Monitoring Urban Tree Cover Using Object-Based Image Analysis and Public Domain Remotely Sensed Data

Urban forest ecosystems provide a range of social and ecological services, but due to the heterogeneity of these canopies their spatial extent is difficult to quantify and monitor. Traditional per-pixel classification methods have been used to map urban canopies, however, such techniques are not generally appropriate for assessing these highly variable landscapes. Landsat imagery has historically been used for per-pixel driven land use/land cover (LULC) classifications, but the spatial resolution limits our ability to map small urban features. In such cases, hyperspatial resolution imagery such as aerial or satellite imagery with a resolution of 1 meter or below is preferred. Object-based image analysis (OBIA) allows for use of additional variables such as texture, shape, context, and other cognitive information provided by the image analyst to segment and classify image features, and thus, improve classifications. As part of this research we created LULC classifications for a pilot study area in Seattle, WA, USA, using OBIA techniques and freely available public aerial photography. We analyzed the differences in accuracies which can be achieved with OBIA using multispectral and true-color imagery. We also compared our results to a satellite based OBIA LULC and discussed the implications of per-pixel driven vs. OBIA-driven field sampling campaigns. We demonstrated that the OBIA approach can generate good and repeatable LULC classifications suitable for tree cover assessment in urban areas. Another important finding is that spectral content appeared to be more important than spatial detail of hyperspatial data when it comes to an OBIA-driven LULC. OPEN ACCESS Remote Sens. 2011, 3 2244


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Urban landscapes are a unique combination of natural and built environments. Natural systems and the intertwined ecological services they provide are key components of a city 's infrastructure. For example, a city's urban tree cover could be considered part of the local storm water management system, aiding in pollutant filtration, and reduction of surface runoff and thermal loading on streams.
However, our ability to quantify and monitor these services over time is heavily dependent on accurate and timely tree cover assessments, which can also be used to optimize ecosystem health and resiliency [1 ]. These assessments are typically achieved through field methods limited by access to private lands. Moreover, fe w cities have adequate staff or budget resources that are required to undertake urban fo restry assessments to achieve planning and management goals. Remote sens ing approaches can provide a complimentary, spatially explicit dataset that can be used to devise an on ground sampling regime. Moreover, remote sensing canopy assessments are reasonably simple and can be conducted quickly, inexpensively, and without access or disturbance issues encountered in ground based data collections [2 ,3]; thus, they can provide valuable supplemental information in areas that cannot be accessed on the ground. These spatially explicit assessments provide a means to measure and monitor over time complex urban environments, and their dynamic ecologies [4 ,5], fo r example, through the use of spatial metrics [6]. For instance, tree cover surveys and fo rest pattern metrics are useful to help a city quantify current tree cover status [7], determine the locations and drivers of cover loss or gain [8], and monitor these trends over time [9]. These data can then be used to establish tree protection requirements for new developments, assist with urban tree health management, and determine target areas fo r planting projects. Tree cover information is but one variable available fr om this remote sensing approach, which can also provide information on impervious surfaces and many other ground covers.
Land use/land cover (LULC) classifications are often created to visually assess the composition of urban landscapes and quantify different aspects of the environment. "Land cover" describes natural and built objects covering the land surface, while "land use" documents human uses of the landscape [10]. Remote sensing imagery effectively captures characteristics of the Earth's surface, but it takes an interpreter's knowledge about shape, texture, patterns, and site context to derive information about land use activities fr om information about land cover [1 1]. Classifications typically utilize some modification of the Anderson hierarchical system (Table 1), with generalized LULC classes described at Levels I and II and more detailed classifications fo r Levels III and beyond [1 OJ.
Land use/land cover needs to be class ified at a very fine scale to be effective fo r city planning and urban land management [ 1 1 -13].
Remote Sens. 2011,3 Table 1. Anderson hierarchical classification system showing examples of Levels I-III fo r Urban and Forest Lands [10]; only the classes in red and green have been expanded upon in the hierarchies. Level [14]; this assessment was performed by non-spatially explicit, semi-manual image interpretation [15]. This ambitious policy goal would attain the difference in current estimated and planned urban fo rest cover and certainly increase the urban fo rest. To establish a spatially explicit baseline, an independent remotely sensed-based urban tree cover assessment was contracted in 2007 by the City of Seattle. Native Communities Development Corporation (NCDC) used high spatial resolution or hyperspatial [16] QuickBird satellite imagery in this assessment and tree cover was reported at 22.9% [15 ]. If an overall goal fo r tree cover is 30%, as is common fo r many Pacific Northwest cities, a 50/0 discrepancy in cover could affect planning, management, and policy de cisions aimed at increasing overall urban tree cover. As such, a good monitoring program is required not only in Seattle, but most urban areas interested in preserving or increasing their tree cover. An effective monitoring program will help us quantify how much tree cover there was in the past, is currently, and will be in the fu ture in order to meet tree cover goals.
Remote sensing technologies can provide a means to classify tree cover and a variety of other continuous environmental variables over large spatial extents and moderate temporal extents [9].
Interestingly, remote sensing of urban fo rests originally evolved fr om aerial photography assessment to coarse pixel remote sensing and now is returning to hyperspatial image analysis [17]. Traditional pixel-based classification methods use Landsat satellite imagery to produce LULC maps (e.g., 2001 National Land Cover Database) by assigning individual pixels to a specific class based on a unique spectral signature [11,18]. These coarse per-pixel resolution data, including Landsat, AVHRR and MODIS, generally have greater spectral extents (Landsat) and temporal extents (A VHRR and MODIS), compared to hyperspatial satellite (e.g., QuickBird and IKONOS) and aerial photography (e.g., US National Agricultural Imagery Program-NAIP). Thus, moderate resolution remote sensing has played a critical role in urban tree cover assessment at regional and global scales [19,20].
However, in general, the spatial resolution of Landsat imagery (30 m) limits the ability to identify and map fe atures within a property parcel, yet, decision making typically takes place at the parcel level, and 900 m 2 is larger than most urban property parcels [13]. Furthermore, in heterogeneous canopies fo und in urban enviro nments, the scale between what is considered a fo rest patch and what can be resolved by a 30 m or coarser pixel presents a special challenge [17]. Thus, it is now a well-accepted princip le that this moderate resolution imagery is not appropriate fo r LULC mapping in heterogeneous urban areas [12,13,18].
A relatively new classification method, object-based image analysis (OBIA), sometimes referred to as fe ature extraction, fe ature analysis or object-based remote sensing, appears to work best on hyperspatial satellite and aerial imagery as well as  [18]. The significant strength of OBIA is that it can also be used on fr ee, publicly available, hyperspatial, NAIP imagery, which is limited in the number of spectral bands available. NAIP imagery has a national extent, offers repeatability, allows fo r spatial and often spectral comparability, and can be classified to achieve detailed LULC maps fo r urban planning, management, and scientific research [13,21]. OBIA approach on NAIP imagery has been used in other applications, specifically wetland detection [23], but its utility in urban tree cover mapping has not been explored.
The purpose of this study was to examine the ability of OBIA methods using fr eely-available, public domain imagery and ancillary datasets for classify ing land use and land cover in a heterogeneous urban landscape with suitable detail to allow fo r monitoring and planning at the parcel level. Therefore, specific attention is paid to developing a method that not only determines the amount or extent of tree cover, but also provides the explicit spatial location of that tree cover. It was our goal to generate a repeatable algorithm that can be tailored fo r use with imagery that might have other spatial/spectral resolutions and that could allow for the integration of other data sources.
Specific objectives included: (1) create a flexible algorithm, (2) test algorithm performance on imagery of varying spatial and spectral resolutions, and (3) assess the accuracy and implications fo r tree cover assessment of the resulting classifications, specifically, the im plication on ground sampling design.
We aimed to develop an accurate method that is repeatable on fu ture dates of imagery and at other locations.

Study Area
We created an OBIA algorithm fo r a small, yet diverse pilot study area in Seattle, W A, USA.
Seattle is unique in that it has a diverse evergreen and deciduous tree cover due to distinct soils and microclimates resulting fr om glacially-carved topography and human activity. The pilot study area to look like. We selected this zip code fo r our pilot study area because it is said to be the most culturally diverse in the US [24,25] and has several socioeconomic characteristics such as a wide divergence in education, which could affe ct urban tree cover [26]. Due to this diversity, the variety of LULC in this zip code encompasses the range we expect to see in the whole of the Seattle area.

Datasets
We used two types of remotely sensed data for the OBIA classifications presented in this research and compared our work to a third independent tree cover assessment proj ect created for the City of Seattle using the OBIA technique [15]. Finally, we also used the 2001 National Land Cover Database (NLCD), a nationwide moderate resolution (30 m) % canopy cover product derived fr om per-pixel driven classifiers using Landsat satellite and generated by the US Geological Survey (USGS) [27]; the 2006 data were not available at the time of analysis.
We chose a public domain, 2009 dataset consisting of orthorectified TIFF im agery acquired during leaf-on summer months (August) with fo ur spectral bands including three color and one near-infr ared bands; allowing for fa lse-color im agery display. The NAIP imagery was acquired with the Leica ADS80 Digital Imaging Sensor, at a one-meter ground sample distance (GSD) with a horizontal accuracy that matched within six meters of photo-identifiable ground control points, which were used during image inspection. The reference system used was NAD 1983/uTM Zone ION. We selected these images because the spectral and spatial resolutions should be sufficient to capture small urban fe atures in order to produce a detailed classification and because the imagery was readily available at no cost. We also acquired a 2002 NAIP imagery which consisted of orthorectified TIFF im agery collected during the leaf-on month of June with three spectral bands in the color range (true-color) of the electromagnetic spectrum; no near-infrared band was acquired with the film based sensor. The imagery GSD was 30 cm with horizontal accuracies similar to NAIP imagery; these data were also fu rnished fr eely by the USGS.
We were also given access to 2009 true-color oblique photography of our study area collected by King County, Washington State. The data were accessible through Pictometry extensions for ArcGIS and used for the visual classification accuracy assessment. In addition to the oblique view, fo ur-direction neighborhood-level views were available, at a nominal ground sample distance (GSD) of 15 cm. We also applied these data in the visual classification accuracy assessment.
For comparative purposes only, we used a 2007 QuickBird-based NCDC LULC classification, which was created using the OBIA technique with the goal of determining existing urban tree cover and potential tree planting sites [16] in the city of Seattle, WA, USA.
The City of Seattle put a lot of prior investment into producing parcel datasets, building fo otprints, road layers, etc. These datasets were also utilized because they are a good publically available fr ee resource which can be downloaded online fr om the City of Seattle website, and can save time necessary for classification development and/or refinement. All datasets, dates, sources, description and uses in our proj ect are summarized in Table 2.

Land Use/Land Cover Classifications
We developed LULC classifications using two temporally spaced datasets with varying spatial and spectral resolution. We used Definiens 8.0 to create classificatio n algorithms individualized for each date of im agery. Although the two classification algorithms fo llow a similar basic structure, the fe atures used to create the algorithms are quite different fr om one another. This is due to spatial and spectral resolution of each set of imagery as well as the timing of image acquisition. Further, we used the same anc illary data for both algorithms: a King County parcel shapefile and a building fo otprint shapefile. The building fo otprint shapefile was created in 1993 and did not perfectly represent the building outlines, but it was valuable as a tool to locate buildings that could later be grown or subtracted fr om based on segments generated fr om the imagery. The general steps in our methods included: (l) a primary segmentation using imagery and ancillary building and roads layers to separate vegetation and impervious cover; (2) a secondary segmentation within each of the primary classes using various derivatives (e.g., texture) and spatial and spectral characteristics of the imagery; and (3) a classification using fe atures derived fr om the imagery.
Although the algorithms are too lengthy to describe in their entirety, there are specific themes that were useful in their creation, and are described in more detail below. The target classes used in our approach and in the 2007 dataset created by NCDC are shown and described in Figure 2. Our aim was to produce classes that could be hierarchically aggregated back to the vegetation and impervious covers, suitable fo r fu ture ecological modeling and applications.  Used in Case Study 1 and 2.
Aggregates to an impervious hierarchical class.
Grass -Includes both green, dry grass and hay.
U sed in Case Study 1, 2 and 3.
Aggregates to vegetation hierarchical class.
Developed -Includes 25% -75% impervious with an average 50% impervious; the red line delineates the :-. ... �t---t image elements associated with this class (cars, drive ways, vegetation and bare ground patches less then 2 m2. Used in Case Study 2.
Aggregates to an impervious hierarchical class.
Impervious -Includes roads, parking lots, compacted ground and gravel.
Used in Case Study 1,2 and 3.
Aggregates to an impervious hierarchical class.  Other -Includes shadows that are not part of another class; this class comprises less than 1 % of the landscape.

Case Study 1: Rainier Valley, 2002 Hyperspatial True Color Imagery
In the initial segmentation process we aimed to separate the image into impervious and vegetated surfaces (Scale parameter = 75 Shape (0. 1) Compactness (0. 7)); Table 3. Without an infrared band available we weighted the green band slightly (R (1), G (2), B (1 )), which appeared to assist in the vegetation extraction process.
For vegetation extraction, we ran a second segmentation on a temporary "vegetation" class. We increased the scale parameter to 50 and removed the ancillary data prior to the secondary segmentation.  Table 3 were chosen using a recursive visual selection process by the analyst where the parameters were manipulated by small increments (e.g., value of 5 in the case of scale) and the produced segment or classification fit was compared to the aerial and oblique imagery for randomly selected locations in every class.

Field Sampling Design
One of the main purposes of a remotely sensed tree cover assessment is to guide a complimentary field data inventory of parameters such as tree cover health and species. Part of this proj ect was to design a sampling regime fo r fu ture monitoring of tree cover and tree cover health assessment. We used the 2009 OBIA classification to generate 100 random field sampling points within the study area.
We performed a similar 100 random point generation on the 2001 NLCD tree cover layer. This allowed us to compare the spatial distribution of the field sampling points for the two tree cover classification sources. Although we did perform a visual assessment of these points using the oblique imagery, no actual field assessment was performed at this time, but will be used fo r monitoring tree cover in fu ture projects.

Case Study 1: Rainier Valley, 2002 Hyperspatial True Color Aerial Imagery
Overall classification accuracy fo r 2002 was 7l.3% (khat = 0.63); Table 4. The OBIA method appeared to be most effective at extracting tree cover, buildings, and impervious surfaces (e.g., roads, driveways, paved parking lots). Tree cover was classified most easily, with most of the misclassified points generally fa lling into the grass and shrub classes, although three points were misclassified as impervious. The buildings class had a user's accuracy of 82.5% and a producer's accuracy of 85.3%.
Building points were misclassified as either impervious, grass, or tree. This would not be an issue if one wishes to hierarchically aggregate the broader classes to an impervious and vegetation classification scheme, but could be problematic if the classification product is used fo r other applications such as quantifying building structures or distances fr om buildings to tree cover (e.g., thermal loading calculations). The impervious class had a higher user's accuracy (76.50/0) than producer's accuracy (72.1 %) indicating that the data type could be improved fo r the extraction of this class, at least within the impervious class. A subset of the classification is shown in Figure 3(a).

Error Attribution for Case Study 1
The 2002 classification had 86 points that were in disagreement with the reference data. The greatest source of error (44 points) was due to spectral confusion, as certain classes were difficult to spectrally separate. For example, grass was commonly misclassified as trees. This is the result of (1) limited spectral bands (red, green, blue), where the addition of an infrared band would help improve classification, and (2) seasonality, or timing of the photo acquisition. In this case, the air photo was taken early in the season when grass fields were still green, and therefore appearing spectrally similar to trees. Two points were misclassified due to issues of image spatial resolution, thus it was difficult fo r the image analyst to determine the class the point actually represented, seven points were due to unexplained error. Of the 86 total points, the analyst and the photo interpreter disagreed on the classification of 9 points. Lastly, twenty-one points turned out to be "false error"; these were classified and mapped correctly but because the accuracy assessment was conducted using 2009 data these points were assessed as error. For example, in 2002, there was a building, but it has since been demolished, and thus not present in the 2009 imagery. As demonstrated in other research, the inclusion of LiDAR can provide additional information to the analysis, and should be explored in future research [3 1,32]. However, such an approach needs to clearly justify the additional costs LiDAR data acquisition would incur [33], as a national LiDAR dataset is not yet easily available fo r all areas in the US, unlike the NAIP imagery program.

Case Study 2: Rainier Valley, 2009 Hyperspatial Near-Infrared Aerial Imagery
The OBIA method produced sufficient results using the 1 m, 4-band infrared, NAIP aerial photography (Table 5). Overall accuracy for the 2009 LULC classification was 79.7% (khat = 0.74). In each of these three classes producer's accuracy was greater than (or equal to) user's accuracy, suggesting that we have achieved the greatest amount of detail in our classification using these data and class definitions. Tree cover was classified most easily, and had a user's accuracy of 80.5% and a producer's accuracy of 93 .9%. This indicates that the classification algorithm over-classifies tree cover, and points were generally misclassified as shrub or grass. The building class had user's and producer's accuracy of 88.5%. Building points were misclassified as either impervious, developed (mix of impervious + vegetation), or grass. The impervious class had a user's accuracy of 82.5% and a producer's accuracy of 83.5%, with misclassified points in the building and grass classes. A subset of the classification is shown in Figure 3(b).  (a) (b)

Error Attribution for Case Study 2
For 2009, a total of 61 points were classified in error. Twenty-one points were due to the spatial resolution being too low to accurately determine in which class the point belonged. Eighteen points were outright misclassified. Since the error mostly occurred due to our inability to determine the height of the objects, of these, 17 could probably be attributed to the right class if we added LiDAR data to the classification algorithm [3 1,32]. For example, points were classified as impervious, but actually represented a building, or were classified as grass when it should have been tree cover. Sixteen of the error points were due to differences in photo interpretation between the image analyst who created the classification and the photo interpreter who conducted the accuracy assessment. Most of these were also due to an individual's point designation as grass vs. shrub vs. tree, which again could be addressed with the addition of LiDAR [3 1,32]. Four of the developed class points were classified in error as other (e.g., ground according to the photo interpreter). Finally, two error points occurred because the reference oblique imagery was two months older than the classification imagery and the site had changed; arguably, this is not true error.

Case Study 3: Rainier Valley, 2007 Hyperspatial Near-Infrared Satellite Imagery
We wanted to examine how our classification, created using fr eely available public data, compared to a satellite based hyperspatial imagery with similar spatial and spectral characteristics. The 2007 QuickBird-based NCDC LULC classification was created using the OBIA technique with the goal of determining existing urban tree cover and potential tree planting sites [16] in the city of Seattle, W A, USA. For the purpose of comparison only, we assessed this classification accuracy using the same 300 ground control points used in the two case studies described above. The overall classification accuracy was the highest in all classifications compared in the study at 83.3% (khat = 0.75); Table 6. The 2007 dataset had the highest producer's accuracy fo r the impervious class (93.8%), although this number is slightly less than the user's accuracy of 95.1 % (khat = 0.91). The tree cover class had a producer's accuracy of 89.4% and a user's accuracy of 80.80/0. The shrub and grass classes each had higher user's accuracy than producer's accuracy. Although the ground class had a higher producer's over user's accuracy, both were very low (44.40/0 and 33.3%, respectively).

Other Issues
Based on the error attributions and comparison study discussed above, it appears that our classification errors are due, at least in part, to limitations of the imagery used therein. These can be broken down into three categories: spectral content, spatial detail and temporal availability (seasonal).
The 2002 classification had the highest spatial resolution (�30.5 cm) yet the lowest classification accuracy (71.3%). This could possibly indicate that spectral resolution, specifically information contained within the infrared band, is more important fo r accurately classifying urban landscapes.
Time of year also appears to be a major factor in classification accuracy, quite possibly even bigger than the number of spectral bands. The 2009 imagery was flown later in the summer, so most of the grass was dead, yet the trees were still photosynthetically active and healthy, making it easier to distinguish between grass and trees. In the 2002 imagery, flown in June, both the grass and trees are green making it more difficult to separate these two classes, especially using only spectral information.
Multi-date imagery flown in the same year would be ideal; however, it is rarely available. Another approach would be to utilize a hybrid classification that supplements aerial photography with spectral characteristics derived fr om a coarser dataset such as Landsat [34].  Trade-offs between increases in spatial vs. spectral resolutions and vice versa need to be studied further and taken into consideration when one undertakes tree cover and LULC analysis.
Although we had two hyperspatial datasets fr om different years, and a third assessment conducted using hyperspatial satellite imagery by the City of Seattle, the data were not viewed as suitable for a change analysis as the spatial and spectral dissimilarities in the datasets would make the comparisons difficult and interpretation even more challenging. More research is required into the possibility of standardizing change assessments with discrepant datasets, and more importantly, establishing protocols for interpreting such changes in tree cover and other LULC classes. Of the 100 NLCD sample points generated only 2 did not fa ll into our tree cover classification.
Upon fu rther examination, using the oblique imagery, these 2 points did not fa ll into tree cover at all, and therefore are in error. This is likely due to the coarser resolution of Landsat imagery on which the NLCD is based as the points are close to tree cover, but do not actually fa ll onto it. More importantly, of the 100 points generated by the 2009 NAIP imagery OBIA-drive classification cover (Case Study 2), 72 do not fa ll into the NLCD canopy class. This is because the NLCD data does not capture most of the smaller tree cover patches within the study area. Conversely, only 28 sample points generated fr om the 2009 classification match up with the NLCD % canopy cover layer. The sampling points and tree canopy cover estimates generated using the 2001 NLCD and 2009 NAIP OBIA datasets are shown in Figure 4(a,b) respectively. The NLCD estimates 174 ha of existent canopy cover (regardless of % cover) in this zip code; however our method using the 2009 imagery estimates 403 ha. Some of the discrepancy between NLCD and our estimates can be attributed to dates of the data. Furthermore, we suspect that our tree class is also over-estimated due to shadows in hyperspatial data that might be misclassified as trees with the OBIA approach. The other two OBIA-based classifications also more than double the NLCD existent tree canopy estimates in our study area. Others have shown that the NLCD classification of % canopy cover is misleading [3 6] and that the NLCD is better at mapping canopy cover composed of continuous tree canopies unlike the heterogeneous tree cover of urban areas. Furthermore, we demonstrate that a sampling design based on the NLCD fa ils to capture these small and highly variable patches of urban tree cover that can comprise more than half of the tree cover in an urban area. Failure to ignore these smaller patches of tree cover can result in gross underestimates of ecosystem services provided by urban tree cover and lead to management strategies that favor park lands and larger tracts of urban tree cover.

Conclusions
Similar to previous research applying OBIA to urban landscape characterization [13,3 5,36], we demonstrated that the OBIA approach can generate good and repeatable LULC classifications suitable fo r tree cover assessment in urban areas. This has been shown in arid urban environments [3 5], and human-dominated eastern US fo rest types [3 6], and is now confirmed in a more temperate urban setting such as Seattle. More importantly, we demonstrate that these objectives can be met using fr eely available hyperspatial imagery such as NAIP which has not been done in previous studies. Whereas others have shown the applicability of non-public ally available true color imagery only [3 5], or, near-infrared imagery only [3 6], we compare publically available true color imagery to near-infrared imagery as well as satellite derived imagery. Moreover, NAIP near-infrared imagery has characteristics similar to hyperspatial satellite imagery such as IKONOS and QuickBird, making these techniques potentially interchangeable with those data when the data are available. The OBIA-based classification examined in our three case studies demonstrates higher accuracies in heterogeneous fo rests compared to classifications such as NLCD. This discrepancy is likely due to the classification methods used (e.g., per-pixel vs. OBIA) and the resolution (e.g., spatial and spectral) of the data. This confirms work done by others on urban, suburban, and agricultural landscapes [2 1] and the urban -wildland interface [12].
More importantly, our work suggests that there could be potential trade-offs in spatial vs. spectral resolutions, where spectral content appears to be of more use than spatial detail in tree cover assessments. This trend should be investigated fu rther in experiments where spectral and spatial resolutions can be manipulated. This trend is opposite of the trade-offs fo und when using medium spatial resolution imagery with increased spectral resolution (e.g., Landsat), where higher spatial resolutions are often preferred to additional increases in spectral resolution [3 7]. While undertaking an OBIA approach it is critical to define the 'object', captured by image segments, of analysis. For example, in the instance of mapping urban tree cover, we suspect that imagery with a spatial resolution greater than a pixel size of �5 m (average Seattle urban tree crown width, based on 2010 iTree Eco assessment data) would show lowered accuracies using an OBIA method because the object or image segment no longer represents an individual tree crown. Thus, at that point, additional spectral or 3D spatial (e.g. , LiDAR) information might be of benefit. Further research into data resolution trade-offs that also take into consideration temporal resolution is needed.
Land cover classifications derived fr om hyperspatial remotely sensed data yields information on the urban fo rest that is more accurate and spatially consistent with other high resolution GIS datasets, such as parcel data [13]. Such spatial consistency is critical if the data are to be used as a sustainable management and a decision support tool at the local level. As such, OBIA-based LULC are detailed enough to fac ilitate parcel-based analysis. A range of software solutions capable of the OBIA approach is available; further study looking into open-source vs. proprietary solutions would be valuable.
Although OBIA analysis is resource intensive, requiring large data storage and processing capabilities, these issues could be resolved through a consortia approach where partners off-set some of these costs because a significant cost of production comes fr om fixed costs (e.g., algorithm development). A consortia approach would take advantage of economies of scale and lower production costs through replication of the algorithm over greater extents. Partnership in field data acquisition [1 5,38], using sampling design derived fr om hyperspatial data, can aid in the validation of these heterogeneous datasets; this role could potentially rely on citizen science/public involvement [3 9].