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26 May 2016 Stock Complexes for Fisheries Management in the Gulf of Mexico
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The Magnuson—Stevens Fishery Conservation and Management Act of 2006 required that regional fishery management councils implement annual catch limits and accountability measures for all federally managed stocks by 2011. Many managed species are data limited and no formal stock assessment has been done for them. One possible approach to managing unassessed species is to assign them to assemblages that are managed as units. The utility of this approach was evaluated using fishery-dependent and fishery-independent data from the Gulf of Mexico. Multivariate statistical analyses revealed several consistent assemblages among the 42 reef fish species managed by the Gulf of Mexico Fishery Management Council. Pearson correlation matrices, nodal analyses, and a weighted mean cluster association index integrated results across cluster analyses and provided additional guidance regarding the placement of rare species into groups. Productivity—susceptibility analysis and life history were also considered, as differences in productivity, vulnerability, life history, and other population-dynamic parameters for the species within complexes might imply different population responses to a similar change in fishing mortality. Identified linkages between species also provide guidance for the impacts of regulations on multispecies fisheries.

The Magnuson—Stevens Fishery Conservation and Management Act (Magnuson—Stevens Fishery Conservation and Management Reauthorization Act of 2006) required that regional fishery management councils implement annual catch limits (ACLs) and accountability measures (AMs) by 2011 to ensure that overfishing would not occur. These ACLs and AMs were required for nearly all stocks under federal management. Traditionally, management measures have been implemented based on the results of species-specific stock assessments. Unfortunately, due to limitations on funding, resources, and available data, many managed stocks have never been assessed. For example, in 2011 the Gulf of Mexico Fisheries Management Council (hereafter, Gulf Council) was managing 42 finfish stocks under its Reef Fish Fishery Management Plan (FMP; Table 1), yet the Gulf Council's Scientific and Statistical Committee had approved assessments for only 10 of those stocks.

Reference points for data-limited stocks can be set in a number of ways (Berkson et al. 2011; Carruthers et al. 2014). One possible approach for managing unassessed, data-limited species is to group them into stock complexes with a single ACL. A stock complex is defined as “a group of stocks that are sufficiently similar in geographic distribution, life history, and vulnerabilities to the fishery such that the impact of management actions on the stocks is similar” (USOFR 2009). Stocks may be grouped into complexes if (1) they cannot be targeted independently of one another in a multispecies fishery, (2) there are insufficient data to determine their status relative to established criteria, or (3) it is infeasible for fishermen to distinguish between individual stocks (USOFR 2009). The Gulf Council previously used stock complexes in the development of its commercial Grouper—Tilefish Individual Fishing Quota (IFQ) program.

The objectives of this study were (1) to determine whether stock complexes can be identified among the 42 managed Reef Fish FMP stocks in the Gulf of Mexico and, if so, (2) to determine whether the complexes are consistent between commercial and recreational fisheries. The results of these analyses were used to provide guidance to the Gulf Council in setting ACLs for stocks and stock complexes in their 2011 Generic Comprehensive ACL/AM Amendment (Gulf Council 2011).


Following Lee and Sampson (2000), multiple factors and statistical techniques were used to identify species assemblages: (1) species life history, depth of occurrence, and catch history; (2) dimension reduction and hierarchical cluster analyses based on life history, abundance, and presence/ absence; (3) correlation matrices, nodal analyses, and weighted mean cluster association indices; and (4) maps of species distributions. These analytical approaches are subject to different biases and limitations. Rather than focusing on a single approach, the results were synthesized across approaches to develop potential species complexes for ACL management. The analytical methods and data sources that provided the most information for each species were weighted so that they exerted more influence on the synthesized results.

Life history and catch data.—As species with similar life histories and body physiologies may respond to management measures in a similar fashion, life history and growth parameters were considered as one of the factors in species associations. Life history parameters were assembled from peer-reviewed literature, Southeast Data Assessment and Review (SEDAR) reports, unpublished data from the National Marine Fisheries Service (NMFS) Panama City Laboratory, Stock Assessment and Fishery Evaluation reports, and FishBase (Froese and Pauly 2009). Data from the Gulf of Mexico were used whenever possible. A categorical variable for taxonomic family captured aspects of body morphology and life history not described by the growth parameters in Table 1.

Commercial logbook, commercial observer, headboat logbook, recreational survey, and fishery-independent bottom longline data were used to evaluate similarities in the spatial and temporal patterns of fisheries exploitation in the Gulf of Mexico for species in the Gulf Reef Fish FMP. Commercial logbook records (Southeast Fisheries Science Center, Coastal Fisheries Logbook Program) summarize landings at the trip level, with information for each species encountered, including landings (to the nearest pound), the primary gear used, and the primary area and depth of capture (feet). Following recommendations from SEDAR-10 (2006), trip-level adjustments were made to Black Grouper Mycteroperca bonaci and Gag Mycteroperca microlepis landings to account for misidentification. Area fished was based on the 21 Gulf of Mexico commercial logbook statistical areas. A single depth of fishing is reported for each species per trip, although the species may be encountered at numerous depths during multiple sets and even within a single drifting longline set. Separate analyses were conducted for commercial longline (CLL) and commercial vertical line (CVL) gear types. Depth of capture was aggregated into atmospheric pressure bins (e.g., 33 ft = 2 atmospheres, 66 ft = 3 atmospheres, etc.). Records with no reported depth or area of capture were removed from consideration; these represented approximately 9% of the available records for both the longline and vertical line clusters. Overall, 27,566 longline and 121,767 vertical line commercial logbook records from 2005 to 2009 were evaluated.

In July 2006, the NMFS implemented a mandatory commercial reef fish observer program (RFOP) to characterize the reef fish fishery operating in the U.S. Gulf of Mexico. The RFOP provides set-level information on species encountered on trips using bottom longlines, electric (bandit) reels, and handlines. Overall, 125,368 records representing encounters (landings plus discards) by species for 7,105 observed sets in the Gulf of Mexico from 2006 to 2009 were evaluated.

The recreational headboat sector of the reef fish fishery was evaluated using Southeast Region Headboat Survey (HBS) logbook data reported by headboat operators. Headboats are large, for-hire vessels that typically accommodate 20 or more anglers on half- or full-day trips. Headboat records contain trip-level information on the number of anglers, trip duration, date, and area fished for encounters (landings and releases) of each species. Trip duration was the best available proxy for depth fished, as trips of longer duration are more likely to go farther offshore and fish deeper waters. Headboat captains fishing in multiple areas during a trip are constrained by the present data form to identify one “area fished” for the trip, which limits the spatial precision of the analysis. Area fished was aggregated at the most common reporting level (1° latitude × 1° longitude) to reduce the undesirable influence of empty bins. Records with no reported area fished (°3%) were removed from consideration. Overall, 121,334 headboat records from 2004 to 2009 were evaluated.


Life history parameters for species covered by the Gulf of Mexico Reef Fish FMP, by family (see Table A.1 in the appendix for citations). Abbreviations are as follows: aλ = the maximum age in years, K = the Brody growth coefficient, L= the asymptotic length from the von Bertalanffy growth equation, a0 = the scaling parameter for the theoretical age at length zero from the von Bertlanffy growth equation, W = the theoretical maximum weight (kg), Lm = length at maturity (mm), and am = age at maturity (months).




The private, rental, and for-hire charter sectors were evaluated using data from Marine Recreational Fisheries Statistics Survey (MRFSS) dockside intercept records. The MRFSS intercepts collect data on port agent—observed landings and angler—reported landings and discards by species, 2-month wave (wave 1 = January–February, wave 2 = March–April, etc.), state ([western] Florida, Alabama, Mississippi, or Louisiana), mode of fishing (charter, private/rental, or shore), and area fished (inland, state, or federal waters). Overall, 64,782 dockside intercept records from 2000 to 2009 were evaluated.

Since 1995, the NMFS began conducting fishery-independent bottom-longline (BLL) surveys throughout the Gulf of Mexico at depths ranging from 9 to 55 m (Grace and Henwood 1997). In 1999, the BLL survey was expanded out to depths of 366 m (Henwood et al. 2004). Study sites are randomly selected. Longline sets are made parallel to depth contours. Gangion test and length have varied between years. J-hooks were used prior to 1999, while circle hooks have been used since 1999. Soak times are always 1 h and use 100 #15/0 hooks baited with Atlantic Mackerel Scomber scombrus. Methods were standardized in 2001. Effort is proportionally allocated based on shelf width within 60—nautical mile statistical zones (81–82°W, 82–83°W, etc.) and stratified by depth (50%: 9–73 m, 40%: 73–183 m, 10%: 183–366 m). Overall, 851 BLL records of managed reef fish landings from 1995 to 2009 were evaluated.

Data sets were formatted as matrices, with columns representing species (i) and rows representing aggregation bins (j). Aggregation levels were chosen to minimize the number of empty bins while maximizing the spatial and temporal precision of the bin based on the available data. For commercial fisheries, species-specific landings in weight were aggregated into 3,257 CLL and 7,243 CVL year—month—area—depth bins. For the RFOP, species-specific encounters were aggregated into 7,105 set—level bins. For the HBS, species-specific encounters were aggregated into 2,615 year—month—area—trip duration bins. For the MRFSS, species-specific encounters by intercepted anglers were aggregated into 430 year—wave— mode—area bins. For the BLL, species-specific encounters were aggregated into 684 set—level bins. Each element of the matrix (cij) quantified the number of individuals of a species landed in a specific bin. No data matrix had more than one empty bin at these levels of aggregation.

Because rare species may distort inferred patterns (Koch 1987; Mueter and Norcross 2000), species were initially excluded from analyses if they appeared in less than 1% of the bins (Shertzer and Williams 2008). However, because preliminary examination suggested that the inclusion of rare species did not affect the inferred patterns in any of the cluster analyses and because one of our primary goals was to assign less abundant species to species complexes, all 42 managed species were included in the final analyses.

Prior to clustering, data were transformed using a root-root transformation, namely,


This transformation moderates the influence of abundant species on the resultant clusters and is recommended for density and biomass data (Field et al. 1982; Shertzer and Williams 2008).

Because the fishing effort that generated the landings data was inconsistent through time, the data may not be quantitatively comparable between collections. Additionally, while many species are heavily targeted, the catch of others is incidental. To address this concern, additional clustering was performed on binary transformations of the landings data matrices. Boesch (1977) suggests that a binary index (e.g., presence/absence) is a more appropriate measure of similarity with fisheries-dependent data. A binary index also reduces distortions caused by superabundant (headboat and commercial) and heavier (commercial) species.

Hierarchical cluster analyses and dimension reduction.— Cluster analysis and dimension reduction provide both quantitative and visual measures of association. Overall, 2 life history and 24 fishery-data clusters were generated for the stocks in the Gulf Council's Reef Fish FMP. For the life history data set (described above) and each of the six fishery catch input data sets (CLL, CVL, RFOP, HBS, MRFSS, and BLL), hierarchical cluster analysis (HCA) and dimension reduction analysis (DRA) were conducted on root-root- and presence/absence—transformed data.

The HCAs were conducted with PASW version 17.0.3 (SPSS, Chicago). Such analyses identify relatively homogeneous groups of cases (or variables) based on selected characteristics. They employ an agglomerative method that optimizes a route between individual entities to the entire set of entities through progressive fusion (Boesch 1977).

The life history parameters (Table 1) plus a categorical variable denoting taxonomic family were clustered using HCA with Ward's minimum-variance linkage method (Sneath and Sokal 1973), a Euclidean distance measure, and a Z-score transformation by variable. The Z-score transformation normalized the data by parameter, facilitating comparisons between species.

For the HCAs of the fisheries data sets (CLL, CVL, RFOP, HBS, MRFSS, and BLL), we used a chi-square measure of distance with Ward’s minimum-variance linkage method. For the HCA of the binary-transformed fisheries data sets, we used the average linkage between groups with a Sørenson measure of dissimilarity. These methods introduce little distortion into the relationships expressed in the similarity matrix and are widely used in ecology (Beals 1973; Boesch 1977; Field et al. 1982; Faith et al. 1987; McGarigal et al. 2000; Mueter and Norcross 2000; Gomes et al. 2001; Williams and Ralston 2002; Shertzer and Williams 2008; Shertzer et al. 2009).

A DRA was conducted using PROC VARCLUS in SAS version 9.2 (SAS Institute, Cary, North Carolina). This algorithm is binary and divisive: all variables start in one cluster; cluster is chosen for splitting and is split into two clusters by performing an orthoblique rotation on the first two principal components; each variable is then assigned to the rotated component with which it has the higher squared correlation. Dimension reduction analysis is nonhierarchical; variables are iteratively reassigned to clusters to maximize the variance accounted for by the cluster components. Clusters are split until 95% of the variance has been explained. Our DRA was applied identically to all input data.

Nodal analysis, correlation, and weighted mean cluster association.—As the CVL data set represented a large proportion of Gulf reef fish landings, had relatively high data resolution, and featured records for a variety of species, it was selected for nodal analysis (Sedberry and Van Dolah 1984). Percent landings by species and CVL area were tabulated and sorted by the CVL presence/absence HCA dendrogram. This nodal analysis provided a visual representation of how the spatial distribution of stocks impacted cluster output.

Pearson correlation matrices were also generated for the six catch-based input data sets. The table resulting from the co-occurrence analysis was subsequently sorted by columns according to the dendrogram from the CVL binary cluster output and by rows according to the dendrogram from the MRFSS binary cluster output. The CVL data set was selected due to its high species richness, and the MRFSS data set was selected because it represented the most contrasting sector. The cells were conditionally formatted to facilitate visual identification of the dense cells, or nodes, within the data matrix in which groups of species and groups of collections coincide between the two fisheries clusters and co-occur with high frequency between species (Williams and Lambert 1961; Lambert and Williams 1962). This nodal analysis was used to identify clusters of species that were often caught together across different sectors and to suggest cluster assignment for rare species by providing a visual reference for co-occurrence with more ubiquitous or heavily exploited species.

A weighted mean cluster association index was developed to synthesize results across the 2 life history and 24 fishery-data clusters. The cluster association matrix for each dendrogram was completed by species. For a given species in row r, the association level (α) with species in column c was computed as


where η is the number of species lower than the species in row r on the branches of the dendrogram. For example, species D and E are both below species F on the branch; thus σF→D = 0.5 and αF→E = 0.5 in the association matrix (see Figure 1).

Unique cluster association matrices were assembled for each of the 26 dendrograms, and a weighted mean cluster association index matrix was computed. For a given species in row r, the weighted mean association level (fi01_177.gif) with species in column c was computed as


where D is the data set under examination, m is the clustering method, and ωD is the weighting term for the data set. The weighting terms were computed by data set, were based on the proportional representation of the species within bins, and were scaled to 1 as a proportion of the maximum representation of that species across the seven data sets, with life history given the maximal default value of 1 (Table 3). For example, if a species appeared in 80% of the bins in the CLL and 40% of the bins in the other data sets, its weighting term would be 1.0 for CLL (ωCLL = 1.0) and 0.5 for the other data sets. This weighted mean approach was employed for two reasons: (1) clusters are generally considered more reliable for species that appear frequently in the bins (Koch 1987; Mueter and Norcross 2000) and (2) management measures targeting a species complex would typically be expected to have a higher proportional impact on the sector that encounters the species most frequently. Sensitivity runs were performed with life history downweighted or removed from consideration.


Example dendrogram and cluster association matrix. See the text for a more detailed explanation.


Maps of stock distributions.—The RFOP and BLL surveys provide spatially explicit information regarding encounters with managed species in the Gulf of Mexico. These data sets were imported into ArcGIS (ESRI, Redlands, California) and displayed with respect to presence/absence on bathymetric maps of the Gulf. Trends in species distributions were used to explain inconsistencies between cluster analyses and to evaluate the “[similar] geographic distribution” requirement for stock complexes under the Magnuson—Stevens Fishery Conservation and Management Reauthorization Act of 2006. Some points were removed to protect the confidentiality of contributors to the RFOP data set.


Life History and Catch Data

Table 1 provides life history parameters for managed Gulf reef fish species. Because life history may be influenced by time (Shertzer et al. 2009), geography, habitat (Hoss and Engel 1996), exploitation (Hughes 1994), and climate (Holbrook et al. 1997), these point estimates may not accurately express the life history dynamics of the unexploited population or of all subpopulations. Additionally, life history data may be less reliable for data-poor species, lending uncertainty to the resultant clusters. Not surprisingly, HCA of the life history and depth of occurrence parameters in Table 1 showed clustering by family, depth of occurrence, and maximum size (Figure 2). All of these variables are highly intercorrelated (P < 0.05). Additionally, the von Bertalanffy growth parameters (L∞, W∞, αλ, and am; Table 1) were significantly correlated (P < 0.05). A cursory examination of Table 1 and Figure 2 reveals some trends: species of the same genus often exhibit similar growth patterns, and larger and deepwater fish tend to live longer and grow more slowly.

Dimension Reduction and Hierarchical Cluster Analyses

The CVL and RFOP were the most representative data sets in terms of species encountered (Table 2), which is probably attributable to the broad depth ranges covered and the high levels of effort. In general, HCA and DRA outputs should be considered more reliable for species that are more prevalent in the input data matrices (Table 3). The CLL heavily weighted Red Grouper, Scamp, Gag, Yellowedge Grouper, and Snowy Grouper. The CVL heavily weighted Red Snapper, Vermilion Snapper, Scamp, Gray Triggerfish, Red Grouper, and Gag. The RFOP heavily weighted Red Grouper, Red Snapper, Vermilion Snapper, and Gag. The HBS heavily weighted Gray Triggerfish, Gag, Red Snapper, and Vermilion Snapper. The MRFSS heavily weighted Gray Snapper, Gag, Red Snapper, and Lane Snapper. The BLL survey was the only fishery-independent data set examined. Unfortunately, the selectivity characteristic of longline gear led to low encounter rates with most reef fish species (Table 3). Only Red Snapper, Red Grouper, Yellowedge Grouper, and Tilefish were encountered in more than 5% of sets. Blueline Tilefish were landed on both sets that also landed Queen Snapper. Similarly, Tilefish was the only species landed on the only set that also landed a Goldface Tilefish. Red Snapper, Yellowedge Grouper, Warsaw Grouper, and Tilefish were all landed on sets that also landed Wenchman. The landings of Goldface Tilefish, Yellowmouth Grouper, Hogfish, Cubera Snapper, Dog Snapper, Anchor Tilefish, Schoolmaster, Nassau Grouper, Blackline Tilefish, and Mahogany Snapper were extremely low for all data sources. Other rare species were found predominantly in only one data set; for example, the Speckled Hind group assignment was heavily influenced by its CLL clustering and the Rock Hind group assignment was heavily influenced by its MRFSS clustering.

Commercial longline.—For the HCA and DRA of the CLL data, major clusters were formed by shallow-water, moderate-depth, and deepwater complexes (Figure 3). The most apparent cluster was formed by the major shallow-water grouper species (i.e., Red and Black Grouper, Gag, and Scamp). The relative lack of separation between Black Grouper and Gag in this cluster originated from the adjustment of the landings data for misidentification, which inflated the co-occurrence of these species. Within the deepwater group, Tilefish was somewhat distinct, and the deeper-water Snowy Grouper and Yellowedge Grouper were separated from the shallower-water Blueline Tilefish and Speckled Hind (Figure 3). Within the moderate-depth group, Gray Triggerfish and Vermilion Snapper were often caught together in large numbers. Queen Snapper and Wenchman both clustered with deepwater grouper and tilefish species (Figure 3). The clustering of shallow-water species was confounded because bottom longline fishing for reef fish is prohibited in waters of less than 20 fathoms (36 m; Figure 3; Table 3).

Commercial vertical line.—Cluster analyses of the CVL data provided results similar to those of the CLL data (Figure 4). Both HCA and DRA produced clusters of shallow-water grouper (Red and Black Grouper and Gag). Also apparent were moderate-depth complexes containing Silk and Blackfin Snapper and Gray Triggerfish with Vermilion, Red, and Lane Snapper. Clusters for deepwater (Yellowedge, Snowy, and Warsaw Grouper) and moderate-depth species were less clearly separated for the CVL fishery than for the CLL fishery, perhaps due to shallower average operating depths (mean = 88 in for the CLL, 50 m for the CVL) and less selective types of gear. The jacks (Greater Amberjack, Almaco Jack, Banded Rudderfish, and Lesser Amberjack) clustered relatively tightly (Figure 4). Gray Snapper clustered with the shallow-water grouper species (Figure 4). Dog Snapper and Schoolmaster clustered together, as did Mutton Snapper, Yellowtail Snapper, and Hogfish (Figure 4).


Hierarchical cluster analysis of life history parameters for managed Gulf of Mexico reef fish species with dummy code for genus (linkage: Ward's; measure: Euclidean distance; transformation: Z-score by variable). The letter “F” denotes female.


Reef fish observer program.—The RFOP represents an aggregated, high-resolution subsample of the CLL and CVL data sets. Thus, it is not surprising that many of the trends observed in those clusters are repeated in the RFOP cluster (Figure 5). For example, deepwater groupers, snappers, and tilefish clustered together (i.e., Yellowedge Grouper, Blueline Tilefish, Snowy Grouper, Speckled Hind, Anchor Tilefish, Queen Snapper, and Goldface Tilefish). Red Snapper and Lane Snapper clustered together, as did Scamp and Gag, Almaco Jack, and Greater Ambeijack (Figure 5). Additional clusters were formed by the hinds (i.e., Red Hind and Rock Hind), as well as by Mutton and Cubera Snapper. A cluster was formed between Red Grouper and Vermilion Snapper, and Sand Perch clustered with Scamp and Gag.


Species diversity metrics for the presence of managed species in the Gulf in binned commercial longline (CLL), vertical line (CVL), reef fish observer (RFOP), headboat (HBS), Marine Recreational Fisheries Statistics Survey (MRFSS), and NMFS bottom-longline (BLL) data sets.


Headboat survey.—The HBS clusters provided results similar to those for the CLL and CVL data (Figure 6). Clusters of Red Grouper, Gag, Scamp, and Gray Snapper were observed. Moderate-depth species (Gray Triggerfish with Vermilion, Red, and Lane Snapper), and deepwater species (Yellowedge and Snowy Grouper) tended to cluster together. Greater Amberjack and Almaco Jack clustered with each other. Tropical species such as Black Grouper, Mutton Snapper, and Yellowtail Snapper clustered together. Misidentification issues may have led to the observed clustering of Yellowedge, Yellowfin, and Yellowmouth Grouper (see SEDAR-22-DW-13 2010).

Marine Recreational Fisheries Statistics Survey.—The MRFSS clusters formed few distinct groups (Figure 7). Of the deepwater species, Warsaw Grouper and Snowy Grouper clustered, as did Yellowedge Grouper and Tilefish. A moderate-depth group containing Gray Triggerfish, Red Snapper, Lane Snapper, Vermilion Snapper, Scamp, Banded Rudderfish, Greater Amberjack, Misty Grouper, and Speckled Hind was also identified. Gag and Red Grouper clustered strongly. Yellowtail Snapper and Mutton Snapper also clustered together.

Bottom longline.—The BLL survey clusters formed a few apparent groups (Figure 8). Mutton Snapper grouped strongly with Gray Snapper. Red Grouper and Gag again clustered tightly. Two deepwater complexes were identified, one containing Blueline Tilefish, Speckled Hind, Snowy Grouper, and Queen Snapper, the other containing Yellowedge Grouper, Tilefish, Warsaw Grouper, and Wenchman. Red Snapper was also loosely associated with this second deepwater complex.


Weighting terms for the mean cluster strength matrix. Note that the life history weight = 1 for all species.



Dimension reduction cluster analysis of presence—absence for Gulf of Mexico reef fish commercial longline landings (2005–2009) aggregated by year, month, area, and depth (linkage: VARCLUS; measure: proportion variance explained; transformation: binary).


Nodal Analysis and Correlation

Geographic differences in the distribution of landings by the CVL sector explain many of the patterns observed in Figure 4. For example, Mutton Snapper, Yellowtail Snapper, and Hogfish were most frequently landed in the Florida Keys. A nodal analysis of median Pearson correlation values aggregated across the six fishery data sets provides additional validation of the observed clusters as well as guidance in the placement of rare species into complexes (Figure 9). Apparent nodes were formed by moderate-depth snapper species and jacks, deepwater snapper species and tilefish, deepwater grouper, shallow-water snapper, and grouper. Median correlation values were high between “jacks” (i.e., Almaco Jack and Banded Rudderfish), “deepwater” stocks (i.e., Queen Snapper with Blueline Tilefish and Snowy Grouper, Blackfin Snapper with Silk Snapper, Anchor Tilefish with Blueline Tilefish and Snowy Grouper, Blackline Tilefish with Yellowedge Grouper, and Wenchman with Warsaw and Yellowedge Grouper), and “shallow-water” snapper (i.e., Cubera Snapper with Mutton Snapper and Dog Snapper with Schoolmaster)

The weighted mean cluster association index provided a quantitative approach to synthesizing the information contained in the 26 unique cluster analyses performed. Stocks were arranged by association and vulnerability to provide guidance on management complexes. Vulnerability was defined using productivity–susceptibility analysis (PSA) scores of overall risk from a MRAG Americas Gulf of Mexico Final Report (MRAG Americas 2009a). Among the 42 species analyzed, eight major complexes were identified, with some potential subgroups due to differences in life history (Table 4). The results presented in Table 4 are explored further in the Discussion.

Maps of Stock Distributions

Maps of the distribution of the observed BLL and RFOP interactions with managed Gulf species provide insight into the outcomes of the cluster analyses described above (Figure 10). Gray Snapper were most commonly encountered in shallow to middepth waters from central Florida to the Big Bend, with some landings off Louisiana and Texas (Figure 10A). Cubera, Dog, Mutton, and Yellowtail Snapper were most commonly encountered off southwest Florida (Figure 10A). Red and Vermilion Snapper were ubiquitous in the Gulf at a broad range of depths (Figure 10B). Red Snapper co-occurred with Vermilion Snapper but also appeared inshore (Figure 10B). Silk Snapper were rarely encountered but occurred in the deeper portion of the Red and Vermilion Snapper distributions (Figure 10B). Gray Triggerfish and Lane Snapper co-occurred with Red and Vermilion Snapper; Gray Triggerfish were most common off West Florida and the Panhandle and Lane Snapper off West Florida and Louisiana (Figure 10B).


Hierarchical cluster analysis of species presence—absence in Gulf of Mexico reef fish commercial vertical line landings aggregated by year, month, area, and depth (linkage: between [average]; measure: Sørenson [binary]).



Dimension reduction cluster analysis of species presence—absence in Gulf of Mexico reef fish observer program landings aggregated at the individual set level (linkage: VARCLUS; measure: proportion variance explained).


Jack stocks were encountered throughout the Gulf but less frequently off Texas (Figure 10C). Greater Amberjack encounters were broadly distributed, overlapping all other species and extending into much deeper waters off West Florida. The Lesser Amberjack and Almaco Jack distributions overlapped. Banded Rudderfish were less commonly encountered outside of Florida.

The bulk of shallow-water grouper encounters were between Red Grouper and Gag, which were heavily concentrated off West Florida at a broad range of depths (Figure 10D). Black Grouper were most commonly encountered off southwest Florida. Red and Rock Hind occurred on the inshore portion of the Red Grouper and Gag distribution. Yellowmouth Grouper co-occurred with Red Grouper and Scamp. Scamp were observed predominantly along the deeper portion of the Gag and Red Grouper distribution off West Florida but were broadly distributed throughout the Gulf, typically at depths between 91 and 327 m. The tendency of Scamp to occasionally cluster with moderate-depth species was probably due to their high concentration off the coast of Louisiana, where there are large fisheries for Almaco Jack, Red Snapper, and Vermilion Snapper; other shallow-water grouper species are less common and longline fishing is prohibited in waters 91 m or less in depth.

The broad, overlapping distributions of Snowy and Yellowedge Grouper help explain the consistency observed in the clustering of these stocks across analyses (Figure 10E). Speckled Hind, Warsaw Grouper, and Wenchman were more broadly distributed across depths. Speckled Hind were most commonly encountered off West Florida. Queen Snapper were rarely encountered but co-occurred with Snowy Grouper when observed.


Hierarchical cluster analysis of species presence-absence in Gulf of Mexico reef fish headboat landings aggregated by year, month, trip duration, and area fished (linkage: average [between]; measure: Sørenson [binary]).


Tilefish were encountered in the deepest waters and were broadly distributed across the Gulf (Figure 10F). In contrast, Blueline Tilefish co-occurred with Tilefish off Florida but were also encountered in shallower waters. Anchor, Blackline, and Goldface Tilefish were all very rare but were observed co-occurring with both Blueline Tilefish and Tilefish.


Dimension reduction cluster analysis of species presence—absence in Gulf of Mexico reef fish recreational MRFSS-reported landings aggregated by year, wave, mode of fishing, and area fished (linkage: VARCLUS; measure: proportion variance explained; transformation: binary).



A comprehensive understanding of concurrent stock vulnerabilities to various fisheries is critical to achieving the goals of ACL/AM management. The myriad of statistical approaches explored in this study tell a relatively consistent story regarding what stocks might be impacted by similar management measures. By considering fishery and ecosystem variables such as life history, vulnerability, sector, gear, area, and depth fished, these analyses provide insights that may facilitate multispecies or place-based management. The impacts of regulatory measures for one species on associated species are more easily understood when the associations between the species have been quantified by gear and the spatial distributions of these species are better understood. For this reason, the establishment of complexes of associated species may help reduce bycatch by linking regulations to species that are frequently caught together.

Of the cluster analysis input variables, depth appeared to be the most important, and apparent shallow-water, moderate depth, and deepwater assemblages appeared in most analyses. A similar approach by Bortone et al. (1979) also found that community association was predominantly influenced by depth, with substrate, latitude, and season also playing significant roles. Identified assemblages varied slightly by data set. The HBS data set contained less information for deepwater stocks because they are farther offshore and not often targeted by limited-duration headboat trips. The CLL data set contained less information for shallow-water stocks because commercial bottom longlining is prohibited inshore of 36-m depth in the eastern Gulf of Mexico and 91-m depth in the western Gulf (e.g., west of Cape San Blas, Florida). Subtle spatial trends were also observed in assemblages. For example, in many data sets, Mutton Snapper, Red Hind, Yellowtail Snapper, and Hogfish formed a tropical assemblage due to their high landings in the Florida Keys. Genus was also important; for example, snappers and groupers were often separated. This may be due to differences in vulnerability to different gear types and fishing methods as well as to differences in geographic and depth distributions. In addition, years of overexploitation may have altered community structure (Hughes 1994).


Hierarchical cluster analysis of species presence—absence in Gulf of Mexico NMFS bottom-longline survey landings aggregated by set (linkage: average [between], measure: Sørenson [binary]).


Although the cluster analyses were based on vulnerabilities to selective types of fishing gear, the major controlling factors included season, area, and depth; thus, some aspects of life history were included de facto in the analyses. These analyses mostly supported the Gulf Council's deepwater grouper IFQ assemblage of Yellowedge Grouper, Snowy Grouper, Warsaw Grouper, Speckled Hind, and Misty Grouper (Table 4). Due to their distance from shore and the specialized types of gear required to capture the deepwater component of these stocks, there was a low relative percentage of encounters of these species in all but the CLL and BLL data sets (Table 3). Yellowedge and Snowy Grouper stocks had extremely high weighted mean cluster association index values and have overlapping geographic distributions (Figure 10E). The Yellowedge Grouper is extremely long-lived and highly productive compared with other members of this complex (Table 1). Warsaw Grouper is the most vulnerable member of this complex and was most highly associated with Misty and Snowy Grouper (Table 4). As with Speckled Hind, there is a substantial inshore fishery for Warsaw Grouper in addition to the core deepwater component of the stock (Figure 10E). Fishing gear rarely interacted with Misty Grouper and Speckled Hind; however, reported encounters were most often associated with other deepwater stocks such as Warsaw Grouper and various tilefish species (Table 4).

A snapper assemblage was identified for middepth to deep water that comprised Blackfin Snapper, Silk Snapper, Wenchman, and Queen Snapper. Blackfin and Silk Snapper often strongly clustered together. Queen Snapper and Wenchman landings were relatively rare but the two species appeared to be loosely associated with each other and other deepwater species (Table 4).


Plot of species presence—absence for Gulf of Mexico reef fish commercial vertical line landings aggregated by year, month, area, and depth (linkage: VARCLUS; measure: proportion variance explained; transformation: binary) relative to the percent of landings (2005–2009) originating from commercial logbook statistical areas 1–21. Similar color patterns in adjacent rows illustrate the importance of stock spatial distributions for the resultant clusters. Abbreviations are as follows: SW FL = southwest Florida, NWFL = northwest Florida, AL = Alabama, MS = Mississippi, LA = Louisiana, and TX = Texas.


Our analyses support the current tilefish assemblage, although there were moderately high levels of association with several deepwater groupers, which suggest that management regulations applied to stocks in either assemblage might affect stocks in the other (Table 4). Tilefish occur at depths similar to those of Yellowedge Grouper and are occasionally caught on the same set, but they are less structure affiliated, preferring soft-bottom habitats on the upper continental slope (Palmer et al. 2004; Sedberry et al. 2006). Tilefish clustered with other deepwater species but was often separated from the other members of the complex (see Figure 4). Blueline Tilefish frequently clustered with Speckled Hind, along with other deepwater stocks (Table 4). The distributions of both Blueline Tilefish and Speckled Hind extend farther inshore along the West Florida shelf than do those of the other deepwater stocks (Figure 10D–F). Blueline Tilefish prefer irregular, rocky bottom from the outer shelf edge to the upper slope (Struhsaker 1969; Ross 1978; Ross and Huntsman 1982; Parker and Ross 1986; Harris et al. 2004). Blueline Tilefish, Snowy Grouper, Warsaw Grouper, Speckled Hind, Yellowedge Grouper, and Greater Amberjack have all been documented to co-occur on the top edge of sinkholes (Reed et al. 2005). Little is known about Anchor, Blackline, and Goldface Tilefish, but they may co-occur and even share burrows with Blueline Tilefish and Tilefish (Able et al. 1987).


Potential stock complexes derived from weighted mean cluster association indexes (in parentheses) indicating the top five associated species for each species. Productivity—susceptibility analysis (PSA) scores of overall risk from 15 MRAG Americas Gulf of Mexico final reports are provided when available (MRAG Americas 2009a). Solid lines separate major groups, while dashed lines show potential life history-based subgroups. Bold type indicates species for which the stock assessment includes a recommendation as to the allowable biological catch; italics indicate assessed species for which there is no recommendation. Abbreviations are as follows: GR = Grouper, Snap = Snapper, Amber = Amberjack, Rudder = Rudderfish, Tile = Tilefish, and Trigger = Triggerfish.





Maps of aggregated NMFS bottom-longline survey and Reef Fish Observer Program observations of (A) shallow-water snapper, (B) midwater stocks, (C) jacks, (D) shallow-water grouper, (E) deepwater grouper, and (F) tilefish groupings relative to bathymetry and commercial fishery statistical reporting areas in the Gulf of Mexico. Some observations were removed to maintain confidentiality.


FIG 10. (Cont.)

Maps of aggregated NMFS bottom-longline survey and Reef Fish Observer Program observations of (A) shallow-water snapper, (B) midwater stocks, (C) jacks, (D) shallow-water grouper, (E) deepwater grouper, and (F) tilefish groupings relative to bathymetry and commercial fishery statistical reporting areas in the Gulf of Mexico. Some observations were removed to maintain confidentiality.


The four managed jack species (Greater Amberjack, Lesser Amberjack, Banded Rudderfish, and Almaco Jack) were highly associated (Table 4) and were most frequently encountered by the HBS and CLL sectors (Table 3). SEDAR-15 (2008) concluded that Lesser Amberjack and Almaco Jack were correctly identified in most instances, but smaller Greater Amberjack and Banded Rudderfish were often misidentified. Misidentifications might lead to problems computing single-species ACLs for these species unless the rate of misidentification is quantifiable or has been constant through time. Encounters off the West Florida Shelf beyond 236 m were almost exclusively with Greater Amberjack; thus, regulatory changes on the deepwater component of any jacks complex might impact only Greater Amberjack (Figure 10C). Managing these jacks as a complex would mitigate issues with species identification.

Several species occurring at moderate depths consistently clustered together: Gray Triggerfish and Vermilion, Red, and Lane Snapper (Table 4). Their clusters often overlapped with some of the more broadly distributed shallow-water species, such as Gray Snapper, Scamp, Red Grouper, and Mutton Snapper. Gray Triggerfish and Vermilion, Red, and Lane Snapper were most consistently encountered in the HBS data (Table 3) and were strongly associated in this data set (Figure 6). Among the snappers, the strongest association was between Red and Vermilion Snapper (Table 4). Although Gray Triggerfish clustered with these snapper species, it may be desirable to manage it separately due to differences in its life history (Table 1). Red and Vermilion Snapper are both highly productive stocks and are ubiquitously distributed throughout the Gulf (Figure 10B).

Our analyses partly support the Gulf IFQ program's shallow-water grouper complex of Red, Black, Yellowmouth, and Yellowfin Grouper, Red and Rock Hind, Scamp, and Gag (Table 4). Red Grouper and Gag consistently clustered together and were often clustered with Scamp and Black Grouper (Table 4). Black Grouper and Gag were highly associated in the CLL and CVL clusters, but this is likely an artifact of the misidentification adjustment that was applied. These species were separated in the HBS clusters (Figure 6). Although these species overlap in their distributions and are vulnerable to the same gear types and fishing techniques, the core of the Black Grouper distribution is in the Florida Keys, whereas the Gag is nearly ubiquitous across the eastern Gulf (Figure 10D). Red Hind, Rock Hind, Yellowfin Grouper, and Yellowmouth Grouper were rarely encountered but were associated with each other when they were (Table 4). An assessed species (Gag) is the most vulnerable species in the complex (Table 4).

The clustering for shallow-water snappers (i.e., Gray, Mutton, Yellowtail, Cubera, Dog, and Mahogany Snapper and Schoolmaster) was reasonably tight (Table 4). These stocks are primarily found on the West Florida Shelf (Figure 10A). Of these, Gray, Mutton, and Yellowtail Snapper are abundant, but encounters with other shallowwater snapper species are rare (Table 3). Gray Snapper was most commonly encountered in the MRFSS and formed a somewhat distinct cluster (Table 3; Figure 7). Gray Snapper is common in Florida waters, especially in the Florida Keys, where it co-occurs to some extent with Mutton Snapper; but it also has a sizeable fishery on the offshore reefs and oil rigs in the western Gulf of Mexico. This may explain why Gray Snapper sometimes clustered with shallow-water groupers (i.e., Gag and Scamp) and moderate-depth snapper species (i.e., Lane and Red Snapper).

Yellowtail Snapper was most common in the CVL data set, where it clustered with Mutton Snapper and Hogfish. Yellowtail Snapper was most highly correlated and associated with Dog and Mutton Snapper (Table 4). Mutton Snapper was associated with Schoolmaster and Yellowtail and Gray Snapper. Gulf landings of Hogfish, Mutton Snapper, and Yellowtail Snapper are predominantly concentrated in southwest Florida and the Florida Keys (Figure 10A). The unique fishing techniques used to land Yellowtail Snapper (surface chumming and unweighted lines) and Hogfish (spearfishing) may make them good candidates for species-specific ACLs.

Clustering the rare snapper species was done primarily through an examination of the nodal analysis and weighted mean cluster association index output (Figure 9; Table 4). Schoolmaster was highly correlated with Dog and Mutton Snapper and highly associated with Mutton, Dog, Yellowtail, and Cubera Snapper. Cubera Snapper has a life history similar to that of Mutton Snapper (Figure 2). Dog Snapper was highly correlated and associated with Yellowtail Snapper (Table 4). Mahogany Snapper was only recorded in the CVL data set, and every trip landing a Mahogany Snapper also landed a Gray Snapper. Mahogany Snapper was associated with Cubera Snapper (Table 4).

The Magnuson—Stevens Fishery Conservation and Management Reauthorizatoin Act of 2006 requires that fishery management plans “establish a mechanism for specifying annual catch limits … at a level such that overfishing does not occur in the fishery.” Setting stock-specific ACLs for many unassessed stocks may be unrealistic because data are inadequate for determining stock status relative to established status determination criteria. Many of these stocks are data poor, difficult to identify, or experience extreme fluctuations in relative landings due to their large yearclasses, rarity, inadequate data collection procedures, or lack of targeted fishing effort. Using stock complexes to set ACLs may be the best management option when formal stock assessments are unavailable and the data requirements (e.g., a stable catch for several years and reliable estimates of natural mortality) of other methods (such as depletionadjusted average catch; MacCall 2007) are not met. Using stock complexes for ACL/AM management reduces the management burden for quota monitoring and may help mitigate the impacts of uncertainty in landings data or species identification by pooling data-poor species. Another option would be to use assessed stocks as indicator species; however, the use of an indicator species implicitly assumes that the population trends of that species reflect those of others in the assemblage (Simberloff 1998; Zacharias and Roff 2001; Carignan and Villard 2002)—an assumption that is often violated in practice (Niemi et al. 1997). For an assessed stock to be an appropriate indicator stock for a stock complex, assessed stocks and unassessed stocks in the complex should show similar trends in population abundance in response to environmental forcing, fishing pressure, and fisheries management regulations. Unfortunately, it is extremely difficult to separate out these signals for Gulf stocks given the absence of fishery-independent data (e.g., Jay 1996; Collie et al. 2008).

Using fishery-dependent data as a proxy for trends in population abundance introduces several layers of bias (e.g., gear, spatial, temporal, and depth) into any evaluation of indices of abundance. These biases might generate spurious correlations that would be difficult to separate from actual population trends (May and MacArthur 1972; Landres et al. 1988; Leibold 1995; Niemi et al. 1997; Shaul et al. 2007; Shertzer and Williams 2008). In the absence of a fully resolved analysis of indices of abundance that adequately controls for the confounding variability introduced by environmental forcing, fishing pressure, and fisheries management regulations, a comprehensive understanding of co-occurrence in the catch across sectors is critical to simplifying ACL/AM management. Simberloff (1998) recommends identifying keystone species instead, which might not be assessed or even appropriate targets for management but whose activities govern the well-being of many other species. Unfortunately, keystone species are difficult to identify. More recently, the establishment of fully protected areas in representative habitats has been suggested as a way to restore natural ecosystem dynamics and protect a portion of the reproductive stock (Bohnsack et al. 2004; Lindenmayer et al. 2006).

In establishing stock complexes, managers should consider the geographic and depth distribution of species, along with their life history characteristics, exploitation patterns, and vulnerabilities. As new information and understanding of species linkages and complexes arises, managers should adapt their management strategies. This will allow for proactive management that accounts for ecosystem-based management considerations (such as temporal fluctuations in stock abundance due to environmental forcing or multispecies interactions) as well as comprehensive assessments of the impacts of regulations on associated species. For this approach to succeed, data collection will need to aim at developing a high-resolution map of the biogeographic distribution of fish stocks and the spatial distribution of fishing effort as well as improved estimation of life history parameters and the trophic linkages between species. This approach is especially relevant given that community structure may change through time (Shertzer et al. 2009) due to heavy exploitation (Hughes 1994; McClenachan 2009), invasive species (Albins and Hixon 2008), habitat degradation (Hoss and Engel 1996; Anderson et al. 2008), and climate change (Holbrook et al. 1997; Attrill and Power 2002; Genner et al. 2004; Perry et al. 2005; Collie et al. 2008). Similarly, the structure of stock complexes may change through time if the fishery begins operating more heavily in different areas, using different gear types, or targeting different species. Complexes derived from methods such as those explored in this study should be revisited periodically and supplemented with fishery-independent indices of abundance or ecosystem-based approaches.


The authors are grateful for comments from N. Mehta, A. Strelcheck, J. Walter III, J. Quinlan, C. Porch, S. Calay, J. McGovern, S. Branstetter, J. Kimmel, C. Simmons, L. Barbieri, S. Atran, and B. Crowder. We are also grateful to K. Shertzer and E. Williams, who provided input and suggestions on clustering methods. These analyses would not have been possible without the greatly appreciated efforts of the commercial fishermen and headboat operators who submitted logbook data, and the recreational anglers and charter boat captains participating in MRFSS. We thank the Southeast Fisheries Science Center's (SEFSC) K. Brennan, K. McCarthy, S. Turner, V. Matter, J. Bennett, W. Ingram, and L. Scott-Denton for providing data used in this work. We also thank SEFSC staff for their comprehensive scientific review of this manuscript.



Able, K. W. , D. C. Twichell , C. B. Grimes , and R. S. Jones . 1987. Tilefishes of the genus Caulolatilus construct burrows on the seafloor. Bulletin of Marine Science 40:1–10. Google Scholar


Albins, M. A. , and M. A. Hixon . 2008. Invasive Indo-Pacific Lionfish Pterois volitans reduce recruitment of Atlantic coral reef fishes. Marine Ecology Progress Series 367:233–238. Google Scholar


Anderson, D. M. , J. M. Burkholder , W. P. Cochlan , P. M. Glibert , C. J. Gobler , C. A. Heil , R. M. Kudela , M. L. Parsons , J. E. Rensel , D. W. Townsend , V. L. Trainer , and G. A. Vargo . 2008. Harmful algal blooms and eutrophication: examining linkages from selected coastal regions of the United States. Harmful Algae 8:39–53. Google Scholar


Attrill, M. J. , and M. Power . 2002. Climatic influence on a marine fish assemblage. Nature 417:275–278. Google Scholar


Beals, E. W. 1973. Mathematical elegance and ecological naiveté. Journal of Ecology 61:23–35. Google Scholar


Berkson, J. , L. Barbieri , S. Cadrin , S. Cass-Calay , P. Crone , M. Dorn , C. Friess , D. Kobayashi , T. J. Miller , W. S. Patrick , S. Pautzke , S. Ralston , and M. Trianni . 2011. Calculating acceptable biological catch for stocks that have reliable catch data only (Only Reliable Catch Stocks—ORCS). NOAA Technical Memorandum NMFS-SEFSC-616. Google Scholar


Boesch, D. F. 1977. Application of numerical classification in ecological investigations of water pollution. Virginia Institute of Marine Science Special Scientific Report 77. Google Scholar


Bohnsack, J. A. , J. S. Ault , and B. Causey . 2004. Why have no-take marine protected areas? Pages 185–193 in J. B. Shipley , editor. Aquatic protected areas as fisheries management tools. American Fisheries Society, Symposium 42, Bethesda, Maryland. Google Scholar


Bortone, S. A. , R. L. Shipp , G. F. Mayer , and J. L. Oglesby . 1979. Taxometric analysis of a demersal fish fauna. Ambio Special Report 6:83–85. Google Scholar


Carignan, V. , and M. A. Villard . 2002. Selecting indicator species to monitor ecological integrity: a review. Environmental Monitoring and Assessment 78:45–61. Google Scholar


Carruthers, T. R. , A. E. Punt , C. J. Walters , A. MacCall , M. K. McAllister , E. J. Dick , and J. Cope . 2014. Evaluating methods for setting catch limits in data-limited fisheries. Fisheries Research 153:48–68. Google Scholar


Collie, J. S. , A. D. Wood , and H. P. Jeffries . 2008. Long-term shifts in the species composition of a coastal fish community. Canadian Journal of Fisheries and Aquatic Sciences 65:1352–1365. Google Scholar


Faith, D. P. , P. R. Minchin , and L. Belbin . 1987. Compositional dissimilarity as a robust measure of ecological distance. Plant Ecology 69:57–68. Google Scholar


Field, J. G. , K. R. Clarke , and R. M. Warwick . 1982. A practical strategy for analysing multispecies distribution patterns. Marine Ecology Progress Series 8:37–52. Google Scholar


Froese, R. , and D. Pauly , editors. 2009. Species summaries of the 42 reef fish species evaluated in this study. Available: (September 2010). Google Scholar


Genner, M. J. , D. W. Sims , V. J. Wearmouth , E. J. Southall , A. J. Southward , P. A. Henderson , and S. J. Hawkins . 2004. Regional climatic warming drives long-term community changes of British marine fish. Proceedings of the Royal Society of London B 271:655–661. Google Scholar


Gomes, M. C. , E. Serrão , and M. F. Borges . 2001. Spatial patterns of groundfish assemblages on the continental shelf of Portugal. ICES Journal of Marine Science 58:633–647. Google Scholar


Grace, M. A. , and T. Henwood . 1997. Assessment of the distribution and abundance of coastal sharks in the U.S. Gulf of Mexico and Eastern Seaboard, 1995 and 1996. U.S. National Marine Fisheries Service Marine Fisheries Review 59:23–32. Google Scholar


Gulf of Mexico Fishery Management Council. 2011. Final generic annual catch limits/accountability measures amendment for the Gulf of Mexico Fishery Management Council's Red Drum, reef fish, shrimp, coral, and coral reefs fishery management plans. Gulf of Mexico Fishery Management Council, Tampa, Florida. Google Scholar


Harris, P. J. , D. M. Wyanski , and P. T. Powers Mikell . 2004. Age, growth, and reproductive biology of Blueline Tilefish along the southeastern coast of the United States. Transactions of the American Fisheries Society 133:1190–1204. Google Scholar


Henwood, T. , W. Ingram , and M. Grace . 2004. Shark/snapper/grouper longline surveys. National Marine Fisheries Service, Southwest Fisheries Science Center, SEDAR-7 Data Workshop Technical Document 8, Pascagoula, Mississippi. Google Scholar


Holbrook, S. J. , R. J. Schmitt , and J. S. Stephens Jr . 1997. Changes in an assemblage of temperate reef fishes associated with a climate shift. Ecological Applications 74:1299–1310. Google Scholar


Hoss, D. E. , and D. W. Engel . 1996. Sustainable development in the southeastern coastal zone: environmental impacts on fisheries. Pages 171–186 in F. J. Vernberg , W. B. Vernberg , and T. Siewicki , editors. Sustainable development in the southeastern coastal zone. University of South Carolina Press, Columbia. Google Scholar


Hughes, T. P. 1994. Catastrophes, phase shifts, and large-scale degradation of a Caribbean coral reef. Science 265:1547–1551. Google Scholar


Jay, C. V. 1996. Distribution of bottom-trawl fish assemblages over the continental shelf and upper slope of the U.S. West Coast, 1977–1992. Canadian Journal of Fisheries and Aquatic Sciences 53:1203–1225. Google Scholar


Koch, C. F. 1987. Prediction of sample size effects on the measured temporal and geographic distribution patterns of species. Paleobiology 13:100–107. Google Scholar


Lambert, J. M. , and W. T. Williams . 1962. Multivariate methods in plant ecology, IV. Nodal analysis. Journal of Ecology 50:775–802. Google Scholar


Landres, P. B. , J. Verner , and J. W. Thomas . 1988. Ecological uses of vertebrate indicator species: a critique. Conservation Biology 2:316–328. Google Scholar


Lee, Y. , and B. Sampson . 2000. Spatial and temporal stability of commercial groundfish assemblages off Oregon and Washington as inferred from Oregon trawl logbooks. Canadian Journal of Fisheries and Aquatic Sciences 57:2443–2454. Google Scholar


Leibold, M. A. 1995. The niche concept revisited: mechanistic models and community context. Ecology 76:1371–1382. Google Scholar


Lindenmayer, D. B. , J. F. Franklin , and J. Fischer . 2006. General management principles and a checklist of strategies to guide forest biodiversity conservation. Biological Conservation 131:433–445. Google Scholar


MacCall, A. 2007. Depletion-adjusted average catch. Pages 27–31 in A. Rosenberg , D. Agnew , E. Babcock , C. Mogensen , R. O'Boyle , J. Powers , G. Stefansson , and J. Swasey , editors. Setting annual catch limits for U.S. fisheries: an expert working group report. Lenfest Ocean Program, Washington, D.C. Google Scholar


Magnuson—Stevens Fishery Conservation and Management Reauthorization Act of 2006. U.S. Statutes at Large 120:3575–3663. Google Scholar


May, R. M. , and R. H. Mac Arthur . 1972. Niche overlap as a function of environmental variability. Proceedings of the National Academy of Sciences of the USA 69:1109–1113. Google Scholar


McClenachan, L. 2009. Documenting loss of large trophy fish from the Florida Keys with historical photographs. Conservation Biology 23:636–643. Google Scholar


McGarigal, K. , S. Cushman , and S. G. Stafford . 2000. Multivariate statistics for wildlife and ecology research. University of Chicago Press, Chicago. Google Scholar


MRAG (Marine Resources Assessment Group) Americas. 2009a. Productivity—susceptibility analyses: Gulf of Mexico. Available: (March 2016). Google Scholar


MRAG (Marine Resources Assessment Group) Americas. 2009b. Productivity—susceptibility analyses: South Atlantic. Available: (March 2016). Google Scholar


Mueter, F. J. , and B. L. Norcross . 2000. Changes in species composition of the demersal fish community in nearshore waters of Kodiak Island, Alaska. Canadian Journal of Fisheries and Aquatic Sciences 57:1169–1180. Google Scholar


Niemi, J. G. , J. M. Hanowski , A. R. Lima , T. Nicholls , and N. Weiland . 1997. A critical analysis on the use of indicator species in management. Journal of Wildlife Management 61:1240–1252. Google Scholar


Palmer, S. M. , P. J. Harris , and P. T. Powers . 2004. Age, growth, and reproduction of Tilefish, Lopholatilus chamaeleonticeps, along the southeast Atlantic coast of the United States, 1980–87 and 1996–98. Marine Resource Research Institute, South Carolina Department of Natural Resources, SEDAR4-DW-18, Charleston. Google Scholar


Parker, R. O. Jr. , and J. L. Ross . 1986. Observing reef fishes from submersibles off North Carolina. Northeast Gulf Science 8:31–49. Google Scholar


Perry, A. L. , P. J. Low , J. R. Ellis , and J. D. Reynolds . 2005. Climate change and distribution shifts in marine fishes. Science 308:1912–1915. Google Scholar


Reed, J. K. , S. A. Pomponi , D. Weaver , C. K. Paull , and A. E. Wright . 2005. Deep-water sinkholes and bioherms of South Florida and the Pourtalés terrace: habitat and fauna. Bulletin of Marine Science 77:267–296. Google Scholar


Ross, J. L. 1978. Life history aspects of the Gray Tilefish Caulolatilus microps (Goode and Bean, 1878). Master's thesis. College of William and Mary, Williamsburg, Virginia. Google Scholar


Ross, J. L. , and G. R. Huntsman . 1982. Age, growth, and mortality of Blueline Tilefish from North Carolina and South Carolina. Transactions of the American Fisheries Society 111:585–592. Google Scholar


SEDAR-10 (Southeast Data Assessment and Review). 2006. Gulf of Mexico Gag grouper. Available: (March 2015). Google Scholar


SEDAR-15 (Southeast Data Assessment and Review). 2008. South Atlantic Greater Amberjack. Available: (March 2015). Google Scholar


SEDAR-22-DW-13 (Southeast Data Assessment and Review Data Workshop Report). 2010. Estimation of species misidentification in the commercial landing data of Yellowedge Groupers in the Gulf of Mexico from 1984 to 2009. Available: pdf?id=DOCUMENT. (March 2015). Google Scholar


Sedberry, G. R. , and R. F. Van Dolah . 1984. Demersal fish assemblages associated with hard bottom habitat in the South Atlantic Bight of the U. S.A. Environmental Biology of Fishes 11:241–258. Google Scholar


Sedberry, G. R. , O. Pashuk , D. M. Wyanski , J. A. Stephen , and P. Weinbach . 2006. Spawning locations for Atlantic reef fishes off the southeastern U.S. Proceedings of the Gulf and Caribbean Fisheries Institute 57:463–514. Google Scholar


Shaul, L. , L. Weitkamp , K. Simpson , and J. Sawada . 2007. Trends in abundance and size of Coho Salmon in the Pacific Rim. North Pacific Anadromous Fish Commission Bulletin 4:93–104. Google Scholar


Shertzer, K. W. , and E. H. Williams . 2008. Fish assemblages and indicator species: reef fishes off the southeastern United States. U.S. National Marine Fisheries Service Fishery Bulletin 106:257–269. Google Scholar


Shertzer, K. W. , E. H. Williams , and J. C. Taylor . 2009. Spatial structure and temporal patterns in a large marine ecosystem: exploited reef fishes of the southeast United States. Fisheries Research 100:126–133. Google Scholar


Simberloff, D. 1998. Flagships, umbrellas, and keystones: is single-species management passé in the landscape era? Biological Conservation 83:247–257. Google Scholar


Sneath, P. H. A. , and R. R. Sokal . 1973. Numerical taxonomy: the principles and practice of numerical classification. Freeman, San Francisco. Google Scholar


Struhsaker, P. , 1969. Demersal fish resources: composition, distribution, and commercial potential of the continental shelf stocks off the southeastern United States. Fishery Industrial Research 4:261–300. Google Scholar


USOFR (U.S. Office of the Federal Register). 2009. Magnuson—Stevens Act provisions; annual catch limits; national standard guidelines. Code of Federal Regulations, Title 50, Part 600. U.S. Government Printing Office, Washington, D.C. Google Scholar


Williams, W. T. , and J. M. Lambert . 1961. Nodal analysis of associated populations. Nature 191:202. Google Scholar


Williams, E. H. , and S. Ralston . 2002. Distribution and co-occurrence of rockfishes (family: Sebastidae) over trawlable shelf and slope habitats of California and southern Oregon. U.S. National Marine Fisheries Service Fishery Bulletin 100:836–855. Google Scholar


Zacharias, M. A. , and J. C. Roff . 2001. Use of focal species in marine conservation and management: a review and critique. Aquatic Conservation of Marine and Freshwater Ecosystems 11:59–76. Google Scholar


Appendix: Life History Parameter Information Sources


References for life history parameters (see Table 1). Abbreviations are as follows: SEDAR = Southeast Data Assessment and Review, SAR = Stock Assessment Report.



© Nicholas A. Farmer, Richard P. Malinowski, Mary F. McGovern, and Peter J. Rubec This is an Open Access article distributed under the terms of the Creative Commons Attribution License (, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited. The moral rights of the named author(s) have been asserted.
Nicholas A. Farmer, Richard P. Malinowski, Mary F. McGovern, and Peter J. Rubec "Stock Complexes for Fisheries Management in the Gulf of Mexico," Marine and Coastal Fisheries: Dynamics, Management, and Ecosystem Science 8(8), 177-201, (26 May 2016).
Received: 31 December 2014; Accepted: 18 February 2015; Published: 26 May 2016

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