Research Article | Open Access
Nickolas E. Zeibig-Kichas, Christopher W. Ardis, John-Pascal Berrill, Joseph P. King, "Bark Thickness Equations for Mixed-Conifer Forest Type in Klamath and Sierra Nevada Mountains of California", International Journal of Forestry Research, vol. 2016, Article ID 1864039, 10 pages, 2016. https://doi.org/10.1155/2016/1864039
Bark Thickness Equations for Mixed-Conifer Forest Type in Klamath and Sierra Nevada Mountains of California
We studied bark thickness in the mixed-conifer forest type throughout California. Sampling included eight conifer species and covered latitude and elevation gradients. The thickness of tree bark at 1.37 m correlated with diameter at breast height (DBH) and varied among species. Trees exhibiting more rapid growth had slightly thinner bark for a given DBH. Variability in bark thickness obscured differences between sample locations. Model predictions for 50 cm DBH trees of each species indicated that bark thickness was ranked Calocedrus decurrens > Pinus jeffreyi > Pinus lambertiana > Abies concolor > Pseudotsuga menziesii > Abies magnifica > Pinus monticola > Pinus contorta. We failed to find reasonable agreement between our bark thickness data and existing bark thickness regressions used in models predicting fire-induced mortality in the mixed-conifer forest type in California. The fire effects software systems generally underpredicted bark thickness for most species, which could lead to an overprediction in fire-caused tree mortality in California. A model for conifers in Oregon predicted that bark was 49% thinner in Abies concolor and 37% thicker in Pseudotsuga menziesii than our samples from across California, suggesting that more data are needed to validate and refine bark thickness equations within existing fire effects models.
There is interest in predicting fire-caused tree mortality in places where prescribed fire or wildfires are common [1–4]. Heat from flames or smoldering duff at a tree’s base can kill trees, especially those with thinner bark [5–8]. Species-specific bark thickness equations are central to fire effects models such as FOFEM (First Order Fire Effects Model) [9, 10] and FFE-FVS (Fire and Fuels Extension for the Forest Vegetation Simulator) [1, 11, 12].
Tree bark plays a critical role in reducing mortality from fire. Bark protects living cambial tissues from external biotic and abiotic forces [14–17]. Different tree species exhibit distinct strategies in growth and the development of defense features with some allocating proportionally more resources to bark development than others [18–21]. However, there are many factors that can influence the formation of bark and little information exists comparing this trait across geographic gradients [22, 23]. The properties and function of bark are a result of complex evolutionary strategies by these organisms to perform more efficiently and competitively within their native ranges [21, 22].
Bark is comprised of various tissues covering the stem, branches, and roots of woody plants. It is found outside the secondary xylem and includes the inner living phloem and dead outer tissue [5, 24]. Inner bark is produced directly by the secondary cambium and consists of secondary phloem tissues . Outer bark, also known as the rhytidome, is composed of periderm, cortical, and phloem tissue . Bark plays an important physiological role in protecting trees from the environment and infectious microorganisms as well as containing mechanical injuries [18, 26]. Bark thickness (BT) is the most important characteristic for cambial protection from fire, more so than other bark properties like density, moisture content, or structure [14, 20, 27]. Trees with thicker bark are more likely to survive wildfire events. Thick bark provides an insulating layer of protection from heat for the underlying vascular tissues which can prevent cambial girdling [6, 28–31].
Standard fire-caused tree mortality models use BT, derived from species-specific BT equations, along with percent crown scorch as predictors of tree mortality [1, 9, 11, 12]. However, despite its importance in fire-induced tree mortality modeling, there are few studies assessing BT across a range of species and locations . Studies analyzing external factors influencing BT are limited . Site quality and soil fertility have been considered , but site quality cannot be easily altered by forest management. Measures of tree vigor, such as annual radial growth rates, can be associated with reduced likelihood of tree mortality during disturbances such as wildfire . Competition can be reduced to enhance tree vigor but with an unknown influence on BT.
While there are studies correlating BT to tree diameter [34–37], we did not find any that tested for the influence of tree growth and vigor on BT. Therefore, we sought to test whether vigorous rapidly growing trees (in terms of crown ratio or recent growth rate) might allocate more or less resources to bark production. Also unknown is whether BT is an adaptation to fire that differs among areas with different climates and fire regimes. Therefore, we used regression analysis to test for such effects and compared our BT data and best BT models against existing BT models implemented within fire effects models. Our objectives were to(i)examine how BT relates to measures of tree size [diameter at breast height (DBH)], recent growth rates (GR), vigor [crown ratio (CR)], and crown position [crown class (CC)];(ii)quantify BT variation among species along a latitudinal gradient;(iii)develop BT prediction models and compare their predictions against published BT models for the mixed-conifer forest type.
2. Materials and Methods
2.1. Study Sites
Data for the mixed-conifer forest type were collected from Klamath, Tahoe, and Sequoia National Forests and the Stanislaus-Tuolumne Experimental Forest in California. Sampling at these locations provided a latitudinal gradient across the range of mixed-conifer species (Figure 1). Eight species were sampled for BT: white fir (Abies concolor) [ABCO], red fir (Abies magnifica) [ABMA], incense-cedar (Calocedrus decurrens) [CADE], lodgepole pine (Pinus contorta) [PICO], Jeffrey pine (Pinus jeffreyi) [PIJE], sugar pine (Pinus lambertiana) [PILA], western white pine (Pinus monticola) [PIMO], and Douglas-fir (Pseudotsuga menziesii) [PSME]. Climate and geology varied among the study sites (Table 1). The Klamath National Forest (KNF) is recognized as one of America’s most biologically diverse regions [38, 39]. It is situated in a transitional region between hotter and drier areas to the south and colder, wetter climate to the north . Unlike our other study sites, KNF has the Shasta red fir variety (Abies magnifica var. shastensis). The Tahoe National Forest (TNF) data were collected in the Blackwood Creek watershed of the Lake Tahoe Basin Management Unit. This area has a Mediterranean continental climate with warm, dry summers and cold winters with most precipitation falling as snow. The Stanislaus-Tuolumne Experimental Forest (STEF) is located near the town of Pinecrest, California. It is a mixed-conifer forest of high site quality on the western slope of the Sierra Nevada, at lower elevation than the other two Sierra Nevada sites (TNF and SNF). Climate of the region is characterized by warm, dry summers and cold, wet winters, with over half of annual precipitation falling as snow between December and March. The Sequoia National Forest (SNF) sampling was conducted in the Bull Run Creek watershed which has characteristic expansive areas of exposed rock, particularly at higher elevations. The area experiences warm to hot, dry summers and cool to cold, wet winters. Summer brings occasional thunderstorms but most precipitation is in the form of snow falling from October through April.
2.1.1. Field Data Collection
At KNF, TNF, and SNF, trees were sampled along transects spanning an elevation gradient. Every 100 m the closest tree was sampled, followed by one tree of each species in understory and overstory positions, giving data for a range of tree sizes and stand densities. Transects were not straight; they climbed and traversed the slope from bottom to top of each watershed, running approximately parallel to the main creek and avoiding road corridors. Trees below five cm DBH (diameter at breast height), noticeably unhealthy trees, and malformed trees were not sampled. Bark thickness, recent radial growth, and diameter measurements were taken at a height of 1.37 m on each sample tree. Total height and live crown base height were also measured to calculate live crown ratio (CR). Crown class was recorded for each sample tree.
Two BT measurements were taken using a handheld Swedish bark gauge at approximately 90 degrees apart around the tree circumference. Bark thickness was measured from the wood surface to the contour of the diameter tape wrapped snugly around the tree . One shallow increment core was collected at the site of BT measurements. The collective width of the most recent five complete rings measured to the nearest 0.1 mm gave tree growth (GR) in terms of a five-year periodic average annual radial increment (although the series was not crossdated so it is possible that increment was over/underestimated due to missing/false tree rings).
We obtained independently collected data for BT and DBH in ABCO, CADE, PIJE, and PILA at the STEF site in the central Sierra Nevada (Andrew Slack, Humboldt State University, personal communication). Here, sample trees were nearest neighbors of individual PILA trees randomly selected throughout the forest for a different study. Growth and crown ratio were not measured at STEF.
We used multiple linear regression and nonlinear regression to model BT for each species at three study sites with growth and crown ratio data (KNF, TNF, and SNF). Individual variables were either square root- or log-transformed to reduce skewness in data distributions. We compared regression models with and without candidate predictor variables representing tree size (DBH), growth (GR, converted from radial increment to a basal area increment), and tree vigor (CR). The -intercept was forced through the origin because a tree with zero DBH is exactly 1.37 m tall and essentially has zero BT at that height (the tip) but begins to develop bark at breast height as the tree grows taller. We used a second-order correction for Akaike information criterion (AICc) in model selection as this takes into account sample size by increasing the relative penalty for model complexity with small data sets . Models with delta AICc < 2 were treated as similar, among which the most parsimonious model was favored. We also calculated average BT prediction error (mm) in terms of root-mean-square error (RMSE) as an indicator of model performance.
The large sample size for ABCO and ABMA allowed for investigation of geographic location (north, central, and southern latitudes), as well as crown class (dominant, codominant, intermediate, and suppressed) influence on BT. Dummy variables were included in nonlinear regressions to test for differences in BT between categorical variables of site and crown class.
We examined performance of existing, widely used BT models by comparing predictions from these BT models against our California BT models and data. Specifically, we compared our California BT data against predictions from diameter inside bark equations for ABCO, CADE, PILA, and PSME in southwest Oregon  as well as those embedded in the Fire and Fuels Extension (FFE) of the Forest Vegetation Simulator (FVS) [11, 12]. We did not validate another commonly used fire mortality model, FOFEM (First Order Fire Effects Model) version 6.3.1, because the same bark thickness equations were also embedded in the Fire and Fuels Extension (FFE) version 2.0. Prediction errors were calculated in percent terms for each tree in our dataset (percent error = 100 × (predicted-actual)/predicted). We used  and SPSS  to analyze data.
3. Results and Discussion
Sample trees covered a broad range of tree sizes, crown ratio, and growth (Supplementary File, Table S1, in Supplementary Material available online at http://dx.doi.org/10.1155/2016/1864039). Sample size across the KNF, TNF, and SNF sites differed among species. ABCO and ABMA were encountered most frequently along the sample transects. The independent dataset from STEF added records for four species, including very large PILA, as well as CADE, PIJE, and ABCO (Supplementary File, Table S2).
There was a positive trend of increasing tree size (DBH) and BT, although the BT of some conifers varied widely for any given tree size. In general, nonlinear relationships best explained our empirical data with the exception of PSME and CADE where simpler linear models were adopted. Incorporating tree vigor (in terms of recent growth, GR) improved model predictions of bark thickness for four mixed-conifer species, ABCO, ABMA, PICO, and PIJE, indicating that faster growth came at the expense of BT (Supplementary Files, Tables S3 and S4). However, in practice the small differences in prediction errors (8% overall average reduction in RMSE; range 4%–16% reduction by species) indicated that including GR as a predictor of BT only gave marginal improvements over the simplified models with only DBH as a parameter (Supplementary File, Table S3).
We found no significant difference in BT for ABMA or ABCO along the latitude gradient of northern (KNF), central (TNF), and southern (SNF) sample locations. On average, the shastensis variety of ABMA had thinner bark for a given tree size than ABMA along the Sierra Nevada. Bark thickness was slightly but not significantly greater at TNF than further south at SNF (Table 2) where mean GR for ABMA was 3.18 mm yr−1 (i.e., 31% faster). ABCO exhibited a similar but less pronounced trend of thicker bark at TNF and thinner bark at KNF but variability in BT at each site prevented detection of significant differences. Variability in BT was greater among ABMA than ABCO sample trees. For a given tree size in ABMA or ABCO, average BT by crown class was ranked as follows: suppressed > intermediate > codominant > dominant; however, these differences were not statistically significant but were consistent with negative coefficients for GR indicating that faster-growing trees had thinner bark (Supplementary File, Table S3). It should be noted that there are several other factors beyond latitudinal variation which could contribute to the observed differences in BT, such as past management and disturbance regimes, as well as variations in climate and site quality between each of the study locations.
Independently collected BT data from STEF exhibited greater BT for a given DBH than BT at the three National Forest sites. In comparison with STEF data, predictions from our simple BT-DBH models for the KNF, TNF, and SNF locations (models shown in Supplementary File, Table S3) revealed that predicted BT was 10.5% less for ABCO, 20.9% less for CADE, 15.1% less for PIJE, and 21.2% less for PILA than the BT data for the STEF site. To increase the geographic range of applicability of our BT-DBH models, we merged the data from KNF, TNF, SNF, and STEF sites and fitted final models to this expanded dataset (Table 3 and Figure 2). The STEF dataset included BT for larger CADE, PIJE, and PILA than the other sites. Our final models indicated that BT among large-sized (100 cm DBH) California mixed-conifers was thickest for CADE and thinnest for PIMO and PICO (Figure 3). Modeled averages for BT in sample trees above 150 cm DBH ranked PSME > ABCO > PILA. Expected bark thickness (i.e., modeled average) for a 50 cm DBH tree fell into three groupings, where CADE, PIJE, and PILA had relatively thick bark, ABCO, PSME, and ABMA had intermediate BT, and PIMO and PICO had relatively thin bark. Our California models can be used to estimate BT using forest inventory data and quantify diameter inside bark at breast height. The minimum and maximum DBH for each species define the range of application of BT models (Supplementary File, Tables S1 and S2).
The percent differences between our data and predicted BT from the FFE-FVS [11, 12] or Oregon  BT models indicated that these models generally underpredicted BT in California mixed-conifers, most noticeably for ABCO, ABMA, CADE, and PIJE (Table 4, Figure 4). Prediction errors were greatest among smaller trees, where underprediction was common. When compared against California BT data, the FFE-FVS model underpredicted BT for CADE, ABMA, and ABCO of all sizes. For PICO, PILA, and PIMO trees in California, the FFE-FVS model underpredicted BT for smaller trees and overpredicted BT for larger trees. The Oregon models overpredicted BT for PILA and PSME, especially among larger PILA and smaller PSME trees (Figure 4).
Underpredicted bark thickness for most species suggested that the FFE-FVS fire effects model may overestimate fire severity in California. This finding is consistent with validation of the postfire tree mortality models in Hood et al.  where mortality was overpredicted for many of the same species that we studied. The models for conifers in Oregon indicated that bark was 49% thinner in Abies concolor and 37% thicker in Pseudotsuga menziesii than our sample from across California. These important differences and subtler differences according to location and growth rate suggested that more BT data are needed to validate and, if needed, refine equations within existing fire effects models or develop local or regional model variants. Overall, our findings suggest that further study and revision of BT models implemented within fire models are warranted for mixed-conifer forests in California.
Bark thickness correlated with DBH but varied among conifer species. Our modeling indicated that, among 50 cm DBH conifers, BT ranked CADE > PIJE > PILA > ABCO > PSME > ABMA > PIMO > PICO. We did not detect regional differences in BT nor differences between crown class and only slight differences according to recent tree radial growth. These findings suggest that our linear and nonlinear models of BT-DBH have general application within California. We failed to find reasonable agreement between our newly developed BT model predictions and most existing BT models currently used to model fire-induced mortality in the mixed-conifer forest type in California.
The authors declare that they have no competing interests.
NEZ-K summarized and analyzed data and prepared figures. CWA assisted with data summary and performed validations. J-PB designed sampling, assisted with data analysis, and obtained funding. JPK assisted with data summary and validation. All authors contributed to writing of the manuscript.
Andrew Slack provided the independent bark thickness dataset and valuable advice. Scott Burdette collected field data. This work was supported in part by the USDA National Institute of Food and Agriculture, McIntire Stennis Cooperative Research Program.
Supplementary material includes summary statistics for sampled trees in each of the mixed-conifer forest sites in California. Statistics are separated by tree species and include mean, standard deviation, as well as minimum and maximum values for parameters of interest. Additional supplementary materials include original species-specific models for both tree size (DBH) and models incorporating measures of tree vigor (CR/GR), as well as comparative information utilized in final model selection.
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