207 chapter 7 Sulfite Pulp Mill Restoration 7.1 Introduction Sulfite paper mills use ammonia in various processes. A pulp mill on the Amelia estuary (north Florida) was responsible for extremely high ammonia loading (Livingston, 1996b; Livingston et al., 2002). Ammonia toxicity to marine phytoplankton has not been well established in the scientific literature. The U.S. Environmental Protection Agency (1976, 1989) proposed a limit of 0.02 mg L –1 as un-ionized ammonia for protection of freshwater aquatic life. Admiraal (1977) showed that toxicity to phytoplankton is due to ammonia (NH 3 ) rather than ammonium (NH 4 + ), and that concentrations of 0.247 mg L –1 ammonia retarded the growth of seven species of benthic diatoms. Concentrations of 0.039 mg L –1 ammonia reduced reproduction of a red macroalga, Champia parvula (Admiraal, 1977). These concentrations were within the range of ammonia found in polluted parts of the Amelia system (Florida Department of Environmental Regulation, 1991). Ammonia is also an important nutrient for coastal phytoplankton, with studies that indicate preferential uptake by individual plankton species that sometimes leads to blooms (Admiraal and Peltier, 1980; Flemer et al., 1997; Livingston, 2000; U.S. Environmental Protection Agency, 1989). Ammonia has been shown to be a selective factor in the species composition of benthic diatoms due to species-specific variation of the ammonia toxicity (Van Raalte et al., 1976; Sullivan, 1978; Admiraal and Peletier, 1980). Thus, the potential effects of ammonia discharges on coastal phytoplankton can be both stimulatory and inhibitory with species- specific responses to ranges of ammonia concentrations. Ammonium toxicity in water can be due to the effects of both the ionized (NH 4 + ) and un-ionized (NH 3 ) forms with the relative concentration of each dependent on ambient pH and temperature (Kórner et al., 2001). Un-ionized ammonia toxicity increases with increased pH and temperature (U. S. Environmental Protection Agency, 1989). Whitfield (1974) defined the relationships of the ionized and un-ionized forms under different conditions of temperature, atmospheric pressure, and pH. Downing and Merkens (1955) found that the un-ionized form is the most toxic as it is uncharged and therefore traverses the cell membrane more readily. Some authors (Clement and Merlin, 1995) attributed toxicity to NH 3 only. Other studies (Monselise and Kost, 1993) attributed toxicity to both forms. With respect to the effects of ammonium on duckweed ( Lemna gibba ), Kórner et al. (2001) did not have a firm conclusion regarding the relative toxicity of the ionized (NH 4 + ) and un-ionized (NH 3 ) forms. In this study, we determined the ammonium concentrations as un-ionized ammonia with the pH of the study areas being relatively constant (mean, 7.64; S. D., 0.32; Livingston, 1996b). 1966_book.fm Page 207 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC 208 Restoration of Aquatic Systems 7.1.1 Study Area The Amelia and Nassau River estuaries (Figure 7.1) are located in coastal northeast Florida, and are characterized by extensive marsh development and relatively high salinities. Tidal ranges approximate 2 to 3 m. The study area is a maze of channels and bayous with direct connections to the Atlantic Ocean. Major parts of the Nassau system are within a state park, and preliminary water quality analyses indicated relatively high water quality (Livingston, 1996b). The climate along this part of the coast is mild. Annual rainfall averages around 120 cm, with peaks during summer months. A sulfite pulp mill discharges effluents (approx. 114 million gallons day –1 [mgd]) into the Amelia River-estuary (Figure 7.1). Mill effluents currently are discharged into a 125,000 m 2 mixing zone on outgoing tides. Dennison et al. (1977) found that effluent-receiving areas of the Amelia system were characterized by low dissolved oxygen (DO) and pH, Figure 7.1 Locations of sampling sites for the Amelia/Nassau River estuary Study (1994–1995; 1997–1998; 2000–2001). Geographic data provided by the Florida Geographic Data Library (FGDL). 1966_book.fm Page 208 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC Chapter 7: Sulfite Pulp Mill Restoration 209 high watercolor, and low primary production relative to reference sites. Secchi depths were relatively low and total organic carbon (TOC) levels were relatively high in receiving areas of the Amelia estuary. Generally, phytoplankton and zooplankton numbers and diversity in the Amelia system were comparable to those in reference areas elsewhere (Dennison et al., 1977). The Florida Department of Environmental Regulation (1991) reported high (approx. 1.7 mg L –1 ) concentrations of free ammonia in areas affected by the pulp mill; recent analyses (Livingston, 1996b) corroborated these findings. There were also indications of low phytoplankton species richness in the discharge areas (Florida Department of Environmental Regulation, 1991). Based on a 12-month field analysis (1994–1995), Livingston (1996b) found that the Nassau system was an adequate (i.e., unpolluted, with comparable habitat distribution) reference area for studies of the Amelia system. Determinations of water quality and phytoplankton/zooplankton distributions in the Amelia and Nassau River estuaries indi- cated that ammonia was present in significantly high concentrations in the Amelia system. A combined field descriptive and field/laboratory experimental program (1997–1998) was then established to determine the effects of ammonia on phytoplankton assemblages. Specific research questions for this study were (1) whether pulp mill effluents were asso- ciated with observed reductions of phytoplankton assemblages in the Amelia system and (2) whether ammonia and/or light transmission were responsible for such effects. 7.2 Methods and Materials for collection of physicochemical field data are given by Flemer et al. (1997); Livingston (1979, 1982a, 2000): and Livingston et al. (1997, 1998a, 2000). Stations were determined that defined the distribution of mill effluents in the receiving area. Matching stations, chosen for comparability of habitat characteristics (temperature, salinity), were established were taken monthly over three 12-month sampling periods (1994–1995, 1997–1998, and 2000–2001). Microcosm and mesocosm experiments with pulp mill effluents and ammonia were carried out during the 1997–1998 sampling period under conditions approximating those observed in the field. Net phytoplankton samples were taken with two 25-µm nets (bongo configuration) in duplicate runs for periods of 1 to 2 minutes. Repetitive (3) 1-L whole water phytoplank- ton samples were taken at the surface. Zooplankton were taken with two 202-µm nets (bongo configuration) in duplicate runs. Methods used for the comparison of monthly data (water quality, biological factors) were developed to determine significant differences between matching Amelia and Nassau sites (polluted and unpolluted) over the 12-month study periods (Livingston et al., 1998; Livingston, 2000) (Appendix I). Field data were analyzed using a Principle Components Analysis (PCA) as a preliminary review of the the physicochemical variables into a smaller set of linear combinations that could account for most of the total variation of the original set. Significant principal components were then applied to regression models, with phytoplankton and zooplankton abundance and species richness as dependent variables. A combination of background field monitoring, controlled laboratory experiments using microcosms of Skeletonema costatum (Grev.) Cleve, and field mesocosm experiments (multispecies) was used to evaluate the effects of pulp mill effluents and ammonia on plankton assemblages in the Amelia River estuary. Measured solutions of ammonia were used to evaluate the effects of ammonia by itself relative to the effects of ammonia as part of the whole mill effluent. Target concentrations for the ammonia experiments were based 1966_book.fm Page 209 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC in the Nassau River estuary as reference sites for comparative analyses (Figure 7.1). Data Detailed protocols for this work are given in Appendix I. Detailed descriptions of methods water quality variables (Appendix II; Livingston et al., 1998b). The PCA was used to reduce 210 Restoration of Aquatic Systems on known field concentrations in polluted areas of the Amelia system. We carried out one microcosm test (June 29–July 4, 1998) using lab-cultured Skeletonema with measured injec- tions of ammonia, and two tests (July 7–July 22, 1998 and August 28–September 1, 1998) with pulp mill effluents, with ammonia concentrations approximating those in the field. We performed six larger-volume mesocosm tests in the field, with natural phytoplankton assemblages taken from the reference Nassau area. Two tests (August 19–August 21, 1997 and October 27–October 29, 1997) were run with measured injections of ammonia, and four tests (May 20–May 22, 1998; June 24–June 26, 1998; August 4–August 6, 1998; and September 23–September 25, 1998) were carried out with pulp mill effluents that were added to basal mixtures to approximate ammonia concentrations determined in the field. For all tests, ammonia dosages were tested daily and ammonia was added where necessary to maintain target concentrations. During 2000–2001, the mill reduced ammonia loading to near-natural conditions, and another field survey of water quality, phytoplankton, and zooplankton was carried out in first two sampling periods is given by Livingston et al. (2002). 7.3 Results 7.3.1 Water Quality Data There were no consistently significant differences in surface temperature, salinity, Secchi depths, BOD, DOC, TSS, silica, TP, POC, or sulfide between cognate station pairs during the survey periods 1994–1995 and 1997–1998 (Livingston et al., 2002). Surface watercolor was significantly (P < 0.05) higher at stations R03, R04, R10, N06, N09, and N11 than their paired matches during 1994–1995 and at stations R01, R08, and R11 during 1997–1998. Color was highest in the upper parts of both estuaries during winter months of increased rainfall. There were no significant differences in mean orthophosphate concentrations between cognate stations during both sampling periods although the upper Nassau system (Stations N07, N08, N09, and N10) had uniformly higher concentrations of orthophosphate significantly higher at Stations R01, R04, R05, and R11 during 1994–1995 and was higher at Stations R02, R03, R09, N08, and N10 during 1997–1998. During 1994–1995, surface ammonia concentrations were significantly (P < 0.05) higher at all stations in the Amelia system with the exception of R04 and R12 (Table 7.1). The relatively high ammonia concentrations near the mill outfall and gradients of surrounding stations indicated the pulp mill as the source. Mean annual surface ammonia concentra- tions ranged from 0.19 to 0.43 mg L –1 No such gradient was noted in the Nassau estuary with annual means ranging from 0.09 to 0.11 mg L –1 . The highest ammonia concentrations in the Amelia system appeared during spring/summer months during both sampling periods (Livingston et al., 2002). Mean nitrite/nitrate concentrations near the outfall (Stations R01, R03, and R06) followed this trend, although differences were not statistically significant in the upper parts of the respective study areas. Surface total nitrogen was generally higher throughout the Amelia system during both sampling periods with significant (P < 0.05) differences at Stations R01, R02, R03, R06, R09, and R11. Mean surface chlorophyll a concentrations were generally lower in the lower Amelia River estuary than matched stations in the Nassau system during both sampling periods, and were significantly reduced (P < 0.05) at Stations R01, R08, R11, and R12 during 1997–1998. Spatial and temporal chlorophyll a trends followed (inversely) those of ammonia. 1966_book.fm Page 210 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC than the paired stations in the Amelia system (Table 7.1). Total phosphorus (TP) was in the Amelia estuary during 1997–1998 (Table 7.2). the manner described above and in Appendix I. A detailed account of the results of the Chapter 7: Sulfite Pulp Mill Restoration 211 Table 7.1 Statistical Comparison (means tests: paired t -test, Wilcoxon signed rank test) of Physicochemical Data Collected at Stations in the Nassau and Amelia River Estuaries Monthly for 15 Months from November 1994 thr ough October 1995 Cognate NH 3 NO 3 TN PO 4 TP SiO 2 Chlor. a Sulfide Station Pair (mgN L −− −− 1 ) (mgN L −− −− 1 ) (mgP L −− −− 1 ) (mg L −− −− 1 ) Surface R01/N04 0.274/0.083 0.016/0.006 1.211/0.640 0.016/0.018 0.086/0.052 0.364/0.358 5.28/5.59 0.328/0.141 WS (P < 0.005) WS (P < 0.05) WS (P < 0 .05) WN WS (P < 0.05) WN WN WS (P < 0.005) R02/N04 0.138/0.083 0.009/0.006 0.946/0.640 0.018/0.018 0.087/0.052 0.347/0.358 5.38/5.59 0.262/0.141 WS (P < 0.025) WN WS (P < 0.005) WN WN WN WN WS (P < 0.025) R03/N04 0.141/0.083 0.013/0.006 1.133/0.640 0.020/0.018 0.083/0.052 0.379/0.358 6.50/5.59 0.226/0.141 WS (P < 0.05) WS (P < 0.005) WS (P < 0.005) WN WN WN WN WS (P < 0.005) R04/N02 0.150/0.118 0.016/0.013 0.978/0.680 0.026/0.022 0.087/0.066 0.569/0.397 7.88/6.34 0.232/0.128 WN WN WN WN WS (P < 0.025) WN WN WS (P < 0.025) R05/N11 0.157/0.104 0.016/0.014 1.202/0.815 0.022/0.022 0.150/0.073 0.421/0.390 6.13/7.24 0.274/0.216 WS (P < 0.02) WN WN WN WS (P < 0.01) WN WN WN R06/N03 0.234/0.104 0.017/0.011 1.092/0.619 0.017/0.022 0.103/0.068 0.352/0.297 4.68/5.53 0.264/0.195 WS (P < 0.025) WS (P < 0.025) WS (P < 0.005) WN WN WN WN WS (P < 0.025) R07/N03 0.179/0.104 0.012/0.011 0.860/0.619 0.017/0.022 0.112/0.068 0.341/0.297 5.46/5.53 0.173/0.195 WS (P < 0.025) WN WN WN WN WS (P < 0.025) WN WN R08/N03 0.156/0.104 0.014/0.011 0.864/0.619 0.016/0.022 0.054/0.068 0.289/0.297 5.97/5.53 0.129/0.195 WS (P < 0.05) WN WN WN WN WN WN WN R09/N01 0.147/0.100 0.014/0.013 0.798/0.622 0.016/0.011 0.092/0.065 0.262/0.241 5.20/6.58 0.214/0.167 WS (P < 0.05) WN WS (P < 0.025) WN WN WN WN WN 1966_book.fm Page 211 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC 212 Restoration of Aquatic Systems Table 7.1 (continued) Statistical Comparison (means tests: paired t -test, Wilcoxon signed rank test) of Physicochemical Data Collected at Stations in the Nassau and Amelia River Estuaries Monthly for 15 Months from November 1994 through October 1995 Cognate NH 3 NO 3 TN PO4 TP SiO 2 Chlor. a Sulfide Station Pair (mgN L −− −− 1 ) (mgN L −− −− 1 ) (mgP L −− −− 1 ) (mg L −− −− 1 ) R10/N01 0.147/0.100 0.017/0.013 0.683/0.622 0.017/0.011 0.055/0.065 0.323/0.241 5.68/6.58 0.181/0.167 WS (P < 0.05) WN WN WN WN WN WN WN R11/N05 0.141/0.082 0.010/0.008 0.782/0.582 0.017/0.014 0.170/0.052 0.265/0.263 5.48/6.81 0.212/0.146 WS (P < 0.01) WN WS (P < 0.05) WN WS (P < 0.025) WN WN WN R14/N06 0.146/0.086 0.010/0.011 0.765/0.610 0.015/0.022 0.102/0.065 0.473/0.428 5.57/5.41 0.199/0.234 WS (P < 0.005) WN WS (P < 0.025) WS (P < 0.01) WN WN WN WN R12/N09 0.162/0.081 0.010/0.013 0.685/0.664 0.016/0.027 0.088/0.071 0.348/0.523 6.06/6.81 0.161/0.233 WS (P < 0.01) WN WN WN WN WN WN WS (P < 0.05) R12/N07 0.162/0.085 0.010/0.013 0.685/0.655 0.016/0.020 0.088/0.059 0.348/0.389 6.06/6.00 0.161/0.167 WN WN WN WN WN WN WN WN R13/N10 0.181/0.091 0.016/0.015 0.863/0.689 0.020/0.027 0.063/0.076 0.501/0.493 6.00/6.68 0.209/0.201 WS (P < 0.01) WN WN WN WN WN WN WN R13/N08 0.181/0.083 0.016/0.010 0.863/0.689 0.020/0.024 0.063/0.077 0.501/0.490 6.00/6.43 0.209/0.197 WS (P < 0.01) WN WN WN WN WN WN WN WN, not sig. WS, sig. Boldface = bloom species. 1966_book.fm Page 212 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC Chapter 7: Sulfite Pulp Mill Restoration 213 Table 7.2 Statistical Comparison (means tests: paired t -test, Wilcoxon signed rank test) of Physicochemical Data Collected at Stations in the Nassau and Amelia River Estuaries Monthly for 15 Months from July 1997 through September 1998 Cognate NH 3 NO 2 +NO 3 PO 4 TP SiO 2 POC Chlor. a Sulfide Station Pair (mg L −− −− 1 ) (mgN L −− −− 1 ) (mgP L −− −− 1 ) (mgP L −− −− 1 ) (mg L −− −− 1 ) (mg L −− −− 1 )( µγ L −− −− 1 ) (mg L −− −− 1 ) Surface N04/R01 0.11/0.43 0.07/0.02 0.03/0.03 0.14/0.09 1.27/1.55 1.68/1.47 7.65/5.95 0.19/0.24 WS (P < 0.01) WS (P < 0.01) WN WN WN WN WS (P < 0.05) WN N03/R08 0.10/0.37 0.06/0.08 0.03/0.03 0.08/0.07 1.12/1.29 1.17/1.76 7.84/5.09 0.18/0.16 WS (P < 0.01) WS (P < 0.05) WN WN WN WN WS (P < 0.01) WN N05/R11 0.09/0.29 0.05/0.09 0.02/0.03 0.09/0.08 0.84/1.41 1.76/1.97 7.31/5.60 0.17/0.21 WS (P < 0.01) WS (P < 0.01) WN WN WS (P < 0.01) WN WS (P < 0.05) WN N06/R12 0.11/0.27 0.08/0.10 0.28/0.30 0.08/0.07 1.31/1.61 1.94/1.34 7.31/4.98 0.20/0.27 WS (P < 0.01) WN WN WN WN WN WS (P < 0.05) WN N08/R13 0.10/0.19 0.08/0.10 0.03/0.03 0.10/0.08 1.61/2.03 2.45/1.97 8.35/8.79 0.20/0.21 WS (P < 0.01) WN WN WS (P < 0.05) WN WN WN WN Bottom N04-R01 0.11/0.30 0.07/0.09 0.03/0.03 0.09/0.09 1.51 1.51/2.05 8.13/5.99 0.17/0.19 WS (P < 0.01) WN WN WN WN WS (P < 0.05) WS (P < 0.02) WN N03/R08 0.11/0.29 0.06/0.09 0.02/0.03 0.09/0.08 1.06/1.21 1.9/2.4 8.57/4.95 0.19/0.21 WS (P < 0.01) WS (P < 0.01) WN WN WN WN WS (P < 0.01) WN N05/R11 0.11/0.27 0.04/0.09 0.03/0.03 0.11/0.08 0.73/1.40 3.52/1.82 9.3/5.8 0.17/0.22 WS (P < 0.01) WS (P < 0.01) WN WS (P < 0.05) WS (P < 0.01) WN WS (P < 0.01) WN N06/R12 0.12/0.26 0.07/0.11 0.03/0.03 0.09/0.08 1.14/1.66 2.53/1.85 7.56/5.6 0.21/0.18 WS (P < 0.01) WS (P < 0.01) WN WN WS (P < 0.01) WN WS (P < 0.05) WN N08/R13 0.26.0.23 0.07/0.11 0.03/0.03 0.13/0.10 1.50/2.05 3.32/2.24 9.17/7.97 0.20/0.23 WN WN WN WN WS (P < 0.05) WN WN WN WN, not sig. WS, sig. Boldface = bloom species. 1966_book.fm Page 213 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC 214 Restoration of Aquatic Systems 7.3.2 Light Transmission Light data indicated that during 1994–1995, there were no major differences in light at Station R01 were lower than at Station N04 during 1997–1998, this was not consistent throughout the entire sampling period. In three of the eight noted readings, the differences were negligible. When viewed as differences in euphotic depths at different wavelengths, there were no significant differences between paired Stations N04 and R01. The lowest euphotic depths (and highest extinction coefficients) in both systems were noted during February 1998, a period of low chlorophyll a concentrations. With the exception of Station R11 at the 430-nm level, light extinction coefficients in the Amelia system were not signif- icantly higher than those in the Nassau system. There were no significant reductions in euphotic depths in the Amelia system. In both systems, there was evidence of a “gelbstoff shift” (Livingston et al., 1998b), whereby humic substances absorb light at lower wavelengths. Extinction coefficients were significantly higher and euphotic depths were significantly lower in the upper Nassau system where the highest levels of color were noted. The highest light extinction coeffi- cients were noted at Station N08. Although there was thus no evidence of a significant mill effect on light transmission in the Amelia River estuary relative to the reference system, the upper parts of the Nassau River estuary were subject to the effects of runoff that affected both color and light transmission. 7.3.3 Phytoplankton and Zooplankton Nearly 250 species of whole water phytoplankton were identified in the two study areas during the 1994–1995 survey. Numerical abundance of phytoplankton was reduced in the Amelia system relative to the reference area, and totaled only about 57% of the phytoplank- ton numbers found in the Nassau system. Skeletonema costatum was dominant in both study areas. Other dominants included Cylindrotheca closterium, Thalassionema nitzschioides, and Asterionellopsis glacialis. Major reductions were noted for S. costatum, A. glacialis, T. nitzschioides, and Pseudonitzschia sp. in the Amelia system relative to the reference area. The 1997–1998 results were similar to those of 1994–1995. Of the ten top dominant species, representing over 75% of the numbers of phytoplankton taken during the 1997–1998 survey, seven such species had considerably higher numbers in the Nassau system than in the Amelia system. The top dominant in the Nassau system was S. costatum, whereas phytoplankton assemblages in the Amelia system were dominated by Chaetoceros socialis. Cryptophytes and nannoflagellates were somewhat higher in the Amelia system than in the reference system. Nannococcoids were noted primarily at the outfall station. Blooms of Navicula sp. were found at Station R13 during July 1998. In addition to S. costatum, several species were notably higher in the Nassau system; these included Thalassiosira proschikinae and T. decipiens, Asterionellopsis japonica, C. closterium, T. nitzschoides, Chaetoceros curvisetus, and Chaetoceros laciniosus. With the exception of Station R13, densities of diatoms (Class Bacillariophyceae) were lower in the Amelia system than in the Nassau system during both sampling periods. The silicoflagellates were often more abundant in the Nassau system. The cryptophytes (Division Cryptophyta), green algae (Division Chlorophyta), dinoflagellates (Division Dinophyta), and blue-green algae (Division Cyanophyta) were generally found in higher concentra- tions in the Amelia system. Phytoplankton numbers and species richness of the net (25 µm) and whole water differences were statistically significant (P < 0.05) in the whole water phytoplankton but 1966_book.fm Page 214 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC penetration between the Amelia and Nassau systems (Table 7.3). Although euphotic depths phytoplankton were higher in the Nassau system during 1994–1995 (Table 7.4); such Chapter 7: Sulfite Pulp Mill Restoration 215 Table 7.3 Statistical Comparison (independence tests, Chi-square normality tests, variance tests, means tests, pair ed t-test, Wilcoxon signed rank test, and distribution shape tests) of Light Transmission Data (Kd, Euphotic Depths) Collected at Stations in the Nassau and Amelia River Estuaries Monthly for 12 Months from August 1997 through August 1998 (no data taken, July 1998). Euphotic Depth and Kd Given for the Overall Spectrum and at Specific Wavelengths (430, 550, 665 nm) Cognate Kd Kd-430 Kd-550 Kd-665 Eup. Dpth. 430-Eup. Dpth. 550-Eup. Dpth. 665-Eup. Dpth. Station Pair (m) (m) (m) (m) N04/R01 2.91/2.37 5.65/4.31 3.13/2.85 2.56/2.22 1.87/2.11 1.01/1.28 1.77/1.87 2.05/2.33 WN WN WN WN WN WN WN WN N03/R08 2.16/2.36 4.43/5.17 2.6/2.89 2.01/2.27 2.38/2.15 1.22/0.97 2.20/1.89 2.48/2.38 WN WN WN WN WN WN WN WN N05/R11 2.59/2.81 4.37/6.82 3.04/3.60 2.28/2.33 2.26/1.75 1.22/0.81 2.16/1.55 2.38/2.11 WN WS (P < 0.05) WN WN WN WS (P < 0.05) WN WN N06/R12 2.94/2.21 4.34/4.26 2.83/2.83 2.56/1.90 2.08/2.25 1.25/1.33 1.97/1.89 2.24/2.57 WN WN WN WN WN WN WN WN N08/R13 3.74/2.61 4.59/5.91 3.67/2.81 3.11/2.35 1.53/2.04 1.68/1.34 1.48/1.73 1.63/2.31 WS (P < 0.05) WN WN WS (P < 0.05) WN WN WN WS (P < 0.05) WN, not sig. WS, sig. Boldface = bloom species. 1966_book.fm Page 215 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC 216 Restoration of Aquatic Systems Table 7.4 Statistical Comparison (independence tests, Chi-square normality tests, variance tests), means tests (pair ed t-test, Wilcoxon signed rank test, and distribution shape tests) of Whole Water and 25-µm Phytoplankton and Zooplankton Data Collected at Stations in the Nassau and Amelia River Estuaries Monthly for 12 Months in 1994–1995 and 1997–1998 (data given for numbers of cells L –1 , species richness, and Shannon–Wiener diversity) A. 1994–1995 Cognate WW Phytoplankton WW Species WW Shannon 25 µm Phytoplankton 25 Species 25 Shannon Station Pair (Numbers L −− −− 1 ) Richness Diversity (Numbers L −− −− 1 ) Richness Diversity R01/N04 137707.5/308265.8 14.2/17.8 1.550/1.508 34340.8/93061.6 32.5/38.0 1.837/1.821 WS (P < 0.01) WS (P < 0.02) WN CV WN WN R03/N04 126539.2/308265.8 15.3/17.8 1.437/1.508 37181.7/93061.6 38.5/38.0 2.023/1.821 WS (P < 0.02) WS (P < 0.05) WN WN WN WN R04/N02 115747.5/238463.3 13.6/16.8 1.494/1.493 36003.3/40900.4 35.1/33.3 2.071/1.901 WS (P < 0.01) WS (P < 0.02) WN WN WN WN R08/N03 169075.8/285895.8 14.3/19.7 1.523/1.509 42883.8/82276.3 36.2/42.1 1.923/1.796 WS (P < 0.05) WS (P < 0.05) WN WS (P < 0.05) WS (P < 0.05) WS (P < 0.05) R10/N01 134003.3/334136.7 15.4/18.9 1.620/1.312 50691.7/96422.1 37.7/42.7 1.953/1.683 WS (p < 0.01) WN WS (p < 0.05) WN WN WN R11/N05 154910.8/340943.3 15.2/17.7 1.527/1.344 44840.83/92260.0 39.1/40.8 2.009/1.762 WN WN WN WN WN WN R12/N06 109955.8/222757.5 14.0/17.1 1.633/1.572 35049.6/77239.2 36.0/37.3 2.081/1.978 WS (P < 0.05) WN WN WN WN WN R12/N07 109955.8/353772.5 14.0/17.4 1.633/1.491 35049.6/74410.0 36.0/34.3 2.081/1.815 CV WN WN WN WN WN R13/N08 107782.5/282419.2 11.9/15.4 1.580/1.434 32555.8/76985.4 33.1/35.8 2.121/1.778 WS (P < 0.05) WS (P < 0.05) WN WS (P < 0.05) WN WN 1966_book.fm Page 216 Friday, June 3, 2005 9:20 AM © 2006 by Taylor & Francis Group, LLC [...]... 0.02) 2. 078 /2.699 WS (P < 0.01) 0 .79 8/1. 074 WS (P < 0.01) 2.028/2 .74 1 WS (P < 0.01) 2.313/2.891 WS (P < 0.01) 1 .72 9/1.699 WN 3.486/4.051 WN 1 .75 3/2.085 WN 1. 570 /1.829 WN 3. 073 /2 .74 7 WN 1. 476 /1.251 WN 3.3 67/ 2.926 WN 3. 471 /2.931 WN R10/N01 2.042/1.605 WS (P < 0.05) 3.940/2.514 WS (P < 0.01) 1.855/1. 473 WN 1 .75 7/1.564 WN 2.458/3. 077 WN 1.295/1.550 WN 2 .70 5/3.451 WN 2 .78 0/3.115 WN R11/N05 1.888/1 .71 8 WN... 0.01) 5. 17/ 7.18 WS (P < 0.01) 0.05/0.05 WN R11/N05 0. 075 /0.061 WN 0.022/0.0 17 WN 0.16/0. 17 WN 0.0 17/ 0.014 WN 0.055/0.0 47 WN 0.95/0.80 WN 5.11/5.09 WN 0. 07/ 0.04 WN R11/N06 0.080/0. 075 WN 0.021/0.018 WN 0.16/0.16 WN 0.0 17/ 0.020 WS (P < 0.02) 0.055/0.058 WN 0.95/1.14 WN 5.11/5 .73 WN 0. 07/ 0.10 WN R12/N 07 0.080/0. 070 WN 0.018/0.015 WN 0.19/0.14 WN 0.0 17/ 0.019 WN 0.051/0. 075 WN 1. 17/ 1.08 WN 4.65/6. 67 WS (P... Evenness R01/N04 9 57, 9 17/ 6 97, 023 WN 20 .7/ 18.0 WN 1 .78 /1 .78 WN 0.60/0.63 WN R03/N04 8 57, 9 17/ 1,020,923 WN 20.6/20.3 WN 1 .79 /1. 87 WN 0.60/0.65 WN R04/N02 601,588 /74 1, 674 WN 23.2/ 17. 0 WN 1.80/1 .73 WN 0.60/0.62 WN R08/N03 921,885/4 47, 310 WS (P < 0.01) 27. 1/21.8 WS (P < 0.02) 2.04/1.94 WN 0.62/0.64 WN R10/N01 681,610/361,193 WS (P < 0.01) 26.4/23.8 WN 2.06/2.05 WN 0.63/0. 67 WN R11/N05 694,165 /78 1,122 WN 23.3/20.4... 4.503/3.518 WN 1.834/1 .70 9 WN 1 .74 7/1.610 WN 2 .79 7/3.101 WN 1.2 37/ 1.585 WN 3.055/3.311 WN 2.956/2.235 WN R11/N06 1.888/1.805 WN 4.503/4.554 WN 1.834/1.846 WN 1 .74 7/1.682 WN 2 .70 7/2 .74 4 WN 1.2 37/ 1.158 WN 3.055/2.940 WN 2.956/2.8 97 WN R12/N 07 2.0 47/ 2.348 WN 5.118/4.908 WN 2.096/2.514 WN 2.086/2.222 WN 2.395/2.119 WN 0.955/10028 WN 2.369/2.120 WN 2.689/2.235 WN R13/N08 2.514/2. 079 WN 5.263/4.5 97 WN 2.695/2.283... 0.893/1. 074 WS (P < 0.02) 1.938/2.263 WN 2.225/2.515 WN Kd-430 Kd-550 Kd-665 R01/N04 2.092/1.634 WS (P < 0.01) 5.430/4.106 WS (P < 0.02) 2. 274 /1.626 WS (P < 0.02) R03/N04 2.306/1 .76 7 WS (P < 0.05) 5. 27/ 4.106 WS (P < 0.02) R04/N02 2.332/1 .76 7 WS (P < 0.01) R08/N03 WN, not sig WS, sig CV = RHO > Critical Value Boldface = bloom species © 2006 by Taylor & Francis Group, LLC Restoration of Aquatic Systems PFD-Eup... R01/N04 2 37, 111/285,219 WN 27. 3/34.8 WS (p < 0.05) 1 .79 8/2.055 WN 72 8.8/ 176 0.5 WS (p < 0.01) R08/N03 249,286/342,5 17 WN 31.3/35.6 WN 2.068/2.060 WN 70 1.3/ 176 0.5 WS (P < 0.05) R11/N05 185,109/ 272 ,78 7 WS (p < 0.01) 28.9/ 37. 1 WS (p < 0.02) 1.953/2.158 WN 4 07. 4/919.9 WS (p < 0.01) R12/N06 139,010/319.956 WS (p < 0.05) 25.2/32.2 WS (P < 0.01) 1.898/1.865 WN 601 .7/ 1860.3 WS (p < 0.01) R13/N08 1,361,296/223 ,79 5... 22.5/26 .7 WN 19.9/21.3 WN 1.46/1.25 WN 47. 76/66.03 WS (P < 0.02) 7. 7/11.5 WS (P < 0.05) R13/N08 33.3/33.9 WN 2.09/1.21 WS (P < 0.02) 0 .78 /0 .75 WN 26.9/38.1 WN 21.5/21.6 WN 1.43/1.29 WN 49.23/53.25 WN 8.01/8.94 WN 225 © 2006 by Taylor & Francis Group, LLC 1966_book.fm Page 225 Friday, June 3, 2005 9:20 AM Cognate Station Pair Sulfite Pulp Mill Restoration A Nassau and Amelia Systems Chapter 7: Table 7. 6... 0.05) 20.9/19.6 WN 1.59/1.14 WS (P < 0.05) 40.3/ 47. 29 WN 7. 36 /7. 83 WN R03/N04 34.3/33.6 WN 1 .78 /0 .79 WS (P < 0.02) 0.84/0.84 WN 24.1/19.4 WS (P < 0.02) 20.9/19.6 WN 1.45/1.14 WS (P < 0.02) 51.48/ 47. 29 WN 8.41 /7. 83 WN R04/N02 34.1/33.2 WN 2.55/1 .75 WS (P < 0.05) 0 .76 /0 .71 WN 28.8/21.6 WS (P < 0.05) 22.9/19.4 WS (P < 0.02) 1.44/1.43 WN 49 .79 /62.04 WN 8 .7/ 10.3 WN R08/N03 34.6/34.3 WN 1.16/0.42 WS (P . 154910.8/340943.3 15.2/ 17. 7 1.5 27/ 1.344 44840.83/92260.0 39.1/40.8 2.009/1 .76 2 WN WN WN WN WN WN R12/N06 109955.8/22 275 7.5 14.0/ 17. 1 1.633/1. 572 35049.6 /77 239.2 36.0/ 37. 3 2.081/1. 978 WS (P < 0.05). WN R12/N 07 109955.8/35 377 2.5 14.0/ 17. 4 1.633/1.491 35049.6 /74 410.0 36.0/34.3 2.081/1.815 CV WN WN WN WN WN R13/N08 1 077 82.5/282419.2 11.9/15.4 1.580/1.434 32555.8 /76 985.4 33.1/35.8 2.121/1 .77 8 WS. Diversity R01/N04 1 377 07. 5/308265.8 14.2/ 17. 8 1.550/1.508 34340.8/93061.6 32.5/38.0 1.8 37/ 1.821 WS (P < 0.01) WS (P < 0.02) WN CV WN WN R03/N04 126539.2/308265.8 15.3/ 17. 8 1.4 37/ 1.508 371 81 .7/ 93061.6