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The effect of spatial structure of forests on the precision and costs of plotlevel forest resource estimation
Forest Ecosystems volume 6, Article number: 8 (2019)
Abstract
Background
We investigated how the precision and costs of forest resource estimates for sample plots of different type and size depend on the spatial structure of forests and jointly studied the effects of tree density and size distribution. Statistically thinking, the trees in a forest can be regarded as a point pattern. Based on the spatial properties of the point pattern, we classified the forests into clustered, random, and regular. We used empirical data from 396 mapped forest plots from Finland. The variance of the unbiased HorvitzThompson estimator and expected costs of the basal area and tree density estimation were calculated for 99 different sample plots of different type and size in each of the 396 forest plots. Further, we considered the estimation of the change between two time points for a subset of the data.
Results
The precision and expected cost depended on the tree size distribution and spatial pattern of trees. While large sample plots are advisable for clustered forests or the monitoring of young forests with small trees, we see potential for measuring smaller sample plots in regular forests. The choice of sample plot was more important in clustered forests, where also the variability of the expected costs was higher.
Conclusions
If the spatial structure of forests could be predicted accurately and precisely prior to field measurements, for instance from remote sensing data, the precision of forest inventories could potentially be improved or costs decreased by allowing the sample plot size and type to vary from one forest stand to another. When using a compromise sample plot over a large region and a long inventory rotation, optimizing the sample plot for one time point ignores possible changes in forest structures caused by changes in forest management practices.
Background
Typically, a samplingbased national forest inventory (NFI) is carried out to provide statistics, for example for national or regional forest programs, sustainability assessments, investment calculations for forest industry, and reporting to international conventions (Tomppo et al. 2010). Forest management inventories (FMI), on the other hand, are carried out to support forest owners in their strategic planning as well as aid decision making concerning harvests and silvicultural measures.
NFIs are based on a set of field plots, for instance in Finland about 15 000 plots are measured each year (Kangas et al. 2018) totaling to 75 000 plots during each five year inventory rotation. In recent years the forest management inventories have been carried out using airborne laser scanning (ALS) data and field plots (e.g. Næsset (2004)). The field plots used may be the NFI field plots or plots measured as a separate measurement campaign. Thus, the field plot measurement is a large investment, and it is important to make it as costefficiently as possible.
In NFI, the inventory design is optimized in the sense that we wish to have the highest accuracy and precision given a fixed budget or we wish to have the lowest cost for a given precision (Päivinen 1987). In a cluster design, that entails selecting the number of clusters or distance between them, the number of plots in each cluster and the distance between them, and the type and size of plots within each cluster. Optimization is possible, if we make assumptions concerning the population (Mandallaz 2007). In an analytic setting, we need to be able to anticipate the betweenplot variance (Mandallaz and Ye 1999).
Defining optimal sample plot size and type analytically would require that we can anticipate the effects of the plot size and type on the betweenplot variance. If the expected betweenplot variation could be expressed as a function of plot size (see Zeide (1980)) the optimal plot size could be calculated analytically. The optimal size, however, also depends on the size distributions of the forest stands as well as on the spatial patterns of trees.
While some factors affecting the accuracy and precision can be accounted for analytically, other aspects like the spatial structure of forests are more complicated. The analytic calculations usually assume a random pattern (Mandallaz 2007). In Finland, however, regular patterns of trees have been observed more commonly (57%) than random (25%) and clustered (18%) patterns (Tomppo 1986). Therefore, the optimal plot is typically addressed using simulation (e.g. Henttonen and Kangas (2015)).
In this study based on field data from different types of forests, we compared the precision of the basal area and tree density estimation and costs for various sample plots of different type and size. We used the unbiased HorvitzThompson estimator to estimate the basal area and tree density and obtained its variance by integrating over the forest plot. The resulting standard deviation and corresponding costs of various sample plots were investigated with respect to the spatial structure of forests and other stand variables such as tree density, basal area and diameter distribution that are potentially correlated with the spatial structure (see e.g. Tomppo (1986) p. 40 ff.). By classifying our data, we studied how the spatial structure of forests and other stand variables affect precision and costs of different sample plots. Further, we examined the effect of small trees on the spatial structure, precision and costs.
Methods
Materials
We used data of tree locations and diameters measured at 1.3 m (dbh) from different types of forest stands, including experiments of unevenaged forest management and thinnings from below resulting in different spatial patterns of trees. Also data from natural forests and peatlands were included. The total number of forest plots from different data sources was 396 (Fig. 1). In order to distinguish this data from the sample plots, they are henceforth referred to as forest plots.
Erika
The Erika data set consists of 21 experimental plots of 40 m ×40 m in managed, unevenaged Norway spruce dominated forests at five locations in southern Finland (Eerikäinen et al. 2014). Between 1991 and 2012, the plots were measured usually four to five times with five years’ intervals, recording the locations, tree species, and size characteristics (dbh and height) of all trees ≥ 10 cm tall. Trees with dbh ≥ 0.1 cm were included in our calculations. Only the fourth measurement of each plot was included in our main study. These measurements were taken either in 2007 or 2012. From one plot with only two measurements, the data from 1992 was used.
Harkas
The Harkas data set comprises 312 plots from 39 longterm thinning experiments mainly in southern and central Finland (Mäkinen and Isomäki 2004). These experiments have been established in evenaged, pure, or almost pure Scots pine or Norway spruce stands growing on mineral soil. The recording of tree locations on plots started in the late 1980s. We used the locations and tree dbhs from the most recent measurement for each plot, since the more recent locations were measured with more accurate methods, i.e. tachymeter, instead of distance (measuring tape) and compass direction used earlier. Only plots where both tree locations and plot corners had been mapped were included. Plot areas were estimated using the coordinates of plot corners and therefore these areas are not exactly equal to those presented in earlier reports. The median area of the plots was 1004 m^{2} (range 788 m^{2}  2460 m^{2}). The minimum dbh in the Harkas measurements was 4.5 cm.
Inari
The Inari data set consists of 18 forest plots of size 50 m ×50 m measured on the locations of plots from the 8th National Forest Inventory in northernmost Finland (Henttonen and Kangas 2015). The coordinates (tachymeter measurement) and dbh of all trees with dbh ≥2.5 cm were recorded.
Multia
The Multia data set consists of 30 field plots of size 32 m ×32 m measured in 2014 in Multia and Keuruu, southern Finland (Tomppo et al. 2016). These data were collected for validation of a remotesensing based forest resource estimation. Therefore, plots were subjectively located to young thinning stands, advanced thinning stands and mature stands. The coordinates and dbhs of trees with dbh ≥2.5 cm were measured using Sonar caliper.
Various additional data sets
The Various additional datasets consist of large plots measured in different types of forests. Data from Vesijako, southern Finland, comprises two plots of size 100 m ×100 m and 70 m ×130 m. The plots were located in mixed coniferous advanced thinning stands dominated by Norway spruce and Scots pine, respectively. The coordinates (tachymeter measurement) and size characteristics (dbh and height) of all trees were recorded. The smallest observed dbh in these plots was 5.7 cm.
The data from Kreutz et al. (2015) was collected from Värriö Strict Nature Reserve in northeastern Finland and it consists of three plots of size 300 m ×40 m located in natural forests at different successional stages. In measuring tree dbhs they were rounded to the closest cm. The minimum dbh was 1 cm.
Hökkä et al. (2008) collected mapped tree data from seven Scots pine dominated stands growing on drained peatlands in different parts of Finland. We used their data from a total of 10 plots in five stands. Similarly to the processing of Harkas data set, we left out some parts of the data because of missing or unclear plot corner or tachymeter location measurements and the plot areas were thus not equal to the report of Hökkä et al. (2008). The median area of plots in our calculations was 6392 m^{2} (range 1604 m^{2}  15620 m^{2}). The minimum dbh was 4.5 cm.
Sample plot types and sizes
We considered 99 different sample plots, including different specifications for the circular fixed radius determining the overall size, relascope and circular concentric plots specifying the type as follows:

(i)
Fixed radius plots with the radius r_{max}=3,4,…,11 m in which all trees above a certain dbh are measured (9 different plots).

(ii)
Relascope plots with the maximum radius r_{max}=3,4,…,11 m and basal area factors q=1,1.5,2,2.5,3 (45 different plots). A tree is included in the sample plot if its distance to the sample plot center is at most \(\min (r_{\text {max}},50\,dbh/\sqrt {q})\) (see Tomppo et al. (2011, p. 25 f.) for more details).

(iii)
Concentric plots with radii (r_{1},r_{max})=(1,3),(2,4),(3,5),(4,6),(5,7),(5,8),(6,9),(6,10),(7,11) m for the two circles where the trees with the dbh smaller than 5, 7.5, 10, 12.5, 15 cm are measured only from the smaller circle with radius r_{1} (45 different plots).
Precision of forest resource estimation
We assumed that the sample plot location s is chosen uniformly randomly from the observed forest plot window \(W\subset \mathbb {R}^{2}\) and that the forest characteristic Y is estimated using the unbiased Horvitz–Thompson estimator (Horvitz and Thompson 1952)
where n is the finite number of observed trees in the observation window W of the forest plot, I_{i}(s) is the indicator that tree i is in the sample plot centered at s, Y_{i} is the characteristic of tree i, π_{i} is the inclusion probability of tree i, and W denotes the forest plot area. We considered the estimation of the tree density measured in number of stems per hectare (Y_{i}=1) and the basal area per hectare (Y_{i}=π(dbh_{i}/2)^{2}).
We measured the precision of the forest resource estimation by the variance of the estimator (1). Based on Theorem 4.2.1. from Mandallaz (2007), the variance is
where π_{ij} is the inclusion probability for the pair of trees i and j, given by
where x_{i} is the location of tree i, r_{i} is the inclusion radius for tree i given by the sample plot type and size, and B(x_{i},r_{i}) is the inclusion zone of tree i, i.e. a circle with centre at x_{i} and radius r_{i}. For i=j,π_{ii}=π_{i}=B(x_{i},r_{i})∩W/W. The intersection areas in (3) were computed approximately using the R library spatstat (Baddeley et al. 2015). Consequently, the variance (2) was calculated for each sample plot in each forest plot described above going through all pairs of trees in a forest plot.
We further considered the estimation of the change from a time point 1 to time point 2 for the Erika data with measurements repeatedly over time, and estimated the change simply as the difference of the estimates at the two time points, \(\hat {Y}^{(2)}(s)  \hat {Y}^{(1)}(s)\). The formula for the variance of the difference is
where
where 1i and 2j refer to tree i at time point 1 and tree j at time point 2, respectively.
Costs for the comparison of sample plot types and sizes
We assumed that the cost (time in minutes) to measure tree i in the sample plot of certain type and size was
where s is the sampling location and r_{i} is the inclusion radius of tree i. Thus, we assumed simply a fixed cost per measured tree (0.5 min) and an additional cost per borderline tree (0.5 min). A tree was defined to be a borderline tree if its distance from the sample location was between 0.9r_{i} and 1.1r_{i}. Given the single tree cost (6), the expected cost for measuring the sample plot is
where
Similarly as the variance (2), the expected cost (7) was calculated for each sample plot in each forest plot.
The expected cost for trees of the sample plot in a size class D_{k}=[d_{k},d_{k+1}), k=1,…,K, is
Classification of forest structure
In order to study the effect of spatial structure of forests on the precision and costs of different sample plots, the forest plots were divided into different groups of similar stand variables.
For the classification of the spatial structure of a forest plot, tree locations (at stem center) are mathematically expressed as point patterns (x_{1},…,x_{n}) with a finite number of n trees observed on a forest plot window W. Each point pattern is analyzed as a realization of a point process X, which is assumed to be translation and rotation invariant. In what follows, the terms point and tree location can be used interchangeably. Likewise, the intensity λ of the point process is equal to the tree density, albeit per m^{2}.
The tree locations were divided into clustered, random and regular patterns by utilizing the Lfunction, which is the variance stabilizing transformation of Ripley’s Kfunction (Chiu et al. 2013, Chapter 4.6) given by
The function λK(r) gives the expected number of points of X within a circle B(o,r) around a typical point o and radius r (in m) without counting o itself given that there is a point of X in o.
In the completely spatially random (CSR) case with no interaction between the points, L(r)−r=0 for all r≥0. This fact can be used in a test for CSR based on the test statistic
with Ripley’s isotropic edge corrected estimator \(\widehat {L}\). The CSR hypothesis can be rejected at a 5% significance level if
(Chiu et al. 2013, pp. 57 f., 139 ff.). Due to size limitations of some forest plots in the Harkas data, distances up to r_{t}=5 m were taken into account for a short range classification.
For the analysis, the statistical software R version 3.4.4 (Core Team 2018) was used together with the package spatstat (Baddeley et al. 2015).
Results
Relationship between spatial structure and stand variables
In order to understand the relationship between the spatial structure of forests and other stand variables in different types of forests, we calculated the average (standard deviation) tree density, mean basal area weighted dbh, and basal area of the forest plots and coupled them to the results of the spatial structure classification (Table 1). The Erika data with the smallest minimum dbh of 0.1 cm have mainly clustered plots with a relatively high tree density and mean dbh. The Harkas data including the thinning experiments have regular tree patterns, a lower average tree density, and the largest basal area. The Inari data with a minimum dbh of 2.5 cm have relatively few trees and appear mostly clustered, whereas the Multia data with the same minimum dbh, but higher tree density, have both clustered and regular patterns. In contrast to Tomppo (1986), where smaller forest plots where considered, only 12 forest plots (3%) were classified as random. This small proportion of random forests results from large forest plots of this study that facilitate the detection of clustering and regularity due to more observations.
Given the classification according to spatial structure, the forest plots were partitioned according to standard deviation of dbh, basal area and tree density using the recursive partitioning function implemented in the rpart R package (Therneau et al. 2017). We concluded from the partitioning for forest structure that clustered patterns had a larger dbh range than regular patterns, whereas regular patterns tended to have larger trees with about the same size. Consequently, a grouping with respect to dbh standard deviation was not informative for this study since one group would mainly contain clustered and the other mainly regular forests. In our data, all forest plots with a tree density ≥3214 trees/ha were classified as clustered.
Based on the partitioning, each forest plot was classified as a plot with small (< 9.8 m^{2}/ha), medium (in [9.8,32) m^{2}/ha) or large (≥ 32 m^{2}/ha) basal area. We further defined different development classes also taking Tomppo et al. (2011, Table 2.17) into consideration. The resulting development classes are based on the mean basal area weighted dbh (dbh_{BA}) and tree density:

seedling stand: mean dbh_{BA}< 8 cm or density > 3214 trees/ha,

young stand: mean dbh_{BA} in [8,26] cm and density in (1500,3214] trees/ha,

advanced stand: mean dbh_{BA} in [8,26] cm and density in (500, 1500] trees/ha,

mature stand: mean dbh_{BA}> 26 cm or tree density ≤ 500 trees/ha.
Seedling stands tend to be clustered and forest plots with large basal area regular (Table 2).
The effect of spatial structure on precision and costs
In order to study the effect of clustered and regular patterns on precision and costs of different sample plot types and sizes, we focused on forest plots with medium basal area ([9.8,32) m^{2}/ha) not belonging to the seedling class. We selected this group of forest plots as it contains both clustered and regular patterns with more than two observations each. Then, we compared the mean standard deviation of the estimator (1) and mean expected costs (7) per forest structure group and sample plot type and size (Fig. 2). The higher the tree density (younger development classes), the lower the precision of the estimated tree density and the bigger differences between the different sample plot types both for clustered and regular forest plots. The differences between different development classes and different sample plot types in the basal area estimation were smaller, largest differences between the sample plot types occurring for clustered patterns and in the youngest development class. In any case, both for clustered and regular forest plots, the relascope sample plots appeared to be the most efficient choice to estimate basal area. On the contrary, they were unfeasible for the tree density estimation. In this case, the fixed radius plots seems to be the best design. In general, the precision was lower in clustered forests than in regular forests. Increasing the maximum radius r_{max} (increasing the costs) further led to a more pronounced improvement of precision for clustered than for regular patterns (see also Table 3).
In a more detailed study, we focused on eight different sample plots with two different maximum radii, namely 7 and 9 m. For the relascope plot we considered the basal area factors 1 and 2 for each case. The inner radii of the concentric plots with these maximum radii were 5 and 6 m, respectively, and the dbh limit was set to 10 cm. We compared the average expected costs for clustered and regular patterns (Table 3) and found that the fixed radius plots were almost twice as expensive for clustered than for regular patterns. As expected, the difference in costs was not as prominent for the other designs where fewer small trees are measured. In the case of the relascope plots, it was slightly more expensive to measure the regular patterns. Furthermore, we calculated the cost savings and loss of precision in percentage (determined by the increase in standard deviation of the estimator) in comparison to the values for the concentric plot with a 9 m maximum and a 6 m inner radius, which is the design closest to the one currently used in the Finnish NFI. For clustered patterns, using a fixed radius plot instead of the concentric design would increase the costs by 45% and would achieve a 18% improvement of the tree density estimation, but it would not lead to any improvement of precision for basal area. Again it can be seen that the relascope design has a large loss of precision (over 350%) for the tree density estimation especially for clustered patterns. For the basal area estimation of regular patterns, all designs with a maximum radius of 9 m seem to have about the same precision. When lowering the maximum radius to 7 m, the precision is reduced by 14% on average which comes with a cost saving of between 33 and 52%. The overall best solution for basal area estimation among the evaluated sample plots seems to be the relascope plot with a maximum radius of 9 m and the basal area factor 1, but even the basal area factor 2 gave reasonable precision. For tree density, it appeared worth taking the fixed radius plot with a maximum radius of 7 m into account instead of the concentric plot with a 9 m maximum radius. Not only can costs be saved, but there is even an improvement in precision for clustered patterns.
We also studied the distribution of costs and precision among the clustered and regular forests for the selected eight sample plots with boxplots (Fig. 3). In general, the precision was higher (lower standard deviation of the estimators) for regular patterns than for clustered. Further, the variability was lower for regular than for clustered patterns in all cases, especially for the precision of the relascope estimation of tree density and expected costs of the fixed radius plots. The variability of the basal area estimation appears similar for all sample plots for either clustered or regular forests. Relascope plots had the smallest cost variability, but they showed a large variability in precision for tree density estimation.
The effect of minimum dbh on spatial structure and change estimation
We studied the effect of the minimum dbh on the spatial structure classification and the estimation of change in tree density between consecutive time measurements using all 98 measurements from the Erika data source. The spatial structure classification depended on the minimum dbh of the trees measured in the forest plots, where with a minimum dbh of 0.1 cm, most of the patterns were classified as clustered (Fig. 4). There was a clear shift towards more regular patterns with increasing dbh limit.
The minimum dbh also had an effect on precision and costs in the change estimation, where with increasing minimum dbh, precision increased while cost and cost variability decreased (Fig. 5). Consequently, minimum dbhs of 2.5 or 4.5 cm decreased the costs considerably in comparison to the 0.1 cm limit, but the patterns were still clustered (Fig. 4). With a minimum dbh of 9.5, the locations of the measured trees mostly formed a regular pattern, where all sample plot types included almost the same trees (Fig. 5). If the main interest is to study the development of young forests, e.g. changes in small trees (with dbh≤9.5 cm), the tree density is typically more important than the basal area. In order to minimize the variance (4) of the estimated change such studies should be based on large fixed radius plots (Fig. 5).
Discussion
It is well known from earlier studies (e.g. Henttonen and Kangas (2015)) that the optimal sample plot type depends on the variable of interest. For volume and basal area, relascope sample plots are both cost efficient and precise, but also other types of sample plots produce precise results. For tree density, fixed area plots are the most precise. This study confirms those results. In cases where the relascope cannot be used reliably, e.g. in very dense forests, additional measurements have to be made to check whether a tree truly belongs to the sample plot. The resulting additional costs have not been included in the cost calculations for this study and could increase the workload variability of relascope plots. We originally considered also more complicated cost models, but finally based the current study on the simple costs (6), because of lack of support for the more complicated cost models. Our simple cost model is based on the assumption that the number of trees and borderline trees are the main factors affecting the costs.
If the spatial structure of forests could be predicted prior to field measurements, for instance from remote sensing data (see e.g. Packalen et al. (2013); Pippuri et al. (2012); Häbel et al. (2018)), it would in principle be possible to let the sample plot size and type vary from a forest to another. However, in the current inventories, the same sample plot is used over the whole inventory region and, thus, a compromise solution is needed. Another aspect is the operational requirements of NFIs. One solution would be to define a budget for a day’s work, and select the sample plot in a cluster by minimizing the RMSEs of the selected forest variables, using the budget as a constraint. However, this approach always leads to measuring as many trees as the budget allows. In addition, it does not take the variability in the workload into account. The plot type with the minimum variability in the costs is the relascope plot and the fixed radius plots have the highest variability due to high variability in the number of measured small trees.
For selecting a sample plot for an operational NFI, we need to balance the measurements of small trees so that the RMSE of tree density is acceptable while the plot design is costefficient and robust. In order to produce an optimal and operational plot, we could introduce a probabilistic budget constraint, such that \(\mathbb {P}\)(time used for measuring a cluster of x plots <8 h) >p, and minimize the RMSE of tree density subject to that constraint. In this approach, the parameters to be defined are the number of plots within a cluster and the required probability p.
Measurements from forest plots are not only used in inventory calculations, but they are also used as auxiliary variables in modelassisted stand variable estimation. In FMIs, for instance, the collected data are used to build a model to predict the forest variables of interest to all pixels (raster cells) for a map of a certain region of interest. In such a case, the quality of sample plots may be assessed based on the performance of those models. Adnan et al. (2017) studied the effect of sample plot size and stand density on the quality of estimation of tree size heterogeneity from ALS. Tree size heterogeneity can be related to the spatial structure of forests since regular patterns have a tendency to be evenaged with about the same size for all trees and clustered patterns tend to be unevenaged or show at least a larger variation in tree size. Adnan et al. (2017) concluded that for a reliable fieldbased estimation the smallest sample plot size required is 6 m, but that plot sizes between 9 and 12 m maximize the correlation between field values and ALS metrics. Tomppo et al. (2016) also studied ALSassisted forest resource estimation, but not for the spatial structure. They suggested that a relascope plot with a basal area factor 1 or a concentric plot with a maximum radius of 9 m and an inner radius of 5.64 m and a lower dbh limit of 9.5 cm for the outer circle (used in the Finnish NFI) could be used to reduce the cost in comparison to a fixed radius plot with a 9 m maximum radius while still being feasible for ALSassisted inventories. Future studies could assess whether case depended optimal sample plots can be found for remote sensingassisted inventories.
Conclusions
We classified forests according to spatial structure, tree density and size distribution and found that regular and clustered patterns of trees tend to have different forest characteristics. All in all, it can be concluded that both precision and costs vary depending on the tree density, basal area, diameter distribution, and spatial structure of a forest as well as estimated forest variable. Therefore, there seems to be no obvious overall optimal sample plot.
Today’s forests in Finland are most often regular as a result of the silvicultural methods used since the 1950s, which include forest regeneration most often by clearcut and planting, or due to thinnings from below in younger forests. The amendments to the Forest Act (2013) allow unevenaged forest management since 2014. This will slowly increase the proportion of clustered forests. This trend makes the monitoring of the development of small trees even more important than before e.g., for the estimation of forest growth and for the prediction of scenarios for the future development of forests. For these purposes, sample plots which give more weight to small trees than relascope plots, where the inclusion probability is proportional to dbh^{2}, could be considered. For example, this could be achieved by estimating the inclusion probabilities of trees as a function of several tree characteristics (instead of only dbh^{2}) using data from previous inventories. Also step functions, leading to multiple concentric circles with the radii depending on tree characteristics, could be used in practice.
Abbreviations
 ALS:

Airborne laser scanning
 dbh:

Diameter at breast height measured at 1.3 m
 FMI:

Forest management inventory
 NFI:

National forest inventory
 RMSE:

Root mean squared error
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Acknowledgements
We wish to thank Saija Huuskonen, Hannu Hökkä, Harri Mäkinen, Risto Ojansuu and Erkki Tomppo for providing the data as well as Merja Arola and Ville Pietilä for advice in data processing. The authors would also like to thank Kari T. Korhonen for helpful discussions.
Funding
Henrike Häbel, Mikko Kuronen and Helena Henttonen were financially supported by the Academy of Finland (Project Number 304212) and Mari Myllymäki similarly by the Academy of Finland (Project Numbers 295100 and 306875).
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The data is not owned by the authors and cannot be shared. The R code is available upon request.
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All authors were involved in planning and conducting the study as well as writing the manuscript. HH conducted the classification, statistical analysis and most of the manuscript writing. MK did the variance and cost calculations. HMH was responsible for the data management. AK mainly contributed to the background and discussion. MM was the principal investigator of this study, had acquired the funding, and supervised HH and MK. All authors read and approved the final manuscript.
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Häbel, H., Kuronen, M., Henttonen, H.M. et al. The effect of spatial structure of forests on the precision and costs of plotlevel forest resource estimation. For. Ecosyst. 6, 8 (2019). https://doi.org/10.1186/s4066301901671
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DOI: https://doi.org/10.1186/s4066301901671