Monitoring Cruise at the Central Long Island Sound Disposal Site September 1995 Disposal Area Monitoring System DAMOS a eae oe oF DA;|M O §$ DISPOSAL AREA MONITORING SYSTEM Contribution 118 November 1997 US Army Corps of Engineers» New England District 1c O &hSb900 TOEO O WCQ 1OHM/18lNi REPORT DOCUMENTATION PAGE SSS en *ublic reporting concern for the collection of information is estimated to average 1 hour per response including the time for reviewing instructions, earching existing data sources, gathering and measuring the data needed and correcting and reviewing the collection of information. Send comments egarding this burden estimate or any other aspect of this collection of information including suggestions for reducing this burden to Washington Jeadquarters Services, Directorate for information Observations and Records, 1215 Jefferson Davis Highway, Suite 1204, Arlington VA 22202-4302 |and to the Office of Management and Support, Paperwork Reduction Project (0704-0188), Washington, D.C. 20503. |. AGENCY USE ONLY (LEAVE BLANK) — |2. REPORT DATE 3. REPORT TYPE AND DATES COVERED November 1997 FINAL REPORT {. TITLE AND SUBTITLE 5. FUNDING NUMBERS MONITORING CRUISE AT THE CENTRAL LONG ISLAND SOUND DISPOSAL SITE, SEPTEMBER 1995 5. AUTHOR(S) JOPHN T. MORRIS 8. PERFORMIGORGANIZATION REPORT NUMBER SAIC No. 373 7, PERFORMING ORGANIZATION NAME(S) AND ADDRESS(ES) Science Applications International Corporation 221 Third Street Newport, RI 02840 ), SPONSORING/MONITORING AGENCY NAME(S) AND ADDRESS(ES) US Army Corps of Engineers-New England Division 424 Trapelo Road Waltham, MA 02254-9149 11. SUPPLEMENTARY NOTES Available from DAMOS Program Manager, Regulatory Division USACE-NED, 424 Trapelo Road, Waltham, MA 02254-9149 10. SPONSORING/MONITORING AGENCY REPORT NUMBER DAMOS Contribution #118 12a. DISTRIBUTION/AVAILABILITY STATEMENT 12b. DISTRIBUTION CODE Approved for public release; distribution unlimited 13. ABSTRACT Science Applications International Corporation (SAIC) conducted a monitoring survey at the Central Long Island Sound Disposal Site (CLIS) from 27 August to 1 September 1995 as part of the Disposal Area Monitoring System (DAMOS) Program. The field operations were concentrated over the New Haven 1993 (NHAV 93), CLIS 1994 (CLIS 94), and Field Verification Program (FVP) mounds and consisted of precision bathymetric surveys, Remote Ecological Monitoring of the Seafloor (REMOTS®) sediment-profile photography, and geotechnical coring. These surveying techniques were employed to monitor the stability, cap thicknesses, consolidation rates, and benthic recolonization of the NHAV 93, CLIS 94, and FVP mounds. The NHAV 93 mound was developed during the 1993/94 disposal season as part of a large scale confined aquatic disposal (CAD) project. SAIC has conducted a total of seven bathymetric, four REMOTS® sediment-profiling, and five geotechnical coring surveys over the NHAV 93 mound since September 1993. The comprehensive time-series data set documents the formation of the mound within the containment cell as well as its gradual consolidation and benthic recolonization. The results of the September 1995 field effort indicate a moderate amount of consolidation (0.25 m) over the majority of NHAV 93 with several pockets of 0.5 m consolidation near the center of the mound. The heterogeneity of the material collected in the five-member geotechnical coring data set makes tracking a single sediment horizon throughout the project difficult. However, indicators such as shell fragments, gravel, and detritus were useful in differentiating ambient, historic, UDM, and CDM sediment strata. REMOTS® sediment profile-photography found the biota occupying the surface sediments of the NHAV 93 mound to be recovering as anticipated. A seasonal reduction in dissolved oxygen within the central Long Island Sound region appeared to be responsible for shallow redox potential discontinuity (RPD) depths over the NHAV 93 mound as well as the CLIS reference areas. As a result, lower than expected organism-sediment index (OSI) values were found near the center and extreme southern and eastern stations despite the presence of Stage III organisms at eleven of thirteen stations over the NHAV 93 mound. In September 1994, a disposal buoy marked “CDA” was deployed at 41°09.343' N, 72°53.099' W by SAIC to the northeast of the NHAV 93 mound. |Approximately 129,900 m? of UDM was deposited at the buoy from late November through mid-December 1994 to form the foundation of the CLIS 94 mound. The UDM deposit was capped to a thickness of 0.5 to 1.0 m from January through May 1995 with an estimated volume of 161,000 m? of CDM. The placement of the CLIS 94 mound approximately 630 m northeast of NHAV 93 began the formation of a second containment ring capable of accommodating a future CAD mound project. Bathymetric data collected over the CLIS 94 mound exhibited a moderate sized, stable, and completely capped feature of the CLIS seafloor. The new CLIS bottom feature is approximately 470 m wide at the center with a mound height of 3.25 m at the apex. The CLIS 94 mound has completely incorporated the CS-90-1 mound, a capped mound developed during the 1989/90 disposal season. Benthic recovery of CLIS 94 was advanced with Stage III organisms present at the majority of REMOTS® stations in spite of the recent impact of disposal and added stress of seasonal hypoxia. The FVP mound is a small mound in the northeast corner of CLIS composed of uncapped UDM dredged from Black Rock Harbor in the spring of 1983. It was formed as part of an Environmental Protection Agency (EPA) and US Army Corps of Engineers, Waterways Experiment Station (WES) joint effort to evaluate various dredged material disposal alternatives. Since 1991, FVP has displayed instability in the benthic infaunal population inhabiting the surface sediments. September 1995 REMOTS?® results from FVP continue to show a lack of a stable, healthy benthic environment with the presence of depressed RPD and OSI values near the center of the mound. However, the effects of a decrease in available oxygen on the organisms inhabiting FVP might be amplified due to the preexisting stress of occupying a deposit of uncapped UDM. The FVP mound has been monitored periodically as a source of comparison for other mounds at CLIS since its formation in 1983. Now that the WES/EPA experimentation has concluded, capping of the FVP mound in order to isolate the UDM from the marine environment is recommended. 14. SUBJECT TERMS Central Long Island Sound (CLIS) , Confined Aquatic Disposal (CAD), |15. NUMBER OF PAGE = 137 Capping Dredged Material (CDM) 16. PRICE CODE 17. SECURITY CLASSIFICATION OF]18. SECURITY CLASSIFICATION |19. SECURITY CLASSIFICATION |20. LIMITATION OF REPORT Unclassified OF THIS PAGE OF ABSTRACT ABSTRACT MONITORING CRUISE AT THE CENTRAL LONG ISLAND SOUND DISPOSAL SITE SEPTEMBER 1995 CONTRIBUTION #118 November 1997 Report No. SAIC 373 oe Submitted to: _ Regulatory Branch New England District U.S. Army Corps of Engineers 424 Trapelo Road Waltham, MA 02254-9149 Prepared by: John T. Morris Submitted by: © Science Applications International Corporation Admiral's Gate 221 Third Street Newport, RI 02840 (401) 847-4210 US Army Corps of Engineerse New England District ' ain bea) cudly 7 ea net 16 fpr, ee en sk Re * bgodd olgana? BC Ge PESO AM ‘rel ae We beaaqort | BE WONVE SE paket TABLE OF CONTENTS Page PISTOF FIGURES Ose See SIO I RT TORR AI, BI, SIMI So lil BOE CULV E'S WMINIAR YE sccslsctnaratrcratrctraleeistorar vatatetereletetcrviteivevlouelactaltevetse alelebeciootonmisralierdiae Vill (FO Ree INTRODUCTION: WAS BEM EIS LIA FM AE Leen os 1 Dee METHODS eee Bae SURI BM 55 rasaraeoveleatarereshcend eatallaroatevorbeteisctote slag 10 Dale SULVEVSATCAS hoc esac sce cies eam rere a cis cute eat ee aera eed wera NA nce Leanne 10 2:2 Bathymetry and) Navigation yy ne Beau AS ON es PP 10 2.3. REMOTS® Sediment-Profile Photography ...................ccccecceeeceeeeecees 14 2.4 «Geotechnical Corning sss. .ccaswacoswsscumacionsoandec Lata ereievay aera etasieraroeie aaa 14 SV), PUBS ON BS CSREES A SME RA Ace AE RA Oe mS GSB core 3 a 18 Sl 3 NEVAN OS" Mound iat Sucve eras. ee oeerne BOGS Skate cas oe 18 DSMLIEMB ath ye tty seer aero cra svar a nsrolevateraistace tate esa onsintesatarsenahe scien sot 18 3.1.2 REMOTS® Sediment-Profile Photography ......................0c0c0e0es 18 SHleS 1 GeotechnicaléC oningiysgene, Sey AAP RE RO Oe A ee 27 32 CHS 4i Mound ty se boa TAs Ly Ss TRE SMS cov ahae sone 34 SEZ MGS AG VME CY sss nai scat ataiycia att oc nancial aeinceciib neta is osc one poets eee 34 3.2.2 REMOTS® Sediment-Profile Photography ................0...0ceceeeeees 49 SoS > EM PYNIOUIT Berea eee ISTE I Ta Bid eS Pies oc seca clsaleu be 50 S3yly; Sediment Grain'Sizerand| Stratigraphy: ..5..2.2.5...cssc-se0sc-ceceseceas: 54 313.2 Benthic Community ASsessmentesn eee cman eee eses eee ee 54 gray | ClIStReferencerAreas oi. 2 See aN SEE, I, Nome MeSH 2 58 3.4.1 Sediment Grain Size and Stratigraphy ......................ccceceeeeeeees 58 3.432, Benthic: CommunityvASsessment sic. sese sence sesso c sass dees 58 ANC DISC WSSTON: Societies Hes Vie fancies ey AUN OR se AU Mk REY. cou a ce tants 60 SORE CONCISUSTONS spn (4) exe one aneinanienal us SW Nc ee a eas 69 GO phe REFERENCES} ic ihirk ant eye. LAO ee, ias8 BUN ie ernie is astele seyaaype ahi ous cusacteess Wik INDEX APPENDICES iN tans SP eae Mw AS ee Aa saan Peer up CA AMA a he PER DRS at ga a pre We ale he a ee Py } i ANE Mee ewe pe aa Ig lsat Cher ass ‘in bos ante ws ie soi ee Se | CTV Rw a 8 0 eet ee ot a ele i , Be... ee ee ee er ee be MOM! ioe Hee ia oa Be A ee ace Pa Cee Ie Figure 1-1. Figure 1-2. Figure 1-3. Figure 1-4. Figure 2-1. Figure 2-2. Figure 2-3. Figure 2-4. Figure 3-1. Figure 3-2. Figure 3-3. LIST OF FIGURES Page Location of the Central Long Island Sound Disposal Site and shore Stationvbenchmiarksy sens ee) Seer ed. eesti cE OR oe 2 The historic DAMOS and Final Programmatic Environmental Impact Statement boundaries of the Central Long Island Sound Disposal Site over the Julyal 994: bathymetric sunveyrc¥-ce-m- sae-ceeeceantet ns -a-ne one teases 3 September 1993 baseline bathymetry depicting a ring of seven historic disposal mounds with plotted position of the NHAV 93 buoy, 0.25 m COMLOUBAINLET Vale amie rNsaGe NON of nee Rae sernts dln OE Berypete 5 Depth difference contour chart based on the comparisons of the March 1994 postcap survey versus the September 1993 baseline SULVE YL IRR Rucci 20h orion 3 acl nmmnesin alee Me Ds CR ALi SSE pce tel 6 Base map displaying the bathymetric survey areas and REMOTS® stations relative to the Central Long Island Sound Disposal Site boundariess sates nis welt pete piles erbelny SREY REO, 10), an coat 11 Comparisons of the two types of tidal data collected for the Septemben1995, bathyimetriciSumveySpesccse ste scereecinnc ee Gereeceemacce ooo 13) Chart of the 1600 m x 1600 m survey area with plotted geotechnical COFE POSItIONS and Names; -adocensaee ce em one e eee aN ie ee meatier tee 15 Diagram of the URI/MGL large-diameter gravity corer ...................0055 MG Bathymetric chart of the 1600 m x 1600 m survey area over the NHAWV£93smound>10/5 mi contour anterval Sapa. asete tes. itil see sec sce ee ces 19 Bathymetric chart of the 1600 m x 1600 m survey area over the NHAV 93 mound, with mound names, 0.25 m contour interval ............. 20 Depth difference plot of the postcap survey of March 1994 versus the September 1995 survey over the NHAV 93 mound, 0.25 m contour Interval ey. 8 eal) NO CRM Ae CO A. Sat, Bh MNS neds beelilonees 21 ii Figure 3-4. Figure 3-5. Figure 3-6. Figure 3-7. Figure 3-8. Figure 3-9. Figure 3-10. Figure 3-11. Figure 3-12. Figure 3-13. LIST OF FIGURES (continued) Depth difference plot of the baseline survey of September 1993 versus the September 1995 survey, 0.25 m contour interval. Chart represents the total apparent accumulation of dredged material since September L993 niceties. Laas. Ute. PEAS Sse eh ee cea Distribution of RPD (cm) and OSI values over the NHAV 93 mound, overlaid on September 1995 bathymetry and detectable margins of the MOUNT. BHi4S Mees toe ell belied BEY Ege cteom eee OE tae Distribution of successional stage assemblages over the NHAV 93 mound, overlaid on September 1995 bathymetry and detectable Margins Ofsthenmound 3 ewes eee es eae en eee ane eee REMOTS® photographs showing the improving conditions at Station 400S over the NHAV 93 mound during the September 1995 (A) survey relative to the July 1994 (B) survey...................ccceeeeeeeeeees REMOTS® photographs showing the improving conditions at Station CTR over the NHAV 93 mound during the September 1995 (A) survey relative to the July 1994 (B) survey...................ceceeeeeeeeeees Location of geotechnical cores GC-1 through GC-11 over the apparent total accumulation of dredged material since September 1993 Color geotechnical core descriptions oriented to display the results of the SW-NE transect over the NHAV 93 mound.....................0000005 Color geotechnical core descriptions oriented to display the results of the NW-SE transect over the NHAV 93 mound.......................00005 Bathymetric chart of the 1000 m x 1000 m survey area over the CLIS 94 mound with plotted CDA 94 buoy positions, 0.25 m contour IDO Ce) UF [gear eee Oi Epon y na RONNIE e)Ae ROR Meg NC AN AE DOA NER a ee ae Depth difference plot of SAIC's July 1994 baseline survey versus SAIC's September 1995 postcap survey, 0.25 m contour interval....... Page seni 22 Figure 3-14. Figure 3-15. Figure 3-16. Figure 3-17. Figure 3-18. Figure 3-19. Figure 3-20. Figure 3-21. Figure 3-22. LIST OF FIGURES (continued) Page Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CS 90-1 mound, SAIC's July 1994 baseline survey, 0.25 m COMLOUTSITICET VAIS: re We rete tcrccc er Ss wrarnistans ears ei ee ateloa Mee crete ere Meniedlamimaleas ait 38 Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CLIS 94 mound UDM deposit, OSI's December 1994 precap sunvey; 0225) m:icontour interval yy a sass essccs aces ciehisteaciissiencstenssicnee ieee 39 Depth difference plot of SAIC's July 1994 baseline survey versus OSI's December 1994 precap survey with plotted CDA 94 buoy positions: O:Z25imcontoun intenval. Nass ceacn dea secacoanas/cacseceeeccacseesn ees 40 Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CLIS 94 mound at interim cap status, OSI's April 1995 interim cap survey, 0.25 m contour interval ................... eee eeeeeeee ee eee 41 Depth difference plot of SAIC's July 1994 baseline survey versus OSI's April 1995 interim cap survey, overlaid with the detectable margin of the UDM deposit, 0.25 m contour interval .......................08 42 Depth difference plot of OSI's December 1994 baseline survey versus OSI's April 1995 interim cap survey, overlaid with the reported 700 yd? barge release positions, 0.25 m contour interval ...................... 43 Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CLIS 94 mound at postcap status, SAIC's September 1995 posicapisurvey, 0:25 mi contour intenvall-2i5.-cwssesecacisne se nnat scene seins cee: 45 ‘Depth difference plot of SAIC's September 1995 postcap survey versus OSI's April 1995 interim cap survey with plotted CDA 94 buoy and reported barge release positions, 0.25 m contour interval ......... 46 Depth difference plot of SAIC's September 1995 postcap survey versus OSI's December 1994 precap survey, overlaid with the CDA 94 buoy and reported barge release positions, 0.25 m contour interval...... 47 Figure 3-23. Figure 3-24. Figure 3-25. Figure 3-26. Figure 3-27. Figure 3-28. Figure 3-29. Figure 4-1. Figure 4-2. Figure 4-3. LIST OF FIGURES (continued) Page Plot of the three stages of CLIS 94 mound development, overlaid with the;\€DA: 94 buoy positions, 2.52322 05s Bes boc cases seees 48 Distribution of RPD (cm) and OSI values over the CLIS 94 mound, overlaid on September 1995 bathymetry and final detectable margin ofithesmound(s c2ii06 3. sedan debe. aaa acs IR Oe sae aise eecwewcies Sil REMOTS® photographs at Station 300S displaying the differences in benthic conditions (deep RPD [A] versus low DO [B]) within the confines: of ithe same ‘Station: .2:¢ sosevaset ened Cae e se bee eee + ates a veces 52 Distribution of successional stage assemblages over the CLIS 94 mound, overlaid on September 1995 bathymetry and final detectable Margin Of the mounds 3325. sse esas. Ah. Sats sees Beoake cieie deease eee e wociner 53 Distribution of RPD (cm) and OSI values over the FVP mound.............. 55 Distribution of successional stage assemblages over the FVP mound........ 56 REMOTS® photographs of Stations 100N (A) and 300W (B) displaying differences in benthic conditions between the center and apronohthesEVP mound eases paisa soca ae ee cae ae ss sesceeeeiees M7 Position of the Connecticut Department of Environmental Protection Dissolved Oxygen Sampling Stations and bottom DO trends at summer monitoring stations 23, 26, and 27 for 1994 and 1995............... 61 Observed changes in bottom DO concentrations at Connecticut Department of Environmental Protection Dissolved Oxygen Sampling StationsyH2 and sH4 ford 995 oe acces Ses ce chet tag aastais sweetest ee ene se 63 Histogram displaying recorded RPD calculations from June 1991, November 1993, and September 1995 at Stations 100E, 100N, 100W, andi @TRyovers the RV Pamound 3 s9ee esate cceyscetsisee de teads ois esac eels 64 vi LIST OF FIGURES (continued) Page Figure 4-4. Histogram displaying recorded OSI values from June 1991, November 1993, and September 1995 at Stations 100E, 100N, 100W, andi@DR¥overthesR VPimound ese 7. scsi eee ate ee cee lonee enone ce: 65 Vil io it Mi i EXECUTIVE SUMMARY Science Applications International Corporation (SAIC) conducted a monitoring survey at the Central Long Island Sound Disposal Site (CLIS) from 27 August to 1 September 1995 as part of the Disposal Area Monitoring System (DAMOS) Program. The field operations were concentrated over the New Haven 1993 (NHAV 93), CLIS 1994 (CLIS 94), and Field Verification Program (FVP) mounds and consisted of precision bathymetric surveys, Remote Ecological Monitoring of the Seafloor (REMOTS®) sediment-profile photography, and geotechnical coring. These surveying techniques were employed to monitor the stability, cap thicknesses, consolidation rates, and benthic recolonization of the NHAV 93, CLIS 94, and FVP mounds. The NHAV 93 mound represents the culmination of ten years of thoughtful planning and controlled disposal at CLIS. This mound was developed during the 1993/94 disposal season as part of a large scale confined aquatic disposal (CAD) project. From 1984 through 1992, disposal operations at CLIS led to the construction of a ring of disposal mounds. This ring formed an artificial containment cell that was capable of accepting a large volume of unacceptably contaminated dredged material (UDM), limiting the lateral spread of the deposit and, in turn, facilitating efficient capping operations. The NHAV 93 mound was formed by the placement of approximately 590,000 m? of UDM within the ring of seven historic disposal mounds. The UDM deposit was then covered to a thickness of 0.5 m to 1.0 m by 569,000 m3 of capping dredged material (CDM). SAIC has conducted a total of seven bathymetric, four REMOTS® sediment- profiling, and five geotechnical coring surveys over the NHAV 93 mound since September 1993. The comprehensive time-series data set documents the formation of the mound within the containment cell as well as its gradual consolidation and benthic recolonization. In addition, the wealth of data has provided SAIC and the US Army Corps of Engineers, New England Division (NED), with significant insight into the short- and long-term effects of disposal and oceanographic processes on large dredged material mounds. The results of the September 1995 field effort indicate a moderate amount of consolidation (0.25 m) over the majority of NHAV 93 with several pockets of 0.5 m consolidation near the center of the mound. The heterogeneity of the material collected in the five-member geotechnical coring data set makes tracking a single sediment horizon throughout the project difficult. However, indicators such as shell fragments, gravel, and detritus were useful in differentiating ambient, historic, UDM, and CDM sediment strata. REMOTS® sediment profile-photography found the biota occupying the surface sediments of the NHAV 93 mound to be recovering as anticipated. A seasonal reduction in dissolved oxygen within the central Long Island Sound region appeared to be responsible for viii EXECUTIVE SUMMARY (continued) shallow redox potential discontinuity (RPD) depths over the NHAV 93 mound as well as the CLIS reference areas. As a result, lower than expected organism-sediment index (OSI) values were found near the center and extreme southern and eastern stations despite the presence of Stage III organisms at eleven of thirteen stations over the NHAV 93 mound. In September 1994, a disposal buoy marked “CDA” was deployed at 41°09.343' N, 72°53.099' W by SAIC to the northeast of the NHAV 93 mound. Approximately 129,900 m3 of UDM was deposited at the buoy from late November through mid- December 1994 to form the foundation of the CLIS 94 mound. At the conclusion of UDM disposal operations, the CDA buoy was struck by a disposal barge and dragged off-station. The buoy was repositioned to 41°09.334' N, 72°53.084' W before the start of CDM deposition over the CLIS 94 mound. The UDM deposit was capped to a thickness of 0.5 to 1.0 m from January through May 1995 with an estimated volume of 161,000 m? of CDM. The placement of the CLIS 94 mound approximately 630 m northeast of NHAV 93 began the formation of a second containment ring capable of accommodating a future CAD mound project. Bathymetric data collected over the CLIS 94 mound exhibited a moderate sized, stable, and completely capped feature of the CLIS seafloor. The new CLIS bottom feature is approximately 470 m wide at the center with a mound height of 3.25 m at the apex. The CLIS 94 mound has completely incorporated the CS-90-1 mound, a capped mound developed during the 1989/90 disposal season. Benthic recovery of CLIS 94 was advanced with Stage III organisms present at the majority of REMOTS® stations in spite of the recent impact of disposal and added stress of seasonal hypoxia. The FVP mound is a small mound in the northeast corner of CLIS composed of uncapped UDM dredged from Black Rock Harbor in the spring of 1983. It was formed as part of an Environmental Protection Agency (EPA) and US Army Corps of Engineers, Waterways Experiment Station (WES) joint effort to evaluate various dredged material disposal alternatives. Since 1991, FVP has displayed instability in the benthic infaunal population inhabiting the surface sediments. September 1995 REMOTS® results from FVP continue to show a lack of a stable, healthy benthic environment with the presence of depressed RPD and OSI values near the center of the mound. However, the effects of a decrease in available oxygen on the organisms inhabiting FVP might be amplified due to the preexisting stress of occupying a deposit of uncapped UDM. The FVP mound has been monitored periodically as a source of comparison for other mounds at CLIS since its formation in 1983. Now that the WES/EPA experimentation has concluded, capping of the FVP mound in order to isolate the UDM from the marine environment is recommended. ~ 1.0 INTRODUCTION The managed disposal of dredged material was introduced to the central Long Island Sound region in October 1973 with the development of the New Haven 1974 (NHAV 74) mound in the center of the newly created New Haven Disposal Site. An estimated 1,150,000 m3 of material dredged from the New Haven Harbor was deposited at this site between October 1973 and March 1977. In 1977, the US Army Corps of Engineers, New England Division (NED), instituted the Disposal Area Monitoring System (DAMOS) Program in response to the recognized need for long-term management and monitoring of the New Haven Disposal Site as well as 10 other disposal sites in New England waters (NUSC 1979). Since 1977, advances in dredged material disposal, precision navigation, and environmental monitoring technology have continually improved the tools used in disposal site management. In 1979, the configuration of the New Haven Disposal Site was modified, expanding the boundaries of the site and changing its name to Central Long Island Sound Disposal Site (CLIS; SAI 1979). The new disposal site boundaries encompassed a 6.86 km? (2 nmi?) area located approximately 10.39 km (5.6 nmi) south of South End Point, East Haven, Connecticut (Figure 1-1). Since its expansion in 1979, the disposal site shown in DAMOS reports has been centered at 41°08.950' N, 72°52.850' W. However, after recognizing a slight discrepancy, NED began using the set of center coordinates for CLIS as defined in the Final Programmatic Environmental Impact Statement (FPEIS; US Army Corps of Engineers 1982). CLIS is now centered at 41°08.900' N, 72°53.100' W longitude in North American Datum of 1927 (NAD 27), 362 m west-southwest of the historic DAMOS center (Figures 1-1 and 1-2). The reasons for the discrepancy between the historic and FPEIS coordinates are unknown; however, this modification corrects the locational inconsistency. Similar changes are being made for the New London Disposal Site (NLDS) and Cornfield Shoals Disposal Site (CSDS) in the eastern Long Island Sound. Historically, CLIS has been one of the most active disposal sites in the New England region. The disposal site has received sediments dredged from New Haven, Bridgeport, Stamford, and Norwalk Harbors, as well as adjacent coastal areas. The abundance of disposal activity within the boundaries of the disposal site allowed NED to develop and refine a variety of dredged material management strategies. During the 1978/79 disposal season, subaqueous capping was introduced as a new dredged material management approach with the formation of the Stamford-New Haven mounds (STNH-N and STNH-S; SAIC 1995). Capping is a containment method which uses sediments determined to be suitable for unconfined open water disposal, or capping dredged material (CDM), to overlay and Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 MILFORD END POINT E x oO) Se j=) - STRATFORD FPEIS Central Long Island Sound Disposal Site LONG ISLAND SOUND Location of the Central Long Island Sound Disposal Site and shore station benchmarks Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 Figure 1-1. Adains oLenouAMIeG P661 A[NE dP 19AO0 IS [esodsiq punos puryjs] suoT fenusd op JO SoLrepunog JuouTaIe)g 1edu] [eyWOUNMOMIAUY INeUURISOLg [LULL puke SOV Holst oy | -° 7-7 andy wo — Zé GVN SJB} Ul SUIdeq SIT9 M _.000°2S .éZ M _.000°€S .éZ M_.000°VS .cZ N .00S°80 oLP in O N .000°60 LP N .00S°60 oLP AsyowAyjeg p66l Ajing¢ pue soluepunog Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 4 isolate deposits of unacceptably contaminated dredged material (UDM) from the environment (Fredette 1994). As a result of the operational success of the 1979 capping project, many additional capped mounds have been formed at CLIS (SAIC 1995). From 1977 through 1983 the site management strategy at CLIS entailed the formation of many independent mounds over the given area of the disposal site. Each mound was monitored individually, assessing mound stability, cap thickness, benthic recolonization status, etc. Although this practice was highly successful, the overall capacity of the disposal site was compromised due to the unusable area between the discrete sediment mounds (Morris et al. 1996). In 1983, a new management strategy was instituted at CLIS. Utilizing the ten-year dredging cycle that exists in the central Long Island Sound region, NED managed the deposition of small to moderate volumes of dredged material at CLIS to form a disposal mound ring. Upon completion in 1992, this network of disposal mounds formed an artificial containment cell that was capable of accepting a large volume of UDM, limiting the lateral spread of the deposit, and facilitating efficient capping operations. The containment ring was employed during the 1993/94 disposal season as part of the New Haven Harbor Capping Project. In September 1993, the NHAV buoy was placed in the center of seven historic disposal mounds (41°09.122' N, 72°53.453' W) designating the disposal point for approximately 590,226 m? of UDM dredged from the inner New Haven Harbor (Figure 1-3). The UDM deposit was then capped to a thickness of 0.5 m to 1.0 m with an estimated barge volume of 569,287 m3 of outer New Haven Harbor CDM, forming the New Haven 1993 (NHAV 93) mound. Upon completion of disposal and capping operations in March 1994, the NHAV 93 mound displayed a height of 2.5 m and an overall diameter of 800 m (Figure 1-4; Morris et al. 1996). Due to the utilization of an artificial containment structure, the NHAV 93 mound is considered a confined aquatic disposal (CAD) mound. The use of the disposal mound ring significantly reduced the outward migration of the UDM mound apron relative to an uncontained UDM deposit. As a result, cap material distribution was concentrated over a smaller area, decreasing the total volume of CDM required to cap the inner New Haven Harbor sediments (Morris et al. 1996). The completed CAD mound was found to be broad, stable, adequately capped, and exhibiting a CDM to UDM ratio of 0.96:1.0 (Morris and Tufts 1997). In the past, CDM to UDM ratios varied from 2:1 to 6:1 when initiating a capping operation on a flat or gently sloping area of seafloor. The NHAV 93 mound represents the first capped mound composed of a smaller volume of CDM than the initial UDM deposit. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 September 1993 Baseline Bathymetry ies es é 41° 09.500° N- 41° 09.250° N 41° 09.000° N T 41° 08.750° N W .000° 53 W 72° W 72° 53.250° 53.500° 72° W .750° “W 72° 53 000 72° 54 in meters 1a) ®O _ (0) > _ = ep) iS oO [e)} Oo ~- x ‘S je) oO i 6 L Zz CLIS Depth NAD 27 400 m ric f seven histo icting a ring o Figure 1-3. September 1993 baseline bathymetry dep disposal mounds with plotted position of the NHAV 93 buoy, 0.25 m contour interv he Central Long Island Sound Disposal Site, September 1995 ing Cruise at t itor Mon Depth Difference March 1994 vs. September 1993 41° 09.500° N 41° 09.250° N 41° 09.000 N+ 41° 08.750°N 72° 54.000°W 72°53.750°W 72°53.500°W 72°53.250°W 72° 53.000’ W Difference in meters NAD 27 EZ 6) 1Om 400 m Figure 1-4. Depth difference contour chart based on the comparisons of the March 1994 postcap survey versus the September 1993 baseline survey Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 In September 1994, the CDA buoy was deployed over the historic CS-90-1 mound at 41°09.343' N, 72°53.099' W, approximately 630 m northeast of the NHAV 93 mound apex. The placement of a moderate-sized, capped mound in close proximity to the NHAV 93 mound complex began the formation of a second containment ring capable of accommodating a future CAD mound project. In addition, the deposition of new material over CS-90-1 was intended to cover the smaller CS-90-1 capped mound, further isolating its UDM deposit and conserving the usable surface area of the CLIS seafloor. An estimated barge volume of 129,900 m3 of UDM was released at the CDA buoy from late November through mid-December 1994. Toward the end of UDM disposal activity, the CDA buoy was struck by a disposal barge and dragged off-station. The buoy was repositioned at 41°09.334' N, 72°53.084' W on 27 December 1994 before the start of CDM deposition. During capping operations, the UDM deposit was covered to a thickness of 0.5 to 1.0 m from January through May 1995 with an estimated volume of 161,000 m3 of CDM. In 1983, the Field Verification Program (FVP) mound was formed in the northeastern corner of CLIS as the subaqueous disposal component of a joint research effort between the US Environmental Protection Agency (EPA) and US Army Corps of Engineers, Waterways Experiment Station (WES). The two agencies were evaluating upland containment, wetland creation, and subaqueous disposal alternatives for UDM (Peddicord 1988). The FVP mound is a small mound composed of 55,000 m3 of uncapped UDM dredged from Black Rock Harbor in the spring of 1983 (Morton 1983). Since 1991, FVP has displayed instability in the benthic infaunal population inhabiting the surface sediments, suggesting an increase in environmental stress. Science Applications International Corporation (SAIC) conducted a monitoring survey at CLIS from 27 August to 1 September 1995 as part of the DAMOS Program. The field efforts were concentrated over the NHAV 93, CLIS 94, and FVP disposal mounds, and consisted of bathymetric profiling, Remote Ecological Monitoring of the Seafloor (REMOTS®), and geotechnical coring. Precision bathymetry and REMOTS® technology are well-tested and highly regarded methods of investigating the properties and processes of dredged material disposal within the DAMOS tiered monitoring protocols. The use of geotechnical coring is not a routine monitoring approach but is used in the special study of dredged material mounds to improve our understanding of the dynamics and mass properties of these mounds. The DAMOS tiered monitoring protocols are based on the use of a control or alternate condition to provide solid statistical testing and serve as a foundation for experimental design (Germano et al. 1994). Three reference areas surrounding CLIS are Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 8 used as zones of primary control to allow comparisons between the surface sediments of the disposal mounds and ambient bottom. CLIS-REF (41°08.085' N, 72°50.109' W), 2500W (41°09.254' N, 72°55.569' W), and 4500E (41°09.254' N, 72°50.565' W) are devoid of dredged material and physically, chemically, and biologically represent the ambient bottom of CLIS. The DAMOS Program uses a multiple reference approach to strengthen the statistical models as well as provide contingencies for acute benthic disturbances (i.e., trawling) that affect smaller areas of seafloor at a reference site before or during field operations causing degradation of the data collected. The objectives of the September 1995 field operations were to e conduct two bathymetric surveys over CLIS to examine any topographical changes in the NHAV 93 mound and delineate the dredged material footprint of the new CLIS 94 capped mound; e assess the benthic recolonization status of the NHAV 93, CLIS 94, and FVP mounds relative to the three surrounding CLIS reference areas; and e sample the various layers of sediment that make up the NHAV 93 mound and quantify the amount of dredged material consolidation and de-watering within those layers. The September 1995 field effort tested the following predictions: e Small to moderate amounts of consolidation will be found over the majority of the NHAV 93 mound, while the CLIS 94 mound will be of moderate size, conical in shape, and fully capped. e The sediments of NHAV 93 are expected to be supporting Stage II and Stage III individuals over the surface of the mound in accordance with the DAMOS tered monitoring protocols. e The benthic community over the CLIS 94 mound should consist primarily of Stage I individuals with some progression into Stage II assemblages as predicted by the DAMOS tiered monitoring protocols. e The conditions over the FVP mound should have returned to a state similar to the three CLIS reference areas; however, seasonal changes in water quality parameters may increase the susceptibility of the benthic community to environmental stress relative to the reference areas. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 e Consolidation of the NHAV 93 mound is expected to obscure the UDM/CDM interface within the geotechnical cores. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 10 2.0 METHODS 2.1 Survey Areas In order to fulfill the objectives of the 1995 CLIS monitoring survey, two bathymetric survey areas were defined over the CLIS 94 and NHAV 93 disposal mounds. The survey over the CLIS 94 mound was 1000 m x 1000 m, centered on the first. position of the 1994 CDA buoy (41°09.343' N, 72°53.099' W). A total of 41 survey lanes at 25 m lane spacing were required to delineate the topography of the new CLIS 94 mound (Figure 2-1). The second, larger survey was conducted over a 1600 m x 1600 m area, and centered at 41°09.125' N, 72°53.413' W (Figure 2-1). The layout of this survey was identical to the surveys run over the NHAV 93 mound in the 1993 and 1994 disposal seasons, requiring 65 survey lanes to map the changes in the now historic NHAV 93 mound. Detailed bathymetric charts were generated for both areas to quantify mound height, lateral distribution of dredged material, and position relative to other disposal mounds. 2.2 Bathymetry and Navigation The SAIC Integrated Navigation and Data Acquisition System (INDAS) provided the precision navigation and data collection required for all SAIC field operations. This system utilizes a Hewlett-Packard 9920® series computer to provide real-time navigation, as well as collect position, depth, and time data for later analysis. A Del Norte Trisponder® System provided positioning to an accuracy of +3 m. Shore stations were established along the Connecticut coast at the known benchmarks of Stratford Point (41°09.112' N, 72°06.227' W) and Lighthouse Point (41°14.931' N, 72°54.255' W) (Figure 1-1). A detailed description of the navigation system and its operation can be found in the DAMOS Navigation and Bathymetry Reference Report (Murray and Selvitelli 1996). An ODOM DF3200 Echotrac® Survey Fathometer with a narrow beam, 208 kHz transducer measured individual depths to a resolution of 3.0 cm (0.1 ft) as described in DAMOS Contribution No. 48 (SAIC 1985). Depth values transmitted to INDAS were adjusted for transducer depth. The acoustic returns of the fathometer can reliably detect changes in depth of 20 cm or greater due to the accumulation of errors introduced by the positioning system, tidal corrections, changes in sound velocity through the water column, the slope of the bottom, and vertical motion of the survey vessel. The expanding resources of the Internet have allowed SAIC to access the National Oceanographic and Atmospheric Administration (NOAA), Ocean and Lake Levels Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 | SaLrepunog ag [esodsiq punos purjs] suo] [LNUID I} 0} IANLIAI SUONLIS gS LOWAA pue seare AdAIns sLHNoWATIeG oy SuTALidsip dew oseg °[-7 saNSIy Ww OO9L wo SIT9 ease WOOO! X WOOO! {4 phi, indicating no significant coarsening of surface CDM due to bedload transport of fine-grained material. Boundary roughness values ranged from 0.42 cm to 1.82 cm with the lowest surface Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 19 NHAV 93 Disposal Mound 1600 m x 1600 m Survey Area = ° S wo ror) ra) ° 2 + N , 41° 09.250 N , 41° 09.000 N , 41° 08.750 .000° W 53 72° WwW W 72° 53.250° 500° 53 72° Ww 750° W 72°53 72° 54.000° CLIS wn a a) ®O = In Depths NAD 27 400 m Bathymetric chart of the 1600 m x 1600 m survey area over the NHAV 93 mound, 0.5 m contour interval Figure 3-1. 1 Site, September 1995 isposa ng Cruise at the Central Long Island Sound D tort Mon 20 NHAV 93 Disposal Mound 1600 m x 1600 m Survey Area 41° 09.500° N-E 41° 09.250°N N ° 09.000° 41 N ° 08.750° 41 W 72° 53.000° W .250° 53 Wieh2s 500° 53 72° W 53.750° Wie .000° 54 72° CLIS in Meters Depths NAD 27 m 0 hart of the 1600 m x 1600 m survey area over the NHAV 93 mound, with mound names, 0.25 m contour interval Bathymetric c 2 Figure 3 Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 21 Depth Difference March 1994 versus September 1995 41° 09.500’ N- 41° 09.250° N- 41° 09.000° N 41° 08.750’ N- 72° 54.000°W =72° 53.750° W Difference in Meters NAD 27 a Om 400 m Figure 3-3. Depth difference plot of the postcap survey of March 1994 versus the September 1995 survey over the NHAV 93 mound, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 NHAV 93 Disposal Mound Total Accumulation of Dredged Material 41° 09.500° N \ ms aN ( } Sean 0.507 | | ¢ oo \ SNK 2 B A 7 \ 4.00 > “No \ RECs 0 (= = \ {| : 41° 09.250" N < a 2 ea \ Cer > . ) ») ane wy, yy ‘< “| 9° 2 41° 09.000’ N - 41° 08.750° N 72° 54.000°W 72° 53.750°W 72°53.500°W 72°53.250°W 72° 53.000° W CLIS Mound Height in Meters NAD 27 a Om 400 m Figure 3-4. Depth difference plot of the baseline survey of September 1993 versus the September 1995 survey, 0.25 m contour interval. Chart represents the total apparent accumulation of dredged material since September 1993. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 23 disturbance values (<0.5 cm) concentrated at the center of the mound (CTR, 200E, 2008S; Appendix A: Table 3-1a). The primary cause of boundary roughness was biogenic activity within surface sediments. The replicate-averaged mean camera penetration ranged from 12.86 cm to 18.91 cm (Appendix A: Table 3-1a). Dredged material was absent at three stations (400N, 600N, 600W), and measured replicate-averaged dredged material thicknesses ranged from 3 cm at 600S to full penetration (20 cm) at many stations (Appendix A: Table 3-1a). The apparent absence of dredged material at stations 400N, 600N, and 600W may be attributed to complete reworking of historical dredged material, to the extent that there are no recognizable indicators. Redox rebound intervals, areas of intermittent or seasonal oxidation below the oxidized surface layer, were noted at several stations, including two of the three stations which had no measurable dredged material (400N, 600N). Sol W474 Benthic Community Assessment Three parameters were used to assess the benthic recolonization rate and overall health of the project mounds relative to the CLIS reference areas. The apparent Redox Potential Discontinuity (RPD) depth, infaunal successional status, and the Organism- Sediment Index (OSI) were mapped on station location plots to outline the biological conditions at each station. The apparent RPD depth is the depth of oxygenation in the upper sediment layers. This value indicates dissolved oxygen conditions within sediment pore water as well as the availability and consumption of molecular oxygen (O,) in the surface sediments. Since actual oxygen status in the sediment is not measured, the apparent RPD is estimated by measuring the thickness of the layer of high reflectance in contrast to the usually gray to black reduced sediments at depth (Rhoads and Germano 1982). Replicate-averaged RPD values over the NHAV 93 mound ranged from 0.91 cm at 600E to 4.23 cm at 400E, indicating improvement relative to the 1994 survey, especially at the stations previously exhibiting slow benthic recovery (Figure 3-5; Appendix A: Tables 3-la and 3-1b). RPDs of <2 cm were measured at the central, south, and east sections of the sampling grid (CTR; 200E, W, and S; 400S; and 600S and E). Station 600E, displaying a relatively shallow RPD depth, has probably been affected by the recent deposition of CDM over the CLIS 94 mound reducing the level of oxidation in the surface sediment layers. However, the mean RPD value for the entire project area was 2.14 cm, indicating improving conditions relative to the 0.78 cm RPD value for July 1994. Neither methane nor low dissolved oxygen was noted in any photograph. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 24 NHAV 93 Disposal Mound September 1995 REMOTS® Stations over Bathymetry and 1993-1995 Dredged Material Deposit 41° 09.500° N 41° 09.250° N 41° 09.000° N 41° 08.750° N 72° 54.000°W = 72°53.750°W = 72°53.500°W 72°53.250°W 72°53.000° W CLIS Overall Depths in Meters RPD 2.14 NAD 27 TS a Osi 6.4 Om 400 m Figure 3-5. Distribution of RPD (cm) and OSI values over the NHAV 93 mound, overlaid on September 1995 bathymetry and detectable margins of the mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 25 The mapping of successional stages is based on the theory that organism-sediment interactions follow a predictable sequence after a major seafloor disturbance (Rhoads and Germano 1982). This sequence is defined by end-member assemblages of benthic organisms. Stage I is made up of pioneering assemblages usually consisting of dense aggregations of near-surface, tube-dwelling polychaetes. If left undisturbed, Stage II infaunal deposit feeders such as shallow-dwelling bivalves or tubicolous amphipods then colonize the recovering seafloor. Stage III organisms are generally head-down deposit- feeding invertebrates whose presence results in distinctive subsurface feeding voids. Stage III taxa are associated with relatively low-disturbance regimes (Rhoads and Germano 1986). Organism-sediment index values are calculated by summarizing the apparent RPD depth, successional status, and indicators of methane or low oxygen. OSIs can range from -10 (azoic with methane gas present in sediment) to 11 (aerobic bottom with deep apparent RPD, evidence of mature macrofaunal assemblage, and no apparent methane). OSI values are useful in mapping disturbances and quantifying ecosystem recovery (Rhoads and Germano 1982). Eleven stations within the thirteen-station survey grid showed evidence of Stage III organisms (Figure 3-6). The most common stages noted in the replicate photographs were Stage I and Stage I on III. Replicate median OSIs range from 2.5 at 600E (low RPD, no Stage III due to recent CDM deposition) to 11 at 400E (Figure 3-6; Appendix A: Table 3- la). Low OSIs (<6) are concentrated at the center (CTR, 200E, 200S), and at the extremes of the southern and eastern legs of the grid (600S, 600E). Overall, the mean OSI value for the NHAV 93 mound was 6.4, a substantial improvement over the July 1994 value of 3.5. The results of the July 1994 REMOTS® survey indicated the presence of three areas of concern (CTR, 200N, and 4008S; Morris and Tufts 1997). All three stations exhibited shallow to diffusional RPD depths, limited recolonization, and lower OSI values than anticipated. As part of the DAMOS tiered monitoring protocols, sediment from stations CTR, 200N, and 400S was collected and subjected to Ampelisca bioassay testing for toxicity. No significant differences in mortality were found between the sediment samples originating from NHAV 93 stations CTR, 200N, and 400S and the sediments collected from CLIS-REF (Mueller 1994). As a result, no action was taken at NHAV 93 (i.e., cap supplementation) and the stations were closely monitored for changes in benthic conditions (Morris and Tufts 1997). The September 1995 REMOTS® results indicate that, in general, the NHAV 93 mound is recovering from the impact of dredged material disposal as predicted (Germano et al. 1994). The three stations that exhibited poor benthic conditions with low RPDs in Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 26 NHAV 93 Disposal Mound September 1995 REMOTS® Stations over Bathymetry and 1993-1995 Dredged Material Deposit 41° 09.500° N 41° 09.250° N 41° 09.000° N 41° 08.750° N 0 72° 54.000°W 72°53.750°W 72°53.500°W 72°53.250°W 72°53.000° W CLIS Depths in Meters NAD 27 ee Om 400 m Figure 3-6. Distribution of successional stage assemblages over the NHAV 93 mound, overlaid on September 1995 bathymetry and detectable margins of the mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 27 the 1994 survey (CTR, 200N, 400S) showed improvement, although two replicates at CTR had thin and patchy RPD and low OSI values of 2 and 3 (Figures 3-7 and 3-8). Comparisons of the 1995 NHAV 93 REMOTS® results to the reference areas indicate the oxygenation status at the sediment/water interface over the region may have been affected by seasonal hypoxia. As a result, RPD and OSI values on the mound and in the reference areas may have decreased in response to the reduction in available oxygen. 3.1.3 Geotechnical Coring A total of eleven geotechnical cores were collected to provide a deep, cross- sectional view of the multiple sediment layers that make up the NHAV 93 mound (Figure 3-9; Appendix A: Table 2-2). Seven cores with penetration depths varying from 131 cm (GC-9) to 272 cm (GC-6) were split, visually described, and analyzed for the properties listed in Section 2.4 of this document. These seven cores represent the end-member of a five-core data set collected over the NHAV 93 mound at different stages of development (baseline, precap, postcap, four months postcap, and eighteen months postcap; Appendix C: Table 1). Graphics depicting the entire time-series data set are provided in Appendix C. A report pertaining to the geotechnical analysis of cores GC-1 through GC-11 will be included in a final report submitted by Armand J. Silva, P.E., of Geotechnical Consulting Engineers. Core GC-5 was obtained over the southwest flank of the NHAV 93 mound (41°08.996' N, 72°53.629' W) and penetrated 269 cm into the sediments (Figure 3-9). The visual core description indicates the first 180 cm of material constitutes the New Haven project CDM (Figure 3-10). The CDM layer is composed of several sediment strata of soft, black and olive-gray sands, silts, and clays. A thin layer of New Haven UDM, olive-grey clayey silt, was visible from 180 cm to 200 cm of penetration. A 10 cm to 15 cm layer of dark silt is representative of the historic dredged material that makes up the CLIS 88 and Norwalk mound aprons. The remaining 55 cm of sediment collected in Core GC-5, olive-gray, clayey silt with shell fragments, is typical of ambient, basement material at CLIS. Core GC-10 was taken approximately 75 m southwest of the NHAV 93 mound center (41°09.075' N, 72°53.521' W; Figure 3-9). A total of 248 cm of CDM, UDM, and historic dredged material was recovered in GC-10. The top 134 cm of sediment was composed of soft, black, clayey silt with organics and shell fragments (Figure 3-10). No distinct horizon was visually detected between New Haven cap and dredged material layers; however, the UDM/CDM interface is estimated at approximately 100 cm of penetration. From 100 cm to 218 cm of penetration this core is made up of the various layers of silt, sand, and gravel. The division between New Haven dredged material and Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 28 €6 AVH ADAINS ({) PE6T ATM Wp 01 DANIO ADAINS (W) S66] Joquiaidas ay) BU N 92 J0A0 SQOP UONRIS Iv suONIpUOS SuTAOIdUT ay) SuUTMOYsS syde1s0}0yd (a) ( inp punour es LON Vv) L-€ oAnsiy Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 29 ADAINS ({) P66T Atne sy OF dANeTAI ADAINS (VY) S66T Joquiaidas oy) SuLInp punow €6 AVHN 9} 1900 YLD voNeig 1e suontpuos surAoidun sty surmoys sydessojoyd gS LOWAY (a) (Vv) 8-€ ons 1 Site, September 1995 isposa he Central Long Island Sound D. ise at t Monitoring Cru 30 NHAV 93 Disposal Mound Geotechnical Core Positions 41° 09.500’ N - 41° 09.250°N 41° 09.000’ N - 41° 08.750° N 72° 54.000°W 72°53.750°W 72°53.500°W 72°53.250°W 72° 53.000° W GC-1 Fifth member geotechnical core collected in August 1995 CLIS Mound Height in Meters NAD 27 U Corresponding fourth member geotechnical core collected July 1994 Om 400 m Figure 3-9. 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No ambient material was sampled in Core GC- 10. Core GC-3B, collected over the center of the NHAV 93 mound (41°09.134' N, 72°53.458' W), penetrated 185 cm into the New Haven sediments (Figure 3-9). The core description indicates that the top 93 cm is composed of two layers of black, clayey silt, representative of the CDM layer (Figures 3-10 and 3-11). The remaining 92 cm of sediment displayed the various strata of the UDM deposit with alternating layers of silt and sands. The multiple sediment horizons within the UDM component depict the heterogeneity of material disposed over the center of the NHAV 93 mound. Core GC-9, obtained approximately 100 m northeast of the NHAV 93 mound apex (41°09.175' N, 72°53.407' W), penetrated 131 cm into the New Haven Harbor sediments (Figure 3-9). A visual description of Core GC-9 shows three layers of silt, sand, and shell fragments making up the 89 cm thick cap (Figure 3-10). The sediment sampled from 90 cm to 110 cm was a uniform black, clayey silt and considered to be UDM. The second UDM stratum, a layer of brown to black sand and gravel, was visible from 111 cm to the penetration limit. Core GC-11 was collected on the northeast flank of the NHAV 93 mound (41°09.264' N, 72°53.306' W) and is composed of both NHAV 93 and CLIS 94 dredged material (Figure 3-9). The top 60 cm of sediment in Core GC-11 is consistent with the clayey silt material used as CDM over the CLIS 94 mound (Figure 3-10). The alternating layers of dark olive-gray and black clayey silt that extends from 60 cm to 120 cm correspond to the NHAV 93 cap material, as collected in previous cores. New Haven UDM was sampled at 120 cm of penetration and meets the dark, olive-gray, basement material at 155 cm. The basement material is visible from 155 cm to the penetration limit of 262 cm. Core GC-7, collected 50 m from the center of the mound, represents the southeast quadrant of NHAV 93 (Figure 3-9). The core penetrated 223 cm into the sediments, providing a cross-section of the CDM and UDM making up the NHAV 93 mound as well as the ambient basement material (Figure 3-11). The top 67 cm of penetration represents the clayey silt cap over the UDM deposit. Layers of soft black, and an olive-gray, clayey silt overlay 147 cm of New Haven dredged material composed of a heterogenous mixture of clay, silt, sand, and gravel. The bottom 9 cm of Core GC-7 is composed of olive-gray silt, the ambient sediment at CLIS. Core GC-6 was obtained 60 m northwest of the mound center (41°09.182' N, 72°53.509' W) and penetrated 272 cm through NHAV 93 sediments and historic dredged Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 33 ‘JUeJUCD 1EyDM BurspesOU! ur] Uo|Dsyoueg sBpy wg HOYs Popul] UM jIIs AeApjo AeiBb-ealjo Dg sBpy |]eys PUD jIIs YODIG Jo se AD] UM IIs ‘Ae ADO ‘Apups Aoi6-ealjo 410g W O'S PuDs UMOIq @SID09 Oj BUY qIs PuD pups A@ib-enlo Dg pups jo seopdy Uyim fis AeADIO JB - 0 Aes6-@AO DG ws'| pups wnjpew Pub seul) 491g —P>} }@AD16 pup pups @SIDOD O} euly Wo'l UM {IIs A@ADIO ‘HOD] |}]e4s pud pups jo soopy a0 UM Is AeADIO ‘YODIg WO S66l 4snBny 9-OD 810 MAN Wg'0 WO elpos {UL}T UO}JDIJoUed “sy []OYs UIA Alls Apps ‘yOD{q of AeId “Uls HODIq Jo seul “pups Ajiis euy ‘yooiq oj Aeib-eA1O “pups Adi6-anqjo ‘Ays Pup IIs A2ADIS ‘yODIG Jo si9An} Buyousayty Wd g'[ iis A@ADIS ‘Aes6-aAl1O WQ'L “ADIB UM poxyUL IIIS As Anjo ‘ojuDHiso ‘yong Ws'0 *sojuDBJo pub ‘pups ‘nis AerB-anito UM wis A@ADIO ‘yODIa wo G66L JsnB6ny ge-OD e109 ujIM [@ADI5 pup pups uMolg Ae Anjo ‘Apups AoJ6-aA|lo punouw! €6 AVHN 2} IOA0 109SURT YS-M\N 9} JO sinsar ou Avydsip 0} paso suonddsap 3109 [eotUyINHOIS IO[OD “[][-¢ sans JIWW}] UO}DI}aUed ais AsAnjo Aei6-aayjo IDG pups 490/q Ajjeus us AeApp Aei6-2anijo y10q WQ' ills pub pups nares Jo sjayood UNM Js A2s6-aA]f0 DG MIS NODIG Jo siaAD] Wg" UNM IIS Aes6-2 Alo 41Dq iis AeApjo ‘ojuDBso yong alls A@AD[D YODIG Jo sjayxD0d UIA IIIs Aes6-eAl|o DG souy Payull MYO feani6 uy ts Apups ‘ojup6s0 yoni sBpy Heys Poy] UM HIS PUDS JO SOODJ UJIM us ABADID ‘ODI Yos WO GOL JsnBny L-DD 8109 As wWg'd Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 34 material into ambient bottom (Figure 3-9). The top 70 cm of sediment in GC-6 is composed of black, clayey silt with traces of sand and shell and is representative of New Haven CDM (Figure 3-11). The second layer of sediment extends from 70 cm down to 122 cm and is similar to the cap material but displays a noticeable increase in water content. As a result, the second stratum is likely to be a constituent of the New Haven UDM. Two thin layers of sands and gravel also appear to be part of the heterogenous UDM deposit. From 123 cm to 210 cm of penetration, several strata of clays, silts, and sands make up a deposit of historic dredged material originating from disposal activity at the CLIS 89 mound. 3.2 CLIS 94 Mound 3.2.1 Bathymetry The new CLIS 94 mound is evident in both the large 2.56 km? (1600 m x 1600 m) and the smaller 1.0 km? (1000 m x 1000 m) survey areas. The mound is approximately 490 m wide at the center with a minimum depth of 15.75 m (Figure 3-12). The CLIS 94 mound is irregularly shaped with the apex of the mound 20 m northwest of the first position of the 1994 “CDA” disposal buoy (CDA #1). The mound becomes broader and less pronounced as it extends to the south. The new mound has completely incorporated the historic CS 90-1 mound and encroaches on the northeast flank of the historic CLIS 90 mound. Depth difference plots indicate a mound height of 3.0 m at the apex (Figure 3- 2) Barge logs indicated that approximately 290,900 m3 of dredged material was released at the CDA 94 buoy positions. Volume calculations based on depth differences between the July 1994 and September 1995 surveys indicate that 169,600 m? of sediment accumulated in the vicinity of the disposal buoy (Appendix A: Table 3-2). A large percentage of the 121,300 m3 mass balance shortfall can be accounted for by restricting the size of the analysis models and closely monitoring the development of the CLIS 94 mound. The refocused analysis of the CLIS 94 bathymetric data has revealed a significant amount of consolidation, mainly due to compression and de-watering of the UDM deposit at the center of the mound during capping operations. Bathymetric survey data collected by Ocean Surveys, Inc. (OSI) of Old Saybrook, Connecticut, at the precap (18 December 1994) and interim cap (23 April 1995) stages of development, in conjunction with SAIC's baseline (July 1994) and postcap (September 1995) surveys, were used to document the development of the CLIS 94 mound as well as detect significant amounts of central mound consolidation. By performing several depth Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 35 CLIS 1994 Disposal Mound 1000 m x 1000 m Survey Area 41° 09.500° N 41° 09.250" N- 72° 53.250° W 72° 53.000° W 72° 52.750° W CLIS Depths in Meters NAD 27 a) Om 200 m Figure 3-12. Bathymetric chart of the 1000 m x 1000 m survey area over the CLIS 94 mound with plotted CDA 94 buoy positions, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 36 Depth Difference July 1994 versus September 1995 41° 09.500° N- 41° 09.250° N 72° 53.250° W 72° 53.000° W 72° 52.750° W CLIS Differences in Meters 200m Figure 3-13. Depth difference plot of SAIC's July 1994 baseline survey versus SAIC's September 1995 postcap survey, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 differencing routines with the four bathymetric data sets, both total accumulations and apparent losses of material can be identified. By comparing a scaled down version of SAIC's baseline survey in July 1994 to the OSI precap bathymetry, a UDM deposit with a height of 2.75 m and a width of 380 m was detected south of the CDA buoy positions (Figures 3-14, 3-15, and 3-16). The apex of the UDM mound was located approximately 145 m south of the CDA #1 buoy position. DAMOS disposal logs reported the deposition of approximately 129,900 m3 of UDM at CLIS between the dates of 30 November and 13 December 1994 (Appendix D: Table 1). Volume difference calculations detected a total accumulation of 114,700 m3 of new material in the vicinity of the CDA buoy (Appendix A: Table 3-2). By utilizing the bathymetric profile of the disposal mound at the precap stage of development, calculations based on successive bathymetric surveys accounted for 88% of the barge log estimates submitted by on-site inspectors. These findings represent extremely good agreement between the two methods of volume estimates (barge volume vs. sequential bathymetric survey). The first phase of capping over the CLIS 94 mound was performed from 16 January 1995 through 22 April 1995 (Appendix D: Table 2). During that time period an estimated barge volume of 41,700 m? of CDM was released over the initial UDM deposit, isolating the majority of the contaminated material from the sediment/water interface. An interim cap bathymetric survey was performed on 23 April 1995 to document the progress of capping operations. The depth difference calculations based on comparisons of the April 1995 interim cap and July 1994 baseline surveys show the total accumulation of material over the CLIS 94 mound (Figures 3-17 and 3-18). A maximum height of 2.75 m was detected over the CLIS 94 mound, and the deposition of CDM has caused the dredged material apron to expand to the north, east, and south, increasing its diameter to approximately 490 m. Further bathymetric analysis between the December 1994 and April 1995 bathymetric surveys revealed a large pocket of consolidation over the center of the disposal mound. Depth difference plots indicate a net loss in mound height, up to 1.0 m relative to the precap stage of development (Figure 3-19). The deposition of 41,700 m3 of capping material over the UDM deposit caused the formation of three peaks of CDM approximately 1.25 m thick over the north, southeast, and southwest regions of the mound. The majority of the CDM was reportedly released over the fringes of the consolidation pocket during the initial stages of capping operations (Figure 3-19). Volume calculations detected 38,664 m3 of new material over the restricted analysis area, which is considered to make up the ring of accumulation around the CLIS 94 mound. In addition, a negative volume of 26,500 m3 Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 38 SAIC July 1994 Baseline Bathymetry me ~~ 41° 09.400° N 41° 09.300’ N+ 72° 53.200. W = 72°53.100°W 72° 53.000° W CLIS Depths in Meters NAD 27 a Om 100m 200 m Figure 3-14. Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CS 90-1 mound, SAIC's July 1994 baseline survey, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 39 CLIS 1994 Disposal Mound OSI Precap Bathymetry, December 1994 41° 09.400° N- , 41° 09.300° N 41° 09.200° N 72° 53.200°W = 72°53.100°W 72° 53.000° W CLIS* = Mound Height in Meters NAD 27 i Om 100 m 200 m Figure 3-15. Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CLIS 94 mound UDM deposit, OSI's December 1994 precap survey, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 CLIS 1994 UDM Deposit Depth Difference SAIC July 1994 Baseline versus OSI December 1994 Precap 41° 09.400° N 41° 09.300° N 7) urvey Artifact 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Mound Height in Meters NAD 27 a Om 100 m 200 m Figure 3-16. Depth difference plot of SAIC's July 1994 baseline survey versus OSI's December 1994 precap survey with plotted CDA 94 buoy positions, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 41 CLIS 1994 Mound OSI April 1995 Interim Cap Bathymetry 41° 09.400° N 41° 09.300° N 41° 09.200° N 72° 53.200° W 72° 53.100° W 72° 53.000° W Depths in Meters NAD 27 Om 100 m Figure 3-17. Bathymetric chart of the 675 m x 500 m area of concentrated analysis over the CLIS 94 mound at interim cap status, OSI's April 1995 interim cap survey, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 42 CLIS 1994 Mound Depth Difference SAIC July 1994 versus OSI April 1995 Total Accumulation of 41° 09.400" N aterial at Phase 1 Cap Stage 41° 09.300° N 41° 09.200° N 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Mound Height in Meters NAD 27 Figure 3-18. Depth difference plot of SAIC's July 1994 baseline survey versus OSI's April 1995 interim cap survey, overlaid with the detectable margin of the UDM deposit, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 43 Phase 1 Apparent CDM Thickness Depth Difference OSI December 1994 versus OSI April 1995 Bathymetry 41° 09.400’ N CDM & Accumulation Net Consolidation 41° 09.300° N 41° 09.200° N Artifact Accumulation -++ CDM Release Positions (700 yd?) 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Mound Height in Meters NAD 27 ES Om 100 m 200 m Figure 3-19. Depth difference plot of OSI's December 1994 baseline survey versus OSI's April 1995 interim cap survey, overlaid with the reported 700 yd? barge release positions, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 44 of material was found and is considered to be the product of the central mound consolidation (Appendix A: Table 3-2). These results suggest that the amount of consolidation was significant, concentrated in the UDM deposit, and expedited by the placement of capping material. The area of dredged material subsidence showed an overall reduction in height up to 1.0 m beyond the thickness of the new cap material. This major dredged material consolidation within the center of the mound is responsible for 22% of the 121,300 m3 mass balance shortfall experienced in the standard baseline to postcap volume difference calculations. From 24 April to 27 May 1995 the final 119,300 m3? of capping was released over the CLIS 94 mound (Appendix D: Table 2). The bottom feature was resurveyed in September 1995, three months after capping operations were completed (Figure 3-20). Comparisons between the September postcap and April interim cap surveys show the additional capping material placed over the CLIS 94 mound (Figure 3-21). Major accumulations of CDM were detected in the vicinity of the CDA buoy, as well as over the northwest and southeast flanks of the mound. Volume calculations have determined an additional of 51,000 m3 (43%) of CDM detectable through the use of successive bathymetric surveys had accumulated over the CLIS bottom (Appendix A: Table 3-2). Larger disposal barges (4000 yd?) were employed during the last phase of capping and were fundamental in the placement of a large volume of capping material in a short period of time (35 days). Further analysis of the postcap survey shows an apparent ring of CDM approximately 375 m in diameter clearly visible as “Total Net CDM Accumulation” as well as a central “Total Net Consolidation” feature (Figure 3-22). The majority of smaller barge (700 yd3) release points appear to be north-northwest of the CDA #2 buoy position, adding to the small mound of capping material visible at the interim cap stage of development. The northern CDM feature is 3.0 m high at the apex and 110 m wide and is responsible for the irregular shape of the CLIS 94 mound. The remainder of the CDM layer exhibits several other high spots south and southeast along the ring. The 4000 yd? capacity barges concentrated their efforts over the central area of the mound. As a result, the pocket of consolidation discovered in the analysis of earlier surveys seems to have been filled to a certain degree, as a total negative volume of 10,800 m? is the end result (Appendix A: Table 3-2). By tracking the three stages of development for the CLIS 94 mound, the UDM deposit appears to be successfully capped and laterally stable (Figure 3-23). The survey artifact that is visible as an irregular projection of UDM in most of the depth difference plots corresponds to the northeast apron of the CLIS 90 mound. Differences in lane Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 45 CLIS 1994 Mound SAIC September 1995 Bathymetry 41° 09.400" N 41° 09.300° N-. 41° 09.200° N 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Depths in Meters NAD 27 Om 100 m Figure 3-20. Bathymetric chart of the 675 m Xx 500 m area of concentrated analysis over the CLIS 94 mound at postcap status, SAIC's September 1995 postcap survey, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 46 Phase 2 Cap Material Placement Depth Difference SAIC September 1995 versus OSI April 1995 41° 09.400° N 41° 09.300° N 41° 09.200°N - 700 yd? barge release positions ©} - 4000 yd? barge release positions 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Mound Height in Meters NAD 27 = Om 100m 200 m Figure 3-21. Depth difference plot of SAIC’s September 1995 postcap survey versus OSI's April 1995 interim cap survey with plotted CDA 94 buoy and reported barge release positions, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 47 Final Apparent CDM Thickness Depth Difference SAIC September 1995 versus OSI December 1994 Total Net CDM Accumulation 41° 09.400°N 41° 09.300°N 41° 09.200° N Survey Artifact + - phase 1 CDM +- - phase 2 CDM 700 yd? } - phase 2 CDM 4000 yd* 72° 53.200° W 72° 53.100° W 72° 53.000° W CLIS Mound Height in Meters NAD 27 | om 100 m 200 m Figure 3-22. Depth difference plot of SAIC's September 1995 postcap survey versus OSI's December 1994 precap survey, overlaid with the CDA 94 buoy and reported barge release positions, 0.25 m contour interval Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 4§ Stages of Mound Development CLIS 1994 Capped Mound Detectable Dredged Material Deposits Postcap Stage 41° 09.400°N 41° 09.300° N 41° 09.200° N Survey Artifact 72° 53.200° W 72° 53.100° W 72° 53.000° W Figure 3-23. Plot of the three stages of CLIS 94 mound development, overlaid with the CDA 94 buoy positions Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 49 orientation and gridding routines between SAIC and OSI are responsible for its appearance. Due to the effects of consolidation, tracking volumes of material throughout the different phases of mound development accounted for more of the reported volumes than comparisons over long expanses of time. The cumulative volume detected by the use of multiple surveys is 204,362 m3 or 70% of the total reported volume (Appendix A: Table 3- 2). Without the use of interim survey data, volume calculations detected 70,643 m3 of CDM, 44% of the reported cap material volume, and 169,624 m3 or 58% of the total material volume. These latter calculations are typically utilized as part of most disposal and/or Capping projects where depositional volumes are quantified using differences in depth between a predisposal and a postcap survey only. Results of in-depth research studies of the operations surrounding clamshell dredging and subaqueous disposal of dredged material have demonstrated an apparent 41% reduction in volume between consecutive bathymetric surveys (Tavolaro 1984). Differences of this magnitude are expected and are attributed to barge volume over-estimation, the volume of material undetectable through acoustic bathymetric data processing techniques, and dredged material consolidation over time; they do not represent actual material loss. 3.2.2 REMOTS® Sediment-Profile Photography REMOTS® sediment-profile photography was used to document benthic recolonization, as well as map thin layers of material and assess the overall impact of dredged material deposition at the CLIS 94 disposal mound. Complete REMOTS® results for the disposal mound are available in Appendix B: Table 2. 3.2.2.1 Sediment Grain Size and Stratigraphy Fresh dredged material was detected and measured at every station except for one replicate at 200N. Replicate-averaged mean dredged material thickness ranged from 8.8 cm to full camera penetration (20 cm) (Appendix A: Table 3-3). Redox rebound intervals, areas showing evidence of intermittent or seasonal oxidation below the oxidized surface layer, were noted at stations 200 m and 300 m from the center. Physical REMOTS® parameters showed that the major modal grain size was consistently reported as >4 phi (silt and clay), indicating the deposition of predominantly fine-grained dredged material. However, the sediments detected at Station 100E were slightly coarser (4 to 3 phi) silts and fine sands. The replicate-averaged mean camera Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 50 penetration ranged from 12.86 cm to full penetration (20 cm), generally increasing towards the center of the mound, except at the center station (14.47 cm; Appendix A: Table 3-3). In general, the lower camera penetration values correlated with the highest surface disturbance values; values >1 cm occurred at 200S, 300E, 300N, 300W, and CTR. The primary cause of surface disturbance over the CLIS 1994 mound was biogenic activity. 322222 Benthic Community Assessment The replicate-averaged mean Redox Potential Discontinuity (RPD) values ranged from 0.46 cm at CTR to 4.03 cm at 300S (Figure 3-24). A gradient of RPDs increased from the center out towards the edges of the mound, ranging from approximately 0.5 cm at CTR, to 1.5 cm at 100 m, to 2-4 cm at 300 m. The overall average RPD value for the mound was 1.76 cm, despite indications of low dissolved oxygen resulting from hypoxic conditions within the bottom waters over many REMOTS® sediment-profile photography stations (100W, 200S, 200W, 300E, 300N, 300S, 300W). No methane was noted in any photograph obtained on the surface of the CLIS 94 mound. However, the RPD depths varied among replicates of the same station, indicating a patchy benthic environment. Replicate A at Station 300S exhibits a mean RPD depth of 5.87 cm indicative of a healthy benthic environment (Figure 3-25A). Conversely, replicate B of Station 300S displays a shallow RPD and indications of low dissolved oxygen (Figure 3-25B). The successional stage status was relatively advanced for Station 300S and the remainder of the CLIS 94 mound as an area recently impacted by dredged material (Germano et al. 1994). Station 100W was the only station without evidence of Stage III organisms in any of the replicates (Figure 3-26). The most common stages noted in the replicate photographs were Stage I and Stage I on III. Median Organism-Sediment Index (OSI) values of the replicates ranged from -1 at 200S (low RPD, low DO) to 9 at 200N. Low OSIs (<6) are concentrated along the western and southern arms of the grid primarily due to the indication of a low dissolved oxygen event (Figure 3-24). 3.3 FVP Mound The experimental FVP mound, located in the far northeast quadrant of CLIS, was monitored extensively as part of the Field Verification Program during the 1980s. Historically, benthic infaunal communities inhabiting the FVP sediments have been more susceptible to benthic disturbances, relative to other CLIS mounds. Composed of uncapped UDM deposited in 1983, the FVP mound continues to be periodically monitored as part of the DAMOS Program. No bathymetric data were collected over the historic Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 41° 09.500° N 51 CLIS 1994 Disposal Mound September 1995 REMOTS® Stations over Bathymetry and Fresh Dredged Material Deposit See ags 41° 09.250° N+ ~~ ye 1.77; 4:23 > 70.91 / 0 : IA NHAV63 /\NHAV}93, A NHAV 93 aan eae 2001 i “4o0E WEEE \ N \ / \ H aN / 23 pa es Lua ey. Se go Ne 72° 53.250° W Overall CLIS ee 1.76 Depths in Meters A NAD 27 Osi 5.93 = Om 200 m Figure 3-24. Distribution of RPD (cm) and OSI values over the CLIS 94 mound, overlaid on September 1995 bathymetry and final detectable margin of the mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 52 uoneIs sues ay) JO souTUOS oy) UTM ([{] OG MOT snsi9A [Y] dd¥y deep) SUOTIIPUOD dItUAQ UT sadUaIATJIp ay) Surkepdsip SOE UoNRIg Iv syderso}oyd gSLOWAA ‘“S7Z-¢€ WANs (a) (Vv) Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 2p} CLIS 1994 Disposal Mound September 1995 REMOTS® Stations over Bathymetry and Fresh Dredged Material Deposit 41° 09.500° N 41° 09.250° N , 9) ee ( he A nuaves y) Naa 93 ( wan, .AOOIEL | --600Be 3.) 22a 8 Vie! ay (eee a y eae: 72° 53.250° W 72° 53.000° W 72° 52.750° W CLIS Depths in Meters NAD 27 a Om 200 m Figure 3-26. Distribution of successional stage assemblages over the CLIS 94 mound, overlaid on September 1995 bathymetry and final detectable margin of the mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 54 FVP mound during the September 1995 survey at CLIS. However, a full thirteen-station REMOTS® sampling grid was occupied over the mound. Complete REMOTS® results for the FVP disposal mound are available in Appendix B: Table 3. 3.3.1 Sediment Grain Size and Stratigraphy Grain size and surface roughness data indicated no distinct pattern at the FVP disposal mound. The major modal grain size at every station was >4 phi, except for one replicate at 200W where the major mode was 4 to 3 phi. The replicate-averaged mean camera penetration ranged from 12.73 to 15.69 cm (Appendix A: Table 3-4). Boundary roughness values ranged from 0.52 cm to 1.33 cm. The primary cause of surface disturbance was biogenic except at individual replicates at CTR and 200E where boundary roughness was classified as physical in nature. Dredged material was present in all stations, except for the replicates at stations 300 m from the center. At stations where dredged material was present, replicate-averaged thicknesses ranged from approximately 5 cm at 100W and 200N to full penetration (20 cm) at several stations (Appendix A: Table 3-4). The apparent absence of dredged material 300 m from the center may be attributed to complete reworking of historical dredged material, to the extent that there are no recognizable indicators commonly attributed to dredged material. Redox rebound intervals were noted in one replicate at several stations (100N, 100E, 200W). 3.3.2 Benthic Community Assessment Replicate-averaged RPDs ranged from 0.77 cm at 100N to 2.84 cm at 200E (Figure 3-27; Appendix A: Table 3-4). This range is slightly higher than the average RPD depths measured in the three reference areas. Methane was detected in two replicates at Station 100E, but indications of low dissolved oxygen within the bottom waters were not noted in any photograph. The majority of the REMOTS® stations occupied over the FVP mound displayed Stage III activity within the surface sediments. Only one station showed no evidence of Stage III organisms (100N; Figure 3-28). Replicate median OSIs ranged from 2 at 100E and 100N (low RPD, no Stage III, methane) to 8 at 300W (Figures 3-29A and 3-29B). Several stations at FVP indicated, as at the CLIS reference areas, a decrease in benthic habitat quality relative to prior monitoring surveys. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 2p) FVP Disposal Mound September 1995 REMOTS® Stations ot i=) WY 1 As 4 1.07 = 41° 09.500° N A 7 0.77 A S 2 41° 09.400’ N4 2:38 ‘ : 4 1.08 2.84 0.96 YS A A 2 cn 4 “A, 6 | 41° 09.300° N 41° 09.200° N 72° 51.900° W Overall RPD 1.62 A AN kt — OZ —SCtCtCS OSi 5.5 100 m Figure 3-27. Distribution of RPD (cm) and OSI values over the FVP mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 56 FVP Disposal Mound September 1995 REMOTS® Stations 41° 09.500° N 41° 09.400’ N I, III I, Il I, III I, TW I, Ill I, Il A IS A A A A RS ) 7) S Ss & Qe. Qe. 41° 09.300° N 41° 09.200° N 72° 51.900° W 72° 51.700° W ND = No Data CLIS NAD 27 100 m 200 m Om Figure 3-28. Distribution of successional stage assemblages over the FVP mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 57 punow qAj oy) Jo uoide pur 19]99 ay] UsaMI0q SUOTIIPUOD oIYUAq UL ssousJayJIp Survtdsip ({) MODE Pur (VW) NOOT suoneis Jo sydeisoi0yd gS LOWAY °67-¢ 2NSIy (a) (Vv) Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 58 3.4 CLIS Reference Areas As part of the DAMOS tiered monitoring protocols, reference area data are collected to provide a baseline against which results from the dredged material mounds are compared. CLIS-REF has been a reference area for CLIS since the beginning of the DAMOS Program. The two newer reference areas, 2500W and 4500E, have been monitored since approximately 1987. A total of thirteen stations were occupied over the three reference areas. Complete REMOTS® results for the CLIS reference areas (CLIS- REF, 2500W, 4500E) are available in Appendix B: Table 4. 3.4.1 Sediment Grain Size and Stratigraphy Physical indicators of the benthic environment include the grain size and boundary roughness of the sediment surface. The major modal grain size was >4 phi in all reference station replicates. Replicate-averaged camera penetration ranged from 8.93 cm to 13.68 cm (Appendix A: Table 3-5). Boundary roughness values ranged from 0.42 cm to 1.23 cm and were determined to be caused by biogenic or unidentifiable processes. Biological disturbance tends to be associated with a mature sediment deposit, whereas physical disturbance is often associated with recent benthic impact. Dredged material was not identified in any photograph, and no redox rebound intervals were identified. No station exhibited indications of methane or low dissolved oxygen. 3.4.2 Benthic Community Assessment Replicate-averaged RPD depths at all three reference areas ranged from 0.62 cm to 1.60 cm (Appendix A: Table 3-5). This is a relatively low range of RPDs for CLIS reference stations and was lower than the averaged values for all three dredged material mounds sampled in 1995. In the past, reference area RPDs ranged from 0.55 cm to 2.7 cm during the July 1994 survey; 5.68 cm to 1.49 cm in June 1991; and 3.4 cm to 6.6 cm in July 1990 (Morris and Tufts 1997; Wiley and Charles 1995; Germano et al. 1995). The successional stage status at all reference stations was most commonly Stage I on Stage III, indicating a mature benthic assemblage. Only one station exhibited no Stage III community in any replicates (Station 3 at CLIS-REF). Stage II was identified in one replicate at 4500E. Median OSIs at the reference areas generally ranged from 6 to 7, except for a minimum OSI of 3 at CLIS-REF Station 3 (lack of Stage III) and a maximum of 8 at 4500E Station 3. OSIs of 6 or less were present at four of five CLIS-REF stations, Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 59 one of four stations at 2500W, and one of four stations at 4500E. These relatively low OSIs are due primarily to the low RPDs measured in CLIS reference areas. The REMOTS® photographs collected during previous monitoring surveys (July 1990, June 1991, and July 1994) indicated healthy benthic environments, with median OSI values consistently reported as 6 or above. The slight decline in habitat quality observed at several reference area stations during the August 1995 survey suggests the presence, or recent occurrence, of environmental stress (i.e., hypoxic bottom waters). Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 60 4.0 DISCUSSION During the September 1995 REMOTS® sediment-profile photography surveys over NHAV 93, CLIS 94, FVP, and the CLIS reference areas, a trend of lower than expected RPDs and indications of low dissolved oxygen (DO) concentrations was observed. Seasonal hypoxia, due to eutrophication in the protected waters of the central and western Long Island Sound causing the degradation of water quality, had apparently affected both the benthic and near-bottom pelagic habitats. The Long Island Sound Study (LISS), a US Environmental Protection Agency (EPA) monitoring program, officially recognizes the onset of hypoxia at a DO concentration of 3.0 mg-I'. However, the appearance of hypoxic conditions in the bottom waters and surface sediments has been documented with DO concentrations as high as 5.0 mg-I’ (LISS 1990). For the past several years DAMOS monitoring activity has not included water sampling for DO or other water quality parameters as part of its field operations because the instantaneous measure during the relatively short survey period was not sufficient to determine seasonal events. However, further investigation was required to determine whether the decline in the RPD and OSI values at CLIS and the reference stations was related to disposal activity or a regional hypoxia event. A comprehensive DO data set for stations throughout the Long Island Sound was obtained from the Connecticut Department of Environmental Protection, Water Management Division (DEP). The data was collected as part of the DEP Long Island Sound Summer Hypoxia Monitoring Program and consisted of surface and bottom DO values for 18 primary stations that were monitored throughout the year as well as a number of secondary summer stations (June to September). Seasonal monitoring stations 23, 26, and 27 and annual monitoring stations H2 and H4 were chosen due to their location relative to CLIS (Figure 4-1). Although the data for seasonal stations 23, 26, and 27 does not Comune through the September 1995 field effort, a decrease in DO concentrations (4.5 mg:I ) was observed at stations 23 and 27 in mid-August (Julian Day 226) suggesting a seasonal DO event within the central Long Island Sound region (Figure 4-1). Stations 23 and 27 are situated in close proximity to the disposal site in similar water depths and bottom current patterns. Both stations show a downward progression in DO values for the summer of 1995. Station 26, approximately 7 km north of CLIS, is located in shallower water and tends to be influenced by the drainage of the Quinnipiac River and New Haven Harbor. The can at Station ae show a drastic reduction in bottom water DO, decreasing from 8.2 mg: 1! to 3.4 mg: 1! over the first forty days of the monitoring program. Oxygen levels then show significant rebound to 6.4 mg-I! on Julian Day 226, displaying higher concentrations of DO data, relative to the deeper stations. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 61 py66l IO} LZ pue aR ADAG SSS SZNONINIS | | fecal {TNOLLVIs | 1 suoijeis buljdwes “ 97 ‘ ‘QUIIIJAI IOJ poppe saiep AdAINS SOWVC ‘S661 pue sdeq neqn{ COE j vw WOSAXO poagossicyT $66] FoUTUANS e1eq Ayjend sw dad wadeuy0D~~ (Lar) wails poajossig 92VLS Lt NOLLWLS seh SNOLLYLS fNOLLVIS = uasHAXO PdsAjOSsig 1N91}09UUOD punos puejs| Huo7 jesjzueg €Z SUONLIS SULIOIUOU IOUS Je spud OC WONOg puke suoneig surjdures UasAXO POATOSSIC UONIAOIg [eUsUMMOIMAUT JO JuoUNIedag MoNd.0NNIO_D 94) JO UONISOg sheq very i} 4 wn (1/3~W) w294xO poarossi WadAXE Poafossig PE6. JOUTAMS eye Aqyengdy soIeM TAC 3nd IDeuUUO,) "T-p aansiy Roa) + ~~ Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 The data collected at primary monitoring stations H2 and H4 also suggest a seasonal hypoxic episode was occurring in the central Long Island Sound region during the summer months. A steady decrease in detectable oxygen was observed from Julian Day 100 (7 April 1995) through Julian Day 226 (mid-August; Figure 4-2). As the water temperature began to increase in the spring and summer months, water quality in Long Island Sound was slowly depressed by falling DO concentrations and lack of significant fresh water input from the surrounding tributaries due to drought. Station H4 was located in the center of Long Island Sound, approximately 6 km southeast of CLIS, in water 30 m deep (Figure 4-1). Bottom DO concentrations at Station H4 dropped to 4.2 mg: -!' in early August and remained at those levels through the September 1995 survey. Station H2 showed a major decrease in DO in ony and mid- August, with values falling to 2.4 mg: I’ then slowly increasing to 3.8 mg- I! by late August. This station was located 6.5 km northwest of the center of CLIS in water 15 m deep (Figure 4-1). In September, dissolved oxygen concentrations began to climb towards 6.0 mg- iF and continued to increase as the autumn of 1995 progressed. The primary and secondary station data both indicated a decrease in dissolved oxygen concentrations within the central Long Island Sound region immediately preceding the September 1995 field activity. The REMOTS® sediment-profile photographic survey over the project mounds and reference areas at CLIS observed the aftermath of the hypoxic event within the benthic community. Although DO concentrations seemed to be increasing at the time of the REMOTS® survey, complete recovery within the benthic community (OSI values 26, deep RPD, presence of Stage II and Stage III assemblages) would not be seen for several weeks. The degree and effects of the seasonal hypoxia varied with the sampling location at CLIS during the 1995 monitoring cruise. In general, the CLIS reference areas showed a decline in benthic habitat quality with lower RPD depths than expected and no Stage Il organisms present. The NHAV 93 mound showed improvement relative to the July 1994 survey; Stage I organisms occupied the surface sediments, and Stage III individuals were present at depth. The CLIS 94 mound recovered better than expected with a Stage I on Ill recolonization status, and several deep RPD measurements, but displayed indications of a low DO event. The FVP mound continued to exhibit difficulty in fully establishing and maintaining a stable benthic community with low RPD and OSI values near the mound center. The REMOTS® data from the FVP mound show a steady decline in the apparent RPD and OSI since the 1991 CLIS survey, with the exception of Station CTR, where the OSI has ranged from 4 to 6 since the 1987 CLIS survey (Figures 4-3 and 4-4). This trend was also noted in the data collected during the CLIS survey in November 1993. The Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 63 C661 10} pH pue ZH suoneis surdures uashxC paajossiq wonsda01g [eWOUIMOMIAUY JO JuoUNIedsq INoNIBUUO| 1 sUOR.NUIDN0D OC WoON0g UI sasueyo paarasqg Adains @SLOINAY SIT9 sdeq uernf ; | i { i C661 BICC UASAxE pdalossiq WIO}WO0g "T-p dN (T/SIN) UeSAXC) pealossiq] Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 Apparent RPD at FVP, 1991-95 400E TOON 100W CTR [| June 91 fg Nov 93 | | Sept 95 Figure 4-3. Histogram displaying recorded RPD calculations from June 1991, November 1993, and September 1995 at Stations 100E, 100N, 100W, and CTR over the FVP mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 49 orientation and gridding routines between SAIC and OSI are responsible for its appearance. Due to the effects of consolidation, tracking volumes of material throughout the different phases of mound development accounted for more of the reported volumes than comparisons over long expanses of time. The cumulative volume detected by the use of multiple surveys is 204,362 m3 or 70% of the total reported volume (Appendix A: Table 3- 2). Without the use of interim survey data, volume calculations detected 70,643 m? of CDM, 44% of the reported cap material volume, and 169,624 m? or 58% of the total material volume. These latter calculations are typically utilized as part of most disposal and/or capping projects where depositional volumes are quantified using differences in depth between a predisposal and a postcap survey only. Results of in-depth research studies of the operations surrounding clamshell dredging and subaqueous disposal of dredged material have demonstrated an apparent 41% reduction in volume between consecutive bathymetric surveys (Tavolaro 1984). Differences of this magnitude are expected and are attributed to barge volume over-estimation, the volume of material undetectable through acoustic bathymetric data processing techniques, and dredged material consolidation over time; they do not represent actual material loss. 3.2.2 REMOTS® Sediment-Profile Photography REMOTS® sediment-profile photography was used to document benthic recolonization, as well as map thin layers of material and assess the overall impact of dredged material deposition at the CLIS 94 disposal mound. Complete REMOTS® results for the disposal mound are available in Appendix B: Table 2. 3-2-2 Sediment Grain Size and Stratigraphy Fresh dredged material was detected and measured at every station except for one replicate at 200N. Replicate-averaged mean dredged material thickness ranged from 8.8 cm to full camera penetration (20 cm) (Appendix A: Table 3-3). Redox rebound intervals, areas showing evidence of intermittent or seasonal oxidation below the oxidized surface layer, were noted at stations 200 m and 300 m from the center. Physical REMOTS® parameters showed that the major modal grain size was consistently reported as >4 phi (silt and clay), indicating the deposition of predominantly fine-grained dredged material. However, the sediments detected at Station 100E were slightly coarser (4 to 3 phi) silts and fine sands. The replicate-averaged mean camera Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 50 penetration ranged from 12.86 cm to full penetration (20 cm), generally increasing towards the center of the mound, except at the center station (14.47 cm; Appendix A: Table 3-3). In general, the lower camera penetration values correlated with the highest surface disturbance values; values >1 cm occurred at 200S, 300E, 300N, 300W, and CTR. The primary cause of surface disturbance over the CLIS 1994 mound was biogenic activity. 322222 Benthic Community Assessment The replicate-averaged mean Redox Potential Discontinuity (RPD) values ranged from 0.46 cm at CTR to 4.03 cm at 300S (Figure 3-24). A gradient of RPDs increased from the center out towards the edges of the mound, ranging from approximately 0.5 cm at CTR, to 1.5 cm at 100 m, to 2-4 cm at 300 m. The overall average RPD value for the mound was 1.76 cm, despite indications of low dissolved oxygen resulting from hypoxic conditions within the bottom waters over many REMOTS® sediment-profile photography stations (100W, 200S, 200W, 300E, 300N, 300S, 300W). No methane was noted in any photograph obtained on the surface of the CLIS 94 mound. However, the RPD depths varied among replicates of the same station, indicating a patchy benthic environment. Replicate A at Station 300S exhibits a mean RPD depth of 5.87 cm indicative of a healthy benthic environment (Figure 3-25A). Conversely, replicate B of Station 300S displays a shallow RPD and indications of low dissolved oxygen (Figure 3-25B). The successional stage status was relatively advanced for Station 300S and the remainder of the CLIS 94 mound as an area recently impacted by dredged material (Germano et al. 1994). Station 100W was the only station without evidence of Stage III organisms in any of the replicates (Figure 3-26). The most common stages noted in the replicate photographs were Stage I and Stage I on III. Median Organism-Sediment Index (OSI) values of the replicates ranged from -1 at 200S (low RPD, low DO) to 9 at 200N. Low OSIs (<6) are concentrated along the western and southern arms of the grid primarily due to the indication of a low dissolved oxygen event (Figure 3-24). 3.3 FVP Mound The experimental FVP mound, located in the far northeast quadrant of CLIS, was monitored extensively as part of the Field Verification Program during the 1980s. Historically, benthic infaunal communities inhabiting the FVP sediments have been more susceptible to benthic disturbances, relative to other CLIS mounds. Composed of uncapped UDM deposited in 1983, the FVP mound continues to be periodically monitored as part of the DAMOS Program. No bathymetric data were collected over the historic Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 Median OSI at FVP, 1991-95 Oo NM fF O 400N 100W | June 91 Nov 93 [| Sept 95 100E Figure 4-4. Histogram displaying recorded OSI values from June 1991, November 1993, and September 1995 at Stations 100E, 100N, 100W, and CTR over the FVP mound Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 66 benthic population at FVP appears to be more susceptible to environmental stress than the benthic infaunal populations of the capped mounds. As a result, hypoxic events or other disturbances tend to have a more pronounced and longer lasting effect on the invertebrates inhabiting the uncapped sediments of FVP. The Field Verification Program was concluded in 1988 with a report which determined that, in comparison to upland containment and wetland creation, subaqueous mound development within a designated disposal site is the most environmentally sound method of disposing of large volumes of UDM (Peddicord 1988). The FVP mound was targeted for capping during the 1993 disposal season using excess CDM generated by the New Haven Harbor maintenance dredging project. A lack of an adequate volume of CDM during the NHAV 93 mound development caused the deletion of the FVP capping operations phase of the project (Morris et al. 1996). However, in order to improve the conditions of the benthic environment over the FVP mound, an effort should be made in future disposal seasons to cap the experimental mound with a 0.5 m thick layer of CDM. In addition, the adoption of the FPEIS disposal site center of CLIS shifts the entire disposal site 362 m west-southwest, leaving the majority of the FVP mound outside of the disposal site boundaries. In order to officially conclude the EPA/WES joint experiment, the area surrounding the FVP mound, ideally, should be restored to near ambient conditions with the placement of a silt cap over the exposed UDM deposit. The cap over the NHAV 93 mound continues to support a stable benthic community with marked improvement at stations CTR, 200N, and 400S relative to the July 1994 survey (Morris and Tufts 1997). Despite a decrease in dissolved oxygen, the mound was supporting Stage I and Stage III individuals in the surface and subsurface sediments. There was a noticeable lack of Stage II individuals over all three project mounds as well as the three reference areas, suggesting an intolerance to lower water column induced DO concentrations. The Stage I surface dwellers may have been able to tolerate the hypoxia or may be the pioneering species recolonizing the sediments as DO concentrations began to increase. The overall integrity of the NHAV 93 mound remains uncompromised eighteen months after the completion of the New Haven Capping Project. There were no noticeable changes in size or shape over the NHAV 93 mound, indicating the large bottom feature is stable. The moderate consolidation detected since the completion of capping operations is well within the forecast norm. The mound is expected to continue to consolidate as pore water extrusion and basement material compression yield to the shear weight of the capped sediment deposit over the coming years (Poindexter-Rollings 1990). Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 67 Geotechnical cores collected over the NHAV 93 mound within the past two years have attempted to document the development and subsequent consolidation of the NHAV 93 mound. Despite the use of precision navigation and consistently revisiting stations, the observed heterogeneity within the UDM and historic dredged material layers of the NHAV 93 mound tends to lessen the ability to track sediment layers through the five-member time-series data set. A certain degree of repeatability within the collected sediments was required to follow individual sediment strata throughout the project, providing a baseline used to quantify changes in layer thickness. However, cross-sections of a dredged material mound have been proven to be valuable as “snapshot” data as well as ground-truth data for comparison with subbottom profiling (Morris and Tufts 1997). Geotechnical coring as an investigative technique could be improved by acquiring longer cores to obtain a sample of the ambient bottom throughout the time-series data set. The gravity coring device utilized during the New Haven Capping Project had difficulty penetrating the consolidated center of the 2.5 m high NHAV 93 mound, resulting in partial recovery. The use of a pneumatic vibrocore equipped with a 5 m steel core barrel would ensure complete penetration into the basement material to provide a baseline for consolidation measurements. In addition, the use of chemical sampling of the recovered sediment could provide valuable information on the origins of the various strata. Determination of the relative concentrations of various contaminants would allow for the differentiation of basement, historic, UDM, and CDM layers in either ubiquitous or heterogeneous samples. The use of repetitive bathymetric surveys during the New Haven Capping Project was proven to be an invaluable tool in observing the usually hidden dynamics of dredged material mound construction (Morris et al. 1996). The same technique was employed during the post processing of the CLIS 94 mound bathymetric survey data. A total of four bathymetric survey data sets were used to follow the construction of the CLIS 94 mound and expose the accumulation and consolidation of the bottom feature. By utilizing SAIC's July 1994 and September 1995 surveys in conjunction with OSI's December 1994 and April 1995 data sets, the events leading up to the final capped mound could be tracked and volumes of material calculated. In the past, efforts have been made to account for differences in the volume of material reported in disposal barge logs to the volumes of material detected acoustically. The issue of mass balance has become clouded by large volumes of undetectable mound apron material, over-estimation of barge volume by on-site inspectors, and compaction of dredged material on the seafloor (Tavolaro 1984). The repetitive surveys over the CLIS 94 mound have found central mound consolidation during disposal and capping activity to Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 68 be another factor causing large discrepancies between barge estimates and detected volumes. By restricting the window of analysis to the area immediately around the CLIS 94 mound and performing various depth and volume differencing routines, physical changes in the dredged material deposit and in the volume of material were detected. A large central pocket of dredged material consolidation within the CLIS 94 mound was detected during the interim cap survey of the bottom feature. This pocket of consolidation is believed to be the chief cause of the mass balance shortfall. Although the use of multiple surveys improved the tracking of large volumes of material disposed, rapid consolidation due to compression and de-watering complicate precise volume comparisons. Studies conducted at CLIS by the US Army Corps of Engineers, Waterways Experiment Station (WES), have documented significant amounts of dredged material consolidation over short periods of time (0.5 m in 30 days; Poindexter-Rollings 1990). The observed behavior of the CLIS 94 mound supports those findings with up to 1.0 m of consolidation over a 126-day period of time without evidence of UDM surface movement or collapse of the mound. If the CLIS 94 mound continues as predicted, the mound should subside an additional 0.5 m to 0.75 m over the next year and then show gradual reduction due to compression of the basement material over the next 5 to 10 years. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 69 5.0 CONCLUSIONS The September 1995 field efforts at CLIS allowed SAIC and NED to examine three bottom features constructed by three different dredged material management approaches. The NHAV 93 mound is an example of a highly successful CAD structure. The mound was found to have maintained its lateral stability and cap integrity. The site management strategy of creating a ring of mounds from smaller disposal projects to accept large quantities of dredged material within the basin has proven to be an efficient method of UDM lateral containment and CAD mound construction. This management strategy should continue at CLIS in order to provide large cells of lateral containment and maximize the available space within the 6.86 km? area of the disposal site. Overall, the NHAV 93 mound appears to be recovering from the disposal activity as anticipated (Germano et al. 1994). The mound supports a stable benthic infaunal population with Stage I and Stage III organisms present in the surface and subsurface sediments. Three areas of concern detected during the July 1994 monitoring cruise (CTR, 200N, and 400S) show marked improvement with deeper RPD depths and higher OSI values despite the occurrence of a hypoxic event in the central Long Island Sound region. The sediments of the NHAV 93 mound are expected to support a Stage II on Stage III population in the coming years barring benthic disturbance (hypoxia, trawling, etc.). The development of the CLIS 94 mound represents the next step in the successful site management strategy. The construction of an independent capped mound to the northeast of the NHAV 93 mound begins to enclose another basin at CLIS. The CLIS 94 mound appears to be a discrete and stable bottom feature that has completely incorporated the historic CS 90-1 mound that was formed during the 1989/90 disposal season. Approximately 129,900 m3 of UDM from Norwalk Harbor, New Haven Harbor, and Long Wharf Pier projects was deposited over CS 90-1. A total of 161,000 m3 of CDM was | placed over the unsuitable material to isolate it from the marine environment. A CDM to UDM ratio of 1.24:1.0 was found to be sufficient to cap the UDM deposit without lateral containment as both disposal and capping operations were consistently controlled. The overall size and shape of CLIS 94, as well as the volume of new material detected by bathymetry, suggests that mound development proceeded without difficulty. Comparisons between the July 1994 (baseline) and September 1995 (postcap) surveys performed by SAIC and the results of a precap and interim cap bathymetric surveys obtained through Ocean Surveys, Inc. support that conclusion. Intensive analysis of the four data sets detected significant central consolidation within the UDM layer during the first phase of capping operations, supporting previous studies performed by WES in the 1980s. Up to 1.0 m of dredged material subsidence was detected over a 126-day period Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 70 between the precap and interim cap surveys of the CLIS 94 mound. The pocket of central consolidation was responsible for a large percentage of a 121,300 m? shortfall in the mass balance of material. However, agreement between the reported barge volume and the volume detected acoustically improved by tracking the volume through the four phases of mound development. Physical and biological indicators of overall benthic community health suggest the CLIS 94 mound is recovering faster than expected. A few stations displayed signs of low dissolved oxygen; however, the majority of the mound was characterized with moderate to deep RPDs and evidence of Stage III organism activity. Asa result, the overall OSI value of 5.23 suggests the CLIS 94 mound should reach full recovery (RPD > 6) in the next two years. Conversely, the FVP mound, composed of an uncapped UDM deposit, is continuing to show signs of low habitat quality with shallow RPDs and low OSI values over the center of the mound. Although the regional hypoxic event may have contributed to the problems at FVP, the mound has traditionally been more susceptible to benthic disturbances and slower to recover, relative to other project mounds. Now that the Field Verification Program is complete and long-term monitoring has documented a chronic response, the FVP mound should be capped in order to isolate the UDM from the sediment/water interface and return the area to near-ambient conditions. In addition, the movement of the disposal site boundaries to the west-southwest lends further support to this recommendation. The low water column dissolved oxygen event that seemed to affect the FVP mound was also noticed over the CLIS 94 and NHAV 93 mounds, as well as the three CLIS reference areas (CLISREF, 4500E, and 2500W). Data obtained from the Connecticut DEP indicated a summer hypoxia event occurred several days before the September 1995 monitoring cruise. The REMOTS® photographs obtained over the reference areas and project mounds depict the aftermath of the low DO event within the benthic community. The Stage I organisms occupying the surface sediments could represent benthic recolonization as the DO concentrations began to rise approximately 10 days before the survey. In order to avoid a downward trend or skew in future data, monitoring cruises in the western and central Long Island Sound should be scheduled for early July. By conducting environmental sampling activity earlier in the summer and avoiding the possibility of recurring hypoxia, NED will gain a more realistic perspective of the benthic community at the Long Island Sound disposal sites. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 71 6.0 REFERENCES Fredette, T. J. 1994. Disposal site capping management: New Haven Harbor. Reprinted from Dredging '94, Proceedings of the Second International Conference, November 13-16, 1994. US Army Corps of Engineers, New England Division, Waltham, MA. Germano, J. D.; Parker, J.; Wiley, M. B. 1995. Monitoring cruise at the Central Long Island Sound Disposal Site, July 1990. DAMOS Contribution No. 94 (SAIC Report No. SAIC 90/7594&C89). US Army Corps of Engineers, New England Division, Waltham, MA. Germano, J. D.; Rhoads, D. C.; Lunz, J. D. 1994. An integrated, tiered approach to monitoring and management of dredged material disposal sites in the New England Region. DAMOS Contribution No. 87 (SAIC Report No. SAIC-90/7575&234). US Army Corps of Engineers, New England Division, Waltham, MA. Long Island Sound Study (LISS). 1990. Status report and interim actions for hypoxia management. US Environmental Protection Agency, Region I, Boston, MA and Region II, New York, NY. Morris, J. T.; Tufts, G. J. 1997. Monitoring cruise at the Central Long Island Sound Disposal Site, July 1994. SAIC Report No. 327. Final report submitted to US Army Corps of Engineers, New England Division, Waltham, MA. Morris, J. T.; Charles, J.; Inglin, D. C. 1996. Monitoring surveys of the New Haven Capping Project, 1993-1994. SAIC Report No. 319. Final report submitted to US Army Corps of Engineers, New England Division, Waltham, MA. Morton, R. W. 1983. Status report: disposal operations at the Central Long Island Sound Disposal Site. SAIC Report No. C25. Submitted to US Army Corps of Engineers, New England Division, Waltham, MA. Mueller, C. 1994. Results of the Central Long Island Sound Disposal Site sediment testing: October 1994. SAIC Environmental Testing Center report submitted to SAIC Marine Environment Division, Newport, RI. Murray, P. M.; Selvitelli, P. 1996. DAMOS navigation and bathymetry standard operating procedures. SAIC Report No. 290. DAMOS Reference Report. US Army Corps of Engineers, New England Division, Waltham, MA. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 72 Naval Underwater Systems Center (NUSC). 1979. Disposal Area Monitoring System (DAMOS) annual data report - 1978. Submitted to US Army Corps of Engineers, New England Division, Waltham, MA. Peddicord, R. K. 1988. Summary of the US Army Corps of Engineers/US Environmental Protection Agency field verification program. Tech. Report D-88-6. US Army Corps of Engineers, Waterways Experiment Station, Vicksburg, MS. Poindexter-Rollings, M. E. 1990. Methodology for analysis of subaqueous sediment mounds. Tech. Report D-90-2. US Army Corps of Engineers, Waterways Experiment Station, Vicksburg, MS. Rhoads, D. C.; Germano, J. D. 1982. Characterization of organism-sediment relations using sediment-profile imaging: An effective method of Remote Ecological Monitoring of the Seafloor (REMOTS® System). Mar. Ecol. Prog. Ser. 8:115-128. Rhoads, D. C.; Germano, J. D. 1986. Interpreting long-term changes in benthic community structure: A new protocol. Hydrobiologia 142:291-308. SAI. 1979. Stamford-New Haven disposal operation: monitoring survey report. DAMOS Contribution No. 1. US Army Corps of Engineers, New England Division, Waltham, MA. SAIC. 1985. Standard operating procedure manual for DAMOS monitoring activities: volume I and volume II. DAMOS Contribution No. 48 (SAIC Report No. SAIC- 85/7516&C48). US Army Corps of Engineers, New England Division, Waltham, MA. SAIC. 1995. Sediment capping of subaqueous dredged material disposal mounds: an overview of the New England experience, 1979-1993. DAMOS Contribution No. 95 (SAIC Report No. 90/7573&C84). US Army Corps of Engineers, New England Division, Waltham, MA. Silva, A. J.; Brandes, H. G.; Brogan, D. R. 1996. Geotechnical characterization of the NHAV 93 mound: Coring and core processing summary, August 1995 survey. DAMOS Project Central Long Island Sound, New Haven Harbor Maintenance 1993-1995. Report submitted to SAIC, Newport, RI. Available from: Geotechnical Consulting Engineers, Saunderstown, RI. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 73 -Tavolaro, J. F. 1984. Sediment budget for clamshell dredging and ocean disposal activities in the New York Bight. Environ. Geol. Water Sci. 6(3):133-140. US Army Corps of Engineers, New England Division. 1982. Final programmatic environmental impact statement for the disposal of dredged material in the Long Island Sound region. Waltham, MA. Wiley, M. B.; Charles, J. 1995. Monitoring cruise at the Central Long Island Sound Disposal Site, June 1991. DAMOS Contribution No. 97 (SAIC Report No. SAIC 92/7621&C100). US Army Corps of Engineers, New England Division, Waltham, MA. Monitoring Cruise at the Central Long Island Sound Disposal Site, September 1995 chal sillipbioneth Stet " selon ino 298 Le B wert 2 se mie i a ¥ a ator psy. bieaeil pt : Kina th | wang Chapiceinailesn site RAEN BM 2 plage lhl pe gh aN ene Agi aiieintine vunthectio Reiter oe sameeren: leat ia ice ee date Shire Whee bis Bi haat s we * Slee lv : i ct 1s Siemeiensite ‘iyo ign tn k kh ty ak: ae 6 Mis F iia: Py: dee va prone a. sida chalacnesce puecad 5 seit: i bi ipatore. Nes iis ett dis; Mena: Lopereaion: ‘monitoring ee q belehiione om Men Ws Arye ‘oii i dasa agrviens %, iad Bing wW aheblaaee WE “ = Bk. LORS, Sen ib iy eben ee ars ste i | . PET Shh Ay i ohne, rr 3 ii gi 2 a a ' WHA 83 tet, & ee iy dais eH proce enna ANOS Propant Cuntrat leap ‘Folunt Sound). New havent ¥ 198° ORS Reet waned wr SAkG; i ies LOR ets Page Lae, Sunray Leal i om il ogra 7) Ere Quan nba Cabo INDEX aerobic, 25 azoic, 25 barge, ix, 4, 7, 34, 37, 44, 49, 67, 70 disposal, ix, 7, 44, 67 benthos, viii, ix, 4, 7, 8, 14, 23, 25, 49, 50, 54, 58, 59, 60, 62, 66, 69, 70, 72 ampeliscids, 25 amphipod, 25 bivalve, 25 deposit feeder, 25 macro-, 25 polychaete, 25 bioassay, 25 bioturbation feeding void, 25 Black Rock Harbor, ix, 7 body burden bioassay, 25 boundary roughness, 23, 54, 58 buoy, ix, 4, 7, 10, 14, 34, 37, 44 disposal, ix, 34 capping, viii, 1, 4, 7, 18, 34, 37, 44, 49, 66, 67, 69, WS Central Long Island Sound (CLIS) FVP, viii, ix, 7, 8, 14, 50, 54, 60, 62, 64, 65, 66, 70 Norwalk (NOR), 1, 27, 69 conductivity, 12 consolidation, viii, 9, 18, 34, 37, 44, 49, 66, 67, 68, 69 containment, viii, ix, 4, 7, 66, 69 contaminant, 67 CTD meter, 12 density, 12, 16 deposition, ix, 4, 7, 23, 25, 37, 49 detritus, vill dispersive site Cornfield Shoals (CSDS), 1 disposal site Central Long Island Sound (CLIS), viii, ix, 1, 4, 7, 8, 10, 12, 14, 16, 18, 23, 25, 27, 32, 34, 37, 44, 49, 50, 54, 58, 60, 62, 66, 67, 68, 69, 70, 71, 72, 73 Cornfield Shoals (CSDS), 1 New London (NLDS), 1 dissolved oxygen (DO), 23, 50, 54, 58, 60, 62, 66, 70 dredging clamshell, 49, 73 feeding void, 25 Field Verification Program (FVP), viii, 7, 50, 66, 70 grain size, 16, 18, 49, 54, 58 habitat, 59, 60, 62, 70 hypoxia, ix, 27, 60, 62, 66, 69, 70, 71 methane, 25, 50, 54, 58 National Oceanic and Atmospheric Administration (NOAA), 12 organics, 27 oxidation, 18, 23, 49 recolonization, viii, 4, 8, 14, 18, 23, 25, 49, 62, 70 reference area, ix, 8, 14, 23, 27, 54, 58, 59, 60, 62, 66, 70 reference station, 8, 58, 60 REMOTSS®, viii, ix, 7, 14, 18, 25, 27, 49, 50, 54, 58, 59, 60, 62, 70, 72 boundary roughness, 23, 54, 58 Organism-Sediment Index (OSI), ix, 23, 25, 27, 34, 37, 49, 50, 59, 60, 62, 65, 67, 69, 70 redox potential discontinuity (RPD), ix RPD REMOTSS®, redox potential discontinuity (RPD), ix, 23, 25, 27, 50, 54, 58, 59, 60, 62, 64, 69, 70 sediment clay, 27, 32, 34, 49 gravel, viii, 27, 32, 34 sand, 27, 32, 34 silt, 27, 32, 34, 49, 66 sediment sampling cores, 9, 14, 16, 27, 32, 67, 72 shore station, 10 Statistical testing, 7 stratigraphy, 18, 49, 54, 58 succession pioneer stage, 25, 66 successional stage, 25, 50, 58 survey baseline, 12, 18, 27, 34, 37, 44, 58, 67, 69 bathymetry, viii, ix, 7, 8, 10, 12, 14, 18, 34, 37, 44, 49, 67, 69 predisposal, 49 REMOTS®, 14, 25, 62 subbottom, 67 temperature, 12, 62 tide, 10, 12 topography, 8, 10 toxicity, 25 trawling, 8, 69 volume difference, 37, 44 estimate, 37 waves, 12 APPENDIX A TABLES Table 2-1. APPENDIX A TABLES September 1995 Central Long Island Sound Disposal Site REMOTS® Table 2-2. Table 3-la. Table 3-1b. Table 3-2. Table 3-3. Table 3-4a. Table 3-4b. Table 3-4c. | Table 3-5. Camera Stations August 1995 Central Long Island Sound Disposal Site Geotechnical Core Positions and Lengths REMOTS® Parameters Summary Table for the September 1995 Survey of the NHAV 93 Mound REMOTS® Parameters Summary Table for the July 1994 Survey of the NHAV 93 Mound Summary Table of the Reported and Detected Volumes of Dredged Material Disposed over the CLIS 94 Mound REMOTS® Parameters Summary Table for the September 1995 Survey of the CLIS 94 Mound REMOTS® Parameters Summary Table for the September 1995 Survey of the FVP Mound REMOTS® Parameters Summary Table for the November 1993 Survey of the FVP Mound REMOTS® Parameters Summary Table for the June 1991 Survey of the FVP Mound REMOTS® Parameters Summary Table for the September 1995 Survey of the CLIS Reference Areas ae i vata noioenesed Appendix A: Table 2-1 September 1995 Central Long Island Sound Disposal Site REMOTS® Camera Stations Horizontal Datum: North American Datum of 1927 Latitude NHAV 93 41° 09.122'N 72° 53.453' W CLIS 94 41° 09.343'N 72° 53.099' W FVP 41° 09.390'N 72° 51.750'W 2500 W 41° 09.254' N 72° 55.569' W 4500 E 41° 09.254'N 72° 50.565' W CLIS REF 41° 08.085' N 72° 50.109' W 41° 09.390' N 41° 09.444'N 41° 09.498'N 41° 09.552' N 41° 09.336' N 41° 09.282' N 41° 09.228'N 41° 09.390'N 41° 09.390' N 41° 09.390' N 41° 09.390'N 41° 09.390' N 41° 09.390'N 41° 09.227'N 41° 08.135'N 72° 53.453' W 72° 53.453' W 72° 53.453' W 72° 53.453' W 72° 53.453' W 72° 53.453' W 72° 53.453' W 72° 53.310' W 72° 53.167'W 72° 53.024'W 72° 53.596' W 72° 53.739' W 72° 53.882' W 72° 53.099' W 72° 53.099' W 72° 53.099' W 72° 53.099' W 72° 53.099' W 72° 53.099' W 72° 53.099' W 72° 53.028' W 72° 52.956' W 72° 52.885' W 72° 53.171'W 72° 53.242' W 72° 53.313' W 72° 51.750' W 72° 51.750' W 72° 51.750' W 72° 51.750' W 72° 51.750' W 72° 51.750' W 72° 51.750' W 72° 51.679' W 72° 51.607'W 72° 51.536' W 72° 51.821'W 72° 51.893' W 72° 51.964' W 72° 55.640' W 72° 55.465' W 72° 55.567' W 72° 55.664' W 72° 50.638' W 72° 50.583' W 72° 50.602' W 72° 50.518' W 72° 50.106' W 72° 50.028' W 72° 50.007' W 72° 50.238' W 72° 50.112'W Appendix A: Table 2-2 August 1995 Central Long Island Sound Disposal Site Geotechnical Core Positions and Lengths Horizontal Datum: North American Datum of 1927 Latitude Replicate of. 41° 09.280° 41° 09.180° 41° 09.134° 41° 09.078" 41° 08.996" 72° 53.334" 72° 53.385" 72° 53.458" 72° 53.536" 72° 53.629° 72° 53.509" 72° 53.403" 72° 53.443° 72° 53.407" 72° 53.521" 72° 53.306" 41° 09.182° 41° 09.100° 41° 09.136" 41° 09.175" 41° 09.075" 41° 09.264° Zea Lee Le CeLe SSSSSSEEzz2&2 Ssx Aijfs ‘A@1B-8AI10 “sBDyy joys puD PUDs YIM {IIs Aeu6-eAI1IO "PUDS YIM JIS JODIE “ys Apups ‘y9DIg “AD|O Ajiis ‘Aei6-@A}|o pub yODIG “pups Ajijs euy *yODIq oj Aei6-eA}|IO Tees ae KeIB-OMIO Neus ‘puns Aele ‘pups wig “sBDY [}OYS UIA Ws) *AD|D we ‘ ‘ Kolb onecAlie att pups Ae6-e A110 Salis ‘Ae16 eniio 0} 2190Ig SL “Apo Aus 4OD]g pup qIs Kadnjo SyonIq “Apo Ayjts ‘Aes6-98Ajjo puD yODIg Jo sIoAD] Buyyouayy ‘pups umoig “Ape Ayjts 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Jo ; WG'0 s¥2yD0d YUM HIS Ae ADIO “YODIG “ins AeAnjo 49014 ‘pups Jo S@ODIF- UM Apj> Ajiis ‘Yos 901g. . WO doolsod sujuoOWw V66L AInr M e10D {W]] UOYD1eUed “HIS AKakpjo ‘Aai6-anio *PUDS Jo SJ@AD] UIA ss Aai6-anqjo O} AODIE ‘pups uMoig "yuaJUOd JOJDM PSeSD9JOU] UJI jus A@ADIS ‘YODIG *s6p4) |}eYusS PUD ‘j@A0J6 ‘pups uy ‘ADD pub jus ueal6 of yODIG “Ajo Ayis ‘yos ‘yODIg Is Apups uee6 of yODIg “Add Ayis ‘yos ‘ODI WG’? W O'S Wg" WO'l wggQ WO 7661 YB ~y APPENDIX D DAMOS DISPOSAL LOG TABLES APPENDIX D DAMOS DISPOSAL LOG TABLES Table 1. UDM Disposal Activity over the CLIS 94 Mound Table 2. CDM Disposal Activity over the CLIS 94 Mound Appendix D: Table 1 UDM Disposal Activity over the CLIS 94 Mound TALLAMDGE BROTHERS |NORWALK HARBOR TALLAMDGE BROTHERS |NORWALK HARBOR TALLAMDGE BROTHERS |NORWALK HARBOR TALLAMDGE BROTHERS |NORWALK HARBOR LONG WHARF PIER LONG WHARF PIER LONG WHARF PIER LONG WHARF PIER LONG WHARF PIER LONG WHARF PIER UNITED ILLUMINATING UNITED ILLUMINATING UNITED ILLUMINATING cooo0oao~0a~e~a~aeaeeGedaeaeAaGaMOeGeeaGMGeGeGeGGeGeGCeeGeececca0coc0c0c00o0cd lo Mo Mo MoM -MoM-M-M-M-M-M-M—-M-M-M--o--- -- - - NEW HAVEN HARBOR ee Appendix D: Table 2 CDM Disposal Activity over the CLIS 94 Mound = ast eee ta ee ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC ASSOC AT THE GUILFORD YC CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL WEST RIVER CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL ocooo0oo0o0cooeoco0co0o0ccoe0coecececocecocoacocc0cocecoccacoac0ccaccoccco00c0cd cooo0o0o0oocoe0cocaooco0coococcaoaoaooco0occoq0cococo0cocoec0c0c0co0c0co0co0c00c00c000cd NATIT NTTITNANTAAAANANNTNTNTNNNNNNANANNNANANAANANN Appendix D: Table 2 (continued) Sa TEETER psf aa} eles CENED-CD-EDA |STONY CREEK CT CHANNEL 31-Mar-95 STONY CREEK CT CHANNEL 01-Apr-95 STONY CREEK CT CHANNEL 03-Apr-95 STONY CREEK CT CHANNEL 06-Apr-95 07-Apr-95 07-Apr-95 08-Apr-95 08-Apr-95 09-Apr-95 09-Apr-95 10-Apr-95 11-Apr-95 a — STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA oooooooo0co0co0coocoacocadcoaaoaoaococoaocacoacaoaoaoaomMvaococcce0o0ncnd oooooo0coea~0ceae0aaoaaaaaaaaac0ecae0c0cecoececoecoceececececococceco0c00cd Appendix D: Table 2 (continued) SS ee CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL STONY CREEK CT CHANNEL CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA CENED-CD-EDA coo0o0o0c00o0coe0ceCcC0cecCeCGCecCeceecececeece0c0cce0c000acCcCeecC0o0no C0000 0CCCOCMCOCOMAOMOMOVGGAGGCACGCGMOeGOeeGCGeCeCGeCCeGCMAGeCeCeAeACACGeCeCecC0Ood PINE ORCHARD MARINE TERMINAL-BRANFORD|CLIS Appendix D: Table 2 (continued) ee PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD PINE ORCHARD MARINE TERMINAL-BRANFORD cooooooo0oo0co0coco0co0cocococo0co0ocoeco0cocn NINTNTTTTNTNNNANNNNANTIAAANANN CDM ye? | 210616) ie : pesabhls tias | EEO OE a 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