Search
Search Results
-
29241. [Image] Restoring Harmony in the Klamath Basin
-
29242. [Image] Ecology of shortnose and Lost River suckers in Tule Lake National Wildlife Refuge, California : progress report, April - November 1999
Ecology of shortnose and Lost River suckers in Tule Lake National Wildlife Refuge, California, Progress Report, April - November 1999 Lisa A. Hicks, U. S. Fish and Wildlife Service, Klamath Basin National ...Citation Citation
- Title:
- Ecology of shortnose and Lost River suckers in Tule Lake National Wildlife Refuge, California : progress report, April - November 1999
- Author:
- Hicks, Lisa A.; Mauser, David M.; Beckstrand, John; Thomson, Dani
- Year:
- 2000, 2005
Ecology of shortnose and Lost River suckers in Tule Lake National Wildlife Refuge, California, Progress Report, April - November 1999 Lisa A. Hicks, U. S. Fish and Wildlife Service, Klamath Basin National Wildlife Refuge, Route 1, Box 74, Tulelake, CA 96134 David M. Mauser, U. S. Fish and Wildlife Service, Klamath Basin National Wildlife Refuge, Route 1, Box 74, Tulelake, CA 96134 John Beckstrand, U. S. Fish and Wildlife Service, Klamath Basin National Wildlife Refuge, Route 1, Box 74, Tulelake, CA 96134 Dani Thomson, U. S. Fish and Wildlife Service, Klamath Basin National Wildlife Refuge, Route 1, Box 74, Tulelake, CA 96134 Introduction The Lost River ( Deltistes luxatus) and shortnose ( Chasmistes brevirostris) suckers were federally listed as endangered species on July 18, 1988 ( Federal Register 53: 27130- 27134). Both sucker species are relatively long- lived, have a limited geographic range, and are endemic to the Upper Klamath Basin of Northern California and Southern Oregon. Habitat degradation from water diversions and loss of riparian and wetlands habitats associated with agricultural development within their historic range is believed to be the major reason for the species decline ( U. S. Fish and Wildlife Service 1993). A more detailed description on the life history, habitat requirements, and causes of decline of the species can be found in the Lost River and Shortnose Sucker Recovery Plan ( U. S. Fish and Wildlife Service 1993). Tule Lake National Wildlife Refuge ( NWR), established in 1928, consists of 2 return flow sumps ( Sump 1( A) and 1( B)) totaling 13,000 acres surrounded by 17,000 acres of intensively farmed lands ( Fig. 1). The refuge and surrounding private agricultural lands occupy the historic lake bed of Tule Lake, a 95,000 acre lake and marsh area that was reclaimed in the early 1900fs as part of the Klamath Reclamation Project. Current management of the refuge is directed by the Kuchel Act of 1964 which mandates the refuge be managed for the major purpose of waterfowl management but with optimal agricultural use that is consistent therewith. Both sumps are shallow ( 0.1 - 2.0 m) and consist of approximately 10,500 acres of open water with a 2,500 acre shallow (< 0.1 m) emergent marsh at the northeast corner of Sump 1( A). Tule Lake has been identified as a potential refugia for both sucker species ( U. S. Fish and Wildlife Service 1993). Tule T like National Wildlife Sump 3 Lease lands Field . Station Cocbetative Fanning Fields Area J Lease Lands Sump 2 I ease I , ands Figure 1. Tule Lake National Wildlife Refuge, California. During winter, water within the sumps is comprised primarily of local runoff and during summer water is comprised primarily of irrigation return flows, originating from Upper Klamath Lake. Summer water quality in the sumps is similar to other water bodies within the Upper Klamath Basin and is considered hypereutrophic ( Dileanis et al. 1996). Water quality problems include low dissolved oxygen ( DO) and high hydrogen ion concentrations ( pH) and unionized ammonia. Water quality in the Tule Lake sumps is directly affected by hypereutrophic conditions in Upper Klamath Lake ( U. S. Fish and Wildlife Service 1993). Studies conducted after publication of the Shortnose and Lost River Sucker Recovery Plan indicate that Tule Lake contains an estimated 159 ( 95% CI = 48- 289) shortnose and 105 ( 95% CI = 25- 175) Lost River suckers ( Scoppetone and Buettner 1995). Confidence intervals for these estimates are large because of small sample sizes and low rates of recapture. Recruitment rates for the Tule Lake population via spawning below Anderson- Rose Dam is low with significant larval production occurring only in 1995 ( monitoring occurred 1991- 99) ( M. Buettner, pers. comm). Entrainment from the irrigation system is likely the largest source offish for Tule Lake ( U. S. Bureau of Reclamation 1998). Both species of suckers in Tule lake are in good physical condition relative to fish in Clear Lake and Upper Klamath Lake with Tule Lake fish being generally heavier and exhibiting few if any problems with parasites or lamprey. ( Scoppetone and Buettner 1995). U. S. Bureau of Reclamation ( Reclamation) biologists tracked 10 radio- marked suckers in Tule Lake from 1993- 95. From these studies, specific use areas by time period were identified with over 99% of radio locations occurring in Sump 1( A). Of particular importance from these studies was identification of an over- summer site in the south central region of Sump 1( A) termed the ADonut Hole# ( DH). In early 1999, the U. S. Fish and Wildlife Service ( Service) proposed a wetland enhancement project on the 3,500 acre Sump 1( B). The project was designed to improve habitat for waterfowl and other associated wetland species as well as improve water quality through the conversion of Sump 1( B) from an open body of shallow water to an emergent year- round flooded wetland. The primary mechanism to create the desired habitat condition is a series of annual spring/ summer drawdowns thereby creating conditions suitable for germination of desired emergent plant species. Of principal concern in developing the project was the potential effects on suckers within the sumps. Because of the proximity of both sucker species in adjacent Sump 1( A), a project monitoring plan was developed to ascertain the potential effects of the Sump 1( B) Project on suckers and water quality. Our monitoring design benefitted from studies of water quality and sucker movements by Reclamation biologists from 1992- 95. This report summarizes findings of the first year= s pre- project monitoring effort ( April- December, 1999) relative to water quality and movements of radio- marked suckers. Objectives 1. Describe seasonal distribution and movement patterns of both sucker species in Tule Lake NWR and determine if fish movements have changed since initial studies by Reclamation biologists in 1993- 95. 2. Characterize water quality, in space and time, of areas used by adult suckers compared to areas which are not used. 3. Document and describe movements of radio- marked suckers to spawning areas below Anderson- Rose dam. 4. Determine whether recruitment of larvae and juvenile was occurring below Anderson- Rose Dam. Methods Monitoring radio- marked adult suckers In April and May, 1999, Reclamation biologists captured 14 suckers and surgically implanted radio- transmitters ( ATS, Isanti, MN) having a projected battery life of 12 months. Each transmitter had an external antennae that exited the body cavity near the lateral line of the fish. Eleven Lost River and 3 shortnose suckers were captured using trammel nets at the northwest corner of Sump 1( A) ( 9 fish) and immediately downstream of Anderson- Rose Dam on the Lost River ( 5 fish) ( Table 1). We located radio- marked fish via air thrust boats using a scanning receiver and 4- element yagi antennae. Fish were located fish 4 times/ month during March and April, 2 times/ month from May through September, and once per month from October through December. Fish not located via boat were located from fixed wing aircraft. We determined fish locations by moving as close as possible to undisturbed fish and recording locations with a Global Positioning System ( GPS). All GPS positions consisted of 180 rover points/ location and were differentially corrected via post processing software ( PFinder ver. 2.11). We recorded depth information at each fish location. To determine timing and duration of the spawning migration, we monitored radio-marked fish from vehicles on the east levee of the Lost River downstream of Anderson- Rose Dam. Table 1. Data from Lost River and shortnose suckers captured on Tule Lake National Wildlife Refuge, California and Anderson- Rose Dam, Oregon in 1999. RADIO TAG 165.043 165.063 165.073 165.103 165.084 165.094 164.641 164.863 164.494 164.854 165.054 164.845 164.763 164.914 CAPTURE DATE 4/ 2/ 99 4/ 2/ 99 4/ 2/ 99 4/ 2/ 99 4/ 2/ 99 4/ 2/ 99 4/ 9/ 99 4/ 2/ 99 4/ 9/ 99 4/ 30/ 99 5/ 5/ 99 5/ 5/ 99 5/ 18/ 99 5/ 18/ 99 CAPTURE LOCATION TULELAKE SUMP1A TULELAKE SUMP 1A TULELAKE SUMP 1A TULELAKE SUMP 1A TULELAKE SUMP1A TULELAKE SUMP 1A TULELAKE SUMP1A TULELAKE SUMP1A TULELAKE SUMP 1A ANDERSON ROSE DAM ANDERSON ROSE DAM ANDERSON ROSE DAM ANDERSON ROSE DAM ANDERSON ROSE DAM SPECIES LOST RIVER LOST RIVER LOST RIVER SHORTNOSE SHORTNOSE LOST RIVER SHORTNOSE LOST RIVER LOST RIVER LOST RIVER LOST RIVER LOST RIVER LOST RIVER LOST RIVER SEX FEMALE FEMALE FEMALE MALE FEMALE FEMALE FEMALE MALE FEMALE FEMALE MALE MALE MALE FEMALE WEIGHT NO DATA NO DATA NO DATA NO DATA NO DATA NO DATA 2830 g 1040 g 5260 g NO DATA 2214 g 1542g 2350 g 1811 g FORK LENGTH 777 mm 681 mm 754 mm 473 mm 523 mm 754 mm 544 mm 440 mm 775 mm 753 mm 556 mm 486 mm 594 mm 477 mm PIT TAG NO. 1F3E34432C 1F39064959 1F4C5A6754 1F07315752 1F31462743 1F4C5A6754 1F3726750F 1F36490062 1F37103466 1F390F1801 1F3E2A7702 1F36443235 1F30753309 1F390E6B2F Recruitment Reclamation biologists conducted larval and juvenile sucker surveys during May and June by sampling, visually and with dip nets, the emergent vegetation at the periphery of the Lost River downstream of Anderson- Rose Dam. Egg viability surveys were conducted in the gravel sediments immediately below the dam in May. Water quality We preselected water quality sampling sites ( Fig. 2, Table 2) in Sump 1( A) to correspond to adult sucker use areas as determined by studies of radio- marked adult suckers conducted by Reclamation in 1993- 95 ( Fig. 3). We selected 2 sites in Sump 1( B) which met or exceeded the minimum depth requirement (> 3ft) for both sucker species ( M. Buettner, pers. comm.) after referring to 1986 bathymetric maps. We attempted to obtain data from each site twice/ month. We moved 2 sample sites ( Donut Hole and Donut Hole Northwest) early in the summer and 1 site ( Donut Hole West) ( Fig. 2) during mid- summer to better represent summer use locations of radio- marked fish. From May through November, we measured water quality parameters ( dissolved oxygen ( DO), hydrogen ion concentration ( pH), and temperature (° C)) using DataSonde 3, 4 and 4a= s ( Hydrolab Corp., Austin, Texas) ( hereafter referred to as Hydrolabs) 26 cm ( 12 in) above the sediment. We suspended Hydrolabs, within PVC tubes, from metal fence posts driven into the sediment. Data were collected hourly over a 96 hr period at each monitoring site. We downloaded data from Hydrolabs using the Hyperterminal software package v. 690170 to a personal computer. Unit probes were cleaned and calibrated according to Hydrolab guidelines ( Hydrolab Corporation 1997) and local geographic standards. Using the same deployment schedule as with our Hydrolabs, we sampled turbidity at each site using a Portable Turbidimeter model 21 OOP ( Hach Corp., P. O. Box 389, Loveland, CO 80539). We collected water samples 27 cm ( 12 in) above the sediment at each sample site. We measured turbidity in NTUs, following the guidelines in the product manual and we measured water depth using a hand- crafted wooden pole, marked in measured increments. We summarized water quality data using Microsoft 8 EXCEL software v. 97 SR- 1 and SPSS for Windows release 9.0.0. Because of the apparent difference in summer water quality in the DH versus other sampling sites, data were summarized as DH sites and Non- DH ( NDH) sites. Tule Lake NWR Water Quality Monitoring 1999 MfSVTHOLE \ OKTIIH ' w Background Hvdrolon> Luke m Mudflats Uplands X Water Vionitonny Stations ( Hydrolafa sites) MK ker Radio \ ckmcin L. Hicks. D. .1 Beckitraod, K Miller, USFWS Background HydfOlOf} Sat'I Wetlands Invcnlon LSI Sh S Map Projection UTMZCM IO, WGS-* 4 By: L. Hkks. USFWSUSBR 02/ 00 i Figure 2. Water quality sample sites, Tule Lake National Wildlife Refuge, California, 1999. 8 Table 2. Characteristics of water quality sampling sites, Tule Lake National Wildlife Refuge, Tulelake, California, 1999. SITE NAME NORTHWEST SUMP 1A DONUT HOLE NORTHWEST DONUT HOLE WEST DONUT HOLE SOUTH DONUT HOLE DONUT HOLE EAST ENGLISH CHANNEL WEST SUMP IB EAST SUMP IB PUMP 10 SUMP 1A2 SITE ABBREVIATION NWS1A DHNWSlAor DHNW DHWEST DHSOUTH DHSlAorDH DHEAST ECSlAorEC WS1B ES1B PMP10 UTM N 4642199 4638316 4638881 4638144 4637299 4639024 4634604 4634153 4633948 4636635 UTME 620803 620542 321022 621355 621475 621971 625041 636647 628835 624748 DEPTH of MONITORING SITE ( m) 1 1.2 0.9 0.9 0.8 0.7 0.8 0.8 1.0 0.8 0.5 1 Depth of water at deployment 2 Pump 10 data will not be discussed in this document. Results Radio- marked suckers We located fish 231 times in locations similar to those determined by Reclamation biologists in 1993- 95 ( Figs 3- 4). Lost River and shortnose suckers did not appear to differentiate use of the sump by species; we located both species intermixed throughout the monitoring period. With the exception DH and DHNW ( Fig. 2), water quality sampling sites were close to seasonal sucker use areas. Of 14 suckers marked, mortality occurred in only 1 fish. A Lost River sucker (# X9) was tagged on 18 May at the Anderson Rose Dam; she was not located again until 23 days later on 9 June. From 9 June to 17 November, # X9 was located by signal within approximately 15 m of the original location based on the location data. It is likely that this fish died in early June within 2- 3 weeks of being radio- marked. It is unknown if this mortality was related to the stress of handling and marking or some other cause. April - May - In April- May, a period of maximum fish movements ( Figs. 5- 18), most suckers congregated in the AEnglish Channel ® between the sumps with a scattering offish located between the northwest corner of Sump 1( A) and the AEnglish Channel ® ( Fig. 4). Only 1 fish radio- marked in Tule Lake moved into the Lost River. This particular fish, a female shortnose sucker (# G9) was radio- marked in the northwest corner of Tule Lake on 9 April, was located in the AEnglish Channel ® on 14 April, and subsequently was located in Lost River below Anderson Rose Dam on 29 April and 6 May. Tule Lake Sucker Radio Telemetry \ pril 1993 - \! a> 1995 Hi tckwtstmd H) drohgy mm Marth/ Wi'lhiml • • River I Sucker Locations o Jan - Mar & Apr - May ° Jim - Sep • O t t - l h i 1 I . . . . . . ydtOl Ig) -: i '•'•, l: i M h - c .1 J I SI WS UtoBiihywwUy KkmrtiiB ••. iraOffia MapPinoiccii.- i rM2oni VM, S- » 4 • HJ I-. IKKV USffW& n SBB Figure 3. Locations of radio- marked suckers from studies conducted by U. S. Bureau of Reclamation, on Tule Lake National Wildlife Refuge, California, 1993- 1995. 10 Tule Lake NWR Sucker Radio Telemetry April - December 1999 Oregon California [ Sump 1A Background Hydrology J Lake Uplands SOcker Locations • Apr May o Jun - Sep • Oc! - Dec | Qanuthole area = * 466 acres ( manually est from fish bca Suckei EUdiQ Tdctrcter: L Hi cks, D TtccnsDn, : Nati Wedatd^ Inventory. USTWS i t Hi cfa, usFwsnrsBH o 2/ 00 Figure 4. Locations of radio- marked suckers on Tule Lake National Wildlife Refuge, California, 1999. 11 Tule Lake- Sucker Radio Telemetr> - 1999 MMti « phrnl Fish: Lost River Sucker " A9" Sex Female Length: 777 mm fag I ocation I ulc I ; ike Sump IA Tai: Dare: 04/ 02 99 Vlort. Date: 3 - O 5 ni 0 5 - 1 ni ( Surface Fixation - 4034.9( 1') Lain' ihpth 1 - 15m Itydrolah tUm » t tm fcdarl .' i rein: l. llni. i. Becb- rmc l^ . I M I ^ I V I M . Kl; nn: nli limm Xvtup,- :, rr, k, I M •'• - \ * e BMb% « ldry KIWWHI I t em ,^ wnOi-... I SB I Background Hy* » : 4.. .. , „ | WCIIWKIJ faivewior^. I'SI A S >• • ••• i •• i MZcne IC ' •..-• .: i;% i n . , i s , u s Figure 5. Movements of radio- marked sucker A9 on Tule Lake National Wildlife Refuge, California, 1999. 12 Tule Lake- Sucker Radio Telemetry ~- 1999 Hsh ], ost River Sucker"! Sc\ Female Length: UK] mm Tag Location [ We Lake Sump IA IML Dace U4/ O? W Mort Date: • i Khrr( m » depth) • 1 Mwrvl. Will. 1.1,1 I |- l Muil I t * 3 - O 5 m 0 5 - t rn ( Surtax i: Nation - 4O34. W) flyJrttlaff SiKker RacfcTclemdn: I. IliduU. Bccks CompK. i BFW8 I. a.- Mil ,. l klmulklfaun \ « » OI.. . I MM Background llyfrotogv \ « bonB| W ctlands inv « « or., U8FWS Map IVv^ vi ... i M ,. !• ' ••"• . I:-. | || ... i JFWS Figure 6. Movements of radio- marked sucker B9 on Tule Lake National Wildlife Refuge, California, 1999. 13 Tule Lake- Sucker Radio Telemetry - 1999 Fidi Lost River Sucker * C9" Sex Male Length: 619 mm Tag Location I ule Lake Sump IA Fag Date: M/ 02 w VIon. Date: { Surface Fixation - 4II34. W) tiat- ttffawmf th- frohf(\ • • Khii i> nJv|> th) H i \ iM, vh\ wtl,..., i UplniKi Lak mm MU. I n. i 3 - 0 5 ni 0 5 - 1 ru • I n kaAo Tckwdn: LHkfcaJ. Beduimd P HMUWM K V'l « • .|: I- II: I-| I I n i ii Cwnpk. I 8FWS Klmwil.[ ten< •• . : M . . . I M : mind I l > * o t i c \ Ntttaaal Wetlands Inventory* I ^| •.!•••• • • . • I -. I \ | . , K 1 1 . i •• » •• -; !:•• I II . I SFWS r Mil . Figure 7. Movements of radio- marked sucker C9 on Tule Lake National Wildlife Refuge, California, 1999. 14 Tule Lake- Sucker Radio Telemetry - 1999 Haf kgnm n BB Rh « ' i MM. Fish Shortnose Sucker " l) l>" Sex Male Length: 473 nun ail Location: I ale Lake Sump IA Tag Date 04/ 02/ 99 Mort. Date: I Surface Fixation - 41> 34. lW) /....'.:• Depth Mi, I lbtx 0- OSm ^ ^ 0 5 - 1 rti - I - ' I •' • • ' ' • I HkfcU. lUbrxilHil) I ! . . . ! - . K Mil M KlttiHtfiBttk K « Aig « : . , - , - , L . I M ''. •• Ifydrolah Kit,-* i., i.- . il ... (.. , , , i , , •. . ; „ , . . , M ! - U a d ^ r t w n d ! ! > * • ••'• • t n | XVctinjKlt [ mcTrt « . T\. • SFWS I • • . . • • , , • l:% | n ...... i M A S * £*> Figure 8. Movements of radio- marked sucker D9 on Tule Lake National Wildlife Refuge, California, 1999. 15 Tule Lake- Sucker Radio Telemetry - 1999 Fish Shortnose Sucker T39" Sc\ Female Length: 523 mm rag Location I ule I ake Sump IA rag Date M/ 02 w Date: • 1.1 I i) I 1-.. 1 • | i i . . I. llcct. M m i l l ) ] Compl- • ' "* I '• S 5> NJUOIWI Wetlands b i v c m u r y I IS I » S • ••• I " I ••. l/. nc It. i . . . : - . , ' II-. | || ..... Figure 9. Movements of radio- marked sucker E9 on Tule Lake National Wildlife Refuge, California, 1999. 16 Tule Lake- Sucker Radio Telemetry - 1999 Fish Lost River Sucker " IV Sc\ female Length: 754 mm Tag Location Tule Lake Sump 1A * rag Date 040; 99 Vkirt Date: ( Surface Fixation - 4( 134.90') Hat ground Hydrology U • : • • Rhtr< iM » < Jvpfh) • iM.., lll » r • i M. tvh\ VHl,, na 0.0,5m Uphml » 0S- 1rt. 1 - 1 5 IT » 1 £ m fackcrRadk> 1 r .. In: UfisfcaJ. Ikvkwjjjui P » •, K V, 1 • l: m: rli M a Jfcflifc* CorapUv I IFWS Uydrolth sit,- s i , i t \ t, il*> m. f n Klmwlh tfewn .\ wn < » flfa . I SBR K o t o ^ : \ ai,,, na| Wctljmd* bivcm^ f • I SFWS Map hV^ vl .. . I MZpftClO Cony aid I;-, i n , . UWTOS Figure 10. Movements of radio- marked sucker F9 on Tule Lake National Wildlife Refuge, California, 1999. 17 Tule Lake- Sucker Radio Telemetry - 1999 Fish Shortnose Sucker " Q9" I cm ale Length: 544mm I. IL1 Location Tule Lake Sump IA * rag Date 04/ 09/ 99 Mori ( Surface rloaliun - I II . . I. \'-.-\-- m.' I-K V i ! l • l : n i : r l l ! - i i : ii : . r , : . | , . I s|\ VS KlmuHi Btom Aivs 4 M1K. I SBR \ j i > i m l Wetlands invcnlon i 5FWS M. « ;. ' - . . I - . I M / . „ . • | » . I II , • I SFWS BB Ki^ i imi M \ hrvh\\ ilhiml Upland Lais Otfttk MuiJ Hals Figure 11. Movements of radio- marked sucker G9 on Tule Lake National Wildlife Refuge, California, 1999. 18 Tule Lake- Sucker Radio Telemetry ~ 1999 • Jit" Fish Sex Length: Tag Location: Tag Date: Sh oi1no so Male 440 mm Tule 1 < ikc 04/ 09/ 99 / Sucker Sump " H9" IA f tif( rtitiini / / i Kh< < 1- 1 . ri. l Mud FliitK 0 - 0 5 m 05 - 1 ni < SurfiKi 1 , - > 18m K V , , • l; , - n : , l , 5 , , , : . • „ • , '• • ' • • : ' k • ' s | ' ' ' s K i i. l I-. . . . tVu. I M i ^ ' ^ \ tbonn\ Wetl « nd « faiv « mor>. I . \ I A • » - i I M „, | i. Ih | || , , I M Figure 12. Movements of radio- marked sucker H9 on Tule Lake National Wildlife Refuge, California, 1999. 19 Tule Lake- Sucker Radio Telemetry - 1999 I- isii Lost River Sucker " 1 Sc\ Female Length: 775 mm Tag Location: Tule Lake Sump IA Tag Dale: 04/ 09/ 99 Mort. Date: ( Surface I* k^ atinn Tckmrtn: l.|| uk. I. K J y me l> I..: II> M K •-.•. I - I : . . , : Compkv • BPWS "' ••' Klmwlbl? ti » m A* MOffice I SBR IvckuioRv : \ atxin » l Wetlands biv « Mory. I > I / i < n k j f M U U l f i x • • • ' < • . • • Khri ( IM » tlr|> rh) Mat vh Wit I HI ii I LpbmJ Figure 13. Movements of radio- marked sucker 19 on Tule Lake National Wildlife Refuge, California, 1999. 20 Tule Lake- Sucker Radio Telemetry - 1999 Fish: I- osi River Sucker " P9" Sc\ Female Length: 7^ ' m m lag Location Anderson Rose Dam Tag Dale: 04/ 30/ 99 Mort. Date: ( Surface bk'talkm - 4UJ4. W) % mkm i .' i eraetn: |.| ikk* J. lkvl> « uui I) . . . . i - K '•.'. . - i . . r . . i . BMte Rvtug « , « ., .. . . - . M V . . Compk. i IPWa I « l.- . ll ,. t ,.. , , , | , , •. . „ ,. . | M i • E* K* gr° umi I K v H , ^ htaHml Wctl » nd » knvMori i -- I - s ^ • •• I •• I M i . , - It. > •—•• . i;-. i II . . i MWN Figure 14. Movements of radio- marked sucker P9 on Tule Lake National Wildlife Refuge, California, 1999. 21 Tule Lake- Sucker Radio Telemetry - 1999 Fish Lost River Sucker " i;(>" Sex Male Length: 556mm Tag Location Anderson Rose Dam Tag Date 05 05 w Mort. Date: ( Surface H o at ion - - MM4. W) • i • i n. t . i. ikJ^•. m..- I) . M. HV*. K Vi . • hnrnflh ii » m Hvfil^- '" I - I K ••. . I" K i r •• . M ... I MiM \-, ..,.•. \ , ,,.| v. , |,,.|. ( r. v : , f . l MH • . ! ., I M „ |. Figure 15. Movements of radio- marked sucker U9 on Tule Lake National Wildlife Refuge, California, 1999. 22 Tule Lake- Sucker Radio Telemetry - 1999 Fish: Lost River Sucker " W Sox: Male Leagth 486 mm \ AII Location; Anderson Rose Dam Tag Date: 05/ 05/ 99 Mort. Date: ( SurfiK- c Floaiiun 4 « . U. W| •• ' • •• ' • ; • ' ' ' ' I I I . . • 1. Bedu HI.- D . K V I " , I . < l: iMi; iTh : - i • : .1 MIK! KI. HH I - • • > • . • • \ 1 i i i v . v l . r i l - i r . v : • ! • . 1 • . . . 1 . • 1 \ | , , c 1. Figure 16. Movements of radio- marked sucker V9 on Tule Lake National Wildlife Refuge, California, 1999. 23 Tule Lake- Sucker Radio Telemetrv - 1999 Fish: Lost River Sticker " W(>" Sex: Male Length 594 nun I nil Location: Anderson Rose Dam Tag Date: 05/ 18/ 99 Meet. Date ( Surface H o at inn 4< i. U/) i » ') - ' • ' I ' : ' - ' • I Hid • i. Bcvl. v.' im: P . , i iikr. Klanwlh B* oi R< tu^ : . . r v . k v I M •'•- ' -*•• Mil - >•> • KlMmth IViim .\ wn 0 1 . . . I SBR g \ ^ m u l Wcllmls En^ :• r I ^ | V \ • • • I - i I M/ V. u- It; 1 ••••:•• .-.' II-. W Figure 17. Movements of radio- marked sucker W9 on Tule Lake National Wildlife Refuge, California, 1999. 24 Tule Lake- Sucker Radio Telemetry - 1999 Fish: Lost River Sucker " X9" Sex: Female Length 477 mm Tag Location; Anderson Rose Dam Tag Date: 05,1899 Mori. Date, suspected in June 1999 Hn i in Mat* h Will •. 1. fackn RadioTclenvtn; i. tfidbU. lkvk « ramLI>. r* Mmw « t K ','. . hmtdth B* m R^ UB* CompK- • n •'• • B % VJI < Kflb . I M i ,• h> tir> l Wetlands Envcntun. I SFft'S \ I , \ ' I K I I | , ... | s.| , \ s Figure 18. Movements of radio- marked sucker X9 on Tule Lake National Wildlife Refuge, California, 1999. 25 June - September - During this period, nearly all suckers ( particularly during July and August) could be found in the DH at the south central portion of Sump 1( A) ( Fig. 4). By connecting the outermost locations of approximately 90% of radio locations, the calculated area of the DH was 188 ha. Suckers using the DH were found in depths ranging from 1.0- 1.3 m ( 39- 50 in) ( Fig. 19). September - December - During this period suckers moved from the DH to the northwest corner of Sump 1( A). As of the writing of this report, ( February 15, 2000) the 13 remaining fish occupy the same area. Recruitment Surveys by Reclamation biologists for larval and juvenile suckers in the Lost River below Anderson- Rose Dam failed to document the presence young of the year fish. Below is a summary of surveys: Date 5/ 25/ 99 6/ 2/ 99 6/ 10/ 99 Result Searches for eggs in gravel below Anderson- Rose Dam revealed eggs in 4 of 5 sites, some of which were viable. Larval surveys conducted at 3 sites ( visual and dip net) from the dam to the wooden bridge were negative. Larval surveys conducted at 5 sites including the dam, 2 and 1 mile downstream, the wooden bridge, and East- West Road were negative. Larval surveys conducted at 2 sites downstream of dam were negative. Water quality pHBln general, pH values were less variable in the DH then areas outside this region ( Fig. 20). In all areas, median pH values remained below 9.5 until early June at which time values outside the DH were frequently above 10.0. pH values were particularly high (> 10.0) in late June through August in ESIB and NWS1A and periodically in the EC and WS1B. pH values in the DH and areas adjacent, remained below 10.0 through September; however, there was a gradual rise in pH values in DH sites from May through September. In late September and early October, DH pH values exceeded all other sites. rem/ reratareBTemperatures in all regions reached a peak in late July through early August with no discernible difference between DH or NDH sites ( Fig. 21). Dissolved oxvgenBDonut Hole sampling station s differed in dissolved oxygen characteristics relative to other areas of the sumps. During the June through August period DH sites ranged from 4.5 to 11.2 mg/ 1 while areas outside this region ranged from 1.1 mg/ 1 to 18.2 mg/ 1 ( Fig. 21). Toward November DH and NDH sites became similar DO dynamics ( Fig. 21). 26 Turbiditvllln general, turbidity values appeared greater in the DH versus areas outside, although some sites particularly in Sump 1( B) were quite variable particularly in June and July. This may have been due to the large amount of filamentous algae in Sump 1( B), potentially interfering with the measurement. Turbidity rose sharply at sites by late October and November ( Fig. 23- 24). 20 >• 1 5 O UJ a UJ DC 10 0 39 41 43 45 47 More DEPTH Figure 19. Water depth used by radio- marked suckers in the " Donut Hole" ( June- August), Tule Lake NWR. California. 27 BJll I U r S o I! Figure 20. pH data collected from " Donut Hole" and non- Donut Hole water quality sampling sites on Tule Lake National Wildlife Refuge, California, 1999. Box and whisker plots represent the median, 25- 75* and 10- 90* percentiles, and outliers. 28 temp rC) S 2 £ ' I j 1 II i 9 E 9 S Figure 21. Water temperatures collected at " Donut Hole" and non- Donut Hole sites on Tule Lake National Wildlife Refuge, California, 1999. Box and whisker plots represent the median, 25- 75^ and 10- 90^ percentiles, and outliers. 29 do ( mgfl) I do ( mg/ l) OP> !*• WKamm 01900 gGBM s ' S:' TP" » S i I ! if Figure 22. Dissolved oxygen concentrations at " Donut Hole" and non- Donut Hole sites on Tule Lake National Wildlife Refuge, California, 1999. Box and whisker plots represent the median, 25- 75* and 10- 90* percentiles, and outliers. 30 260.0 -. 240.0 220.0 - 200 0 180.0 => 160.0 H 140.0 - z 120.0 100.0 - 80.0 60.0 40.0 20.0 n n - » NT" —•— Depth ( m) fc= _ 6/ 2 107.00 0.8 Donut Hole Northwest - — .^^^ 6/ 7 77.20 0.8 H •—-^^ ' '—^ 6/ 14 25.30 0.8 6/ 21 24.80 0.8 - 1.0 o o O CJl depth ( m) 260.0 -, 240.0 220 0 200.0 180.0 - 2 160.0 z 140.0 - 120.0 100.0 - 80.0 - 60.0 40.0 20 0 0.0 » NTU — a— Depth ( m) , •=— mmm •= « a 6/ 22 44.00 0.9 Donut Hole West — « — — » - 6/ 28 26.60 08 •— 7/ 6 19.90 08 . ^ m — _ _ _ _ _ _ _ 7/ 13 25.70 0.8 • - _ — r- • 7/ 19 51.40 0.8 1.0 0.5 £ a. T3 0.0 260 0 240.0 - 220.0 - 200.0 - 180.0 i « n n _ H 140.0 - z 120 0 ^ 100.0 • 80 0 60.0 40.0 20.0 - u. u » NTU — m— Depth ( m) 6/ 22 93.70 0.8 6/ 28 95.40 0.7 Donut Hole East 7/ 6 72.70 0.7 7/ 13 32.30 0.7 —•'•"-""* 7/ 19 50.20 0.5 -*"— 7/ 28 62.50 0.8 8/ 2 73.30 0.8 \ ^ 8/ 10 18.55 0.8 8/ 19 50.20 0.8 8/ 25 22.20 0.8 8/ 31 58.67 0.7 \ 9/ 8 14.38 0.8 9/ 14 11.03 0.8 9/ 20 7.00 0.7 9/ 29 7.80 0.7 j / A - 10/ 25 51.00 0.7 t - fT u 11/ 23 210.00 0.6 1 0 - 0.5 JZ jepi - 0.0 Figure 23. Turbidity at " Donut Hole" sites on Tule Lake National Wildlife Refuge, California, May to November 1999. 31 260.0 i 240.0 220.0 200.0 180.0 3 160.0 £ 140.0 - 120.0 100.0 80.0 60.0 40.0 20.0 0.0 » NTU —•— Depth ( m) • ^ 6/ 2 81.10 0.8 Donut Hole - — - ^ 6/ 7 49.20 0.8 — • 6/ 14 21.50 0.8 =— 1 6/ 21 24.80 0.8 r 1 0 o p d en depth ( m) 260 0 240.0 • 220.0 - 200.0 . 180.0 - K 160.0 • z 140.0 - 120.0 100.0 80.0 . 60.0 - 40.0 - 20.0 0.0 . t K » TII — a— Depth ( m) B — • 7/ 21 53.30 0.8 .— m-— 7/ 28 40.50 0.8 Donut Hole South _—• 8/ 2 56.80 0 9 » - ^ 8/ 10 17.13 0.9 *—• 8/ 18 19.70 0 8 8/ 25 21.73 0.9 ^ \ 8/ 31 64.90 0.8 9/ 8 21.27 0.8 9/ 14 20.80 0.8 9/ 20 29.97 0.8 ^ - • - ^ 9/ 29 49.30 0.8 / / 10/ 25 33.70 0.8 / / 11/ 23 170.00 0.7 1 0 o o d en depth ( m) Figure 23 ( cont.). Turbidity at " Donut Hole" sites on Tule Lake National Wildlife Refuge, California, May- November, 1999. 32 260.0 -, 240.0 - 220.0 200.0 180.0 - 160.0 Z> 140.0 \ z 120.0 - z 100.0 80.0 60.0 40.0 20.0 - 0.0 *_ NTU • depth ( m) y 5/ 26 12.30 0.7 6/ 2 58.70 0.8 A- 6/ 7 20.30 0.9 / / 6/ 21 57.40 0.8 // A A\\ 6/ 28 239.0C 0.8 V\ East Sump 1B J s in 81.70 0.7 : / I 7/ 12 10.40 1.0 | A / \ J I s f 7/ 27 228.00 1.0 \ - V \ 8/ 2 88.00 0.8 8/ 10 40.00 0.9 8/ 18 38.17 0.8 8/ 31 11.30 0.7 9/ 9 7.00 0.7 9/ 14 6.17 0.7 9/ 20 5.83 0.7 • / 10/ 25 44.80 1.0 * 4-— \ ft . 11/ 23 186.00 0.5 1.0 ? e Q. 0.5 • 0.0 260.0 n 240.0 - 220.0 200.0 180.0 160.0 D 140.0 1— 120 0 z 100^ 0 80.0 60.0 An n 20.0 - 0.0 - —+— NTU —•— depth ( m) —•— 5/ 26 13.70 1.0 _, • —- « - 6/ 2 57.30 1.1 --•— ' \ 6/ 7 41.10 1.1 6/ 21 18.70 1.0 —•— / \ 6/ 28 138.0( 1.0 \ \ / ¥ West Sump 1B - . • — • / 7/ 7 ) 29.90 1.0 A \\ 7/ 12 88.90 1.0 k / \ / 7/ 27 19.00 0.9 / \ / \ 8/ 2 73.00 1.0 L \ \ 8/ 10 5.47 1.0 8/ 18 6.40 1.0 8/ 31 9.20 1.0 9/ 9 8.58 1.0 9/ 14 8.37 0.9 9/ 20 11.73 0.9 / / 10/ 25 39.50 0.7 f 11/ 23 85.00 0.8 1 5 sz Q. - 0 . 5 • - 0.0 260 0 240.0 220.0 - 200.0 - 180.0 160.0 3 140.0 t ; 120.0 100.0 80.0 - 60.0 An n . 20.0 0.0 » NT" — m— Depth ( m) 6/ 2 46.50 0.8 -~ « — 6/ 7 16.10 0.9 —•—. 6/ 14 39.00 0.8 / 6/ 22 9.71 0.8 English Channel Sump 1A 6/ 28 6.79 0.8 \ ^ _ 7/ 13 17.90 0.8 7/ 20 17.60 0.8 7/ 28 26.80 0.8 8/ 10 4.80 0.9 8/ 19 7.33 0.8 8/ 25 6.50 0.8 8/ 31 7.10 0.8 9/ 8 13.34 0.8 ==•== 9/ 20 15.50 0.8 J 9/ 29 22.60 0.7 — y / 10/ 25 98.70 0.8 11/ 23 146.00 0.8 1 5 - 1.0 — 0.5 - g 0.0 260 0 240.0 220 0 - 200.0 - 180.0 - 160.0 => 140.0 - £ 120.0 mnn . 60.0 40.0 - 20.0 u. u J •— NTU —•— Depth ( m) I 6/ 2 36.50 1.2 —•— 6 / 7 12.60 1.2 6/ 14 13.10 1.2 y 6/ 28 7.40 1.1 7/ 6 71.60 1.0 Northwest Sump 1A —•— 7/ 13 5.27 1.1 — » — —•— 7/ 19 28.50 1.1 7/ 28 20.50 1.2 8/ 2 32.10 1.2 ^- B—' 8/ 19 4.50 1.1 / 8/ 25 52.87 1.1 A ' \ 8/ 31 115.67 1.2 ="-•— \ —•*=; 9/ 8 4.10 1.1 1 4- 9/ 14 7.89 1.1 —•— J I \ 9/ 20 12.43 1.1 — « ^ 10/ 25 180.00 1.1 11/ 23 164.00 0.9 1 S d jpth ( m) • 0.5 - o - 0.0 Figure 24. Turbidity at non- Donut Hole sites on Tule Lake National Wildlife Refuge, California, 1999. 33 Discussion Water Quality The area of the DH was delineated from plotted June through September locations of radio-marked suckers ( approximately 188 ha.). The location of the DH could also be seen as an area of relatively turbid water from aerial photographs from August 1998 ( Fig. 25) as well as aerial photographs taken in 1984. It is possible that the combination of 2 factors may cause the observed turbidity in the DH. First, seeps or springs may be present in the area which result in more favorable water quality during summer which attracts suckers as well as other fish species to the area. The resultant concentration offish ( suckers and chubs) may stir the sediments during feeding activities, thereby creating the observed turbidity. The additional turbidity in the DH may inhibit light penetration and the production of algae, thereby reducing photo synthetically elevated pH and the extreme minimum and maximums in DO typical of may water bodies in the Klamath Basin including Tule Lake ( Dileanis et al. 1996). The rise in turbidity at all sites in fall is likely due to the break down of rooted aquatic vegetation which then allows for wind induced wave action to stir the sediments. Other than the DH, all other sites had dense concentrations of rooted aquatic plants and/ or filamentous green algae during summer. June to September DO and pH dynamics in the DH appeared different than at NDH sites ( Figs. 20 and 22). The difference was greatest in early summer with the difference becoming smaller by late summer and essentially disappearing by fall. Whether this water quality difference was a result of the more turbid waters or inflow from springs is unknown. However, attempts by Service hydrologists to model inflows, evapotranspiration, and outflows from the sumps have resulted in a positive imbalance of approximately 21,000 acre- feet of water from April through September. This positive imbalance is greatest in spring and early summer, gradually lessening by summer and essentially disappearing by fall ( Tim Mayer, pers. comm.). If this inflow is occurring, it may explain differences in summer water quality between DH and NDH sites. June to September water quality in the DH may be critical to the over summer survival of suckers in Tule Lake as pH and DO in NDH sites during summer often exceeded the tolerance limits for the fish. DO and pH levels at DH sites were less variable and did not reach the extremes that were reached in NDH sites. The lowest DO measured during June through September at DH sites were 4.83 mg/ 1 ( DHWEST) and 4.96 mg/ 1 ( DHEAST). DO and pH during summer from this study were similar to values collected by Reclamation in 1992 ( Table 3). Buettner and Scoppettone ( 1990) found juvenile suckers only where DO was above 4.5 mg/ 1. It is currently believed that adult suckers become stressed at DO levels below 4.0 mg/ 1 with mortality occurring at or below 2.0 mg/ 1 ( M. Buettner, pers. comm.). The relatively high over- summer survival of radio- marked suckers, compared to suckers radio- marked in Upper Klamath Lake ( M. Buettner, pers. comm), is further evidence of suitable summer water quality conditions in the DH on Tule Lake. 34 Figure 25. " Donut Hole" in Sump 1( A) of Tule Lake NWR. Note visible turbidity of area. 35 Table 3. Mean dissolved oxygen, pH, conductivity, and temperature on Tule Lake National Wildlife Refuge, California, July and August 1992. Data are from 2 sites; 1 site each in Sump 1( A) ( within the ADonut Hole@) and 1( B). All data were from 96 hour continuous readings from Hydrolabs. Data were collected at intervals of 1- 2 hours. ( Data summarized from U. S. Bureau of Reclamation). Site Sump 1( A) Sump ( IB) Depth ( M) < 0.5 0.51- 1.5 > 1.5 < 0.5 0.51- 1.5 > 1.5 pH (± SD) ( 1200- 1700 hrs) 9.32 ± 0.83 n= 81 9.22 ± 0.93 n= 26 8.30 ± 0.71 n= 10 9.65 + 0.44 n= 21 9.79 ± 0.45 n= 7 No data Temp ° C (± SD) ( 1200- 1700 hrs) 21.85 ± 2.84 n= 81 21.53 ± 2.46 n= 26 19.90 ± 1.59 n= 10 22.96+ 1.10 n= 21 22.11 ± 0.51 n= 7 No data Conductivity 500 ± 266 n= 81 598 ± 277 n= 26 859 ± 694 628 ± 148 n= 21 571 ± 74 n= 7 No data DO1 Oof 31 days - - 8 of 21 days - - 1 Proportion of monitored days having a minimum dissolved oxygen level below 5 mg/ 1. ( Data from U. S. Bureau of Reclamation) pH levels in the DH generally remained below 10.0 whereas non DH sites frequently exceeded 10.0 ( Fig. 19). Falter and Cech ( 1991) determined a maximum pH tolerance in shortnose suckers of 9.55+ 0.43 under laboratory conditions, levels generally exceeded in June - September at non DH sites and some DH sites in late summer. Buettner and Scoppettone ( 1990) found juvenile fish in Upper Klamath Lake largely at sites with pH < 9.0, as did Simon et al. ( 1996) in 1994. However, in 1995, Simon et al. ( 1996) found that most juvenile fish ( 54%) were captured in areas of higher pH (> 10.0). Laboratory studies indicate significant mortality of larval and juvenile fish at high pH values (> 9.55) ( Falter and Cech 1991) and 9.92- 10.46 ( Bellerud and Saiki 1995). Previous water quality and fish health studies on the refuge determined that water quality conditions were stressful to aquatic life and was resulting in a high ( up to 37%) proportion offish with deformities ( Dileanis et al. 1996), however, studies of sucker ecology in Tule Lake have indicated that individual fish in the lake have a high condition factor and are free of external parasites ( Scoppettone and Buettner 1995). Bennet ( 1994) recognized this apparent inconsistency, stating, A... the observation that Tule Lake suckers are in better physical condition than Upper Klamath Lake suckers indicates that certain areas of the aquatic system may be of particular importance for the recovery of those species. ® In the case of Tule Lake this Acertain area@ is likely the DH.. Suckers in Tule Lake may be in good condition because of their limited population size, the abundant food resources in this lake, and adequate water quality ( in the DH) to survive the summer period. 36 Sucker movements Although, suckers were relatively sedentary during most periods of the year, they exhibited the ability to make long distance moves in relatively short periods of time, particularly during the April spawning period. The northwest corner of Sump 1( A) receives about 90% of the inflow from the Lost River and spring winds on Tule Lake tend to move large quantities of water through the AEnglish Channels back and forth between Sump 1( A) and 1( B). This movement of water at both locations may explain the movement of fish observed in April and May. Suckers may be attracted to both locations when seeking spawning habitat in spring. Recruitment During the April marking period, most captured suckers appeared to be physiologically ready to spawn; however, only one fish moved into the river. Of 10 radio- marked fish monitored by Reclamation in 1993- 95 no fish attempted to run the Lost River. This low proportion offish that attempt to spawn may have one or several causes or a combination, including: 1. Stress of handling and implanting radio- transmitters so close to the spawning season may prevent fish from becoming reproductively active. 2. Under normal conditions, only a small proportion of Tule Lake suckers may attempt to spawn in any particular year. 3. Flow conditions in or at the mouth of the Lost River may be inadequate to draw the fish into the river. 4. A shallow bar (< 0.3 m) of deposited silt exists between the lake and the mouth of the river which may form a physical barrier to the fish. At the present time, a mandated flow of 30 cfs is released below Anderson- Rose Dam to provide spawning habitat at the Dam. Although this flow is intended to provide suitable spawning conditions at the Dam, these flows may be inadequate to entice fish into the river. It is likely that the historic spring flows in the Lost River were many times higher than current regulated flows. However, given that the fish are largely unsuccessful in spawning and risk additional mortality traversing the river, adult survival may be enhanced by remaining in the lake. Scoppettone and Buettner ( 1995) also observed no radio- marked fish from Clear Lake to move into Willow Creek during the spring spawning period. In this case the authors attributed this result to either capture stress or low stream flows during spring. 37 Habitat use Although the DH is relatively shallow relative to other areas of Tule Lake, use of the DH may be mandatory to ensure over- summer survival. Although deeper waters are available to the fish, especially in the northwest corner of Sump 1( A), DO levels, in particular, likely preclude their use. Suckers did not move out of the DH until October when DO levels began to rise with cooler water temperatures. Although, Sump 1( B) contained suitable water depths and water quality conditions in fall, no suckers were located in this area. It is possible that suckers may prefer not to pass through the pipes connecting the Sumps or the proximity and flow from the Lost River in the northwest corner of Sump 1( A) may make this area more attractive as an over- winter habitat area. The relative lack of water depth in the DH as well as other areas of the sumps is becoming of increasing concern because of the loss of water depth through sedimentation. If suckers require a minimum of 3 ft of water, as is current believed ( M. Buettner, pers. comm.), current rates of sedimentation in the sumps threaten the future suitability of Tule Lake for suckers. Based on a comparison of bathymetric surveys conducted by Reclamation in 1958 and again in 1986, sedimentation has been steadily reducing the water holding capacity of both sumps. Between the 1958 and 1986 surveys ( 28 years), Sump 1( A) has lost 22.4% of its water capacity and Sump 1( B) has lost 30.8% of its capacity due to sedimentation. This would indicate a total mean sedimentation of 11.8 inches over this time period ( U. S. Bureau of Reclamation, unpubl. rep). Over the last several years, an attempt has been made to store additional water in Tule Lake during summer by raising water levels above 4034.60 ft. This increase in water elevations ( between 4034.60 and 4034.90 ft) has somewhat mitigated the loss of depth through sedimentation. However, without reinforcing and raising the levees around the sumps, there is a limit as to how high water elevations can rise. At elevation 4035.50 ft., operating regulations require breaching the sumps into overflow areas ( Sump 2 or 3). Although increased summer operating levels may assist the fish, they may also increase the risk of a flood event requiring the breaching of the sumps with potentially negative impacts to the fish. Acknowledgements The authors are indebted to fisheries biologist from the U. S. Bureau of Reclamation, Klamath Project, especially M. Buettner, B. Peck, and M. Green whom provided and surgically implanted radio transmitters, captured adult suckers, located fish from fixed wing aircraft, and assisted with study design. K. Miller from Klamath Basin National Wildlife Refuge collected telemetry, water quality, and GPS data and ensured all data were collected and coordinated consistent with study design. T. Mayer provide training in the calibration, deployment, and downloading of data from the hydrolabs and assisted with interpretation of water quality data. 38 Personnel Communications Buettner, M., Fisheries Biologist, U. S. Bureau of Reclamation, Klamath Project Office, 6600 Washburn Way, Klamath Falls, Oregon. Mayer, T., Hydrologist, U. S. Fish and Wildlife Service, Portland Regional Office, Lloyd Center, Portland, Oregon. Literature Cited Bellerud, B., and M. K. Saiki. 1995. Tolerance of larval and juvenile Lost River and shortnose suckers to high ph, ammonia concentration, and temperature, and to low dissolved oxygen concentration, National Biological Service, California Pacific Science Center, Dixon 103pp. Bennett, J. K. 1994. Bioassessment of irrigation drain water effects on aquatic resources in the Klamath Basin of California and Oregon. Ph. D Dissertation. University of Washington, Seattle. 197pp. Buettner, M. E., and G. Scoppettone. 1990. Life history and status of catostomids in Upper Klamath Lake, Oregon. National Fisheries Research Center, Reno Field Station, Reno, Nevada, 108pp. Coots, M. 1965. Occurrences of the Lost River sucker, Deltistes luxatus ( Cope), and shortnose sucker, Chasmistes brevirostris ( Cope), in Northern California. Calif. Fish and Game 51: 68- 73. Dileanis, P. D., S. K. Schwarzbach, and J. K. Bennett. 1996. Detailed study of water quality, bottom sediment, and biota associated with irrigation drainage in the Klamath Basin, California and Oregon, 1990- 92. U. S. Geological Survey, Water- Resources Investigations Report 95- 4232, 68pp. Falter, M. A., and J. J. Cech. 1991. Maximum pH tolerance of three Klamath Basin fishes. Copia 4: 1109- 1 111. Simon, D. C, G. R. Hoff, D. J. Logan, and D. F. Markle. 1996. Larval and juvenile ecology of Upper Klamath Lake suckers. Annual Report: 1995, Department of Fisheries and Wildlife, Oregon State Univ., Corvallis. 60pp. 39 Scoppettone, G. G., and M. E. Buettner. 1995. Information on population dynamics and life history of shortnose suckers ( Chasmistes brevirostris) and Lost River suckers ( Deltistes luxatus) in Tule and Clear Lakes. U. S. Geological Survey, Reno Field Station, Reno, Nevada. 79pp. U. S. Bureau of Reclamation. 1998. Lost River and shortnose sucker spawning in Lower Lost River, Oregon, U. S. Bureau of Reclamation, Klamath Falls, Oregon. 1 lpp. . 1993. Lost River { Deltistes luxatus) and shortnose { Chasmistes brevirostris) Sucker Recovery Plan. Portland, Oregon 108pp. Hydrolab Corporation. 1997. DataSondeR 4 and MiniSondeR water quality multiprobes, users manual. Hydrolab Corp., Austin, Texas.
-
19 p.; Caption title; "November 19, 2004"
Citation Citation
- Title:
- Critical Habitat Reform Act of 2004: report together with dissenting views (to accompany H.R. 2933) (including cost estimate of the Congressional Budget Office)
- Author:
- United States. Congress. House. Committee on Resources
- Year:
- 2004, 2006, 2005
19 p.; Caption title; "November 19, 2004"
-
29244. [Image] Nitrogen and phosphorus loading from drained wetlands adjacent to Upper Klamath and Agency Lakes, Oregon
Two maps digitized separately; Includes bibliographical references (p. 44-49)Citation -
"Serial no. 108-104."
Citation Citation
- Title:
- Oversight field hearing on the Endangered Species Act 30 years later : the Klamath Project : oversight field hearing before the Subcommittee on Water and Power of the Committee on Resources, House of Representatives, One Hundred Eighth Congress, second session, Saturday, July 17, 2004, in Klamath Falls, Oregon
- Author:
- United States. Congress. House. Committee on Resources. Subcommittee on Water and Power
- Year:
- 2005
"Serial no. 108-104."
-
Determining Surface Water Availability in Oregon By Richard M. Cooper, PE Abstract The Oregon Water Resources Department (Department or OWRD) limits appropriation from Oregon streams to assure new applicants ...
Citation Citation
- Title:
- Determining surface water availability in Oregon : open file report SW 02-002
- Author:
- Oregon. Water Resources Dept.
- Year:
- 2002, 2005
Determining Surface Water Availability in Oregon By Richard M. Cooper, PE Abstract The Oregon Water Resources Department (Department or OWRD) limits appropriation from Oregon streams to assure new applicants use of surface water a reasonable amount of time and to minimize regulatory conflict. The standards for new appropriation of water are: (1) consumptive use from allocations for out-of-stream uses can total no more than the 80-percent ex-ceedance natural stream flow, and (2) allocations for in-stream flows can be no more than the 50-percent exceedance natural stream flow. OWRD has created and maintains a database of the amount of surface water available for appropriation for most waters in the state. This database is used to evaluate applications for new uses of water. Water availability (WA) is obtained from natural stream flow (QNSF) by subtracting existing storage (ST), out-of-stream consumptive uses (CU) and in-stream demands (IS). WA = QN -ST-CU-IS Ideally, water availability would be calculated for every watershed above a point of diversion or in-stream demand. Practically, the number of watersheds must be limited. The watersheds selected for analysis are called Water Availability Basins (WABs). Stream flow can be highly variable, and it is useful to characterize it in some way, usually by a statistic, e.g., a monthly or annual mean. For water availability, it is important to know how often water is available. The appropriate statistic in this case is exceedance stream flow. This statistic tells us how often to expect a given rate of stream flow to occur. Exceedance stream flows are determined directly from gage records, or for ungaged streams, by estimation through modeling. When determined from gage records, the exceedance flows must be corrected to a common base period, and then, to natural stream flow. When determined through modeling, the exceedance flows are estimated from statistical models that relate watershed characteristics to natural stream flow. The models are derived by multiple linear regression. Storage is water retained in a reservoir. It is debited from water availability when the water is stored. It diminishes availability both upstream and downstream of the point of diversion. Consumptive use is divided into three major categories: irrigation, municipal, and all others e.g., domestic, livestock. These uses are less than 100 percent consumptive. It is assumed the non-consumed part of a diversion is returned to the stream from which it was diverted. Consumptive use from irrigation is from estimates made by the US Geological Survey (Portland). Consumption from other uses is based on the associated water rights. In these cases, consumptive use is obtained by multiplying the maximum diversion rate allowed for the water right by a consumptive use coefficient. Consumptive use diminishes availability both upstream and downstream of the point of diversion. There are two types of in-stream demands: in-stream water rights and scenic waterway flows. In-stream demands diminish availability upstream only. Because they are non-consumptive, they do not diminish stream flow downstream as do consumptive uses. Water availability has been calculated for over 2500 WABs. In general, the calculation of water availability at one WAB cannot be considered in isolation from other WABs in the same stream system. For water to be available at any given upstream point, it must be available at all points of calculation downstream.
-
29247. [Image] Final progress report for fisheries investigations on Blue Creek, tributary to Klamath River, northern California, FY 1993
FINAL PROGRESS REPORT FOR FISHERIES INVESTIGATIONS ON BLUE CREEK, TRIBUTARY TO K1AMATH RIVER, NORTHERN CALIFORNIA FY 1993 (October 1992 - September 1993) ABSTRACT The U.S. Fish and Wildlife Service, ...Citation Citation
- Title:
- Final progress report for fisheries investigations on Blue Creek, tributary to Klamath River, northern California, FY 1993
- Author:
- Longenbaugh, Matthew H.; Chan, Jeffrey R.
- Year:
- 1994, 2008, 2005
FINAL PROGRESS REPORT FOR FISHERIES INVESTIGATIONS ON BLUE CREEK, TRIBUTARY TO K1AMATH RIVER, NORTHERN CALIFORNIA FY 1993 (October 1992 - September 1993) ABSTRACT The U.S. Fish and Wildlife Service, Coastal California Fishery Resource Office (CCFRO) in Arcata, CA, was funded to investigate chinook salmon spawning use, juvenile salmonid emigration and characterize habitats in Blue Creek, Klamath Basin, CA. Investigations that began in October, 1988, have continued to date, with this reporting period covering Fiscal Year 1993 (FY 1993, October, 1992, through September, 1993). In addition, some information already presented in previous progress reports, FY 1989 - FY 1992, is summarized. In 1993, adult chinook spawner escapements were addressed by snorkel surveys of redds and carcasses. Spawner numbers were very low, with only 17 redds observed in fall/winter 1992-93. The peak count of adult chinook was 136 fish in early November. Emigrating juvenile s&lmonids were trapped at river kilometer (rkm) 3.35 with a screw trap and panel weir. The screw trapping period extended from April through July for a total of 91 trapping nights. Screw trap catches totaled 14,526 chinook, 912 steelhead and 69 coho. Chinook emigration was spread over the entire trapping period, with increases during mid-May, and from mid-June throughout July. A juvenile weir was operated 60 nights, and caught a total of 6,334 chinook, 992 steelhead, 49 coho salmon, and 0 juvenile cutthroat. The total index of production for emigrating chinook during the 1993 juvenile trapping period was 101,819. Chinook that were marked with coded-wire tags (n-12,299) were released, with other juvenile fish, into Blue Creek at rkm 3.3. Mean temperatures varied from 6.3 to 18.6 ?C and flows ranged from 0.91 cubic m/s (32 cubic feet/s) to 202.6 cubic m/s (7,160 cubic feet/s) during FY 1993. Extreme flows for FY 1993 were the lowest and highest observed by CCFRO since the project began in 1989, and lower than the previous low of the 13 years of record.
-
Summary The Upper Klamath Basin (UKB) is a high desert region straddling the California-Oregon border east of the Cascade Range. Irrigation and other agricultural practices in the U. S. Bureau of Reclamation's ...
Citation Citation
- Title:
- Farming practices and water quality in the Upper Klamath Basin : final report to the California State Water Resources Control Board : 205j program
- Author:
- Danosky, Earl; Kaffka, Stephen
- Year:
- 2002, 2007, 2006
Summary The Upper Klamath Basin (UKB) is a high desert region straddling the California-Oregon border east of the Cascade Range. Irrigation and other agricultural practices in the U. S. Bureau of Reclamation's Klamath Project may result in impaired surface water quality, reducing its use for wildlife and fish in important national wildlife refuges that receive drainage water from farms, and in the Klamath River. By 2004, a system of total maximum daily loads (TMDL) for nutrients must be established for the Klamath River. To investigate the relationships among agricultural practices and surface water quality in the Upper Klamath Basin, a two year reconnaissance survey of surface water and agricultural tile drain locations, focusing on nitrogen and phosphorus concentrations and mass transfers was conducted. Data was collected at 18 surface locations and 10 tile drain locations. Triplicate samples were taken every ten days during the growing season (April through October) and one or two times a month during the remainder of the months, depending on opportunity. No samples were taken from tile drains during the winter months because there was no irrigation and drainage during that period. Water samples were analyzed for phosphorus (total P, soluble reactive P, total filterable P, and particulate P) and nitrogen (total N, soluble N, Soluble organic N, total filterable N, particulate N, and ammonia N), temperature, pH and electrical conductivity, a measure of salinity or total dissolved solids. Analyses of data, including data quality, estimates of the transfer of nutrients in surface waters in the region, and hypotheses about the relationship between agriculture and water quality are reported. 1. The salt and nutrient content of surface waters increases nearly threefold as water moves through the watershed from the Lost River and J canal diversion to the Klamath Straits Drain. Mean ECW levels in input waters at the J canal diversion were approximately 250 \iS cm1, while water sampled at the D pump increased to 600 ^S cm"1 on average over the sample period. By the time water reenters the Klamath River, salt concentrations have increased to approximately 700 jaS cm1. 2. The ECW values observed in subsurface tile drains were higher on average than in input waters and surface waters elsewhere in the region, especially in the Lease Lands area of the Tulelake Irrigation District (TID). ECW values averaged approximately 2,500 ^S cm"1 . Recycling irrigation water through soils in the TID increases the salinity of the water, especially by the time it reaches and is reused in the Lease Lands area of the Tulelake National Wildlife Refuge (TLNWR). Soils in this part of the Klamath Project area are naturally high in salt. 3. Water temperatures in agricultural subsurface tile drains were significantly lower than surface water temperatures during the growing season when tile drains were active. pH values in tile drains were lower than surface water values. The temperature and pH of tile drains does not influence surface water values. 1. 4. For total phosphorus (TP) input waters at the J canal irrigation diversion for the TED averaged approximately 0.27 mg L1 for the two years reported. Water leaving the Tulelake Sumps at the D pump increases to 0.33 mg L1. Water leaving the Lower Klamath National Wildlife Refuge (LKNWR) sampled at the start of the Klamath Straits Drain, averaged 0.33 mg L1, similar to those at the D pump. TP increased further to 0.40 mg L"1 a the end of the Klamath Straits Drain. The overall increase in P concentration in surface waters was much less than for salt, suggesting that processes other than simple enrichment are occurring, particularly those associated with the exchange of sedimentary P and aquatic plant species. TN increases from 2.3 mg L"1 to 4.0 mg L1 over the same pathway. Atomic ratios (TN:TP) of surface water samples remain constant at approximately 10:1 throughout the system, suggesting that the amount of sediment and other small particulate matter in surface waters affects the values observed. The amount of sediment is influenced in part by the agitation of surface water as it passes through pumps and over weirs. 5. The average seasonal TP value in tile drains beneath farm fields is approximately 0.34 mg L"1 . While average total P values in subsurface tile drains were not different from those found at the D pump and the LKNWR outlet, the range in values was great (0.1 to 0.8 mg L1). Similarly, high NO3 -N values were observed at times in tile drains. Very high values in tile drains lead to the inference that some fertilizer N and P is lost in drainage water, combined with nutrients derived from decaying soil organic matter. The amount estimated as lost is much less than the amount of surplus fertilizer P applied and the amount of P surmised to be mineralized from decaying soil organic matter. P from fertilizer and decaying organic matter appears to be accumulating in soils and lake sediments in the region. 6. Ammonia N concentrations are at or below the limit of detection in subsurface agricultural tile lines and one to two orders of magnitude below the values observed in surface soils. Un ionized ammonia increases with temperature. Values above 0.25 mg L1 were observed in late summer at several locations. 7. Some leaching of soluble salts and nutrients is unavoidable when crops are irrigated. P fertilizer is applied at rates higher than crop removal, while fertilizer n is applied at rates less than crop removal. Reduced fertilizer use can help bring P inputs and outputs into balance and may reduce further any avoidable losses of P. This objective should be the subject of an agronomic research program in the region. 8. Surface waters entering the TDD, the TLNWR, and the LKNWR are already enriched with N and P. It seems unlikely that reducing N and P losses from farming in the TID, if possible, would influence surface water quality sufficiently to make them significantly less eutrophic. For P, the hypothesized threshold concentration limiting algae growth in fresh waters is 5 to 25 times smaller than the values observed in waters entering the TID for irrigation use. The addition of 1. nutrients from agriculture probably does not influence significantly surface water quality in the region. Wetland sediments, large amounts of organic matter in soils, and water introduced for irrigation contain essentially unlimited amounts of nutrients for aquatic plant growth. It is not clear how this circumstance could be changed under any reasonable time frame, if ever. 9. Using a TMDL approach may not result in reduced amounts of nutrients returned to the Klamath River because wetlands and farming practices in the southern portion of the Klamath Project result in the net removal of nutrients from the waters diverted for irrigation on a yearly basis, compared to allowing the same amount of water simply to flow down the river unused. Because of large errors of estimation for the amounts of water transferred, combined with smaller errors associated with estimating nutrient concentrations in water samples, and with year to year climate variation, TMDLs may not be an effective or efficient means of reducing nutrients in return flows to the Klamath River. Rational confidence limits for TMDLs may have to be too broad to be effective. Recycling of some drainage water for irrigation would reduce the amount of nutrients returned to the river more effectively than implementing a TMDL program.
-
29249. [Image] Status of Oregon's bull trout : distribution, life history, limiting factors, management considerations, and status
EXECUTIVE SUMMARY Limited historical references indicate that bull trout Salvelinus confluentus in Oregon were once widely spread throughout at least 12 basins in the Klamath River and Columbia River ...Citation Citation
- Title:
- Status of Oregon's bull trout : distribution, life history, limiting factors, management considerations, and status
- Author:
- Buchanan, David V; Hanson, Mary L; Hooton, Robert M
- Year:
- 1997, 2007, 2005
EXECUTIVE SUMMARY Limited historical references indicate that bull trout Salvelinus confluentus in Oregon were once widely spread throughout at least 12 basins in the Klamath River and Columbia River systems. No bull trout have been observed in Oregon's coastal systems. A total of 69 bull trout populations in 12 basins are currently identified in Oregon. A comparison of the 1991 bull trout status (Ratliff and Ho well 1992) to the revised 1996 status found that 7 populations were newly discovered and 1 population showed a positive or upgraded status while 22 populations showed a negative or downgraded status. The general downgrading of 32% of Oregon's bull trout populations appears largely due to increased survey efforts and increased survey accuracy rather than reduced numbers or distribution. However, three populations in the upper Klamath Basin, two in the Walla Walla Basin, and one in the Willamette Basin showed decreases in estimated population abundance or distribution. Some Oregon river basins have bull trout populations at extreme risk of extinction. This statewide status review listed only 19% of the bull trout populations in Oregon with a ulow risk of extinction" or "of special concern." Therefore, 81% of Oregon's bull trout populations are considered to be at a "moderate risk of extinction," "high risk of extinction," or "probably extinct." Populations in the Hood, Klamath, and Powder basins, as well as the Odell Lake population in the Deschutes basin, which contain only a few remaining bull trout, are examples of populations having a "moderate" or "high risk" of extinction. Approximately 55% of current bull trout distribution occurs on lands managed by the U.S. Forest Service. A much smaller proportion occurs on Bureau of Land Management managed lands (2%). Only 16% of current bull trout distribution occurs within a protected area defined as Wilderness, Wild and Scenic River, or within a National Park. The Northwest Forest Plan, Inland Native Fish Strategy, and Interim Strategies for Managing Anadromous Fish-producing Watersheds in Eastern Oregon and Washington, Idaho, and Portions of California have provided increased protection for bull trout habitat depending on their scope and geographic areas affected, and the extent to which they are being effectively implemented in watersheds containing bull trout. Recent reduction in timber production on National Forests (up to 50% in western Oregon National Forests and over 30% in eastern Oregon National Forests) should help improve riparian and stream habitat conditions for bull trout. The remaining bull trout distribution occurs on private, state, or tribal owned lands. A comparison of approximately 39 locations throughout the state with protective angling regulations on bull trout (in some areas more than one bull trout population is protected by one regulation) shows that all state managed areas were upgraded in a protective angling status or at least maintained in 1996 compared to 1989. Restrictive angling regulations prohibit angler harvest of all bull trout populations in Oregon except for one in the Deschutes Basin. Restrictive bull trout angling regulation changes (including the elimination of bull Vll trout harvest in all spawning areas) may be the major reasons why the Metolius River/Lake Billy Chinook and mainstem McKenzie River populations have shown significant increases in abundance. Statewide stocking of non-native brook trout, including the high lakes stocking program, has been discontinued in locations where managers believe brook trout could migrate downstream and potentially interact with native bull trout. Hatchery stocking of legal rainbow trout to promote recreational fisheries has been discontinued in most locations near bull trout populations to avoid incidental catch of bull trout. The spatial and temporal distributions of bull trout reported for each river basin in this status report should be used as an accurate baseline for fisheries managers. Current distribution and relative change of distribution should be useful indicators of population health and status. The GIS maps in this report provide a template to add new layers of data such as critical spawning and juvenile rearing areas, or as a method to compare distribution changes through time. Length frequency data are presented for most Oregon bull trout populations. This should provide estimates for the presence of multiple age classes and the percent of fluvial size life history component. Vlll
-
29250. [Image] Klamath River water quality and acoustic Doppler current profiler data from Link River Dam to Keno Dam, 2007
Klamath River Water Quality and Acoustic Doppler Current Profiler Data from Link River Dam to Keno Dam, 2007 By Annett B. Sullivan, Michael L. Deas, Jessica Asbill, Julie D. Kirshtein, Kenna Butler, Roy ...Citation Citation
- Title:
- Klamath River water quality and acoustic Doppler current profiler data from Link River Dam to Keno Dam, 2007
- Author:
- Sullivan, Annett B. (Annett Brigitte), 1970-
- Year:
- 2008
Klamath River Water Quality and Acoustic Doppler Current Profiler Data from Link River Dam to Keno Dam, 2007 By Annett B. Sullivan, Michael L. Deas, Jessica Asbill, Julie D. Kirshtein, Kenna Butler, Roy E. Wellman, Marc A. Stewart, and Jennifer Vaughn Abstract In 2007, the U.S. Geological Survey, Watercourse Engineering, and Bureau of Reclamation began a project to construct and calibrate a water quality and hydrodynamic model of the 21-mile reach of the Klamath River from Link River Dam to Keno Dam. To provide a basis for this work, data collection and experimental work were planned for 2007 and 2008. This report documents sampling and analytical methods and presents data from the first year of work. To determine water velocities and discharge, a series of cross-sectional acoustic Doppler current profiler (ADCP) measurements were made on the mainstem and four canals on May 30 and September 19, 2007. Water quality was sampled weekly at five mainstem sites and five tributaries from early April through early November, 2007. Constituents reported here include field parameters (water temperature, pH, dissolved oxygen concentration, specific conductance); total nitrogen and phosphorus; particulate carbon and nitrogen; filtered orthophosphate, nitrite, nitrite plus nitrate, ammonia, organic carbon, iron, silica, and alkalinity; specific UV absorbance at 254 nm; phytoplankton and zooplankton enumeration and species identification; and bacterial abundance and morphological subgroups. The ADCP measurements conducted in good weather conditions in May showed that four major canals accounted for most changes in discharge along the mainstem on that day. Direction of velocity at measured locations was fairly homogeneous across the channel, while velocities were generally lowest near the bottom, and highest near surface, ranging from 0.0 to 0.8 ft/s. Measurements in September, made in windy conditions, raised questions about the effect of wind on flow. Most nutrient and carbon concentrations were lowest in spring, increased and remained elevated in summer, and decreased in fall. Dissolved nitrite plus nitrate and nitrite had a different seasonal cycle and were below detection or at low concentration in summer. Many nutrient and carbon concentrations were similar at the top and bottom of the water column, though ammonia and particulate carbon showed more variability in summer. Averaged over the season, particulate carbon and particulate nitrogen decreased in the downstream direction, while ammonia and orthophosphate concentrations increased in the downstream direction. At most sites, bacteria, phytoplankton, and zooplankton populations reached their maximums in summer. Large bacterial cells made up most of the bacteria biovolume, though cocci were the most numerous bacteria type. The cocci were smaller than the filter pore sizes used to separate dissolved from particulate matter in this study. Phytoplankton biovolumes were dominated by the blue-green alga Aphanizomenonflos aquae most of the sampling season, though a spring diatom bloom occurred. Phytoplankton biovolumes were generally highest at the upstream Link River and Railroad Bridge sites and decreased in the downstream direction. Zooplankton populations were dominated by copepods in early spring, and by cladocerans and rotifers in summer, with rotifers more common farther downstream. l