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HomeMy WebLinkAboutCOM 0319.000 1998-2000 o,,r?•.'`.'!y~ Virginia Goldstein Stephen K. Yamashiro Direc;nr . _ rr ,N„~r,r Lff` 1 LU • RLI.~L~V` RussellKolmbun s=;: Depurv Director '99 ~1RY 28 PSI 1 16 ~it1llt~~J II~ ~tI~2ltt CO ~ N OF HAWAII PLANNING DEPARTMENT May 28, 1999 25 Aupuni Street, Room 109 • Hilo, Hawau 967204252 (808) 961.8288 • Fax (808) 961-8742 Ms. Lynn M. Okada Huehue Ranch Associates, L.P. Kings' Shops, Suite B 14 250 Waikoloa Beach Drive Waikoloa, HI 96738 Deaz Ms. Okada: Change of Zone Ordinance No. 88 158 (REZ 609) Special Management Area (SMA) Use Permits Nos. 273 and 311) Applicant: Huehue Ranch Associates, LP Subject: 1997 Water Quality Status Report for Regent Kona Coast TMK: 7~-4: Por. 5 and 6 This is to acknowledge receipt of the 1997 Water Quality Status Report submitted in compliance with Condition P(1) of the above-referenced ordinance, Condition No. 9 of SMA Use Permit No. 273 and Condition No. 15 of SMA Use Permit No. 311. Thank you for your submittal. By copy of this letter, we will forwazd your report to the County Council and the Planning Commission for their information. As a reminder, you are required to comply with all conditions as stated in the above-referenced ordinance and permits within their appropriate timetables. Should you have any questions, please call Phyllis Fujimoto or Susan Gagorik of this office at 961-8288. Sincerely, ,.~IRGINIA GOLDSTEIN Planning Director PF:gP t:~wpwin6oiphylliaVhaahuo 1. plcf Comm. No. ~ / / _ ISIe No. zNG ~'N Ref, To: Ref. Date Y 2 8 ~ Ms. Lynn M. Okada Huehue Ranch Associates, L.P. Page 2 May 28, 1999 c w/ltr: West Hawaii Office P}/anning Commission ounty Council HUEHUE RANCH ASSOCIATES, L.P. Kings' Shops, Sui[e B 14 250 Waikoloa Beach Drive Waikoloa, Hawaii 96738 _ _ - 1 Telephone: (808) 886-6066 ~ ~ ~ - Facsimile: (808) 886-2138 Toll Free Inver-Island: 1-800-201-6066 County of Hawaii Date: February 09, 1999 Planning Department 25 Aupuni Street, Suite #109 Hilo, HI 96720 Attention: Ms. Virginia H. Goldstein, Director U SUBJECT: 1997 Water Quality tatus Report or egent ona oast Gentlemen: We are sending you herewith Under sepazate cover ( ) Item Descrintion 1 -Copy of Regent Kona Coast Water Quality Status Report as prepared by Dr. Richard Brock for the period ending December 1997. This is our regulaz monitoring program conducted by our pond manager, Dr. Richazd Brock, Ph.D., relating to the Anchialine Pond Management and Mitigation Plan as required under Ordinance 88-158 and SMA Use Permit Nos. 273 and 311. These are transmitted as follows: ( For approval ( )For signature ( ) As requested ( V) For review ( )For your use Remarks: Should you have at>,y questions regarding this project, please do not hesitate to contact Mr. Milton Morinaga at (808) 886-6066. Sincerely, HUEHUE RANCH ASSOCIATES, L.P. BY: Lynn M. Okada w: i iam ong, e - o ept. o Health, Safe Drinking Water Branch cc: Michael Wilson, Chairperson-DLNR, Commission on Water Res. Mgmt. cc: Michael T. Lee, Acting Chief-Dept. of the Army, U.S. Army Eng. District, Opns Div. cc: James Leonazd-PBR Hawaii cc: Dr. Richard Brock, Ph.D.-Environmental Assessment Co. (w/o encls.) cc: Milton Morinaga, General Manager-Huehue Ranch Associates, L.P. 0~3~~~~ STATUS OF WATER QUALITY FOR KUKIO, NORTH KONA, HAWAII FOR THE PERIOD ENDING DECEMBER 1997 Prepared For: Huehue Ranch Associates, L.P. King's Shops, Suite B-14 P.O. Box 384359 Waikoloa, Hawaii 96738 By: Richard E. Brock, Ph.D. Environmental Assessment Co. 1820 Kihi Street Honolulu, Hawaii 96821 December 1998 EAC Report No. 98-12 EXECUTIVE SUMMARY In response to the future development of the Kona Coast Regent Hotel and golf course at Kukio, North Kona, a water quality/anchialine pool resource monitoring program was initiated in 1990 and has continued up to the present time. In January 1993 grading for the future golf course was started on this otherwise undisturbed parcel but was halted soon thereafter due to economic difficulties. The program monitors seven coastal observation wells, nine anchialine pool sites and ten marine locations fronting the future development. Because construction terminated in 1993 sampling has been carried out on a biannual to annual basis, usually once during the wet winter season and again during the drier summer season. In years such as 1997 when the wet season was poorly defined, sampling was completed on an annual basis. The results of the monitoring program has shown that the concentration of most inorganic nutrient species has a strong relationship with location; thus nutrient concentrations are higher at more inland sample sites than at more seawazd locations. These inland-seaward (mauka-makai) gradients aze due to the natural occurrence of these nutrients in relatively high concentrations in groundwater and their normally lows oncentrations found in near shore marine waters. As the high nutrient groundwater moves in a seaward direction through the porous lava and anchialine pools, uptake and dilution of these materials occurs thus concentration gradients are present. On entering the ocean, the nutrient concentrations rapidly decline to background levels within 100m of the shore due to dilution, advection and uptake. Since the commencement of this program the concentration of nitrate nitrogen in the observation wells and anchialine pools at Kukio has been among the highest recorded from coastal brackish groundwater anywhere on the West Hawaii coastline. The source(s) of this material are unknown but appear to be completely natural. Other measured inorganic nutrients are well within the usual range encountered elsewhere on the Kona coast. Despite the high nitrate concentrations, there is no evidence of impact to the biota at Kukio. The recorded levels are well below those reported in the literature as being toxic to aquatic organisms. Examination-of the nutrient concentrations of the brackish groundwater at Kukio using a simple hydrographic linear mixing model suggests that there is little allochthonous input (i.e., produced elsewhere and brought into the groundwater system) of these nutrients to the coastal groundwater. The mixing model data demonstrate that some uptake and/or denitrification of nitrate occurring in the anchialine pools at Kukio. State water quality standazds apply to the marine waters at Kukio because there aze no criteria for anchialine pools. With respect to compliance with state standards, the marine waters at Kukio have exceeded the "dry coastline standazds on every survey since the commencement of this study for nitrate and ammonia nitrogen. Total nitrogen exceeded the standazds on 11 of 16 surveys since 1990; chlorophyll-a has exceeded the standazds on 14 of 16 surveys and total phosphorus has exceeded the standards on 3 of 16 surveys. In general the highest values for nitrate and total nitrogen are found at the marine stations with the lowest salinities which are all adjacent to the shoreline. These dissolved nutrients occur naturally in high concentration in groundwater. The percolation of high nutrient groundwater into the sea serves as stimulus for the growth of phytoplankton which is measured here as chlorophyll-a thus explaining the lack of compliance to standards with this parameter. Examination of marine water quality samples from many other coastal areas with little or no coastal development reveals that often these waters like those at Kukio do not meet state standazds. Usually groundwater inputs account for the lack of compliance which suggests that human imposed standards may not be realistic for many undisturbed coastal sites like Kukio. Did the golf course grading undertaken in early 1993 or more recently, the construction of the Four Seasons Hotel and golf coursejust north of Kukio have an impact on the water quality or biota of the Kukio anchialine system? In marine samples only ammonia nitrogen has increased significantly (from a baseline mean = 9.27 ug/I to apost-baseline mean of 11.77 ug/I). Significant declines in nitrate nitrogen, total nitrogen, chlorophyll-a, salinity, temperature and pH have occurred in the same period. If the changes to water quality are from anthropogenic activities on land (i. e., development of hotels, infrastructure or golf courses), then the brackish groundwater in the anchialine pools and coastal wells should manifest problems first. Accordingly, a statistical analysis of water quality data from the anchialine pools and coastal monitoring wells has found that silica concentrations and measured turbidities have increased significantly since the preliminary golf course grading was done in 1993. Ho~yever, the increases in silica are well within the normal ranges encountered in coastal groundwater and the increases in turbidity are due to more difficulty in sampling shallow mud-bottom pools that are rapidly undergoing senescence (i.e., in filling) at Kukio due to the rampant growth of vegetation. Recently this study has encountered an increase in the concentration of dissolved organic nitrogen (or DON) as measured in anchialine pools and coastal wells at the Kukio parcel. DON is the result of biological activity (decomposition and/or metabolism) and in high concentrations along with other parameters may be indicative of sewage pollution. However, other than high DON, other parameters appear to be normal strongly supporting the view that the source of the DON is not sewage. The increase in DON at Kukio may be due to as yet unidentified natural biological activity in the anchialine pools at the study site. The data to date support the contention that the small amount of grading occurring in early 1993 as well as the crxnpletion of the Four Seasons Hotel and golf course to the north of the Kukio parcel two years ago have not impacted the quality of the waters in anchialine pools, coastal monitoring wells or in the ocean fronting the Kukio project site. Furthermore, statistical analyses of the biological data from the anchialine pools at Kukio show that there have been no statistically significant changes over the 84-month period of this study. INTRODUCTION Purpose With any coastal development there exists the potential for impacts to occur to resident aquatic biota. These may be duect impacts, such as those that occur during coastal construction or they may be more indirect resulting from gradual, long-term disturbances, as may occur with non-point source discharges causing gradual and chronic impacts to the aquatic community. Short-term impacts and potential mitigation measures are often addressed in detail through the EIS process, however, the long-term impacts can be overlooked. The regulatory agencies recognize the potential for long-term negative impacts to aquatic communities resulting from coastal development and have instituted requirements to developers to prepare and conduct environmental monitoring and mitigation programs aimed at adverting these potential environmental perturbations. As part of the pemut process for the development of the Kona Regent at Kunio, North Kona, Huehue Ranch Associates, L.P. commenced on such a program in August 1990. This document summarizes the findings of this program from its inception through December 1997. Strategy Potential environmental degradation processes may be minimized if the proper information is assembled early on in any coastal development scheme. Environmental data can serve to identify areas that may be susceptible to anthropogenic impacts, or conversely, particularly resistant to such perturbations. The first step in the protection of environmental quality is to (1) develop an approved environmental monitoring and mitigation plan and (2) to carry out a quantitative baseline assessment against which later measurements of change can be made. The approved environmental monitoring and mitigation plan has been developed for the coastal and near shore marine resources at Kukio and serves as the guiding framework for environmental studies at this site. The preconsuuction environmental baseline data for the Kukio site span the period from August 1990 through December 1992. Golf course construction (i.e., leveling of barren lava mauka of the aquatic features at Kukio) commenced in January 1993 but was halted soon therea@er due to economic difficulties. The situation remains unchanged today (December 1998) with some barren lava inland or mauka of the anchialine pools at Kukio having been leveled but most of the terrain of this parcel remains in a natural state. Because some change was initiated, this document reports on the characteristics of water quality at Kukio since the short period of construction activity and comparatively analyzes these data to the two-year baseline. I An objective of any environmental baseline assessment is to establish quantitative information to accurately depict the community structure of the extant aquatic communities as well as describe the physio-chemical environment. The quantitative description of the physio-chemical environment provides the baseline upon which subsequent monitoring can be compared; significant deviation from the baseline may serve as an "early warning" of impact to the aquatic community. Alteration in the physio-chemical environment may cause a change in aquatic communities. If the changes in physio-chemical inputs are not too great, a potential for chronic, low-level disturbance can result in adjacent aquatic communities. In the operation of a coastal development, chronic disturbance may come from the irrigation and upkeep of golf courses and associated grounds. A golf course is planned for the Kona Regent Resort inland of the anchialine pools situated along the coast. In West Hawaii, golf courses are irrigated by a combination of brackish groundwater and treated resort sewage effiuent. With golf course development, a nutrient subsidy from fertilizers and sewage as well as inputs from pesticides could leach or migrate downwazd to the groundwater table and move laterally in the low salinity watertable towards the shoreline. Because of their inland location, anchialine pools would probably be the first point of chemical detection and manifestation'oflmpacts to aquatic biota. Ongoing studies at Waikoloa (a developed site about 12 miles north along the coast from Kukio) suggest that in monitoring chemical parameters, changes aze first and most evident in anchialine pools; changes in water chemistry are much less obvious in the marine environment (Brock et al. 1987). Thus far despite changes in water chemistry, no quantifiable changes have been noted in the anchialine communities at Waikoloa (Brock and Kam 1992). Thus an appropriate strategy in monitoring for chronic, low-level impact in aquatic communities following baseline assessments is to focus first on change in chemical parameters in ground- and near shore marine waters. If statistically significant changes are noted, a search for quantitative change in adjacent anchialine and marine communities should be made. If discernible impacts are evident, the approved mitigation plan should be effected to alleviate impacts. The quantitative baseline for the marine communities offshore of the Kukio parcel was completed in 1991 (Brock 1991 a) and the management and mitigation plan for the anchialine resources on the project site was also completed in 1991 (Brock 1991b). Baseline monitoring of water quality in both the anchialine pools and near shore marine environment span the period from August 1990 - December 1992; subsequent data presented here have been collected since the preliminary grading that occurred in 1993 for the future golf course. METHODS Initially, water quality parameters were measured at 18 sites. At present 26 locations are routinely monitored. The reasons for the increase in the number of sample sites has been a recognition in the field of the need for additional information as well as the fact that in July 1991 six small coastal wells were drilled to provide additional sample points. The locations of all the sample sites are presented in Figure 1. Presently seven samples are from wells, 9 from anchialine pools and 10 from near shore 2 FIGURE 1. Outline map of Kukio Bay and coastal anchialine pools showing the approximate locations of 2Ti water quality sampling sites sampled commencing in August 1990. Stations aze located in anchialine pools, brackish water observation wells and in the neaz shore waters of Uluweoweo Bay. Note that station 1 in the northern part of the project site was dropped because of heavy vegetation and natural in filling hampering sample collection. The shoreline is stippled. Approximate scale: finch = 60m. 3 1 ~ ~ ? , . ~ 4 - ~ ~ 23 ~ 5 b • ~o ~q •'a.. ' • 25 a 10 0 22 p p ULUWEOWEO BAY .t,' 1 26 s'- 3 IS 1 21 16 ~ 27 17 f=t. . .w .i i , a~ . KIKAUA POINT ~':<<~;~ :i~ I K marine waters. Other than marine bottom samples or wells, all samples aze collected just under the water's surface (within the upper 20cm of the water column). Water quality constituents that aze evaluated include the specific criteria as designated for open coastal waters in Chapter 11-54, Section 06 (Open Coastal Waters) of the State of Hawaii, Department of Health Water Quality Standards. These criteria include ammonia nitrogen (NH,), nitrate + nitrite nitrogen (NO, + NOZ, hereafter referred to as nitrate or NO,), total nitrogen (TN), total phosphorus (TP), chlorophyll-a (chl-a), turbidity, as well as the nonspecific criteria of temperature, pH, and salinity. In addition, orthophosphate phosphorus (PO,) is measured because of its biological importance as well as silica (Si) due to its usefulness as a conservative groundwater tracer. Dissolved organic nitrogen (DON) is calculated as the difference between total nitrogen and dissolved inorganic nitrogen and dissolved organic phosphorus (DOP) is calculated as the difference between total phosphorus and orthophosphorus. Water samples were collected try opening one liter polyethylene bottles at the desired depth. These bottles were all triple rinsed using the sample water prior to sample collection. Subsamples for nutrient analyses were filtered through glass fiber filters and immediately placed in 125m1 acid-washed, triple rinsed polyethylene bottles and stored on ice until returned to Honolulu for later analysis. Arfalyses for ammonia nitrogen, orthophosphate and nitrate are performed using a Technicon autoanalyzer following standard methods for seawater analysis (Strickland and Pazsons 1968, Grasshoff 1983). Total nitrogen and total phosphorus are similazly analyzed following digestion (Standard Methods 1985). Turbidity samples are collected as unfiltered water and stored on ice in 125m1 polyethylene bottles until measurements aze made. Turbidity is measured on a Monitek Model 21 Nephalometer following procedures as described in Standard Methods (1985). Chlorophyll-a samples are collected by filtering known volumes of sample water through glass microfiber filters; filters are stored frozen in dark containers until analysis. Pigments aze extracted in 90 percent acetone in the dark for 12 to 24 hours and fluorscensce before and after acidification is measured on a Turner Designs fluorometer. Salinity samples are collected in triple rinsed 125m1 polyethylene bottles and are analyzed on a AGE Model 2100 laboratory salinometer with precision of 0.0001%. hr-situ field measurements of temperature, oxygen and pH are made using a YSI Mode158 oxygen meter, ahand-held thermometer and a Hanna Portable Microprocessor pH/mV meter (No. IP-67) equipped with a Sensorex probe. All methods used in the Kukio program comply to and follow those as outlined in the "West Hawaii Coastal Monitoring Program Monitoring Protocol Guidelines" as formulated and prepared by the West Hawaii Coastal Monitoring Task Force (May 1992, 30p.). Statistical and other data procedures are described where used in the text. In general to avoid the assumptions of normality in the data, non-parametric methods were used (Siegel 1956, SAS Institute, Inc. 1985). 5 RESULTS AND DISCUSSION This program commenced on 14 August 1990 with the sampling of 18 sites at Kukio. Since that initial effort, baseline sampling was carried out on 22 April 1991, 16 May 1991, 15-16 July 1991, 26 November 1991, 28 July 1992, 30 September 1992 and on 27 December 1992. Note that sampling was curtailed between November 1991 and July 1992 because construction schedules were unknown. Golf course construction was initiated in January 1993 with the leveling of some barren lava mauka (inland) of the anchialine pool system at Kukio. This construction effort continued at a low level until May 1993 when the activity was essentially halted. Field sampling in this "during construction" phase was carried out on 3 Mazch, 12 May, and 6 December 1993. Because construction had terminated, field work became a biannual effort with sampling occurring once during the dry season and again during the wet season. In yeazs when rainfall was light and the wet season poorly defined, sampling occurred once during the dry period only. Under this latter effort, sampling was completed on 23 September 1994 (dry period), on 11 October 1995 (dry period), 4 January 1996 (wet period), 1 October 1996 (dry period), 6 December 1996 (wet period) and 30 September 1997 (dry period). This report presents the results of the most recent (September 1997) survey and summarizes the status of coastal water quality at Kukio for that year. The 14 August 1990 sampling effort collected water samples from 9 anchialine pools and 9 ocean sites fronting the Kukio project azea (stations 1 through 18 as shown in Figure 1). The second survey was carried out on 16 May 1991 and sampled the same 18 sites plus a new shoreline station (site 19) as well as a small newly discovered anchialine pool well inland from the beach (site 20, see Figure 1). The third survey on 15-16 July 1991 sampled these same sites as well as the six newly drilled coastal observation wells (sites 21 through 26, see Figure 1). Site 26 was not sampled on the July 1991 survey because there of a problem with a lock securing the well. The same 26 sites were again sampled on 26 November 1991 as well as on the subsequent survey carried out on 28 July 1992. In the July 1992 survey a new well site (site 27) was added to the list of routine sampling locations. This well was constructed as a source of brackish water that was pumped to a small tank for use by visiting Huehue Ranch personnel. As of 28 July 1992 site 1 was eliminated from the routine sample effort because it had become completely overgrown and choked by California grass, Indian pluchea and Christmas berry. The vegetation not only made obtaining the water sample difficult, but it caused an in filling of the pond such that there was insufficient water present through most of the tide cycle for sampling. Prior to that date, this site was regularly sampled at high tide when water was present. Sample site 2 is only about 20m seaward from site 1 thus probably provides sufficient sampling coverage for the immediate area. Since construction commenced in January 1993, the program routinely samples 26 sites; 9 are anchialine pools, 7 are coastal brackish water wells and 10 are near shore marine locations. Sample site 19 (Figure 1) is a tidepool that falls either into the marine samples if sampled during mid to high tide or with the anchialine pooUlow salinity samples as has occurred on four occasions: May 1991, July 1992, 3 March 1993 and 30 September 1997. Station 19 is a groundwater "spring" that lies subtidally in the ocean through most of the tidal cycle. When first observed in November 6 1990 this "spring" was an obvious welling up of water in the ocean (at high tide). On the morning of the 16 May 1991 survey, the tide was very low (-0.4 foot) and the "single source spring" could not be located. Rather in the general vicinity of where it had been was a "tidepool" (about 4m2 in surface azea) above the low water mark with groundwater entering the pool from five or six sources. This "tidepool" has become the sample point and since it was above sealevel at that time (i.e.,low tide) and contained very low salinity water (5.50°/00), this sample was placed with the anchialine pools. This occurred again on the July 1992, March 1993 and September 1997 surveys and site 19 was placed with the anchialine pools. With higher tides, site 19 is awash from the surf and the samples aze higher salinity (i.e., above 30°/00) and thus aze more representative of a coastal marine setting; hence when tides are high site 19 samples are classed with the marine or ocean samples as has occurred on all other sample dates. A third site that requires some explanation is site 10. The August 1990 survey established site 10 in a shallow marshy anchialine pool that contained water only at intermediate and high tides. This site was cleared of the thick canopy of trees overgrowing it and in the interim between the August 1990 and May 1991 surveys, became completely overgrown and choked by a variety of sedges, grasses as well as pickleweed probably in response to the increased light levels. The thick growth of vegetation made sampling at this site difficult so in May 1991 station 10 was moved about lOm to the north fi'bm the old site (in the middle of the marsh pool) to a small (surface azea about 1.25m~ "cave pond" situated in pahoehoe. Subsequently, the overgrown marsh pool (old location for station 10) was excavated with the vegetation and mud being removed to restore this anchialine pool. The restoration was completed prior to the 28 July 1992 sample period and at that time station 10 was moved back to the original location of the original marsh area (i.e., in the newly restored pool) but biological monitoring continues in the small adjacent "cave pool" (see biological results below). Site 10 is the pond used in a recent collaborative study on exotic fish removal with the U.S. Fish and Wildlife Service and Huehue Ranch Associates, L.P. Thus because of the heavy growth of vegetation at station 1, 26 sites have been routinely sampled since July 1991. As noted above, the field effort now includes 7 wells, 9 anchialine pools and 10 ocean sites. The geometric means by date for the preconstructionbase1ine period (7 surveys -August 1990 through December 1992) are presented in Table 1. Table 2 lists the geometric means by date from the period since construction was initiated (9 periods - 3 March 1993 through 30 September 1997). Table 3 presents the data from the most recent (30 September 1997) survey; complete data from previous surveys is available in earlier Kukio reports. Inspection of these tables show that the geometric means for all water quality parameters measured since the commencement of construction all similar to the concentrations found in the baseline data (comparison of Tables 1 and 2). However, the geometric means for nitrate nitrogen appear to be increasing through time (see below). One interesting fact through all of the sample periods is the relatively high concentration of nitrate at Kukio. Studies by Brock and Kam (1990, 1992) in both developed and completely natural sites suggest that the nutrient chemistry of West Hawaii coastal groundwater is highly variable and concentrations are frequently in excess of biological needs, i.e., more than 40-60uM (560 to 840 ug/1; Brock et al. 1988). Mean inorganic 7 TABLE 1. Summary of the geometric means presented in ug/l (in the body of the table) for DOH water quality criteria from 165 samples collected on 7 occasions between August 1990 and December 1992 which comprise the preliminary baseline dataset at Kukio. Marine samples (on first page) are sepazated for other water sources (anchialine pools and coastal brackish water observation wells) that aze presented on the second page. Underlined values exceed state standards for open coastal (marine) waters for "dry" conditions. Note that there are no applicable standards for anchialine pools. DATE NO, Iv'H, TN PO, TP Si DON DOP MARINE SAMPLES Dec 92 11.06 3 36 ~ 76 5.58 13.33 263.76 108.08 7.44 Sept 92 14.28 5 74 158..62 5.58 12.09 316.40 121.66 5.89 July 92 ~2 4_0 51$ 1ZZ,~4 5.58 17.05 521.08 102.77 9.30 Nov 91 $,54 ~ 116.20 4.65 10.85 229.60 79.24 4.65 July 91 17.36 7 00 71 7.38 6.20 13.95 480.76 102.20 5.58 May 91 2$ 48 7~6 1,.2~Z 6.51 13.64 442.96 94.50 5.27 Aug 90 $ 5_4 ~ 4 0 4.34 11.47 355.04 80.92 6.82 Oxygen Temp NTU Chl-a S°/oo % Sat. (°C) pH Dec 92 0.12 0.361 34.080 103 26.0 8.12 Sept 92 0.09 0.220 33.689 103 27.7 8.12 July 92 0.14 0 4 31.90 103 27.1 8.10 Nov 91 0.13 0.270 33.77 102 26.5 8.22 July 91 0.17 0.350 31.81 102 25.4 8.17 May 91 0.13 0.290 32.45 102 25.0 8.13 Aug 90 0.1'7 0 260 34.30 101 28.7 8.04 8 TABLE 1. Continued. DATE NO3 NH, TN PO4 TP Si DON DOP ANCHIALINE POOL AND WELL SAMPLES Dec 92 1640.10 6.72 2037.7 87.42 93.93 26516.3 49.42 3.41 Sept 92 1577.52 6.02 2050.3 81.53 87.11 24680.9 54.46 3.41 July 92 1574.16 6.02 2068.8 87.11 92.38 25178.7 115.78 1.86 Nov 91 1450.12 3.64 2000.5 93.62 94.55 23332.7 30.10 0.93 July 91 1899.10 8.82 1988.7 89.90 92.07 23315.9 49.98 1.55 May 91* 1330.00 15.12 2105.3 81.53 97.03 24747.8 54.88 3.10 Aug 90* 2048.76 15.12 2133.2 95.17 101.68 25161.6 49.56 2.79 Oxygen Temp NTU Chl-a S°/oo % Sat. (°C) pH Dec 92 0.21 0.155 3.680 85 22.5 7:85 Sept 92 0.12 0.108 3.766 78 23.3 7.87 July 92 0.23 0.168 3.78 84 24.4 7.95 Nov 91 0.15 0.081 3.74 80 22.5 7.89 July 91 0.25 0.14 3.46 97 23.8 7.99 May 91 * 0.18 0.09 3.44 100 24.3 8.02 Aug 90* 0.31, 0.21 3.25 100 25.6 7.79 *NOTE: No wells sampled in August 1990 or May 1991. 9 TABLE 2. Summary of the geometric means presented in ug/1(in the body of the table) for DOH water quality criteria from 234 samples collected on 9 occasions (3 Mazch, 12 May, 6 December 1993, 23 September 1994, 11 October 1995, 4 January 1996, 1 October, 6 December 1996 and 30 September 1997) that have been collected since the short period of preliminary golf course grading in 1993 at Kukio. Data are presented by sample date. Marine samples are sepazated for other water sources (anchialine pools and coastal brackish water observation wells). Underlined values exceed state standards for open coastal (marine) waters for "dry" conditions. Note that there are no applicable standards for anchialine pools. Table continued on the next page. DATE NO3 NHQ TN PO, TP Si DON DOP MARINE SAMPLES ' Mar93 29.68 S,Q4 1~4 44 5.27 13.64 716.24 99.68 8.37 May93 14.56 4 06 88.20 3.72 9.30 331.52 69.58 5.58 Dec93 ~ 6 72 102.76 2.79 10.85 215.60 90.02 8.06 Sep94 ~ ~ 89.34 2.46 7.53 225.62 71.27 4.31 Oct95 15.36 2 4 105.89 7.11 11.23 334.65 48.98 2.27 Jan96 26.88 18 157.08 9.30 19.22 620.76 76.21 9.14 Oct96 23.97 99.28 8.39 30.89 117.56 53.96 20.54 Dec96 30.23 4 04 134.37 5.63 11.51 621.46 100.10 5.88 Sep97 53.47 21.54 211.17 3.93 10.92 710.36 117.97 6.48 Oxygen Temp NTU Chl-a S°/oo % Sat. (°C) pH Mar93 0.11 0.134 33.452 102 24.7 8.15 May93 0.17 0.151 33.560 103 26.4 8.14 Dec93 ~ 0.160 34.368 102 25.9 8.10 Sep94 ~ 0.176 34.074 103 26.8 8.02 Oct95 0.12 0.301 33.492 104 26.6 8.09 Jan96 0.18 0.157 31.835 102 24.9 8.08 Oct96 0.12 0.094 30.660 103 27.5 8.16 Dec96 0.10 0.198 33.633 103 25.6 8.15 Set97 0.12 0.298 32.110 101 26.9 8.03 10 TABLE 2. Continued. DATE NO, NH, TN PO, TP Si DON DOP ANCHIALINE POOL AND WELL SAMPLES May93 1350.30 9.10 1602.44 72.85 79.36 14325 243.04 6.51 May93 1321.74 4.34 1558.34 77.19 83.70 25499 232.26 6.51 Dec93 1455.30 6.30 1800.54 89.28 91.45 23255 338.94 2.17 Sep94 955.32 2.99 1305.54 68.35 73.44 31531 28.55 3.10 Oct95 2015.53 19.39 2396.02 80.16 89.71 30813 109.40 2.09 Jan96 1670.97 14.04 2311.71 93.64 102.62 36573 50.29 3.93 Oct96 1700.07 5.17 2396.30 82.07 99.72 33584 304.35 10.15 Dec96 1849.32 5.49 2293.65 84.04 97.70 36113 458.84 13.66 Sep97 811.97 18.48 2007.99 55.29 68.11 23364 852.89 10.01 Oxygen Temp NTU Chl-a S°/oo % Sat. (°C) pH May93 0.26 0.149 4.276 89 22.4 7.99 May93 0.34 0.146 3.897 86 23.9 7.98 Dec93 0.45 0.132 3.518 84 23.1 7.93 Sep94 0.41 0.076 3.580 78 23.8 7.86 Oct95 0.35 0.339 3.853 79 23.6 7.94 Jan96 0.39 0.173 3.790 82 21.4 7.81 Oct96 0.22 0.053 3.186 83 24.0 7.97 Dec96 0.16 0.227 3.583 91 22.5 7.99 Sep97 0.17 0.525 3.630 83 23.6 7.87 11 TABLE 3. Summary of the water quality parameters as measured at 26 sites in the study area on 30 September 1997. Sixteen samples from anchialine pools and observation wells aze presented first followed by ten ocean samples. Ocean samples are divided into surface ("S") or bottom ("B") samples. In the body of the table aze given the concentrations of dissolved nutrients in ug/I unless otherwise noted. For ocean samples the underlined geometric means exceed Department of Health water quality standards for "Dry" conditions. There are no standazds for anchialine waters. Table continued on next page. ND =below detection limits. Station NO, NH3 TN PO, TP Si DON DOP ANCHIALINE POOL/LOW SALRVITY SAMPLES 1 Not Sampled 2 1777.30 32.34 2044.70 80.91 96.41 28539.28 235.06 15.50 7 1514.66 92.54 1807.68 59.21 73.47 29039.92 200.48 14.26 8 1502.76 230.44 1949.92 120.59 130.82 29290.52 216.72 10.23 9 1443.12 15.12 3158.68 63.24 79.67 28038.36 1700.44 16.43 10 1108.94 64.54 2566.06 70.99 83.08 25033.68 1392.58 12.09 11 1419.18 23.66 3303.78 88.97 96.41 24532.76 1860.94 7.44 12 1025.36 19.32 2352.84 27.59 34.10 23781.52 1308.16 6.51 13 201.88 53.90 741.16 9.92 20.77 23030.28 485.38 10.85 19 237.58 25.90 640.04 17.67 30.69 5593.00 376.56 13.02 20 1204.42 8.68 2684.64 57.35 65.41 28539.28 1471.54 8.06 OBSERVATION WELLS 21 1156.68 4.34 2613.52 96.52 105.40 19524.68 1452.50 8.88 22 1431.08 4.34 3206.00 90.83 99.82 25284.00 1770.58 8.99 23 1562.40 2.10 3585.26 57.35 75.64 23030.28 2020.76 18.29 24 1108.94 4.34 2518.74 104.78 117.18 27537.72 1405.46 12.40 25 1371.44 4.34 3324.58 33.48- 41.23 26535.88 1948.80 7.75 26 10.92 142.10 338.24 104.78 110.36 25784.92 185.22 5.58 27 1240.12 8.68 2850.54 35.65 40.90 23531.20 1601.74 5.27 OCEAN SAMPLES 3-S 174.72 32.34 327.46 13.95 20.15 2406.04 120.40 6.20 4-S 32.62 21.56 146.58 4.03 11.47 334.60 92.40 7.44 5-S 14.14 17.22 125.02 1.86 7.13 177.52 93.66 5.27 6-B 9.80 17.22 118.44 1.86 7.44 113.96 91.42 5.58 14-5 20832 28.00 359.80 5.89 13.64 2838.64 123.48 7.75 15-5 83.58 17.22 234.92 4.03 10.85 1029.00 134.12 6.82 16-5 70.56 17.22 170.24 1.86 6.51 835.52 82.46 4.65 17-B 11.90 10.78 105.56 1.86 7.75 182.00 82.88 5.89 18-5 309.26 53.90 773.50 13.95 24.18 6367.20 410.34 10.23 Geometric Means 53.47 21.54 211.17 3.93 10.92 710.36 117.97 6.48 12 TABLE 3. Continued. Oxygen Temp NTU Chl-a S°/oo % Sat. (°C) pH ANCHIALINE POOL/LOW SALRIITY SAMPLES 1 Not Sampled -Outside of Property 2 0.15 0.173 2.781 97 22.6 7.73 7 0.67 0.928 2.619 101 22.8 7.63 8 1.18 0.981 2.656 100 23.1 7.51 9 0.07 0.102 2.811 102 22.8 7.70 10 0.16 I.O50 3.583 103 23.9 7.91 11 0.08 0.059 3.618 101 23.6 8.33 IZ 0.30 0.699 3.724 101 24.5 8.19 13 0.52 2.055 3'.933 102 24.6 7.84 19 0.15 0.681 27.165 96 25.7 7.86 20 0.10 0.018 2.581 100 22.2 8.00 OBSERVATION WELLS 21 0.23 2.841 87 23.5 8.10 22 0.06 3.551 87 23.1 7.99 23 0.27 2.085 87 23.2 7.82 24 0.08 2.372 87 23.5 7.76 25 0.13 2.948 81 23.3 7.96 26 0.17 7.489 9 25.8 7.45 27 0.06 4.138 94 24.0 8.14 OCEAN SAMPLES 3-S 0.11 0.428 31.585 102 26.3 7.91 4-S 0.07 0.252 33.916 lUl 26.4 8.00 5-S 0.07 0.236 34.078 103 26.2 8.01 6-B 0.12 0.173 34.144 101 26.3 8.04 14-S 0.20 0.900 30.228 100 27.3 8.05 15-5 0.07 0.221 33.064 103 27.3 8.07 16-5 0.0'8 0.170 33.290 102 27.3 8.06 17-B 0.05 0.275 34.099 101 27.3 8.11 18-S 1.07 0.455 25.657 101 27.4 8.04 Geometric Means 0.12 0.298 32.110 102 26.9 8.03 * Chlorophyll-~ is not measured in well samples. 13 nutrient concentrations from anchialine pools and coastal brackish.water irrigation wells aze similar to the concentrations found in Kona coast drinking water (Brock and Kam 1992). Reported natural groundwater nutrient levels in other localities maybe Beater. Johannes (1980) reported groundwater nitrate levels between 115 to 380uM (1,610-5,320 ug/t) from Perth, Australia, and Mazsh (1977) noted nitrate concentrations in Agana, Guam groundwater of 178uM (2,492 ug/1). Gradients Because the "during construction" data aze similaz to the information collected over the three-year baseline, the data are first collectively examined below to point out generalities in groundwater chemistry at Kukio. In general samples may be considered in two natural groups that aze related to salinity. Samples from the seven well sites and nine anchialine pools provide information on the quality of the groundwater as it moves through the coastal study site towazds the sea, mixing with intruding seawater neaz the shoreline. The marine samples provide information on the fate of groundwater and its constituents as it enters the ocean. Groundwater is usually relatively high in the concentration of silica, nitrate and orthophosphate relative to seawater where these nutrients occur in low concentrations. Water quality data from the Kukio project site spans the period from August 1990 through September 1997. Plotting the arithematic means for nitrate and orthophosphate against distance from the shoreline from specific sites that lie approximately in ainland-seaward (mauka-makai) line demonstrates the nature of the concentration gradient (Figures 2 and 3). Thus biologically important inorganic nutrients such as nitrate and phosphate occur at relatively high concentrations in the groundwater and anchialine pools at Kukio. The adjacent ocean waters are low in these nutrients, thus dilution, uptake and advection of these constituents occurs as the groundwater moves towards the shoreline and into the sea. Since there has been little meaningful change in these concentration of these nutrients through time other than for dissolved organic nitrogen (see below), our hypothesis is that the relatively high concentrations of these components is completely natural. As in many other locations sampled along the West Hawaii coast, there has been cattle grazing for many years occurring several miles inland of the Kukio anchialine system. However, none of the sampling to date at Kukio or elsewhere suggests that cattle grazing has been responsible for the nitrate concentrations encountered at Kukio. Inspection of the geometric means for dissolved organic nitrogen (DON) in marine samples (Tables 1 and 2) suggests that there has been little change through the period of this study. However, examination of anchialine pool and observation well DON geometric means in Tables 1, 2 and 3 suggest little change in DON until the December 1996 sample period when DON values began increasing; this increase appears to continue unabated in the September 1997 survey of anchialine pools and wells. Sewage and animal wastes are often a source of DON that, if present, result in high concentrations (up to 100uM or 1400 ug/1) relative to other waters. Dissolved organic nitrogen is 14 3000 Station 22 (Well) 2500 Station 11 (Pond) rn Z 2000 ~ Station 12 (Pond) O ~ 1500 Z W 1000 H Z Station 13 (Pond) 500 Station 15 (Ocean) Station 16 (Ocean) Station 14 (Shoreline) 0 -200 -100 0 100 200 300 DISTANCE (m) FIGURE 2. Mean nitrate nitrogen (ug/1) values from seven routine sampling locations at Kukio that aze approximately in a line from an inland location out into the ocean plotted against distance from shore (see Figure 1). Data span the period from August 1990 through September 1997. 15 100 Station 22 (Well) 80 m Station 11 (Pond) W Q 60 Station 12 (Pond) d N O a ao 0 a' ° za Station 13 (Pond) Station 15 (Ocean) Station 16 (Ocean) Station 14 (Shoreline) 0 -200 -100 0 100 200 300 DISTANCE (m) FIGURE 3. Mean orthophosphate values (ug/l) from seven routine sampling locations at Kukio that aze approximately in a line from an inland location out into the ocean plotted against distance from shore (see Figure 1). Data span the period from August 1990 through September 1997. 16 present in surface seawater at concentrations between 5 to 10 uM (70 to 140 ug/1) and it usually occurs in low concentration (0-SuM or to -70 ug/I) in groundwater. Thus DON can potentially be used as a tracer of sewage particularly at locations that sample groundwater. Other probable sources ofDON in aquatic systems is from the decomposition of organic matter in low oxygen environments. However if the source of DON is from sewage, other nutrients (ammonia and/or nitrate nitrogen as well as silica) should likewise be elevated. This is not the case in these data. Besides high DON, human sewage will have a high concentration of ammonia (-1,400 to ug/1) or in an oxidizing setting (i.e., exposure to air), will convert to nitrate nitrogen (--2,100 ug/1) which then should be elevated along with a concurrently high silica concentration (-36,000 to 46,000 ug/1). In this case, the low ammonia values (mean -26 ugfl, Table 5) and a decrease in mean nitrate concentrations since the baseline period (Table 5) suggests that sewage or animal wastes have not been the source of the high nitrate concentrations at Kukio particulazly in light of the fact that the elevation of DON is a relatively recent phenomenon. The relatively high nitrate nitrogen concentrations seen at Kukio are considered to be completely natural and the recent rise in DON remains unexplained. Dissolved organic nitrogen.is showing similaz recent increases in the two most southem anchialine pools sampled in the Four Seasons Hotel water quality monitoring prograzn (Dr. S. Dollar, personal communication). The Four Seasons Hotel is on the pazcel just north of the Kukio project site and these pools are probably no more than 100 to 200m north of our sample site 2. It is interesting to note that the Four Seasons Hotel sample sites north of the two southern anchialine pools show no elevation of DON suggesting that the increase is centered close to the northern boundary of the Kukio pazcel. It should be noted that in the last two years with the completion of the Four Seasons Hotel, many more people use the beach at Kukio. The public right-of--way developed by the Four Seasons Hotel is just along the northern boundary for the Kukio parcel. We have encountered evidence of human use of the area under the kiawe trees adjacent to some of the anchialine pools as evidenced by trash, etc. With the development to the north has also come an increase in use of the Kukio azea by wild donkeys. These donkeys travel daily to the coastline under the cover of darkness to obtain brackish water from the anchialine pools and move mauka (inland and uphill) before sunup to graze. Prior to the hotel and golf course development at Kaupulehu, these donkeys would spread out along the coastline. Following the development, the donkeys appear to avoid the developed azeas and are more common in thenndeveloped Kukio pazcel. Although the water chemistry data do not support it, both the humans and donkeys could contribute to the increases seen in DON. Consistently through all sample periods of this study, one site (station 26, observation well) has shown an elevation of ammonia, a low concentration of nitrate, and very low dissolved oxygen concentrations (see Table 3) which suggests a problem at that site. The well is located in a compacted sandy berm planted with coconut trees separating the makai (ocean) side of a large anchialine pool (site 13) and the ocean (site 14). Water samples from this well always smell of hydrogen sulfide suggesting very poor movement of water through the berm and a reducing environ- ment which lacks dissolved oxygen. It is probable that the low nitrate concentrations are due to uptake by the surrounding coconut trees and high ammonia nitrogen (mean = 141 ug/1) is due to 17 decomposition of organic matter as well as possible conversion of nitrate to ammonia in a low oxygen envircrunent, not to other sources. Hydrographic Miaing Model Analysis A chazacteristic feature of West Hawaii is its diffuse groundwater discharge at the shoreline (Cox et al. 1969). This discharge is the result of the island's geologically young laves; estimates of this dischazge range from less than 1 to more than 4 million gallons per day per mile of coastline (U.S. Army Corps of Engineers 1985). The high porosity of these young laves will not support water contained above sea level near the shoreline (Cox et al. 1969), resulting in a system where groundwater moves rapidly through the lava towards the sea and seawater readily intrudes. Anchialine pools aze defined as brackish water land-locked pools that show tidal rhythms thus they are restricted to depressions in the lava that extend down and intersect with the watertable. The chazacteristic mixohaline water is the result of seawazd flowing groundwater interfacing and mixing with warmer, more saline waters intruding from below. Because seawater is typically very low in inorganic nutrients and groundwater usually shows some elevation of these components, gradienu of nutrient concentrations might be expected as groundwater moves towards the sea. A simple dilution model has been proposed to explain these gradients (Officer 1979, Smith and Allinson 1993). In its simplest form, the model plots the concentration of a dissolved chemical species as a function of salinity or other conservative tracers. Comparison of the curves produced by such plots with conservative mixing lines provides an indication of the origin and fate of the material in question. The dilution model is based on the premise that mixing two waters with differing compositions will yield straight lines on two-dimensional plots (see Smith et al. 1987, Dollar and Smith 1988). Straight line plots will result if the differing waters are composed of conservative (i.e., non-reactive) constituents and if the waters aze not physically impeded (i.e., that the lava fields adjacent to the shore have high porosity). Both salinity and silicate are conservative and the resulting plot of these two species is roughly linear (Figure 4). The conservative mixing line is constructed for each nutrient by connecting the endpoint concentrations of open ocean water and uncontaminated groundwater from sources inland of any anthropogenic inputs. Deviation from the straight line implies an additional source or sink of material, or the presence of some physical bamer to movement. Dissolved silica represents a check on the model as this material occurs in high concentration in groundwater but is low in seawater and in developed azeas is not a major component of fertilizer. Silica is used by some organisms (diatoms and sponges principally) but is not otherwise rapidly assimilated by biological activity in near shore waters. Thus a plot of silica against salinity (Figure 4) shows the data points fall reasonably close to the theoretical conservative (linear) mixing line suggesting that the mixing model and the assumptions used in developing it aze an reasonably accurate reflection of the system under study. The lineaz relationship of the salinity/silicate plot (Figure 4) also suggests that the lava . field through which the water flows at Kukio does not materially impede the flow of water either towards the land or sea. The plots of salinity (conservative) against nitrate (Figure 5) and orthophosphate (Figure 6) show 18 50000 • BASELINE DATA o PRESENT DATA 40000 ~ 30000 Q ~ • ~ U O J 20000 ~ O O 10000 O O 0 0 5 10 15 20 25 30 35 SALINITY (o/oo) FIGURE 4. Plot of the mean silica concentrations (ug/1) against salinity. These data aze from 27 sample sites at Kukio and Uluweoweo Bay. The baseline data (from August 1990 through December 1992, n=167) are shown as dark circles; the period from initial golf course grading (in 1993) to present aze shown as open circles (n=234). Also given is the conservative mixing line; these data demonstrate the conservative nature of silica in the system. 19 4000 O • BASELINE DATA 00 O PRESENT DATA p7 3000 Z W O ~ 2000 Z W O f- 1000 ~ ~ Z , • 9 O O O O• aO 0 0 5 10 15 20 25 30 35 SALINITY (o/oo) FIGURE 5. Plot of the mean nitrate concentrations (ug/1) against salinity. These data aze from 27 sample sites at Kukio and Uluweoweo Bay. The baseline data (from August 1990 through December 1992, n=167) are shown as dark circles; the period from initial golf course grading (in 1993) to present are shown as open circles (n=234). Also shown is the conservative mining line; points below the line suggest a "sink" (uptake or denitrification) in the system. 20 250 • BASELINE DATA O O PRESENT DATA 200 m W O Q 150 ~ 2 O b 4. O O O O ~ d 100 00 O O 0 O ~ • 50 O O ~ ~ O O 0 0 5 10 15 20 25 30 35 SALINITY (o/oo) FIGURE 6. Plot of the mean orthophosphate concentrations (ug/1) against salinity. These data aze from 27 sample sites at Kukio and Uluweoweo Bay. The baseline data (from August 1990 through December 1992, n=167) aze shown as darkened circles; the period from initial golf course grading (in 1993) to present aze shown as open circles (n=234). Also shown is the conservative mixing line; points below the line suggest uptake of this biologically important nutrient as the groundwater moves through the anchialine pools in the system. 21 that most points are either on the conservative mixing line or below this line. Points below the line suggest that some uptake is occurring (and/or in the case of nitrate, denitrification) as the high nutrient groundwater passes through the anchialine pond system. Phosphorus (as orthophosphate) is a common component of groundwater on the West Hawaii coast. The plot of orthophosphate concentration with salinity shows a small number of points above the conservative mixing line (Figure 6). The source(s) of this orthophosphate are unknown but orthophosphate values at Makalawena, North Kona (several miles south of Kukio) where there has been no development for many miles in any direction have higher orthophosphate values than found at Kukio (Brock and Kam 1992). These high values appear to be a natural part of the West Hawaii coastal groundwater. Ammonia nitrogen or ammonium is the other form of dissolved inorganic nitrogen. Ammonium shows no relationship with the conservative mixing line (Figure 7). This is not unexpected in that the concentration of ammonium is about the same in both the inland groundwater and near shore marine water which results in a line with little or no slope. The lack of correlation in the concentration of ammonia nitrogen with salinity with many points falling above the conservative mixing line suggests in situ generation of this nutrient at Kukio. Ammonia nitrogen may be produced by. biological activity. The production is probably occurring in the anchialine pools and marine waters which is not unexpected considering the biota of the ponds and diversity of organisms in Uluweoweo Bay. Compliance With Department of Health Criteria The Hawaii State Department of Health has developed specific criteria for different classes of water in the state (e.g., as for harbors, streams and marine waters). The waters fronting Kukio are classed as "open coastal waters" and are to remain in their natural pristine state with an absolute minimum of pollution or alteration of water quality from any human-caused source or action" (Hawaii Administrative Rules, Chapter 11-54-01). The most stringent standards have been set for open coastal waters. There aze no standazds set for anchialine pools or coastal brackish wells for imgation purposes, thus the water samples collected at Kukio maybe considered in two groups: ocean samples and "other" samples that include all other sites away from the ocean. The standards are presented in Table 4 (in ugll). The standazds are established on the basis of the volume of local freshwater input either as surface runoff or as groundwater. "Dry" conditions in the standards are defined as those coastal waters that receive less than three million gallons of freshwater discharge per day per shoreline mile and "wet" coastlines are those with greater input. To our knowledge there are no estimates of groundwater efflux to the ocean at Kukio. At Waikoloa early estimates (Kanehiro 1977) placed the groundwater efflux in the range of 0.97 to 3.97 million gallons of groundwater discharge per day per mile of shoreline. Recent estimates are higher; presently the groundwater discharge in the Waikoloa area is estimated to be in the range of 6 million gallons per day per shoreline mile (Mr. T. Nance, hydrologist, personal communication). The groundwater discharge at Kukio is probably similar to that at Waikoloa. However, since it is unknown, we assume that the more stringent "Dry" standazds apply to the marine samples. 22 zoo ~ BASELINE DATA O PRESENT DATA m w 0 H O F- Z O ~ 0 • ~ B ~ O Z 'O ~ ~ 00 ~ • • Q ~O O O ~ O 8 ~O m O O ~ O O O O UJ ~ O 0 0 5 10 15 20 25 30 35 SALINITY (o/oo) FIGURE 7. Plot of the mean ammonia nitrogen concentrations (ug/I) against salinity. These data are from 27 sample sites at Kukio and Uluweoweo Bay. The baseline data (from August 1990 through December 1992, n=167) are shown as dark cucles; the period from initial golf course grading (in 1993) to present aze shown as open circles (n=234). Also shown is the conservative mixing line; the spread of points suggests no positive relationship of ammonia nitrogen with salinity. Because groundwater and ocean water have ammonia nitrogen at similar concentrations, a "flat" mixing line results. 23 TABLE 4. Specific criteria specified by the Department of Health water quality standazds for open coastal waters as amended in 1988. Nutrient standards are presented in ug/l. Geometric Not to exceed mean not to the given value Not to exceed the more than 10% exceed the Parameter given value of the time given value Total Nitrogen 150.00* 250.00* 350.00* (ug/1) 110.00** 180.00** 250.00** Ammonia Nitrogen 3.50* 8.50* 15.00* (ug/1) 2.00** 5.00** 9.00** Nitrate+Nitrite 5.00* 14.00* 25.00* (ug/1) 3.50** 10.00** 20.00** Total Phosphorus 20.00* 40.00* 60.00* (ug/1) 16.00** 30.00** 45.00** Chlorophyll-a 0.30* 0.90* 1.75* (ug/1) 0.15** 0.50** 1.00** Turbidity (NTi~ 0.50* 1.25* 2.00* 0.20** 0.50** L00** * "Wet" criteria apply when the open coastal waters receive more than three million gallons per day of fresh water discharge per shoreline mile. "Dry" criteria apply when the open coastal waters receive less than three million gallons per day of fresh water discharge per shoreline mile. Applicable to both "Wet" and "Dry" conditions: Salinity -Shall not vary more than 10 percent from natural or seasonal changes considering hydrologic input and oceanographic factors. Orthophosphate was eliminated from the list of requirements in the revised 1988 document but because of its biological importance, it was measured in this study. The old "Wet" criteria was 7.00 ug/I and the "Dry" standard was 5.00 ug/I. 24 The Department of Health "Dry" standazds were exceeded for nitrate nitrogen, ammonia nitrogen, total ~utrogen and chlorophyll-a (Table 1) on every survey of the preconstruaion baseline. The geometric means for nitrate exceeded the "not to exceed 10 percent of the time" on all baseline surveys except for August 1990 and similarly ammonia nitrogen geometric means exceeded the "not to exceed 10 percent of the time" on all surveys except for the August 1990 and December 1992 field efforts. Since the initial golf course grading activity in 1993, nitrate and ammonia nitrogen have continued to exceed "dry" standazds on every survey; in the March 1993, January, December 1996 and September 1997 surveys, total nitrogen also exceeded the "dry" standazd. Similazly chlorophyll-a concentrations exceeded state "dry" standazds in seven of the nine surveys of this period and turbidity concentrations exceeded these standazds in the December 1993 and September 1994 surveys due to surf (see Table 2). In genera] the highest values for nitrate and total nitrogen are found at the marine stations with the lowest salinities and these sites are all adjacent to the shoreline. As previously noted, groundwater is high in nitrate and total nitrogen; simple mixing of this groundwater with seawater can account for the lack of compliance in these data. The conservative mixing line in the plot of nitrate versus salinity (Figure 5) is an estimate of the simple mixing of uncontaminated (high nitrate) groundwater with ocean water. Extrapolation of these data suggest that at salinities of less than about 34.0°/ob the measured concentration of nitrate will exceed the standards. Fully 39% of the marine samples in this study had salinities below 34.0°/00. Nitrate is the lazgest component of total nitrogen which probably explains the lack of compliance in this pazameter. The relatively high measured chlorophyll-a values aze probably a response of phytoplankton to the inorganic nutrient input via groundwater. The response of phytoplankton is not instantaneous, thus the measurement of high chlorophyll-a does not often drrectly coincide with nutrient source(s) particulazly where local currents may rapidly move and mix incoming high nutrient water. Sampling stations with consistently high chlorophyll~r measurements include station 18 at the head of the small partially enclosed bay at the southern end of the project site and three shoreline stations in Uluweoweo Bay (stations 3, 14 and 19). Offshore stations have lower measured chlorophyll-a suggesting that circulation along the shoreline is probably not as well developed as it is further offshore. Examination o~marine water quality samples from many coastal areas with little or no hinterland development (South Kohala, North Kona, South Kona, Lanai, etc,) reveals that often the waters do not meet the state standazds for open coastal waters. As noted above, groundwater inputs may easily account for the lack of compliance. In some localities such as the West Hawaii coast, the standards represent criteria imposed on a natural system that may never be in compliance. This suggests that some revision of the state standards should be considered. This suggestion was made by the West Hawaii Coastal Monitoring Task Force and the Department of Health responded by funding a recently completed study by the author and others at the University of Hawaii to determine if new criteria are warranted. The results suggests that new ecologically-based standard would be appropriate and the Department of Health has proposed new ecologically-based standards specific to the West Hawaii coast. These proposed standazds are undergoing review. Additionally, the 25 Department of Health funded this author to conduct a study to examine the sources of ammonium and to' determine if an ecologically-based standard maybe appropriate. Thus some of the problems with the present standazds may be resolved in the future. Impact of Construction on Water Quality The question maybe asked "Has the quality of the ground and near shore marine waters changed significantly at Kukio since the limited grading activity in the January to May 1993 period?" A second related question is "Has the quality of the ground and near shore waters changed significantly due to the recent completion of the Four Seasons Hotel and golf course just north of the Kukio parcel?" If changes aze related from activities inland of the anchialine pool system at Kukio (i.e., the azea graded for the golf course) or to the activities occurring to the north, the greatest opportunity for observation of these changes would be at sample sites in closest proximity to the possible points of input (here the most inland and northerly sample sites). Plotting the measured concentration of nitrate and orthophosphate at these inland sample sites through the course of the study should provide some insight; if there are increases in a parameter through time, it suggests that input is occurring. Figure 8 presents a plot of the nitrate concentrations as measured at the five most inland and northerly sample points (sites 2, 20, 22, 23 and 24) since the inception of the sampling program in 1990. Figure 9 presents the orthophosphate concentrations as measured at these same locations over the period of this study. Also included in both plots are the fitted regression lines. The fitted regression line for nitrate nitrogen shows a slight decrease (slope = -0.05, r-0.08, n=68) however, the low correlation coefficient (r--0.08) suggests that the lineaz model provides a poor fit to the data. In the case of orthophosphate, the fit of the line to the points is similazly poor (r=0.22) and the slope of the line is also slightly negative (slope = -0.006). Neither slope differs significantly from zero which means that the decreases are not significant for either nutrient species at these inland and northerly sample sites at Kukio through the August 1990 -September 1997 period. However, the use of regression analysis to address the question of change does not provide a cleaz picture because the wide spread of the data points and the resulting poor fit of the regression lines. A second approach to the question of change in the water quality is to statistically analyze the data. Results of the non-pazametric Kruskal-Wallis analysis of variance (SAS Institute 1985, but see also Siegel 1956, Sokal and Rohlf 1981) comparatively analyzing samples collected during the baseline (August 1990 -December 1992) to samples taken subsequently (January 1993 to present) are presented in Table 5. This table also presents the arithematic means for each pazameter in the baseline and subsequent periods. Significant changes have occurred in comparing the grand means for some parameters between the August 1990 -December 1992 period to that from January 1993 to present (Table 5). With marine samples, statistically significant decreases have occurred for nitrate and total nitrogen, chlorophyll-a, salinity, temperature and pH in comparing these two time periods. The only statisti- cally significant increase in marine sample parameters occurred with the concentration of ammonia nitrogen (from 9.27 ug/l to 11.70 ug/l). All other statistically significant changes were decreases in 26 4000 3500 • • • • • p~ 3000 • • • • • • • • • • W 2500 e~ • • • • • • ~ • • • • • ~ 2000 • • • • • • • ~j • • • • • 1500 • • ~ 1000 Z 500 0 AUG AUG AUG AUG AUG AUG AUG AUG AUG 1990 1991 1992 1993 1994 1995 1996 1997 1998 DATE FIGURE 8. Scatter plot of measured nitrate nitrogen concentrations at five inland and northerly sample sites at Kukio from August 1990 through September 1997. The sample sites are nos. 2, 20, 22, 23, 24 as shown in Figure 1. Also given is the fitted regression line (Y = 2511.76 - 0.05X, n=68, r=0.08, not significant). The slightly negative slope of the fitted regression line suggests a small nonsignificant decrease in nitrate has occurred over this time period. 27 1ao 1so • 1ao • • • • • t • • ~ ~ w 1zo • • j ~ • • = 100 • ~ • • • O 80 • j•• • : • a O 60 • H O 40 20 0 AUG AUG AUG AUG AUG AUG AUG AUG AUG 1990 1991 1992 1993 1994 1995 1996 1997 1998 DATE FIGURE 9. Scatter plot of measured orthophosphorus concentrations at five inland and northerly sample sites at Ku}do from August 1990 through September 1997. The sample sites are nos. 2, 20, 22, 23, 24 as shown in Figure 1. Also given is the fitted regression line (Y = 118.73 - 0.006X, n=68, r=0.22, not significant). The slope of the fitted regression line is slightly negative suggesting that there has been a slight decrease in the concentration of orthophosphorus at these sites over the course of this study. 28 TABLE 5. Table summarizing the grand arithematic means (in the body of the table) from the baseline dataset (spanning August 1990 -December 1992) and from the period subsequent to this (to present) which includes the short period of preliminary golf course grading in 1993 at Kukio. Also given are the results of the Kruskal-Wallis ANOVA. Means aze given in the body of the table and aze in ug/l unless otherwise noted. Sample sizes aze: marine baseline n=67, marine subsequent period n=88; anchialine pool and observation well baseline n=100, anchialine pool and observation well subsequent period n=146. MEANS ANOVA Significant PARAMETER Baseline Subsequent Period Results Change? MARINE SAMPLES Nitrate N 89.65 58.16 P>0.02 YES Nitrate N has declined significantly since the baseline period Ammonia N 9.27 11.77 P>0.01 YES Ammonia N has increased significantly since the baseline period Total N 192.75 150.50 P>0.02 YES Total N has significantly declined since the baseline period Ortho P 7.89 6.44 P>0.75 No Total P 14.54 14.86 P>0.72 No Silica 1329.17 916.19 P>0.42 No Turbidity (NTT 0.18 0.17 P>0.06 No Chl-a 0.528 0.212 P>0.03 YES Chlorophy_]1-a has significantly declined since the baseline period Salinity (°/oo) 33.283 32.991 P>0.0001 YES Salinity has significantly declined since the baseline period Oxygen % Sat. 102.3 102.5 P>0.16 No Temp °C 26.6 26.1 P>0.05 YES Temperature has significantly declined since the baseline period pH 8.13 8.10 P>0.02 YES pH has significantly decreased since the baseline period 29 TABLE 5. Continued. MEANS ANOVA Significant PARAMETER Baseline Subsequent Period Results Change? ANCHIALINE POOL AND OBSERVATION WELL SAMPLES Nitrate N 2135.83 2014.76 P>0.20 No Ammonia N 14.66 27.69 P>0.79 No Total N 2227.09 2327.01 P>0.17 No Ortho P 96.05 91.38 P>0.27 No Total P 99.47 98.24 P>0.81 No Silica 24738.94 29215.64 P>0.0001 YES Silica concentration has increased significantly since the baseline period Turbidity (NTU) 0.29 0.56 P>0.007 YES Turbidity has significantly increased since the baseline period Chl-a 0.417 0.424 P>0.22 No Salinity (°/oo) 3.827 4.238 P>0.28 No Oxygen % Sat. 92.7 88.8 P>0.54 No Temp °C ~ 23.7 23.2 P>0.14 No pH 7.91 7.93 P>0.31 No 30 the measured concentrations of the parameters comparing the baseline to the post-baseline period. The Kruskal-Wallis ANOVA carried out on the grand means of parameters from the anchialine pools and observation wells in two periods (i.e., baseline from August 1990 through December 1992 to the later period from January 1993 to present) noted only two statistically significant changes (Table 5). The statistically significant increases between these two periods were for silica (from 24,738 ug/l to 29,215 ug/1) and for turbidity (from 0.29 NTU to 0.56 NTU). In groundwater silica is usually in the range from 18,200 to 33,600 ug~l (650-1,200 uM); the changes seen in silica aze well within the usual range encountered in anchialine pools and shallow coastal wells along the West Hawaii coast. Significantly higher silica values may be related to changes (albeit nonsignificant) in salinity. As noted above, high silica concentrations are found in ground (fresh) water so with lower salinities, higher silica concentrations would be expected. The increases in turbidity are probably related to sample collection more than anything else. Over the last 3.5 years there has been little human activity in the area around the Kukio anchialine ponds. Prior to that, there was an active program of brush and tree clearing mound the pools. This activity has allowed more sunlight to reach the ground and since the clearing program ended, the under story has rapidly grown back often covering many of the shallower pools. This has made sample collection at all but the highest of tides difficult since most of the Kukio anchialine pools are quite shallow through most of the tidal cycle. Thus under th2 present conditions as samples are collected, the soft bottom substratum is often stirred up which results in higher turbidity readings. The statistically significant changes between the baseline and period since preliminary grading for the golf course in 1993 encountered in the Kukio data have no relationship to the small amount of construction that occurred on the project site. At this point in time, there is no evidence in the water quality data to suggest that increases in any parameters are occurring due to the development and operation of the Four Seasons Hotel and golf course to the north of the Kukio project site. Biological Monitoring Among the prominent coastal resources at Kukio are a number of anchialine pools. Anchialine pools are landlocked bodies of water that may be characterized as not having surface connections to the sea, yet have measurable salinities and display damped tidal fluctuations. Naturally occurring anchialine pools are restricted to highly porous substrates such as recent lavas or limestone adjacent to the sea. These unique habitats have been described from a number of widely dispersed tropical localities; anchialine pools are most numerous at sites in Fiji, the Ryukyus and Hawaii. Most of the known anchialine resources occur along the West Hawaii (I{ona) shoreline and have in recent yeazs been the focus of attention with respect to coastal development. Anchialine pools harbor a distinctive assemblage of organisms, some of which are found nowhere else. Anchialine pond organisms fall into two classes, i.e., epigeal and hypogeal species. The epigeal fauna is comprised of species that require the well-illuminated (sunlit) part of the anchialine system. Most of these species are found in other Hawaiian habitats albeit individuals from anchialine systems 31 frequently show ecotype (morphologic) variations. The hypogeal organisms occur not only in the illuminated part of the system but also in the interconnected watertable below. These species are primarily decapod crustaceans, some of which are known only from the anchialine biotope. Species characteristic of Hawaiian anchialine pools include crustaceans (shrimps and amphipods), fishes, mollusks, a hydroid, sponges, polychaetes, tunicates, aquatic insects, algae and aquatic macrophytes. Most striking are a number of red-pigmented caridean shrimp species and the most abundant of these is the opae'ula or Halocaridina rubra. Anchialine resources at Kukio are located in the low-lying coastal plain fronting much of the project site. Early studies at Kukio focused on the major complex of pools situated in the southern part of the site; these have been set aside ut a 4.4 acre preserve. Pools to the north are situated under a heavy canopy of kiawe and until 1991-92, the brush restricted access. About 30 pools are in the area north of the 4.4 acre preserve. There have been a number of inventories commencing in 1972 that sampled parts of the Kukio system (Maciolek and Brock 1974) but it was not until the recent surveys that the more northern anchialine pools were sampled (Brock 1991c). In recent years the biota in the southern pools has changed with the introduction of topminnows which has effectively precluded a number of native species formerly present in the system. Pools to the north have the usual complement of native species. With the decline of anchialine resources due to the recent spread of exotic fishes on the Kona coast, the approximately 30 pools in the northern part of the site have a greater biological importance (see Brock 1991c for a discussion of this). The West Hawaii Coastal Monitoring Task Force Monitoring Guidelines (1992) suggests that because of its ubiquitous distribution in anchialine systems, the red shrimp Halocaridina rubra should be the most important species in the quantitative monitoring of anchialine pools. Accordingly, this program monitors the abundance of these shrimp at five locations where they occur at Kukio. The sampling of the biota is done using 0. lmZ quadrats placed in the pools and counts of shrimp within quadrats is made. A minimum of four quadrats are placed in each of the sampled pools where sufficient substratum is present as not to have quadrats overlap. Other less common motile species aze enumerated by making a visual census of the entire pool. No emphasis was placed on quantifying non-native species such as topminnows or poecilids. At present four of the anchialine pools of nine sites routinely sampled contain the complement usual native species (opae'ula). (The remaining five pools have been colonized by exotic fishes that prey on native crustaceans). The results of these censuses are presented in Table 6 and are separated by date. In some cases our activities have encouraged the development of the native fauna at a particular site; for example, this occurred at site 20. Initially the water surface area of pond at site 20 was small (about 100cmZ at high tide). In July 1991 we removed some of the loose rock to assist in the water sampling increasing the pool surface area to more than 900cmZ. With this increase in surface area appeared Halocaridina rubra thus on the following survey (November 1991) censuses of this species began at that location. Station 9 is a small anchialine pool that was cleared of loose 32 TABLE 6. Summary of the aquatic fauna censuses carried out in the anchialine pools sampled on 7 occasions during the baseline sampling (August 1990-December 1992) and subsequently on nine occasions during and since the preliminary golf course grading in 1993. In the body of the table are presented the means from counts made in O.ImZ quadrats. "TL" indicates that the tide was too low to allow censusing. Whole pond counts are shown with an asterisk. Table continued on next two pages. Pond Species Aug90 May91 Ju191 Nov91 Ju192 Sep92 1 H. nrbra 86 10 47 13 overgrown same 2 H.rubra 95 115 109 37 119 97 M.lohena 1 4 2 1 7 H.rubra 90 149 144 56 161 204 M.lohena 3 7 4 3 14 7 Red Amphipoda 13 18 37 13 17 14 8 H. rubra 295 TL TL 62 360 29 M.lohena 17 3 2 9 no aquatic same same same same fauna M. grandimanus 1 10 H. rubra 3 M.lohena 18 M. grandimanus 2* 3* 3* 2* Awaous genivattitus 1 guppies not same counted 11 guppies not same same same same same counted 12 guppies not same same .same same same counted 13 guppies not same same same same same ' counted 20 no aquatic same same fauna H.rubra 9** 7 6 **Note during the July 1991 survey, we cleared some of the stones blocking access to the water . of this small pool allowing sunlight to reach the water. This has probably served as a stimulus for the colonization of the pool by H. rubra. 33 TABLE 6. Continued. Dec Maz May Dec Sep Oct Jan Pond Species 92 93 93 93 94 95 96 i H. rubra overgrown same same same same same same 2 H.rubra 127 94 83 69 35 200 79 M.lohena 2 1 1 3 1 5 8 7 H.rubra 197 118 118 95 125 180 139 M.lohena 12 2 1 15 15 19 15 Red Amphipoda 22 34 12 14 37 2 27 8 H.rubra 79 95 128 136 75 114 120 M.lohena 2 1 0 22 3 18 14 Red'Amphipoda 0 23 29 17 27 0 38 9 no aquatic same same same same same same fauna 10 M. grandimmrus 2* 1 * 1 * 1 * 0 2* 1 Awaous genivattitus 1* 1* 0 1* 0 0 1* guppies not counted same same same same 11 guppies not counted same same same same same same 12 guppies not counted same same same same same same 13 guppies not counted same same same same same same 20 H.rubra 6 25 12 5 21 16 21 34 TABLE 6. Continued. Oct Dec Sep Pond Species 96 96 97 1 H. rubra overgrown same same 2 H.rubra 132 195 122 M.lohena 4 3 3 Red Amphipoda 7 7 H.rubra 104 99 200 M.lohena 14 6 Z Red Amphipoda 26 19 28 8 H.rubra 94 125 147 M.lohena 12 12 9 Red Amphipoda 4 14 16 9 no aquatic fauna seen M. grandimanus 2 , 10 M.grandimanus 2* 1* 1* Awaous genivattttus guppies not counted same same 11 guppies not counted same same 12 guppies not counted same same 13 guppies not counted same same 20 H.rubra 26 40 19 35 rock in July 1991. This pool was badly overgrown with Indian pluchea (Pluchea odorata) in the July 1992 sample period which was removed at that time. During the December 1992 survey, the Indian pluchea was again cleazed from this pool and we have continued these activities to keep this pond free of vegetation on every survey since that time. Other than sighting of the native prawn or opae'o'eha'a (Macrobrachium grarufima~rus) encountered in November 1991 and again in December 1996, there have been no aquatic species seen in this small pond. The newly restored anchialine pool at sample site 10 has been in existence since May 1992. This pool was dug by hand by clearing vegetation, sand, debris and mud at the site of a badly degraded anchialine pool. The loose material was removed down to pahoehoe bedrock and a dry stacked rock wall laid along the makai side to prevent sand from filling the pool. Within about three weeks the pond had been heavily colonized by Halocaridina rubra (personal observations by Mr. Dustin Crimmins). By the 28 July 1992 survey guppies were in the pond and no K rubra were present. The mechanism of colonization by the guppies is not known. During the construction of the pond a suction pump was used to remove 'silt at the bottom of the pond. Since the natural replacement of water was slow, a second pump was used to supply water to the pond under construction from a pool to the south that probably contained fish; this may have been the source of guppies in the new pool. )n the September 1992 survey, site 10 had large schools of guppies and numerous dragonfly nymphs. The alga, Cladophora sp. has become well established. In 1994 a cooperative venture between the developer, U. S. Fish and Wildlife Service and myself was undertaken to remove the vegetation and unwanted exotic fishes in an attempt to restore this pond. The guppies were eradicated and Halocaridina rubra quickly returned to the pool for several weeks but subsequently disappeared. Guppies re-established themselves in the pool and H. rubra is not present and the pond is once again badly overgrown by vegetation. Because of the exotic fishes, biological sampling for site 10 has continued in the small adjacent "cave pond" that still has native crustaceans present. Anon-parametric analysis of variance (Kruskal-Wallis ANOVA; SAS Institute 1985, but see also Siegel 1956, Sokal and Rohlf 1981) of the mean number of Halocaridina rubra at the anchialine pools where this species occurs (Table 6) showed that there has been no statistically significant change in abundance of this shrimp species over the period from August 1990 through September 1997 (d.f.=15, P>0.80, not significant). Similarly, use of the Student-Newman-Keuls test shows no statistically sigrLficant differences in the number of shrimp over this 84-month period of observation. These data suggest that the population of red shrimp in the sampled anchialine pools at Kukio has remained stable over the period of this study. Concern has been voiced over impacts to native waterbirds with the development of the Regent Kona Coast Resort. As part of the monitoring program, a census of native waterbirds was tamed out during each site visit. No waterbirds were present during the August 1990 visit, two Hawaiian stilt were present in the middle of the southern complex on 16 May, I S July and 16 July 1991. On 18 April and again on 22 April 1991 two stilt were present in approximately the same location. These two birds appear to be present during most visits to the southern pool complex; however on 30 July 1991 there were four stilt present. Visiting the site on 18 October 1991 we noted five stilt present in the middle of the southern complex. On the 26 November 1991 survey we again noted five stilt 36 present in the southern complex and in the 28 July 1992 sample effort there were three stilt and one night crowned heron present in the southern anchialine pond complex. In the 30 September and 27 December 1992 surveys there were no waterbirds present. In 1993 three surveys were carried out at Kukio; the 3 Mazch 1993 survey noted no stilt present, the 12 May 1993 sample effort found 2 stilt present and the 6 December 1993 survey encountered 2 stilt at Kukio. In September 1994 four stih were present and in October 1994 there was one night crowned heron in the area. All sampling since that time has resulted in no Hawaiian stilts encountered at the Kukio ponds. The fluctuation in the number of waterbirds maybe related to disturbance or the lack of it occurring at other known bird habitats (such as Aimakapa'a or Opae'ula) along the West Hawaii coast; when disturbance is low at the primary habitat the birds probably do not remain at Kukio but rather return to their usual habitat. LITERATURE CITED Brock, R.E. (Environmental Assessment Co.). 1991a. Baseline studies of the marine biota of Uluweoweo Bay, Kukio, North Kona, Hawaii. Prepazed for Huehue Ranch Associates, L.P., 75-5722 Kuakini Highway, Suite 107, Kailua-Kona, Hawaii 96740. EAC Report No. 91-07. 32p. Brock, RE. (Environmental Assessment Co.). 1991b. Anchialine pond management and mitigation plan and marine life and water quality management and mitigation plan for the Regent Kona Coast Resort, Kukio, North Kona, Hawaii. Prepazed for Huehue Ranch Associates, L.P., 75-5722 Kuakini Highway, Suite 107, Kailua-Kona, Hawaii 96740. EAC Report No. 91-08. 43p. Brock, RE. (Environmental Assessment Co.). 1991c. AnchiaGne pond management and mitigation plan, marine life and water quality management and mitigation plan for the Regent Kona Coast Resort, Kukio, North Kona, Hawaii. Prepared for Huehue Ranch Associates, I.P., 75-5722 Kuakini Highway, Suite 107, Kailua-Kona, Hawaii 96740. EAC Rept No. 91-08. 35p. Brock, RE., J.E. Noms, D.A Ziemann and M.T. Lee. 1988. Characteristics of water quality in the anchialine ponds of the Kona, Hawaii coast. Pacif. Sci. 41:200-208. Brock, RE. and AK.H. Kam. 1990. Waikoloa pond program annual report. 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