The forest cover in the world was estimated at approximately 3999 million ha in 2015 of which only 291 million ha were planted forests [ 1 ]. The forests provide many ecological, economic, social and cultural benefits such as the regulation of hydrological cycles, wood production, soil protection, provision of food and shelter for animals, recreation, carbon sequestration, and many others [ 2 - 4 ]. While forests suffer from the pressure of population growth and deforestation [ 1 , 5 ], they are also affected by insects, diseases, animals, weather events (as windstorm, ice, snow, and flooding) and others. The damage to the trees can cause problems such as reduced growth, or even tree death [ 6 ], resulting in an impact to forest production and ecological services.
Traditionally, the damage is evaluated by field inventories which are an expensive and time-consuming activity, usually applied with subjective methods and have a limited extent [ 6 , 7 ]. An alternative option is to use remote sensing data to observe damages since spectral signatures can be observed in vegetation under stress [ 8 , 9 ]. There are at least three major strategies for using remote sensing to assess forest damage: early damage detection, extent mapping, and damage quantification [ 6 ]. In forest health, most studies have used remote sensing techniques to map forest conditions at a regional or stand level [ 9 - 15 ]. Individual tree damage is often investigated for disturbance across stand level extents [ 16 - 18 ]. Few studies have been able to examine individual branch scale disturbance because of the high spatial resolution needed for detection.
The use of aerial imagery with unmanned aerial vehicles (UAVs) has greatly increased in the past five years across different fields of study because it has many advantages in comparison with other remote sensing technologies. The main advantages of the UAV are the low cost of acquisition [ 19 , 20 ], possibility of frequent monitoring [ 21 , 22 ], adaptability to carry various sensors, as thermal, infrared and multispectral cameras or even Lidar scanners [ 19 , 23 - 25 ], the high resolution obtained [ 19 , 23 , 26 ], and the development of processing software focused on the automatic reconstruction of surfaces using the UAV data [ 27 , 28 ]. An example of surface reconstruction has been in forest structure [ 29 ]. Studies have shown that UAVs can help with species identification [ 30 , 31 ], tree height [ 26 , 32 ], crown delineation [ 26 , 33 , 34 ], and forest health [ 35 - 37 ]. The use of UAVs has great potential for analyzing tree branch conditions as an early detection of tree health [ 35 ]. Besides this potential, most of the studies applying UAV imagery to forest health are based in multispectral bands, as near infrared and red edge, in addition to the traditional visible light bands [ 35 - 37 ] as presented in this paper.
This study examined forest health by analyzing the defoliation or blight caused by 17 years period cicadas in a central Appalachian, USA forest plot. A preview of some results was presented in [ 38 ]. The periodical cicadas are from the genus Magicicada and are known as the species with the longest juvenile development since they stay as nymphs on the underground being fed from root xylem fluids for 13 or 17 years [ 39 ], and emerge from the ground to become adults, reproduce, and die shortly after. They are present in the eastern region of United States, and emerge each 13 years in the southern and midwestern deciduous forest, and every 17 years in the northern and Great Plains states [ 40 ]. Along with the high density of cicadas presence, it is also been observed that the mortality of tree branches occurs due to cicada oviposition in the trees [ 41 ]. The oviposition occurs primarily in young trees [ 41 ], and more in tree species susceptible to oviposition, however, it does differ by year of the cicada brood [ 42 ].
The effect of the cicada’s oviposition in the trees is controversial [ 42 ], but it is generally considered that they do not permanently damage the trees [ 41 , 43 , 44 ], even if some species result in a reduction in growth after the oviposition [ 41 , 43 ]. The dead branches can increase the susceptibility to diseases and from other forest pests [ 42 ]. In this study, we wanted to investigate the utility of using UAV imagery to map the extent of cicada damage in a mixed mesophytic hardwood stand in an Appalachian forest field plot.
2. Materials and Methods
2.1. Study Area
This study was performed at the West Virginia University Research Forest (WVURF), which is composed of approximately 3075 ha of mixed hardwood forest. During the summer of 2016 the WVURF encountered a 17-year cicada occurrence in which many deciduous trees were damaged by the insects. To analyze the extent of the cicada damage, we selected one 21 ha site at the WVURF and collected aerial imagery by UAV (Figure 1).
In the 21 ha site we focused on 15 circular plots with a 25 m radius. In each of the plots we calculated the cicada damage as a percentage to the amount of forest. This site was selected because it has been monitored for various forest management projects, and the collection of the imagery was coincident with the cicada occurrence. This site is representative of forest species in the region.
2.2. Data Collection
The imagery was collected over four seasons between 2016-2017, starting in Spring 2016. For this study we only utilized the images collected in the summer (July of 2016) and winter (March of 2017). The imagery collected in the summer was used to highlight the cicada occurrence, while the imagery from the winter was used to generate a digital terrain model.
The images were collected using a Phantom 3 professional UAV, equipped with a RGB (FC300X) camera. The FC300X camera sensor had dimensions of 6.317 mm × 4.738 mm and a focal length of 3.6 mm. The UAV the RGB camera was gimbal mounted in order to minimize vibrations in the camera.
Flight planning was done with the Maps Made Easy application, which allowed the selection of overlap, height and direction of the flight. Images were captured using two flight directions (called double grid collection), which means that the area was flown two times (one north-south and another west-east). The double grid format is important in forests because the tree crown positions can obscure important features. We chose an overlap of 85% (lateral and forward) with an altitude of approximately 100 m.
Since the area had a large variation in elevation (mostly in the north-south direction), it was critical to integrate the mapped topography to assure the UAV followed the elevation contours. This option is available in Maps Made Easy by the Terrain Awareness tool.
Figure 1. Study site location. Sources: top two left, vector files from the US Census Bureau website, and bottom left map from © OpenStreetMap (and) contributors, CC-BY-SA, and in the right, data imagery obtained from the UAV collection.
During the leaf-on phenology (summer), we obtained 1673 images as compared to the winter leaf-off collection of 971. The smaller number of images during the leaf-off collection was due to a single grid acquisition of the imagery processed. For the leaf-off data collection, the illumination conditions were highly variable and therefore we only processed one dataset.
In addition to the imagery collection, we also placed targets and collected control and check points during the image processing. We placed 12 targets in the area and we used 3 as check points, while the other 9 were used as control points. The targets were made using 0.38 m2 plywood panels painted in black and white. These targets were placed in the roads at north and south of the site, as well inside the forest. The placement of targets inside the forest was a challenge since it required locating canopy gaps to allow their viewing during the leaf-on imagery. The coordinates of the targets were obtained using an iGage X900S-OPUS GNSS static receiver, mounted in a tripod at a standard height of 2 m above the ground. For each point the receiver recorded at least 15 minutes of data positions, and in some cases, we collected 2 hours (when the 15 min did not provide a solution). The recorded data was sent to the Online Positioning User Service (OPUS), which returned the real point position calculated using GPS and corrections calculated by available CORS (Continuously Operating Reference Station) stations.
2.3. Image Processing
After data collection, the images were processed using Agisoft Photoscan Professional Version 1.2.6. Each dataset (leaf-on and leaf-off seasons) was processed separately. The processing was similar for both datasets, but the leaf-off dataset required extra steps. The images were aligned using the ground control point and the coordinates from the pictures (from the UAV onboard GPS). The alignment step was done using the high accuracy setting on Agisoft. The dense cloud was created using the Medium density and Moderate depth filtering.
We generated a digital surface model (DSM) from the dense point cloud. For the leaf-on dataset, the DSM was built using all the points, while for the leaf-off this process was done using only the points classified as ground. The leaf-off point cloud classification was accomplished using a tool available on Agisoft, which considered the parameters maximum angle, maximum distance and cell size. The classification was improved by manually selecting groups of points and placing them in the correct class. This way instead of a DSM we obtained a digital terrain model (DTM) of the area.
Lastly, we generated an orthomosaic using the DSM as a surface for the leaf-on dataset, and DTM for leaf-off dataset. After the orthomosaic generation, all the products (dense clouds, DSM and DTM, and the orthomosaics) were exported. During the steps of DMS/DTM and orthomosaic generation we selected the best possible resolution which was 3 cm for all data. The processing is summarized in Figure 2.
Figure 2. UAV processing steps applied on the leaf-on and leaf-off UAV imagery datasets to obtain the othomosaic, DSM and DTM.
2.4. Cicada Damage Detection
The cicada damage was determined using the Maximum Likelihood Classification (MLC) method in two different configurations. In the first classification (MLC 1), we used only the orthomosaic to classify the damage, which meant a spectral response of the image. In a second attempt (MLC 2), we included the altitude of the area within the orthomosaic. Therefore, in this second situation the classification was made using spectral and elevation values. We hypothesized that the high resolution orthomosaic generated from the UAV imagery and the 3D information obtained from these vehicles could be very useful to many remote sensing classification applications.
For the first classification (MLC 1), we clipped the orthomosaic to the study area, selected samples for all the classes of interest, and generated a signature file to execute the MLC. For the second classification (MLC 2), we first created a Canopy Height Model (CHM), by subtracting the DTM values from the DSM. In some locations, we observed negative values as a result of small variations in the area. These anomalies were converted to zero by a search and replace. The CHM was added to the orthomosaic and then we applied the same classification method to the MLC 1. In both cases we used the same samples, we only generated a different signature file.
To classify healthy and damaged forest extents, we created six classes: Damage, the leaves that are dead because of the cicada oviposition; Healthy forest, all the forest that does not present signals of damage; Ground, the roads and large open spaces in the canopy that penetrate to the ground; Shadows, all dark regions created by the shadows of the trees in the images; Small vegetation, the scrubs and bushes mostly founded in the edge between the forest and the roads, as well portions of grass; and Wood, representing the dead trees where only the trunks are visible. Examples of the classes and selected samples are presented in Figure 3.
Figure 3. Training samples collected and utilized in Maximum Likelihood Classification. In (a) the blue polygons represent damaged tree branches; in (b) the yellow represents areas with healthy forest; in (c) the brown shape represents a sample of ground; in (d) the white represents a sample of shadows in the image; in (e) the orange highlights a sample of small vegetation; and in (f) the red polygons represent samples of wood.
We used 50 random points to calculate the accuracy of the classification. These points were randomly distributed throughout the area. We derived features from the two classifications (MLC 1 and MLC 2) and the real feature (classified by visual interpretation) in each point position. With these values, we built a confusion matrix and calculated the Kappa index.
To better evaluate the severity of the cicada damage in the forest, we calculated the percentage to the total of forest in the 15 plots.
The leaf-on and leaf-off imagery produced a complete dataset for the study area. The leaf-on imagery provided a high resolution orthomosaic where we could observe the cicada damage, a 3D point cloud and a DSM. The ground resolution obtained from the leaf-on imagery was 3.03 cm/pix, and the DSM presented a resolution of 12.1 cm/pix with 68.2 points/m2.
The leaf-off imagery was used to create a DTM for the MLC 2, yet this dataset also created an orthomosaic and a 3D point cloud. The leaf-off imagery presented a ground resolution of 4.85 cm/pix, the DTM presented a resolution of 19.4 cm/pix, and a dense point density of 26.5 points/m2. The accuracy of the processing by the control and check points is shown in Table 1.
In Figure 4, the results are presented from the image processing of both datasets, leaf-on (orthomosaic and DSM) and leaf-off (orthomosaic and DTM), as well the CHM from the DSM-DTM operation.
Based on this data, we performed the two classifications and found the values for each category by plot. This information is presented in Table 2 and Table 3, respectively for MLC 1 and MLC 2, as well in Figure 5.
The classification accuracy based on the Kappa index was calculated as 0.35 for MLC 1, while it was 0.86 for MLC 2. The confusion matrix is presented in Table 4.
Figure 4. Orthomosaics, DSM, DTM and CHM obtained from the UAV imagery leaf-on and leaf-off datasets.
Table 1. Processing accuracy.
Table 2. Classification results for MLC 1, using only orthomosaic.
aResults for plots and total are in m2, while the result for the total area is in ha. Value in brackets is the standard deviation.
Table 3. Classification results for MLC 2, using orthomosaic and CHM.
aResults for plots and total are in m2, while the result for the total area is in ha. Value in bracket is the standard deviation.
Table 4. Confusion matrix from the classifications MLC 1 and MLC 2.
Where: D = Damage; HF = Healthy forest; SM = Small vegetation; S = Shadows; G = Ground; W = Wood.
Based on the results presented in the Table 4, as well in the Figure 5, we can conclude that some classes are much more affected by the existence of the CHM than others. The classes Ground, Small vegetation and Healthy forest are the most affected. The Healthy forest was in many cases confounded with Small vegetation in the MLC 1, especially for the species with a light green color. In the MLC 2 that did not happen as much because the smaller vegetation presents a lower value in the CHM. Similarly, the ground was classified as damage in some cases when the MLC 1 was applied. This result was observed in plots 1 and 2.
Figure 5. Maximum likelihood classification results on the cicada damage detection using only spectral information (MCL 1), and using spectral and height information (MCL 2).
This study highlighted the importance of additionally produced UAV outputs for classifying a unique forest disturbance. Specifically, the inclusion of DTM and DSM to create a CHM proved to be critical for the classification of the cicada damage. A similar approach was earlier applied using combinations of high-resolution imagery and Lidar and was found to be successful in many applications [ 15 , 45 - 47 ]. We believe that the UAV data can be used in many of these situations, being a source of 3D and spectral information from the same source, reducing costs and time of acquisition.
Our result helps to bring attention to the use of UAV imagery for many landscape classification studies in which a unique feature at a high resolution is required for mapping. This may include not only vegetated features but any structure in which the goal is to better classify its extent or compare a location to its neighbors such as in stream riparian corridor analysis for the purpose of additional derivatives such as flow direction, accumulation, heat load index, topographic moisture index, and other geomorphic attributes [ 22 , 48 - 50 ]. Compared to earlier remote sensing platforms in which only satellite or fixed wing aircraft provide spectral information, the inclusion of the structure from motion output from UAVs makes it a unique and very promising alternative to the traditional aerial imagery sources. This is especially relevant as more and more UAV platforms, camera components, and flight times improve.
While structure from motion was shown to be important for detecting the cicada impact in this study, it should be noted that the approach does have its limitations. The calculation of the point cloud can result in elevation values with accuracies dependent on ground cover and topographic structure [ 28 , 48 , 50 - 52 ]. Depending on the study, it is critical to acknowledge this limitation. Better positional control and additional processing can improve the structure from motion calculations [ 48 , 51 , 53 ] or the imagery can be combined with Lidar data to better capture the range of elevation values. This is primarily due to the laser pulses ability to penetrate canopy or understory features [ 26 , 28 , 54 ].
However, with Lidar there is a significant time and money investment required to acquire the technology especially when the structure from motion may suffice [ 52 , 55 ]. The value of the information must be considered in future flight and project planning. This study suggests that future research look at the contributions that structure from motion compared to Lidar data provides to make the most cost-effective decisions regarding their use. We believe that one answer or threshold will not always suffice due to the different variable inputs that make up that decision making process. Fortunately, as technology improves, this decision may become easier and the resource management questions that this technology helps to answer will become more widespread across applications.
In this study, we highlight the benefits of using UAV data as a tool to monitor forest health. The potential of this technology does not only exist in the low-cost acquisition of high-resolution imagery, but also in the integration of this data with advances in processing techniques that allow the extraction of 3D information.
This technology is capable to obtain both structural and visual information and to characterize the physiologic status of the forest. The information can be applied in future studies to detect early occurrence of diseases and pests. Since early detection is critical, the approach can be irreplaceable tool for forest management.
This paper is based upon work supported by the National Science Foundation under Cooperative Agreement Number OIA-1458952. Any opinions, findings, and conclusions or recommendations expressed in this material are those of the author(s) and do not necessarily reflect the views of the National Science Foundation. The work was also supported by the USDA National Institute of Food and Agriculture, Hatch project, and the West Virginia Agricultural and Forestry Experiment Station.
 Wunder, S. and Thorsen, B.J. (2014) Ecosystem Services and Their Quantificatio. In: Thorsen, B.J., Mavsar, R., Tyrvainen, L., Prokofieva, I. and Stenger, A., Ed., The Provision of Forest Ecosystem Services. Volume I: Quantifying and Valuing Non-Marketed Ecosystem Services, European Forest Institute, Finland.
 Binder, S., Haight, R.G., Polasky, S., Warziniack, T., Mockrin, M.H., Deal, R.L. and Arthaud, G. (2017) Assessment and Valuation of Forest Ecosystem Services: State of the Science Review. Forest Service, Northern Research Station, General Technical Report NRS-170.
 Defries, R.S., Rudel, T., Uriarte, M. and Hansen, M. (2010) Deforestation Driven by Urban Population Growth and Agricultural Trade in the Twenty-First Century. Nature Geoscience, 3, 178-181.
 Hatala, J.A., Crabtree, R.L., Halligan, K.Q. and Moorcroft, P.R. (2010) Landscape-Scale Patterns of Forest Pest and Pathogen Damage in the Greater Yellowstone Ecosystem. Remote Sensing of Environment, 114, 375-384.
 Meng, J., Li, S., Wang, W., Liu, Q., Xie, S. and Ma, W. (2016) Mapping Forest Health Using Spectral and Textural Information Extracted from SPOT-5 Satellite Images. Remote Sensing, 8, 719-739.
 Olsson, P.O., Jonsson, A.M. and Eklundh, L. (2012) A New Invasive Insect in Sweden—Physokermesinopinatus: Tracing Forest Damage with Satellite Based Remote Sensing. Forest Ecology and Management, 285, 29-37.
 Wulder, M.A., Dymond, C.C., White, J.C., Leckie, D.G. and Carroll, A.L. (2006) Surveying Mountain Pine Beetle Damage of Forests: A Review of Remote Sensing Opportunities. Forest Ecology and Management, 221, 27-41.
 King, D.J., Olthof, I., Pellikka, P.K.E., Seed, E.D. and Butson, C. (2005) Modelling and Mapping Damage to Forests from an Ice Storm Using Remote Sensing and Environmental Data. Natural Hazards, 35, 321-342.
 Honkavaara, E., Litkey, P. and Nurminen, K. (2013) Automatic Storm Damage Detection in Forests Using High-Altitude Photogrammetric Imagery. Remote Sensing, 5, 1405-1424.
 White, J.C., Wulder, M.A., Brooks, D., Reich, R. and Wheate, R.D. (2005) Detection of Red Attack Stage Mountain Pine Beetle Infestation with High Spatial Resolution Satellite Imagery. Remote Sensing of Environment, 96, 340-351.
 Wulder, M.A., White, J.C., Coggins, S., Ortlepp, S.M., Coops, N.C., Heath, J. and Mora, B. (2012) Digital High Spatial Resolution Aerial Imagery to Support Forest Health Monitoring: The Mountain Pine Beetle Context. Journal of Applied Remote Sensing, 6, 62510-62527.
 Wulder, M.A., Ortlepp, S.M., White, J.C., Coops, N.C. and Coggins, S.B. (2009) Monitoring the Impacts of Mountain Pine Beetle Mitigation. Forest Ecology and Management, 258, 1181-1187.
 Murfitt, S.L., Allan, B.M., Bellgrove, A., Rattray, A., Young, M.A. and Ierodiaconou, D. (2017) Applications of Unmanned Aerial Vehicles in Intertidal Reef Monitoring. Scientific Reports, 7, Article No. 10259.
 Zarco-Tejada, P.J., Diaz-Varela, R., Angileri, V. and Loudjani, P. (2014) Tree Height Quantification using Very High Resolution Imagery Acquired from an Unmanned Aerial Vehicle (UAV) and Automatic 3D Photo-Reconstruction Methods. European Journal of Agronomy, 55, 89-99.
 Colomina, I. and Molina, P. (2014) Unmanned Aerial Systems for Photogrammetry and Remote Sensing: A Review. ISPRS Journal of Photogrammetry and Remote Sensing, 92, 79-97.
 Wallace, L., Lucieer, A., Malenovsky, Z., Turner, D. and Vopenka, P. (2016) Assessment of Forest Structure using Two UAV Techniques: A Comparison of Airborne Laser Scanning and Structure from Motion (SfM) Point Clouds. Forests, 7, 1-16.
 Verhoeven, G. (2011) Taking Computer Vision Aloft-Archaeological Three-Dimensional Reconstructions from Aerial Photographs with Photoscan. Archaeological Prospection, 62, 61-62.
 Lisein, J., Michez, A., Claessens, H. and Lejeune, P. (2015) Discrimination of Deciduous Tree Species from Time Series of Unmanned Aerial System Imagery. PLoS ONE, 10, e0141006.
 Hung, C., Bryson, M. and Sukkarieh, S. (2012) Multi-Class Predictive Template for Tree Crown Detection. ISPRS Journal of Photogrammetry and Remote Sensing, 68, 170-183.
 Díaz-Varela, R., de la Rosa, R., León, L. and Zarco-Tejada, P. (2015) High-Resolution Airborne UAV Imagery to Assess Olive Tree Crown Parameters using 3D Photo Reconstruction: Application in Breeding Trials. Remote Sensing, 7, 4213-4232.
 Panagiotidis, D., Abdollahnejad, A., Surovy, P. and Chiteculo, V. (2016) Determining Tree Height and Crown Diameter from High-Resolution UAV Imagery. International Journal of Remote Sensing, 38, 2392-2410.
 Dash, J.P., Watt, M.S., Pearse, G.D., Heaphy, M. and Dungey, H.S. (2017) Assessing Very High Resolution UAV Imagery for Monitoring Forest Health during a Simulated Disease Outbreak. ISPRS Journal of Photogrammetry and Remote Sensing, 131, 1-14.
 Nasi, R., Honkavaara, E., Lyytikainen-Saarenmaa, P., Blomqvist, M., Litkey, P., Hakala, T., Viljanen, N., Kantola, T., Tanhuanpaa, T. and Holopainen, M. (2015) Using UAV-Based Photogrammetry and Hyperspectral Imaging for Mapping Bark Beetle Damage at Tree-Level. Remote Sensing, 7, 15467-15493.
 Lehmann, J.R.K., Nieberding, F., Prinz, T. and Knoth, C. (2015) Analysis of Unmanned Aerial System-Based CIR Images in Forestry—A New Perspective to Monitor Pest Infestation Levels. Forests, 6, 594-612.
 Cooley, J.R., Kritsky, G., Marshall, D.C., Hill, K.B.R., Bunker, G., Neckermann, M.L., Yoshimura, J.I.N., Cooley, J.E. and Simon, C. (2017) A GIS-Based Map of Periodical Cicada Brood XIII in 2007, with Notes on Adjacent Populations of Broods III and X (Hemiptera: Magicicada spp.). American Entomologist, 62, 241-246.
 Clay, K., Shelton, A.L. and Winkle, C. (2009) Differential Susceptibility of Tree Species to Oviposition by Periodical Cicadas. Ecological Entomology, 34, 277-286.
 Speer, J.H., Clay, K., Bishop, G. and Creech, M. (2010) The Effect of Periodical Cicadas on Growth of Five Tree Species in Midwestern Deciduous Forests. The American Midland Naturalist, 164, 173-186.
 Chen, Y., Su, W., Li, J. and Sun, Z. (2009) Hierarchical Object Oriented Classification using Very High Resolution Imagery and LIDAR Data over Urban Areas. Advances in Space Research, 43, 1101-1110.
 Ke, Y., Quackenbush, L.J. and Im, J. (2010) Synergistic Use of QuickBird Multispectral Imagery and LIDAR Data for Object-Based Forest Species Classification. Remote Sensing of Environment, 114, 1141-1154.
 Dalponte, M., Bruzzone, L. and Gianelle, D. (2012) Tree Species Classification in the Southern Alps Based on the Fusion of Very High Geometrical Resolution Multispectral/Hyperspectral Images and LiDAR Data. Remote Sensing of Environment, 123, 258-270.
 Tamminga, A., Hugenholtz, C., Eaton, B. and Lapointe, M. (2015) Hyperspatial Remote Sensing of Channel Reach Morphology and Hydraulic Fish Habitat using an Unmanned Aerial Vehicle (UAV): A First Assessment in the Context of River Research and Management. River Research and Applications, 31, 379-391.
 Lucieer, A., Turner, D., King, D.H. and Robinson, S.A. (2014) Using an Unmanned Aerial Vehicle (UAV) to Capture Micro-Topography of Antarctic Moss Beds. International Journal of Applied Earth Observation and Geoinformation, 27, 53-62.
 Smith, M.W. and Vericat, D. (2015) From Experimental Plots to Experimental Landscapes: Topography, Erosion and Deposition in Sub-Humid Badlands from Structure-from-Motion Photogrammetry. Earth Surface Processes and Landforms, 40, 1656-1671.
 Mancini, F., Dubbini, M., Gattelli, M., Stecchi, F., Fabbri, S. and Gabbianelli, G. (2013) Using Unmanned Aerial Vehicles (UAV) for High-Resolution Reconstruction of Topography: The Structure from Motion Approach on Coastal Environments. Remote Sensing, 5, 6880-6898.
 Hugenholtz, C.H., Whitehead, K., Brown, O.W., Barchyn, T.E., Moorman, B.J., Leclair, A., Riddell, K. and Hamilton, T. (2013) Geomorphological Mapping with a Small Unmanned Aircraft System (sUAS): Feature Detection and Accuracy Assessment of a Photogrammetrically-Derived Digital Terrain Model. Geomorphology, 194, 16-24.
 Harwin, S. and Lucieer, A. (2012) Assessing the Accuracy of Georeferenced Point Clouds Produced via Multi-View Stereopsis from Unmanned Aerial Vehicle (UAV) Imagery. Remote Sensing, 4, 1573-1599.
 Mathews, A.J. and Jensen, J.L.R. (2013) Visualizing and Quantifying Vineyard Canopy LAI using an Unmanned Aerial Vehicle (UAV) Collected High Density Structure from Motion Point Cloud. Remote Sensing, 5, 2164-2183.
 Dandois, J.P. and Ellis, E.C. (2013) High Spatial Resolution Three-Dimensional Mapping of Vegetation Spectral Dynamics using Computer Vision. Remote Sensing of Environment, 136, 259-276.