Harmful algal blooms (HABs) of the toxic dinoflagellate, Karenia brevis, occur annually on the West Florida shelf (WFS) in the eastern Gulf of Mexico (GOM),1 often causing fish and marine mammal mortality as well as other environmental and economic problems.2 Timely information of K. brevis blooms in terms of their spatial extent, intensity, transport, and dissipation provides guidance on field sampling and mitigation efforts, and retrospective information on such bloom characteristics helps understand bloom formation and their impact on the ocean’s biophysical and biogeochemical properties. Satellite remote sensing has proven to be an effective tool to provide such information because K. brevis blooms cause water discoloration, making bloom waters greenish, brownish, or reddish as compared with the nearby nonbloom waters. For the reason of discoloration, K. brevis blooms are often called “red tides.” The discoloration is caused primarily by the light absorption pigments in the dinoflagellate cells. Although the pigment concentration varies among cells, typically a concentration of is equivalent to about chlorophyll, enough to be differentiated from the typical background concentrations of 0.1 to in most of surface waters on the WFS. In some offshore waters during certain seasons, the background concentration may be or even lower, making it possible to detect K. brevis concentrations of (corresponding to about ) in such clear waters. In the GOM, background concentrations of K. brevis are below . Above , commercial shellfish areas are mandated to close for harvesting according to regulations of the U.S. Food and Drug Administration.3 At , fish kills are often reported and above reach water discoloration can typically be observed.4
Because of the chlorophyll content in the K. brevis cells, most remote sensing techniques have relied on the use of satellite ocean color sensors because these sensors were designed to estimate chlorophyll concentrations in surface waters. The most often used sensors for the GOM include the sea-viewing wide field-of-view sensor (SeaWiFS, 1997 to 2010), medium resolution imaging spectrometer (2002 to 2012), moderate resolution imaging spectroradiometer (MODIS, 2000 to present on Terra and 2002 to present on Aqua), and the most recent visible-infrared imager radiometer suite (VIIRS, 2011 to present). Although their sensor characteristics differ from each other (e.g., signal-to-noise ratio, number of spectral bands, band widths, band centers, spatial resolution, swath width, and revisit frequency), the principle is the same: to detect and quantify the color changes in certain spectral bands, which are further related to changes in Chl or K. brevis cell concentrations. Here, the term “color” refers to the spectral remote sensing reflectance (Rrs, ) or normalized water-leaving radiance (nLw, ) after atmospheric correction of the calibrated sensor signal.
Although the principle is the same, several different methods have been developed for bloom detection and tracking.22.214.171.124.–10 In these methods, a bloom is first detected and then determined whether it is mainly dominated by K. brevis. The former requires the use of algorithms with either blue/green bands9 or near-infrared/red bands,5,8 whereas the latter is done through inspection of the backscattering efficiency,6 spectral curvature,10 or nLw in the green.7 Recently, a thorough review has been conducted to evaluate all of these different methods11,12 and concluded that they all perform similarly with different strengths and weaknesses for different conditions.
Among these various methods, two have been used routinely by the U.S. federal and state agencies for bloom monitoring in the GOM. The first has been used by the U.S. National Oceanic and Atmospheric Administration (NOAA) through its HAB bulletin,13 which is based on the Chla-anomaly method9 to detect “new” bloom patches and on the spectral curvature method to discriminate K. brevis blooms.10 The second has been used by the Florida Fish and Wildlife Conservation Commission (FWC), the official agency of the state of Florida responsible for red tide monitoring and mitigation. It is based on the MODIS normalized fluorescence line height ( normalized to solar irradiance) imagery to detect bloom patches,8 and then on field measurements to discriminate K. brevis blooms.14 These MODIS and field-based detections are first interpreted by human analysts and summarized in HAB bulletins, and then distributed to various stakeholders through e-mail subscriptions after combining results from numerical models. The combination of these products has essentially formed an integrated red tide monitoring system to provide relevant information in near real-time through a web portal.15
However, one shortcoming in the use of MODIS nFLH to detect blooms is its sensitivity to inorganic particles (i.e., resuspended sediments). Through observations and model simulations, it is well known that nFLH is insensitive to perturbations by colored dissolved organic matter (CDOM, mostly terrestrial origin on the WFS).8,1617.–18 A 20-fold increase in CDOM will only decrease nFLH by half.18 The same observations and simulations also suggest strong sensitivity of nFLH to resuspended sediments, causing false-positive bloom detection. On the WFS, wind storms from hurricanes or cold fronts can cause significant sediment resuspension. In the past, this problem has been circumvented by examining another type of MODIS imagery, namely enhanced red-green-blue (ERGB) imagery.8,19 This is because sediment plumes in ERGB imagery appear bright while bloom waters appear dark, making it straightforward to differentiate the two. However, this involves inspection and presentation of two image types, often making it difficult for most users, especially when they are untrained for image interpretation. Although some alternative ways have been proposed to overcome this difficulty through band subtraction or band normalization,5,7 they have not been implemented for near real-time production due to extra steps required in satellite data processing and quality control. While in the long run they may eventually be implemented and tested for operational use, for continuity of the FWC bulletins the perturbation of suspended sediments to MODIS nFLH needs to be addressed.
It is thus desirable to develop a new product to take the full advantage of the MODIS nFLH (i.e., readily available from standard data processing, tolerant to CDOM perturbation, routine use in FWC HAB bulletins) while minimizing the impact of resuspended sediments. The objective of this paper is, therefore, not to compare the performance of different bloom detection methods as such as a comparison has already been performed elsewhere,9,10 but to develop and validate such a new product to serve as an algal bloom index (ABI), with the ultimate goal to replace the default MODIS nFLH to improve image interpretation and bloom detection for near real-time applications.
Data and Method
MODIS level-0 data were obtained from NASA Goddard Space Flight Center (GSFC).20 The purpose of starting from level-0 instead of level-2 was to generate several nonstandard data products used in the integrated red tide information system (IRIS),15,21 e.g., imagery generated from Rayleigh-corrected reflectance (Rrc, dimensionless). Level-0 data were processed using the NASA standard processing package (SeaDAS) to generate both standard and nonstandard level-2 products. The former include nFLH (i.e., FLH normalized to solar irradiance inputs), spectral Rrs, spectral nLw, and data quality control flags. The latter includes spectral Rrc and products (e.g., red-green-blue imagery to visualize and floating algae index22 to detect floating macroalgae and Trichodesmium) generated from Rrc. All data products were mapped to a cylindrical-equidistant projection at resolution through resampling.
The NASA standard product of nFLH is derived as5 5, a pixel meeting the following criteria was classified as a K. brevis bloom pixel: , and .
The last index, to be developed in this study [Eq. (4)], is an ABI. It is basically the same nFLH index but modulated by Rrs(547) to minimize the influence of suspended sediments. Similar empirical approaches have been developed by Wynne et al.23 to empirically adjust satellite-derived chlorophyll concentration (Chl, ) in sediment-rich waters and by Qi et al.24 to empirically adjust satellite-derived maximum chlorophyll index in sediment-rich waters. The idea is to add an extra term to adjust nFLH for sediment-rich waters, where the term has minimal influence on nFLH for sediment-poor waters. In this work, the following considerations were used to design the empirical fix.
While the relative abundance of sediment can be expressed through Rrs in the red band, e.g., Refs. 2526.27.–28, in practice Rrs in the red is noisy for clear waters. Therefore, to retain image quality for both sediment-rich and sediment-poor waters, the red band was not used. Instead, Rrs in the green (547 nm for MODIS) was used for the adjustment of nFLH. This is because Rrs(547) is relatively a constant for clear waters with Chl (Ref. 29) but it is also sensitive to changes in sediment concentrations in coastal waters. Actually, Carvalho et al.7 suggested the use of water-leaving radiance (Lw) in the green band to “normalize” Chl, yet Lw is a function of solar/viewing geometry and atmospheric transmittance, thus could change with time. The use of Rrs(547) would avoid this problem.
By convention, a normalization is usually through division against the reference, thus a normalized nFLH against Rrs(547) would have the form of nFLH/Rrs(547). In practice, however, this would lead to very high nFLH/Rrs(547) values for clear waters because Rrs(547) for clear water is very low and nearly a constant of .29 Therefore, to avoid this problem, the normalization was designed to take the following form:
Note that by taking this empirical adjustment, ABI is basically the same as nFLH for clear waters where Rrs(547) , and ABI also has the same units as nFLH (). For turbid waters where Rrs(547) is , ABI is , thus greatly reducing the false-positive signals caused by sediment resuspension. The validity of ABI and its improvement over the original nFLH are shown below through point validations and image inspections.
As the official state agency responsible for red tide monitoring and mitigation, the FWC has maintained a state-wide ret tide monitoring program, where periodic sampling of coastal waters from either dedicated research groups or volunteers has been conducted. In these sampling efforts, surface water samples were collected with a 2.2-L beta sampling bottle (Wildco, Yulee, Florida). From each bottle, 250 mL subsamples were preserved in Lugol’s iodine,30 and then sent to the FWC lab for phytoplankton enumeration to determine cell concentrations. During the enumeration, the subsamples were examined with microscopy within 24 h of sample collection, where identification and enumeration of HAB species were performed under 200× magnification using either a Olympus DP70 inverted microscope or a Zeiss Axiovert 100.31 For cell enumeration, 3 mL of each preserved sample was settled for in a Lab-Tek coverslip bottom chamber (Nalgene-Nunc #155379).32 HAB species in the entire chamber were identified to the lowest taxonomic level possible and enumerated. Figure 1 shows the locations of some of the water samples collected between 2002 and 2012, where same-day MODIS data were also collected over the same locations.
Two methods were used to evaluate the newly developed MODIS ABI: pixel-wise comparison with concurrent cell counts data and inspection of image pairs between nFLH and ABI from typical bloom and nonbloom cases on the WFS.
For the first method, matching pairs between MODIS satellite observations and field samples have been obtained using two criteria: (1) MODIS/Aqua data were acquired on the same day of the in situ measurements and (2) variance of MODIS pixels centered at the in situ station was to assure that water was relatively homogeneous. A total number of 557 matching pairs were found after applying the two criteria, with locations shown in Fig. 1. As the background Chl of the offshore GOM waters is , corresponding to (Ref. 8) (this is actually the threshold K. brevis concentration above which the class of “low” bloom condition is defined by the FWC) only the 145 matching pairs with K. brevis cell concentrations of were used for validation in this study. Note that the actual detection threshold may be much higher than unless the bloom is a mixture of K. brevis and other phytoplankton such as diatoms, but to follow the FWC convention to define “low concentration bloom” the threshold of was used here. For comparison, a threshold of was also used. In the comprehensive analysis of Soto et al.,12 the bloom threshold was based on the nFLH value of . Here for comparison, correlation analysis was used to examine the relationships between K. brevis cell concentrations of water samples and the corresponding MODIS-derived nFLH, ABI, RBD, and KBBI using these matching pairs, and regression was used to estimate cell concentrations from ABI.
For the second method, typical cases on the WFS that could potentially be falsely recognized as red tide blooms include hurricane- or other wind-induced sediment resuspension, and river plumes. Therefore, each of these cases was selected to examine the effectiveness of ABI in ruling out these false positives. For reference, a case of K. brevis bloom without the perturbations of sediment resuspension and river plumes was also selected. The cases were selected when concurrent field data were available to confirm the visual interpretations. For each case, the following images were selected for visual inspection: (1) MODIS nFLH; (2) MODIS ERGB (to differentiate sediment-rich from sediment-poor waters, and to differentiate optically shallow from optically deep waters); (3) MODIS RBD; and (4) MODIS ABI. The selection of visual inspection as the method for validation is because (1) MODIS imagery has been interpreted visually together with concurrent field data by the FWC to determine the spatial extend of red tide, and such information was summarized in HAB bulletins and distributed to various user groups through e-mail subscription.15 This is also how NOAA determined red tide spatial extent in the NOAA HAB bulletins; (2) red tide is very patchy,10 making a pixel-wise validation subject to large uncertainties. In practice, once one or more water samples from the satellite-identified bloom patch confirmed high concentration of K. brevis, the entire bloom patch was inferred to be K. brevis bloom. This type of visual validation has been a standard method used by many agencies to verify whether a patch of color anomaly in satellite imagery is K. brevis bloom. Note that because the FWC releases field data and HAB bulletins once a week, the time window to show “concurrent” field data and MODIS imagery was selected to be . Given the typical retention periods of K. brevis HABs of month (can reach 6 months), the 7-day time window is unlikely to cause major mismatches between field and MODIS observations.
Figure 1 shows where concurrent MODIS and field data were collected between 2002 and 2012 (red dots). Most of the field data were from shallow waters () on the WFS where most red tides have been reported, but some data were from the Florida Keys and the Florida Panhandle. The synoptic coverage of the field data suggests that the data used in this study can represent most, if not all, oceanographic conditions such as blooms, river plumes, sediment resuspension, and optically shallow waters.
Figure 2 shows the comparison between K. brevis cell concentrations and four MODIS indices (nFLH, ABI, RBD, and HBBI) over the same locations on the same day. Overall, despite the large data scattering due to K. brevis bloom patchiness and the difficulty in having an exact match between MODIS pixels (1 km) and field samples (a point),10 all four indices are significantly correlated with K. brevis cell concentrations. The correlation coefficient is the highest for ABI (0.57), followed by RBD (0.53), nFLH (0.52), and KBBI (0.49). In terms of bloom detection, they are about the same effective, with ABI being slightly better. What is more important is that some of the high-nFLH low-K. brevis points appear to be shifted to the left on the ABI-K. brevis plot, confirming that the design of Eq. (4) to avoid false positive in sediment-rich waters may be effective (i.e., high nFLH values are reduced in ABI). This observation is further verified in the case studies below.
1. Day 2003292: River Plume (see Fig. 3);
2. Day 2005300: Hurricane Wilma (see Fig. 4);
3. Day 2005361: Windstorm [maximum wind speed of during this day, according to data collected from a National Data Buoy Center (NDBC) station in Long Key of Florida Keys, 24.844°N, 80.864°W] (see Fig. 5);
4. Day 2003279: Mixed K. brevis bloom and diatom bloom (see Fig. 6);
5. Day 2006280: K. brevis bloom (see Fig. 7).
While the case-specific interpretations can be found in the figure captions, a common finding from these case studies is that the high nFLH values in sediment-rich waters have always been dampened in the RBD and ABI images, thus reducing false-positive detection. Although a combination of ERGB and nFLH can serve for the same purpose, the FWC only uses one type of imagery to combine with field measurements to have interpreted results in the HAB bulletins to distribute to registered users. Therefore, the use of ABI as a replacement of nFLH is an effective way to improve image quality and bloom detection accuracy. What is important is that while the false-positive detection in sediment-rich waters is reduced, the ABI image patterns are nearly the same as the nFLH image patterns in sediment-poor waters, maintaining the effectiveness of the original nFLH in bloom detection. This is exactly the purpose of the ABI design in Eq. (4).
The use of RBD appears to be also effective in reducing false-positive detection, yet the spatial patterns in RBD imagery are less coherent than in ABI imagery, as RBD values from offshore to nearshore waters are reversed. Although this reversal does not impact bloom detection, it does impact image appearance, especially to users without too much remote sensing experience. After all, the audience of the FWC bulletins includes users from all backgrounds.
The case studies shown here include all possible cases on the WFS that can cause sediment resuspension, therefore, proving unambiguously that ABI is a better way than nFLH in bloom detection and false-positive reduction. Indeed, inspection of other similar cases showed the same results. Therefore, in the IRIS15 and also in the FWC bulletins, ABI is used in the replacement of nFLH, although for the reason of continuity the name is still kept as nFLH. Likewise, the name of nFLH is still in the FWC red tide information bulletin distributed to registered users through e-mail subscription.
Through pixel-wise comparison and image inspection for case studies, the modulated MODIS nFLH (i.e., ABI) clearly showed its advantage over the original nFLH. While the purpose of this work was not to compare nFLH with other published algorithms as such as a comparison that has already shown similar statistical performance among those algorithms,9,10 the results here also showed slight improvement in ABI as compared with other indices that also use the same 667- and 678-nm bands for bloom detection. Overall, pixel-wise comparison showed its slightly improved correlation with K. brevis cell counts, and image comparison showed its ability to reduce false-positive detection in sediment-rich waters while maintaining the ability of nFLH for bloom detection in sediment-poor waters. We attribute these improvements to the design of Eq. (4) in further normalizing the nFLH data product against a sediment index, Rrs(547).
However, similar to nFLH, ABI is only an index to detect phytoplankton blooms but it does not differentiate bloom type between K. brevis blooms and non-K. brevis blooms (on the WFS, most of the latter are diatom blooms although occasionally there are cyanobacterial blooms). In this regard, ABI is not as effective as a combination of RBD and KBBI,5 or a combination of Chl anomaly and spectral curvature10 in separating K. brevis blooms from non-K. brevis blooms. However, as stated earlier, the purpose of using ABI is to provide a simple imagery type for pattern visualization, where integration of field-measured K. brevis cell concentrations can confirm whether the elevated ABI values are due to K. brevis. Such a purpose has been fulfilled through the IRIS11 since the implementation of ABI in 2014, which has been used by the FWC routinely for image interpretation and information distribution. Indeed, although the requirement of concurrent field sampling data may limit its use for many other areas due to lack of a routine sampling program for HABs monitoring, at least ABI can serve as an effective bloom index for both sediment-rich and sediment-poor waters. The empirical coefficient may need to be adjusted through local tuning to account for different sediment types. In case of lack of field data as used in Fig. 2, trial-and-error adjustment may be used until the final ABI image shows similar values in sediment-rich waters as compared with the same waters in adjacent days, assuming benthic algae is negligible. Note that because of the empirical nature, the final value of (80 in our case) is often a compromise between overcorrection and undercorrection. For example, in extremely turbid waters, ABI may not remove the false positives completely (e.g., circle 3 in Fig. 3), but further increases in would lead to overcorrection [e.g., the elongated blue band around Tampa Bay in Fig. 5(d)].
All analyses in this study were conducted using MODIS/Aqua data only as MODIS/Terra data were considered of having lower quality due to calibration and noise issues. However, an image analyst can usually tell noise from real features, so in routine operations MODIS/Terra images have also been used in order to have a better chance to observe cloud-free and glint-free ocean features. On the other hand, at the time of this writing, both MODIS sensors are aging, with MODIS/Terra being 16-years old and MODIS/Aqua 14-years old. The question is then what to use if they stop functioning. VIIRS (2012 to present) is supposed to continue the MODIS observations, yet VIIRS lacks a fluorescence band and thus a similar nFLH or ABI product. However, the VIIRS 672-nm band covers a bandpass of 662 to 682 nm, and therefore, captures a small portion of the fluorescence signal around 685 nm (25-nm full-width-half-maximum). Qi et al.36 showed that such a feature could be used to design a bloom index for dark waters through a 672/551 band ratio of VIIRS. Before the launch of the next-generation ocean color sensors with either hyperspectral capacity (e.g., PACE) or specific fluorescence bands (e.g., Sentinel-3), the use of such a red/green band ratio may be an alternative way to assure relative continuity from MODIS observations in case both MODIS sensors stop functioning.
In any case, neither nFLH nor ABI can provide a full solution to bloom detection in optically complex waters, as the ultimate way is to separate nonphytoplankton water constituents from phytoplankton through the use of radiative transfer16,18 or semianalytical inversion.37,38 However, due to a variety of reasons including large uncertainties in atmospheric correction over turbid coastal waters, these sophisticated methods often do not work well. Adding to this difficulty is the land-adjacent straylight problem in the satellite-retrieved Rrs; such a problem impacts not just the nFLH or ABI imagery but also all other imagery, regardless of the algorithm used. The consequence is that within 2-km of shoreline there is often no data even when the images have no clouds or sun glint. This is clearly shown in nearly all image examples in Figs. 3–7. Future efforts need to focus on minimizing the impact of land-adjacent straylight on data products to maximize the value of satellite data in bloom monitoring.
The use of ABI provides a simple but effective way to further improve nFLH imagery to make them less sensitive to perturbations by resuspended sediments. Although the improvement is not perfect (e.g., there may be still residual errors for extremely turbid waters such as those shown in Fig. 4), its impact on sediment-rich waters can be clearly visualized. Compared to nFLH, ABI is also less sensitive to perturbations by the very shallow bottom () in very clear waters such as those in the Florida Keys [e.g., Fig. 3(b) versus Fig. 3(d); Fig. 7(b) versus Fig. 7(d)]. In such cases of optically shallow waters, although nFLH does not suffer significantly from the bottom interference because of high water attenuation in all three nFLH bands (667, 678, and 754 nm) for water depths ,39 for water depths nFLH may still be “contaminated” by the shallow bottom when the water is clear. The effect is elevated nFLH values over shallow, clear waters of . Such an effect is compensated by basically “normalizing” the nFLH using Rrs(547) through Eq. (4) because Rrs(547) is significantly enhanced by the bottom reflection. Therefore, although Eq. (4) was designed to minimize the impact of sediment resuspension on nFLH, for the same reason, it also reduces the impact of shallow bottom in clear waters. Although not shown explicitly here, the Rrs spectra in the shallow waters () of the Florida Keys showed the bottom interference in nearly all bands, but its impact was reduced in ABI through normalization to Rrs(547). These effects are annotated in Figs. 3(b) and 3(d) and Figs. 7(b) and 7(d).
The MODIS nFLH data product has been shown effective in detecting blooms in CDOM-rich waters and therefore has been used by the FWC for routine assessment of K. brevis HABs in the eastern GOM. However, both radiative transfer and image inspection showed that it was sensitive to perturbations by resuspended sediments, causing false-positive detection. This short article demonstrates a simple but effective method to normalize nFLH data to Rrs(547), resulting in an ABI that is essentially the same as nFLH for sediment-poor waters but much less sensitive than nFLH to sediment perturbations. The ABI is also shown to be less sensitive than nFLH to perturbations by shallow bottom in very clear waters. ABI has been used by the FWC to replace nFLH in near real-time for routine red tide monitoring, although for continuity reason the name has not been changed. Because of its simple design and the availability of both nFLH and Rrs(547) as the NASA standard data products, the approach may be implemented for other regions for bloom monitoring after local tuning of the empirical correction where nFLH has been found to suffer from the same problems. However, this does not imply that ABI should be used globally over other suggested bloom detection methods (e.g., RBD, KBBI, Chl anomaly, and so on), especially when these methods may have already been used in local systems.
This work was supported by NASA’s Ocean Biology and Biogeochemistry Program and Gulf of Mexico Program. MODIS data were provided by the NASA Ocean Biology Processing Group (OBPG) through an online data portal ( http://oceancolor.gsfc.nasa.gov). Water samples have been collected by the Florida Fish and Wildlife Commission’s Law Enforcement Division and Fish and Wildlife Health Group, which were analyzed by Karen Henschen, Laura Markley, and Katherine Hubbard. We also thank and Karen Atwood of the FWC for preparing and distributing the HAB bulletins. Two anonymous reviewers provided extensive comments and suggestions to help improve the presentation of this work, whose effort is appreciated.
Chuanmin Hu received his PhD in physics from the University of Miami, Coral Gables, Florida, in 1997. He is currently a professor at the College of Marine Science, University of South Florida, St. Petersburg, Florida, USA. He has been a principal or a co-principal investigator of several projects funded by the U.S. federal and state agencies to study river plumes, harmful and nonharmful algal blooms, oil spills, coastal/inland water quality, and benthic habitat health.
Lian Feng received his PhD in cartography and geography information systems from Wuhan University, Wuhan, China, in 2013. He is currently a postdoctoral associate at the College of Marine Science, University of South Florida, St. Petersburg, Florida, USA. His research interests include remote sensing of inland and coastal water environments and how these environments are influenced by climate variability and human activities.