- freely available
Remote Sensing 2012, 4(2), 484-508; doi:10.3390/rs4020484
Published: 15 February 2012
Abstract: Quantification of biophysical parameters of urban trees is important for urban planning, and for assessing carbon sequestration and ecosystem services. Airborne lidar has been used extensively in recent years to estimate biophysical parameters of trees in forested ecosystems. However, similar studies are largely lacking for individual trees in urban landscapes. Prediction models to estimate biophysical parameters such as height, crown area, diameter at breast height, and biomass for over two thousand individual trees were developed using best subsets multiple linear regression for a study area in central Oklahoma, USA using point cloud distributional metrics from an Optech ALTM 2050 lidar system. A high level of accuracy was attained for estimating individual tree height (R2 = 0.89), dbh (R2 = 0.82), crown diameter (R2 = 0.90), and biomass (R2 = 0.67) using lidar-based metrics for pooled data of all tree species. More variance was explained in species-specific estimates of biomass (R2 = 0.68 for Juniperus virginiana to 0.84 for Ulmus parviflora) than in estimates from broadleaf deciduous (R2 = 0.63) and coniferous (R2 = 0.45) taxonomic groups—or the data set analysed as a whole (R2 = 0.67). The metric crown area performed particularly well for most of the species-specific biomass equations, which suggests that tree crowns should be delineated accurately, whether manually or using automatic individual tree detection algorithms, to obtain a good estimation of biomass using lidar-based metrics.
Urban trees perform ecosystem functions such as sequestering carbon, improving air quality and providing general amenities [1,2]. Urban trees in the USA store 700 million tonnes of carbon (tC) with a gross carbon sequestration rate of 22.8 million tC/yr . The quantification of urban tree carbon storage can lead to a better understanding of the role of urban trees in global carbon accounting for greenhouse gas emissions . However, uncertainties exist in such quantification due to a lack of direct measurements of urban tree allometry and biomass .
Only 10% of the trees in urban areas in the USA are publicly-owned; the remaining 90% are on private property . Thus the management of urban trees varies immensely. At the same time, urban trees are subjected to different stresses—they often grow on compacted soil, are subjected to intense pruning, have very little space in which to grow, are improperly staked, etc. . These factors affect the rate of growth as well as the shape and form of the trees, which makes the ability to predict biophysical parameters such as tree height, biomass, and crown dimensions more difficult than with forests, where trees are more homogenous in their growth and form for a particular locality and species. Unlike traditional forests, where trees experience a change in growth and allocation after certain events like thinning, low density of trees in urban environments reduces potential competition for light and other resources .
Urban tree inventories can provide estimates of trees’ biophysical parameters. But urban tree inventories are labor intensive, and thus expensive, because they often place emphasis on measuring individual trees . Cost-effective approaches such as using optical remote sensing and airborne lidar data may provide alternatives for urban tree inventories. Additional cost-savings may occur in urban tree inventories because they are more complex and often take into account a wider range of parameters at the individual tree level.
High resolution to moderate or coarser resolution satellite images and airborne hyperspectral data have been widely used to estimate forest biophysical parameters [10,11]. Some examples include estimating forest biomass using moderate resolution Landsat Thematic Mapper , estimating leaf area index using hyperspectral HyMap data , and estimating several forest inventory parameters using high resolution IKONOS imagery . Issues on using remote sensing for estimation of forest biophysical parameters have been reviewed by  and .
Because of their ability to record vertical structure, airborne lidar data are more useful than two-dimensional optical images in estimating forest biophysical parameters like tree height, aboveground biomass, leaf area index, crown, etc. ([17–25]). Lidar based estimation of forest biophysical parameters has been implemented at the grid level [26,27], stand level [28–30], sub-stand segment level , plot level [32–34], tree cluster level , and individual tree level [36–38]. Only a few parameters, such as height and crown diameter, can be measured directly from the lidar data (e.g., [39,40]). For most biophysical parameters, lidar-based estimation generally involves establishing the relationship between the metrics describing the distribution of lidar-derived heights in a given area and metrics measured (or derived from) in situ measurements [26,41].
The synergistic integration of vertical structure information from lidar data with spectral information from optical remote sensing data improves forest canopy characterization . Such integration has been used to increase accuracy for species classification [43,44], height estimation , and biomass/volume estimation .
The estimation of biophysical parameters, such as biomass, using lidar relies on a strong relationship between the amount of foliage and the various tree components since foliage normally is the main element blocking laser pulses . Despite a growing body of studies using small-footprint discrete return lidar for forest parameter estimation, studies using distributional approaches, which exploit the relationships between distributional height metrics (e.g., mean, range, skewness, percentiles, etc.) and forest biophysical parameters, are rare [26,35,46,47] at the individual tree level [38,48]. Furthermore, there are few to no related studies for individual trees in urban landscapes. Our assumption is that metrics computed directly from the lidar point cloud, rather than from an interpolated raster surface which represents the outer canopy return data and misses the returns from the inner foliage, will improve the estimation of the biophysical parameters.
This study evaluates the potential of height distribution metrics derived from normalized lidar point clouds to estimate total height, diameter, crown radius, and biomass for individual urban trees (defined as vegetation 1 m or greater in height). The study also evaluates the potential improvements to urban tree biomass estimation when high-resolution spectral remote sensing is combined with airborne lidar data.
2. Biomass Estimation Using Airborne Lidar
Forest biomass estimation using lidar data is dependent on how well the height of the tree is related to diameter. Naesset  found bias of the difference between predicted and actual diameter at the stand level to be 0.15–0.74 cm, which was better than using methods based on field inventory and photo interpretation. Biomass is estimated based on height metrics obtained from lidar data [26,50,51] or based on lidar-measured crown variables, e.g., crown width  or canopy cover density . Table 1 shows the results of recent biomass/volume studies in primarily coniferous forests (with some deciduous forests) conducted using lidar data. Because these studies were conducted using different sensors in different forest types, the root mean square error (RMSE) values may not be directly comparable, but in general less of the overall variance is explained in deciduous stands.
Popescu et al.  found the explanatory power of the lidar-derived metrics for predicting biomass for deciduous plots lower than that for pines. One factor contributing to this may be the deliquescent tree forms of hardwoods which result in greater amounts of woody biomass into lateral branches, thereby making the height-volume or height-biomass relationship noisier [23,52,55]. But, additional differences between coniferous and deciduous species related to (1) crown material (leaves versus needles) and (2) branch size and structure may also affect the lidar penetration depth and resulting precision of stand characteristics derived from laser data . Naesset  found that only 2–3% of pulses reached an area of the canopy 2 m or less above ground in a young deciduous forest plot, and 20–25% of pulses reached the same portion of the canopy in a mature conifer stand. The difference in penetration rates may affect the residuals for stand variables that are related to canopy density. Difference in crown shape between hardwoods and softwoods has an effect on the height estimation from lidar data, and hence on the prediction of biomass or volume. Nelson  found that as the crown shape changes from conical (most softwood) to spherical (most hardwoods) the estimates of lidar-based forest height tend to be 16–25% higher with elliptical and spherical canopies than with a conical canopy.
Later studies [41,49] reported a higher biomass and volume for spruce compared to deciduous trees of similar size. The narrow and conical-shaped crown of spruce trees allows for a relatively large portion of the laser pulses to hit low in the tree crowns, whereas more rounded crown shapes of deciduous trees normally will result in laser point clouds located higher up in the canopy.
A mixture of coniferous and deciduous trees within stands degrades the precision of lidar-based biomass estimation and presents a major challenge in practical applications . There is a relative scarcity of component biomass equations, along with substantial variation in the observed estimates from existing equations . Jenkins et al.  compiled component biomass equations for several hardwood and softwood species and developed equations to estimate component biomass as a proportion of total above ground biomass, which shows that hardwoods distribute more biomass in the branches than the stem as compared to softwoods, especially for trees with smaller diameters. Contrary to assumption, the hardwood trees distribute less biomass in foliage than the softwood trees.
Naesset  estimated stand volume of Norway spruce and Scots pine using various tree lidar-based metrics of canopy height and canopy cover density. Two test sites were used, one with 97% pine and the other with 69% spruce and 28% pine. The pine site had a coefficient of determination (for stand volume estimation) of 0.4 and the spruce site 0.8. Norway spruce is usually taller (24–30 m), with a relatively compact crown spread (8–12 m). Scots pine is usually shorter (9–12 m) with a large crown spread (8–9 m). Even though both are conifers, the Norway spruce has a greater height to spread ratio. According to the “apical-deliquescent” hypothesis, a spruce distributes its biomass more to stem than to branches. This might explain the difference in the coefficient of determination, though Naesset  points out several other factors—such as a larger footprint size and lack of stratification—that may also have contributed to the low R2 in pine.
Biomass is dependent on site properties, management regime, and stand age. Thinning changes the distribution of biomass within the crown. Gary  found a strongly skewed distribution of needles and branch wood in the top half of the canopy of unthinned 80-year old lodgepole pine stand compared to a normal distribution in thinned stands. Within species, the distribution of aboveground biomass among the various components changes with stand age. Peichl and Arain  found the relative proportion of stem biomass to total tree biomass increased from 25% for a 2 year old stand to 69% for a 65 year old stand of white pine, while the relative contribution of foliage and branches decreased with stand age.
3.1. Study Area
The study area is on Tinker Air Force Base in central Oklahoma, USA (latitude: 35°25′35.43″N; longitude: 97°24′37.73″W) (Figure 1). The area represents a typical suburban residential area with detached and row houses with trees, both broadleaves and conifers, growing along the road and in the yards and parks. The base is around 20 km2 (5,000 acres) in area and has 472 buildings . There are about 6,600 trees, the most common species being Eastern red cedar (Juniperus virgiana), Austrian pine (Pinus nigra) and Siberian elm (Ulmus pumila) .
3.2. Lidar Data
Lidar data were acquired using an Optech ALTM 2050 lidar system in July 2004 in leaf-on condition. The Optech ALTM 2050 is a small-footprint multiple-return lidar system which uses a 1,064 nm laser. The provided lidar data did not have any return numbers. There were about 8 pulses per m2. The system was flown at a 640 m flight height with a swath overlap of 40%. The pulse repetition frequency was 50 KHz and the scan frequency 45 Hz. The scan angle was less than 15 degrees.
To do away with any complications arising from classifying lidar data using height-filtering algorithms in urban areas, a 2 m-resolution bare-earth digital elevation model (DEM) delivered by the vendor (Tobin Aerial Surveys, Texas) was used. The DEM was evaluated by the vendor using ground control points and vertical accuracy within ±15 cm was reported. A normalized point cloud was computed by subtracting the digital elevation model (DEM) of the area from the elevation of lidar returns. In the normalized point cloud, all points with less than 1 m height were filtered out, which resulted in retaining only the lidar returns from trees and other urban objects. With the help of the normalized point cloud and a color orthophoto (acquired 17 February 2004 with a spatial resolution of 10.2 cm), lidar points within each tree with distinctly separable crowns (3,564 in total) were manually selected. The boundary of each crown was delineated by computing the planimetric convex hull around the lidar points within each tree in ArcGIS. We opted for a manual approach to avoid the discrepancies common when using an automated crown-delineation algorithm, especially in cases where tree crowns are overlapping with other trees or with buildings. Only a few individual tree crown delineating algorithms have been tested in urban landscapes (e.g., ), where conditions are different than forested environments. Various lidar metrics were computed for lidar returns within each individual tree (Table 2).
3.3. High-Resolution Satellite Image
High-resolution satellite data of the area was obtained from a Quickbird satellite image (DigitalGlobe Inc., USA) acquired 17 May 2005. The image was radiometrically corrected, sensor corrected, and geometrically corrected. The image consisted of a panchromatic image with 0.6 m spatial resolution and a 4-band multispectral image with 2 m resolution. The spectral resolution of the Quickbird image is shown in Table 3.
Subsequent to preprocessing, three vegetation indices were computed as follows: normalized difference vegetation index (NDVI) , soil-adjusted vegetation index (SAVI) , and modified soil-adjusted vegetation index (MSAVI) . For each of these three indices, and for spectral bands one through four, tree-specific descriptive statistics (minimum, maximum, mean, and standard deviation) were calculated (Table 4). NDVI enhances vegetation but is sensitive to optical properties of soil background, especially in areas with considerable soil-brightness variation. SAVI minimizes the effect of soil by introducing an adjustment factor to NDVI to account for first-order soil variation and differential red and near-infrared flux extinction through vegetation . Unlike NDVI, SAVI vegetation isolines do not converge to the origin and are independent of soil background . The constant factor varies from 0 to infinity depending on the vegetation density. A factor of 0.5 was used for this study as it has been found optimal in a wide range of conditions. MSAVI replaces the constant factor of SAVI with an iterative self-adjusting factor.
3.4. Field Measurement
Field measurements of the urban trees used for this study were made in 2006. The coordinates of each individual tree were recorded using a GPS unit. A high resolution digital orthoimage was used in the field to verify the location of each tree. Various tree attributes were recorded including species, diameter at breast height, tree height, condition of tree, crown radius, age class, etc. . Diameter at breast height (dbh) was measured to the nearest inch using a logger’s tape. If the tree was co-dominant, the largest leader at breast height (1.37 m) was measured and recorded. Tree height was measured to the nearest foot (0.3048 m) using an Opti-Logic 100 LH Laser Rangefinder Hypsometer. On windy days several measurements were taken and averaged. Crown radius was measured at two directions perpendicular to each other with a logger’s tape to the nearest foot from the center of the trunk to the drip line of the canopy by using a nail to secure the tape to the trunk. For this study, a total of 3,562 trees, 60 broadleaf species and 12 conifer species, were used (Table 5). Most of the conifers are shorter than the broadleaf trees. Among broadleaf species, Platanus occidentalis and Acer saccharinum are, in general, taller than the other species. The descriptive statistics for diameter at breast height and crown size are shown in Table 6. Ulmus pumila, Acer saccharinum, and Platanus occidentalis are among those having larger diameter and crown widths. Conifers generally have smaller dbh and crown size than broadleaf trees.
3.5. Variables Predicted
The biophysical parameters of the trees, including tree height, diameter at breast height, mean crown radius, and biomass were estimated. Tree biomass is usually estimated either through direct measurement such as destructive sampling, or through use of biomass equations and tables . Because the direct method of biomass measurement is often impractical, allometric equations developed for specific tree species and localities are often used to estimate biomass. As there are few allometric equations developed specifically for urban trees (e.g., ), most studies rely on the equations based on forest trees. Allometric equations developed for a tree species in different parts of the world differ little in the values of the parameters [70,71]. This suggests that biomass equations developed for certain tree species in one part of the world can satisfactorily predict the biomass of the species in another part of the world, albeit with some bias in the predictions . The USDA Forest Service has developed and evaluated models to quantify the benefit of urban trees—namely i-Tree Streets (http://www.itreetools.org/streets) and Urban Forest Effects Model (http://nrs.fs.fed.us/tools/ufore). These models also use allometric equations from urban trees of the specific region where available.
For the present study, due to lack of availability of urban tree allometry, forest-derived aboveground biomass equations were used in most cases. The species-specific allometric equations were chosen such that they represent the climatic conditions of the study area, where available, and were based on trees with sufficient range of dbh. Equations used to estimate above ground biomass for major species are listed in Table 7. McHale et al.  compared biomass equations derived from terrestrial lidar scanning of urban trees to equations developed from traditional forests and found that variability ranged from 60–300%, but when a variety of equations are used for the entire urban forest community, variability was reduced to 10%. In the present study, we used multiple species-specific biomass equations, rather than one or two general biomass equations for all the trees in the area, as this should reduce the potential errors associated with using forest-based allometry.
Once all significant variables were identified among the lidar descriptive statistics (Table 3), best subsets regression was used in Minitab version 16.1.1 software (Minitab Inc., Pennsylvania, USA) to select the best subset of candidate predictor variables to be included in each final model. Multicollinearity of all the independent variables were tested using variance inflation factors (VIF) . If any of the variables had VIF value >10, then the variables with the highest VIF was removed, and the VIF computed again with the new set of variables. This process was repeated until all the variables had VIF of ≤10. The best subsets regression was performed with the remaining independent variables that were significant (α = 0.05). The regression models were evaluated using the following three criteria to select the best model : (1) maximum adjusted coefficient of determination (R2adj), (2) minimum Mallows Cp, and (3) minimum mean square error (MSE). In this study, the most parsimonious models with Cp ≤ (p + 1), where p is the number of variables in the model, were chosen.
Each resulting model was subjected to residual and influential analysis. While selecting the final model, the parsimony principle was employed whereby fewer variables were preferred over slightly better values of R2adj or Cp. The predictive capability of the selected model was assessed using cross-validation multiple-correlation  and prediction sum of squares (PRESS) . Outliers in the model were identified using jackknife residuals , where the multivariate distance for each observation is calculated using means, variances, and covariances that do not include the observation itself. Each outlier, as defined by jacknife residuals, was investigated carefully to determine the cause of the outlier. Only when the outlier was due to unnatural causes, such as lidar returns from power wires or dead trees, or anomalous measurements, was it discarded from the data analysis. Outlier removal was particularly important for this study because there was a lapse of two years between the lidar flight and the field data collection. In the two years between lidar data collection in 2004 and field data collection in 2006, some trees had growth in height and crown diameter, others were pruned, and some were completely removed.
4. Results and Discussion
4.1. Relationship between Tree Height and HMAX
The lidar return with maximum height (HMAX) from an individual tree is representative of the return coming from the topmost branch of the tree, and is most often related to the field-measured height of the tree. The mean field-measured height was higher compared to mean HMAX in both conifers (field measured 7.2 m, HMAX 7. 1 m) and broadleaf trees (field measured 10.1 m, HMAX 9.6 m). The height underestimation may have become compounded because of the two year lapse between the lidar flight (2004) and field data collection (2006), in which time the height of tree could have increased.
Previous studies (e.g. ) using individual tree height with lidar have found similar underestimation in forested environments. Hyyppä et al.  and Persson et al.  found an underestimation of 0.14 m and 1.73 m respectively in Norway spruce and Scots pine forests. The difference in bias between the two studies was attributed to lidar point density. Hyyppä et al.  used a point density of 24 points/m2, which was considerably denser than the present study. Using fairly dense lidar data (10 points/m2) in a mixed Bavarian forest, Heurich et al.  obtained similar underestimation of 0.42 m for deciduous trees, but a much larger underestimation of 0.65 m for coniferous trees. The smaller underestimation of conifers in the present study can be attributed to lower growth during the two year lapse period compared to broadleaf trees.
The distribution of the field-measured total height and HMAX for broadleaf trees shows a larger number of trees in taller height classes having lower HMAX than field-measured height, while for shorter trees fewer numbers of trees had lower HMAX (Figure 2). This positive shift in height distribution of field-measured broadleaf trees is likely due to growth during the two year lapse. In conifers, however, the total number of trees was lower for most of the trees in the middle height range (Figure 2). For very tall and very short trees, HMAX overestimated the total height. This result does not conform to the findings by other studies showing lidar underestimates the tree height consistently. In mixed temperate forests of Northern Idaho, Falkowski et al.  found that lidar underestimated high tree height and overestimated low tree height, which is similar to the results obtained for broadleaf trees by the present study. Brandtberg et al.  also found similar results in an oak-dominated forest in West Virginia using leaf-off lidar data. Since the overall height growth for the conifers over two years’ period was minimal, the height underestimation in the upper height class may also be due to lidar pulses missing the conifer top or to random errors in field measurement where it is sometimes harder to locate the tree-tops, leading to over- or under-estimation of tree heights [25,88].
The field-measured tree height and HMAX of 3562 total trees had an R2 of 0.887 and RMSE of 1.34 m (Figure 3). Conifers (R2 = 0.789), had a poorer relationship with HMAX than the broadleaf trees (R2 = 0.889) (Figure 4). The increased probability that lidar pulses missed the conical and pointed tip of the conifers may have contributed to the lower R2 than in broadleaf trees, whose tips are not as pronounced as that of conifers.
The less-pronounced tips of broadleaf trees also contribute to error in field-measured height. The well-defined tips of conifers, on the other hand, make it easier to spot the tip in the field. Two factors are important for achieving good height estimation of individual trees using lidar: (1) correct height filtering and hence accurate estimation of bare-earth surface, and (2) correct delineation of the crown, which reduces error due to false tree tops. Poorer crown boundary delineation can contribute to false tree tops and reduce the R2 considerably .
Some species had a better relationship and others had a worse relationship with HMAX (Figure 5). Ulmus parviflora and Acer saccharinum had R2 below 0.7. These species have a rounded crown with no distinct tree top, thus making it difficult to identify the tree top for the lidar as well as for the field measurer.
4.2. Diameter at Breast Height
Diameter at breast height (dbh) was estimated with crown-based metrics and height-based metrics separately (Table 8). For both sets, one variable with the best relationship was chosen. Among crown-metrics, crown perimeter, Cp, performed best in all cases, and among height-based metrics different variables performed best in different cases. HMEAN had a good fit with all trees, broadleaf trees, and both conifer species, while for broadleaf species the best variables were HMAX or one of the upper quantiles. Crown metrics had a better R2 value than height-based metrics. The result is similar to that reported by Chen et al.  who also found that crown metrics performed better than height metrics to predict basal area and stem volume for individual trees in a deciduous oak woodland in California.
Broadleaf dbh is better estimated using either crown or height metrics than conifer dbh. If measuring crown size with relatively high accuracy is achievable, crown metrics are better predictors of dbh than height-based metrics. Height-based metrics can also give a robust estimate of dbh for individual broadleaf trees, but are not as good for conifers. Persson et al.  and Popescu et al.  found both height and crown width significant for predicting dbh for individual trees in forested areas. Estimation of diameter at breast height can be greatly improved through complementary use of terrestrial lidar, as has been demonstrated for urban trees by Omasa et al. .
4.3 Crown Radius
A strong correlation (R2 = 0.90) was obtained from the relationship between field measured crown radius and the radius measured on the trees identified with lidar (Figure 6(a)). Field-measured crown radius was the average of the two perpendicular measurements taken in the field. Lidar-based radius was computed by assuming the tree crown as a circle: .
Because crown radius is often a function of tree height—taller trees have larger crowns and smaller trees have smaller crowns—field-measured crown radius is related to lidar-measured maximum height but has a lower R2 of 0.75 (Figure 6(b)).
An attempt was made to estimate the crown radius using only height-based lidar distribution metrics (Table 9). Lidar height metrics from conifers have a poorer relationship with crown radius compared to those from broadleaf trees. Among broadleaf species only Acer saccharinum has the lowest R2. Among the metrics, HMEAN, HMAX, and the upper quantiles resulted in the best fit with crown-diameter.
4.4. Aboveground Biomass
Aboveground biomass of conifers had the lowest R2 value among broadleaf trees and all trees combined (Table 10). The lower performance of the biomass models for all trees, broadleaf trees, and conifers compared to individual species (Table 11) might have resulted from aggregating the species-wise models to estimate biomass for broader categories. This might have compounded the variation of biomass between species within the category.
Predictors based on Quickbird performed poorly for all trees, broadleaves and conifers (Table 10). While studies have found good stand-level biomass prediction capacity using hyperspectral or multispectral data in forested areas [91–95], studies exploring the relationship between spectral metrics from high-resolution imagery and forest biomass are largely lacking. Instead of using spectral metrics, most studies have used crown-size information from high-resolution imagery to predict forest biomass. Leboeuf et al.  used Quickbird-derived tree shadow fraction, which is calculated as the ratio of the area of tree shadows to the ground reference, to predict biomass in black spruce stands in Canada. Gonzalez et al.  used Quickbird-derived crown diameter to predict biomass of old-growth forests in California, but found higher uncertainty and lower accuracy than with lidar-derived height. This is due to the poorer relationship between crown diameter and biomass than between lidar-derived height and biomass.
Species-specific relationships had a much higher R2 (from 0.68 to 0.84), Table 11 and Figure 7. Naesset  also suggested the use of careful stratification to improve accuracy. The metric crown area (CA) performed well in all the species biomass models, except for Q. schumardii. In Q. schumardii the number of crown returns explained more variance than crown area. Popescu et al.  similarly found that lidar-derived crown diameter alone explained 78% of the variance associated with pine biomass.
This study is one of the early attempts at estimating biophysical parameters for individual trees in an urban area based on point-based lidar distributional metrics. A high level of accuracy was attained for estimating tree height (R2 = 0.89), dbh (R2 = 0.82), crown diameter (R2 = 0.90) and biomass (R2 = 0.67) using LiDAR based metrics for pooled data of all tree species. Tree height of most species had a good relationship with lidar-measured maximum height, except for species with a round crown and no distinct tree top, which makes it difficult to detect the tree-top for the lidar as well as for the field measurer. The good relationship between field-measured and lidar-measured crown radius indicates that individual tree crown delineation from lidar data was fairly accurate. Species-specific relationships had much higher R2 (0.68 for Juniperus virginiana to 0.84 for Ulmus parviflora) than for general broadleaf (0.63) and conifer (0.45) relationships. Using a general, instead of species-specific, allometric relationship should improve the biomass models for broadleaves and conifers. When estimating the biomass of individual trees during an urban forest inventory, a priori stratification of trees by species affords the use of lidar-based biomass equations developed for the particular species rather than those developed for broader classes. We found that the metric crown area (CA) performed particularly well for most of the species biomass equations. It is imperative that tree crown be delineated accurately, whether manually or using automatic individual tree detection algorithms, to obtain a good estimation of biomass using lidar-based metrics. Though spectral metrics from high-resolution satellite imagery did not perform particularly well in predicting individual tree biomass, future studies can explore other vegetation indices and grey-level texture (such as [98,99]) to improve the prediction capacity of high-resolution imagery. Prediction models from this study, even though developed from trees from a specific urban area, can be applied to other urban areas with similar climate and species composition, and when the lidar data were acquired with mission parameters similar to this study, e.g., density of 8 pulses/m2 and similar footprint size. These kinds of lidar-based prediction models will help in accurate quantification of urban carbon storage at the individual tree level. Future studies should develop models that can predict other biophysical parameters such as leaf area index, stem volume, etc., and management attributes useful for the urban planner such as the pruning level required, potential hazard rating, and age-class of the individual trees. Applicability of the models can be improved by incorporating data from other urban areas, and, if available, using allometric equations based on trees from urban areas rather than forests.
This study was funded by grants from NASA (grant number NNS06AA57G) and USDA (NIFA PINEMAP Project). Authors would also thank Jennifer McKee for data collection and Jessica Dorr and the Virginia Tech Conservation Management Institute for providing lidar data.
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|Table 1. Studies using small footprint lidar to estimate aboveground biomass/volume in forests.|
|Naesset ||Volume||-||0.2§||-||Pine /Spruce|
|van Aardt et al. ||Volume||56.0||8.2||28.0||3-class volume|
|Næsset and Gobakken ||Biomass||-||0.2§||-||Coniferous boreal|
|Popescu ||Biomass||-||16.7||-||Individual loblolly pines|
|Nelson et al. ||Biomass||-||33.9||-||Loblolly pine|
|Hyde et al. ||Biomass||-||24.8||-||Pondorosa pine|
|Hall et al. ||Biomass||-||35.8||-||Ponderosa pine|
|Bortolot and Wynne ||Biomass||-||13.7||-||Loblolly pine|
|Popescu et al. ||Biomass||44.0||29.0||-|
*Volume m3 ha−1, Biomass t ha−1;§ln-ln model RMSE,†Dec = Deciduous and Con = Coniferous.
|Table 2. Candidate predictor variables computed using normalized point clouds from individual trees.|
|Height Distribution Statistics1||Density Measures|
|HMEAN||Mean height||NC||Number of crown returns|
|HVAR||Variance of height||NT||Number of total returns|
|HMIN||Minimum height||NP||Point density (NC /NT)|
|HMAX||Maximum height||NCD||NC /CA|
|HR||Range of height (HMAX – HMIN)||NTD||NT /CA|
|HSTD||Standard deviation of height||NX||(Number of crown returns in x% of HR)/ CA (x = <20, 40, 80, 90, 95, >95)|
|HMODE||Most frequent height of crown returns|
|HCV||Coefficient of variation of height|
|HSE||Standard error of mean of height||Crown Dimension2|
|HKUR||Kurtosis of height||CA||Area of crown projected onto XY plane|
|HSKW||Skewness of height||CP||Perimeter of crown projected onto XY plane|
|HQX||x % Quantile of height (x = 5, 10, 25, 50, 75, 90, and 95)|
1Heights are lidar returns lying under the delineated tree crown area. Only returns > 1 m in height were considered;2Crown dimensions calculated by creating a convex hull around the planimetric projection of lidar returns from the tree crown.
|Table 3. Spectral resolution of the Quickbird image.|
|Band 1 (Blue)||450–520|
|Band 2 (Green)||520–600|
|Band 3 (Red)||630–690|
|Band 4 (Near Infrared)||780–900|
|BandXMIN, BandXMEAN, BandXMAX, BandXSTD||Minimum, mean, maximum and standard deviation of spectral value of Band X, where X = 1 to 4|
|NDVIMIN, NDVIMEAN, NDVIMAX, NDVISTD||Minimum, mean, maximum and standard deviation of normalized difference vegetation index (NDVI) computed as :|
|SAVIMIN, SAVIMEAN, SAVIMAX, SAVISTD||Minimum, mean, maximum and standard deviation of soil-adjusted vegetation index (SAVI) computed as :|
|MSAVIMIN, MSAVIMEAN, MSAVIMAX, MSAVISTD||Minimum, mean, maximum and standard deviation of modified soil-adjusted vegetation index (MSAVI) computed as :|
1NIR = Near infrared band; Red = Red band.
|Table 5. Number of trees measured in the field by height class.|
|Species||Total Trees||Height Class (m)|
|Others conifer (10 species)||182||60||96||21||5||0||0|
|Other broadleaf species (53)||928||313||272||151||122||52||18|
|Table 6. Statistics for diameter at breast height and crown radius of the trees measured in the field.|
|Species||Diameter at Breast Height (cm)||Crown Radius (m)|
|Others conifers (10 species)||25.9||11.5||7.6||66.0||9.7||3.1||3.5||23.0|
|Other broadleaf species (53)||31.3||22.9||0.0||200.7||14.8||7.7||0.0||44.5|
†Std = sample standard deviation.
|Table 7. Biomass equations used to estimate individual tree aboveground biomass.|
|Species§||Biomass Equation#||R2||dbh Range (cm)||N||Locality||Source|
|JUVI||Ln (Y, kg)= −0.912+2.322 Ln (dbh, cm)||0.98||13–37||12||Kansas, Oklahoma|||
|ULPU||(Y, lb) = 2.17565 (dbh, in) 2.4962||0.98||6–70||15||Piedmont (SE USA)|||
|FRPE||Ln(Y, lb) = −1.104+0.88814 ln((dbh, in)2(H, ft))||0.91||2–77||70||West-central Mississipi|||
|ULPA||(Y, lb) = 2.17565 (dbh, in)2.4962||0.98||6–70||15||Piedmont (SE USA)|||
|ACSA||log10(Y, lb) = log10(2.4439)+ 2.5735 log10(dbh, in)||0.98||5–50||119||W. Virginia|||
|QUSH||Ln(Y, kg)= −2.0127 + 2.4342 Ln(dbh, cm)||0.99||<73||485||-|||
|PYCA||(Y, kg) =0.0029 ((dbh, cm)2(H, m))1.4607||0.89||4.0–11.0||6||Pennsylvania, Ohio|||
|PINI||Ln (Y, kg) = −2.5356+ 2.4349 Ln (dbh, cm)||0.99||<180||331||-|||
|PLOC||(Y, lb) = 1.57573 (dbh, in) 2.5801||0.98||12.3–60.7||14||Piedmont (SE USA)|||
§JUVI = Juniperus virginiana, PINI = Pinus nigra, ULPU = Ulmus pumila, PYCA = Pyrus calleryana, PLOC = Platanus occidentalis, FRPE = Fraxinus pennsylvanica, ULPA= Ulmus parviflora, ACSA= Acer saccharinum, QUSH = Quercus shumardii;§Y = above ground biomass, dbh = diameter at breast height, H = total height;#1 lb = 0.4536 kg.
|Table 8. Relationship of diameter at breast height (cm) with crown-size and height metrics.|
|Speciesa||N||Crown-Size Metrics||Height Metrics|
aACSA = Acer saccharinum, FRPA = Fraxinus pennsylvannica, JUVI = Juniperus virginiana, PINI = Pinus nigra, PLOC = Platanus occidentalis, PYCA = Pyrus calleryana, QUSH = Quercus shumardii, ULPA = Ulmus parvifolia, ULPU = Ulmus pumila;bCP = crown perimeter, HMEAN = mean lidar height, HMAX = maximum lidar height, HQx = x% quantile of height.
|Table 9. Results of regression analysis of crown radius with height-metrics.|
|All trees||3,517||Y= 0.30898 + 0.74960 × HMEAN||0.771||0.770||0.770||1.1|
|All broadleaf species||2,414||Y= 0.21928 + 0.76909 × HMEAN||0.779||0.778||0.778||1.2|
|ULPU||378||Y= 0.71799 + 0.59987 × HQ95||0.643||0.642||0.639||1.3|
|PYCA||272||Y= −0.36681 + 0.76381 × HMED||0.733||0.732||0.729||0.7|
|PLOC||205||Y= 0.84456 + 0.42798 × HMAX||0.770||0.768||0.766||1.0|
|FRPA||178||Y= −0.24987 + 0.67583 × HQ75||0.730||0.729||0.724||1.1|
|ULPA||167||Y= 0.70168 + 0.58483 × HQ90||0.818||0.817||0.813||0.7|
|ACSA||160||Y= 0.39968 + 0.56739 × HQ90||0.589||0.587||0.580||1.3|
|QUSH||114||Y= −0.05268 + 0.50024 × HMAX||0.810||0.809||0.804||0.7|
|All conifers||1,092||Y= 1.19172 + 0.38139 × HQ90||0.460||0.459||0.458||0.8|
|JUVI||449||Y= 1.28095 + 0.33242 × HMAX||0.530||0.529||0.525||0.8|
|PINI||440||Y= 1.05681 + 0.39898 × HQ90||0.531||0.530||0.527||0.7|
aACSA = Acer saccharinum, FRPA = Fraxinus pennsylvannica, JUVI = Juniperus virginiana, PINI = Pinus nigra, PLOC = Platanus occidentalis, PYCA = Pyrus calleryana, QUSH = Quercus shumardii, ULPA = Ulmus parvifolia, ULPU = Ulmus pumila;bHMEAN = mean lidar height, HMAX = maximum lidar height, HMED = median lidar height, HQx = x% quantile of height;cR2pred calculated using leave one out cross-validation assessment.
|Table 10. Results of regression analysis of aboveground biomass (kg) of individual trees.|
|R2||R2adj||MSE||R2preda||PRESS||Best Modelb, c|
|All trees (n = 2,425)|
|Lidar only||0.665||0.665||1093.1||0.663||2907146469||Y = −828.1762 + 18.135676 CA + 242.3016 HQ5|
|Quickbird only||0.405||0.404||1456.9||0.403||5156216255||Y = 1261.291+0.00617 MSAVIMAX − 0005016 MSAVIMEAN − 17.67353 * Band4STDEV|
|Broadleaf trees (n = 1,489)|
|Lidar only||0.634||0.633||1303.3||0.632||2538508726||Y = −808.7527 + 18.106044 CA + 264.14317 HQ5|
|Quickbird only||0.432||0.430||1625.5||0.428||3945573886||Y = 9421.6382 − 0.002867 MSAVIMIN − 5.64675 Band2MEAN − 12.89806 Band4MIN − 31.22805 Band4STD|
|Conifers (n = 897)|
|Lidar only||0.453||0.451||680.2||0.447||417899538||Y = −84.97512 + 25.5688 CA − 306.7143 N>90 + 144.889 N40-60|
|Quickbird only||0.336||0.333||750.1||0.328||507518718||Y = −1045.448 + 0.003535 MSAVIMAX + 1925.2053 SAVIMAX + 4.552205 Band4MAX − 13.70097 Band4STDEV|
aR2pred calculated using leave one out cross-validation assessment;bMSAVI = Modified soil-adjusted vegetation index, SAVI = Soil-adjusted vegetation index, and BandX = Xth band of Quickbird imagery;cCA = crown area, HQ5 = 5% quantile of height.
|Table 11. Results of regression analysis of aboveground biomass (kg) of individual trees.|
|ULPU||377||0.702||0.699||1098.9||0.694||Y = −932.5395 + 16.3418 CA+ 161.10597 HVAR + 263.449 HQ5|
|PYCA||274||0.697||0.695||450.1||0.688||Y = −345.3206 + 34.9041 CA+ 1808.5412 HSE|
|PLOC||210||0.803||0.800||780.7||0.792||Y = 1517.2267 + 9.46736 CA+ 158.7919 HVAR − 79.73756 HCV|
|FRPA||175||0.783||0.779||259.2||0.767||Y = −351.1855 + 4.197 CA+ 67.9569 HVAR + 89.8835 HQ5|
|ULPA||171||0.841||0.839||354.3||0.833||Y = −171.942 + 19.2475 CA – 0.5355 NT|
|ACSA||158||0.706||0.701||1964.1||0.687||Y = −3674.714 + 24.5642 CA + 286.0985 HVAR + 593.973 HQ5|
|QUSH||115||0.838||0.833||330.1||0.771||Y = −569.97 + 1.9247 NC + 141.973 HVAR + 198.2907 HQ5|
|JUVI||459||0.684||0.683||737.1||0.678||Y = −660.1173 + 44.694116 CA + 327.94367 HMIN|
|PINI||449||0.715||0.713||197.6||0.708||Y = −284.7497 + 12.792 CA + 1043.889 HSE + 77.7504 HQ5|
aR2pred calculated using leave one out cross-validation assessment;bACSA = Acer saccharinum, FRPA = Fraxinus pennsylvannica, JUV I = Juniperus virginiana, PINI = Pinus nigra, PLOC = Platanus occidentalis, PYCA = Pyrus calleryana, QUSH = Quercus shumardii, ULPA = Ulmus parvifolia, ULPU = Ulmus pumila;cCA = crown area, HQ5 = 5% quantile of height, HVAR = variance of height, HSE = standard error of height, HMIN = minimum of height, HCV = coefficient of variation of height, NT = number of total returns, and NC = number of crown returns.