and the highest average was obtained for the treatment called “medium overstorey density”.
The nonlinear mixed-effects model on spruce height increment over height (Equation 1) is still too simplistic for use in simulation system applications. However, it serves the purpose of being a straightforward and unbiased analysis and demonstration tool for assessing the development of an average pattern observed in these experimental stands and supporting future efforts to construct operational models for simulation systems. The effects of complexity clearly apparent in these data shall be described in greater detail for simulation purposes. Then the true influence of stand density and its variation within stand on the growth and survival of trees needs to be analysed and modelled in order to obtain statistically sound predictors required for simulation studies. However, even this preliminary exercise clearly revealed that the average growth of the small trees is slow in the ERIKA stands, especially in the smallest size classes. This corresponds closely to the recent findings by Saksa and Valkonen (2011): it took from 13 to 16 years for spruce germinants to grow into the height class of 15-30 cm in these same stands, and trees reached breast height at 60 years of age on average, and 5 m at 90 years, respectively. It is noteworthy that according to Lundqvist (1989) it took from 24 to 47 years for 0.1 m tall spruces in six different stands and corresponding conditions in central Sweden to reach breast height. Even if the tree growth rates in ERIKA stands were lower than those in Swedish selection cutting stands, the differences between stand-wise predicted mean growth rates were also substantial as demonstrated in Figure 2.
Stand basal area significantly reduced spruce height growth in the analysis conducted with the nonlinear mixed-effects model (Equation 1). Lundqvist (1989) and Lundqvist and Fridman (1996) did not detect any negative influence from high levels of standing volume on height increment, but it was also concluded that it was not possible to determine whether it would represent a general pattern or just a peculiarity of their dataset. Nilson and Lundqvist (2001) found that standing volume did have a negative correlation with the growth of small trees with thinning from below but not with thinning from above, i.e. in the case of stands with greater structural complexity. Chrimes and Nilson (2005) found a pronounced negative correlation between the growth of small trees with stand basal area or canopy openness at a subarctic location in Northern Sweden. Nilson (2001) and Chrimes and Nilson (2005) suggested that canopy openness, or light availability, could be more closely related to the growth of small trees than stemwood-based density attributes in such stands. Stemwood-based variables seemed to work better with increasing tree size as the role of root competition became more important. It seems likely that the acceleration of growth of small spruces during the monitoring years from 10 to 15 would be attributable to the selection cutting carried out at year 5. The pattern was similar as in the study of Nilson and Lundqvist (2001) who reported that stand density alone did not have a significant effect on increment, whereas cuttings (thinning from above or below) itself and the combined effect of cuttings and stand density influenced height increment significantly. It is expected, however, that local competition measures with spatiotemporal analysis could explain the variation in the growth characteristics of young trees in the structurally heterogeneous uneven-aged forest stands more profoundly (cf. Eerikäinen et al., 2007).
A total of 11 out of the 16 study stands were treated with a selection cutting after the 5th growth season. Theoretically, this could have resulted in different increment regimes between the two categories, but it was very unlikely though. Altogether three out of five uncut stands (VES13, VES14, and VES16) were left untouched because they had already been cut three years prior to the start of ERIKA monitoring. In the other two stands (LAP1, EVO3), 8 years had elapsed since the previous cutting, but tree growth had been too slow to facilitate (or necessitate) another cutting. A poorer site (a stony outcrop with shallow soil) combined with rather old dominant trees was the obvious reason for the slow growth rates of advanced trees at ERIKA plot called “EVO3”. We could not identify any such distinct factors for LAP1 where the site fertility was definitely at least at average level. Consequently, we believe that all of the uncut stands were similar enough with the cut ones to be included in the data.
Indistinct background factors and interactions included in experimental conditions and data structure are probably involved. The short observation periods in the studies (≤ 15 years) are certainly part of the issue, because the response of understorey spruce trees to harvesting treatments is slow. Typically it takes several years for heavily suppressed spruces to show any positive growth response, and more than 10 years to attain full growth after complete release, i.e. removal of overstorey (Koistinen and Valkonen, 1993; Nilson and Lundqvist, 2001).
For birch and pine, the relationship between tree growth and height was not nearly as consistent as it was for spruce. One explanation could be that their data was patchy due to the limited presence of the two species in the experimental ERIKA stands. Perhaps more importantly, their initially quite good growth rate did not accelerate with height at all like it did in the case of spruce. Both of these two patterns point to the same basic feature which is the inability of birch and pine to survive and grow under dense spruce main canopies.
Mortality estimates were obtained for trees that had existed at a particular measurement but died or went missing five years later. The results underestimated true mortality rates for the smallest height class by failing to capture trees that grew in to the class and then died between measurements, not leaving a mark in the records. Conversely, estimates for the second period (1996–2001) included losses incurred in logging. Since trees were not remeasured after harvesting, it was not possible to make any distinction between their disappearance due to logging or due to other reasons. The proportion of trees lost in logging seemed to be relatively low in this dataset. The total loss rate (died or vanished during the period) of spruce obtained for the second period was higher when compared to the first and third period, whereas an increasing rate of loss was obtained for birch. The data for pine was too erratic for more complete conclusions. Under comparable circumstances, a logging entry can cause death or injury from 30 to 40% of small spruces (Granhus and Fjeld, 2001; Surakka and Sirén, 2007; Surakka et al., 2011). Nilson and Lundqvist (2001) observed that annual mortality rates of spruces (0.1 m ≤ h < 0.5 m and 0.5 m ≤ h < 2.0 m) varied from 2 to 7% and from 0 to 4%, respectively. In the data of this study, the annual mortality rates were from the same magnitude, i.e. 3.7% and 3.1%, when obtained for the corresponding height classes of spruces, respectively.
Lundqvist (1989,1991,1993) estimated that with the threshold height of 1.3 m an average annual spruce ingrowth varied from 43 to 55 ha-1, whereas Saksa (2004) found it to be 26 ha-1. Both data were characterised by a high variability in stand density. In central Sweden, Lundqvist et al. (2007) observed an annual ingrowth rate of 21 spruces per hectare with the threshold of 5 cm at breast height, which was a lump average for plots treated with light to heavy thinning from below or above. Correlation with standing volume was significantly negative. It is essential to understand that short-term ingrowth is largely a function of the initial size distribution of trees, while stand density should have a more meaningful impact over a longer period. Such is also the case in this study, and the observed ingrowth rates must be interpreted accordingly.
As the product of the growth and mortality processes, the height distribution of small spruces was little changed during the 15 years in ERIKA plots. The sizeable ingrowth rate in the lowest height classes (0.1 ≤ h ≤ 0.7 m) of spruce obviously resulted from the very abundant regeneration cohorts of 1990 and 1993 (see Saksa and Valkonen, 2011). Ingrowth and mortality seemed to have cancelled each other out in higher height classes. As reported by Saksa and Valkonen (2011), the experimental ERIKA stands have a good regeneration potential on average, and quite a few spruces are about to reach 1.3 m in height because of the two abundant cohorts emerged in the early 1990s.
In addition to tree survival, growth, and momentary ingrowth rate, their long-term dynamic is controlled by developments at the consecutive stages of their development. However, the very large variations within and between stands suggest that problems may surface in many cases. More intensive harvestings (i.e., lower post-harvest stand densities) than those implemented in the ERIKA stands could be applied to enhance the survival and growth of small spruces, but their true impacts remain uncertain. It is also obvious that the shade intolerant species such as birch and pine cannot develop into serviceable undergrowth, let alone full-fledged trees, in these spruce-dominated selection stands with relatively high stand density levels. More intensive management including much heavier thinning programs or group selection practices would be required to sustain their participation in the uneven-aged spruce-dominated forest stands.
In conclusion, the performed analyses inspected and demonstrated some of the major elements of the dynamics among small trees in the uneven-aged spruce forest stands. The height increment model for spruce is simplistic for use in simulation systems but supports our future efforts to construct operational model systems. The inherent complexity of the phenomena involved became clearly apparent. To reveal the true influence of stand density and its within-stand variation on the growth and survival of small trees is of particular importance for practical needs and simulation purposes. Many of our empirical results are very well in line with their counterparts in the Nordic area. This reinforces our understanding that it would be possible and very beneficial to compound our rather patchy data sets for comparison, testing and modelling.
The study was based on the experiments established and managed under the ERIKA project of the Finnish Forest Research Institute (Metla). We thank all project participants and supporters for their cooperation. Ms. Hilkka Ollikainen and Mr. Juhani Korhonen deserve our special gratitude for their inexorable endeavour in the field.
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